220319

UNITED NATIONS

BC

UNEP/CHW.14/INF/9

Distr.: General

18 March 2019

English only

Conference of the Parties to the Basel Convention

on the Control of Transboundary Movements of

Hazardous Wastes and Their Disposal

Fourteenth meeting

Geneva, 29 April–10 May 2019

Item 4 (b) (i) of the provisional agenda

Matters related to the implementation of the

Convention: scientific and technical matters:

technical guidelines

Compilation of comments received from Parties and others on

the draft updated general technical guidelines and four newly

developed technical guidelines on wastes consisting of,

containing or contaminated with persistent organic pollutants

Note by the Secretariat

1. As is mentioned in the note by the Secretariat on technical guidelines (UNEP/CHW.14/7), the

annexes to the present note set out the compilation of comments received from Parties and others on

the draft new and updated technical guidelines as per paragraphs 5 and 6 of decision OEWG-11/3.

Comments were received from the European Union and its Member States, the European Automobile

Manufacturers' Association (ACEA), Bromine Science Environmental Forum (BSEF), Confederation

of European Waste-to-Energy Plants (CEWEP), Research and Education Center for Developent

(CREPD), European Electronics Recyclers Association (EERA), European HBCD Industry Working

Group (HBCD IG), Hazardous Waste Europe and IPEN.1

2. Annex I contains comments regarding document UNEP/CHW.14/7/Add.1; Annex II contains

comments regarding document UNEP/CHW.14/7/Add.2; Annex III contains comments regarding

document UNEP/CHW.14/7/Add.3; Annex IV contains comments regarding document

UNEP/CHW.14/7/Add.4; and Annex V contains comments regarding document

UNEP/CHW.14/7/Add.5.

3. The present note, including its annexes, has not been formally edited.

UNEP/CHW.14/1. 1 The comments provided are also available on the Convention website:

http://www.basel.int/Implementation/POPsWastes/TechnicalGuidelines/CommentsbeforeCOP14/tabid/7958/Defa

ult.aspx

UNEP/CHW.14/INF/9

2

Annex I

Compilation of comments regarding document

UNEP/CHW.14/7/Add.1 (General technical guidelines)

1. The Secretariat has received comments regarding document UNEP/CHW.14/7/Add.1 from:

the European Union and its Member States, from European Automobile Manufacturers' Association

(ACEA), Confederation of European Waste-to-Energy Plants (CEWEP), Research and Education

Center for Developent (CREPD), European Electronics Recyclers Association (EERA), European

HBCD Industry Working Group (HBCD IG), Hazardous Waste Europe and IPEN.

2. Comments from the EU and its Member States, ACEA, CEWEP, HBCD IG and Hazardous

Waste Europe are presented in the draft technical guidelines themselves.

3. Comments from CREPD, EERA and IPEN follow in a separate section after the technical

guidelines.

UNEP/CHW.14/INF/9

3

1. Comments from the European Union and its Member States, ACEA,

CEWEP, HBCD IG and Hazardous Waste Europe

Draft updated general technical guidelines on the environmentally sound

management of wastes consisting of, containing or contaminated with

persistent organic pollutants

(Draft of 8 November 2018)

General comments

The European Union and its Member States have a few comments shown highlighted in yellow.

We would like to flag that we do not have comments on the low POP contents at this stage. As to

the low POP contents, we would like to draw attention to a study commissioned by the European

Commission which is available at:

http://ec.europa.eu/environment/waste/pdf/Study_POPS_Waste_final.pdf

UNEP/CHW.14/INF/9

4

Contents

Abbreviations and acronyms ................................................................................................................ 6

Units of measurement ........................................................................................................................... 7

I. Introduction ................................................................................................................................ 8

A. Scope ....................................................................................................................................... 8 B. About POPs and POP wastes ............................................................................................... 11

II. Relevant provisions of the Basel and Stockholm conventions .............................................. 11 A. Basel Convention .................................................................................................................. 12

1. General provisions .................................................................................................... 12 2. POP-related provisions ............................................................................................. 13

B. Stockholm Convention ......................................................................................................... 13 1. General provisions .................................................................................................... 13 2. Waste-related provisions .......................................................................................... 14

III. Issues under the Stockholm Convention to be addressed cooperatively with the Basel

Convention ................................................................................................................................ 15

A. Low POP content .................................................................................................................. 15 B. Levels of destruction and irreversible transformation........................................................ 18 C. Methods that constitute environmentally sound disposal .................................................. 18

IV. Guidance on environmentally sound management (ESM) ................................................... 19

A. General considerations ......................................................................................................... 19 B. Legislative and regulatory framework ................................................................................ 19

1. Phase-out dates for production and use of POPs .................................................... 20 2. Transboundary movement requirements ................................................................. 20 3. Specifications for containers, equipment, bulk containers and storage sites

containing POPs ........................................................................................................ 21 4. Health and safety ...................................................................................................... 21 5. Specification of acceptable procedures for sampling and analysis of POPs ......... 21 6. Requirements for hazardous waste treatment and disposal facilities .................... 21 7. General requirement for public participation .......................................................... 21 8. Contaminated sites .................................................................................................... 22 9. Other legislative controls ......................................................................................... 22

C. Waste prevention and minimization .................................................................................... 22 D. Identification of wastes ........................................................................................................ 23

1. General considerations ............................................................................................. 23 2. Inventories ................................................................................................................. 24

E. Sampling, analysis and monitoring ..................................................................................... 25 1. Sampling .................................................................................................................... 25 2. Analysis ..................................................................................................................... 26 3. Monitoring ................................................................................................................. 28

F. Handling, collection, packaging, labelling, transportation and storage ............................ 29 1. Handling .................................................................................................................... 29 2. Collection .................................................................................................................. 30 3. Packaging .................................................................................................................. 31 4. Labelling .................................................................................................................... 32 5. Transportation ........................................................................................................... 32 6. Storage ....................................................................................................................... 32

G. Environmentally sound disposal .......................................................................................... 34 1. Pre-treatment ............................................................................................................. 34 2. Destruction and irreversible transformation methods ............................................ 36 3. Other disposal methods when neither destruction nor irreversible transformation

is the environmentally preferable option ................................................................. 55 4. Other disposal methods when the POP content is low ........................................... 57

H. Remediation of contaminated sites ...................................................................................... 57 1. Contaminated site identification .............................................................................. 57 2. Environmentally sound remediation ........................................................................ 58

UNEP/CHW.14/INF/9

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I. Health and safety .................................................................................................................. 59 1. Higher-risk situations ............................................................................................... 59 2. Lower-risk situations ................................................................................................ 60

J. Emergency response ............................................................................................................. 61 K. Public participation ............................................................................................................... 61

Annex I: International instruments ................................................................................................... 63

Annex II: Examples of pertinent national legislation ....................................................................... 64

Annex III: Bibliography ..................................................................................................................... 67

UNEP/CHW.14/INF/9

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Abbreviations and acronyms

AOAC Association of Official Analytical Chemists (United States of America)

ASTM American Society for Testing and Materials

BAT best available techniques

BCD base-catalysed decomposition

BDE bromodiphenyl ether

BEP best environmental practices

CEN European Committee for Standardization

CFCs chlorofluorocarbons

CHD catalytic hydrodechlorination

DDT 1,1,1-trichloro-2,2-bis(4-chlorophenyl)ethane (dichlorodiphenyltrichloroethane)

DE destruction efficiency

DRE destruction removal efficiency

DRI

ECD

direct reduced iron

electron capture detector

EPA Environmental Protection Agency (United States of America)

ESM environmentally sound management

ESWI

EU

Expert Team to Support Waste Implementation

European Union

FAO Food and Agriculture Organization of the United Nations

FRTR Federal Remediation Technologies Roundtable (United States of America)

GAC

GEMS

granular activated carbon

Global Environment Monitoring System

GEF Global Environment Facility

GHS

GPCR

Globally Harmonized System of Classification and Labelling of Chemicals

gas-phase chemical reduction

HASP

HBB

HBCD

health and safety plan

hexabromobiphenyl

hexabromocyclododecane

HCB

HCBD

HCH

Hexachlorobenzene

hexachlorobutadiene

hexachlorocyclohexane

HRGC high-resolution gas chromatography

HRMS high-resolution mass spectrometry/spectrometer

IATA International Air Transport Association

ICAO International Civil Aviation Organization

ILO

IMO

International Labour Organization

International Maritime Organization

IPCS International Programme on Chemical Safety

ISO International Organization for Standardization

JESCO Japan Environmental Storage & Safety Corporation

LRMS low-resolution mass spectrometry/spectrometer

LTTD low-temperature thermal desorption

LWPS liquid waste pre-heater system

MSW

NFM

municipal solid waste

non-ferrous metal

NIP national implementation plan (Stockholm Convention)

OECD Organisation for Economic Co-operation and Development

OEWG Open-ended Working Group of the Basel Convention

PAH polycyclic aromatic hydrocarbon

PBB polybrominated biphenyl

PBDD

PBDE

PBDF

polybrominated dibenzo-p-dioxin

polybrominated diphenyl ethers (may also contain BDE that are not listed in the

Stockholm Convention)

polybrominated dibenzofuran

PCB polychlorinated biphenyl

PCDD polychlorinated dibenzo-p-dioxin

PCDF

PCP

polychlorinated dibenzo-furan

pentachlorophenol

PCT polychlorinated terphenyl

Pd/C

PeCB

PFOS

palladium on carbon

pentachlorobenzene

perfluorooctane sulfonic acid

POP persistent organic pollutant

POP-BDE brominated diphenyl-ethers listed in the Stockholm Convention: tetra-BDE, penta-

BDE, hexa-BDE, hepta-BDE, deca-BDE

QA quality assurance

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QC quality control

SCCPs short-chain chlorinated paraffins

SCWO supercritical water oxidation

SOP standard operational procedure

TEAP

TEQ

Technology and Economic Assessment Panel (of the Montreal Protocol)

toxicity equivalence

TRBP thermal reduction batch processor

UNECE United Nations Economic Commission for Europe

UNIDO United Nations Industrial Development Organization

UNEP United Nations Environment Programme

WHO

XRF

World Health Organization

X-ray fluorescence

Units of measurement

μg/kg microgram(s) per kilogram. Corresponds to parts per billion (ppb) by mass.

kg

kW

kWh

mg

mg/kg

kilogram

kilowatt

kilowatt-hour

milligram

milligram(s) per kilogram. Corresponds to parts per million (ppm) by mass.

MJ

ms

ng

megajoule

millisecond

nanogram

Mg megagram (1,000 kg or 1 tonne)

Nm3 normal cubic metre; refers to dry gas, 101.3 kPa and 273.15 K

UNEP/CHW.14/INF/9

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I. Introduction

A. Scope

1. The present general technical guidelines provide guidance on the environmentally sound

management (ESM) of wastes consisting of, containing or contaminated with persistent organic

pollutants (hereinafter referred to as “POP wastes”), pursuant to several decisions of multilateral

environmental agreements on chemicals and wastes.1 This document supersedes the Updated

generalGeneral technical guidelines for the environmentally sound management of wastes consisting of,

containing or contaminated with persistent organic pollutants (POPs) of May 20152017.

2. These technical guidelines servesserve as an “umbrella” document and should be used in

conjunction with the following specific technical guidelines on wastes consisting of, containing or

contaminated with the following POPs:

(a) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with Ppolychlorinated biphenyls (PCBs), polychlorinated terphenyls

(PCTs), polychlorinated naphthalenes (PCNs), and hexabromobiphenyl (HBB), these technical

guidelines also cover polychlorinated terphenyls (PCTs) and or polybrominated biphenyls (PBBs) other

thanincluding hexabromobiphenyl ( HBB), which are subject to the Basel Convention but are not POPs

subject to the Stockholm Convention (PCBs technical guidelines) (UNEP, 2017a);

(b) The pesticide POPs Technical guidelines on the environmentally sound management of

wastes consisting of, containing or contaminated with the pesticides aldrin, alpha

hexachlorocyclohexane, beta hexachlorocyclohexane, chlordane, chlordecone, dieldrin, endrin,

heptachlor, hexachlorobenzene (HCB), hexachlorobutadiene, lindane, mirex, pentachlorobenzene

(PeCB), pentachlorophenol and its salts, perfluorooctane sulfonic acid, technical endosulfan and its

related isomers or toxaphene or HCB as an industrial chemical (Pesticide POPs technical guidelines)

(UNEP, 2017b);

(c) Technical guidelines for the environmentally sound management of wastes consisting of,

containing or contaminated with 1,1,1-Trichloro-2,2-bis(4-chlorophenyl)ethane (DDT) (DDT technical

guidelines) (UNEP, 2006a);

(d) Unintentionally produced polychlorinated dibenzo-p-dioxins (PCDDs), polychlorinated

dibenzofurans (PCDFs), HCB, PCBs, PeCB and PCNs (Unintentional POPs technical guidelines)

(UNEP, 2017c);

(e) Hexabromodiphenyl ether (hexaBDE) and heptabromodiphenyl ether (heptaBDE), or

tetrabromodiphenyl ether (tetraBDE) and pentabromodiphenyl ether (pentaBDE) (POP-BDEs technical

guidelines) (UNEP, 2015b);

(d(f) Hexabromocyclododecane (HBCD) (HBCD technical guidelines) (UNEP, 2015c);

(g) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with Pperfluorooctane sulfonic acid (PFOS), its salts and perfluorooctane

sulfonyl fluoride (PFOSF), or other PFOS-related substances that are precursors of PFOS (PFOS

technical guidelines) (UNEP, 2015d);

(e) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with Hhexabromodiphenyl ether (hexaBDE) and heptabromodiphenyl ether

(heptaBDE), or tetrabromodiphenyl ether (tetraBDE), and pentabromodiphenyl ether (pentaBDE),

andor decabromodiphenyl ether (decaBDE) (POP-BDEs technical guidelines) (UNEP, 2015b [to be

updated]);

1 Decisions IV/17, V/26, VI/23, VII/13, VIII/16, IX/16, BC-10/9, BC-11/3, BC-12/3, BC-13/4 and BC-13/414… of

the Conference of the Parties to the Basel Convention on the Control of Transboundary Movement of Hazardous

Wastes and Their Disposal; decisions I/4, II/10, III/8, IV/11, V/12, VI/5, VII/8, OEWG-8/5, OEWG-9/3, OEWG-

10/4 and OEWG-10/411/3… of the Open-ended Working Group of the Basel Convention; resolution 5 of the

Conference of Plenipotentiaries to the Stockholm Convention on Persistent Organic Pollutants; decisions INC-6/5

and INC-7/6 of the Intergovernmental Negotiating Committee for an International Legally Binding Instrument for

Implementing Action on Certain Persistent Organic Pollutants; and decisions SC-1/2, SC-2/6, SC-3/7, SC-4/10-18,

SC-5/3, SC-6/13, SC-7/12, SC-7/13, SC-7/14, SC-8/10, SC-8/11 and SC-7/148/12 of the Conference of the Parties

to the Stockholm Convention on Persistent Organic Pollutants.

UNEP/CHW.14/INF/9

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(f) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with Hhexabromocyclododecane (HBCD) (HBCD technical guidelines)

(UNEP, 2015c);

(g) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with Ppentachlorophenol (PCP) and its salts and esters (PCP technical

guidelines) (UNEP, 2017e);.

(h) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with Hhexachlorobutadiene (HCBD) (HCBD technical guidelines) (UNEP,

2017d [to be updated]); and

(i) Pentachlorophenol (PCP) and its salts and esters (PCP [Technical guidelines on the

environmentally sound management of wastes consisting of, containing or contaminated with Sshort-

chain chlorinated paraffins (SCCP technical guidelines) (UNEP, 2017e).201X); and]

(j) Technical guidelines on the environmentally sound management of wastes containing or

contaminated with Uunintentionally produced polychlorinated dibenzo-p-dioxins (PCDDs),

polychlorinated dibenzofurans, hexachlorobenzene, polychlorinated biphenyls, pentachlorobenzene,

polychlorinated naphthalenes or hexachlorobutadiene(PCDFs), HCB, PCBs, PeCB, PCNs, and HCBD

(Unintentional POPs technical guidelines) (UNEP, 2017c [to be updated]).

3. The purpose of the general technical guidelines is to:

(a) Provide overarching and common guidance on the ESM of POP wastes; and

(b) Address provisions referred to in Article 6, paragraph 2 of the Stockholm Convention (see

subsection II.B.2 of the present guidelines on waste-related provisions of the Stockholm Convention)

on:

(i) The levels of destruction and irreversible transformation;

(ii) The methods that are considered to constitute environmentally sound disposal; and

(iii) The concentration levels to define low POP content.

4. The guidelines also provide guidance on reducing or eliminating POP releases to the

environment from waste disposal and treatment processes. Considerations pertaining to the

environmentally sound disposal of POP wastes discussed in these guidelines include choices of pre-

treatment since pre-treatment may be important when determining a disposal method.

5. It should be noted that guidance on best available techniques (BAT) and best environmental

practices (BEP) as they apply to the prevention or minimization of the formation and release of

unintentional POPs from the anthropogenic sources listed in Annex C to the Stockholm Convention is

provided under the Stockholm Convention. Guidelines on BAT and provisional guidance on BEP

relevant to Article 5 and Annex C to the Stockholm Convention were adopted by the Conference of the

Parties to the Convention at its third meeting, in 2007.

6. Table 1 indicates which specific POPs technical guidelines address each of the 2628 POPs listed

in Annex A, B or C to the Stockholm Convention.

Table 1: Stockholm Convention POPs listed in Annex A, B or C addressed by specific technical

guidelines under the Basel Convention

Stockholm Convention POPs

Basel Convention POPs technical guidelines

General technical guidelines

UNEP/CHW.14/INF/9

10

PC

Bs

tech

nic

al g

uid

elin

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Pes

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des

tec

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gu

idel

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DD

T t

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Un

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al P

OP

s te

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ical

gu

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PO

P-B

DE

s te

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ical

gu

idel

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HB

CD

tec

hn

ical

gu

idel

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PF

OS

tec

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ical

gu

idel

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HC

BD

tec

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gu

idel

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PC

P t

ech

nic

al g

uid

elin

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SC

CP

tec

hn

ical

gu

idel

ines

Aldrin x

Chlordane x

Chlordecone x

Decabromodiphenyl ether (BDE-209) present in

commercial decabromodiphenyl ether

(decaBDE)

x

Dieldrin x

1,1,1-Trichloro-2,2-bis(4-chlorophenyl)ethane

(DDT)

x

Endrin x

Heptachlor x

Hexabromobiphenyl (HBB) x

Hexabromodiphenyl ether (hexaBDE) and

heptabromodiphenyl ether (heptaBDE)

x

Hexabromocyclododecane (HBCD) x

Hexachlorobenzene (HCB) x x

Hexachlorobutadiene (HCBD) x x x

Alpha hexachlorocyclohexane (alpha-HCH) x

Beta hexachlorocyclohexane (beta-HCH) x

Lindane x

Mirex x

Pentachlorobenzene (PeCB) x x

Pentachlorophenol (PCP) and its salts and esters x x

Perfluorooctane sulfonic acid (PFOS), its salts

and perfluorooctane sulfonyl fluoride (PFOSF)

x x

Polychlorinated biphenyls (PCBs) x x

Polychlorinated dibenzo-p-dioxins (PCDDs) x

Polychlorinated dibenzofurans (PCDFs) x

Polychlorinated naphthalenes (PCNs) x x

Short-chain chlorinated paraffins (SCCP) x

Technical endosulfan and its related isomers x

Tetrabromodiphenyl ether (tetraBDE) and

pentabromodiphenylether (pentaBDE)

x

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Stockholm Convention POPs

Basel Convention POPs technical guidelines

General technical guidelines

PC

Bs

tech

nic

al

guid

elin

es

Pes

tici

des

tec

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al g

uid

elin

es

DD

T t

ech

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Un

inte

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onal

PO

Ps

tech

nic

al

guid

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PO

P-B

DE

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uid

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HB

CD

tec

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PF

OS

tec

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HC

BD

tec

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PC

P t

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SC

CP

tec

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nes

Toxaphene x

B. About POPs2 and POP wastes

7. Most quantities of POPs are of anthropogenic origin. For some POPs, such as HCB, PCNs

PeCB, PCDD and PCDF, listed in Annex C to the Stockholm Convention, some quantities are also

unintentionally generated and released from anthropogenic sources. The characteristics of POPs

(toxicity, persistence and bioaccumulation), the potential for their long-range transport and their

ubiquitous presence in the environment, including ecosystems and in humans, were the impetus for the

Stockholm Convention.

8. POPs are being used or have been used in industrial processes, in products and in articles. Due to

their characteristics, POPs listed in the Annexes of the Stockholm Convention need to be managed to

prevent them from entering the environment. While action is needed to address recently listed POPs,

continued action is equally important to manage the other POPs and prevent their further perpetuation

(Weber et al, 2015).

9. It is important to recognize that even when POPs are adequately managed to “turn off the tap” at

the beginning of POPs life cycles, waste management efforts are ongoing as POPs can last in products

and waste streams for many decades. In addition, the improper management of POP wastes can lead to

releases of POPs into the environment. Furthermore, some disposal technologies can lead to the

unintentional formation and release of POPs listed in Annex C of Stockholm Convention (see section

IV.G). Control techniques to reduce formation and releases are, however, available.

10. Recently listed chemicals under the Stockholm Convention, such as POP-BDEs, PFOS, HBCD,

and HBCD,SCCPs, have brought attention to the use of POPs in products and articles, including

consumer products and articles. The management of these products and articles upon becoming waste

has introduced new challenges to Parties and stakeholders in their work to define strategies and

approaches for their ESM and efforts to prevent, reduce or eliminate their releases. For example,

Rrecycled plastics containing POPs are unintentionally contributing to contamination of new plastic

articlesproducts, when POPs are not removed from the recycling stream (see section IV.G.4).

II. Relevant provisions of the Basel and Stockholm conventions

11. A number of multilateral environmental agreements provide frameworks to prevent and

minimize releases of toxic chemicals and hazardous wastes. The Basel, Stockholm and Rotterdam

conventions are a series of building blocks that dovetail to create a comprehensive life cycle approach

to the management of hazardous chemicals and wastes. Together, these conventions guide decision

makers in their actions to minimize and manage the risks to the environment from a range of chemicals,

products and wastes.

2 Further information on the characteristics of POPs is available from several sources, including the Agency for

Toxic Substances and Disease Registry (United States of America), the Global Programme of Action for the

Protection of the Marine Environment from Land-based Activities, and the International Programme on Chemical

Safety (1995) of the World Health Organization (WHO).

Commented [HBCD IG1]: We propose again the

following editorial changes in the text to make it

clearer and more accurate.

We recommend the author taking into account the

sentence already provided by HBCD IG, which reads

as follows:

“For example, recycled plastics containing POPs may

be unintentionally contributing to contamination in

some new plastic articles produced by blending

impacted recyclate material which contains small

amounts of POPs with virgin polymers.”

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12. A full list of international instruments related to POPs is listed in annex I. The following sections

present a brief explanation and description of relevant Articles of the Basel and Stockholm conventions

to illustrate their complementarity in addition to key obligations of their Parties.

13. Provisions of the Stockholm Convention complement the provisions for the management of

hazardous wastes under the Basel Convention to form a comprehensive regime for managing POP

wastes. Provisions from the two conventions are to be applied to POP wastes in making decisions about

their ESM.

A. Basel Convention

1. General provisions

14. The Basel Convention, which entered into force on 5 May 1992, aims to protect human health

and the environment against the adverse effects resulting from the generation, management,

transboundary movements and disposal of hazardous and other wastes. It does this via a set of

provisions on the transboundary movement of wastes and their ESM. In particular, the Basel

Convention stipulates that any transboundary movement (export, import or transit) of wastes is

permissible only when the movement itself and the planned disposal of the hazardous or other wastes

are environmentally sound.

15. A set of provisions of the Basel Convention lays out Parties obligations to ensure the ESM of

POP wastes. These are listed in paragraphs 16 to 18 below.

16. In Article 2 (“Definitions”), paragraph 1, the Basel Convention defines wastes as “substances or

objects which are disposed of or are intended to be disposed of or are required to be disposed of by the

provisions of national law”. Paragraph 4 defines disposal as “any operation specified in Annex IV” to

the Convention. Paragraph 8 defines the ESM of hazardous wastes or other wastes as “taking all

practicable steps to ensure that hazardous wastes or other wastes are managed in a manner which will

protect human health and the environment against the adverse effects which may result from such

wastes.”

17. Article 4 (“General obligations”), paragraph 1, establishes the procedure by which Parties

exercising their right to prohibit the import of hazardous wastes or other wastes for disposal shall

inform the other Parties of their decision. Paragraph 1 (a) states: “Parties exercising their right to

prohibit the import of hazardous or other wastes for disposal shall inform the other Parties of their

decision pursuant to Article 13.” Paragraph 1 (b) states: “Parties shall prohibit or shall not permit the

export of hazardous or other wastes to the Parties which have prohibited the import of such wastes,

when notified pursuant to subparagraph (a).”

18. Article 4, paragraphs 2 (a) – (e) and 2 (g), contains key provisions of the Basel Convention

directly pertaining to ESM, waste prevention and minimization and waste disposal practices aimed at

mitigating adverse effects on human health and the environment:

Paragraphs 2 (a) – (e) and 2 (g): “Each Party shall take appropriate measures to:

(a) Ensure that the generation of hazardous wastes and other wastes within it is

reduced to a minimum, taking into account social, technological and economic aspects;

(b) Ensure the availability of adequate disposal facilities, for the environmentally

sound management of hazardous wastes and other wastes, that shall be located, to the extent

possible, within it, whatever the place of their disposal;

(c) Ensure that persons involved in the management of hazardous wastes or other

wastes within it take such steps as are necessary to prevent pollution due to hazardous wastes

and other wastes arising from such management and, if such pollution occurs, to minimize the

consequences thereof for human health and the environment;

(d) Ensure that the transboundary movement of hazardous wastes and other wastes is

reduced to the minimum consistent with the environmentally sound and efficient management

of such wastes, and is conducted in a manner which will protect human health and the

environment against the adverse effects which may result from such movement;

(e) Not allow the export of hazardous wastes or other wastes to a State or group of

States belonging to an economic and/or political integration organization that are Parties,

particularly developing countries, which have prohibited by their legislation all imports, or if it

has reason to believe that the wastes in question will not be managed in an environmentally

sound manner, according to criteria to be decided on by the Parties at their first meeting;”

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“(g) Prevent the import of hazardous wastes and other wastes if it has reason to

believe that the wastes in question will not be managed in an environmentally sound manner.”

Paragraph 8: “Each Party shall require that hazardous wastes or other wastes, to be exported, are

managed in an environmentally sound manner in the State of import or elsewhere.”

2. POP-related provisions

19. Article 1 (“Scope of the Convention”) defines the types of waste that are subject to the Basel

Convention. Subparagraph 1 (a) of that article sets forth a two-step process for determining whether a

“waste” is a “hazardous waste” subject to the Convention: first, the waste must belong to any category

contained in Annex I to the Convention (“Categories of wastes to be controlled”), and second, the waste

must possess at least one of the characteristics listed in Annex III to the Convention (“List of hazardous

characteristics”).

20. For a list of Annex I and Annex II wastes that may consist of, contain or be contaminated with a

specific POP, refer to the specific technical guidelines pertaining to that POP.

21. Annex I wastes are presumed to exhibit one or more Annex III hazardous characteristics, which

may include H4.1 “Flammable solids”, H6.1 “Poisonous (Acute)”, H11 “Toxic (Delayed or chronic)”,

H12 “Ecotoxic”, or H13 “Capable, by any means, after disposal, of yielding another material, e.g.,

leachate, which possesses any of the characteristics listed above”, unless, through “national tests”, they

can be shown not to exhibit such characteristics. National tests may be useful for identifying a particular

hazardous characteristic listed in Annex III until such time as the hazardous characteristic is fully

defined. Guidance papers for Annex III hazardous characteristics H11, H12 and H13 were adopted on

an interim basis by the Conference of the Parties to the Basel Convention at its sixth and seventh

meetings.

22. List A of Annex VIII to the Convention lists wastes that are “characterized as hazardous under

Article 1, paragraph 1 (a), of this Convention.” However, designation of a waste on Annex VIII does

not preclude the use of Annex IIIList of hazardous characteristics” to demonstrate that a waste is not

hazardous (Annex I, paragraph (b)). List B of Annex IX lists wastes that “will not be wastes covered by

Article 1, paragraph 1 (a), of this Convention unless they contain Annex I material to an extent causing

them to exhibit an Annex III characteristic.”

23. For a list of Annex VIII waste characteristics that are applicable to a specific POP, refer to the

specific technical guidelines pertaining to that POP.

24. As stated in Article 1, paragraph 1 (b), “Wastes that are not covered under paragraph (a) but are

defined as, or are considered to be, hazardous wastes by the domestic legislation of the Party of export,

import or transit” are also subject to the Basel Convention.

B. Stockholm Convention

1. General provisions

25. The Stockholm Convention on Persistent Organic Pollutants (POPs) is a global treaty aimed at

protecting human health and the environment from persistent organic pollutants.

26. The objective of the Stockholm Convention, which entered into force on 17 May 2004, is set

forth in Article 1 (“Objective”): “Mindful of the precautionary approach as set forth in Principle 15 of

the Rio Declaration on Environment and Development, the objective of this Convention is to protect

human health and the environment from persistent organic pollutants.”

27. The Stockholm Convention differentiates between two categories of POPs:

(a) Intentionally produced POPs, whose production and use are to be:

(i) Eliminated in accordance with the provisions of Article 3 and Annex A; or

(ii) Restricted in accordance with the provisions of Article 3 and Annex B; and

(b) Unintentionally produced POPs, for which Parties are required to take measures, in

accordance with Article 5 and Annex C, to reduce total releases derived from anthropogenic sources

with the goal of their continuing minimization and, where feasible, ultimate elimination.

28. Article 3 also provides that parties may continue producing or using POPs listed in Annexes A

and/or B for specific exemptions or acceptable purposes, if such have been specified by the Conference

of the Parties upon listing.

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14

28.29. Article 5, paragraph (a) (i), of the Stockholm Convention requires the development and

maintenance of source inventories and release estimates for unintentionally produced POPs.

29.30. Article 5, paragraph (b) promotes the application of available, feasible and practical measures

that can expeditiously achieve a realistic and meaningful level of release reduction or source

elimination.

30.31. Under Article 7 (“Implementation plans”), paragraph 1, the Convention requires each Party to:

“(a) Develop and endeavour to implement a plan for the implementation of its obligations

under this Convention;

(b) Transmit its implementation plan to the Conference of the Parties within two years of the

date on which this Convention enters into force for it; and

(c) Review and update, as appropriate, its implementation plan on a periodic basis and in a

manner to be specified by a decision of the Conference of the Parties.”

2. Waste-related provisions

31.32. Article 6 (“Measures to reduce or eliminate releases from stockpiles and wastes”) sets forth

waste-related provisions as follows:

“1. In order to ensure that stockpiles consisting of or containing chemicals listed either in

Annex A or Annex B and wastes, including products and articles upon becoming wastes,

consisting of, containing or contaminated with a chemical listed in Annex A, B or C, are

managed in a manner protective of human health and the environment, each Party shall:

(a) Develop appropriate strategies for identifying:

(i) Stockpiles consisting of or containing chemicals listed either in Annex A or

Annex B; and

(ii) Products and articles in use and wastes consisting of, containing or

contaminated with a chemical listed in Annex A, B or C;

(b) Identify, to the extent practicable, stockpiles consisting of or containing chemicals

listed either in Annex A or Annex B on the basis of the strategies referred to in subparagraph

(a);

(c) Manage stockpiles, as appropriate, in a safe, efficient and environmentally sound

manner. Stockpiles of chemicals listed either in Annex A or Annex B, after they are no longer

allowed to be used according to any specific exemption specified in Annex A or any specific

exemption or acceptable purpose specified in Annex B, except stockpiles which are allowed to

be exported according to paragraph 2 of Article 3, shall be deemed to be waste and shall be

managed in accordance with subparagraph (d);

(d) Take appropriate measures so that such wastes, including products and articles

upon becoming wastes, are:

(i) Handled, collected, transported and stored in an environmentally sound

manner;

(ii) Disposed of in such a way that the persistent organic pollutant content is

destroyed or irreversibly transformed so that they do not exhibit the

characteristics of persistent organic pollutants or otherwise disposed of in

an environmentally sound manner when destruction or irreversible

transformation does not represent the environmentally preferable option or

the persistent organic pollutant content is low, taking into account

international rules, standards, and guidelines, including those that may be

developed pursuant to paragraph 2, and relevant global and regional

regimes governing the management of hazardous wastes;

(iii) Not permitted to be subjected to disposal operations that may lead to

recovery, recycling, reclamation, direct reuse or alternative uses of

persistent organic pollutants; and

(iv) Not transported across international boundaries without taking into account

relevant international rules, standards and guidelines;

UNEP/CHW.14/INF/9

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(e) Endeavour to develop appropriate strategies for identifying sites contaminated by

chemicals listed in Annex A, B or C; if remediation of those sites is undertaken it shall be

performed in an environmentally sound manner.

2. The Conference of the Parties shall cooperate closely with the appropriate bodies of the

Basel Convention on the Control of Transboundary Movements of Hazardous Wastes and Their

Disposal to, inter alia:

(a) Establish levels of destruction and irreversible transformation necessary to ensure

that the characteristics of persistent organic pollutants as specified in paragraph 1 of Annex D

are not exhibited;

(b) Determine what they consider to be the methods that constitute environmentally

sound disposal referred to above; and

(c) Work to establish, as appropriate, the concentration levels of the chemicals listed

in Annexes A, B and C in order to define the low persistent organic pollutant content referred to

in paragraph 1 (d) (ii).”

32.33. Article 3, paragraph 2 (a) (i), pertaining to imports, stipulates: “Each Party shall take measures to

ensure that a chemical listed in Annex A or Annex B is imported only for the purpose of

environmentally sound disposal as set forth in paragraph 1 (d) of Article 6.” Similarly, Article 3,

paragraph 2 (b) (i), requires that: “Each Party take measures to ensure that a chemical listed in Annex A

for which any production or use specific exemption is in effect or a chemical listed in Annex B for

which any production or use specific exemption or acceptable purpose is in effect, taking into account

any relevant provisions in existing international prior informed consent instruments, is exported only for

the purpose of environmentally sound disposal as set forth in paragraph 1 (d) of Article 6.”

33.34. Annex C, Part II, outlines industrial source categories that have the potential for comparatively

high formation and release to the environment of POPs listed in Annex C. Part III outlines source

categories from which POPs listed in Annex C may be unintentionally formed and released. Part V

outlines general guidance on BAT and BEP.

III. Issues under the Stockholm Convention to be addressed cooperatively

with the Basel Convention

A. Low POP content

34.35. As stated in Article 6, paragraph 2 (c), of the Stockholm Convention, the Conference of the

Parties to the Stockholm Convention shall cooperate closely with the appropriate bodies of the Basel

Convention to “work to establish, as appropriate, the concentration levels of the chemicals listed in

annexes A, B and C in order to define the low persistent organic pollutant content referred to in

paragraph 1 (d) (ii).”

35.36. Under the Stockholm Convention, POP wastes are, in accordance with Article 6, paragraph 1 (d)

(ii), to be disposed of in such a way that the POP content is destroyed or irreversibly transformed so that

they do not exhibit the characteristics of POPs or otherwise disposed of in an environmentally sound

manner when destruction or irreversible transformation does not represent the environmentally

preferable option, or the POP content is low, taking into account international rules, standards, and

guidelines, including those that may be developed pursuant to paragraph 2, as well as relevant global

and regional regimes governing the management of hazardous wastes.

36.37. The low POP content described in the Stockholm Convention is independent from the provisions

on hazardous waste under the Basel Convention.

37. Under the Stockholm Convention, wastes with a POP content at or above the defined low POP

content must be disposed of in such a way that the POP content is destroyed or irreversibly transformed

in accordance with the methods described in section IV.G.2. They should otherwise be disposed of in an

environmentally sound manner whenIf destruction or irreversible transformation does not represent the

environmentally preferable option in accordance with the methods described in section IV.G.3., they

could otherwise be disposed of in an environmentally sound manner.

38. Wastes with a POP content at or below the defined low POP content should be disposed of in

accordance with the methods referred to in section IV.G.4.

39.38. Low POP content definitions should be established taking into account the main objectives

objective of the Basel Convention and the Stockholm conventionscConvention, which areis the

UNEP/CHW.14/INF/9

16

protection of the environment and human health, mindful of the precautionary approach as set forth in

the Principle 15 of the Rio Declaration on Environment and Development. The following have been

recognized in the determination of low POP content (See European Commission, 2011, German Federal

Environment Agency, 2015, UNEP/CHW/OEWG.9/INF/9/Add.13 and /Add.24, and

UNEP/CHW.13/INF/665):

(a) Environmental and human health considerations;

(b) Availability of adequate capacity for analysis;

(c) Range of concentrations in articles, materials and waste;

(d) Limit values within national legislation;

(e) Availability of treatment capacity;

(f) Limitations of knowledge and data; and

(g) Economic considerations.

40.39. The provisional definitions of low POP content contained in table 2 below should be applied,

determined in accordance with national or international methods and standards, except for PCDDs and

PCDFs.

3 Draft updated general technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with persistent organic pollutants: supporting document for the development of section

III of the general technical guidelines for the environmentally sound management of wastes consisting of,

containing or contaminated with persistent organic pollutants. 4 Draft updated general technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with persistent organic pollutants: methodology for establishing low persistent organic

pollutant content and its application in the European Union. 5 Supporting information on the concentration levels to define the low persistent organic pollutant content values for

persistent organic pollutants listed in Annexes A, B and C to the Stockholm Convention.

UNEP/CHW.14/INF/9

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Table 2: Provisional definitions of low POP content6

POP Low POP content

Aldrin 50 mg/kg

Alpha-HCH, beta-HCH and lindane 50 mg/kg as a sum7

Chlordane 50 mg/kg

Chlordecone 50 mg/kg

DDT 50 mg/kg

Dieldrin 50 mg/kg

Endrin 50 mg/kg

HBB 50 mg/kg

HBCD 100 mg/kg or 1000 mg/kg

HCB 50 mg/kg

HCBD 100 mg/kg

Heptachlor 50 mg/kg

[OPTION 1: Decabromodiphenyl ether (BDE-209)

present in commercial decabromodiphenyl ether]8

[50 mg/kg]

Hexabromodiphenyl ether and heptabromodiphenyl

ether and tetrabromodiphenyl ether and

pentabromodiphenyl ether

50 mg/kg or 1000 mg/kg as a sum9

[OPTION 2: Hexabromodiphenyl ether and

heptabromodiphenyl ether and tetrabromodiphenyl

ether and pentabromodiphenyl ether and

decabromodiphenyl ether (BDE-209) present in

commercial decabromodiphenyl ether]

[[50 mg/kg] [1000 mg/kg] as a sum10]

Mirex 50 mg/kg

PCBs 50 mg/kg

PCDDs and PCDFs11 [1 g TEQ/kg]15 g TEQ/kg

PCNs 10 mg/kg

PCP and its salts and esters 100 mg/kg

PeCB 50 mg/kg

PFOS, its salts and PFOSF 50 mg/kg

SCCPs [100 mg/kg] [10 000 mg/kg]

6 It is noted that work towards a review of the provisional low POP content values will be undertaken in accordance

with decision BC-13/4. 7 The limit value has been set for the sum of lindane and its by-products alpha- and beta-HCH, because they may be

contained together in pesticides and production wastes. 8 The current limit values for tetra-, penta-, hexa-, and hepta-BDE BDEs may be kept, if an individual value for

decaBDE is agreed, or no agreement is reached with respect to decaBDE. 9 The limit value has been set for the sum of tetra-, penta-, hexa-, and hepta-BDE, because commercial mixtures

have varying congener composition (see section I.B.1 of the POP-BDE guidelines), and for analytical efficiencies. 10 The limit value has been set for the sum of tetra-, penta-, hexa-, and hepta- and decaBDEBDE, because

commercial mixtures have varying congener composition (see section I.B.1 of the POP-BDE guidelines), and for

analytical efficiencies. 11 TEQ as referred to in Annex C, part IV, paragraph 2, to the Stockholm Convention, but only for PCDDs and

PCDFsbut only for PCDDs and PCDFsincluding coplanar PCBs.

Commented [ACEA2]: Please take into consideration the findings of the latest EU-Study “to support the review of waste related issues in Annexes IV and V of POP-Regulation” (http://ec.europa.eu/environment/waste/pdf/Study_POPS_Waste_final.pdf): “According to the evaluation of the limitation criteria, an appropriate LPCL can be set in a range between 200 and 1,000 mg/kg.” For a value below 200 ppm no analytical method is available. For inhomogeneous waste streams very low limit values cannot be monitored and enforced. Several considerations are relevant when considering a value within the proposed range including the precautionary principle, economic, technical and practical feasibility and efficiency. To allow resource efficiency and having the newly fixed UTC of the EU POP-Regulation of 500 ppm as a sum in mind, the LPC from our perspective should be between 500 ppm – 1,000ppm

Commented [ACEA3]: see comment above

Commented [EU/MS4]: Correction in the footnote

Formatted: Complex Script Font: 10 pt, Highlight

UNEP/CHW.14/INF/9

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POP Low POP content

Technical endosulfan and its related isomers 50 mg/kg

Toxaphene 50 mg/kg

B. Levels of destruction and irreversible transformation

41.40. Destruction efficiency12 (DE) is the percentage of originating POPs destroyed or irreversibly

transformed by a particular method or technology. Destruction removal efficiency13 (DRE) only

considers emissions to air and is the percentage of original POPs irreversibly transformed and removed

from gaseous emissions.

42.41. The provisional definition set out in paragraph 43 442 below recognizes the following:

(a) Both DE and DRE are a function of the initial POP content and do not cover any fraction

of other unintentionally produced POPs during destruction or irreversible transformation;

(b) DE is an important criterion to assess technologies performance for destruction and

irreversible transformation, but can be difficult to measure in a reproducible and comparable manner;

(c) BAT and BEP are available in order to ensure the anticipated environmental performance

is achieved, including expected DE; and

(d) Pertinent national legislation14, international rules, standards and guidelines apply to these

operations.

43.42. The following provisional definition for levels of destruction and irreversible transformation,

based upon absolute levels (i.e., waste output streams of treatment processes) should be applied:

(a) Atmospheric emissions:

(i) PCDDs and PCDFs: 0.1 ng TEQ/Nm3;15

(ii) All other POPs: pertinent national legislation and international rules, standards and

guidelines, examples of pertinent national legislation can be found in annex II;

(b) Aqueous releases: pertinent national legislation and international rules, standards and

guidelines, examples of pertinent national legislation can be found in annex II;

(c) Solid residues: POP contents should be below the low POP contents defined in section A

of this chapter. However, if the POP content is above the low POP content defined in section A, the

solid residues should be treated in accordance with section IV.G.

44.43. In addition, technologies for destruction and irreversible transformation should be operated in

accordance with BAT and BEP.

C. Methods that constitute environmentally sound disposal

45.44. Section G of chapter IV below contains a description of methods that are considered to constitute

environmentally sound disposal of POP wastes.

12 Calculated on the basis of the mass of the POP content within the waste, minus the mass of the remaining POP

content in the gaseous, liquid and solid residues, divided by the mass of the POP content within the waste, i.e.,

DE = (POP content within waste – POP content within gas, liquid and solid residual) / POP content within the

waste. 13 Calculated on the basis of the mass of the POP content within the waste, minus the mass of the remaining POP

content in the gaseous residues (stack emissions), divided by the mass of the POP content within the wastes, i.e.,

DRE = (POP content within waste – POP content within gas residual) / POP content within the waste. 14 For example, in Japan, the Ministry of the Environment in 2010 issued a “Technical Guideline for the

Environmentally Sound Treatment of PFOS Wastes”, which states that destruction levels for PFOS and its salts

must be over 99.999 per cent (Ministry of the Environment of Japan, 2013b). 15 TEQ as referred to in Annex C, part IV, paragraph 2, to the Stockholm Convention, but only for PCDDs and PCDFs. Nm3 refers to dry gas,

101.3 kPa and 273.15 K. Standardization at 11 per cent O2. Standardization at 10 per cent O

2 for cement kilns co-incineration.

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IV. Guidance on environmentally sound management (ESM)

A. General considerations

46.45. ESM is a broad policy concept that is understood and implemented in various ways by different

countries, stakeholders and organizations. The provisions and guidance documents pertaining to ESM

of hazardous wastes as it applies to POP wastes within the Basel and Stockholm conventions, together

with performance elements produced by the Organisation for Economic Co-operation and Development

(OECD), core performance elements provide for a common understanding and international guidance to

support and implement the ESM of hazardous wastes and other wastes.

47.46. The 2013 Framework for the environmentally sound management of hazardous wastes and other

wastes (“ESM framework”) 16 (UNEP, 2013a) was adopted at the eleventh meeting of the Conference of

the Parties to the Basel Convention. The framework establishes a common understanding of what ESM

encompasses and identifies tools and strategies to support and promote the implementation of ESM. It is

intended as a practical guide for governments and other stakeholders participating in the management of

hazardous wastes and other wastes and constitutes the most comprehensive guidance on ESM to

complement the Basel technical guidelines.

48.47. As presented in paragraph 17 18 of this document, Article 4 of the Basel Convention contains

provisions related to the ESM of hazardous wastes and other wastes. ESM is also the subject of the

following declarations:

(a) The 1999 Basel Declaration on Environmentally Sound Management, which was adopted

at the fifth meeting of the Conference of the Parties to the Basel Convention calls on the Parties to

enhance and strengthen their efforts and cooperation to achieve ESM, including through prevention,

minimization, recycling, recovery and disposal of hazardous and other wastes subject to the Basel

Convention, taking into account social, technological and economic concerns, and through further

reduction of transboundary movements of hazardous and other wastes subject to the Basel Convention;

(b) The 2011 Cartagena Declaration on the Prevention, Minimization and Recovery of

Hazardous Wastes and Other Wastes, which was adopted at the tenth meeting of the Conference of the

Parties to the Basel Convention and reaffirms that the Basel Convention is the primary global legal

instrument for guiding the ESM of hazardous wastes and other wastes and their disposal.

49.48. Under the Stockholm Convention, the term “environmentally sound management” is not defined.

Environmentally sound methods for disposal of POP wastes are, however, to be determined by the

Conference of the Parties in cooperation with the appropriate bodies of the Basel Convention.

50.49. The OECD has adopted a recommendation on ESM of wastes which includes various items,

inter alia core performance elements of ESM guidelines applying to waste recovery facilities, including

elements of performance that precede collection, transport, treatment and storage and also elements

subsequent to storage, transport, treatment and disposal of pertinent residues (OECD, 2004).

51.50. Parties should develop a range of measures (strategies, policies, legislation, regulations and

programmes) and monitor their implementation to support the meeting of ESM objectives. The

implementation of national strategies, policies and programmes are effective tools to complement the

implementation of legislation and regulations; monitoring and enforcement; incentives and penalties;

technologies; and other tools in which all key stakeholders participate and cooperate (UNEP, 2013a).

The following sections should be taken into account when establishing, implementing or evaluating

ESM.

B. Legislative and regulatory framework

52.51. Parties to the Basel and Stockholm conventions should examine their national strategies,

policies, controls, standards and procedures to ensure that they are in agreement with the two

conventions and with their obligations under them, including those that pertain to ESM of POP wastes.

53.52. Most countries already have in place some form of legislation that outlines broad environmental

protection principles, powers and rights. Such legislation should make ESM operational and include

requirements for protection of both human health and the environment. Such enabling legislation can

16 ESM framework :

http://www.basel.int/Implementation/CountryLedInitiative/EnvironmentallySoundManagement/ESMFr

amework/tabid/3616/Default.aspx

UNEP/CHW.14/INF/9

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give governments the power to enact and enforce specific rules and regulations on hazardous wastes,

conduct inspections and establish penalties for violations.

54.53. Such legislation on hazardous wastes should also define hazardous wastes. Waste with a POP

content above the low POP content specified in the definition referred to in section III.A should be

included in the definition, as appropriate.

55.54. The legislation could define ESM and require adherence to ESM principles, ensuring that

countries satisfy provisions for ESM of POP wastes, including their environmentally sound disposal as

described in the present guidelines and the Stockholm Convention. Specific components or features of a

regulatory framework that would meet the requirements of the Basel and Stockholm conventions and

other international agreements are discussed below.17

1. Phase-out dates for production and use of POPs

56.55. Legislation and voluntary commitments, as applicable, should differentiate between the phase-

out dates for the production of POPs and their use 18 in products and articles (downstream manufacturer)

and the date by which the POPs (whether in pure form or in mixtures), products or articles should be

disposed of once they have become waste. In addition, they should set a time limit for the disposal of

POP wastes, taking into account that such products and articles may have long service lives, so as to

prevent the creation of stockpiles that have no clear phase-out dates. Examples of pertinent national

legislation can be found in annex II.

2. Transboundary movement requirements19

57.56. Hazardous wastes and other wastes should, as far as is compatible with their ESM, be disposed

of in the country where they were generated. Transboundary movements of such wastes are permitted

only under the following conditions:

(a) If conducted under conditions that do not endanger human health and the environment;

(b) If exports are managed in an environmentally sound manner in the country of import or

elsewhere;

(c) If the country of export does not have the technical capacity and the necessary facilities to

dispose of the wastes in question in an environmentally sound and efficient manner;

(d) If the wastes in question are required as a raw material for recycling or recovery

industries in the country of import; or

(e) If the transboundary movements in question are in accordance with other criteria decided

by the Parties.

58.57. Any transboundary movements of hazardous and other wastes are subject to prior written

notification from the exporting country and prior written consent from the importing and, if appropriate,

transit countries. Parties shall prohibit the export of hazardous wastes and other wastes if the country of

import prohibits the import of such wastes. The Basel Convention also requires that information

regarding any proposed transboundary movement be provided using the accepted notification form and

that the approved consignment be accompanied by a movement document from the point where the

transboundary movement commences to the point of disposal.

59.58. Furthermore, hazardous wastes and other wastes subject to transboundary movements should be

packaged, labelled and transported in conformity with international rules and standards.20

60.59. When a transboundary movement of hazardous and other wastes to which consent of the

countries concerned has been given cannot be completed, the country of export shall ensure that the

wastes in question are taken back into the country of export for their disposal if alternative

arrangements cannot be made. In the case of illegal traffic (as defined in Article 9, paragraph 1), as the

17 Further guidance on Basel Convention regulatory frameworks can be found in the following documents: Manual for the Implementation of the Basel

Convention (UNEP, 2015f) and Basel Convention: Guide to the Control System (UNEP, 2015g). Parties to the Stockholm Convention should also

consult the Guidance for Developing a National Implementation Plan for the Stockholm Convention on Persistent Organic Pollutants (UNEP,

2014).

18 Note that Annex A, parts I and II, and Annex B to the Stockholm Convention contain references to the elimination and restriction of production and use

of POPs.

19 This applies only to the Parties to the Basel Convention.

20 In this connection, the United Nations Recommendations on the Transport of Dangerous Goods (Model Regulations) of 2003 (UNECE, 2003a ) or

later versions should be used.

UNEP/CHW.14/INF/9

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result of conduct on the part of the exporter or the generator, the country of export shall ensure that the

wastes in question are taken back into the country of export for their disposal or otherwise disposed of

in accordance with the provisions of the Basel Convention (as per Article 9, paragraph 2).

61.60. No transboundary movements of hazardous wastes and other wastes are permitted between a

Party and a non-Party to the Basel Convention unless a bilateral, multilateral or regional arrangement

exists as required under Article 11 of the Convention.

3. Specifications for containers, equipment, bulk containers and storage sites containing POPs

62.61. To meet the requirements of ESM and specific clauses in the Basel and Stockholm conventions

(for example, Basel Convention Article 4, paragraph 7, and Stockholm Convention Article 6,

paragraph 1), Parties may need to enact specific legislation that describes the types of containers and

storage areas that are acceptable for particular POPs and their relevant waste streams.21 Parties should

ensure that containers that may be transported to another country meet international standards such as

those established by the International Air Transport Association (IATA), the International Maritime

Organization (IMO) and the International Organization for Standardization (ISO).

4. Health and safety22

63.62. A legislative approach should be taken to protect workers from possible exposure to POPs.

These provisions should include requirements for the proper labelling of products and the identification

of appropriate disposal methods. While neither the Basel nor the Stockholm Convention specifically

requires Parties to have worker health and safety legislation, the protection of human health underpins

many of the objectives of both conventions.

64.63. Most countries have existing worker health and safety provisions either in general labour

legislation or in specialized human health or environmental legislation. Parties should re-examine their

existing legislation to ensure that POPs are adequately addressed and that relevant aspects of

international agreements are integrated into such legislation. Worker health and safety is a relatively

mature field and a great deal of guidance and literature is available to assist in the planning and revision

of legislation, policy and technical guidance.

65.64. In its Article 10 (“Public information, awareness and education”), paragraph 1 (e), the

Stockholm Convention calls upon Parties to promote and facilitate the training of workers, scientists,

educators and technical and managerial personnel. National health and safety legislation should include

provisions for the safe handling and storage of POP wastes.

5. Specification of acceptable procedures for sampling and analysis of POPs

66.65. Various methods and protocols for sampling and analysis have been developed for a range of

purposes. Reliable and useful data can be generated only when sampling and analytical methods

appropriate to the waste are used. Parties to the Basel and Stockholm conventions should have

legislation or strong policy guidelines identifying the acceptable sampling and analytical methods for

each POP waste, including the form in which it occurs and the matrix in which it is found. The

procedures specified should be agreed and accepted before any sampling or analysis takes place. The

use of internationally accepted procedures is recommended. This should ensure that the reported results

are acceptable and comparable. See section E of this chapter for further details.

6. Requirements for hazardous waste treatment and disposal facilities

67.66. Most countries have legislation that requires waste treatment and disposal facilities to obtain

some form of approval to commence operations. Approvals can outline specific conditions that must be

maintained in order for such approvals to remain valid. It may be necessary to add requirements specific

to POP wastes to meet the requirements of ESM and to comply with specific requirements of the Basel

and Stockholm conventions.

7. General requirement for public participation

68.67. Public participation is a core principle of the 1999 Basel Declaration on Environmentally Sound

Management and many other international agreements. Public participation as referred to in

section IV.K below may be addressed in legislation or policy.

21 Parties should consult the guidelines pertaining to the storage of pesticides and pesticide waste that have been produced by the Food and Agriculture

Organization (FAO) of the United Nations (FAO, 1996).

22 See section IV.I.

UNEP/CHW.14/INF/9

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8. Contaminated sites

69.68. Provisions enabling the development of an inventory of contaminated sites and remediation of

sites in an environmentally sound manner (Article 6, paragraph 1 (e), of the Stockholm Convention)

may be specified in legislation.

9. Other legislative controls

70.69. Examples of other aspects of the life-cycle management of POP wastes that could be regulated

through legislation include:

(a) Siting provisions and requirements relative to the storage, handling, collection and

transport of wastes;

(b) Decommissioning requirements, including:

(i) Inspection prior to and during decommissioning;

(ii) Procedures to be followed to protect worker and community health and the

environment during decommissioning;

(iii) Post-decommissioning site requirements;

(c) Emergency contingency planning, spill and accident response, including:

(i) Cleanup procedures and post-cleanup concentrations to be achieved;

(ii) Worker training and safety requirements; and

(d) Waste prevention, minimization and management plans.

C. Waste prevention and minimization

71.70. The prevention and minimization of POP wastes are the first and most important steps in the

overall ESM of such wastes. In Article 4, paragraph 2, the Basel Convention calls on Parties to “ensure

that the generation of hazardous wastes and other wastes is reduced to a minimum”. Waste prevention

should be the preferred option in any waste management policy. According to the framework for the

ESM of hazardous wastes and other wastes, the need to manage wastes and/or the risks and costs

associated with doing so are reduced by not generating wastes and by ensuring that generated wastes are

less hazardous (UNEP, 2013a).

72.71. According to the Basel ESM framework, companies that generate wastes (waste generators) are

responsible for ensuring the implementation of BAT and BEP when undertaking activities that generate

wastes. In doing so, they act to minimize the wastes generated by ensuring research, investment in

design, innovation and development of new products and processes that use fewer resources and energy

and that reduce, substitute or eliminate the use of hazardous materials.

73.72. Waste generators and significant downstream industrial users (e.g., pesticide formulators) of

products and articles containing POPs could be required to develop waste management plans. Such

plans should cover all hazardous wastes and all POP wastes.

74.73. Elements of a waste prevention and minimization programme include the following:

(a) Identification of processes possibly unintentionally producing POPs (e.g., incineration)

and determination of whether Stockholm Convention guidelines on BAT and BEP are applicable;

(b) Identification of processes that use POPs and generate POP wastes:

(i) To determine whether process modifications, including updating of older

equipment or material, could reduce POP waste generation; and

(ii) To identify alternative processes that are not linked to the production of POP

wastes;

(c) Identification of products and articles consisting of, containing or contaminated with

POPs and non-POP alternatives; and

(d) Minimization of the volume of POP wastes generated:

(i) By regular maintenance of equipment to increase efficiency and prevent spills and

leaks;

(ii) By prompt containment of spills and leaks;

UNEP/CHW.14/INF/9

23

(iii) By decontamination of containers and equipment containing POP wastes;

(iv) By isolation of POP wastes in order to prevent contamination of other materials;

and

(v) By adoption of appropriate procedures for decommissioning of facilities.

75.74. The mixing and blending of wastes with POP contents above a defined low POP content with

other materials solely for the purpose of generating a mixture with a POP content at or below the

defined low POP content is not environmentally sound. Nevertheless, the mixing or blending of

materials prior to waste treatment may be necessary in order to enable treatment or to optimize

treatment efficiency.

D. Identification of wastes

1. General considerations

76.75. The identification of POP wastes is the starting point for their effective ESM. POP wastes can be

generated via a range of processes and activities that can occur during the whole life cycle of POPs, for

example:

(a) During their intentional manufacture (production facilities);

(b) As by-products of industrial and other processes using these POPs (e.g., manufacturing

facilities of products and articles such as plastics, upholstery, textiles, packaging materials,

electrical/electronic equipment, masterbatches, pellets, expanded polystyrene materials, paints,

adhesives, etc.);

(c) Through contamination of materials or the environment as a result of accidents or leakage

that may occur during production, sale, use, decommissioning, removal, transfer or disposal;

(d) Through contamination of materials during handling, use of products and articles, such as

containers, clothing and in some cases personal protective equipment (hazmat suits, boots, respirators,

etc.) that have been contaminated through contact with a POP;

(e) When products or articles consisting of, containing or contaminated with POPs are used,

become off-specification, are unfit for their original use or have been banned, or when registrations for

such products have been withdrawn; or

(f) When products or articles consisting of, containing or contaminated with POPs are

disposed of (e.g. incineration resulting in ash contaminated with unintentionally produced POPs).

77.76. POP wastes occur as solids and liquids (aqueous, semi-aqueous, solvent-based and emulsions)

and can be released as gases (actual gases, as a liquid dispersion or aerosols), or adsorbed onto

atmospheric pollutants. Examples of such wastes are presented in table 3.

Table 3: Physical forms and types of POP wastes generated

Physical form of the wastes Type of waste

Liquid 1. Obsolete liquid stockpile of pure POPs

2. Industrial wastewater

3. Municipal wastewater

4. Landfill leachate

5. Industrial liquid (e.g., solvent)

6. Liquid household products

7. Liquid fluids (e.g., insulating oils, lubricants, metalworking

and hydraulic fluids)

8. Industrial sludge

9. Municipal sludge

Solid 1. Obsolete solid stockpile of POPs

2. Soil, sediment, rock and mine aggregates

3. Industrial sludge

4. Municipal sludge

5. ResiduesOther residues from wastewater cleaning (e.g.,

activated carbon treatment)

6. Residues from air pollution control system (e.g., fly ashes)

7. Waste incineration residues (e.g. bottom ashes), other than

UNEP/CHW.14/INF/9

24

Physical form of the wastes Type of waste

those from air pollution control system23

7.8. Dust

8.9. Upholstery, textile, carpets, rubber, leather

9.10. Electrical and electronic equipment

10.11. Containers and packaging material

11.12. Contaminated material (e.g., clothing, personal protective

equipment)

12.13. Vehicle and shredder vehicle fluff

13.14. Plastic, paper, metal, wood

14.15. Demolition material (painted materials, resin-based

flooring, sealants, sealed glazing units, insulation boards)

15.16. Fire suppression foam equipment

Gas 1. Landfill gas

2. Gas from incineration facilities

3. Gas from recycling facilities

4. Gas from certain (industrial) processes

78.77. In Article 6, paragraph 1, the Stockholm Convention requires each Party to:

(a) Develop appropriate strategies for the identification of stockpiles consisting of or

containing chemicals listed either in Annex A or Annex B and of products and articles in use and wastes

consisting of, containing or contaminated with a chemical listed in Annex A, B or C; and

(b) Identify, to the extent practicable, stockpiles consisting of or containing chemicals listed

either in Annex A or Annex B on the basis of the strategies referred to in subparagraph (a).

79.78. The list of source categories provided in Annex C to the Stockholm Convention can assist

industrial managers and government regulators, and the general public, in identifying unintentionally

produced POP wastes.

2. Inventories

80.79. Inventories are an important tool for identifying, quantifying and characterizing POP wastes.

81.80. Stockholm Convention articles 5, paragraph (a), 6, paragraph 1(a), and 11, paragraph 1, provide

elements that contribute to the identification of waste-related sources of POPs. For the purpose of the

ESM of wastes, a more specific and complete inventory may be needed. .

82.81. When developing an inventory, priority should be given to the identification of important waste

streams in terms of high volume and high POP concentrations. National inventories may be used:

(a) To establish a baseline quantity of products, articles and POP wastes;

(b) To establish an information registry to assist with safety and regulatory inspections;

(c) To obtain the accurate information needed to draw up plans for site stabilization;

(d) To assist with the preparation of emergency response plans; and

(e) To track progress towards minimizing and phasing out POPs.

83.82. For further information on the development of national inventories, consult the Methodological

guide for the development of inventories of hazardous wastes and other wastes under the Basel

Convention (UNEP, 2015j). The guide focuses on the actions recommended to develop the national

information systems that produce the information needed to assist countries in fulfilling their reporting

obligations under the Basel Convention.

84.83. Guidance documents for the inventory of specific POPs are also available (e.g., PCBs, PFOS

and, POP-BDEs, and HBCD),24 as is guidance for developing release inventories of unintentionally

generated POPs (see Toolkit for Identification and Quantification of Releases of Dioxins, Furans and

23 European Commission, 2005, Wang et al., 2010.

24 Drafts of guidance documents for the inventory of these specific POPs are available and can be consulted at:

http://chm.pops.int/Implementation/BATandBEP/Guidance/tabid/3636/Default.aspx and

http://chm.pops.int/Implementation/NIPs/Guidance/tabid/2882/Default.aspx.

Commented [CEWEP5]: We would like to propose

generic formulation:

7 Waste combustion residues (e.g. bottom ashes), other

than those from air pollution control system.

UNEP/CHW.14/INF/9

25

Other Unintentional Persistent Organic Pollutants under Article 5 of the Stockholm Convention

(UNEP, 2013b)).

85.84. In addition, it should be noted that the 2003 Protocol on Pollutant Release and Transfer Registers

(PRTR) to the 1998 United Nations Economic Commission for Europe (UNECE) Convention on

Access to Information, Public Participation in Decision-making and Access to Justice in Environmental

Matters (Aarhus Convention) includes provisions pertaining to inventories that may be applicable to

POPs. Moreover, it should be noted that, the Regional Agreement on Access to Information, Public

Participation and Justice in Environmental Matters in Latin America and the Caribbean (ECLAC)

establishes that each Party shall take steps to establish a PRTR covering air, water, soil and subsoil

pollutants, as well as materials and waste in its jurisdiction. Reporting on POPs in waste transfers can

take place in PRTRs at national level.25

E. Sampling, analysis and monitoring

86.85. Sampling, analysis and monitoring are important activities in the management of POP wastes

enabling the manager of the wastes and those who regulate its management to identify the concentration

of POPs in some waste streams and select the appropriate management method. The activities may also

be necessary to monitor if the methods of destruction chosen are operating within the set standards and

to ensure that POPs are not released into the environment. Monitoring and surveillance serve as

elements for identifying and tracking environmental concerns and human health risks. Information

collected from monitoring programmes feeds into science-based decision-making processes and is used

for the evaluation of the effectiveness of risk management measures, including regulations.

87.86. Sampling, analysis and monitoring should be conducted by trained professionals in accordance

with a well-designed programme and using internationally accepted or nationally approved methods,

carried out using the same method each time over the time span of the programme. They should also be

subjected to rigorous quality assurance and quality control measures. Mistakes in sampling, analysis or

monitoring, or deviation from standard operational procedures, can result in meaningless data or even

programme-damaging data.

88.87. Each Party should identify its sampling, analysis and monitoring needs and ensure it has

laboratory capacity that will meet the required operating standards. Training and protocols should be in

place to ensure that these standards can be met and that quality data and meaningful results can be

obtained. Building this capacity may be necessary in some countries if none exists.

89.88. Different analytical methods can be used depending on the purpose of the sampling or

monitoring activity and the physical form of the waste. For information on good laboratory practices the

OECD series (OECD, various years) and the Handbook on Good Laboratory Practices (WHO, 2009)

may be consulted; on general methodological considerations, the Guidance for a Global Monitoring

Programme for Persistent Organic Pollutants (UNEP, 2015a) may be used. Further information on

POPs analysis may be obtained from the UNEP/Global Environment Facility (GEF) project on capacity

needs for analyzing POPs at https://www.thegef.org/project/assessment-existing-capacity-and-capacity-

building-needs-analyze-pops-developing-countries

1. Sampling26

90.89. The overall objective of any sampling activity is to obtain a sample that can be used for the

targeted purpose, e.g., waste characterization, compliance with regulatory standards or suitability of

proposed treatment or disposal methods. This objective should be identified before sampling is started.

It is indispensable that quality requirements for equipment, transportation and traceability be met.

91.90. Standardized sampling procedures should be established and agreed upon before the start of the

sampling campaign (both matrix- and POP-specific). Elements of these procedures include the

following:

(a) The number of samples to be taken, the sampling frequency, the duration of the sampling

project and a description of the sampling method (including quality assurance procedures put in place,

e.g., field blanks and chain-of-custody);

25 Such reporting is part of PRTR in the Czech Republic (MŽP, 2017). Integrated Pollutants Releases Register.

Retrieved 12-10-2017, 2017, from http://www.irz.cz (in Czech). 26 Further information on sampling is available in RCRA Waste Sampling Draft Technical Guidance (United States Environmental Protection Agency

(EPA), 2002, and Nordtest method).

UNEP/CHW.14/INF/9

26

(b) Selection of location or sites and time of sample-taking (including description and

geographic localization);

(c) Identity of the person who took the sample and conditions during sampling;

(d) Full description of sample characteristics – labelling;

(e) Preservation of the integrity of samples during transport and storage (before analysis);

(f) Close cooperation between the sampler and the analytical laboratory; and

(g) Appropriately trained sampling personnel.

92.91. Sampling should comply with specific national legislation, where it exists, or with international

regulations and standards. In countries where regulations do not exist, qualified staff should be

appointed. Sampling procedures include the following:

(a) Development of a standard operational procedure (SOP) for sampling each of the

matrices for subsequent POPs analysis;

(b) Application of well-established sampling procedures such as those developed by ISO, the

American Society for Testing and Materials (ASTM), the European Union, the United States

Environmental Protection Agency (EPA), the Global Environment Monitoring System (GEMS), and the

European Committee for Electrotechnical Standardization (CENELEC) (See Standard on Collection,

logistics and treatment requirements for WEEE (Waste Electrical and Electronic Equipment) – Part 1:

General Treatment Requirements, in particular specifications for de-pollution), and the European

Committee for Standardization (CEN) (see EN 14899:2005 Characterization of waste - Sampling of

waste materials - Framework for the preparation and application of a sampling plan and the series of

CEN/TR 15310 1-5: 2006 Characterization of waste - Sampling of waste materials).

(c) Establishment of quality assurance and quality control (QA/QC) procedures.

93.92. All these steps should be followed for a sampling programme to be successful. Similarly,

documentation should be thorough and rigorous.

94.93. Types of waste matrices typically sampled for POPs include solids, liquids and gases:

(a) Liquids:

(i) Leachate from dumpsites and landfills;

(ii) Liquid collected from spills;

(iii) Water (surface water, drinking water and industrial and municipal effluents);

(b) Solids:

(i) Stockpiles, products and formulations consisting of, containing or contaminated

with POPs;

(ii) Solids from industrial sources and treatment or disposal processes (fly ash, bottom

ash, sludge, still bottoms, other residues, clothing, etc.);

(iii) Containers, equipment or other packaging materials (rinse or wipe samples),

including the tissues or fabric used in the collection of wipe samples;

(iv) Soil, sediment, rubble and compost;

(v) Consumer articles and products.

(c) Gases:

(i) Air (indoor);

(ii) Air (emissions).

2. Analysis

95.94. Typically, POPs analysis is performed in a dedicated laboratory. In some situations, for example

in remote areas, testing in the field can be made possible using test kits designed for screening purposes

in the field.

96.95. For analysis in laboratories, there are several analytical methods available, although for some

POPs analytical methods may still be in development. Therefore, Parties should verify the availability

and costs of methods for the POP they want to monitor before developing their monitoring and

UNEP/CHW.14/INF/9

27

sampling programme. Methods of analyzing the various matrices for POPs have been developed by

ISO, the European Committee for Standardization (CEN), EPA, AOAC and ASTM. Most in-house

methods are variations of these, and such in-house methods are also acceptable after validation.

97.96. The identification of a POP can be a difficult task, particularly when the POP consists of a

number of congeners or even isomers.

98.97. A tiered approach for the analysis (for the purpose of identification and quantification of a POP)

is recommended; this would begin with simple steps and thereafter involve more sophisticated methods.

The first step is to identify wastes that potentially contain POPs in order to reduce the number of

samples (and subsequently the amounts of waste to be disposed). The screening methods are especially

valuable in situations where decisions need to be taken rapidly, or where there is a limited capacity, and

also to reduce costs. In general, there are three steps, which sequentially include:

(a) Coarse screening for presence of halogens contained in a POP; these are chlorine (Cl),

bromine (Br) or fluorine (F). The purpose of this step is to identify from a large amount of samples

those that contain chlorine, bromine or fluorine. Hand-held instruments are available to test for these

halogens without “destroying” the sample; e.g., X-ray fluorescence (XRF) has the advantage of being

non-destructive, multi-elemental, fast and cost-effective. XRF is applicable to a wide range of

concentrations, fromalthough it is currently not validated for concentrations below 100 mg/kgper cent to

a few parts per million (ppm);; its main disadvantage is that analyses are generally restricted to elements

heavier than fluorine (Br, Cl) and cannot detect a specific substance.

(b) Biological or chemical screening methods (applied if a sample is positive under step 1):

Test kits o r simple detection methods with less costly instrumentation are available to further reduce

the number of samples which may contain POPs listed in the Stockholm Convention. The determination

of organic chlorine with the DEXSIL27 test kits or the L2000 analyzer28 is well established, as both

methods are able to analyse POPs in oil or soil samples. Bioanalytical methods, such as CALUX,29 are

recognized for the detection of dioxin-like toxic equivalents. Also, fast extraction methods and use of

short GC columns and a simple detector can be used to identify chlorinated POPs.

(c) The final step is the confirmation of the chemical analysis, which is typically required for

all samples that result positive under step 2. Such analysis is done in chemical laboratories, which often

are specialized for a certain group of POPs (e.g., pesticide POPs, dioxin-like POPs, POP brominated

flame retardants, PFOS) and specialized to a certain matrix. Confirmatory chemical analytical methods

have been developed by international and national organizations and include:

(i) For pesticide POPs and PCBs: capillary gas chromatography (GC) + electron

capture detector (ECD), mass spectrometry (MS), or tandem mass spectrometry

(MS/MS);

(ii) For POP-BDEs, dioxin-like POPs: capillary GC + MS (for dioxin-like

preferentially high-resolution);

(iii) For PFOS: liquid chromatography (LC) + (MS/MS);

(iv) For HBCD: GC/MS, LC-MS and HPLC-MS. GC-FID (flame ionization detector)

using a HBCD reference is also able to identify and quantify HBCD. This method

is validated for concentrations above 1000 mg/kg;

(v) For HCBD: GC/MS and GC+ECD;

(vi) For PCP and its salts and esters: Typical analytical detection uses GC+ECD,

GC/MSmass selective detectors, as well as LC/MS methods;

(vii) For PCNs: GC/MS for water analysis.;

(viii) For SCCPs: GC with either high or low resolution electron capture negative ion

mass spectrometry (GC/ECNI-MS), time-of-flight MS (TOF-MS),

deuterodechlorination combined with high resolution GC – high resolution MS

(HRGC-HRMS).

99.98. It is important that the steps described in subsections (a) and (b) of paragraph 98 97 above do not

generate false negatives and that any method comply with the level of interest for the analysis.

27 Information can be found at: DEXSIL test kits: http://www.dexsil.com/products/. 28 L2000 Analyzer http://www.dexsil.com/products/detail.php?product_id=13. 29 CALUX: http://www.crl-freiburg.eu/dioxin/bioanalytical.html.

Commented [HBCD IG6]: We have checked again

the work carried out by the IEC111 WG, and the

conclusion is that XRF method is appropriate for levels

between 500 ppm and 1000 ppm, but it has been

validated only for levels above 1000ppm. Therefore,

we recommend the author taking into account the

proposed comment:

“XRF is applicable to a wide range of concentrations

and appropriate for levels between 500 ppm and 1000

ppm. However, XRF is currently not validated for

concentrations below 1000ppm”.

UNEP/CHW.14/INF/9

28

100.99. Analysis refers to the extraction, purification, separation, identification, quantification and

reporting of POPs concentrations in the matrix of interest. To obtain meaningful and acceptable results,

the analytical laboratory should have the necessary infrastructure (housing) and proven experience with

the matrix and the POP (e.g., successful participation in international intercalibration assessments).

Accreditation of the laboratory in accordance with ISO 17025 or other standards by an independent

body is important. Indispensable criteria for obtaining high-quality results include:

(a) Specification of the analytical technique used;

(b) Maintenance of analytical equipment;

(c) Validation of all methods used (including in-house methods); and

(d) Training of laboratory staff.

101.100. Typically, POPs analysis is performed in a dedicated laboratory. For specific situations, test

kits are available that can be used in the field for screening purposes.

102.101. For laboratory POPs analysis, there is no single analytical method available. Methods of

analyzing the various matrices for POPs have been developed by ISO, the European Committee for

Standardization (CEN), EPA, AOAC and ASTM. Most in-house methods are variations of these, and

after validation such in-house methods are also acceptable.

103.102. In addition, procedures and acceptance criteria for handling and preparation of the sample in

the laboratory, e.g., homogenization, should be established.

104.103. The individual steps in the analytical determination include:

(a) Extraction, e.g., by Soxhlet, pressurized solvent extraction, liquid-liquid, etc.;

(b) Purification, e.g., by column chromatography or with Florisil. Purification should be

efficient enough so that chromatographic retention is not influenced by the matrix;

(c) Separation by capillary gas chromatography (HRGC), which will provide sufficient

separation of analytes;

(d) Identification by suitable detectors such as an ECD or a mass-selective detector, or by

either low-resolution mass spectrometry (LRMS) or high-resolution mass spectrometry (HRMS);

(e) Quantification in accordance with internal standard methodologies (for reference, see

UNEP, 2015d and UNEP, 201706b); and

(f) Reporting in accordance with regulation(s).

3. Monitoring

105.104. In Article 10 (“International Cooperation”), paragraph 2 (b), the Basel Convention requires

Parties to “cooperate in monitoring the effects of the management of hazardous wastes on human health

and the environment”. In Article 11, paragraph 1, the Stockholm Convention requires Parties, within

their capabilities, at the national and international levels, to encourage and/or undertake appropriate

monitoring pertaining to POPs.

106.105. Monitoring programmes should be implemented for facilities managing POP wastes, as they

provide an indication of whether a hazardous waste management operation is functioning in accordance

with its design and environmental regulations.

107.106. In environmental and human monitoring programmes, both biotic and abiotic matrices may be

included:

(a) Plant materials and food;

(b) Fish and wildlife

(c) Biological fluids (e.g. human breast milk , blood, urine);

(d) Air (ambient, wet or dry deposition such as snow, ice, dust);

(e) Water (e.g., leachate, wastewater);

(f) Soil;

(g) Sediment.

108.107. The information from the monitoring programme should be used to:

UNEP/CHW.14/INF/9

29

(a) Detect any releases to or changes in the quality of the surrounding environment;

(b) Ensure that different types of hazardous wastes are properly managed by the waste

management operation; and

(c) Identify potential issues relating to possible release or exposure and determine whether

adjustments to the management approach might be appropriate.

109.108. By implementing a monitoring programme, governments, regulators, municipalities and

recycling and waste facility managers can identify problems and take appropriate measures to remedy

them. Further information on monitoring can be found in the following documents: Monitoring and

research under the Chemicals Management Plan (Government of Canada, 2011; Environment Canada,

2011); General Principles of Monitoring (European Commission, 2003); Guidance for a Global Monitoring Programme for Persistent Organic

Pollutants (UNEP, 2015a); Ministry of the Environment of Japan, 2013a; and German Federation/Länder

Dioxin Database (German Federal Environment Agency Dessau-Roßlau, 2014).

F. Handling, collection, packaging, labelling, transportation and storage

110.109. Handling, collection, packaging, labelling, transportation and storage are critically important

steps as the risk of a spill, leak or fire can be as great as at other stages of the life cycle of a POP.

111.110. Considerations and provisions unique to POP waste streams are presented in the specific POP

technical guidelines when appropriate. A tailored approach for certain POP waste streams (e.g. articles

and products that have become waste) is desirable considering their various sources, waste types,

volumes and POP concentrations. This allows decision makers to consider the risks that various waste

streams may pose at different stages of their management, and the appropriate actions that may be

necessary to prevent, eliminate or minimize their impact on the environment. Best management

practices are, in some cases, in the early stages of being developed or documented.

112.111. Where appropriate, procedures and processes for managing hazardous wastes should be

considered for handling, collecting, packaging, labelling, transporting and storing wastes with a POP

content above the low POP contents referred to in section III.A in order to prevent spills and leaks

resulting in worker exposure, releases to the environment or exposure of the community.

113.112. Relevant information regarding the hazardous characteristics and risks of POP wastes should

be collected and analysed in order to plan for the proper handling of such wastes, for example by

consulting and following the instructions given on the chemicals they contain and related safety data

sheets. For labelling and packaging, the United Nations Globally Harmonized System of Classification

and Labelling of Chemicals (GHS) should be taken into account, accordingly

114.113. For transport and transboundary movement of POP wastes meeting the criteria of hazardous

wastes, the following documents should be consulted to determine specific requirements:

(a) Manual for the Implementation of the Basel Convention (UNEP, 2015h);

(b) International Maritime Dangerous Goods Code (IMO, 2002);

(c) International Civil Aviation Organization (ICAO) Technical Instructions for the Transport

of Dangerous Goods by Air; and

(d) United Nations Recommendations on the Transport of Dangerous Goods Model

Regulations.30

115.114. For the following sections (1–6), detailed information can be obtained from destruction and

decontamination technologies for PCBs and other POP waste under the Basel Convention: A training

manual for hazardous waste project managers (UNEP, 2002a).

1. Handling31

115. The main concerns when handling POP wastes are human exposure, accidental releases to the

environment and contamination of other waste streams with POPs. POP wastes should be handled

separately from other types of waste in order to prevent contamination of other waste streams.

30 European Agreement concerning the International Carriage of Dangerous Goods by Road (ADR); European

Agreement concerning the International Carriage of Dangerous Goods by Inland Waterways (ADN); Regulations

concerning the International Carriage of Dangerous Goods by Rail (RID). 31 Examples of guidelines on the safe handling of hazardous materials and accident prevention include those prepared by the International Labour

Organization (ILO, 1999a and 1999b) and OECD (OECD, 2003).

Commented [HBCD IG7]: We would like to reiterate

the comment made in the draft Technical Guidelines

circulated in March 2018, related to the observation

that the recommendations included in Section F address

primarily liquid waste. We suggest including separate

general recommendations for handling solid bulky

POP-containing waste (see for example Technical

Guidance for HBCD).

UNEP/CHW.14/INF/9

30

116. The management handling of liquid wastes streams and waste from articles and products, in

particular, and other wastes streams as appropriate should include the following recommended

practices:

(a) Inspecting containers for leaks, holes, rust or high temperatureto detect aging and loss of

containment, and appropriate repackaging and relabelling as necessary;

(b) Handling wastes at temperatures below 25°C, if possible, because of increased volatility at

higher temperatures;

(c) Ensuring that spill containment measures are adequate and would contain liquid wastes if

spilled;

(d) Placing plastic sheeting or absorbent mats under containers before opening them if the

surface of the containment area is not coated with a smooth surface material (paint, urethane or epoxy);

(e) Removing liquid wastes either by removing the drain plug or by pumping with a

peristaltic pump and suitable chemical-resistant tubing;

(f) Using dedicated pumps, tubing and drums, not used for any other purpose, to transfer

liquid wastes;

(g) Cleaning up any spills with cloths, paper towels or absorbent;

(h) Triple rinsing of contaminated surfaces with a solvent;

(i) Treating all absorbents and solvent from triple rinsing, disposable protective clothing and

plastic sheeting as wastes containing or contaminated with POPs when appropriate;

(j) In the handling of wastes of articles and products containing POPs, care should be taken

not to release POPs into the environment from such wastes; and

(jk) Training staff in the correct methods of handling POP wastes.

The management of solid waste streams (i.e. waste streams of articles and products containing

POPs) should, as appropriate, include the following recommended practices:

(a) A set of best practice procedures should be prepared by each organization that handles

POP wastes and workers should be trained in the procedures;

(b) In the handling of POP-containing wastes, care should be taken not to release POPs into

the environment from articles and products;

(c) During the treatment of waste, appropriate measures should be taken to protect the human

health and the environment from potential exposure to POPs; and

(d) The waste streams containing POPs should be kept separated from those waste streams

that do not contain POPs to facilitate environmentally sound waste management

2. Collection

117. Although large industries may be responsible for the proper management of the POP wastes that

they generate or own, many smaller entities also possess such wastes. The POP waste possessed by

small entities may, in addition to wastes from articles and products containing POPs (see para 121119

below), include household- or commercial-size pesticide containers, PCB fluorescent light ballasts,

small containers of pentachlorophenol-based wood preservatives with PCDD and PCDF contamination,

small amounts of “pure” POPs in laboratories and research facilities, and pesticide-coated seeds used in

agricultural and research settings. To deal with this scattered assortment of hazardous wastes, many

governments have established depots where small quantities of these wastes can be deposited by the

owner at no charge or for a nominal fee. These depots may be permanent or temporary in nature, or may

be located at existing commercial hazardous waste transfer stations. Waste-collection depots and

transfer stations may be set up on a regional basis by groups of countries or may be provided by a third

party to a developing country.

118. Care should be taken in establishing and operating waste collection programmes, depots and

transfer stations:

(a) To advertise the programme, depot locations and collection time periods to all potential

holders of POP wastes;

Formatted: Highlight

UNEP/CHW.14/INF/9

31

(b) To allow enough time of operation of collection programmes for the complete collection

of all potential POP wastes;32

(c) To include, to the extent practical, all POP wastes in the programme;

(d) To make acceptable containers and safe-transport materials available to waste owners for

those waste materials that may need to be repackaged or made safe for transport;

(e) To establish simple, low-cost mechanisms for collection;

(f) To ensure the safety both of those delivering waste to depots and workers at the depots;

(g) To ensure that the operators of depots are using an accepted method of disposal;

(h) To ensure that the programme and facilities meet all applicable legislative requirements;

and

(i) To ensure the separation of POP wastes from other waste streams.

119. Solid POP waste streams (i.e. waste streams ofWastes from articles and products containing

POPs) should be collected separately from those wastes that do not contain POPs. Concerning waste

electrical and electronic equipment that contains plastics containing POP-BDEs or HBCD, see section

IV.F.2 of the POP-BDEs technical guidelines. Concerning HBCD wastes like The insulation materials,

packaging textile waste containing HBCD, see section IV.F.2 of the HBCD guidelines. Concerning

waste containing SCCPs like PVC plastics, see section IV.F.2 of the SCCP technical guidelines and

other solid waste containing POPs from households can be exempt when these wastes, depending on the

POPs content, are incinerated or otherwise managed according to section IV.G of these guidelines.

120. Waste electrical and electronic equipment (WEEE) may contain plastics containing POPs. For

further information, see section IV.F.2 of the POP-BDEs technical guidelines. In Europe, Technical

Specification (TS) 50625-3-1 Collection logistics treatment requirements for WEEE is currently under

development, describing a sampling method for WEEE.

121. CollectionsCollection depots should not become long-term storage facilities for solid POPs

wastes.

3. Packaging

119.122. POP wastes, whether hazardous or not, should be properly packaged for ease of transport and

as a safety measure to reduce the risk of leaks and spills.

120.123. Packaging of hazardous wastes falls into two categories: packaging for transport and

packaging for storage. Packaging for transport is often controlled by national dangerous goods

transportation legislation. For packaging specifications for transport, the reader should consult reference

materials published by IATA, IMO, UNECE, GHS and national governments.

121.124. Some general precepts for the packaging of liquid POP wastes for storage are as follows:

(a) POPs waste should be properly packaged before transport or storage; however, wastes

from products and articles containing POP-BDEs or HBCD that are typically used by consumers do not

need specific packaging;

(ab) Packaging that is acceptable for transport is, in most cases, suitable for storage, unless

more stringent storage requirements are specified;

(bc) Such wastes in their original product containers are generally safe for storage if the

packaging is in good condition;

(cd) POP wastes should never be stored in product containers that were not intended to contain

such wastes or that have labels on them that incorrectly identify their contents;

(de) Containers that are deteriorating or are deemed to be unsafe should be emptied or placed

inside a sound outer package (overpack). When unsafe containers are emptied, the contents should be

placed in appropriate new or refurbished containers. All new or refurbished containers should be clearly

labelled as to their contents;

(ef) Smaller containers can be packaged together in bulk by placing them in appropriate or

approved larger containers containing absorbent material;

32 Complete collection may require the depots to operate either continuously or intermittently over several years.

UNEP/CHW.14/INF/9

32

(fg) Out-of-service equipment containing POPs may or may not constitute suitable packaging

for storage. The determination of its safety should be made on a case-by-case basis.

Some general precepts for the packaging and containment of solid POP waste streams (i.e. waste

streams of articles and products containing POPs) for storage are as follows:

(a) Such waste should be properly packaged before storage or transport as a means to facilitate

transport and as a safety measure to reduce the risk of spills;

(b) Articles containing POPs are typically consumer products and do not need specific packaging

requirements.

4. Labelling33

122.125. Labelling or registration of products containing POPs may be a necessary measure in order to

effectively manage the products upon becoming wastes.

123.126. Labelling of POP wastes containers is a basic safety feature for liquid POP waste and

important for the success of any waste management system. Each waste container should be labelled to

identify the container (e.g., ID number), the chemical, and the POP present and its hazard level.

5. Transportation

124.127. POP wastes should be transported in an environmentally sound manner to avoid accidental

spills and to track their transport and ultimate destination appropriately. Before transport, contingency

plans should be prepared in order to minimize environmental impacts associated with spills, fires and

other emergencies that could occur during transport. During transportation, such wastes should be

identified, packaged and transported in accordance with the “United Nations Recommendations on the

Transport of Dangerous Goods: Model Regulations (Orange Book)”. PersonsIn case the waste

containing POPs is qualified as hazardous waste, persons transporting such wastes should be qualified

and certified as carriers of hazardous materials and wastes.

125.128. Transportation of dangerous goods and wastes is regulated in most countries and the

transboundary movement of wastes is controlled, in particular by the Basel Convention.

126.129. Companies transporting hazardous wastes within their own countries should be certified as

carriers of hazardous materials and wastes, and their personnel should be qualified.

127.130. Guidance on the safe transportation of hazardous materials can be obtained from IATA, IMO,

UNECE and ICAO.

6. Storage34

128.131. According to Annex IV, sections A and B, of the Basel Convention, storage (operations

D5D15 and R13) is a temporary operation that precedes other disposal operations. POP wastes, after

having been appropriately packaged (see subsection IV.F.3 on packaging) should be stored safely,

preferably away from drinking water winning areas, and in dedicated areas away from other materials

and wastes. However, they could be stored together with other wastes if they were destined for a similar

disposal operation as listed under section IV.G. Storage areas should be designed to prevent the release

of POPs into the environment by any route. Storage rooms, areas and buildings should be designed by

professionals with expertise in the fields of structural design, waste management and occupational

health and safety or can be purchased in prefabricated form from reputable suppliers as approved by the

authorities, as appropriate.

129.132. Where necessary, POP wastes should be segregated at the source to ensure appropriate

arrangements for collection, including the use of collection tanks, taking into account their hazardous

characteristics and the risk of exposure that they present.

130.133. Some basic principles of safe storage of liquid POP wastes are as follows:

(a) Storage sites inside multi-purpose buildings should be in a locked dedicated room or

partition that is not in an area of high use;

33 International standards have been developed for the proper labelling and identification of wastes. Guidelines on the proper labelling and identification

of hazardous materials have been produced by UNECE (2003b). See also FAO, 2001; UNEP, 2015h; and UNEP, UNIDO et al, 2012.

34 Further information can be found in Storage of Hazardous Materials: A Technical Guide for Safe Warehousing of Hazardous Materials (UNEP, 1993) and

Pesticide Storage and Stock Control Manual (FAO, 1996). For full references, see annex III (bibliography) below.

UNEP/CHW.14/INF/9

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(b) Outdoor dedicated storage buildings or containers (shipping containers are often used for

storage) should be stored inside a lockable fenced enclosure;

(c) Separate storage areas, rooms or buildings may be required for each type of POP waste,

unless specific approval has been given for joint storage;

(d) Such wastes should not be stored at or near sensitive sites such as hospitals or other

medical care facilities, schools, residences, food processing facilities, animal feed storage or processing

facilities, agricultural operations, or facilities located near or within environmentally sensitive sites;

(e) Storage rooms, buildings and containers should be located and maintained in conditions

that minimize volatilization, including cool temperatures, reflective roofs and sidings, a shaded location,

etc. When possible, particularly in warm climates, storage rooms and buildings should be maintained

under negative pressure with exhaust gases vented through carbon filters, bearing in mind the following

conditions:

(i) Ventilating a site with carbon filtration of exhaust gases may be appropriate when

exposure to vapours of those who work at the site and those living and working in

the vicinity of the site is a concern;

(ii) Sealing and venting a site so that only well-filtered exhaust gases are released to

outside air may be appropriate when environmental concerns are paramount;

(f) Dedicated buildings or containers should be in good condition and made of hard plastic or

metal, not wood, fibreboard, drywall, plaster or insulation;

(g) The roofs of dedicated buildings or containers and the surrounding land should be sloped

to provide drainage away from the site;

(h) Dedicated buildings or containers should be set on asphalt, concrete or durable

(e.g., 6 mm) plastic sheeting;

(i) The floors of storage sites inside buildings should be concrete or durable (e.g., 6 mm

plastic sheeting). Concrete should be coated with a durable epoxy polymer;

(j) Storage sites should have fire alarm systems;

(k) Storage sites inside buildings should have (preferably non-water) fire suppression

systems. If the fire suppressant is water, then the floor of the storage room should be curbed and the

floor drainage system should not lead to the sewer or storm sewer or directly to surface water but should

have its own collection system, such as a sump;

(l) Liquid wastes should be placed in containment trays or in curbed, leak-proof areas. The

liquid containment volume should be at least 125 per cent of the liquid waste volume, taking into

account the space taken up by stored items in the containment area;

(m) Contaminated solids should be stored in sealed containers such as barrels or pails, steel

waste containers (lugger boxes) or in specially constructed trays or containers. Large volumes of

material may be stored in bulk in dedicated shipping containers, buildings or vaults so long as they meet

the safety and security requirements described herein;

(n) A complete inventory of such wastes in the storage site should be created and kept up to

date as waste is added or disposed of;

(o) The outside of the storage site should be labelled as a waste storage site;

(p) The site should be subjected to routine inspection for leaks, degradation of container

materials, vandalism, integrity of fire alarms and fire suppression systems and general status of the site;.

(q) The storage area for POP wastes should have reasonable access roads for transportation

vehicles.

Some basic principles for the safe storage of solid waste streams (i.e. waste streams of articles

and products containing POPs) are as follows:

(a) POP wastes should be stored in designated sites, with appropriate measures taken to

prevent the scatter, the release, the underground seepage and the spread of odors;

(b) Appropriate measures, such as the installation of partitions or labelling, should be

taken to avoid contamination by POP waste;

(c) The storage area for POP wastes should have reasonable access roads for

transportation vehicles.

UNEP/CHW.14/INF/9

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G. Environmentally sound disposal

134. The methods for destruction or irreversible transformation of the POP content of wastes with a

POP content at or above the defined low POP content are described in subsection 2. The methods for

disposal other than destruction or irreversible transformation of the POP content of wastes with a POP

content at or above the defined low POP content, when destruction or irreversible transformation does

not represent the environmentally preferable option, are described in subsection 3.

135. The methods for disposal other than referred to above for wastes with a POP content below the

defined low POP content are described in subsection 4.

1. Pre-treatment35

131.136. This section presents some of the pre-treatment operations that may be required for the proper

and safe operation of the disposal technologies described in subsections 2 and 3 below. There are other

pre-treatment operations that may be applied. Pre-treatment operations prior to disposal in accordance

with subsections IV.G.2 and IV.G.3 should be performed only if the POPs that are isolated from the

waste during pre-treatment are subsequently disposed of in accordance with subsection IV.G.2. When

only part of a product or waste, such as waste equipment, contains or is contaminated with POPs, it

should be separated and then disposed of as specified in subsections IV.G.1–4, as appropriate.

(a) Adsorption and absorption

132.137. “Sorption” is the general term for both absorption and adsorption processes. Sorption is a

pre-treatment method in which solids are used for removing substances from liquids or gases.

Adsorption involves the separation of a substance (liquid, oil, gas) from one phase and its accumulation

at the surface of another (activated carbon, zeolite, silica, etc.). Absorption is the process whereby a

material transferred from one phase to another interpenetrates the second phase; for example, when

contaminants are transferred from liquid phase onto granular activated carbon (GAC). GAC is widely

applied in the removal of organic contaminants in wastewaters because of its effectiveness, versatility

and relatively low-cost.

133.138. Adsorption and absorption processes can be used to extract contaminants from aqueous wastes

and from gas streams. The concentrate and the adsorbent or absorbent may require treatment prior to

disposal.

(b) Blending

134.139. The blending of waste to create a homogeneous feedstock prior to waste treatment may be

appropriate in order to enable treatment or to optimize treatment efficiency. However, the blending of

wastes with POP contents above a defined low POP content with other materials for the purpose of

generating a mixture with a POP content at or below the defined low POP content is not

environmentally sound.

(c) Desorption

135.140. Desorption includes chemical desorption and thermal desorption. Thermal desorption (e.g.,

through vacuum thermal recycling or the use of a toroidal bed reactor or a liquid waste pre-heater) is a

technology that utilizes heat to increase the volatility of contaminants such that they can be removed

(separated) from a solid matrix (typically soil, sludge or filter cake). Direct fired and indirect fired

desorbers exist. Thermal desorption processes are also categorized into high temperature thermal

desorption (HTTD) and low-temperature thermal desorption (LTTD) processes. In HTTD, wastes are

heated between 320cC and 550cC and in LTTD between 90cC and 350cC. LTTD, also known as low-

temperature thermal volatilization, thermal stripping and soil roasting is used for volatile and semi-

volatile compounds and elements (most commonly light petroleum hydrocarbons) from contaminated

media (most commonly excavated soils). Such processes have been used for the decontamination of

non-porous surfaces of electrical equipment, such as transformer carcasses that formerly contained

PCB-containing dielectric fluids, or fluorescent lamps that contained mercury. Thermal desorption of

POP wastes may result in the unintentional formation of POPs which may require additional treatment

of treated waste or off-gas released.

35 Further information on pre-treatment can be found in the Basel technical guidelines on hazardous wastes-

Physico-Chemical Treatment/Biological Treatment. UNEP, 2000a.

UNEP/CHW.14/INF/9

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(d) Dewatering

136.141. Dewatering is a pre-treatment process in which water is partially removed from the wastes to

be treated. Dewatering can be employed for disposal technologies that are not suitable for aqueous

wastes. For example, water will react explosively with molten salts or sodium. Depending on the nature

of the contaminant, the resulting vapours may require condensation or scrubbing and further treatment.

(e) Dismantling/disassembling

137.142. Dismantling or disassembling is a pre-treatment in which equipment, components or

assemblies are taken apart to separate materials to increase options for reuse, refurbishment, recycling,

recovery and final disposal.

(f) Dissolution

138.143. Pre-treatment by which a waste (liquid, solid or gas) is dissolved into a solvent.

(g) Distillation

139.144. A process which separates a solvent from a mixture by applying thermal energy and vaporising

components and then condensing that vapour in a subsequent stage. Through this process, the solvent is

separated, thereby allowing for subsequent recovery of the solvent and the reduction of the volume of

waste destined for final disposal using other processes.

(h) Drying

140.145. Drying is a pre-treatment that removes water or a solvent by evaporation from a solid, semi-

solid or liquid waste. In general, a gas stream, e.g., air, applies the heat by convection and carries away

the vapor as humidity. Vacuum drying can also be used when heat is supplied by conduction or

radiation (or microwaves), while the vapor produced can be removed with a vacuum system.

(i) Mechanical separation

141.146. Mechanical separation can be used to remove larger-sized debris from the waste stream or for

technologies that may not be suitable for both soils and solid wastes.

(j) Membrane filtration

142.147. Membrane filtration is a thin film separation of two or more components in a liquid and is used

as an option for conventional wastewater treatment. It is a pressure- or vacuum-driven separation

process in which contaminants may be rejected by an engineered barrier, primarily through a size-

exclusion mechanism. Different classifications of membrane treatment applicable to POPs include

nanofiltration and reverse osmosis.

(k) Mixing

143.148. Mixing materials, without blending, prior to waste treatment may be appropriate in order to

enable treatment or to optimize treatment efficiency. However, the mixing of wastes with POP contents

above a defined low POP content with other materials (including other waste with POP content below

the defined low POP content) solely for the purpose of generating a mixture with a POP content at or

below the defined low POP content is not environmentally sound.

(l) Oil-water separation

144.149. Some treatment technologies are not suitable for aqueous wastes, while others are not suitable

for oily wastes. Oil-water separation can be employed in these situations to separate the oily phase from

the water. Both the water and the oily phase may be contaminated after separation and both may require

treatment.

(m) pH adjustment

145.150. Some treatment technologies are most effective over a defined pH range and in these situations

alkali, acid or CO2 are often used to control pH levels. Some technologies may also require pH

adjustment as a post-treatment step.

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(n) Sedimentation

146.151. Sedimentation is a physical process whereby particles settle by gravity. Chemical agents can

be added to facilitate the settling process.

(o) Size reduction

147.152. Some technologies can be used to process wastes only within a certain size limit. For example,

some technologies may be used to handle POP-contaminated solid wastes only if they are less than 200

mm in diameter. Size reduction can be used in these situations to reduce the waste components to a

defined diameter. Size reduction can include crushing, shearing and grinding. Other disposal

technologies require slurries to be prepared prior to injection into the main reactor. It should be noted

that facilities may become contaminated when reducing the size of POP wastes. Precautions should

therefore be taken to prevent subsequent contamination of POP-free waste streams.

(p) Solvent washing

148.153. Solvent washing can be used to remove POPs from electrical equipment such as capacitors and

transformers. This technology has also been used for the treatment of contaminated soil and sorption

materials used in adsorption or absorption pre-treatment.

(q) Stabilization and solidification

149.154. Stabilization and solidification are to be used in conjunction for them to be environmentally

sound. The stabilization of waste refers to the chemical conversion of the hazardous constituents in the

waste to less soluble, mobile or toxic materials. The solidification of waste refers to changes in the

physical properties of the waste to increase its compressive strength, decrease its permeability and

encapsulate its hazardous constituents. Many waste streams require pre-treatment or special additives

prior to stabilization and solidification. Applicability trials and durability tests prior to both stabilization

and solidification are advisable.

(r) Vaporization

150.155. The conversion of liquid or solid substances into a gaseous state prior to waste treatment may

be appropriate in order to enable or optimize treatment efficiency.

(s) Volume reduction

151.156. The reduction of waste volume through compression or compaction to make the waste more

condensed may be appropriate to facilitate waste handling, transport, storage and disposal.

For polystyrene foam (EPS and XPS) wastes containing HBCD, a series of pre-treatment steps

can be applied to separate HBCD from polystyrene for subsequent destruction of the POP. The relevant

pre-treatments operations include volume reduction, size reduction, dissolution, sedimentation, and

distillation. In the case of XPS waste containing HBCD and which may also contain ozone depleting

substances controlled by the Montreal Protocol on Substances That Deplete the Ozone Layer, measures

should be taken to prevent the release of ODS to the environment during these pre-treatment operations.

2. Destruction and irreversible transformation methods

152.157. The following disposal operations, as provided for in Annex IV, sections A and B, of the Basel

Convention, should be permitted for the purpose of destruction and irreversible transformation of the

POP content in wastes when applied in such a way as to ensure that the remaining wastes and releases

do not exhibit the characteristics of POPs:

(a) D9: Physico-chemical treatment;

(b) D10: Incineration on land;

(c) R1: Use as a fuel (other than in direct incineration) or other means to generate energy;

and

(d) R4: Recycling/reclamation of metals and metal compounds, but restricted to activities of

primary and secondary metallurgy described in (k) below.

153.158. POPs that are isolated from a waste stream during pre-treatment should subsequently be

disposed of in accordance with operations D9 and D10.

Commented [HBCD IG8]: As paragraph 157 was

removed by the author, we recommend including a

reference to the Technical Guidelines on HBCD for

polystyrene foam (EPS and XPS) wastes containing

HBCD.

UNEP/CHW.14/INF/9

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159. Subsections (a) to (k) below describe commercially available operations for the environmentally

sound destruction and irreversible transformation of the POP content in wastes that are capable of

achieving the levels of destruction and irreversible transformation referred to in section III.B.36 Table 4

below provides an overview of these operations [whereby the contents in this table on POPs reflects the

information from the paragraphs on waste types, in the subsections (a) to (k)].)]. Table 4 should be used

in conjunction with the following subsections to gain a more fulsome understanding of the many factors

to consider before making decisions concerning the use of destruction and irreversible transformation

methods. It should be noted that pertinent national legislation applyapplies to these operations and that

the operations should be used in accordance with the BAT and BEP standards developed under the

Stockholm Convention, as presented in the Guidelines on best available techniques and provisional

guidance on best environmental practices relevant to Article 5 and Annex C of the Stockholm

Convention on Persistent Organic Pollutants (UNEP, 2007). Consequences of not conducting the

operations according to the standards outlined in the BAT and BEP guidance can lead to the formation

and release of POPs into the environment.37

160. Available information on the technologies, especially for more recent ones, is constantly

evolving. Each facility operator may determine if an appropriate level of destruction and irreversible

transformation will be achieved using a particular technology in given conditions.

154.161. Emerging technologies are not described in this subsection because their commercial

availability and their performance with regard to destruction and irreversible transformation of POPs are

not documented.

162. For assessing the performance of the operations in subsections (a) to (k) below, a minimum DE

of 99.999 per cent, with 99.9999 per cent of DRE as a supplement requirement where applicable,

provides practical benchmark parameters for assessing disposal technology performance. Higher

demonstrated DEs may be preferred on a case-by-case basis. DE and DRE should be used together to

demonstrate a level of destruction and irreversible transformation; Aas neither DE nor DRE take into

account the potential transformation of the original POP to an unintentionally produced POP, potential

releases of unintentionally produced POPs should be considered when choosing a particular operation.

36 Further information regarding these current and emerging technologies can be found in: UNEP, 2004a; volumes A and B of UNEP, 2002a

(currently being updated) and at STAP, 2011; UNEP, 2007. For full references, see annex III (bibliography) below.

37 For example, a contamination of the food chain in the surrounding of a cement kiln co-incinerating HCB wastes

and a hazardous waste incinerator that incinerated HCB wastes have occurred (Weber et al. (2015).

Formatted: Highlight

Commented [EU/MS9]: According to our

understanding, this text has been agreed in the SIWG

meeting in October 2018; the square brackets should

therefore be lifted.

UNEP/CHW.14/INF/9

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Table 4: Overview of technologies for the destruction and irreversible transformation of POPs in

wastes.

Technology POPs

HBB HBCD HCB,

HCBD

and

PeCB

PCB PCDDs/

PCDFs

PCN PCP Pesticides

POPs

PFOS POP-

BDEs

SCCPs

(a) Alkali metal

reduction

ND ND ND Yes ND ND ND Yes for

Yes, for

certain

pesticides:

chlordaneC

hlordane,

HCH

ND ND* ND

(b) Advanced solid

waste incineration

(ASWI)

ND Yes ND ND ND ND Yes ND ND Yes Yes

(c) Base catalyzed

decomposition (BCD)

ND ND ND Yes Yes ND Yes Yes, for

certain

pesticides: chlordane,

HCH

DDT,

HCBYes

ND ND ND

(d) Catalytic

hydrodechlorination

(CHD)

ND NAND ND Yes Yes ND NDY

es

ND NAND NAND

**

ND

(e) Cement kiln

co-incineration

Yes Yes Yes Yes Yes Yes Yes Yes, for all

pesticides

Yes Yes Yes

(f) Gas phase chemical reduction (GPCR)

Yes Yes Yes Yes Yes Yes Yes Yes for all pesticides:

Yes Yes Yes

(g) Hazardous waste

incineration

Yes Yes YesNo

Yes

Yes Yes Yes Yes

NoY

es

Yes, for all

pesticides

Yes Yes Yes

(h) Plasma arc ND ND ND Yes ND ND ND Yes, for

most

pesticides,

including

chlordane, chlordecon

e, DDT,

endosulfan,

heptaclor

ND ND ND

(i) Plasma melting

decomposition

method (PMD)

ND ND ND Yes ND ND ND ND ND ND ND

(j) Supercritical water

oxidation (SCWO)

and subcritical water oxidation

NDYes NDYes NDYes Yes Yes, for

PCDDs

NDY

es

NDY

es

Yes, for

certain

pesticides: chlordane

and DDT

Yes

YesND NDYes Yes

(k) Thermal and

metallurgical

production of metals

ND ND ND ND YesND ND ND ND ND NDYes ND

* ND stands for “not determined” and indicates that information is not available in the literature referred to in this

document to confirm the use of the technology for certain POPs.

** NA stands for “not applicable”.

(a) Alkali metal reduction38

155.163. Process description: Alkali metal reduction involves the treatment of wastes with dispersed

alkali metals. Alkali metals react with chlorine in halogenated waste to produce salts and

38 Additional information is available in UNEP, 1998, UNEP, 2000, and UNEP, 2004a.

Commented [HBCD IG10]: We recommend the

author considering that only ASWI, cement-kiln and

thermal and metallurgical production of metals are

appropriate for bulky HBCD-containing waste. We

also recommend the author adding a reference to the

Technical Guidelines on HBCD.

Commented [EU and MS11]: This symbol should be

shown at the first appearance of “ND”

Commented [EU/MS12]: We would like to seek

clarification why “NA” has been replaced by “ND”

Commented [EU/MS13]: We would like to seek

clarification why “NA” has been replaced by “ND”

Commented [HBCD IG14]: We would like to

reiterate that, for the reasons indicated in paragraph 297

of this draft Technical Guidelines, this technology

cannot effectively treat most HBCD-containing waste

which has a large volume and has more than 20%

organic content.

Paragraph 297 of this draft Technical Guidelines reads

as follows:

“SCWO and subcritical water oxidation are thought to

be applicable to all POPs. 1Applicable waste types

include aqueous wastes, oils, solvents and solids with a

diameter of under 200 µm. The organic content of the

waste is limited to below 20 per cent by weight.1

Supercritical and subcritical fluids have been showed

to decompose HIPS plastics containing

decabromodiphenylether. The main reaction products

were oils containing ethylbenzene. The bromine from

the flame retardant was removed into the aqueous

phase (Onwudili & Williams, 2009, Goto, 2016).”

UNEP/CHW.14/INF/9

39

non-halogenated waste. Typically, the process operates at atmospheric pressure and at temperatures of

between 60°C and 180°C.39 Treatment can take place either in situ (e.g., in the case of

PCB-contaminated transformers), or ex situ in reaction vessels. There are several variations of this

process (Piersol, 1989). Although potassium and potassium-sodium alloy have been used as reducing

agents, metallic sodium is the most commonly used reducing agent. The information discussed in the

remainder of this subsection is based on experiences with the use of metallic sodium.

156.164. Efficiency: Destruction efficiencies (DEs) of more than 99.999 per cent and destruction

removal efficiencies (DREs) of 99.9999 per cent have been reported for chlordane, HCH and PCBs

(Ministry of Environment of Japan, 2004). The sodium reduction process has also been demonstrated to

meet regulatory criteria in Australia, Canada, Japan, South Africa, the United States of America and the

European Union for PCB transformer oil treatment, i.e., less than 2 mg/kg in solid and liquid residues

(UNEP, 2004b).

157.165. Waste types: Sodium reduction has been demonstrated with PCB-contaminated oils containing

concentrations up to 10,000 mg/kg. Some vendors have claimed that this process is capable of treating

whole capacitors and transformers (UNEP, 2004a). It is also reported that alkali metal reduction is

applicable to chlordane and HCH as waste pesticides (Ministry of the Environment of Japan, 2004).

158.166. Pre-treatment: Ex-situ treatment of PCBs can be performed following solvent extraction of

PCBs. Treatment of whole capacitors and transformers could be carried out following size reduction

through shearing. Pre-treatment should include dewatering by phase separation, evaporation, or other

method (UNIDO, 1987) to avoid explosive reactions with metallic sodium. Equipment should be

washed with organic solvents. Similarly, the POPs that are in a solid or adsorbed form would need to be

dissolved to the required concentration or extracted from their matrices (Piersol, 1989 and UNEP,

2004a).

159.167. Emissions and residues: Air emissions include nitrogen and hydrogen gas. Emissions of

organic compounds are expected to be relatively minor (Piersol, 1989). It has been noted, however, that

PCDDs and PCDFs can be formed from chlorophenols under alkaline conditions at temperatures as low

as 150°C (Weber, 20042004b). Residues produced during the process include sodium chloride, sodium

hydroxide, polyphenyls and water. In some variations, a solidified polymer is also formed (UNEP,

2000). According to UNEP (2006d) emissions of dioxin (PCDD), furan (PCDF) and dioxin-like PCBs

to air and water were very low, in the order of <0.002 ng TEQ/m3N in air and 0.00005–0.0001 ng

TEQ/L in waste water. Levels in solid residues were also low (1.7–54 µg/kg for PCB and 0.0018 µg

TEQ/kg for PCDD/PCDF/dioxin-like PCBs).

160.168. Release control and post-treatment: After a reaction, the resulting by-products can be

separated out from the oil through a combination of filtration and centrifugation. The decontaminated

oil can be reused, the sodium chloride can either be reused or disposed of in a landfill, and the solidified

polymer can be disposed of in a landfill (UNEP, 2000), with no or minimal post-treatment required.

Depending on the technology used, the combination of filtration and centrifugation can include off-gas

treatment and neutralization or conservation of residuals. The excess sodium, if not neutralized, may

need to be recovered. Liquid products, if not reused, and solidified polymeric products should be

usually burnt in incinerators, and inorganic salts would require disposal. Minor quantities of volatile

organic compounds in emissions can be captured with the use of activated carbon (UNIDO, 2007).

161.169. Energy requirements: Immediate energy requirements are expected to be relatively low owing

to the low operating temperatures associated with the sodium reduction process.

162.170. Material requirements: Sodium is required to operate this process (UNEP, 2004a).

163.171. Portability: The process is available in transportable and fixed configurations (UNEP, 2000).

164.172. Health and safety: Dispersed metallic sodium can react violently and explosively with water,

presenting a major hazard to operators. Metallic sodium can also react with a variety of other substances

to produce hydrogen, a flammable gas that is explosive in admixture with air. Great care must be taken

in the process design and operation to exclude any water (and certain other substances, e.g., alcohols)

from the waste and to prevent any contact of water (or certain other substances) with the metallic

sodium.

165.173. Capacity: Mobile facilities are capable of treating 15,000 litres per day of PCB-contaminated

transformer oils (UNEP, 2000).

166.174. Other practical issues: Sodium reduction used for in-situ treatment of PCB-contaminated

transformer oils may not destroy all the PCBs contained in the porous internals of the transformer.

39 Ariizumi et al, 1997.

UNEP/CHW.14/INF/9

40

Some authors have noted that there is a lack of information on the characterization of residues (UNEP,

2000).

167.175. State of commercialization: Alkali metal reduction has been used commercially for about

25 years and is still in use today. In Japan, three commercial-scale facilities were installed in 2004,

2005 and 2009 and are currently in operation (JESCO, 2009a; JESCO, 2009b; JESCO, 2013). Plants are

also in France, Spain and Iran, Russian Federation, and Spain.

(b) Advanced Solid Waste Incineration (ASWI)

176. Process description: There are many different types of municipal waste incinerators and not all

municipal waste incinerator technologies or facilities are able to properly destroy POPs in waste.

Advanced solid waste incinerators are designed to safely treat the contaminants present in municipal

solid waste (MSW) and similar commercial and industrial waste, usually in grate furnaces operating at

high temperatures, and incorporating state-of-the-art pollution-control methods. Advanced solid waste

incineration processes involve maintaining a minimum temperature of 850˚C in the combustion

chamber(s) with a residence time in the gas phase of at least two seconds. There are also incineration

facilities dedicated to wood waste that are able to incinerate wood waste containing or contaminated

with PCP under similar conditions as described above (European Commission, 2011)., SEPA 2009), but

the available data suggests the temperature should be 910-1025˚C. The conditions and operating

requirements of the processes described above should be stringent and meet the levels of destruction

and irreversible transformation set out in subsection IV.G.2. Some countries have included such

requirements in their national legislation.40

177. There are also incineration facilities dedicated to wood waste that are able to incinerate wood

waste containing or contaminated with PCP. PCP treated wood combusted at 910-1025°C resulted in no

detectable chemicals in the off-gas (European Commission, 2011). According to the Swedish

Environmental Protection Agency (2009), the controlled combustion conditions under which most

wood and wood based materials are incinerated in Sweden destroy dioxins and other chlorinated

aromatic substances in the treated timber., SEPA 2009), but the available data suggests the temperature

should be 910-1025˚C.

177bis. The conditions and operating requirements of the processes described in paragraphs 176 and

177 above should be stringent and meet the levels of destruction and irreversible transformation set out

in subsection IV.G.2. Some countries have included such requirements in their national legislation. 41

168.178. In order to properly destroy the HBCD contained in waste a temperature higher than 850˚C is

necessary. In the case of a full scale test trial of the treatment of polystyerene foam (EPS and XPS)

waste containing HBCD in the Würzburg Municipal Solid Waste Incinerator (Germany), where the

input contained 1-2 weight-per cent of such foam waste containing 6,000 to 21,000 mg/kg of HBCD,

the necessary combustion temperature was 900–1,000°C (Mark et al, 2015). Similarly, PBDEs have

been found in bottom ashes from combustion of MSW indicating that PBDE is not completely

destroyed (Wang et al 2010) in the combustion chamberIn the case of a full scale test trial of the

treatment of e-waste in the Tamara Municipal Solid Waste Incinerator (Germany), where the input

contained 20.5-3.51% of bromine including POP-BDEs, the temperature was 1,000°C (Vehlow, et al.,

2002). These trial results were confirmed by a full scale facility study conducted in Norway, where total

input of brominated flame retardants was less than 500 g/h (Borgnes & Rikheim, 2005. 0, 5, 10 and

20% of brominated flame retardants containing waste containing brominated flame retardants was fed

into a municipal solid waste incinerator at levels of 0, 5%, 10% and 20% brominated waste

(corresponding to approximately 0.05, 0.1 and 0.2% bromine) (Borgnes & Rikheim, 2005). Increasing

the brominated waste content gave no significant increase in the emissions of chlorinated dioxins, or

either brominated and chlorinated/brominated dioxins in the study. The emission measurement results

indicate that the incineration efficiency and the operating conditions of the APC systems are of greater

importance to the resulting emission levels of dioxins, rather than the bromine content level. In the case

of incineration or co-incineration of hazardous waste with a content of more than 1 per cent of

halogenated organic substances expressed as chlorine, a temperature of at least 1,100˚C is required.

40 See EU Directive 2010/75/EU on industrial emissions, chapter 4. The directive succeeded Directive 2008/1/EC

(integrated pollution prevention and control) and is aimed at minimizing pollution from various industrial sources

throughout the European Union. Operators of industrial installations engaged in activities covered under Annex I to

the Directive are required to obtain an integrated permit from the authorities of EU countries. 41 See EU Directive 2010/75/EU on industrial emissions, chapter 4. The directive succeeded Directive 2008/1/EC

(integrated pollution prevention and control) and is aimed at minimizing pollution from various industrial sources

throughout the European Union. Operators of industrial installations engaged in activities covered under Annex I to

the Directive are required to obtain an integrated permit from the authorities of EU countries.

Formatted: Highlight

Formatted: Strikethrough, Highlight

Formatted: Strikethrough, Highlight

Formatted: Strikethrough, Highlight

Commented [EU and MS15]: Moved to para. 177bis

(and slightly amended) because this text should also

apply to para 177

Formatted: Strikethrough, Highlight

UNEP/CHW.14/INF/9

41

Cable waste (PVC) containing chlorinated paraffins was co-incinerated with ordinary municipal solid

waste in a municipal solid waste incineration plant in Hamburg. Chlorinated paraffins were completely

destroyed in the combustion chamber (~850 °C) (PE Europe GmbH, 2010).

169.179. During incineration, flue gases are released that contain most of the available fuel energy as

heat. The organic substances in the waste burn as soon as they reach the ignition temperature. It is noted

that it may be necessary to add other fuels in order to adjust the temperature during incineration as well

as during the starting up and shutting down of furnaces.

170.180. It should be noted that residual waste typically contains small amounts of heavy metals,

sulphur and chlorine and may contain small amounts of flame retardants in plastic or textile waste.

These substances are found in practically all fractions of residual waste and in a variety of chemical

compounds. For this reason, the requirements for technical systems ensuring safe residual waste

treatment are highly complex.42

171.181. The guidance on BAT/BEP developed by the Stockholm Convention relevant to Article 5 and

Annex C should be used and applied to this technology (UNEP, 2007).

172.182. Efficiency: Under appropriate combustion conditions, organic compounds are destroyed during

incineration.43 Reports by the Technology and Economic Assessment Panel (TEAP) of the Montreal

Protocol on Substances that Deplete the Ozone Layer, in particular a 2002 report of the TEAP Task

Force on Destruction Technologies (TFDT), has shown the high destruction efficiency of ASWI for

halogenated substances such as CFCs and HCFCs in polystyrene foams.

173.183. In the full-scale test trial at the Würzburg Municipal Solid Waste Incinerator it was shown that

ASWI was able to destroy HBCD with a DE of 99.999 per cent for EPS and XPS foams.44 In a mass-

balance study using commercial scale industrial waste incineration plants (Kajiwara et al., 2017), DE of

99.999% was achieved with XPS/waste mixing ratios of up to approximately 3 % (w/w).n a pilot-scale

test in Japan, it was calculated that HBCDs were destroyed in the whole incineration process with DE of

more than 99.9999 for both of EPS and XPS (Takigami et al., 2016). Controlled combustion is

demonstrated to achieve a DE greater than 99.9 and 99.99 per cent for treated wood containing PCP.45

DE for PBDEs in ASWI was calculated at 99.99% (Borgnes and Rikheim, 2005, Mark et al., 2006).

174.184. Waste types: Advanced solid waste incinerators are designed to incinerate MSW, including

residual waste, but can also treat some waste from industry and commerce.46 A full-scale test trial

showed that an ASWI was suitable for the incineration of polystyrene foam (EPS and XPS) waste

containing HBCD.47 ASWI has been demonstrated to treat waste containing POP-BDEs (Borgnes &

Rikheim, 2005; Vehlow, 2002; OECD, 1998; European Commission, 2011).) as well as SCCPs (PE

Europe GmbH, 2010). Wood waste containing or contaminated with PCP can be incinerated in

incineration facilities dedicated to wood waste (European Commission, 2011, German Federal

Environment Agency, 2015).

175.185. Pre-treatment: Waste should be mixed in a bunker in order to keep its calorific value constant.

Volume reduction (crushing or shredding) is needed for bulky waste.

186. Emissions and residues: Emissions include carbon dioxide, water vapour, hydrogen chloride,

hydrogen fluoride, sulphur-dioxide and other oxides of sulphur, particulates, nitrogen oxides, total

organic carbon (TOC), PCDD/PCDF, heavy metals and carbon monoxide,48 and could also include

PBDD/PBDF (UNEP, 2007). Other emissions include hydrogen bromide and PXDD/PXDF (Mark et

al.,2015)49. Incinerators applying BAT that, inter alia, are designed to operate at high temperatures, to

minimize the reformation of PCDDs and PCDFs and to remove PCDD and PCDF (e.g., with the use of

activated carbon filters) have led to very low PCDD and PCDF emissions to air and discharges to

water.50 Increasing the brominated waste content caused no significant increase in the emissions of

chlorinated dioxins, or either brominated and chlorinated/brominated dioxins (Borgnes & Rikheim,

2005). The emission measurement results indicate that the incineration efficiency and the operating

42 See Austrian Federal Ministry of Agriculture, Forestry, Environment and Water Management, 2010. 43 See BiPRO GmbHEuropean Commission, 2005. 44 See Mark et al., 2015.

45 European Commission, 2011, Lee & Valenti, 1998, respectively. 46 See European Commission, 2006. 47 See Mark et al., 2015. 48 See European Commission, 2006. 49 See Mark et al., 2015. 50 See UNEP, 2001.

Commented [CEWEP16]: This sentence makes no

sense if this is deleted.

UNEP/CHW.14/INF/9

42

conditions of the air pollution control systems are of greater importance to the resulting emission levels

of dioxins, rather than the bromine content level.

176.187. Brominated flame retardants have been found in the bottom and fly ash of the incineration

plants. Wang et al. (2010) found PBDEs (78 ng/g) PBDEs were found in bottom ash when BFRs containing waste iswas

incinerated (Wang et al. 2010). The fly ashes in Wang´s study contained substantially lower concentrations of PBDEs than the

bottom ash. In the mass flow analysis of HBCD destruction in commercial-scale industrial waste

incineration plants, a large part of undecomposed HBCD ended up in the bottom ash (Kajiwara et al.,

2017).

177.188. In residues, PCDDs and PCDFs are mainly found in fly ash and flue gas cleaning residues, in

the range from 0.0008 to 35 ng TEQ/g, while bottom ash (representing the largest mass flow of residues

from waste incineration) and scrubber water sludge contain a comparably small amount of PCDDs and

PCDFs.51 According to the facility study conducted in Norway, emission to air of polybrominated

diphenyl ethers was 3,5 ng/Nm3 (Borgnes & Rikheim, 2005).

178.189. Release control and post-treatment: Process gases usually require treatment to remove

hydrogen chloride and fluoride, sulphur and nitrogen oxides, heavy metals and particulate matter, and to

prevent the formation of, or remove, unintentionally produced POPs. This can be achieved through the

combined use of cleaning equipment, including electrostatic precipitators, fabric filters, scrubbers,

selective catalytic or non-catalytic reduction, and carbon adsorption. Depending upon their

characteristics including POPs concentrations, bottom and fly ashes may require disposal within a

specially engineered landfill or permanent storage in underground mines and formations, or may be

used for backfilling in salt mines.52

179.190. Energy requirements: The amount of combustion fuel required depends on the composition of

the waste to be treated and the flue gas treatment technologies to be applied.

180.191. Material requirements: Material requirements may include lime, sodium bicarbonate,

activated carbon and other suitable materials for the removal of acid gases and other pollutants.

181.192. Portability: ASWI facilities are fixed units.

182.193. Health and safety: To ensure that appropriate health and safety measures are taken, ASWI

facilities should be designed and operated in accordance with to the relevant chapters of EU Directive

2010/75/EU on industrial emissions (integrated pollution prevention and control) and the European

Commission Best Available Techniques Reference Document (BREF) on Waste Incineration (See

section 2.8.5 on “overview of safety devices and measures.”) (European Commission, 2006)

183.194. Capacity: Each ASWI facility can treat between 30,000 and more than 1,000,000 tonnes of

waste per year. Due to the high volume of HBCD-containing PS foams (which have a high volume and

densities between 15 and 40 kilogram/cubic meters), the use of 1-2 per cent by weight of such foams,

which corresponds to about 15 per cent to 30 per cent by volume, is recommended (Mark et al, 2015).

184.195. Other practical issues: There are no practical issues to report at this time.

185.196. State of commercialization: There is a long history of experience with municipal waste

incineration.53 Currently, some ASWI facilities are operating in Europe.

(c) Base-catalysed decomposition (BCD)54

186.197. Process description: The BCD process involves treatment of wastes in the presence of a

reagent mixture consisting of a hydrogen-donor oil, an alkali metal hydroxide and a proprietary catalyst.

When the mixture is heated to above 300 °C, the reagent produces highly reactive atomic hydrogen. The

atomic hydrogen reacts with the waste to remove constituents that confer toxicity to the compounds.

187.198. Efficiency: DEs of 99.99–99.9999 per cent have been reported for DDT, HCB, PCBs, PCDDs

and PCDFs (UNEP, 2000), HCH and PCP (UNEP, 2004c). DEs greater than 99.999 per cent and DREs

greater than 99.9999 per cent have also been reported for chlordane and HCH (Ministry of the

Environment of Japan, 2004). It has also been reported that reduction of chlorinated organics to less

than 2 mg/kg is achievable (UNEP, 2001).

51 See BiPRO GmbHEuropean Commission, 2005. 52 See European Commission, 2006. 53 See European Commission, 2006. 54 Additional information is available from CMPS&F – Environment Australia, 1997; Costner, Luscombe and Simpson, 1998; Danish Environmental

Protection Agency (EPA), 2004; Rahuman, Pistone, Trifirò and Miertu, 2000; UNEP, 1998; UNEP, 2001; UNEP, 2004a; and Vijgen, 2002.

Commented [CEWEP17]: We would like to suggest to add more relevant and factual information from this study: “The EF of PBDEs in flue gas (84.5 μg/ton-waste)

estimated in this study were 2 to 21 times lower than

that determined from e-waste (e.g., waste TV housing)

incineration processes in Japan (1200 to 1800 μg/ton)

and were rather small when compared to those from

other processes (including manufacturing of PBDEs,

dismantling and crushing, textile processing, and

plastics processing) (Sakai et al., 2006). Furthermore,

PBDEs were identified in the stack flue gases of sinter

plants revealed that PBDEs can form during the

combustion processes through the similar formation

conditions of PCDD/Fs (Wang et al., 2010b). It has

been indicated that the metallurgical facilities are not

only important PCDD/F but also significant PBDD/F

and PBDE emission sources to the environment. Since

the total emission factor of PBB in the whole MSWI

(12.4 μg/ton-waste) was lower than those from the

processes mentioned above, the influence of PBB

emissions form the investigated MSWI to the

environment should be minor.”

Commented [CEWEP18]: We would like to suggest to add more relevant and factual information from this study: “At all the plants, the HBCD DEs exceeded the value of 99.999% recommended by the Basel Convention technical guidelines, and the DEs for five of the nine plants exceeded 99.9999%. The highest DE (99.999998%) was obtained at Plant H, which has a fluidized-bed furnace and the lowest combustion temperature (880 °C) among all the test plants. This series of incineration tests demonstrated that HBCDs could be efficiently decomposed when end-of-life XPS insulation foam was co-incinerated with ordinary industrial wastes at XPS/waste mixing ratios of up to 3 wt %, which is equivalent to HBCDs concentration of 1,100 mg/kg in the source materials. Furthermore, the type of furnace, the

incineration temperature (880–1210 °C), the APC

system, and the mixing ratio had no practical impact on DEs under the test conditions.”

UNEP/CHW.14/INF/9

43

188.199. Waste types: BCD should be applicable to other POPs in addition to the ones listed in the

previous paragraph (i.e., DDT, PCBs, PCDDs and PCDFs) (UNEP, 2004a and Vijgen, 2002). BCD

should be capable of treating wastes with a high POP concentration, with demonstrated applicability to

wastes with a PCB content of above 30 per cent by weight (Vijgen, 2002). Although there have been

reports that the formation of salt within the treated mixture could limit the concentration of halogenated

material that could be treated with BCD, more recent reports suggest that this problem has been

overcome (see paragraph 202201210 below).

189.200. Pre-treatment: Soils may be treated directly. Different types of soil pre-treatment may be

necessary:

(a) Larger particles may need to be removed by sifting and crushed to reduce their size; or

(b) pH and moisture content may need to be adjusted.

190.201. Thermal desorption has also been used in conjunction with BCD to remove POPs from soils

prior to treatment. In these situations, the soil is pre-mixed with sodium bicarbonate prior to being fed

into the thermal desorption unit. Water will need to be evaporated from aqueous media, including wet

sludge, prior to treatment. Capacitors can be treated following size reduction through shredding. If

volatile solvents are present, as is the case with pesticides, they should be removed by distillation prior

to treatment (CMPS&F – Environment Australia, 1997).

191.202. Emissions and residues: Air emissions are expected to be relatively minor. The potential to

form PCDDs and PCDFs during the BCD process is relatively low. However, it has been noted that

PCDDs can be formed from chlorophenols under alkaline conditions at temperatures as low as 150 °C

(Weber, 20042004b). Other residues produced during the BCD reaction include sludge containing

primarily water, salt, unused hydrogen-donor oil and carbon residue. The vendor claims that the carbon

residue is inert and non-toxic. For further details, refer to the literature produced by BCD Group Inc.

According UNEP (2006d) levels of emissions of PCDD/PCDF to air in two different plants were <0.01

ng TEQ/m3N at a small plant treating 10kg/4 hours of high (10%) concentrations of PCB. In another

plant the residual amounts of PCDD/PCDF in the output oil were less than 0.016 ng TEQ/g and

hexachlorobenzene (HCB) <0.2 µg/g. Levels of PCDD/PCDF in the process off-gas (combined off-gas

from soil treatment and BCD reactors) ranged between 0.013 and 0.031 ng TEQ/m3N; for PCBs

between 0.005 and 0.0014 ng TEQ/m3N; for HCB between <6.7 and 187 ng/m3N; and for total∑ of

organochlorine pesticides, between 17 and 235 µg/m3N.

192.203. Release control and post-treatment: Depending on the type of hydrogen-donor oil used, the

slurry residue may be treated in different ways. If No. 6 fuel oil has been used, the sludge may be

disposed of as a fuel in a cement kiln. If more refined oils are used, these may be removed from the

sludge by gravity or centrifuge separation. The oils can then be reused and the remaining sludge can be

further treated for use as a neutralizing agent, or disposed of in a landfill (UNEP, 2004a). In addition,

BCD facilities are equipped with activated carbon traps to minimize releases of volatile organic

compounds in gaseous emissions.

193.204. Energy requirements: Energy requirements are expected to be relatively low owing to the low

operating temperatures associated with the BCD process.

194.205. Material requirements:

(a) Hydrogen-donor oil;

(b) Alkali or alkaline earth metal carbonate, bicarbonate or hydroxide, such as sodium

bicarbonate. The amount of alkali required is dependent on the concentration of the halogenated

contaminant contained in the medium (CMPS&F – Environment Australia, 1997). Amounts range from 1 per cent to

about 20 per cent by weight of the contaminated medium; and

(c) Proprietary catalyst amounting to 1 per cent by volume of the hydrogen donor oil.

195.206. The equipment associated with this process is thought to be readily available (Rahuman et al,

2000).

196.207. Portability: Modular, transportable and fixed facilities have been built.

197.208. Health and safety: In general, the health and safety risks associated with operation of this

technology are thought to be low, although a BCD facility in Melbourne, Australia, was rendered

inoperable following a fire in 1995. The fire is thought to have resulted from the operation of a storage

vessel without a nitrogen blanket. Some associated pre-treatments such as alkaline pre-treatment of

capacitors and solvent extraction present significant risks of fire and explosions, but those risks can be

minimized through the application of appropriate precautions (CMPS&F – Environment Australia, 1997).

UNEP/CHW.14/INF/9

44

198.209. Capacity: BCD can process up to 2,500 gallons of waste per batch and can treat two–four

batches per day (Vijgen, 2002).

199.210. Other practical issues: Since the BCD process involves stripping chlorine from the waste

compound, the treatment process may result in an increased concentration of lower-chlorinated species.

This can be of potential concern in the treatment of PCDDs and PCDFs, where lower-chlorinated

congeners are more toxic than higher-chlorinated congeners. It is therefore important that the process be

appropriately monitored to ensure that the reaction reaches completion. In the past, it was reported that

the BCD process was unable to treat high-concentration wastes because of salt build-up (CMPS&F –

Environment Australia, 1997). More recently, however, it has been reported that this problem has been overcome

(Vijgen, 2002 and UNEP, 2004a).

200.211. State of commercialization: BCD has been used at two commercial operations in Australia, one

of which is still operating. Another commercial system has been operating in Mexico since 1999. In

addition, BCD systems have been used in projects in Australia, Czech Republic, Spain, and the United

States of America.

(d) Catalytic hydrodechlorination (CHD)

201.212. Process description: CHD involves the treatment of wastes with hydrogen gas and a palladium

on carbon (Pd/C) catalyst dispersed in paraffin oil. Hydrogen reacts with chlorine in halogenated waste

to produce hydrogen chloride (HCl) and non-halogenated waste. In the case of PCBs are transformed

into , biphenyls and hydrochloric acid (Murena et al., 2000) is the main product. The process operates at

atmospheric pressure and at temperatures of between 180°C and 260°C (Sakai, Peter and Oono, 2001;

Noma, Sakai and Oono, 2002; and Noma, Sakai and Oono, 2003a and 2003b).

202.213. Efficiency: DEs of 99.98–99.9999 per cent have been reported for PCBs. It has also been

reported that a reduction of the PCB content to less than 0.5 mg/kg is achievable.

203.214. Waste types: CHD has been demonstrated with PCBs removed from used capacitors. PCDDs

and PCDFs contained in PCBs as impurities have also been dechlorinated. A vendor has also claimed

that all chlorinated wastes in liquid state or dissolved in solventscompounds can be treated using CHD

(McNamara, 2016).

204.215. Pre-treatment: PCBs and PCDDs/PCDFs must be extracted using solvents or isolated by

vaporization. Substances with low boiling points such as water or alcohols should be removed by

distillation prior to treatment.

205.216. Emission and residues: No emissions would occur during the dechlorination reaction because

it takes place in the closed hydrogen circulation system. HCl is not discharged from the reaction

because it is collected with water as hydrochloric acid within the circulation system. Biphenyl isolated

after the reaction by distillation does not contain any toxic materials. The emissions of

PCDD/PCDF/dioxin-like PCBs to air are very low (0.0001 ng TEQ/m3) and no discharge to water, as

the main product is biphenyl, which has levels of PCDD/PCDF/dioxin-like PCBs of around 0.00001-

0.0001 ng TEQ/g (UNEP, 2006d).

206.217. Release control and post-treatment: Biphenyl, the main product, is separated out from the

reaction solvent by distillation after the reaction, and the catalyst and reaction solvent are reused in the

next reaction.

207.218. Energy requirements: Energy requirements are expected to be relatively low owing to the low

operating temperatures associated with the CHD process.

208.219. Material requirements: The CHD process requires the same number of atoms of hydrogen as

those of chlorine in the PCBs, and also 0.5 per cent by weight of catalyst.

209.220. Portability: CHD is available in fixed and transportable configurations depending on the

volume of PCBs to be treated.

210.221. Health and safety: The use of hydrogen gas requires adequate controls and safeguards to

ensure that explosive air-hydrogen mixtures are not formed.

211.222. Capacity: In Japan, a facility capable of treating 2 Mg tonnes PCB per day using the CHD

process was constructed and is in operation. Facilities are also operated in Canton, United States of

America, and Young, Australia. There is no information on the treatment capacities of those

facilities.Bomen, Australia. Reportedly the 2016 capacity of the US plant in Canton iswas 45 million

litres per year and that of the Bowen Australia plant 6.5 million litres per year (Hydrotec, 2018).

UNEP/CHW.14/INF/9

45

212.223. Other practical issues: There are many reports about PCB dechlorination using CHD.

Generally, Pd/C catalysts show the largest degradation rates compared to the other supported metal

catalysts. Reaction temperatures can be increased to 260°C when paraffin oil is used as a reaction

solvent.

213.224. State of commercialization: In Japan, a commercial-scale facility was constructed at the Japan

Environmental Storage & Safety Corporation (JESCO) Osaka facility in 2006 and PCB extracted from

transformers and capacitors are treated using the CHD process (JESCO, 2009c).

(e) Cement kiln co-incineration55

214.225. Process description: Cement kilns typically consist of a long cylinder of 50–150 metres in

length, inclined slightly from the horizontal (3 per cent to 4 per cent gradient), which is rotated at about

1-4 revolutions per minute. Raw materials such as limestone, silica, alumina and iron oxides are fed into

the upper or “cold” end of the rotary kiln. The slope and rotation cause the materials to move toward the

lower or “hot” end of the kiln. The kiln is fired at the lower end of the kiln, where material temperatures

reach 1,400°C–1,500°C. As the materials move through the kiln, they undergo drying and

pyroprocessing reactions to form clinker. The length of the kiln ensures a sufficient residence time of

the incineration gases at high temperatures: about 8 s at temperatures above 1200 ◦C (Vermeulen et al.,

2011).

215.226. Cement kilns treating wastes may require kiln modifications.56 Adequate feed points should

be selected according to the characteristics of the waste, including its physical, chemical and

toxicological properties. For example, combustible toxic compounds found in some hazardous waste,

such as halogenated organic substances, need to be completely destroyed through proper temperature

and residence time. In preheater/precalciner kilns, hazardous waste should generally be fed through

either the main or the secondary burners. Halides (e.g. chlorides, bromides and fluorides) have an

impact on the quality of the cement so their presence must be limited. Chlorine can be found in all raw

materials used in cement manufacture, so total halogen (e.g. chlorine, bromine and fluorine) levels in

the hazardous waste can be critical (European Commission, 2013). However, if they are blended down

sufficiently, cement kilns can treat highly chlorinated hazardous waste.

216.227. The potential feed pointpoints for supplying waste would be:

(a) The main burner at the rotary kiln outlet end;

(b) A feed chute at the transition chamber at the rotary kiln inlet end (for lump fuel);

(c) Secondary burners to the riser duct;

(d) Precalciner burners to the precalciner;

(e) A feed chute to the precalciner/preheater (for lump fuel);

(f) A mid-kiln valve in the case of long wet and dry kilns (for lump fuel) (UNEP, 2004b).

217.228. The guidance on BAT/BEP developed by the Stockholm Convention relevant to Article 5 and

Annex C on cement kiln firing hazardous waste should be used and applied to this technology (UNEP,

2007).

218.229. Efficiency: DREs greater than 99.99998 per cent have been reported for PCBs in several

countries. A facility should demonstrate its capability to destroy (through combustion) or remove

(through settling in ductwork or air pollution control devices) at least 99.9999 per cent of targeted

POPs.57 Reported DE and DRE values for DDT are in the range of 99.9335-99.9998 per cent and

99.9984-99.9999 per cent, respectively (Yan et al, 2014) and DRE greater than 99.9999% per cent (Li et

al., 2012). Considering very high temperaturesA study reported DREs of 99.9997% and long residency

time found99.9998% for deca-BDE in state of the artcontaminated soil treated in a cement kiln co-

incineration facilities, it is expected that PCN, PCP and HCBD would also be destroyed (German

Federal Environment Agency, 2015(Yang et al. 2012). Process operating constraints may become

significant when certain compounds, for example circulating volatile elements such as chlorine, sulphur

or alkalis, are present in excessive quantities (Karstensen, 2008). The destruction efficiency of POP-

PBDEs in the waste depends to a significant extent on the feeding point in the kiln. Stable molecules

55 Additional information is available from CMPS&F – Environment Australia, 1997; Costner et al., 1998; Danish Environmental Protection Agency,

2004; Karstensen, 2001; Rahuman et al., 2000; Stobiecki et al., 2001 and UNEP, 1998. In addition, information on BAT and BEP with respect to cement kilns

firing hazardous waste is available from the European Commission. 56 See CMPS&F – Environment Australia, 1997 and UNEP, 2004b. 57 Karstensen et al, 2009.

UNEP/CHW.14/INF/9

46

need to be fed at the “hot end” of the kiln into the burner flame with temperature up to 2000°C and

residence time of more than 2 seconds which can guarantee a high destruction efficiency. This also

assures the destruction of POP-PBDEs in secondary fuels (UNEP, 2017g).

219.230. Waste types: Virtually any organic compound can be destroyed at the minimum temperature

of 1,400°C of a properly operating cement kiln (UNEP, 2002a). Cement kilns are capable of treating

both liquid and solid wastes.58 In addition upgrading and purification of automotive shredder residue

ASR is required before it is usedits use as fuel substitute in high percentages in a cement kiln

(Vermeulen et al., 2011)

220.231. Pre-treatment: Pre-treatment can involve:

(a) Thermal desorption of solid wastes;

(b) Homogenization of solid and liquid wastes through drying, shredding, blending, mixing

and grinding;

(c) Volume reduction; and

(d) Blending.

221.232. Emissions and residues: Cement kiln co-incineration of hazardous wastes is listed as an

industrial source category that has the potential for comparatively high formation and release of the

unintentionally formed POPs listed in Annex C to the Stockholm Convention. Emissions may include,

inter alia, nitrogen oxides, carbon monoxide, sulphur dioxide and other oxides of sulphur, metals and

their compounds, hydrogen chloride, hydrogen fluoride, ammonia, PCDDs, PCDFs, benzene, toluene,

xylene, polycyclic aromatic hydrocarbons, chlorobenzenes and PCBs (UNEP, 2004b) and PCN (Liu et

al, 2016)., German Federal Environment Agency, 2015) and PBDD/Fs (Du Bing et al. 2011). It should

be noted that cement kilns can comply with PCDD and PCDF air emission levels below 0.1 ng

TEQ/Nm3 although waste with high chlorine levels should be fed together with other wastes to avoid

adversely affecting emission levels, particularly in wet and (long) dry kilns59. Residues include cement

kiln dust captured by the air pollution control systems.

222.233. Release control and post-treatment: Process gases must be treated to remove cement kiln dust

and organic compounds, sulphur dioxide and nitrogen oxide; they must also be heated so that the

formation of PCDDs and PCDFs is minimized. Treatments include the use of preheaters, electrostatic

precipitators, fabric filters and activated carbon filters.60 Recovered cement kiln dusts should be put

back into kilns to the maximum extent practicable, while the remainder may require disposal in a

specially engineered landfill or permanent storage in an underground mine or formation.

223.234. Energy requirements: For new facilities and major upgrades using dry process kiln with

multistage preheating and precalcination, the BAT-associated energy consumption is 2,900-3,200

MJ/tonne clinker under normal (excluding, e.g. start-ups and shutdowns) and optimised operational

conditions (not applying to facilities producing special cement or white cement clinker that require

significantly higher process temperatures due to product specifications). The production capacity has an

influence on the energy demand, with higher capacities providing energy savings and smaller capacities

requiring more energy. Energy consumption also depends on the number of cyclone preheater stages,

with more cyclone preheater stages leading to lower energy consumption of the kiln process. The

appropriate number of cyclone preheater stages is mainly determined by the moisture content of raw

materials (European Commission, 2013).

224.235. Material requirements: Cement manufacturing requires large amounts of materials, including

limestone, silica, alumina, iron oxides and gypsum.

225.236. Portability: Cement kilns are available only in fixed configurations.

226.237. Health and safety: Treatment of wastes in cement kilns can be regarded as relatively safe

provided that kilns are properly designed and operated.

227.238. Capacity: Cement kilns that co-incinerate waste as fuel must normally not meet more than

40 per cent of their heat requirements with hazardous waste. It has been noted, however, that cement

kilns with high throughput can potentially treat significant quantities of waste (CMPS&F – Environment Australia,

1997).

58 See CMPS&F – Environment Australia, 1997; Rahuman et al., 2000 and Karstensen et al, 2006. 59 In exceptional cases, emission levels from cement kilns co-incinerating wastes has been reported at 136 ng

TEQ/m3 (UNEP 2007). 60 See CMPS&F – Environment Australia, 1997; Karstensen et al., 2006 and UNEP, 2004b.

Commented [HWE19]: Indeed all feed points are not

equivalent from the point of view of temperature and

destruction efficiency of POPs. The guidance should at

least mention that the raw mix feed point is not

appropriatete for introducing soils contaminated with

POPs or other POP containing waste. If introduced at

this feed point, POPs (as well as other organic

pollutants) are likely to distillate before reaching the

high temperature section. As the gas flow and the

material flow are counter-current, these POPs and other

organic distillates would be emitted to the atmosphere

through the stack.

UNEP/CHW.14/INF/9

47

228.239. State of commercialization: Cement kilns in the United States, some European countries and a

number of developing countries have been and are used to treat wastes contaminated with POPs

(World Business Council, 2004: Formation and Release of POPs in the Cement Industry and

Karstensen, 2006).

229.240. Additional information: See the UNEP Technical guidelines on the environmentally sound co-

processing of hazardous wastes in cement kilns (UNEP, 2011) and the Commission implementing

decision 2013/163/EU establishing the best available techniques (BAT) conclusions under Directive

2010/75/EU on industrial emissions for the production of cement, lime and magnesium oxide,

(European Commission, 2013b). High levels of HCB was released from a cement kiln incinerating

HCB contaminated waste when the operators failed to follow technology requirements in order to

destroy the POP content (Kundi, 2015).

(f) Gas-phase chemical reduction (GPCR)61

230.241. Process description: The GPCR process62 involves the thermochemical reduction of organic

compounds. At temperatures greater than 850 °C and at low pressures, hydrogen reacts with chlorinated

organic compounds to yield primarily methane, hydrogen chloride (if the waste is chlorinated), and

minor amounts of low molecular weight hydrocarbons (benzene and ethylene). The hydrochloric acid is

neutralized through the addition of caustic soda during the initial cooling of the process gas, or can be

taken off in acid form for reuse. The GPCR technology can be broken down into three basic unit

operations: a front-end system (where the contaminants are transformed into a suitable form for

destruction in the reactor), a reactor (which reduces the contaminants, at this stage in gas phase, using

hydrogen and steam), and a gas scrubbing and compression system.

231.242. Efficiency: DEs of 99.9999 per cent have been reported for DDT, HCB, PCBs, PCDDs and

PCDFs.63 DEs of more than 99.999999 per cent have been reported for PCBs, 99.999% for PCDD

contained in waste oils containing PCBs (UNEP, 2000), as well as DE ofabove 99.9999938 % for HCB

and chlorobenzenes (Kümmling et al., 2002, Arnold, 2003)in mixed waste together with HCBD and

hexachloroethylene (Arnold 2003, European Commission, 2017).

232.243. Waste types: GPCR is expected to be able to treat all POP wastes,64 including aqueous and oily

liquids, soils (USEPA, 2010), sediments, sludges, transformers and capacitors.65

233.244. Pre-treatment: Contaminants must be in gaseous form for a GPCR reactor to reduce them.

While liquid wastes can be preheated and injected directly into the reactor on a continuous basis,

contaminants on solids must first be volatilized from the solids. Depending on the waste type, one of the

following three pre-treatment units is currently used to volatilize wastes prior to treatment in a GPCR

reactor:

(a) Thermal reduction batch processors (TRBPs) for bulk solids, including those in drums;

(b) Toroidal bed reactors for contaminated soils and sediments, but also adapted for liquids;

(c) Liquid waste pre-heater systems (LWPSs) for liquids.66

234.245. In addition, other pre-processing is required for large capacitors and building rubble. Large

capacitors are punctured and drained, while rubble and concrete must be reduced in size to less than one

square metre.67

235.246. Emissions and residues: In addition to hydrogen chloride and methane, low molecular weight

hydrocarbons may be emitted. Residues from the GPCR process include used liquor and water. Solid

residues will also be generated from solid waste inputs.68 Since the GPCR process takes place in a

reducing atmosphere, the possibility of PCDD and PCDF formation is considered limited.69 No ash is

produced. According to UNEP (2006d), a Danish Environmental Protection Agency (2004) review from

61 Additional information is available from CMPS&F – Environment Australia, 1997; Costner et al., 1998; Danish Environmental Protection Agency,

2004; Kümmling et al, 2001; Rahuman et al., 2000; Ray, 2001; UNEP, 2001; UNEP, 2004a; and Vijgen, 2002. 62 The process can also be called hydrogenation (European Commission, 2017).

63 See CMPS&F – Environment Australia, 1997; Kümmling et al., 2001; Rahuman et al., 2000; UNEP, 2004a and Vijgen, 2002. 64 See CMPS&F – Environment Australia, 1997; UNEP, 2004a and Vijgen, 2002. 65 Ibid. 66 See CMPS&F – Environment Australia, 1997; Kümmling et al., 2001; UNEP, 2001; UNEP, 2004a. 67 See CMPS&F – Environment Australia, 1997. 68 See UNEP, 2004a and Vijgen, 2002. 69 See CMPS&F – Environment Australia, 1997; and Rahuman et al., 2000.

Formatted: Strikethrough, Highlight

UNEP/CHW.14/INF/9

48

2004 noted that eEmissionsemissions of PCDD/PCDF from the gas phase chemical reduction process to

all media were lower than those from the base catalysed decomposition (Danish Environmental

Protection Agency (2004)) process.

236.247. Release control and post-treatment: Gases leaving the reactor are scrubbed to remove water,

heat, acid and carbon dioxide.70 Scrubber residue and particulate will require disposal off site.71 Solid

residues generated from solid waste inputs should be suitable for disposal in a landfill.72

237.248. Energy requirements: Methane produced during the GPCR process can provide much of the

fuel needed in the process.73 It has been reported that electricity requirements range from 96 kWh per

ton of soil treated to around 900 kWh per ton of pure organic contaminants treated.74

238.249. Material requirements: There is a need for hydrogen supplies, at least during start-up. It has

been reported that methane produced during the GPCR process can be used to form enough hydrogen to

operate the process thereafter.75 The hydrogen production unit was plagued, however, by reliability

problems in the past.76 Other material requirements include caustic for the acid scrubber.77

239.250. Portability: GPCR is available in fixed and transportable configurations.78

240.251. Health and safety: Use of hydrogen gas under pressure requires suitable controls and

safeguards to ensure that explosive air-hydrogen mixtures are not formed.79 Operating experience

gained to date has indicated that the GPCR process can be undertaken safely.80 GPCR is used to treat

sewage sludge by converting the waste into clean water and a clean hydrogen enriched methane gas

while chemically destroying all pathogens and pharmaceuticals and recovering phosphorous. There are

no fugitive methane emissions in the process.

241.252. Capacity: GPCR process capacity is dependent on the capacities of the following three

pre-treatment units, as specified below:

(a) TRBPs have a capacity of up to 100 tonnes of solids per month or up to four litres per

minute of liquids. Two TRBPs can be used in parallel to double capacity;

(b) Toroidal bed reactors have a capacity of up to 5,000 tonnes of soils and sediments per

month, although these pre-treatment units are still in the development stage; and

(c) LWPSs have a capacity of three litres per minute (UNEP, 2004a and Vijgen, 2002).

242.253. Other practical issues: Contaminants such as sulphur and arsenic were found to inhibit

treatment in earlier development stages, although it is unclear whether this problem persists.81

243.254. State of commercialization: Commercial-scale GPCR facilities have operated in Canada and

Australia. The GPCR facility in Kwinana, Western Australia operated for more than five years until

2000 by which time it has treated most of the PCB stockpiles for that state and a significant quantity of

POPs wastes from other Australian states.82 In the United States, there is a plan to build a GPCR

synthetic diesel facility in Fauquier County, Virginia, with a daily processing capacity of 200 Mg.

70 See Kümmling et al., 2001; CMPS&F – Environment Australia, 1997; and Rahuman et al., 2000. 71 See Rahuman et.al, 2000 and Vijgen, 2002. 72 See UNEP, 2004a. 73 See CMPS&F – Environment Australia, 1997; Rahuman et al., 2000; UNEP, 2001; UNEP, 2004a; and Vijgen, 2002. 74 CMPS&F – Environment Australia, 1997. 75 See CMPS&F – Environment Australia, 1997; Rahuman et al., 2000; UNEP, 2004a; and Vijgen, 2002. 76 See CMPS&F – Environment Australia, 1997. 77 See UNEP, 2004a. 78 See UNEP, 2001; UNEP, 2004a; and Vijgen, 2002. 79 See CMPS&F – Environment Australia, 1997. 80 See CMPS&F – Environment Australia, 1997 and UNEP, 2004a. 81 See CMPS&F – Environment Australia, 1997. 82 See CMPS&F – Environment Australia, 1997; Kümmling et al., 2001; Ray, 2001; UNEP, 2004a and Vijgen, 2002.

UNEP/CHW.14/INF/9

49

(g) Hazardous waste incineration83

244.255. Process description: Hazardous waste incineration uses controlled flame combustion to treat

organic contaminants, mainly in rotary kilns. Typically, a process for treatment involves heating to a

temperature greater than 850°C or, if the waste contains more than 1 per cent of halogenated organic

substances expressed as chlorine, to a temperature greater than 1,100°C, with a residence time greater

than two seconds under conditions that ensure appropriate mixing. Dedicated hazardous waste

incinerators are available in a number of configurations, including rotary kiln incinerators and static

ovens (for liquids with low contamination). High-efficiency boilers and lightweight aggregate kilns are

also used for the co-incineration of hazardous wastes.

245.256. The guidance on BAT/BEP developed by the Stockholm Convention relevant to Article 5 and

Annex C for waste incinerator should be used and applied to this technology (UNEP, 2007).

246.257. Efficiency: DREs greater than 99.9999 per cent have been reported for treatment of PCBs,

PCDDs and PCDFs, chlordane and HCB. 84DEs greater than 99.999 and DREs greater than 99.9999 per

cent have been reported for aldrin, endrin, HCH, DDT and PFOS (Ministry of the Environment of

Japan, 2004 and, 2013b). DE and DRE were reported for PCN at 99.9974 and 99.9995 per cent,

respectively (Yamamoto et al., 2016). State-of-the-art incineration reaches destruction rates of more

than 99.9 per cent for HCBD and PCP and between 99.32 and 99.96 for PCNs. (Germany Federal

Environment Agency, 2015). DE greater than 99.999% is reported (Kajiwara et al., 2017).

247.258. Waste types: Hazardous waste incinerators are capable of treating wastes consisting of,

containing or contaminated with POPs (UNEP, 2002a); Incinerators can be designed to accept wastes in

any concentration or physical form, i.e., as gases, liquids, solids, sludges or slurries.85

248.259. Pre-treatment: Depending upon the configuration, pre-treatment requirements may include

blending and size reduction of wastes.86

249.260. For polystyrene foam (EPS and XPS) wastes containing HBCD, a series of steps can be

applied to separate HBCD from polystyrene and subsequently destroy HBCD in hazardous waste

incinerators. The relevant pre-treatments operations include volume reduction, size reduction,

dissolution, sedimentation, and distillation87. In the case of XPS waste containing HBCD and which

may also contain ozone depleting substances controlled by the Montreal Protocol on Substances That

Deplete the Ozone Layer88, measures should be taken to prevent the release of ODS to the environment

during these pre-treatment operations.

250.261. Emissions and residues: Emissions include carbon monoxide, carbon dioxide, HCB, hydrogen

chloride, particulates, PCDDs, PCDFs and PCBs, heavy metals and water vapour.89 Incinerators

applying BAT that, inter alia, are designed to operate at high temperatures, to prevent the re-formation

of PCDDs and PCDFs and to remove PCDD and PCDF (e.g., with the use of activated carbon filters),

have led to very low PCDD and PCDF emissions to air and discharges to water.90 In residues, PCDDs

and PCDFs are mainly found in fly ash and salt, and to some extent in bottom ash and scrubber water

sludge. Levels of PCDD/Fs in fly ash from hazardous waste incinerators can be in the range from

0.0002 to 124.5 ng TEQ/g 91.

251.262. Release control and post-treatment: Process gases may require treatment to remove hydrogen

chloride and particulate matter and to prevent the formation of, and remove unintentionally produced,

POPs (sulphur and nitrogen oxides, heavy metals and organic micro pollutants such as PAHs, like

83 Additional information is available from Danish Environmental Protection Agency, 2004; Federal Remediation

Technology Roundtable (FRTR), 2002; Rahuman et al., 2000; UNEP, 1995b; UNEP, 1998; UNEP, 2001; and

United States Army Corps of Engineers, 2003. In addition, information on BAT and BEP with respect to hazardous

waste incinerators is available from UNEP, 2015.

84 See FRTR, 2002; Rahuman et al., 2000; UNEP, 1998 and UNEP, 2001. 85 See UNEP, 1995b. 86 See UNEP, 1995b; UNEP, 1998 and UNEP, 2004b. 87 http://polystyreneloop.org/ 88 http://ozone.unep.org/en/treaties-and-decisions/montreal-protocol-substances-deplete-ozone-layer 89 See UNEP, 1995b; UNEP, 1998 and UNEP, 2004b. 90 UNEP, 2001. 91 BiPRO GmbHEuropean Commission, 2005; Petrlik, J. and R. Ryder (2005). After Incineration: The Toxic Ash

Problem. Available at: http://ipen.org/sites/default/files/documents/ipen_incineration_ash-en.pdf. Prague,

Manchaster, IPEN Dioxin, PCBs and Waste Working Group, Arnika Association: 59.; Cobo, M., A. Gálvez, J.

Conesa and C. Montes de Correa (2009). "Characterization of fly ash from a hazardous waste incinerator in

Medellin, Colombia." Journal of Hazardous Materials 168: 1223-1232. Noma et al., 2006.

UNEP/CHW.14/INF/9

50

carbon monoxide, are being used as an indicator of combustion efficiency). This can be achieved

through a combination of types of post-treatments, including the use of cyclones and multi-cyclones,

electrostatic filters, static bed filters, scrubbers, selective catalytic reduction, rapid quenching systems

and carbon adsorption.92 Depending upon their characteristics, bottom and fly ashes may require

disposal within a specially engineered landfill or permanent storage in underground mines and

formations.93

252.263. Energy requirements: The amount of combustion fuel required will depend upon the

composition and calorific value of the waste and also upon the flue gas treatment technologies applied.

253.264. Material requirements: Material requirements include cooling water and lime or another

suitable material for removal of acid gases and other pollutants like active carbon.

254.265. Portability: Hazardous waste incinerators are available in both portable and fixed units.mobile

and fixed units. However, mobile units without air pollution control cannot be used for

environmentally-sound destruction of POPs waste.

255.266. Health and safety: Health and safety hazards include those associated with operations

involving high temperatures.94

256.267. Capacity: Hazardous waste incinerators can treat between 30,000 and 100,000 tonnes of waste

per year.95

257.268. Other practical issues: None to report at this time.

258.269. State of commercialization: There is a long history of experience with hazardous waste

incineration.96

(h) Plasma Arc97

259.270. Process description: The waste, as a liquid or gas, is injected directly into the plasma and is

rapidly (<1 ms) heat up to about 3,100°C and pyrolysed for about 20 ms in the water-cooled reaction

chamber (flight tube). The high temperature causes compounds to dissociate into their elemental ions

and atoms. Recombination occurs in a cooler area of the reaction chamber, followed by a quench,

resulting in the formation of simple molecules.98 The plasma arc system requires a mono-nitrogen

oxides (NOx) abatement device, as important amounts of NOx are produced by the high temperature

flame.

260.271. The guidance on BAT/BEP developed by the Stockholm Convention relevant to Article 5 and

Annex C should be used and applied to this technology (UNEP, 2007).

261.272. Efficiency: Bench-scale tests with oils containing 60 per cent PCBs have achieved DREs

ranging from 99.9999-99.999999 per cent.99 A DE of 99.9999 per cent is achievable for most pesticide

POPs, including chlordane, chlordecone, DDT, endosulfan and heptachlor.

262.273. Waste types: Plasma arc system facilities have been used to treat a wide range of PCBs,

pesticide POPs, halons and chlorofluorohydrocarbons. Waste types to be treated must be liquid or gas,

or solid if the waste is contained in a fine slurry that can be pumped. Very viscous liquids or sludges

thicker than 30–40 weight motor oil cannot be processed without pre-treatment. Other solid wastes

cannot be treated unless some form of pre-treatment is undertaken.100

263.274. Pre-treatment: Pre-treatment is not required for most liquids. Solids such as contaminated

soils, capacitors and transformers can be pre-treated using thermal desorption or solvent extraction.101

92 UNEP, 2004b. 93 See United States Army Corps of Engineers, 2003. 94 Ibid. 95 See UNEP, 2004b. 96 See UNEP, 2001. 97 Additional information is available from CMPS&F – Environment Australia, 1997; Costner et al., 1998;

Rahuman et al., 2000; Ray, 2001; UNEP, 1998; UNEP, 2000; UNEP, 2001 and UNEP, 2004a. 98 See CMPS&F – Environment Australia, 1997.

99 See Rahuman et al., 2000 and UNEP, 2004a. 100 See CMPS&F – Environment Australia, 1997 and UNEP, 2004a.

101 Ibid.

UNEP/CHW.14/INF/9

51

264.275. Emissions and residues: Emissions include gases consisting of argon, carbon dioxide and

water vapour. Residues include an aqueous solution of inorganic sodium salts, such as sodium chloride,

sodium bicarbonate and sodium fluoride. Traces of PCDD and PCDF have been detected in effluent gas

from plasma arc systems. These traces are at a concentration of less than 0.01 ng TEQ/Nm3. POP

concentrations in solid residues are unknown.102 In the Plascon™ process that was operating in

Australia the levels of PCB in effluent discharge to waste water were less than 2 ppb (UNEP, 2006d).

265.276. Release control and post-treatment: Currently, there is little information available regarding

post-treatment requirements.

266.277. Energy requirements: A 150 kW plasma arc system unit requires 1,000–3,000 kWh of

electricity per tonne of waste treated.103

267.278. Material requirements: Currently, there is little information available regarding material

requirements. It has been noted, however, that this process requires argon gas, oxygen gas, caustic and

cooling water.104

268.279. Portability: Plasma arc systems are available in both portable and fixed units.105

269.280. Health and safety: Since the plasma arc system process has a low throughput, there is a low

risk associated with the release of partially treated wastes following process failures.106 Currently, there

is little additional information available regarding health and safety.

270.281. Capacity: A 150 kW plasma arc system unit can process 1–3 Mg of waste per day.107

271.282. Other practical issues: It should be noted that metals or metal-like compounds (e.g., arsenic)

may interfere with catalysts or cause problems in disposing of residues. For example, arsenicals in

pesticide waste exported from Pacific islands for disposal in Australia using the plasma arc system

process have presented problems.

272.283. State of commercialization: BCD Technologies Pty Ltd. operatesThere are two plasma facilities

operating in Australia: one in Brisbane Laverton, Victoria as part of an agricultural chemical plant and

one in Narangba, Queensland. for PCBs and other POPs and another one in Melbourne for treating

CFCs and halons. BCD Technologies Pty Ltd. also operates a BCD facility for low-level PCBs and

POPs and has two thermal desorbers for treating contaminated solids.

(i) Plasma Melting Decomposition Method

273.284. Process description: The plasma melting decomposition method (PMD) is a thermal

destruction method for solid waste containing or contaminated with PCBs. Solid waste containing or

contaminated with PCBs is canned directly into containers, such as drums or pails, without shredding or

disassembling. In a plasma furnace, a plasma torch generates high temperature plasma gas (air) so that

the furnace temperature is maintained to melt the waste together with the container itself. All the

organic substances, including PCBs, are decomposed into CO2, H2O and HCl under the high

temperature conditions of the plasma furnace, and inorganic materials, including metals, are oxidized to

become molten slag. The plasma furnace temperatures exceed 1,400˚C (Tagashira et al., 2006).

274.285. Efficiency: In Japan, a pilot PMD facility was tested for PCB treatment in 2006. The result

showed DEs ranging from 99.9999454-99.9999997 per cent and DREs ranging from 99.9999763-

99.9999998 per cent (Tagashira et al., 2006).

275.286. Waste types: In commercial scale facilities in Japan, solid waste containing or contaminated

with PCBs, such as fluorescent light ballasts, sludge, carbonless paper and secondary contaminants, can

be treated using PMD (JESCO, 2009a2013).

276.287. Pre-treatment: Japan’s commercial-scale facilities uses containers such as drums and pails in

which PCB-contaminated waste is mixed with basicity-controlling agents like limestone or silica sand,

as needed, and pushed into the plasma furnace (JESCO, 2009a, JESCO, 2013).

277.288. Emissions and residues: The JESCO plasma melting treatment facility can comply with

dioxins air emission levels below 0.1 ng TEQ/Nm3 (JESCO, 2009). Air emission levels of dioxins were

102 Ibid 91. 103 See CMPS&F – Environment Australia, 1997. 104 See CMPS&F – Environment Australia, 1997 and UNEP, 2004a. 105 See UNEP, 2004a. 106 See CMPS&F – Environment Australia, 1997 and UNEP, 2004a.

107 Ibid.

UNEP/CHW.14/INF/9

52

0.0000043-0.068 ng TEQ/Nm3 in a pilot scale facility (Tagashira et al., 2006). Together with an

enhanced gas treatment system, dioxin emission levels can be controlled within a range of 0.00001-

0.001 ng TEQ/Nm3 (Tagashira et al., 2007).

278.289. Release and control and post-treatment: In Japan, as exhaust gas pollution control, two-stage

bag filters with lime and pulverized activated carbon injection remove dust, acid gas such as HCl and

SOx and dioxins, while catalyst towers with NH3 gas injection remove NOx. Activated carbon is

installed at the last stage (Tagashira et al., 2006).

279.290. Material requirements: PMD is reported to require lime and pulverized activated carbon

supply (Tagashira et al., 2006). To improve molten slag fluidity, basicity-controlling agents such as

silica sand or limestone may also be required.

280.291. Portability: PMD is available only in fixed units (JESCO, 2009a).

281.292. Capacity: In Japan, it has been demonstrated that the two JESCO plasma melting treatment

facilities operating there are capable of treating 10.4 tonnes and 12.2 tonnes of PCB-containing waste

per day, respectively (JESCO, 2009a; JESCO, 2013).

282.293. State of commercialization: In Japan, the JESCO plasma melting treatment facility in

Kitakyushu has used PMD technology treatment of 10.4 tonnes of PCB waste per day on a commercial

scale since July 2009 (JESCO, 2009a) and ; the same type of facility in Hokkaido has having the

capacity to treat 12.2 tonnes of PCB waste per day and was expected to commencehas also been in

commercial operations in the Autumn ofsince 2013 (JESCO, 2013).

283.294. Additional information: See the following website for further information:

http://www.jesconet.co.jp/eg/pdf/plasma.pdf.

(j) Supercritical water oxidation (SCWO) and subcritical water oxidation108

284.295. Process description: SCWO and subcritical water oxidation treat wastes in an enclosed system

using an oxidant (such as oxygen, hydrogen peroxide, nitrite, nitrate, etc.) in water at temperatures and

pressures above the critical point of water (374°C and 218 atmospheres) and below subcritical

conditions (370°C and 262 atmospheres). Under these conditions, organic materials become highly

soluble in water and are oxidized to produce carbon dioxide, water and inorganic acids or salts.

285.296. Efficiency: DEs greater than 99.999 per cent and DREs greater than 99.9999 per cent have

been reported for chlordane, DDT and PCBs for SCWO (Ministry of the Environment of Japan, 2004).

DEs greater than 99.999999 per cent and DREs of greater than 99.9999999 per cent have been reported

for subcritical water oxidation (Ministry of the Environment of Japan, 2004). DREs as high as

99.9999 per cent have also been demonstrated for PCDDs in bench-scale tests.109 SCWO has been

shown to be effective in the treatment of toxic chlorinated chemicals such as PCBs, pesticides and flame

retardants (Marrone and Hong, 2007). Overall, SCWO usually has a DE greater than 99.99 per cent for

a wide range of organic compounds (Marrone and Hong, 2007).

286.297. Waste types: SCWO and subcritical water oxidation are thought to be applicable to all POPs. 110Applicable waste types include aqueous wastes, oils, solvents and solids with a diameter of under

200 µm. The organic content of the waste is limited to below 20 per cent by weight.111 Supercritical and

subcritical fluids have been showed to decompose ABS and HIPS plastics containing

decabromodiphenylether decaBDE decabromodiphenyletherbrominated flame retardants. The main

reaction products were oils containing ethylbenzene. The bromine from the flame retardant was

removed into the aqueous phase (Onwudili & Williams, 2009, Goto, 2016).

287.298. Pre-treatment: Concentrated wastes may have to be diluted prior to SCWO treatment in order

to reduce their organic content to below 20 per cent by weight. If solids are present, they must be

reduced to less than 200 µm in diameter. Other processing options include addition of fuel to low

concentration wastes, co-processing of dilute and concentrated wastes and partial sludge dewatering,

among others. In the case of subcritical water oxidation, the dilution of wastes is not necessary.

288.299. Emissions and residues: Under operating conditions above the critical range of 500°C–650°C

and 25 MPa with reactor residence times of under one minute for complete destruction PCDD/PCDF,

108 Additional information is available from CMPS&F – Environment Australia, 1997; Costner et al., 1998;

Rahuman et al., 2000; UNEP, 2001; and UNEP, 2004a. 109 See CMPS&F – Environment Australia, 1997; Rahuman et al., 2000; and Vijgen, 2002. 110 See UNEP, 2004a.

111 See CMPS&F – Environment Australia, 1997; Rahuman et al., 2000; and Vijgen, 2002.

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NOx and other toxic by-products are not formed in SCWO (Marrone, 2013). However, during

laboratory-scale PCB destruction, it was has been shown that the SCWO technology has the potential to

form high concentrations of PCDFs during PCB degradation in experiments below 450°C (Weber,

20042004a). It has been reported that emissions contain no oxides of nitrogen or acid gases such as

hydrogen chloride or oxides of sulphur and that process residues consist of water and solids if the waste

contains inorganic salts or organic compounds with halogens, sulphur or phosphorus.112 Limited

information has been reported regarding potential concentrations of undestroyed chemicals.113 The

process is designed so that emissions and residues can be captured for reprocessing if needed.114

Commercial use of SCWO demonstrated emissions of PCDD/PCDF/dioxin-like PCBs to air of 0.00009

ng TEQ/m3 and to water of 0.0006–0.004 ng TEQ/L.(UNEP, 2006d), well below emission standards

usually used for waste incineration.

289.300. Release control and post-treatment: Currently, there is no specific information available

regarding post-treatment requirements.

290.301. Energy requirements: Energy requirements are expected to be relatively high because of the

combinations of high temperatures and pressures. It has been claimed, however, that as long as

relatively high hydrocarbon content is present in the feed, no energy input is required to heat the feed to

supercritical temperatures.115

291.302. Material requirements: SCWO and subcritical water oxidation reaction vessels must be

constructed of materials capable of resisting corrosion caused by halogen ions.116 Material corrosion can

be severe at the temperatures and pressures used in the SCWO and subcritical water oxidation

processes. In the past, the use of titanium alloys has been proposed to tackle this problem. Current

vendors claim to have overcome this problem through the use of advanced materials and engineering

designs.117

292.303. Portability: The SCWO and subcritical water oxidation units are currently used in fixed

configurations, but are thought to be portable.118

293.304. Health and safety: The high temperatures and pressures used in SCWO and subcritical water

oxidation processes require special safety precautions.119

294.305. Capacity: Current SCWO demonstration units are capable of treating 500 kg0.5 t/h, while full-

scale units can be designed to treat up to 10,000 kg t/h (Marrone 2013).

295.306. Other practical issues: Earlier designs were plagued by reliability, corrosion and plugging

problems. Current vendors claim to have addressed these problems through the use of special reactor

designs and corrosion-resistant materials.120

296.307. State of commercialization: A full-scale SWCO commercial facility with the capacity to treat 2

tonnes of waste per day was installed in 2005 and is in operation in Japan (JESCO, 2009d). In addition,

the SCWO process has been approved for full-scale development and use in the chemical-weapon

destruction programme of the United States There are plants in commercial operation also in France and

Korea (Marrone et al, 2013).

(k) Thermal and metallurgical production of metals

297.308. Process description: The processes described below are primarily designed for the recovery of

iron and non-ferrous metals (NFM), e.g., aluminium, zinc, lead, and nickel from ore concentrates as

well as from secondary raw materials (intermediates, wastes, scrap). However, due to their nature, the

processes are in some cases also used on a commercial basis for the destruction of the POP content of

appropriate wastes (see paragraph 303311). A general description of some of the following processes

may also be found in the European BAT reference documents for NFM industries (European

Commission, 2001a and 2001b):

112 See CMPS&F – Environment Australia, 1997. 113 See CMPS&F – Environment Australia, 1997 and UNEP, 2004a. 114 See UNEP, 2004a. 115 See Rahuman et al., 2000. 116 See Vijgen, 2002. 117 Ibid. 118 See UNEP, 2004a and Vijgen, 2004. 119 See CMPS&F – Environment Australia, 1997. 120 Ibid.

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(a) Processes that are relevant for the destruction of the POP content in iron-containing

wastes use certain types of blast furnaces, shaft furnaces or hearth furnaces. All these processes operate

under reducing atmospheres at high temperatures (1,200°C–1,450°C). The reducing atmospheres and

high temperatures destroy PCDDs and PCDFs contained in the wastes and avoid de novo synthesis. The

blast furnace and shaft furnace processes use coke and small amounts of other reducing agents to reduce

the iron-containing input to cast iron. There are no direct emissions of process gas, as gas is used as a

secondary fuel. In the hearth furnace process, the iron-containing material is charged to a multi-hearth

furnace together with coal. The iron oxide is directly reduced to solid direct reduced iron (DRI). In a

second step, the reduced iron is melted in an electric arc furnace to produce cast iron.

(b) Processes that are relevant for the destruction of the POP content in wastes containing

NFMs are the Waelz rotary kiln process and bath melting processes using vertical or horizontal

furnaces. These processes are reductive, reach temperatures of 1,200°C and use rapid quenching, so

PCDDs and PCDFs are destroyed and de novo synthesis is avoided. In the Waelz process,

zinc-containing steel mill dusts, sludges, filter cakes, etc. are pelletized and smelted together with a

reductant. At a temperature of 1,200°C, the zinc volatizes and is oxidized to “Waelz Oxide”, which is

collected in a filter unit. In the vertical bath furnace process, copper-containing residues are used as a

catalyst and smelted at temperatures of at least 1,200°C. The filter dust is used for the production of

zinc and zinc compounds. In the horizontal bath furnace process, lead-containing residues and ore

concentrates are charged continuously into a smelting bath which has an oxidizing zone and a reducing

zone with temperatures of between 1,000°C and 1,200°C. The process gas (sulphur dioxide

concentration above 10 per cent) is used for sulphuric acid production after heat recovery and de-

dusting. The dust from the process is recycled after cadmium leaching.

298.309. The guidance on BAT/BEP developed by the Stockholm Convention relevant to Article 5 and

Annex C for thermal processes in the metallurgical industry should be used and applied to this

technology (UNEP, 2007.)

299.310. Efficiency: According to information provided by industry, results from spot tests from 2010 in

a thermal metallurgical process (bath melting) using printed circuit board as input material indicate a

destruction efficiency for the PBDEs above 99.99 % (European Commission, 2011).Data on DE or

DRE are not available.

300.311. Waste types: The processes described in paragraph 3080 above are specific to the treatment of

the following wastes:

(a) Residues from iron- and steel-making processes such as dusts or sludges from gas

treatment or mill scale that may be contaminated with PCDDs and PCDFs;

(b) Zinc-containing filter dusts from steelworks, dusts from gas cleaning systems of copper

smelters, etc., and lead-containing leaching residues of NMF production that may be contaminated with

PCDDs and PCDFs; and

(c) Waste electrical and electronic equipment that may contain POP-BDEs (Brusselaers et al,

2006) and HBCD (UNEP, 2015c); and.

(d) Automotive shredder residue that may contain POP-BDEs (Oeko Institut, 2018).

301.312. Pre-treatment: Iron-containing materials recycled by the conventional blast furnace process

require pre-treatment in an agglomeration facility. For the shaft furnace (“Oxycup” furnace) process the

iron-containing waste is briquetted. Briquetting is a cold process in which a binder and water are added

to the fines, which are then pressed to briquettes, dried and hardened. Generally, no pre-treatment is

necessary for the multi-hearth furnace process, although in some special cases the fine solids may have

to be pelletized. Pelletizing involves the addition of water and the formation of pellets in a drum.

Special pre-treatment of materials contaminated with POPs is not usually necessary for NFMs.

302.313. Emissions and residues: In iron and NFM production, PCDDs and PCDFs may be emitted

during the process itself or downstream in the flue gas treatment system. Application of BAT should,

however, prevent or at least minimize such emissions. When the processes described in paragraph 300

308 above are used for the destruction of POP content in wastes, appropriate release control and post-

treatment techniques are required (see paragraph 306 314 below). Slags are in many cases used for

construction purposes. For iron metals, emissions can occur from pre-treatment in an agglomeration

facility and also in the off-gas from melting furnaces. Residues from de-dusting systems are mainly

used in the NFM industry. The off-gas of multi-hearth furnaces is de-dusted by a cyclone, underlies a

post-combustion, and is quenched and cleaned with the addition of adsorbent and the use of a bag filter.

The off-gas of melting furnaces also underlies post-combustion and is quenched before it is mixed up

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with the off-gas of multi-hearth furnaces for the joint adsorbance step. For NFMs, residues include filter

dusts and sludges from wastewater treatment.

303.314. Release control and post-treatment: Control of temperatures and rapid quenching are often

suitable means of minimizing PCDD and PCDF formation. Process gases require treatment to remove

dust that consists mainly of metals or metal oxides as well as sulphur dioxide when smelting sulphidic

materials. In the ferrous metals industry, waste gases from agglomeration facilities are treated by an

electrostatic precipitator followed by further flue gas treatment, e.g., with the use of adsorption

techniques followed by an additional bag filter. The off-gases from multi-hearth furnaces are de-dusted

by a cyclone and subjected to treatment by post-combustion, quenching and further cleaning by the

addition of adsorbent followed by the use of a bag filter. The off-gases from melting furnaces also

require post-combustion and quenching and are then combined with the off-gas stream from multi-

hearth furnaces for further treatment with the addition of absorbent followed by the use of a bag filter.

In NFM production, suitable treatment techniques include the use of, inter alia, fabric filters,

electrostatic precipitators or scrubbers, sulphuric acid plants, and adsorption techniques with activated

carbon.

304.315. Energy requirements: Production processes for iron and NFM are energy-intensive with

significant differences between different metals. The treatment of the POP content in wastes within

these processes requires little additional energy.

305.316. Material requirements: For the production of metals, raw materials (ores, concentrates or

secondary material) are used together with additives (e.g., sand, limestone), reductants (coal and coke)

and fuels (oil and gas). Temperature control to avoid de novo synthesis of PCDDs and PCDFs requires

additional water for quenching.

306.317. Portability: Metal smelters are large and fixed installations.

307.318. Health and safety: The treatment of wastes within thermal processes can be regarded as safe if

properly designed and operated.

308.319. Capacity: The metal smelters described above have feedstock capacities above 100,000 tonnes

per year. Current experience with the addition of wastes contaminated with POPs to the feedstock

involves much smaller quantities but the capability for treating larger quantities may well exist and is

being explored.

309.320. Other practical issues: None.

321. State of commercialization: Cast iron production from iron-containing materials of iron and steel

production in a conventional blast furnace has been in operation for some years in Germany

(http://www.dk-duisburg.de),://www.dk-duisburg.de), where a shaft furnace (“Oxycup” furnace) has

been in operation since 2003 (http://www.thyssenkrupp.com).://www.thyssenkrupp.com). The hearth

furnace process has been in operation on an industrial scale in Luxembourg, since 2003

(www.paulwurth.com), and in Italy (www.lucchini.it).(www.paulwurth.com), and in Italy

(www.lucchini.it). The Waelz rotary kiln process is well-established and is covered by BAT that are in

operation at different sites in Europe (http://www.befesa-steel.com).(http://www.befesa-steel.com). The

vertical bath melting process is in operation in Germany (http://www.aurubis.com), as is the horizontal

bath melting process (www.berzelius.de).(www.berzelius.de).

3. Other disposal methods when neither destruction nor irreversible transformation is not the

environmentally preferable option

310.322. [When] neither destruction nor irreversible transformation is not the environmentally

preferable option for wastes with a POP content at or above the low POP content referred to in

subsection A of section III above, countries maycould [otherwise] allow such wastes to be disposed of

in an environmentally sound manner through methods other than those referred to in subsection IV.G.2.

311.323. Wastes containing or contaminated with POPs where such other disposal methods may be

considered include, but are not limited to:

(a) Wastes from power stations and other combustion facilities (except those listed in

subparagraph (d) below), wastes from the iron and steel industry and wastes from aluminium, lead, zinc,

copper and other non-ferrous thermal metallurgy. Such wastes include bottom ash, slag, salt slags, fly

ash, boiler dust, flue gas dust and other particulates and dust, solid wastes from gas treatment, black

drosses, wastes from treatment of salt slags and black drosses, dross and skimmings;

(b) Carbon-based and other linings and refractories from metallurgical processes;

(c) The following construction and demolition wastes:

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(i) Mixtures of, or separate fractions of, concrete, bricks, tiles and ceramics;

(ii) The inorganic fraction of soil and stones, including excavated soil from

contaminated sites; and

(iii) Construction and demolition wastes containing PCBs, excluding equipment

containing PCBs;

(d) Wastes from the incineration or pyrolysis of waste, including solid wastes from gas

treatment, bottom ash, slag, fly ash and boiler dust; and

(e) Vitrified wastes and waste from vitrification, including fly ash and other flue gas

treatment wastes and non-vitrified solid phase wastes.

312.324. The relevant authority of the country concerned should be satisfied that neither destruction nor

irreversible transformation of the POP content, performed using best environmental practices or best

available techniques, is the environmentally preferable option.

313.325. Other disposal methods when neither destruction nor irreversible transformation is the

environmentally preferable option include those described below.

(a) Specially engineered landfill121

314.326. Any landfilling should be carried out in a way that minimizes the potential of the POP content

to enter the environment. This may be achieved through pre-treatment, e.g., a suitable solidification

process. A specially engineered landfill should comply with requirements regarding location,

conditioning, management, control, closure and preventive and protective measures to be taken against

any threat to the environment in both the short and long terms. In particular, measures should prevent

the pollution of groundwater through leachate infiltration into the soil. Protection of soil, groundwater

and surface water should be achieved through a combination of a geological barrier and a synthetic

bottom liner system during the operational phase and through a combination of a geological barrier and

a top liner during the closure and post-closure phases. Measures should be taken to prevent and reduce

the production of gases and, as appropriate, introduce landfill gas collection and control systems.

315.327. Chemicals, including POPs, found in leachate and discharged into the receiving environment

can have an impact on the environment and human health. Landfill leachate on-site treatment

technologies should be in place to reduce and prevent toxic leachate from entering the environment.

Leachate can be treated through the use of physico-chemical and biological treatments or advanced

treatment technologies such as active carbon filtration, reverse osmosis and nanofiltration, among

others.

316.328. In addition, a uniform waste acceptance procedure based on a classification procedure for

acceptable waste, including standardized concentration limit values, should be introduced. Moreover,

monitoring procedures during the operation and post-closure phases of a landfill should be established

in order to identify and prevent any possible adverse environmental effects of the landfill and take the

appropriate corrective measures. A specific permit procedure should be introduced for the landfill.

Permits should include specifications regarding the types and concentrations of wastes to be accepted,

leachate and gas control systems, monitoring, on-site security, and closure and post-closure.

317.329. The following wastes containing or contaminated with POPs are not suitable for disposal in

specially engineered landfills:

(a) Liquids and materials containing free liquids;

(b) Biodegradable organic wastes;

(c) Empty containers, unless they are crushed, shredded or similarly reduced in volume; and

(d) Explosives, flammable solids, self-heating spontaneously combustible materials, water-

reactive materials, pyrophoric solids, self-reactive wastes, oxidizers, organic peroxides, and corrosive

and infectious wastes.

121 Further information is available in UNEP, 1995c, National Guidelines for Hazardous Waste Landfills (Canadian Council of

Ministers of the Environment, 2006), Landfill Guidelines (Centre for Advanced Engineering, 2000), Environmental

Guidelines/ Solid waste landfills. (State of NSW, 2016) and in pertinent national legislation, such as European Council Directive

1999/31/EC of 26 April 1999 on the landfill of waste.

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(b) Permanent storage in underground mines and formations

318.330. Permanent storage in facilities located underground in geohydrologically isolated salt mines

and hard rock formations is an option for separating hazardous wastes from the biosphere for geological

periods of time. A site-specific security assessment conducted in accordance with pertinent national

legislation, such as the provisions contained in European Council Decision 2003/33/EC of 19 December

2002 (establishing criteria and procedures for the acceptance of waste at landfills pursuant to Article 16

of and Annex II to Council Directive 1999/31/EC), Annex, appendix A, should be performed for every

planned underground storage facility.

319.331. Wastes should be disposed of in a manner that excludes any undesirable reaction between

different wastes or between wastes and storage linings, through, among other things, the storage of

wastes in chemically and mechanically secure containers. Wastes that are liquid, gaseous, emit toxic

gases or are explosive, flammable or infectious should not be stored underground in mines. Operational

permits should define waste types that should be generally excluded.

320.332. The following should be considered in the selection of permanent storage for disposal of POP

wastes:

(a) Caverns or tunnels used for storage should be completely separated from active mining

areas and areas that may be reopened for mining;

(b) Caverns or tunnels should be located in geological formations that are well below zones

of available groundwater or in formations that are completely isolated by impermeable rock or clay

layers from water-bearing zones;

(c) Caverns and tunnels should be located in geological formations that are extremely stable

and not in areas subject to earthquakes.

4. Other disposal methods when the POP content is low

321.333. If wastes with a POP content [at or] below the [defined] low POP content referred to in

subsection A of section III above are not disposed of using the methods described above, they should be

disposed of in an environmentally sound manner in accordance with pertinent national legislation and

international rules, standards and guidelines, including specific technical guidelines developed under the

Basel Convention.

322.334. Depending on, inter alia, the type of waste stream in question, the appropriate disposal method

should be chosen to manage the waste in an environmentally sound manner. For example, technical

guidelines on the ESM of a number of waste streams have been developed under the Basel Convention

and are available from www.basel.int.

323.335. Examples of pertinent national legislation are given in annex II to the present guidelines.

H. Remediation of contaminated sites

1. Contaminated site identification

324.336. Poor handling and storage practices in particular may lead to releases of POPs at sites storing

these chemicals122, resulting in contamination of the site with high levels of POPs that may pose serious

environmental and health concerns. Identification of such sites is the first step in addressing potential

concerns.

325.337. Identification of such sites can be undertaken using a phased approach, including:

(a) Identification of suspected sites, such as sites presently or historically involved in:

122 The identification of contaminated sites should also include those where POPs precursors have been used and

stored (e.g. the use of sulfuramid as a pesticide which is a PFOS precursor).

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(i) Manufacture of POPs;

(ii) Other processes listed in Annex C to the Stockholm Convention leading to the

creation of unintentional POPs;

(iii) Formulation of pesticides and filling and retrofilling of transformers;

(iv) Usage and storage of POPs, such as application of pesticides and placement of

transformers; and and usage of PFOS-containing fire-fighting foams;

(v) Disposal of POP wastes;

(vi) Manufacture of equipment, materials, articles (transformers, capacitors, etc)

containing POPs;

(vii) Accidents including fires with liquids and other materials containing or polluted

with POPs; and

(viii) Sites for the maintenance of equipment containing POPs.

(b) Review of current and historical information pertaining to the suspected site;

(c) An initial testing programme to confirm the presence or absence of suspected

contaminants and to characterize the physical conditions of the suspected site; and

(d) A detailed testing programme to identify the nature of the site contamination and gather

any additional information required.

326.338. Information on contaminated site identification is widely available. For example, the United

Nations Industrial Development Organization (UNIDO) Expert Group on POPs has developed a

comprehensive toolkit aimed at assisting developing countries with the identification, classification and

prioritization of POP-contaminated sites and with the development of suitable technologies for land

remediation, in accordance with best available techniques and best environmental practices (BAT/BEP)

(UNIDO, 2010). Other information can be found in the Reference manual for assessing soil contamination (FAO, 2000) and

the Guidance document on the management of contaminated sites in Canada (Canadian Council of Ministers of the Environment, 1997).),

Assessment and management of contaminated sites (Department of Environment Regulation, 2014) and

Brownfields Road Map to Understanding Options for Site Investigation and Cleanup. Sixth Edition (US

EPA, 2017).

2. Environmentally sound remediation

327.339. Contaminated site criteria developed by Governments using risk assessment techniques are

used as general targets in site remediation. Separate criteria can be developed or adopted for soil,

sediment and groundwater. Often, a distinction is made between soil quality criteria depending on the

use of the site: industrial (least stringent criteria), commercial, residential or agricultural (most stringent

criteria) soils. Examples of such criteria can be found in the German Federal Soil Protection and

Contaminated Sites Ordinance, the Swiss Soil Burden Ordinance and the Canadian Environmental

Quality Guidelines. 123 124 and the Austrian Standard ÖNORM S 2088-2 and in European Commission

(2007).125

328.340. Information on methods currently used for the remediation of sites contaminated with POPs,

including guidance on site assessment, remediation programs and risk assessment, is available from a

variety of sources, including:126

(a) Canadian Council of Ministers of the Environment, 1997. Guidance Document on the Management of

Contaminated Sites in Canada. Available from: www.ccme.ca and Canadian Federal Contaminated

Sites Action Plan. Available from

http://www.federalcontaminatedsites.gc.ca/default.asp?lang=en&n=BAC292EB-1

(b) Europe:

http://www.umweltbundesamt.at/en/umweltschutz/altlasten/projekte1/international1/

123 See https://www.ccme.ca/en/resources/canadian_environmental_quality_guidelines/ Canadian Council

of Ministers of the Environment, 2002, and annex II (examples of pertinent national legislation) below.

124 See Canadian Council of Ministers of the Environment, 2002, and annex II (examples of pertinent national

legislation) below.

125 See Canadian Council of Ministers of the Environment, 2002, and annex II (examples of pertinent national

legislation) below.

126 For full references, see annex III (bibliography) below.

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59

http://www.eugris.info

http://www.nicole.org

https://esdac.jrc.ec.europa.eu/themes/soil-contamination

https://www.eea.europa.eu/data-and-maps/indicators/progress-in-management-of-

contaminated-sites-3/assessment

(b)(c) FAO, 2001. Training manual on inventory taking of obsolete pesticides, Pesticide

Disposal Series No. 10. Available from: www.fao.org.

(c)(d) Federal Remediation Technology Roundtable (FRTR), 2002. Remediation Technologies

Screening Matrix and Reference Guide, Version 4.0. Available at www.frtr.gov/matrix2/top_page.html.

(de) United States Environmental Protection Agency (EPA):

http://www.epa.gov/superfund/

http://www.epa.gov/oswer/riskassessment/risk_superfund.htm

http://www.epa.gov/superfund/cleanup/pasi.htm,

http://www.epa.gov/superfund/policy/remedy/sfremedy/rifs.htm,

http://www.epa.gov/superfund/cleanup/rdra.htm

https://clu-in.org/

(ef) United States Army Corps of Engineers, 2003. Safety and Health Aspects of HTRW

Remediation Technologies. Available at: http://140.194.76.129/publications/eng-manuals/EM_1110-1-

4007_sec/EM_1110-1-4007.pdf; and

(fg) Vijgen, 2002. “NATO/CCMS Pilot Study: Evaluation of Demonstrated and Emerging

Technologies for the Treatment of Contaminated Land and Groundwater.” Available at:

https://www.clu-in.org/download/partner/2001annualreport.pdf.

I. Health and safety127

329.341. In general, there are three main ways to protect workers and members of the public from

chemical hazards (in order of preference):

(a) Keep workers and members of the public away from all possible sources of

contamination;

(b) Control contaminants so that the possibility of exposure is minimized; and

(c) Protect workers by ensuring that they use personal protective equipment.

330.342. Information on health and safety is also available from ILO (ILO, 1999a and 1999b), WHO

(WHO, 1995 and 1999), IPCS INCHEM (various dates) the United Kingdom Health and Safety

Executive (See Protection of workers and the general public during the development of contaminated

land, Guidance Note HS (G) 66-H HMSO) and in the Guidance Manual for Hazardous Waste Site

Activities (NIOSH, 1985). Examples of practical implementation can be found in UNEP, 2001.

331.343. Health and safety plans should be in place at all facilities that handle POP wastes to ensure the

protection of every person in and around such facilities. The health and safety plan for each specific

facility should be developed by a trained health and safety professional with experience in managing

health risks associated with the specific POPs at the facility.

332.344. All health and safety plans should adhere to the above principles and recognize local or

national labour standards. Most health and safety programmes recognize various levels of safety, with

risk levels depending on the site in question and the nature of the contaminated materials found there.

The level of protection provided to workers should correspond to the level of risk to which they are

exposed.

333.345. Different POP waste streams can present significantly different risks depending upon toxicity

and exposure. Levels of risk should be established and each situation should be evaluated by health and

safety professionals. Two types of situations are discussed below: higher-risk and lower-risk situations.

1. Higher-risk situations

127 Further information on health and safety is available from ILO, 1999a and 1999b; WHO, 1995 and 1999; IPCS INCHEM, no date. For full

references, see annex III (bibliography) below.

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334.346. Higher-risk situations occur where high concentrations of POPs or high volumes of POP

wastes are found and a high potential for exposure of workers or the general population exists. In such

situations, particular efforts should be made to minimize public exposure. In addition, guidance should

be provided to ensure that the public is aware of the potential risk and of the measures to be taken in

cases of exposure.

335.347. Specific technical guidelines on POP wastes will identify higher-risk situations relevant to the

specific POPs that they cover.

336.348. There is no international quantitative definition of high volume or high concentration. Workers

and employers can be guided by the advice and input of health and safety professionals, labour

representatives, scientific literature and government authorities. Higher-risk situations may occur:

(a) At sites producing, handling and/or using POPs;

(b) At stockpile and large-volume storage sites for chemicals or POP wastes;

(c) At facilities for the treatment or disposal of POP wastes;

(d) At sites contaminated with high concentrations of POPs at or near the surface.

337.349. At a minimum, POPs health and safety planning for higher-risk situations should include the

following elements:

(a) A written health and safety plan (HASP) should be developed and posted at each site;

(b) Workers who are to have access to the site should read the HASP and sign a statement

confirming that they have read it and understood it;

(c) The HASP may be written to encompass all hazards at the site but should have a section

or chapter specifically detailing procedures for POPs;

(d) Workers should be present at the site only when necessary for servicing or inspecting

equipment or stored materials;

(e) Workers entering the site should have appropriate health and safety and operational

training for chemical, physical and biological hazards;

(f) Health and safety training should be performed annually;

(g) Routine air monitoring should be carried out to detect the presence of POP contaminants;

(h) Collective protective measures such as active wet control system (e.g., to prevent

contaminated dust from becoming airborne) and passive covering systems (e.g., sealed impermeable

high-density polyethylene (HDPE) sheets to reduce dust and vapour diffusion), may be advisable;

(i) When appropriate, workers entering the site should wear appropriate respiratory

protection, and impermeable fabrics should cover their entire bodies (i.e., coveralls with hoods, face

shields, gloves and boot covers, or full body suits);

(j) Spill clean-up kits and personal decontamination materials should be present in all areas

containing POPs;

(k) Workers who are or are expected to be routinely entering sites or working with POPs

should undergo medical monitoring, including a baseline medical examination;

(l) When POPs are to be handled in an open system or when it is reasonably expected that

the protective clothing of a worker may be contaminated with POPs, a contaminant reduction zone

should be established where workers can be decontaminated and remove their protective equipment;

(m) The HASP and general work procedures should be reviewed at least annually and revised

if necessary to enhance health and safety at the site.

2. Lower-risk situations

338.350. As with high volume or high concentration, there is no international quantitative definition of

low volume or low concentration. The terms should thus be defined by comparing contaminant levels

with government guidelines or by conducting site-specific risk assessments. Lower-risk situations may

occur:

(a) At sites that contain materials contaminated with POPs in small quantities or at low

concentrations;

(b) In controlled storage rooms that contain small quantities of POPs; and

UNEP/CHW.14/INF/9

61

(c) At sites contaminated with low concentrations of POPs or where the contamination

cannot come directly into contact with people.;

(d) In cases where the POP concentration is low and the chemicalPOP is inside a polymer.

339.351. Despite the low level of risk that the situations described above present, some health and safety

measures should be taken to minimize exposure, including health and safety training of personnel who

are likely to come into contact with POPs.

J. Emergency response128

340.352. Emergency response plans should be in place for all POPs in production, use, storage and

transport or at disposal sites, in line with the exposure and risk profiles of each specific POP. While

emergency response plans can vary for each situation and each type of POP, the principal elements of

an emergency response include:

(a) Identifying all potential hazards, risks and accidents;

(b) Identifying relevant local and national legislation governing emergency response plans;

(c) Planning for anticipated emergency situations and possible responses to them;

(d) Maintaining a complete up-to-date inventory of all POPs on site;

(e) Training personnel in response activities, including simulated response exercises, and first

aid;

(f) Maintaining mobile spill response capabilities or retaining the services of a specialized

firm for spill response;

(g) Notifying fire departments, the police and other government emergency response

agencies of the location of POPs and their routes of transport;

(h) Installing mitigation measures such as fire suppression systems, spill containment

equipment, fire-fighting water containment, spill and fire alarms, and firewalls;

(i) Installing emergency communication systems, including signs indicating emergency

exits, telephone numbers, alarm locations and response instructions;

(j) Installing and maintaining emergency response kits containing sorbents, personal

protective equipment, portable fire extinguishers and first aid supplies;

(k) Integrating facility plans with local, regional, national and global emergency plans, if

appropriate; and

(l) Regularly testing emergency response equipment and reviewing emergency response

plans.

341.353. Emergency response plans should be prepared jointly by interdisciplinary teams that include

emergency response, medical, chemical and technical personnel and labour and management

representatives. When applicable, representatives of potentially impacted communities should also be

included.

K. Public participation

342.354. Public participation is a core principle of the 1999 Basel Declaration on Environmentally

Sound Management and many other international agreements. It is essential that the public and all

stakeholder groups have a chance to participate in the development of policy related to POPs, the

planning of programmes, the development of legislation, the review of documents and data, and

decision-making on local issues related to POPs. Paragraphs 6 (g) and (h) of the Basel Declaration

reflect an agreement to enhance and strengthen efforts and cooperation to achieve environmentally

sound management with regard to the enhancement of information exchange, education and awareness-

raising in all sectors of society; and cooperation and partnership at all levels between countries, public

authorities, international organizations, industry, non-governmental organizations and academic

institutions.

128 Further guidance on emergency response plans can be found in other guidelines developed by international organizations, such as the OECD Guiding

Principles for Chemical Accident Prevention, Preparedness and Response, second edition (2003), or by national, regional or local governments or agencies

(such as civil defence and emergency coordination agencies and fire departments).

UNEP/CHW.14/INF/9

62

343.355. The Stockholm Convention, in Article 10, paragraph 1 (d), calls on each Party, within its

capabilities, to promote and facilitate public participation in addressing POPs and their health and

environmental effects and in developing adequate responses, including by providing opportunities for

public input at the national level regarding the implementation of the Convention.

344.356. Articles 6, 7, 8, and 9 of the UNECE 1998 Convention on Access to Information, Public

Participation in Decision-making and Access to Justice in Environmental Matters (Aarhus Convention)

require the Parties to conduct fairly specific types of activities regarding public participation in specific

government activities, the development of plans, policies and programmes and the development of

legislation, and call for access to justice for the public with regard to the environment.

345.357. The participation of the public in the adoption of standards and regulations on POPs is

essential. Any Government planning new or changed regulations or policies should have an open

process for soliciting comment from any and all persons or groups. This means that a general invitation

to comment should be given through regular media outlets, the Internet, or by direct invitation. The

individuals and groups who should be considered for direct invitation to comment are:

(a) Individual citizens who have expressed an interest in POPs;

(b) Local citizens groups, including local environmental groups, for local issues;

(c) Groups of highly vulnerable people, such as women, children and the least educated;

(d) Regionally, nationally or globally organized environmental groups;

(e) Individual industries and businesses with a stake in the process;

(f) Business associations;

(g) Trade unions and associations;

(h) Professional associations;

(i) Other levels of government.

346.358. A public participation process may have several phases. Groups may be consulted before any

changes or programmes are considered, during the policy development process and after each draft

policy document is prepared. Comments may be invited in person, in writing or through an Internet

website.

347.359. An example of public consultation regarding the development of POPs management plans can

be found in the Australia Department of the Environment and Heritage document titled “A case study of

problem solving through effective community consultation.”129

129 See Australia Department of the Environment and Heritage, 2000.

UNEP/CHW.14/INF/9

63

Annex I to the technical guidelines

International instruments

In addition to the Stockholm and Basel conventions, there are other international instruments or

systems that contain provisions pertaining to POPs or POP wastes, including130:

(a) 1998 Protocol on Persistent Organic Pollutants to the UNECE 1979 Convention on

Long-range Transboundary Air Pollution;

(b) 2003 Protocol on Pollutant Release and Transfer Registers to the UNECE 1998

Convention on Access to Information, Public Participation in Decision-making and Access to Justice

in Environmental Matters (Aarhus Convention);

(c) 1991 Bamako Convention on the Ban of the Import into Africa and the Control of

Transboundary Movement and Management of Hazardous Wastes within Africa;

(d) 1995 Convention to Ban the Importation into Forum Island Countries of Hazardous and

Radioactive Wastes and to Control the Transboundary Movement and Management of Hazardous

Wastes within the South Pacific Region (Waigani Convention);

(e) OECD Council Decision C (2001) 107/FINAL Concerning the Control of

Transboundary Movements of Wastes Destined for Recovery Operations;

(f) Rotterdam Convention on Prior Informed Consent Procedure for Certain Hazardous

Chemicals and Pesticides in International Trade (1998); and

(g) Globally Harmonized System of Classification and Labelling of Chemicals (GHS).

130 The reference is made to the most recent version of the instruments, taking into account the possible

amendments.

UNEP/CHW.14/INF/9

64

Annex II to the technical guidelines

Examples of pertinent national legislation

Examples of national legislation containing provisions related to the management of POP wastes are outlined below.

Country Legislation Brief description

Argentina Law 25.670/2002 and Decree 853/2007 on PCBs • Environmental protection for the management of

PCB prohibiting the production, importation and

use as well as establishing a procedure to remove

functioning equipment containing it due to 2010

Argentina Law 24.051/1992 and Decree 831/1993 on

management of hazardous wastes • Reaches all POP wastes that are classified as

hazardous waste; includes a destruction efficiency

parameter for components in waste incineration

Argentina Resolution 511/2011 from National Health Service

and Food Quality (Servicio Nacional de Sanidad y

Calidad Agroalimentaria-SENASA).

• Prohibits the import of the active ingredient

endosulfan and its formulated products and forbids

the development, formulation, marketing and use

of products containing the active ingredient

endosulfan

Austria Soil Protection Acts • Contains stringent limit values for PCBs, PCDDs

and PCDFs in sewage sludge used as fertilizer.

Brazil Norm ABNT/NBR, N° 8371/1997 • Procedures for handling, transport and storage of

materials containing PCBs

Brazil Resolution CETESB (São Paulo state),

N° 007/1997 • Determines limits for PCDDs and PCDFs on

emissions from medical waste incinerators with

capacity > 200 kg/day

Brazil Resolution CONAMA, N° 264/1999 • Procedures for environmental licensing of waste

co-processing in cement kilns

Brazil Resolution CONAMA, N° 313/2002 • Provides for an inventory of PCB stocks and

industrial wastes

Brazil Resolution CONAMA, N° 316/2002 • Procedures and criteria for operating thermal waste

treatment systems, provides limits on emissions of

PCDDs and PCDFs.

Brazil Resolution CONAMA, N° 334/2003 • Procedures for environmental licensing for

establishments responsible for receiving pesticides

packaging.

Brazil Decision CETESB (São Paulo state), N° 26/2003 • Sets limits for air emissions of PCDDs and PCDFs

of cement kilns treating waste

Brazil Resolution CONAMA, N° 357/2005 • Provides maximum permitted levels for POPs in

effluents discharged to water.

Canada PCB Regulations • Restrict the manufacture, import, export and sale of

PCBs and equipment containing PCBs, and

prohibit PCB releases to the environment. The

regulations have deadlines ending the use of PCBs

and PCB equipment that have concentrations at or

above 50 mg/kg along with maximum storage and

destruction timelines.

China Technical specifications for centralized

incineration disposal engineering (HJ 2037) • Procedures for incineration of materials containing

PCBs

China Technical specification for co-processing of solid

wastes in cement kilns (GB 30760) • Procedures for co-processing of POPs wastes in

cement kilns

• Limitation for dioxin in cement produced by the

co-processing of solid waste

UNEP/CHW.14/INF/9

65

Country Legislation Brief description

China Guidelines for the pollution control of dioxins • Pollution control of dioxins on 4 key-industries

China Standard for pollution control on:

• municipal solid wastes incineration

(GB 18485)

• hazardous wastes incineration

(GB 18484)

• co-processing of solid wastes in cement

kilns (GB 30485)

• the steel smelt industry (GB 28664)

• sintering and pelletizing of iron and the

steel industry (GB 28662)

• Contains standards for releases of PCDDs and

PCDFs in air emissions

European

Union

Regulation (EC) No 850/2004 of the European

Parliament and of the Council of 29 April 2004 on

persistent organic pollutants and amending

Directive 79/117/EEC (last amendment:

Commission Regulation (EU) No 1342/2014)

• Article 7 contains provisions regarding the

management of wastes containing, consisting of or

contaminated with POPs.

European

Union

Council Directive 96/59/EC of 16 September 1996

on the disposal of polychlorinated biphenyls and

polychlorinated terphenyls (PCB/PCT)

• Contains rules regarding the disposal of PCBs and

PCTs, inter alia on the decontamination and/or

disposal of equipment and the PCBs therein.

European

Union

Directive 2010/75/EU on industrial emissions

(Industrial Emissions Directive, IED)

• Annex VI, part 5, contains emission limit values

for discharges of PCDD- and PCDF-contaminated

wastewater from the cleaning of waste gases.

• Annex V contains air emission values for PCDDs

and PCDFs.

European

Union

Council Decision 2003/33/EC of 19 December

2002 establishing criteria and procedures for the

acceptance of waste at landfills pursuant to Article

16 of, and Annex II to Directive 1999/31/EC

• Paragraph 2.1.2.2 of the annex contains criteria for

landfilling of inert waste containing PCBs.

Finland Council of State Decision (1071/1989) on

restricting the use of PCBs and PCTs • Contains limit values for PCBs and PCTs

Finland Council of State Decision (101/1997) on oil waste

management • Contains limit values for PCBs in regenerated oil

and in oil wastes destined for incineration

Finland Council of State Decision (711/1998) on the disuse

of PCB appliances and the treatment of PCB waste • Contains limit values for PCBs

Finland Council of State Decree (1129/2001) on a list of

the most common wastes and of hazardous wastes • Contains limit values for PCBs

Germany Federal Soil Protection and Contaminated Sites

Ordinance • Contains action levels regarding sites contaminated

with aldrin, DDT, HCB, HCH, PCBs, PCP, PCDDs

and PCDFs.

Germany Ordinance on Landfills and Long-Term Storage

Facilities • Contains a limit for PCBs in soils used as

recultivation layers of landfills.

• Prohibits the landfilling of waste that could harm

public welfare due to its content of long-lived or

bio-accumulable toxic substances.

Germany Ordinance on Underground Waste Stowage • Contains limits for the use of waste contaminated

with PCBs as stowage material.

Germany Fertilizer Ordinance • Contains limits for PFOS, PCDDs and PCDFs in

fertilizers

Germany Sewage Sludge Ordinance • Contains limits for the usage of sewage sludge

contaminated with PCBs, PCDDs and PCDFs as

fertilizer.

Germany Waste Wood Ordinance • Contains limits for recycling of waste wood

contaminated with PCBs and PCP.

Germany Waste Oil Ordinance • Contains limits for recycling of PCB-contaminated

oils.

Ghana Hazardous and Electronic Waste Control and • Contains elements related to the implementation of

UNEP/CHW.14/INF/9

66

Country Legislation Brief description

Management-Act, 2016, Act 917 the Basel, Rotterdam and Stockholm Conventions,

especially on all waste which include POP wastes.

Italy Part of the Environmental Frame Law concerning

waste and soil remediation (Part IV of

Legislative Decree No. 152 of 3 April 2006)

• Contains limits for the regeneration and the co-

incineration of PCB/PCT contaminated oils

• Contains action levels regarding sites (residential,

industrial commercial soil and groundwater)

contaminated with aldrin, alfa, beta and gamma

HCH, chlordane, dieldrin, endrin, DDT, HCB,

PCBs, PCDDs and PCDFs.

Italy Regulations for waste recovery with exemption

from permit requirements (simplified

administrative procedures) (Ministerial Decree

5/02/1998)

• Contains limits for PCBs, PCTs and PCDDs in

specific types of waste as conditions for exemption

from permit requirements

Japan Law Concerning Special Measures Against

Dioxins • Contains tolerable daily intake environmental

standards for ambient air, water quality (including

sediment) and soil, emission and residue standards

for gas, effluent, ash and dust regarding PCDDs,

PCDFs and dioxin-like PCBs.

Japan Law Concerning Special Measures for Promotion

of Proper Treatment of PCB Wastes (PCB Special

Measures Law)

• Contains standards for the treatment of plastics and

metals contaminated with PCBs.

Japan Soil Contamination Countermeasures • Contains standards for the treatment of soil

contaminated with PCBs.

Japan Waste Management and Public Cleansing Law • Contains criteria of hazardous wastes containing

PCBs, PCDDs, PCDFs and dioxin-like PCBs.

Japan Water Pollution Control Law • Contains emission standards for effluent containing

PCBs.

Mexico Norm NOM-098 of 2004 • Contains emission and destruction efficiency

standards for waste incinerators.

Mexico Norm NOM-133 of 2001 • Contains regulations regarding handling of PCBs

and a programme for the preparation of inventories.

New Zealand Hazardous Substances and New Organisms Act

1996 • Prohibits the import, manufacture, use or storage of

POPs (sections 25A – 25D, Schedule 1AA,

Schedule 2A).

New Zealand National Environmental Standards for Air Quality

(Resource Management (National Environmental

Standards for Air Quality) Regulations 2004)

• Contains standards banning activities discharging

significant quantities of dioxins and other toxics

into the air, and standards for ambient (outdoor) air

quality.

Norway Norwegian Product Regulations, Chapter 2 on

Regulated substances, preparations and

products.

• Contains a ban on the production, use, import and

export of PCBs, including PCB-containing

capacitors.

Norway Norwegian Waste Regulations, Chapter 14 on

Discarded insulating glass units containing

PCBs

• Lays down requirements for the producers to

collect and handle obsolete windows that contain

PCBs.

Norway Norwegian Pollution Regulations, Chapter 2 on

Clean-up of contaminated soil • Contains limit values below which a soil is

considered to be clean and suitable for use in

sensitive areas.

Switzerland Soil Burden Ordinance • Contains actions levels regarding sites

contaminated with PCBs, PCDDs and PCDFs.

United States

of America

EPA 40 CFR 63 Subpart EEE National Emission

Standards for Hazardous Air Pollutants from

Hazardous Waste Combustors

• Contains standards for releases of PCDDs and

PCDFs within air emissions.

United States

of America

40 CFR 268.48 Universal Treatment Standards for

Hazardous Wastes • Contains standards for the treatment of hazardous

waste prior to land disposal and aqueous waste

prior to release.

United States

of America

40 CFR 761.70 Standards for incineration of PCBs • Contains standards for air emissions when

incinerating PCBs.

UNEP/CHW.14/INF/9

67

Annex III to the technical guidelines

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2. Comments from CREPD

Centre de Recherche et d’Education pour le Développement

Research and Education Centre for Development

B.P : 2970 Yaoundé / Tel: +237 242 8250 94 / +2376 77202271

Déclaration d’Association No 000408/RDA/J06/BAPP

Email : crepdcentre@yahoo.com; website :www.crepdcameroun.org

COMMENTS FROM CREPD ON SUGGESTED LPCLS IN THE DRAFT GENERAL

TECHNICAL GUIDELINES FOR POPs WASTE

The Centre de Recherche et d’Education pour le Développement (CREPD), a public interest non governmental organisation overseeing the work of other public interest NGOs on chemicals and waste in more than 30 (thirty) countries in Francophone Africa, welcome the draft technical guidelines to be prepared after the OEWG-11 meeting and would like to provide the comment below from the standpoint of African context. Cameroon as well as all the countries in Francophone Africa have many products and articles in circulation that content POPs. Some of them are already at the end of their useful life time. The POP waste legislation regime in many African countries is limited to PCB waste due to the recent international effort to eliminate PCBs in developing countries. Still, there is no capacity to manage those PCBs waste in our countries. We have few pilot case studies documenting the occurrences of flame-retardant POPs in large consumer articles and products (mostly deriving from recycled plastic) including children toys and in free range chicken eggs (CREPD’s study (2018)) along site with dioxins from around a medical waste incinerator. This raises high health and environmental concerns as it will take long time for our governments to build national capacities for destruction or irreversibly transformation of POPs in wastes accumulating in the country. Unlike developed countries that already have domestic regulations and capacities outside of the Basel Convention to deal with the POP wastes, developing countries relay on the Basel technical guidelines on POP to guide the first generation of their national regulations on POP wastes definition. Therefore, as public interest NGO supporting the genuine implementation of chemicals and waste conventions, we strongly recommend adoption of the following stricter LPCLs proposed in the current draft general technical guidelines to determine POP wastes: 50 mg/kg (ppm) for sum of PBDEs including deca-BDE;

100 mg/kg (ppm) for HBCD;

100 mg/kg (ppm) for SCCPs; and

1 ug TEQ/kg (ppb) for PCDD/Fs.

These strict limits will contribute to stop transboundary movements of e-waste and fly ashes (with the most negative impacts on developing countries); prevent toxic recycling; and enable green circular economy.

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3. Comments from EERA

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4. Comments from IPEN

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Annex II

Compilation of comments regarding document

UNEP/CHW.14/7/Add.2 (Technical guidelines on SCCP)

The Secretariat received comments regarding document UNEP/CHW.14/7/Add.2 from the European

Union and its Member States.

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Draft technical guidelines on the environmentally sound management of wastes

consisting of, containing or contaminated with short-chain chlorinated paraffins

(Draft of 1 November 2018)

General Comments

The European Union and its Member States have a few editorial comments shown highlighted in

yellow.

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Contents

Abbreviations and acronyms ....................................................................................................................... 87

Units of measurement .................................................................................................................................. 87

I. Introduction ....................................................................................................................................... 88 A. Scope ..................................................................................................................................... 88 B. Description, production, use and wastes ......................................................................... 88

1. Description ................................................................................................................ 88 2. Production ................................................................................................................. 90 3. Use ............................................................................................................................. 91 4. Wastes........................................................................................................................ 93

II. Relevant provisions of the Basel and Stockholm Conventions ..................................................... 97 A. Basel Convention ................................................................................................................ 97 B. Stockholm Convention ....................................................................................................... 99

III. Issues under the Stockholm Convention to be addressed cooperatively with the Basel

Convention ..................................................................................................................................... 100 A. Low POP content ............................................................................................................. 100 B. Levels of destruction and irreversible transformation .............................................. 100 C. Methods that constitute environmentally sound disposal ......................................... 100

IV. Guidance on environmentally sound management (ESM) ......................................................... 100 A. General considerations ................................................................................................... 100 B. Legislative and regulatory framework ......................................................................... 100 C. Waste prevention and minimization ............................................................................. 101 D. Identification of wastes ................................................................................................... 101

1. Identification .......................................................................................................... 101 2. Inventories .............................................................................................................. 102

E. Sampling, analysis and monitoring............................................................................... 102 1. Sampling ................................................................................................................. 102 2. Analysis .................................................................................................................. 103 3. Monitoring .............................................................................................................. 104

F. Handling, collection, packaging, labelling, transportation and storage ................. 104 1. Handling ................................................................................................................. 104 2. Collection ............................................................................................................... 105 3. Packaging ............................................................................................................... 105 4. Labelling ................................................................................................................. 105 5. Transportation ........................................................................................................ 105 6. Storage .................................................................................................................... 105

G. Environmentally sound disposal ................................................................................... 105 1. Pre-treatment .......................................................................................................... 105 2. Destruction and irreversible transformation methods ......................................... 105

3. Other disposal methods when destruction or irreversible transformation is not the

environmentally preferable option ......................................................................................... 105 4. Other disposal methods when the POP content is low ........................................ 105

H. Remediation of contaminated sites ............................................................................... 106 I. Health and safety ............................................................................................................. 106

1. Higher-risk situations ............................................................................................ 106 2. Lower-risk situations ............................................................................................. 106

J. Emergency response ........................................................................................................ 106 K. Public participation ......................................................................................................... 106

Annex I: Synonyms and trade names of commercial formulations that contain or may have contained

SCCPs addressed by Stockholm Convention on POPs ............................................................... 107

Annex II: Consumer products containing SCCPs on the EU market 2013-2017 . Error! Bookmark not

defined.

Annex III: Bibliography ............................................................................ Error! Bookmark not defined.

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Abbreviations and acronyms BAT best available techniques

BEP best environmental practices

CA polychlorinated n-alkanes

CAS Chemical Abstracts Service

CP Chlorinated paraffins

EC European Commission

ESM environmentally sound management

EU European Union

EVA ethylene-vinyl acetate

I-TEQ International Toxic Equivalent

LCCP long-chain chlorinated paraffins based on C18-C20 (liquids), C>20 (liquids) and C20 wax

grades (average carbon chain length approximately C25)

MCCP

NOEC

medium-chain chlorinated paraffins based on C14-C17 paraffin

No-Observed Effect Concentration

OECD Organization for Economic Co-operation and Development

PCB polychlorinated biphenyl

PCDD polychlorinated dibenzo-p-dioxin

PCDF polychlorinated dibenzofuran

POP

POPRC

persistent organic pollutant

Persistent Organic Pollutants Review Committee

PVC polyvinylchloride

SCCPs Short-chain chlorinated paraffins, with straight-chain chlorinated hydrocarbons with

chain lengths ranging from C10 to C13 and a content of chlorine greater than 48 per cent

by weight

TEQ toxic equivalent

UNEP United Nations Environment Programme

XRF X-ray fluorescence

Units of measurement

mg milligram (10-3 gram)

mg/kg milligram(s) per kilogram. Corresponds to parts per million (ppm) by mass

µg microgram (10-6 gram)

µg/kg microgram(s) per kilogram. Corresponds to parts per billion (ppb) by mass

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I. Introduction

A. Scope

1. Short-chain chlorinated paraffins (SCCPs), defined as straight-chain chlorinated

hydrocarbons with chain lengths ranging from C10 to C13 and a content of chlorine greater than 48

per cent by weight, were listed in Annex A (elimination) to the Stockholm Convention in 2017,

through an amendment that entered into force in 2018. Additionally, a limit for the presence of

SCCPs in other chlorinated paraffin (CP) mixtures was set at 1% by weight.

2. The present technical guidelines should be used in conjunction with the General technical

guidelines on the environmentally sound management of wastes consisting of, containing or

contaminated with persistent organic pollutants” (UNEP, […]) (hereinafter referred to as “General

technical guidelines”). The General technical guidelines are intended to serve as an umbrella guide

for the ESM of wastes consisting of, containing or contaminated with persistent organic pollutants

(POPs).

B. Description, production, use and wastes

1. Description

3. SCCPs belong to a larger group of chlorinated paraffins (CPs), or polychlorinated n-alkanes

(CA), which are complex mixtures of substances with the general molecular formula CxH(2x-y+2)Cly.

CPs are characterised by the carbon-chain length range of their n-alkanes and by the chlorine content

of the product. An average chain length for the hydrocarbon feedstock or an average molecular

weight is often stated as well. For example, a chlorinated paraffin referred to as C12, 60% chlorine,

would be a product with an average chain length of 12 carbons with approximately 60% chlorine.

(IARC, 1990, Glüge et al, 2016).

4. The chain lengths of commercial paraffin products are between ten and 38 carbon atoms and

chlorine contents between 10 and 72% by weight. According to their chain length, CPs are divided

into short-chain CPs (short chain CPs, C10–C13131), medium-chain CPs (MCCPs, C14–C17) and long-

chain CPs (LCCPs, C17–C30) (IARC, 1990, Glüge et al, 2016).

5. In Annex A to the Stockholm Convention, only short chain CPs with chain lengths ranging

from C10 to C13 and a content of chlorine greater than 48 per cent by weight (see structural formula

of an example in Figure 1) are listed.

Figure 1: Example of a molecule that can be found within a SCCP mixture (2,3,4,5,6,8-

hexachlorodecane, C10).

6. Because of the complex nature of CPs, it is not always possible to separate SCCPs from other

CPs in chemical references. Commercial SCCP products consist of mixtures of isomers and

congeners, and the chlorine content of a product does not allow for identification of compounds

present in the mixture (Danish Environmental Protection Agency, 2014). CAS numbers, which are

commonly used to identify chemicals, often cover both POP-CPs as well as non-POP-CPs such as

short chain CPs with less than 48% chlorine or MCCPs. Annex A to the Stockholm Convention

contains examples of substances that may contain short-chain chlorinated paraffins with chlorine

content greater than 48% by weight (Table 1). In addition, the POPRC risk profile

(UNEP/POPS/POPRC.11/10/Add.2) mentions other CAS numbers, which contain SCCPs e.g. CAS

No 63449-39-81. The EU Regulation on POPs132 addresses short-chain chlorinated paraffins with

131 Please note that outside the scope of these guidelines, this definition may also cover other short chain

chlorinated paraffins than those covered by the Stockholm Convention restrictions, i.e. C10-C13 with

chlorination degree of 48% or below. 132 Regulation (EC) No 850/2004 of the European Parliament and of the Council of 29 April 2004 on Persistent

Organic Pollutants and Amending Directive 79/117/EEC, see http://eur-lex.europa.eu/legal-

content/EN/TXT/PDF/?uri=CELEX:02004R0850-20160930&qid=1512650945378&from=FI.

Commented [EU/MS21]: Correction; SCCPs are

defined in para. 2; here all short chain CPs are meant,

not only the ones referred to in para. 2. This was agreed

in the SIWG meeting

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CAS number 85535-84-8. This CAS number represents the commercial SCCPs product that is

produced by the chlorination of a single hydrocarbon fraction consisting of n-alkanes that have a

carbon chain length distribution consisting of 10, 11, 12 and 13 carbon atoms; however, this CAS

number # does not specify the degree of chlorination of the SCCPs and may therefore include

substances which are not included in Annex A to the Stockholm Convention. Examples of trade

names of SCCPs products are contained in Annex I.

Table 1: Examples of CAS numbers that may contain SCCPs according to the Stockholm

Convention Annex A.

CAS number Description

85535-84-8 Alkanes C10-C13, chloro

68920-70-7 Alkanes, C6-C18, chloro

71011-12-6 Alkanes, C12-C13, chloro

85536-22-7 Alkanes, C12-C14, chloro

85681-73-8 Alkanes, C10-C14, chloro

108171-26-2 Alkanes, C10-C12, chloro

7. The physical and chemical properties of the SCCPs are determined by the chlorine content

(typically 49-70% for commercial substances). There are a wide number of possible chlorinated

paraffins (of different chain length, degrees of chlorination and position of the chlorine atoms along

the carbon chain) present in any given commercial product. Thus, care has to be taken when

interpreting some of the physico-chemical data. Increasing the chlorine content leads to an increase

in viscosity and a decrease in volatility. SCCPs are relatively inert substances, which are resistant to

chemical attack and are hydrolytically stable. They possess good thermal stability. However, if held

at high temperatures (>200C) for long periods they will darken and release detectable quantities of

hydrogen chloride (ECB, 2000). CPs, including short chain CPs, are practically insoluble in water,

lower alcohols, glycerol and glycols, although they can form emulsions and/or suspensions. They

are soluble in chlorinated solvents, aromatic hydrocarbons, ketones, esters, ethers, mineral oils and

some cutting oils (IARC, 1990, Fiedler, 2010). Measured water solubilities of individual C10-C12

chlorinated alkanes ranged from 400 - 960 µg/L (Drouillard et al. 1998,

UNEP/POPS/POPRC.11/10/Add.2), while estimated solubilities of C10 and C13 chlorinated alkane

mixtures ranged from 6.4 - 2370 µg/L (BUA 1992, UNEP/POPS/POPRC.11/10/Add.2).

8. SCCPs are persistent, bioaccumulative, and toxic, particularly to aquatic organisms, and

undergo long range environmental transport. SCCPs have been measured in sediments also in Arctic

lakes. Although concentrations in water in remote areas are low, SCCPs are measured in Arctic biota

at levels comparable to known POPs indicating widespread contamination. Notably, SCCPs are

present in Arctic terrestrial and marine mammals, which are in turn food for northern indigenous

people. SCCPs are measured in human breast milk both in temperate and Arctic populations. SCCPs

have also been detected in food (e.g. in Denmark, Germany, France, Italy, Japan, the UK, the USA).

(UNEP/POPS/POPRC.11/10/Add.2).

9. According to the Stockholm Convention Persistent Organic Pollutants Review Committee

(POPRC) risk profile (UNEP/POPS/POPRC.11/10/Add.2) SCCPs both empirical (laboratory and

field) and modelled data indicate that SCCPs can accumulate in biota. High concentrations of

SCCPs in upper trophic level organisms, notably in marine mammals and aquatic freshwater biota

(e.g., beluga whales, ringed seals and various fish), is additional evidence of bioaccumulation.

SCCPs are particularly toxic to aquatic invertebrates, with a reported chronic No-Observed Effect

Concentration (NOEC) of 5 µg/L for Daphnia magna and a chronic NOEC of 7.3 µg/L for the

mysid shrimp. Severe liver histopathology has been observed in trout, with Lowest Observed Effect

Concentrations ranging from 0.79 to 5.5 µg/g in whole fish tissue. The International Agency for

Research on Cancer considers some SCCPs (average C12, average 60% chlorination) to be possible

carcinogens (groups 2B), although questions have been raised regarding the mechanisms for

induction of tumors and the relevance for human health of the studies on which this classification

was derived. The EU risk assessment from 2008 concludes that effects on the liver, thyroid, and

kidney have been shown to occur in mammalian species exposed to SCCPs. The effects are

manifested as organ weight increases and histological changes after exposure for weeks or months,

but may turn into carcinomas and adenomas after chronic exposure (ECB, 2008,

UNEP/POPS/POPRC.11/10/Add.2).

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2. Production

10. Parties to the Stockholm Convention shall prohibit and/or eliminate the production of SCCPs,

unless they have notified the Secretariat of their intention to produce it for the time-limited specific

exemptions listed in Annex A to the Convention. In addition, Parties for which the amendment did

not enter into force automatically may continue to produce SCCPs for any purpose until they have

ratified the amendment through which the chemical was listed in Annex A. Information on

production of SCCPs can be found in the register of specific exemptions of the Stockholm

Convention on the Convention website (www.pops.int). Information on the status of ratification by

the Parties of the amendment listing SCCPs in the Stockholm Convention can be found on the

website of the Treaty Section of the United Nations (https://treaties.un.org/).

11. Chlorinated paraffins, including SCCPs, have been produced commercially since the 1930s.

Production took place only in the USA until 1977, when the production began in Europe as well as

Japan (Glüge, 2016). Ordinary commercial chlorinated paraffins are not single compounds but

mixtures, each containing several homologous n-alkanes corresponding to their manufacture from n-

paraffin fractions with several different degrees of chlorination. There are a wide number of possible

CPs of different chain length, degrees of chlorination and position of the chlorine atoms along the

carbon chain present in any given commercial product (ECB, 2000).

12. The mixtures of chlorinated n-alkanes are produced by reacting normal paraffin fractions

obtained from petroleum distillation with gaseous chlorine exothermically at 80-1200° C in the

liquid phase. Ultraviolet light is often used to promote chlorination, particularly at higher chlorine

levels. The linings of the reactor vessels must be inert (e.g., glass or steel) to avoid the formation of

metal chlorides, which cause darkening of the product by decomposition. Additional procedures

include solvent stripping and grinding of the products as necessary (Zitko & Arsenault, 1974, IARC,

1990).

13. Confirmed SCCP production has taken place at least in Italy, Germany, Romania, Slovakia

and the UK (German Federal Environment Agency, 2015). According to the information collected

by POPRC in 2015, CPs of various chain lengths were produced in the Russian Federation, India,

China, Japan and Brazil. (UNEP/POPS/POPRC.11/10/Add.2).

14. Sverko et al. (2012) indicated total production estimates for SCCPs in the United States and

Europe ranging from 7 500 to 11 300 t per year. Information submitted to POPRC in 2007 indicated

that 150 t/year of SCCPs was produced in Brazil. (UNEP/POPS/POPRC.11/10/Add.2). Glüge et al

(2016) estimated the current worldwide production of SCCPs at 165 000 t/year, whereas the global

production of all CPs was estimated at 1 million tonnes. Share of SCCPs from total CP production

was estimated at 15-20 %.

15. Information on production often includes paraffins of all chain-lengths and degrees of

chlorination and it may therefore not be possible to specifically address the production of SCCPs.

For example, in industrial mixtures from China, distinctions between CPs are made based on

chlorination degrees rather than on carbon chain lengths (UNEP/POPS/POPRC.11/10/Add.2).

Therefore, the figures often include short-chained paraffins (C10-C13), but also other chain-length

paraffins such as medium-chained chlorinated paraffins (MCCPs), which are often used as

alternatives to SCCPs. Nevertheless, as the reported environmental concentrations of SCCPs are

higher in China than in other regions, it can be assumed that SCCPs are produced in China (van

Mourik et al, 2016, Zhang et al., 2017).

16. Currently the largest volume producer of CP is China (UNEP/POPS/POPRC.11/10/Add.2)

with 120 CP manufacturers, and it was estimated that China produced approximately 20%-30% of

the total global CPs between 2007-2013 (Jiang et al., 2017, Glüge et al., 2018). The CPs produced

by Chinese manufacturers are mixtures of SCCPs, MCCPs, and LCCPs defined by their degree of

chlorination rather that the chain-length (Glüge et al., 2016, Yin, 2016, Glüge et al., 2018). The

estimated annual production increased from 600 000 t (metric tonnes) in 2007 (Fiedler, 2010) to

1000 000 t/year in 2009 (Chen et al. 2011). European production estimates for all chlorinated

alkanes in 2010 was 45 000 t. The USA reported production volumes for 2007 at 45 000 t, including

both SCCPs and MCCPs. The Chlorinated Paraffins Industry Association (CPIA) submitted Annex

E (2010) information on the yearly production of CPs in North America from 2000 to 2009.

Production was approximately 3700 t in 2000, peaked at approximately 4 000 t in 2001, and steadily

declined to approximately 800 tonnes in 2009. (UNEP/POPS/POPRC.11/10/Add.2).

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3. Use133

17. Parties to the Stockholm Convention shall prohibit and/or eliminate the use of SCCPs, unless

they have notified the Secretariat of their intention to use SCCPs for a time-limited specific

exemption listed in Annex A to the Convention. In addition, Parties for which the amendment did

not enter into force automatically may continue to use SCCPs for any purpose until they have

ratified the amendment through which the chemical was listed in Annex A. Information on use of

the exemptions can be found in the register of specific exemptions of the Stockholm Convention on

the Convention website (www.pops.int). Information on the status of ratification by the Parties of

the amendment listing SCCPs in the Stockholm Convention can be found on the website of the

Treaty Section of the United Nations (https://treaties.un.org/).

18. CPs are chemicals with different carbon lengths and degrees of chlorination, which give

different properties and because of their versatility, they are used for a wide range of applications.

Uses have varied between countries and over time, but main SCCP applications have been for

polyvinylchloride (PVC), metal-working fluids, paints, coatings, sealants, rubber, and textiles, as a

fire-retardant, plasticizer, or water-repellent. They have also been used in leather production.

SCCPs have been used to replace PCBs, and many of the uses are similar. However, SCCPs have

been reported to not be suitable for uses requiring high heat stability (e.g., capacitors, transformers)

(Howard et al., 1975).

19. SCCPs are used as secondary plasticizers for PVC in applications such as electrical cables

when the inherently low inflammability of PVC would be impaired by primary plasticizers (e.g.,

dioctyl phthalate) (IARC, 1990, ECB, 2000, USEPA, 2009). The majority of flexible PVC is

believed to be used in flooring, wall covering, upholstery and insulation of wire and cables (ECB,

2008). In Western Europe, the main use (50 %) in the 1970’s was in PVC and other plastics

production (Schenker, 1979, as quoted in IPCS, 1996 (original source could not be located). SCCPs

were still used in PVC in the EU in the 1990’s (ECB, 2008). In the USA, the second largest use of

SCCPs after metal-working was either as plasticizer or flame retardant in plastics (USEPA, 2009).

20. SCCPs are used as flame retardants in rubber products, also in conjunction with other flame

retarding additives such as antimony trioxide and aluminum hydroxide (ECB, 2000). Rubber

containing SCCPs has been used in conveyor belts for underground mining, sound-insulating

materials in hoses as well as seals in the electrical installation and in vehicles. Among the different

types of conveyor belts, use of SCCPs has been confirmed in mono-ply (solid woven) conveyor

belts (the most modern type) (Danish Environmental Protection Agency, 2014). It is preferred to use

SCCPs, because of their higher degree of chlorination per weight compared to MCCPs and therefore

higher flame retardancy (German Federal Environment Agency, 2015). In 2007, 300 tonnes of

SCCPs was used in Brazil for the purposes of flame retardant in rubber, car carpet and accessories

(UNEP/POPS/POPRC.11/10/Add.2).

21. SCCPs have been used as extreme-pressure additives in metal-machining fluids (lubricants

and coolants), engineering and metal working operations such as drilling, machining/cutting,

drawing and stamping e.g. in the automobile industry, precision engineering industry and in

machinery construction since around 1930 (IPCS, 1996, ECB, 2000). The short chain chlorinated

paraffins (typically 49-69 % chlorine) are blended with other additives including corrosion

inhibitors, emulsifiers, biocides and surface-active agents and can be used either in straight oil

applications (in solution in a hydrocarbon) or in soluble oil emulsions dispersed in water (ECB,

2000). In the EU, 9380 tonnes (70% of all use) of SCCPs were used as metal working lubricants in

1994 (RPA, 2010), until the prohibition in 2003 (ECB, 2008). Similarly, nearly all use of SCCPs in

Canada was related to metalworking (Environment Canada, 2008). IARC (1990) estimated that

approximately 50% of the CPs consumed in the USA was used as extreme-pressure lubricant

additives in the metal working industry. Also in the USA, the largest use of SCCPs was as a

component of lubricants and coolants in metal cutting and metal forming operations (USEPA, 2012).

22. As a plasticizer or binder additive to paints, coatings and sealants, and to improve resistance

to water and chemicals, SCCPs have been used as alternatives to PCBs (ECB, 2000, USEPA, 2009,

UNEP/POPS/POPRC.11/10/Add.2, German Federal Environment Agency, 2015). The paints are

used mainly in industrial/specialist applications such as marine primer paints and fire retardant

paints (ECB, 2000, RPA, 2010). The SCCPs are mixed into the paint during the formulation step

and becomes physically entrained in the coating once applied (ECB, 2008). Other applications

include road marking paints, anti-corrosive coatings for metal surfaces, swimming pool coatings,

133 “Use” covers the use of SCCPs mixtures for the production of products and articles, as well as the use of

those products and articles.

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decorative paints for internal and external surfaces, and primers for polysulfide expansion joint

sealants, SCCPs may also be used in cross-linkable polyester systems with peroxides for the

production of long-term road markings and it may be found in unsaturated polyester resin which is

used in the production of fibre reinforced composites (RPA 2010, European Commission, 2011).

Two main materials onto which SCCP-containing paints and varnishes were applied are metal and

concrete. The sealant uses include rubber and chlorinated rubber coatings, polysulphide,

polyurethane, acrylic and butyl sealants used in building and construction and in sealants for double

and triple glazed windows. (IARC, 1990, WHO, 1996, ECB, 2008, Danish Environmental

Protection Agency, 2014, German Federal Environment Agency, 2015).

23. SCCPs have been used in the production of flame-resistant, water repellent and rot-

preventing textile finishes in sail cloths and industrial protective clothing and tarpaulins (ECB,

2000). The major historical use of chlorinated paraffins was in military tenting and other textile

applications where fire risk must be controlled (Zitko & Arsenault, 1974). According to ECB (2008)

SCCPs were mainly applied as a flame retardant for backcoating of textiles in the EU and less for

waterproofing. Typical applications for back-coated textiles potentially included furniture

upholstery, seating upholstery in transport applications, and interior textiles such as blinds and

curtains as well as industrial protective clothing (RPA, 2010).

24. RPA (2010) suggested that use in the impregnation of commercial and military tents (to

provide a flame retardant, waterproof and rot-proof finish – ‘dry proofing’ of heavy textiles) was

still ongoing in the EU in 2010, and SCCPs were used in polyester-cotton, cotton or linen-flax.

According to European Union (2011), tents were the only application of relevance to SCCPs in the

EU.

25. SCCPs have been used in the leather industry as fat liquoring agents (European Commission,

2011). They show better adhesion to the animal skin than natural oils, with similar fattening and

softening properties. They also impart better washability to the leather than natural oils. They are

usually applied to the moist dressed leather in the form of a 10-30% emulsion or are added to

sulphated or sulphonated oil or synthetic emulsifying agents. (ECB, 2000).

26. As SCCPs have been used in materials such as plastics, textiles, leather, rubbers, inks, paints,

adhesives and surface coatings, that are used to produce apparel, footwear and accessories, they are

commonly found in materials and consumer articles (German Federal Environment Agency, 2015,

KEMI, 2016, Table 2). The articles containing SCCPs are mainly soft plastic items made of PVC

(i.a. toys, beauty cases, exercise mats made of PVC plastic, stickers for wall decoration, dress

costumes, etc.) (BTHA, 2016). In Europe SCCPs have not been used for PVC since 2008 (ECB,

2008), but there are plenty of examples of articles containing SCCPs at present in the EU market

(see Annex II). It has also been reported that hand blenders used for food preparation in Sweden

were found to release chlorinated paraffins under normal use. It has also been demonstrated that the

presence of CPs in household appliances can contaminate food during preparation and is an

unexpected exposure pathway and should be addressed (Strid et al.2014).

27. SCCPs of different chain-lengths and degrees of chlorination have different properties, and

have therefore been used for different applications. In metal machining fluids, pastes, emulsions and

lubricants, chlorinated paraffin grades with good solubility in mineral oils (SCCPs as well as

MCCPs (C10-C17)) and chlorine contents of 40-60% are preferred. For flame-retardant applications,

chlorinated paraffins with approximately 70% chlorine are used; the chain length depends on the

substrate: SCCPs have been used for rubber and soft plastics (Zitko & Arsenault, 1974), but this is

likely not the case anymore.

28. The use of CPs in general (including SCCPs) has only been reported in the USA between

1944-1977, although they may have been used in other countries during this period as well (Danish

Environmental Protection Agency, 2014, Glüge et al. 2016). Since then the use of SCCPs in Europe

and Japan increased significantly, until the use in Europe started to decrease in the early 2000’s

(ECB, 2008, European Union, 2011, Glüge et al. 2016). Since 2000, China has been the largest

consumer of CPs (share of SCCPs not specified), with approximately 500 000 t annually (Glüge et

al. 2016). Use of SCCPs in metalworking and for fat liquoring of leather was prohibited in the EU in

2003. From 13 000 t per year in 1994 (EU-15), the use decreased to estimated 530 t per year in 2010

in EU-27 (RPA, 2010). In 2012 the use of SCCPs in the EU was further restricted to use as fire

retardants in rubber used in conveyor belts in the mining industry, as fire retardants in dam sealants.

The US prohibited use of SCCPs in 2013 (van Mourik et al., 2016). Japanese industry discontinued

the use in metalworking voluntarily in 2007 (UNEP/POPS/POPRC.11/10/Add.2). In Canada, the

production of chlorinated paraffins had stopped by 2008 (Environment Canada 2008), and the use of

SCCPs were prohibited in 2013 (Government of Canada 2013).

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29. CPs, including SCCPs, have been used for other purposes, which are apparently no longer

relevant. These include use as a solvent in a nasal spray, component in clear lacquers for wood and

hardboard, fire-proofing of wood, paper-sizing, antistatic agents on nylon, soot inhibitor for fuel oil,

and coating for tableted calcium hypochlorite, used in the treatment of sewage and swimming pool

waters. Chlorinated paraffin sulfonic acids were also used as emulsifiers for biocidal concentrates

(as quoted in Zitko & Arsenault, 1974).

30. SCCPs have been under scrutiny for their health and environmental impacts, and restrictions

have been implemented in Albania, Canada, EU, Norway and the United States

(UNEP/POPS/POPRC.12/11/Add.3). Norway banned SCCPs in 2002 and Canada banned the

manufacture, use, sale, offer for sale or import in 2013 (Government of Canada, 2013). In the EU

use of SCCPs was limited to use as flame-retardant in mining conveyor belts and dam sealants in

2012.

Table 2: Examples of concentrations of SCCPs in materials and articles.

Material SCCP content (mg/kg) Source

As secondary plasticizer

in PVC

Up to 100 000 BTHA, 2016

KEMI, 2016

EVA foam Up to 70 000 (found in yoga mats) BTHA, 2016, Annex II

Metal working, cutting

fluids

70 000-90 000

50 000-100 000 in oil-based cutting

fluids

<10 000 in emulsion-based cutting

fluids

20 000-100 000, up to 800 000

Koh et al, 2002

European Commission, 2011

-“-

ECB, 2000

Rubber 10 000-40 000, can be up to 150 000

100 000-170 000 in conveyor belts

100 000 in conveyor belts, 100 000-

170 000 for other rubber products

The concentration of SCCPs depends

on the rubber type used

ECB, 2008

-“-

RPA, 2010

European Commission, 2011

Coatings 25000-100 000 in intumescent coatings

100 000-150 000 in anti-corrosive and

protective coatings

RPA, 2010

Textiles Potential flame retardant in cellulosic

textiles

40 000-150 000 in backcoating of

textiles

BTHA, 2016

RPA, 2010

Leather Maximum of 10 000 in leather

20 000 mean

200 000 in fat-liquoring mix

ECB, 2000

RPA, 2010

European Commission, 2011

Paints 50 000-200 000 (after drying)

20 000 (road markings)

10 000-100 000 in road markings

ECB, 2008

European Commission, 2011

RPA, 2010

Adhesives and sealants 50 000-140 000

200 000-300 0000

ECB, 2008

Danish Environmental

Protection Agency, 2014

Paper 130 mg/A4 sheet German Federal

Environment Agency, 2015

4. Wastes

31. Action aimed at waste streams of importance in terms of volume and concentration will be

essential to eliminating, reducing and controlling the environmental load of SCCPs from waste

management activities. In that context, the following should be recognized:

(a) Compared to most other POPs, historical production and use of SCCPs are much

higher. Therefore, also the amount of waste can be expected to be high. However, as the use started

already in the 1930s and hazardous waste management capacity and practices were not developed

until 1970s, it can be assumed that a large amount of wastes containing SCCPs have already been

disposed of;

UNEP/CHW.14/INF/9

94

(b) Many applications of SCCPs have long service-lives (for example conveyor belts,

cooling oils, sealants, paints, adhesives and floorings used in construction sector). European

Commission (2011) cites service-life of a conveyor belt at 2-30 years. Therefore, waste originating

from currently prohibited uses can still be found. On the other hand, metal and leather processing

fluids and also the treated leather products have relatively short product life cycles. It can therefore

be assumed that the used processing fluids, as well as the treated leather products will soon be

disposed of after prohibition (German Federal Environment Agency, 2015);

(c) SCCPs have been used worldwide as a fire retardant or plasticiser in materials, such as

plastics (PVC and EVA), rubbers, fabrics, inks, paints, adhesives and surface coatings and leather,

that are used to produce e.g. equipment, pipes, apparel, clothing, footwear, and accessories. SCCPs

have been found in construction waste and consumer articles in levels of up to 7 000 mg/kg;

(d) SCCPs may be released from products and articles during the service life as well as

after their disposal, unless properly managed. European Commission (2011) assumes that about 8 %

of the SCCPs in sealants is emitted during lifetime. Also landfill leachates and sludges from waste

water treatment contain SCCPs (Danish Environmental Protection Agency, 2014);

(e) There is recent evidence on consumer products (toys, sports accessories, electric

cables of kitchen equipment) containing several thousands of mg/kg SCCPs which are commonly

found on the EU market (KEMI, 2016, BTHA, 2016, see Annex II). It is not possible to identify the

SCCP-containing consumer products without laboratory analysis and there are considerable

uncertainties related to analyses;

(f) Second major use is as an additive in metal-working and machining lubricants and

coolants. In regions where this use has ended due to prohibitions, and there is likely not much waste

containing SCCPs being generated, except where longer chain chlorinated paraffins contain SCCPs;

(g) Many materials containing SCCPs have been recycled or reused (e.g. plastics, rubber

and textiles, building joint sealants). Elevated SCCP concentrations have been found in biota near

an e-waste recycling site in China (Luo et al., 2017, Yuan et al., 2017). Conveyor belts have been

recycled by reduction to powder and subsequent manufacture of new belts, curtains, mats and

building materials (European Commission, 2011);

(h) Use of MCCPs may lead to high concentrations of SCCPs in the products and articles

(the EU limit for unintentional trace contamination was set at 1 500 mg/kg in articles to allow for

continued use of MCCPs). MCCPs containing up to 1% by weight SCCPs,134 are commonly used as

alternatives to SCCPs. Also, possible recycling of metal-working oils may have led to SCCPs being

present in unintended applications.

32. Wastes may contain variable concentrations of SCCPs, depending on the quantities in which

they were originally present in specific products and the quantities released during product use and

waste management. Waste consisting of, containing or contaminated with SCCPS (hereinafter

referred to as “SCCP wastes”) may be found as:

(a) SCCP chemicals:

(i) Pure SCCPs;

(ii) Technical CPs mixtures containing varying levels of SCCPs depending on the

starting material;

(iii) Obsolete SCCPs which can no longer be used;

(b) Packaging materials of SCCP formulations;

(c) Preparations and articles which have been produced using SCCPs:

(i) Metal working lubricants and coolants, swarf from metal cutting

operations;

(ii) Lubricants, in particular for automobile engines, electric generators,

wind power facilities;

(iii) Lubricants in oil production and refining: oil drilling and gas

134 According to the European chlor-alkali industry association Eurochlor, the short carbon chain constituents in

MCCPs are not likely SCCPs as defined in REACH Regulation and the detection of chains below C14 in an

MCCP product does not mean that the product contains SCCPs (http://www.eurochlor.org/chlorinated-

alkanes-(casg)/education-spotlight.aspx, accessed 3 December, 2017).

UNEP/CHW.14/INF/9

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exploration, petroleum refining to produce diesel oil;

(iv) Dried sludges from user process such as paper coating;

(v) Flexible polyvinylchloride (PVC) and ethylene-vinyl acetate (EVA);

(vi) Paints, adhesives, floorings and coatings;

(vii) Sealants, such as fire retardant dam sealants, building sealants, window

sealants;

(viii) Fire-retardant rubber, such as in transmission and conveyor belts;

(ix) Fire-retardant back-coated textiles, such as upholstery, tents;

(x) Leather that has been fat-liquored with SCCPs;

(xi) Other articles made of rubber or soft plastics, i.a. toys, sports

accessories and kitchen equipment;

(d) Contaminated soils;

(e) Municipal and industrial sludge (e.g. leather industry) and landfill leachate.

33. The most important SCCP waste streams in terms of potential volume are expected to be:

(a) PVC and EVA plastics in flooring, wall covering, wire and cable insulation;

(b) Construction waste contaminated with SCCPs in paints, sealants, adhesives and

flooring;

(c) Metal working lubricants and coolants;

(d) Lubricants and coolants in oil and gas exploration and drilling;

(e) Back-coated textiles, including upholstery;

(f) Transmission belts and conveyor belts.

34. The most important SCCP waste streams in terms of potential releases or concentration of

SCCPs are expected to be:

(a) SCCP formulations;

(b) PVC and other plastics with SCCPs as plasticizer;

(c) Rubber containing SCCPs;

(d) Lubricants and coolants in oil and gas exploration and drilling;

(e) Oily waste from metal working;

(f) Paints, adhesives and coatings;

(g) Plasticiser condensates;

(h) Water based mixtures and emulsions;

(i) Consumer articles made of plastics and rubber containing SCCPs;

(j) Leather and textiles.

35. SCCP wastes can be generated in a diverse range of applications, at different stages of life

cycle and through different release media. Knowledge of release media guides the analysis and

choice of methods that may be used to manage such wastes. Table 3 provides an overview of

relevant information regarding the life cycle of wastes containing SCCP. In Europe and North

America some of the applications are believed to have ceased decades ago but may be such

materials could still be in use or disposed of.

Table 3: Overview of the production and application of SCCPs and their release media into the

environment (based on UNEP/POPS/POPRC.11/10/Add.2, ECB, 2000, ECB, 2008, KEMI, 2016).

UNEP/CHW.14/INF/9

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Group Source materials

/Substance used

Applications

/Processes

End product Release media

SCCPs PRODUCTION

Ch

em

ical

prod

ucti

on

Chlorinated

alkanes C10-C13,

chlorine

Chemical synthesis SCCPs • Solid waste

(including filtration

sludge)

• Landfill leachate

• Waste water

• Sludge

• Air Chlorinated

alkanes C14-C17,

chlorine

Chemical synthesis MCCPs, with up to 1% SCCPs

as impurity

PRODUCTION OF FORMULATIONS AND ARTICLES USING SCCP

(The boxes below include articles that have become wastes. Such wastes may also be generated at production sites, such as

leftovers, cutting waste, etc.)

Poly

vin

ylc

hlo

rid

e (

PV

C)

pro

du

ctio

n

SCCPs, MCCPs Production of flexible

PVC products

Flooring, wall covering,

upholstery and insulation of

wire and cables, consumer

articles (such as toys, yoga

mats, game controllers, water

heaters), cable, footwear,

hosing, conveyor belting,

coated fabric and profiles

• Solid waste

• Construction

waste

• WEEE

• Landfill leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

Ru

bb

er p

rod

ucti

on

SCCPs Rubber production Conveyor belts, shoe soles,

industrial sheeting • Solid waste

• Construction

waste

• Liquid industrial

waste

• Landfill leachate

• Wastewater

• Sludge

• Air

Met

al-

work

ing

flu

ids SCCPs Metal-working fluid

production and use

Lubricants and coolants in

machining, e.g. automobile

industry, precision engineering

industry and in machinery

construction

• Solid waste

(swarf from metal-

working)

• Landfill leachate

• Liquid industrial

waste

• Wastewater

• Sludge

• Air

Lea

ther

SCCPs Fat-liquoring of leather Leather • Solid waste

• Landfill leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

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II. Relevant provisions of the Basel and Stockholm Conventions

A. Basel Convention

36. Article 1 (“Scope of the Convention”) defines the waste types subject to the Basel

Convention. Subparagraph 1 (a) of that Article sets forth a two-step process for determining if a

“waste” is a “hazardous waste” subject to the Convention. First, the waste must belong to any

category contained in Annex I of the Convention (“Categories of wastes to be controlled”). Second,

the waste must possess at least one of the characteristics listed in Annex III of the Convention (“List

of hazardous characteristics”).

37. Annex I and II lists some of the wastes which may consist of, contain or be contaminated

with SCCPs:

(a) Y6: Wastes from the production, formulation and use of organic solvents;

(b) Y9: Waste oils/water, hydrocarbons/water mixtures, emulsions;

(c) Y12: Wastes from production, formulation and use of inks, dyes, pigments, paints,

lacquers, varnish;

(d) Y13: Wastes from production, formulation and use of resins, latex, plasticizers,

Tex

tile

s a

nd

fa

bri

c SCCPs,

polyester-cotton,

cotton or linen-flax

Production of

waterproof and fire-

retardant textiles and

fabric

Tents, camouflage nets,

professional clothing

• Solid waste

• Landfill leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

Ad

hesi

ves

an

d s

eala

nts

SCCPs Adhesive production,

building and

construction sealant

production

Polysulphide, polyurethane,

acrylic and butyl sealants used

in building and construction

and in sealants for double and

triple glazed windows

• Solid waste

• Construction

waste

• Liquid industrial

and household

waste

• Landfill leachate

• Wastewater

• Sludge

• Air

Pain

ts

SCCPs Paint production Road marking paint • Solid waste

• Liquid industrial

and household

waste

• Landfill leachate

• Wastewater

• Sludge

• Air

Pap

er c

oa

tin

g

SCCPs Paper production Carbonless copy paper • dried sludges

from paper coating

• Solid waste

• Liquid industrial

and household

waste

• Landfill leachate

• Wastewater

• Sludge

• Air

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glues/adhesives;

(e) Y18: Residues arising from industrial waste disposal operations;

(f) Y45: Organohalogen compounds other than substances referred to in this Annex I

(e.g., Y39, Y41, Y42, Y43, Y44);

(g) Y46: Wastes collected from households.

38. Annex I wastes are presumed to exhibit one or more Annex III hazard characteristics, which

may include H11 “Toxic (Delayed or chronic)”; H12 “Ecotoxic”; or H13 “Capable, by any means,

after disposal, of yielding another material, e.g. leachate, which possesses any of the characteristics

listed above”, unless, through “national tests,” they can be shown not to exhibit these characteristics.

National tests may be useful for identifying a particular hazardous characteristic in Annex III of the

Convention until such time as the hazardous characteristic is fully defined. Guidance documents for

Annex III hazardous characteristics H11, H12 and H13 were adopted on an interim basis by the

Conference of the Parties to the Basel Convention at its sixth and seventh meetings.

39. List A of Annex VIII of the Convention describes wastes that are “characterized as hazardous

under Article 1, paragraph 1 (a), of this Convention.” However, “their designation of a waste on this

Annex does not preclude, in a particular case, the use of Annex III (“List of hazardous

characteristics”) to demonstrate that a waste is not hazardous” (Annex I, paragraph (b)). List A of

Annex VIII includes a number of wastes or waste categories that have the potential to contain or be

contaminated with SCCP, including:

(a) A1090: Ashes from the incineration of insulated copper wire;

(b) A1100: Dusts and residues from gas cleaning systems of copper smelters;

(c) A1190: Waste metal cables coated or insulated with plastics containing or

contaminated with coal tar, PCB, lead, cadmium, other organohalogen compounds or other Annex I

constituents to an extent that they exhibit Annex III characteristics;

(d) A3040: Waste thermal (heat transfer) fluids;

(e) A3050: Wastes from production, formulation and use of resins, latex, plasticizers,

glues/adhesives excluding such wastes specified on list B (note the related entry on list B B4020);

(f) A3110: Fellmongery wastes containing hexavalent chromium compounds or biocides

or infectious substances (note the related entry on list B B3110);

(g) A3120: Fluff-light fraction from shredding;

(h) A4060: Waste oils/water, hydrocarbons/water mixtures, emulsions;

(i) A4070: Wastes from the production, formulation and use of inks, dyes, pigments,

paints, lacquers, varnish excluding any such wastes specified on list B (note the related entry on list

B B4010);

(j) A4130: Waste packages and containers containing Annex I substances in

concentration sufficient to exhibit Annex III hazard characteristic);

(k) A4140: Waste consisting of or containing off specification or outdated chemicals

corresponding to Annex I categories and exhibiting Annex III hazard characteristics;

(l) A4160: Spent activated carbon not included on list B (note the related entry on list B

B2060).

40. List B of Annex IX lists wastes that will not be wastes covered by Article 1, paragraph 1 (a),

unless they contain Annex I material to an extent causing them to exhibit an Annex III characteristic.

List B of Annex IX includes a number of wastes or waste categories that have the potential to

contain or be contaminated with SCCP, including:

(a) B1110 Electrical and electronic assemblies;135

(b) B3010: Solid plastic waste;136

(c) B3020: Paper, paperboard and paper product wastes;137

135 Refer to Annex IX of the Basel Convention for a full description of this entry. 136 Ibid 6. 137 Ibid 6.

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(d) B3030: Textile waste;138

(e) B3035: Waste textile floor coverings, carpets;

(f) B3080: Waste parings and scrap of rubber;

(g) B3090: Paring and other wastes of leather or of composition leather not suitable for

the manufacture of leather articles, excluding leather sludges, not containing hexavalent chromium

compounds and biocides (note the related entry on list A A3100);

(h) B3100: Leather dust, ash, sludges or flours not containing hexavalent chromium

compounds or biocides (note the related entry on list A A3090);

(i) B3110: Fellmongery wastes not containing hexavalent chromium compounds or

biocides or infectious substances (note the related entry on list A A3110);

(j) B4010: Wastes consisting mainly of water-based/latex paints, inks and hardened

varnishes not containing organic solvents, heavy metals or biocides to an extent to render them

hazardous (note the related entry on list A A4070);

(k) B4020: Wastes from production, formulation and use of resins, latex, plasticizers,

glues/adhesives.139

41. For further information, see section II.A of the General technical guidelines.

B. Stockholm Convention

42. The present guidelines cover intentionally-produced SCCP, whose production and use are to

be eliminated in accordance with Article 3 and part I of Annex A to the Stockholm Convention.

43. Annex A defines SCCPs as follows:

“Short-chain chlorinated paraffins (Alkanes, C10-13, chloro) +: straight-chain chlorinated

hydrocarbons with chain lengths ranging from C10 to C13 and a content of chlorine greater

than 48 per cent by weight”.

44. In addition, examples have been added in Annex A as follows:

“For example, the substances with the following CAS numbers may contain short-chain

chlorinated paraffins:

CAS No. 85535-84-8;

CAS No. 68920-70-7;

CAS No. 71011-12-6;

CAS No. 85536-22-7;

CAS No. 85681-73-8;

CAS No. 108171-26-2”

45. Production of SCCPs is allowed for Parties who have notified the Secretariat of their

intention to produce them for the time-limited specific exemptions listed in Annex A to the

Convention for which Parties may continue using SCCPs:

(a) Additives in the production of transmission belts in the natural and synthetic rubber

industry;

(b) Spare parts for rubber conveyor belts in the mining and forestry industries;

(c) Leather industry, in particular fat liquoring in leather;

(d) Lubricant additives, in particular for automobile engines, electric generators, wind

power facilities, drilling in oil and gas exploration and petroleum refining to produce diesel oil;

(e) Tubes for outdoor decoration bulbs;

(f) Waterproofing and fire-retardant paints;

(g) Adhesives;

(h) Metal processing;

138 Ibid 6. 139 Ibid 6.

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(i) Secondary plasticizers in flexible polyvinyl chloride, except in toys and children’s

products.

46. Furthermore, Annex A specifies in Note (vii) that quantities of SCCPs that occur in mixtures

at concentrations greater than or equal to 1 per cent by weight, cannot be considered unintentional

trace contaminants, as outlined for other chemicals in Note (i). This is flagged by a plus sign (“+”) in

the definition (see paragraph 44 above).

47. Further information on the register of specific exemptions for SCCPs is available from:

www.pops.int.

48. For further information, see section II.B of the General technical guidelines.

III. Issues under the Stockholm Convention to be addressed

cooperatively with the Basel Convention

A. Low POP content

49. The provisional definition of low POP content for SCCPs is [100] [10 000] mg/kg.140

50. The low POP content described in the Stockholm Convention is independent from the

provisions on hazardous waste under the Basel Convention.

51. Wastes with a content of SCCPs at or above [100] [10 000] mg/kg must be disposed of in

such a way that the POP content is destroyed or irreversibly transformed in accordance with the

methods described in subsection IV.G.2. Otherwise, they may be disposed of in an environmentally

sound manner when destruction or irreversible transformation does not represent the

environmentally preferable option in accordance with the methods described in subsection IV.G.3.

52. Wastes with a content of SCCPs below [100] [10 000] mg/kg should be disposed of in

accordance with the methods referred to in subsection IV.G.4 of the General technical guidelines

(outlining disposal methods when POP content is low), taking into account section IV.I.1 below

(pertinent to higher-risk situations).

53. For further information on low POP content, refer to section III.A of the General technical

guidelines.

B. Levels of destruction and irreversible transformation

54. For the provisional definition of levels of destruction and irreversible transformation, see

section III.B of the General technical guidelines.

C. Methods that constitute environmentally sound disposal

55. See section IV.G below and section IV.G of the General technical guidelines.

IV. Guidance on environmentally sound management (ESM)

A. General considerations

56. For further information, see section IV.A of the General technical guidelines.

B. Legislative and regulatory framework

57. Parties to the Basel and Stockholm Conventions should examine their national strategies,

policies, controls, standards and procedures to ensure that they are in agreement with the two

conventions and their obligations under them, including those that pertain to ESM of SCCP wastes.

58. Elements of a regulatory framework applicable to SCCPs should include measures to prevent

the generation of wastes and to ensure the ESM of generated wastes. Such elements could include:

(a) Environmental protection legislation establishing a regulatory regime, setting release

limits and establishing environmental quality criteria;

(b) Prohibitions on the production, sale, use, import and export of SCCPs, except in the

140 Determined according to national or international methods and standards.

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case of Parties that have notified the Secretariat of their intention to use or produce SCCPs in

accordance with the time-limited specific exemption listed in Annex A to the Stockholm

Convention;

(c) A requirement that best available technologies (BAT) and best environmental practices

(BEP) be employed in the production and use of SCCPs, in cases where Parties have notified the

Secretariat of their intention to use or produce SCCPs in accordance with the time-limited

exemption listed in Annex A to the Stockholm Convention;

(d) Measures to ensure that SCCP wastes cannot be disposed of in ways that that may lead

to recovery, recycling, reclamation, direct reuse or alternative uses other than those exempted in

Annex A to the Stockholm Convention;

(e) Adequate ESM controls to separate materials containing SCCPs from materials that

can be recycled (e.g., plastics, oils, rubber, construction materials);

(f) Transportation requirements for hazardous materials and waste;

(g) Specifications for containers, equipment, bulk containers and storage sites for obsolete

unused SCCP;

(h) Specification of acceptable analytical and sampling methods for SCCPs;

(i) Requirements for waste management and disposal facilities;

(j) Definitions of hazardous waste and conditions and criteria for the identification and

classification of SCCP wastes as hazardous wastes;

(k) A general requirement for public notification and review of proposed government

waste-related regulations, policies, certificates of approval, licences, inventory information and

national releases and emissions data;

(l) Requirements for identification, assessment and remediation of contaminated sites;

(m) Requirements concerning the health and safety of workers;

(n) Legislative measures on, e.g., waste prevention and minimization, inventory

development and emergency response.

59. For further information, see section IV.B of the General technical guidelines.

C. Waste prevention and minimization

60. Both the Basel and Stockholm conventions advocate waste prevention and minimization. The

production and use of SCCPs is to be eliminated under the Stockholm Convention, unless they fall

under the exemptions listed in part I of Annex A to the Convention.

61. Quantities of waste containing SCCPs should be minimized through isolation and separation

of those wastes from other wastes at source in order to prevent their mixing with, and contamination

of, other waste streams.

62. The mixing and blending of wastes with SCCPs content at or above [10 000] mg/kg with

other materials solely for the purpose of generating a mixture with an SCCPs content below [10 000]

mg/kg are not environmentally sound. Nevertheless, the mixing or blending of materials as a pre-

treatment method may be necessary in order to enable treatment or to optimize treatment efficiency.

63. For further information, see section IV.C on waste prevention and minimization of the

General technical guidelines.

D. Identification of wastes

64. Article 6, paragraph 1 (a), of the Stockholm Convention requires each party to, inter alia,

develop appropriate strategies for the identification of products and articles in use and wastes

consisting of, containing or contaminated with POPs. The identification of wastes containing SCCPs

is the starting point for their effective ESM.

65. For general information on identification and inventories, see section IV.D of the General

technical guidelines.

1. Identification

66. SCCP wastes can be found:

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(a) In residues from SCCPs production and at sites where such chemicals were produced,

formulated and stored;

(b) In storage facilities and at sites where SCCPs were used or applied, e.g., at PVC, EVA

and rubber production facilities, construction material production, construction sites, metal-working,

paint, fabric, textile and leather production;

(c) In contaminated materials, including protective clothing, application equipment and

accessories, empty packaging materials, containers, floors, walls and windows;

(d) In facilities for the collection, recycling and waste management of PVC and other

plastics, textiles, rubber, construction materials, metal-working oils, etc;

(e) In soils, sediments and sewage sludges and in water that has been contaminated by, for

example, spills;

(f) In retail of products containing SCCPs, such as products and articles made of flexible

PVC (cable, footwear, hosing, conveyor belts, coated fabric and profiles), paints, sealants and

adhesives, construction materials;

(g) At dumpsites and in landfills.

67. It should be noted that even experienced technical personnel may not be able to determine the

nature of an effluent, substance, container or piece of equipment by its appearance or markings.

Consequently, Parties may find the information on production, use and types of waste provided in

section I.B of the present guidelines useful in identifying articles and mixtures containing SCCPs.

2. Inventories

68. When developing inventories on SCCP wastes, it is important to consider the service lives of

articles where they have been used and the timing of their placement on the market in relation to

restrictions.

69. The main uses of SCCPs differ from region to region as well as their timing. In several

countries, many historical applications of SCCP have ceased already due to national restrictions or

introduction of alternatives. Therefore, a thorough consideration of potential uses is important to

focus the inventory activities correctly, noting that it may be difficult to estimate whether SCCPs is

present in imported commercial products.

70. Although estimating SCCP waste volumes is difficult due to variety of uses, long service

lives and long history, a few good approaches have been made in the European Union, for example

in Denmark and Germany (European Commission, 2011, Danish Environmental Protection Agency,

2014, German Federal Environment Agency, 2015).

E. Sampling, analysis and monitoring

71. For general information on sampling, analysis and monitoring, see section IV.E of the

General technical guidelines.

72. Sampling, analysis and monitoring procedures, should be established for articles that may

contain SCCPs.

1. Sampling

73. Sampling serves as an important element for identifying and monitoring environmental

concerns and human health risks.

74. Standard sampling procedures should be established and agreed upon before the start of the

sampling campaign. Sampling should comply with specific national legislation, where it exists, or

with international regulations and standards.

75. Types of matrices that are typically sampled for include:

(a) Liquids:

(i) SCCP formulations;

(ii) Oil- and water-based liquids: metal-working fluids, cooking oil;

(iii) Leachates from landfills, water;

(iv) Biological fluids (blood, maternal milk);

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(b) Solids:

(i) Production wastes;

(ii) Biological tissue samples;

(iii) Soils, sediments and municipal and industrial sludges;

(iv) Materials where SCCPs have been used: e.g. PVC, plastic products, rubber,

construction products, paints, textiles, leather, conveyor belts;

(v) Indoor dust.

2. Analysis

76. Analysis refers to the extraction, purification, separation, identification, quantification and

reporting of SCCPs in the matrix of interest. In order to obtain meaningful and acceptable results,

analytical laboratories should have the necessary infrastructure (housing) and proven experience.

77. The development and dissemination of reliable analytical methods and the accumulation of

high-quality analytical data are important to understand the environmental impact of hazardous

chemicals, including POPs. In addition, they are needed to determine whether the waste is classified

hazardous.

78. Analysis of SCCPs is extremely difficult because of the poor description of the reference

materials and their complex compositions with thousands of isomers and homologues (Koh et al,

2002, Bayen et al., 2006, Gao et al., 2016).

79. No fully validated routine analytical method is available yet and only semi-quantitative

analysis is possible (van Mourik et al. 2015). The results from all the methods used are dependent to

some extent on the substance(s) used as reference (ECB, 2000, Bayen et al., 2006). CP

manufacturers (Eurochlor, 2017) list several difficulties related to quantification of CPs, thus

including SCCPs:

(a) It is not currently possible to accurately quantify individual CA components;

(b) State-of-the-art CA analysis techniques can qualitatively identify groups of CA

isomers by carbon chain length and chlorination level, although this remains difficult;

(c) Instrument detector response is affected by both chlorine content and distribution of

chlorine atoms on the carbon chain;

(d) Reference substances matching commercial products are currently unavailable. These

are necessary for more accurate individual congener quantification;

80. In the absence of more complete characterizations of the mixtures and suitable individual

standards, quantification is usually based on a technical product, introducing major uncertainties if

compositions of the sample and the standard do not match (Bayen et al. 2006,

UNEP/POPS/POPRC.11/10/Add.2, Vorkamp & Riget 2014).

81. Detection limits for SCCPs are higher than for most other POPs. The European Commission

(2011) concluded that a detection limit of 10 mg/kg would be realistically achievable in relevant

waste matrices. German Federal Environment Agency (2015) reported detection limit of 1 mg/kg in

the waste materials studied. The German Federal Environment Agency (2015) also reported price

for analysis at 190-370 EUR/sample.

82. Three International Standards Organization (ISO) methods address the standardized analyses

of SCCPs in water, sediment, sewage sludge, suspended matter and leather. A new standard for

analysis of SCCPs in textiles is under development. The methods are:

ISO 12010:2012

Determination of the sum of SCCPs in unfiltered surface water, ground water, drinking water

and wastewater using gas chromatography-mass spectrometry with electron capture negative

ionization (GC-ECNI-MS)

ISO 18635:2016

Water quality -- Determination of short-chain polychlorinated alkanes (SCCPs) in sediment,

sewage sludge and suspended (particulate) matter -- Method using gas chromatography-mass

spectrometry (GC-MS) and electron capture negative ionization (ECNI)

ISO 18219:2015

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Chromatographic method to determine the amount of SCCPs in processed and un-processed

leathers.

ISO/NP 22818 (under development)

Textiles- Determination of SCCP and MCCP in textile products out of different matrices by

use of GC-ECNI-MS

83. The most advanced technique in CPs, which includes SCCPs, detection is 2-dimensional gas

chromatography combined with electron capture detection. The method is able to qualitatively

identify groups of CP isomers by carbon chain length and chlorination level. Currently, the most

commonly used method of detection and quantification used in the literature is gas chromatography

followed by either high or low resolution electron capture negative ion mass spectrometry

(GC/ECNI-MS) (UNEP/POPS/POPRC.11/10/Add.2, Wang et al, 2013).

84. While GC/ECNI-MS remains the most commonly applied technique, novel and promising

use of high resolution time of flight Mass Spectrometry (TOF-MS) has also been reported (van

Mourik et al. 2015). In addition, improved cleanup procedures have been found to remove

interfering compounds, and new instrumental techniques, which distinguish between MCCPs and

SCCPs, have been developed. The study also states that new CP quantification methods have

emerged, including the use of mathematical algorithms, multiple linear regression and principal

component analysis. Gao et al. (2016) developed a novel analytical method, deuterodechlorination

combined with high resolution gas chromatography – high resolution mass spectrometry (HRGC-

HRMS), to determine the congener compositions of SCCPs in commercial chlorinated paraffins and

environmental and biota samples. Internal standard quantification of individual SCCP congeners

was achieved, and the relative standard deviations for quantification of total SCCPs were within

10% (Gao et al. 2016).

85. For more information on analytical methods, see Bayen et al, 2016.

3. Monitoring

86. Monitoring and surveillance serve as means for identifying and tracking environmental

concerns and human health risks. Information collected from monitoring programmes feeds into

science-based decision-making processes and is used for the evaluation of the effectiveness of risk

management measures, including regulations.

87. Monitoring programmes should be implemented in facilities producing and/or using SCCP as

well as wastes containing SCCP.

F. Handling, collection, packaging, labelling, transportation and storage

88. For general information on handling, collection, packaging, labelling, transportation and

storage, see section IV.F of the General technical guidelines.

89. In cases where SCCP wastes are considered hazardous wastes, they should be handled,

collected, packaged, labelled, transported and stored as such in accordance with applicable

provisions of national legislation. Individuals involved in the handling, collection, packaging,

labelling, transportation and storage of hazardous waste should receive proper training.

90. In cases where waste containing SCCPs was a constituent of a product or article (e.g.,

textiles, leather, PVC plastic item), specific handling, collection, packaging, labelling, transportation

and storage considerations may not be required; such waste should be handled, collected, packaged,

labelled, transported and stored in accordance with the environmentally sound management

provisions of national legislation for that type of waste.

1. Handling

91. The main concerns when handling SCCP wastes are human exposure, accidental releases to

the environment and contamination of other waste streams with SCCPs. SCCP wastes should be

handled separately from other waste types in order to prevent contamination of other waste streams.

92. When conducting repairs in or renovation or demolition of buildings, renovators and

contractors should pay attention to the possibility of SCCPs being contained in sealants, paints,

coatings, flooring, double-glazed windows, upholstery and textiles. Should these materials contain

SCCPs, they should be carefully removed and isolated to prevent dust from spreading to surrounding

areas. SCCPs may also be present in electronic and electric appliances, such as in WEEE recycling.

The work should be conducted wearing appropriate protective equipment such as suitable gloves,

disposable coveralls, protective goggles and respiratory protection masks that meet international

standards.

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93. Organizations handling waste containing SCCPs should have in place a set of procedures for

handling such wastes and workers should be trained in such procedures.

2. Collection

94. Collection arrangements that include depots for SCCP wastes should provide for the

separation of SCCP wastes from other wastes. In case the country has existing arrangement for

separate collection of PVC plastics, these may also receive SCCP wastes. Some of SCCP wastes,

however, may be difficult to identify as containing SCCPs.

95. Collections depots should not become long-term storage facilities for SCCP wastes.

3. Packaging

96. In cases where SCCP wastes are considered hazardous wastes they should be properly

packaged in accordance with the applicable provisions of national legislation.

97. SCCP wastes should be placed into leak-proof, sealed drums, where appropriate after

draining.

4. Labelling

98. In cases where SCCP wastes are considered hazardous wastes, every container should be

clearly labelled with a hazard warning label and a label providing details of the container and a

unique serial number. Such details should include container contents (e.g., exact counts of

equipment, volume, weight, type of waste carried), the name of the site from which the waste

originated so as to allow its traceability, the date of any repackaging and the name and telephone

number of the person responsible for the repackaging operation.

5. Transportation

99. In cases where SCCP wastes are considered hazardous wastes, they should be transported in

accordance with applicable provisions of national legislation.

6. Storage

100. SCCP wastes should be stored in designated sites and appropriate measures should be taken

to prevent the scattering, release and underground seepage of SCCPs, and to control the spread of

odors.

101. Appropriate measures, such as the installation of partitions, should be taken to avoid

contamination of other materials and wastes with SCCPs.

102. Storage areas for SCCP wastes should have adequate access roads for vehicles.

103. SCCP wastes in storage should be protected from fire.

G. Environmentally sound disposal

1. Pre-treatment

104. SCCPs are poorly water soluble, and water-based liquid mixtures or emulsions containing

liquid SCCPs principally from metal forming/deforming but also including used leather textile

treatment liquors, should be processed to remove oil and SCCP before being discharged. Eurochlor

(2016) lists three techniques: chemical splitting, aqueous evaporation and ultrafiltration. Recovery

treatments are strongly recommended by the manufacturers (European Commission, 2008).

105. Liquid SCCPs can also be adsorbed onto solids for further treatment (Eurochlor, 2016).

106. Swarf contaminated with SCCPs from metal cutting operations can be degreased and

separated from solvent or incinerated/re-smelted (Eurochlor, 2016).

107. For further information, see subsection IV.G.1 of the General technical guidelines.

2. Destruction and irreversible transformation methods

108. For further information, see subsection IV.G.2 of the General technical guidelines.

3. Other disposal methods when destruction or irreversible transformation is not the

environmentally preferable option

109. For information, see subsection IV.G.3 of the General technical guidelines.

4. Other disposal methods when the POP content is low

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110. For information, see subsection IV.G.4 of the General technical guidelines.

H. Remediation of contaminated sites

111. Soil contamination can take place over a long period of operation by accumulation and also

from spills events. Application of sewage sludge to soil or irrigation by wastewater may be a source

of SCCP loadings to soil (Zeng et al. 2011, 2012, UNEP/POPS/POPRC.11/10/Add.2).

112. For information, see section IV.H of the General technical guidelines.

I. Health and safety

113. For information, see section IV.I of the General technical guidelines.

1. Higher-risk situations

114. For general information, see subsection IV.I.1 of the General technical guidelines.

115. Higher-risk situations occur at sites where high concentrations or high volumes of SCCP

wastes are found and a high potential for exposure of workers or the general population exists.141

Direct dermal exposure to and inhalation of fine dust or particles containing SCCP in the workplace

or home are of particular concern. Exposure to vapour is generally considered insignificant due to

the low vapour pressures involved. However, there is a potential for significant inhalation exposure

to SCCPs during the formulation of hot melt adhesives and in the use of metal working fluids. Local

exhaust ventilation can be used to control inhalation exposure in the hot melt adhesive

manufacturing sector. In the metal working sector, inhalation exposure to mists/aerosols of metal

working fluids can be controlled by using anti-mist additives in the formulation and by enclosing the

workpiece using splash guards (ECB, 2000)

116. While articles containing SCCPs are not documented to exhibit specific risks to the

environment and human health during their handling, collection, transportation and storage, it is

important to bear in mind that large quantities of such wastes, even if properly stored, are more

likely to present risks than smaller quantities scattered over large areas.

117. Higher-risk situations specific to SCCPs may occur:

(a) At sites where SCCPs are produced or used due to spills, facility wash-down and

storm water runoff (Environment Canada, 2008);

(b) At sites where recycling of plastics containing SCCPs takes place. Polymer-

incorporated CPs could be released during recycling of plastics, which may involve processes such

as chopping, grinding and washing (Environment Canada, 2008);

(c) At sites where metal-working/cutting fluids containing SCCPs are used. They may

also be released into aquatic environments from drum disposal, carry-off and spent bath use (ECB,

2000, European Commission, 2011, Environment Canada, 2008);

(d) At facilities using SCCPs for fat-liquoring of leather;

(e) When consumer products containing SCCPs are used.

2. Lower-risk situations

118. For information on lower-risk situations, see subsection IV.I.2 of the General technical

guidelines.

J. Emergency response

119. Emergency response plans should be in place at sites where SCCPs are produced (where

allowed), used, stored, transported or disposed of. Further information on emergency response plans

is given in section IV.J of the General technical guidelines.

K. Public participation

120. Parties to the Basel or Stockholm Convention should have open public participation

processes. For further information see section IV.K of the General technical guidelines.

141 For example, health impacts were identified for workers of organochlorine production facility in Brazil

(ACPO, 2004).

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Annex I to the technical guidelines

Synonyms and trade names of commercial formulations that contain

or may have contained SCCPs addressed by Stockholm Convention

on POPs

Synonyms for SCCPs:

Alkanes, chlorinated; alkanes (C10-C13), chloro (60%); alkanes (C10-C13), chloro (50-70%); chlorinated

alkanes; chlorinated alkanes, chlorinated paraffins; chloroalkanes; chlorocarbons; paraffin, chlorinated;

paraffins, chloro; paroils, chlorinated; polychlorinated alkanes; polychloroalkanes

The synonyms are general in nature.

Tradenames for CPs, potentially SCCPs

The following generic trade names are usually accompanied by a suffix indicating a specific product

(IARC, 1990): A 70; A 70 (wax); Adekacizer E; Arubren; Cereclor; Chlorinated paraffins (CPs);

Chlorcosane; Chlorez; Chlorofin; Chloroflo; Chlorparaffin; Chlorowax, Chlorowax 500AO; Chlorowax

45AO, Chlorowax 52AO; Cloparin; Cloparol; Clorafin; CP F; CW; Diablo; Derminolfett; Derminolöl;

EDC-tar; Electrofine; Enpara; FL X; Hordaflam; Hordaflex; Hordalub; Hulz; KhP; Meflex; Monocizer;

Paroil; Poliks; Tenekil; Toyoparax; Unichlor.

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Annex III

Compilation of comments regarding document

UNEP/CHW.14/7/Add.3 (Technical guidelines on POP-BDEs)

The Secretariat received comments regarding document UNEP/CHW.14/7/Add.3 from: the European

Union and its Member States, the European Automobile Manufacturers' Association (ACEA) and the

Bromine Science Environmental Forum (BSEF). These comments are presented in the draft technical

guidelines themselves.

UNEP/CHW.14/INF/9

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Draft updated technical guidelines on the environmentally sound

management of wastes consisting of, containing or contaminated with

hexabromodiphenyl ether and heptabromodiphenyl ether, or

tetrabromodiphenyl ether and pentabromodiphenyl ether or

decabromodiphenyl ether

(Draft of October 2018)

General comments

The European Union and its Member States have a few editorial comments shown

highlighted in yellow.

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Contents

Abbreviations and acronyms .................................................................................................................... 111

Units of measurement ............................................................................................................................... 112

I. Introduction .................................................................................................................................... 113 A. Scope .................................................................................................................................. 113 B. Description, production, use and wastes .......................................................................... 113

1. Description ............................................................................................................. 113 2. Production .............................................................................................................. 114 3. Use .......................................................................................................................... 115 4. Wastes..................................................................................................................... 116

II. Relevant provisions of the Basel and Stockholm conventions ................................................... 120 A. Basel Convention ............................................................................................................... 120 B. Stockholm Convention ...................................................................................................... 123

III. Issues under the Stockholm Convention to be addressed cooperatively with the Basel

Convention ..................................................................................................................................... 125 A. Low POP content ............................................................................................................... 125 B. Levels of destruction and irreversible transformation..................................................... 125 C. Methods that constitute environmentally sound disposal ............................................... 125

IV. Guidance on environmentally sound management (ESM) ......................................................... 126 A. General considerations ...................................................................................................... 126 B. Legislative and regulatory framework ............................................................................. 126 C. Waste prevention and minimization ................................................................................. 127 D. Identification of wastes ..................................................................................................... 127

1. Identification .......................................................................................................... 127 2. Inventories .............................................................................................................. 128

E. Sampling, analysis and monitoring .................................................................................. 128 1. Sampling ................................................................................................................. 128 2. Analysis .................................................................................................................. 129 3. Monitoring .............................................................................................................. 130

F. Handling, collection, packaging, labelling, transportation and storage ......................... 130 1. Handling ................................................................................................................. 131 2. Collection ............................................................................................................... 131 3. Packaging ............................................................................................................... 131 4. Labelling ................................................................................................................. 131 5. Transportation ........................................................................................................ 131 6. Storage .................................................................................................................... 132

G. Environmentally sound disposal ....................................................................................... 132 1. Pre-treatment .......................................................................................................... 132 2. Destruction and irreversible transformation methods ......................................... 132 3. Other disposal methods when neither destruction nor irreversible transformation

is the environmentally preferable option .............................................................. 132 4. Other disposal methods when the POP content is low ........................................ 132

H. Remediation of contaminated sites ................................................................................... 133 I. Health and safety ............................................................................................................... 133

1. Higher-risk situations ............................................................................................ 133 2. Lower-risk situations ............................................................................................. 133

J. Emergency response .......................................................................................................... 133 K. Public participation ............................................................................................................ 133

Annex: Bibliography ................................................................................................................................. 134

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Abbreviations and acronyms

ABS acrylonitrile-butadiene-styrene

ATSDR Agency for Toxic Substances and Disease Registry

BAT best available technology

BDE brominated diphenyl ether

BDE-209 decabromodiphenyl ether congener 209

BEP best environmental practice

BFR brominated flame retardant

CAS Chemical Abstracts Service

CENELEC National Committees of the European Committee fFor Electrotechnical Standardization

C-decaBDE commercial decabromodiphenyl ether

C-octaBDE commercial octabromodiphenyl ether

C-pentaBDE commercial pentabromodiphenyl ether

decaBDECAS Chemical Abstracts Servicedecabromodiphenyl ether (BDE-209) present in c-decaBDE

EEE electrical and electronic equipment

ELV end-of-life vehicles

EPDM ethylene propylene diene monomer ESM Environmentally sound management

EVA ethylene, vinyl acetate

GC gas chromatography

HeptaBDE heptabromodiphenyl ether

HexaBDE hexabromodiphenyl ether and HeptaBDE heptabromodiphenyl ether

HIPS high-impact polystyrene

ILO International Labor Organization

ISO International Organization for Standardization MAC mobile air-conditioning

MS mass spectrometry

NIP National Implementation Plan

NonaBDE nonabrominated diphenyl ether

OECD Organisation for Economic Co-operation and Development

PA polyamide

PBDD polybrominated dibenzo-p-dioxin

PBDEs polybrominated diphenyl ethers

PBDF polybrominated dibenzofuran PBT polybutylene terephthalate

PBT Persistent, Bioaccumulative and Toxicx

PC polycarbonate

PCB polychlorinated biphenyl

PE polyethylen

PEE poly(ether ester)

PentaBDE pentabromodiphenyl ether

PET Ppolyethylene terephthalate POP persistent organic pollutant

POP-BDEs hexabromodiphenyl ether and heptabromodiphenyl ether, and tetrabromodiphenyl

ether and pentabromodiphenyl ether and decabromodiphenyl ether PP

polyamide polymers/propylene

PUR Polyurethane PBDF polybrominated dibenzofuran

PBT polybutyleneterephthalate

PCB polychlorinated biphenyl

POP persistent organic pollutant

PS polystyrol

PVC polyvinyl chloride

SPE solid phase extraction

TetraBDE tetrabromodiphenyl ether

UNEP United Nations Environment Programme

UPEW unsaturated polyester vPvB very persistent and very

bioaccumulative

UNEP

WEEE

WHO

United Nations Environment Programme

waste electrical and electronic

equipment

World Health Organization

WHO World Health Organization

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Units of measurement

mg/kg

milligram per kilogram. Corresponds to parts per million by mass.

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I. Introduction

A. Scope

1. This document supersedes the Technical guidelines for the environmentally sound

management of wastes consisting of, containing or contaminated with hexabromodiphenyl ether

and heptabromodiphenyl ether, or tetrabromodiphenyl ether and pentabromodiphenyl ether, of

May 2015.

1.2. The present guidelines provide guidance on the environmentally sound management

(ESM) of wastes consisting of, containing or contaminated with hexabromodiphenyl ether and

heptabromodiphenyl ether, or tetrabromodiphenyl ether and pentabromodiphenyl ether, or

decabromodiphenyl ether (i.e. “BDE-209”142) present in commercial decabromodiphenyl ether

(decaBDE), pursuant to several decisions of two multilateral environmental agreements on

chemicals and wastes.1143.

2.3. Hexabromodiphenyl ether (hexaBDE) and heptabromodiphenyl ether (heptaBDE), as

well as tetrabromodiphenyl ether (tetraBDE) and pentabromodiphenyl ether (pentaBDE), were

listed in Annex A to the Stockholm Convention in 2009, through an amendment that entered

into force in 2010. Decabromodiphenyl ether, defined as decabromodiphenyl ether (BDE-209)

present in commercial decabromodiphenyl ether, was listed in Annex A to the Stockholm

Convention in 2017 and the amendment will enter into force in 2018. In the present guidelines,

hexaBDE, heptaBDE, tetraBDE and, pentaBDE and decaBDE as a group are referred to as

“POP-BDEs”.” (for further specification see section II.B.).

3.4. The present guidelines should be used in conjunction with the General technical

guidelines on the environmentally sound management of wastes consisting of, containing or contaminated with persistent organic pollutants (UNEP, [20192017…, to be updated]) (UNEP, XXXX) (hereinafter referred to as “Ggeneral technical guidelines”). The Ggeneral technical

guidelines are intended to serve as an umbrella guide for the ESM of wastes consisting of,

containing or contaminated with persistent organic pollutants (POPs) and provide more detailed

information on the nature and incidence of wastes consisting of, containing or contaminated

with POP-BDEs for purposes of their identification and management.).

B. Description, production, use and wastes

1. Description

4.5. Brominated flame retardants (BFRs) are chemical substances used to reduce fire hazards

by interfering with the combustion of the polymer. Some BFRs, such as polybrominated

diphenyl ethers (PBDEs), are additives that do not chemically bind to plastics but are physically

combined with them and therefore may be easily released into the environment.

5.6. PBDEs have different atomic numbers and degrees of bromination ranging from one to

ten bromine atoms (figure 1). Lower brominated BDEs, such as tetraBDEs and pentaBDEs, are

seen as more dangerous than higher brominated BDEs (i.e., BDEs with more than 5 bromine

atoms per molecule, e.g., octaBDes and decaBDEs) because they bioaccumulate more

efficiently, are slightly more soluble in water and have a greater propensity for volatilization

and atmospheric transport than higher brominated BDEs.

Figure 1: Structure of PBDEs

142 Decabromodiphenyl ether congener 209

143 Decisions BC-11/3, BC-12/3, BC-13/4 and BC-14/… of the Conference of the Parties to the Basel Convention

on the Control of Transboundary Movements of Hazardous Wastes and Their Disposal; decisions OEWG-8/5,

OEWG-9/3, and OEWG-11/3 of the Open-ended Working Group of the Basel Convention; and decisions SC-

4/14, SC-4/18, SC-5/9, SC- 6/11 and SC-8/10 of the Conference of the Parties to the Stockholm Convention on

Persistent Organic Pollutants.

Formatted: Highlight

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6.7. PBDEs are industrial aromatic organobromine chemicals that make up a group

consisting of 209 congeners. The most common commercial formulations of PBDEs

(represented in table 1 below) are commercial octabromodiphenyl ether (c-octaBDE),

commercial pentabromodiphenyl ether (c-pentaBDE) and commercial decabromodiphenyl ether

(c-decaBDE).

7.8. C-octaBDE designates a commercial mixture that typically contains mainly hexaBDEs,

heptaBDEs, octaBDEs and nonabrominated diphenyl ethers (nonaBDEs). “Hexabromodiphenyl

ether and heptabromodiphenyl ether” means, according to Annex A, part III, to the Stockholm

Convention, BDE-153, BDE-154, BDE-175, BDE-183 and other hexa- and

heptabromodiphenyl ethers present incin c-octaBDE.

8.9. C-pentaBDE designates a commercial mixture that typically contains tetraBDEs,

pentaBDEs and hexaBDEs. “Tetrabromodiphenyl ether and pentabromodiphenyl ether” means,

according to Annex A, part III, to the Stockholm Convention, BDE-47, BDE-99 and other tetra-

and pentabromodiphenyl ethers present in c-pentaBDE.

10. There is some evidenceC-decaBDE designates a commercial mixture that higher

brominated BDEstypically contains mainly the congener BDE-209, with low levels of other

PBDE congeners such as nonaBDE ether and octaBDE (UNEP/POPS/POPRC.11/10/Add.1).

9.11. Components of the commercial penta-, octa- and decaBDE mixtures are persistent

organic pollutants according to Annex A to the Stockholm Convention. They have adverse

effects to human health and/ or the environment, are persistent, they bioaccumulate and undergo

long-range transport. Adverse effects are reported for numerous effects on human health and/ or

the environment. C-decaBDE with its main constituent decaBDE is also degradeddecaBDE can

break down to lower brominated congeners. These higherPBDEs including hexaBDE,

heptaBDE, tetraBDE and pentaBDE, with known PBT/ persistent, bioaccumulative, and toxic

persistent, bioaccumulative and toxic vPvB and POP properties which contribute in the outcome

of decaBDE toxicity. Due to debromination and historical reservoirs of c-penta- and c-octaBDE

congeners may therefore be precursors to the POP-BDEs that fall under the scope of the present

technical guidelines.in the environment, organisms are exposed to a complex mixture of PBDEs

that in combination pose a higher risk than BDE-209 alone (see

UNEP/POPS/POPRC.10/10/Add.2).

Table 1: Typical composition of PBDE commercial mixtures (Environment Canada, 2013)

Commercial

Mixtures

PBDE congener groups and concentrations of active ingredient

tetraBDE pentaBDE hexaBDE heptaBDE octaBDE nonaBDE decaBDE

BDE-47,

etc.

BDE-99,

etc. BDE-153,

BDE-

154,

etc.

BDE-175,

BDE-

183,

etc.

BDE-

203,BDE

-204, etc.

BDE-

207,BDE-

208

BDE-209

c-pentaBDE 24 – 38% 50 – 62% 4 – 12% Trace - - -

c-octaBDE - 0.5% 12% 45% 33% 10% 0.7%

c-decaBDE - - - - trace 0.3 – 3% 97 – 98%

1.2. Production

(a) C-octaBDE

12. Parties to the Stockholm Convention mustshall prohibit and/or eliminate the production

of hexaBDE and heptaBDE and there are no exemptions under the Convention for the

production of those chemicals.the chemical. Information on the status of ratification by the

Pparties of the amendment listing hexaBDE and heptaBDE in the Stockholm Convention can be

found on the website of the Treaty Section of the United Nations (https://treaties.un.org/).

10.13. C-octaBDE has been produced in France, Norway, Switzerland, Canada, Japan, Israel,

the Netherlands, the United Kingdom of Great Britain and Northern Ireland, andKingdom and

the United States of America. Estimated annual worldwide production of c-octaBDE was 6,000

tonnes in 1994 and had decreased to 3,800 tonnes by 2001. Estimated total production of c-

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octaBDE from 1970 to 2005 was 102,700 to-118,500 tonnes (Schenker 2008). No information

is available on whether c-octaBDE is being produced in developing countries

(UNEP/POPS/POPRC, 2008). .4/15/Add1).

(b) C-pentaBDE

11.14. Parties of the Stockholm Convention mustshall prohibit and/or eliminate the production

of tetraBDE and pentaBDE and there are no exemptions under the Convention for the

production of the chemical. Information on the status of ratification by the Parties of the

amendment listing tetraBDE and pentaBDE in the Stockholm Convention can be found on the

website of the Treaty Section of the United Nations (https://treaties.un.org/).

14bis. C-pentaBDE was produced in Australia, the European Union, Israel, Japan and the

United States, but production ceased in 2004 (UNEP/POPS/POPRC.2/17/Add.1). According to

(NO EA, 2015), it is possible that China produced for its own market as well. It is assumed that

since the late 1990’s, c-pentaBDE was mainly produced in the United. States. The global

estimated production of c-pentaBDE from 1970 to 2005 was between 91,000 to -105,000 tonnes

(Schenker 2008Watson et al., 2010). Information on the status of ratification by the Pparties of

the amendment listing tetraBDE and pentaBDE in the Stockholm Convention can be found on

the website of the Treaty Section of the United Nations ().

3. Use

(a) C-octaBDE

(c) C-decaBDE

15. Parties to the Stockholm Convention shall prohibit and/or eliminate the production of decaBDE with

specific exemptions for the production of c-decaBDE as specified in part I of Annex A to the

Stockholm Convention as allowed for the Parties listed in the register of specific exemptions of the

Stockholm Convention on the Convention website (www.pops.int). Information on the status of

ratification by the Parties of the amendment listing decaBDE in the Stockholm Convention can be

found on the website of the Treaty Section of the United Nations (https://treaties.un.org/).

15bis. Available production data indicate that about 75% per cent of all the world production

of PBDEs was c-decaBDE. Currently c-decaBDE is manufactured only in a few countries

globally. Many countries have already restricted or initiated voluntary programs to phase out the

production of c-decaBDE. Total production of c-decaBDE in the period from 1970- to 2005 was

between 1.1-1.25 million tonnes. According to document (UNEP/POPS/POPRC.10/3), the

overall scale of c-decaBDE production today is currently unknown, and data on production,

trade and stockpiles is only available for some countries. Production of c-decaBDE is still

ongoing in a few countries (China, India, Japan). For example, the annual processingproduction

capacity of decaBDE in China in 2013 was 49,000 tons (Zhang et al., 2017). Production of c-

decaBDE no longer takes place in the EU and in, the United States and Canada.

3. Use

(a) C-octaBDE

12.16. Parties to the Stockholm Convention shall prohibit and/or eliminate the use of hexaBDE

and heptaBDE, unless they have notified the Secretariat of their intention to use either chemical

for an acceptable purpose or in accordance with a specific exemption listed in part IV of Annex

A to the Convention. HexaBDE and heptaBDE are still being used in accordance with the

specific exemption listed in part IV of Annex A, which allows Pparties to use, recycle or

dispose of articles that contain or may contain hexaBDE and heptaBDE. Information on specific

exemptions can be found in the register of specific exemptions of the Stockholm Convention on

the Convention website (www.pops.int). www.pops.int).

13.17. C-octaBDE is used mostly as an additive flame retardant in the manufacturing of plastic

polymers, particularly in acrylonitrile-butadiene-styrene (ABS) polymers. ABS is used in

housings of electrical and electronic equipment, such as office equipment, automotive parts and

appliances, business machines, computers, business cabinets, pipes and fittings. A minor

Commented [BSEF22]: We kindly ask the author to

provide a source for this statement.

UNEP/CHW.14/INF/9

116

quantity is also being produced for use as an additive in high impact polystyrene (HIPS),

polybutylene terephthalate (PBT) and polyamide polymers (PP) (POPRC, 2008). C-octaBDE

was typically added at concentrations between 10 and -18 %per cent by weight

(UNEP/POPS/POPRC.3/14). Around 95 %per cent of c-octaBDE supplied in the EU was used

in ABS (globally ~approximately 70 %per cent). The total market demand for c-octaBDE was

split with around 40 %per cent each being used in America and Asia, around 15 %per cent in

Europe and approximately 5 %per cent in the rest of the world Around 95 per cent of c-

octaBDE supplied in the EU was used in ABS (globally approximately 70 per cent). (Watson et

al., 2010).

(a)(b) C-pentaBDE

14.18. Parties to the Stockholm Convention mustshall prohibit and/or eliminate the use of

tetraBDE and pentaBDE unless they have notified the Secretariat of their intention to use either

chemical for an acceptable purpose or in accordance with a specific exemption listed in part V

of Annex A to the Convention. TetraBDE and pentaBDE are still being used in accordance with

the specific exemption listed in part V of Annex A, which allows parties to use, recycle or

dispose of articles that contain or may contain tetraBDE and pentaBDE. Information on specific

exemptions can be found in the register of specific exemptions of the Stockholm Convention on

the Convention website (www.pops.int).

15.19. Before C-pentaBDE was phased out in the United States in 2004, 97 per cent of global

production of c-pentaBDE was used in that country, as well as Canada. Alcock et al. have

estimated that up to 2000, 85,000 tonnes of pentaBDE overall were used in the United States

and 15,000 tonnes were used in Europe (Alcock et al., 2003). PentaBDEs may have been used

in Asia but no reliable data are available to confirm this.

16.20. In some regions, c-pentaBDE was used almost exclusively as a flame retardant in the

manufacture of flexible polyurethane (PUR) foams, with between 90 and 95 per cent of c-

pentaBDE used for that purpose. This foam may contain between 10 and 18% per cent of the c-

PentaBDE formulation (UNEP/POPS/POPRC.2/17/Add.1). Flexible PUR foams were used

mainly in automotive and upholstery applications, electrical and electronic

appliancesequipment, building materials, furniture, textiles and packaging.

(b)(c) C-decaBDE

21. Parties of the Stockholm Convention shall prohibit and/or eliminate the use of decaBDE,

unless they have notified the Secretariat of their intention to use it in accordance with a specific

exemption as specified in parts I and IX of Annex A to the Stockholm Convention. Information

on specific exemptions can be found in the register of specific exemptions of the Stockholm

Convention on the Convention website (www.pops.int).The C-decaBDE consumption peaked in

the early 2000's and c-decaBDE is still used worldwide (UNEP/CHW.13/INF/14). C-decaBDE

has a variety of applications including in plastics, textiles, adhesives, sealants, coatings and

inks. C-decaBDE containing plastics are used in electrical and electronic equipment, wires and

cables, pipes and carpets. In textiles, c-decaBDE is mainly used in upholstery, window blinds,

curtains and mattresses for public and domestic buildings, and in the transportation sector. The

amount of c-decaBDE used in plastics and textiles globally varies but up to about 90% per cent

of c-decaBDE ends up in plastics including plastics used in electrical and electronic equipment

while the remainder is used in coated textiles, upholstered furniture and mattresses

(UNEP/POPS/POPRC.11/10/Add.1). C-decaBDE has also been used in modelling clay,

washing and cleaning products and cosmetics and personal care products.144

2.4. Wastes

17.22. Wastes consisting of, containing or contaminated with POP-BDEs (hereinafter referred

to as “POP-BDE wastes”) may be found in:

(a) Solid obsolete stockpiles of POP-BDEs and their related substances in

original packages that are no longer usable;

(b) Solid wastes from producers and users of POP-BDEs;

144 https://echa.europa.eu/substance-information/-/substanceinfo/100.013.277, accessed on 20 March 2018

UNEP/CHW.14/INF/9

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(c) Wastewater from industrial and municipal processes and residues from

wastewater cleaning such as activated carbon treatment;

(d) Products (e.g., electrical and electronic equipment, building materials,

plastics, textiles, adhesives, sealants, coatings, inks present in thermal

resistant papers, wires and cables, pipes, carpets, upholstery, window blinds,

curtains, matresses and vehicles, aircrafts, trains and ships145) including

products fromcontaining recyclates made of plastics which containinged

POP-BDEs146) that have become waste;

(e) Municipal and industrial sludges; and, contaminated soil147 and sediments;

(f) Waste incineration residues , bottom ash in particular148 in case of

incineration of waste containing POP-BDEs waste incineration; and

(g) Landfill leachate.

18.23. Action aimed at waste streams of importance in terms of volume and concentration will

be essential to eliminating, reducing and controlling the environmental load of POP-BDEs from

waste management activities. In that context, the following should be recognized:

(a) It is likely that POP-BDEs are released into the environment throughout their life

cycles (production, product assembly, consumer use, and disposal, including shredding149 and

recycling);

(b) Waste management activities have been identified as one route through which POP-

BDEs can enter the environment, mainly through industrial and municipal wastewater discharges to

surface water and through leachate from landfills;

(c) Wastes may contain variable concentrations of POP-BDEs, depending on the

quantities in which POP-BDEs were originally present in specific products and the quantities

released during product use and wasteend-of-life management.

19.24. Waste streams of importance in terms of potential volume or concentration are:

(a) PUR foams used e.g. for the production of automotiveapplications in the transport

sector and upholstery applications, in the case of c-pentaBDE;

(b) ABS polymers used for casings of electrical and electronic equipment, in the case of

c-octaBDE;

(c) Solid wastes (in particular plastics) from the dismantling of electrical and electronic

wasteequipment, vehicles, aircrafts, trains and the recycling of waste plastics;ships, construction and

demolition, textiles and furniture150.

(d) Sludge and wastewater from municipal treatment plants, contaminated soil; and

(e) Landfill leachate.

20.25. POP-BDE wastes can be generated in a diverse range of applications, at different stages

of the POP-BDEs life cycles and through different environmental release media. Knowledge of

release media guides the analysis and choice of methods that may be required to manage these

wastes. Table 2 below provides an overview of relevant information on the life cycle of POP-

BDE wastes.

145 C-decaBDE is used in all types of vehicles in the transportation sector (cars, airplanes, trains and ships; see

UNEP/POPS/POPRC.11/10/Add.1) 146 e.g., toys, hairdressing accessories and aids, kitchen utensils etc. from black plastic in particular, and carpet

paddings (see DiGangi et al., 2011; DiGangi and Strakova, 2016; DiGangi et al., 2017; Kuang et al. 2018) 147 Soil may be of concern due to application of contaminated sludge and around e-waste sites and recycling

plants (see UNEP/POPS/POPRC.11/10/Add.1, paras 43, 109 and 110) 148 See Borgnes and Rikheim 2005, Wang, Chen et al. 2010 149 Mechanical treatment such as shredding seems to be a relevant source of PBDE releases to the environment;

see (FI MoE, 2016) and (German Federal Environment AgencyUBA, 2017) 150 See UNEP/CHW.13/INF/14; chapter 3.3

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Table 2: Overview of the production and application of POP-BDEs and their release media into the

environment (sources: UNEP/POPS/POPRC.11/10/Add.1, UNEP/CHW.13/INF/14, decision SC-8-10)

Group Source materials

/Substances Used

Application

s

/Processes

End Product Release Media

POP-BDEs CHEMICAL PRODUCTION

Ch

emic

al

Pro

du

ctio

n

Diphenyl oxide, bromine Che

mic

al

synt

hesi

s

POP-BDEs chemical • Solid waste

• Water

• Sludge

• Air

PRODUCTION OF ARTICLES CONTAINING POP-BDEs

Pla

stic

Raw materials

(ethylene, propylene,

vinyl acetate,

acrylonitrile, butadiene,

styrene, isocyanate,

polyhydric alcohols,

polystyrene, prolene,

butanediol,

terephthalate, ethylene

glycol, terephthalic

acid,

hexamethylenediamine,

adipic acid, etc.)

adipic acid, etc.)

POP-BDEs and

other additives

Expansion

and molding

Flame-retardant plasticretardedant polymers:

• ABS

• PUR

• Polyolefins (PE, PP, EVA)

• Styrenics (PS, HIPS , ABS)

• PP

• PBT

• PAEngineering Thermoplastics (PET,

PBT, PA, PC, PC-ABS, PEE-HIPS)

• Thermosets (UPE, epoxies, melamine-

based resins)

• Elastomers (EPDM rubber, thermoplastic

PUR, EVA)

• Waterborne emulsions and coatings

(acrylic-, PVC-, ethylene vinyl chloride-

and urethane-emulsion)

• Solid waste

• Landfill

leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

Bu

ild

ing m

ate

ria

ls

PUR foam

POP-BDEs and

other additives

Plastics made from

flame retardedant

polymers

Expansion

and molding

Board fireproofing:

• Cold bridge insulation

• Floors

• Basement walls and foundations

• Inverted roofs

• Ceilings

• Cavity insulation

• Composite panels and laminates

• Roofing materials such as membranes

and films

• Epoxy adhesive

• Electrical insulation

• Commercial grade carpeting

• Solid waste

• Landfill

leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

Tex

tile

pro

du

ctio

n

Flame-retardedant

textile (back-coating or

fabrics)

Residential and commercial

upholstered furniture Transportation seating Wall coverings and draperies

Protective clothing and other

technical textiles Tents etc.

• Solid waste

• Landfill

leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

UNEP/CHW.14/INF/9

119

Ele

ctric

an

d e

lect

ron

ic e

qu

ipm

ent

HIPS pellets Plastics made

from flame

retardedretardant polymers

Production

of

casingscom

ponents for

electronic

and electric

equipment

Electric and electronic appliances • Solid waste

• Landfill

leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

Tra

nsp

ort

Plastics containing POP-BDEs Flame retardedretardant fabric (made from flame retardedretardant polymers)

Manufacturing of vehicles including cars, aircrafts, trains and ships

Products used in manufacturing cars,

airplanes, trains and ships; examples in

relation to cars include:

• Powertrain and under-hood applications

such as battery mass wires, battery

interconnection wires, mobile air-

conditioning (MAC) pipes, powertrains,

exhaust manifold bushings, under-hood

insulation, wiring and harness under

hood (engine wiring, etc.), speed sensors,

hoses, fan modules and knock sensors;

• Fuel system applications such as fuel

hoses, fuel tanks and fuel tanks under

body;

• Pyrotechnical devices and applications

affected by pyrotechnical devices such as

air bag ignition cables, seat

covers/fabrics (only if airbag relevant)

and airbags (front and side);

• Suspension and interior applications such

as trim components, acoustic material

and seat belts;

• Reinforced plastics (instrument panels

and interior trim);

• Under the hood or dash (terminal/fuse

blocks, higher-amperage wires and cable

jacketing (spark plug wires));

• Electric and electronic equipment

(battery cases and battery trays, engine

control electrical connectors, components

of radio disks, navigation satellite

systems, global positioning systems and

computer systems);

• Fabric such as rear decks, upholstery,

headliners, automobile seats, head rests,

sun visors, trim panels, carpets.

• Solid waste

• Landfill leachate

• Liquid industrial

and household

cleaning waste

• Wastewater

• Sludge

• Air

WASTE RECYCLING AND DISPOSAL

Ele

ctri

cal

and

elect

ron

icw

ast

eele

ctro

nic

was

te d

ism

antl

ing

Electrical and electronic

waste

(Electrical and electronic

plastic shells, circuit

boards, wire and

polyurethane foams,

etc.)

Dismantling Shredding Separation

Metals

PlasticPlastics

Shredder residues

• Solid waste

• Landfill

leachate

• Liquid

industrial and

household

cleaning waste

• Wastewater

• Sludge

• Air

UNEP/CHW.14/INF/9

120

EL

Vs

(ca

rs,

air

cra

fts,

tra

ins

an

d s

hip

s) End of Life

VehiclesLVs (ELVs)

(Electrical and

electronic components,

fuels system

applications,

pyrotechnical devices

and applications,

suspension and interior

applications, reinforced

plastics and fabrics e.g.

as further specified in

Annex A part IX.

Paragraph 2 to the

Stockholm Convention)

Dismantling Shredding Separation

Metals

Plastics

Textiles

Shredder residues

• Solid waste

• Landfill

leachate

• Liquid

industrial and

household

cleaning waste

• Wastewater

• Sludge

• Air

Co

nst

ruct

ion

an

d d

emo

liti

on

wa

ste

Construction and

demolition waste

(e.g. cold bridge insulation,

floors, basement walls and

foundations, inverted roofs,

ceilings, cavity insulation,

composite panels and

laminates, roofing materials

such as membranes and

films, epoxy adhesives,

electrical insulation,

commercial grade carpeting)

Shredding Separation

Metals

Plastics

Textiles

Shredder residues

• Solid waste

• Landfill

leachate

• Liquid

industrial and

household

cleaning waste

• Wastewater

• Sludge

• Air

Tex

tile

an

d f

urn

itu

re

wa

ste

Textile and furniture

waste

(e.g. residential and

commercial upholstered

furniture, wall coverings

and draperies, protective

clothing and other

technical textiles, tents

etc.)

Dismantling Shredding Separation

Plastics

Foams

Textiles

Shredder residues

• Solid waste

• Landfill

leachate

• Liquid

industrial and

household

cleaning waste

• Wastewater

• Sludge

• Air

Wa

ste

pla

stic

recy

clin

g

Waste plastic

(Waste ABS, HIPS, PP,

polyesters, Polyolefins

(PE, PP, EVA), Styrenics

(PS, HIPS, ABS),

Engineering

Thermoplastics (PET,

PBT, PA, PC, PC-ABS,

PEE-HIPS), Thermosets

(UPE, epoxies,

melamine-based resins),

Elastomers (EPDM

rubber, thermoplastic

PUR, EVA), Waterborne

emulsions and coatings

(acrylic-, PVC-, ethylene

vinyl chloride- and

urethane-

emulsion)polyamide,

PBT, thermoplastic

elastomer, polyolefins

and other plastics)

Recycling Plastic • Solid waste

• Landfill

leachate

• Liquid

industrial and

household

cleaning waste

• Wastewater

• Sludge

• Air

II. Relevant provisions of the Basel and Stockholm conventions

A. Basel Convention

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21.26. Article 1 (“Scope of the Convention”) defines the types of waste that are subject to the

Basel Convention. Subparagraph 1 (a) of that Article sets forth a two-step process for

determining whether a “waste” is a “hazardous waste” subject to the Convention. First, the

waste must belong to any category contained in Annex I to the Convention (“Categories of

wastes to be controlled”), and second, the waste must possess at least one of the characteristics

listed in Annex III to the Convention (“List of hazardous characteristics”).

22.27. Annexes I and II to the Basel Convention list some of the wastes that may consist of,

contain or be contaminated with POP-BDEs. These include:

(a) Y9: Waste oils/water, hydrocarbons/water mixtures, emulsions;

(b) Y12: Wastes from production, formulation and use of inks, dyes, pigments,

paints, lacquers, varnish;

(c) Y13 Wastes from production, formulation and use of resins, latex, plasticizers,

glues/adhesives;

(a)(d) Y18: Residues arising from industrial waste disposal operations;

(b)(e) Y40: Ethers;

(c)(f) Y45: Organohalogen compounds other than substances referred to in this

Annex (e.g., Y39, Y41, Y42, Y43, Y44);

(d)(g) Y46: Wastes collected from households.

23.28. Annex I wastes are presumed to exhibit one or more Annex III hazardous characteristics,

which may include H6.1“Poisonous (acute), H11 “Toxic (delayed or chronic)”; H12

“Ecotoxic”; or H13 (“capable after disposal of yielding a material which possess a hazardous

characteristic)”, unless, through “national tests,” they can be shown not to exhibit such

characteristics. National tests may be useful for identifying a particular hazardous characteristic

listed in Annex III until such time as the hazardous characteristic is fully defined. Guidance

papers documents for Annex III hazardous characteristics H11, H12 and H13 were adopted on

an interim basis by the Conference of the Parties at its sixth and seventh meetings.

24.29. List A of Annex VIII describes wastes that are “characterized as hazardous under Article

1, paragraph 1 (a) of this Convention” although “their designation on this Annex does not

preclude the use of Annex III (“[hazardhazardous characteristics”]) to demonstrate that a waste

is not hazardous” (Annex I, paragraph (b)). List A of Annex VIII includes a number of wastes

or waste categories which have the potential to contain or be contaminated with POP-BDEs,

including:

(a) A1180: Waste electrical and electronic assemblies or scrap containing components

such as accumulators and other batteries included on list A, mercury-switches, glass from

cathode- ray tubes and other activated glass and PCB-capacitors, or contaminated with Annex I

constituents (e.g., cadmium, mercury, lead, polychlorinated biphenyl) to an extent that they

possess any of the characteristics contained in Annex III (note the related entry on list B

B1110);

(b) A1190: Waste metal cables coated or insulated with plastics containing or

contaminated with coal tar, PCB11, lead, cadmium, other organohalogen compounds or other

Annex I constituents to an extent that they exhibit Annex III characteristics;

(c) A3050: Wastes from production, formulation and use of resins, latex, plasticizers,

glues/adhesives excluding such wastes specified on list B (note the related entry on list B

B4020)

(a)(d) A3080: Waste ethers not including those specified on list B;

(b)(e) A4070: Wastes from the production, formulation and use of inks, dyes, pigments,

paints, lacquers, varnish excluding any such waste specified on list B (note the related entry on

list B B4010)

(c)(f) A4130: Waste packages and containers containing Annex I substances in

concentrations sufficient to exhibit Annex III hazard characteristics;

(d)(g) A4140: Waste consisting of or containing off specification or outdated chemicals

corresponding to Annex I categories and exhibiting Annex III hazard characteristics;

(e)(h) A4160: Spent activated carbon not included on list B (note the related entry on list B

UNEP/CHW.14/INF/9

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B2060).

25.30. List B of Annex IX includes wastes that “will not be wastes covered in Article 1,

paragraph 1 (a), of this Convention unless they contain Annex I material to an extent causing

them to exhibit an Annex III characteristic.” List B of Annex IX includes a number of wastes or

waste categories which have the potential to contain or be contaminated with POP-BDEs,

including:

(a) B1110: Electrical and electronic assemblies:

• Electronic assemblies consisting only of metals or alloys

• Waste electrical and electronic assemblies or scrap151 (including printed circuit

boards) not containing components such as accumulators and other batteries

included on list A, mercury-switches, glass from cathode-ray tubes and other

activated glass and PCB-capacitors, or not contaminated with Annex I

constituents (e.g., cadmium, mercury, lead, polychlorinated biphenyl) or from

which these have been removed, to an extent that they do not possess any of the

characteristics contained in Annex III (note the related entry on list A A1180)

• Electrical and electronic assemblies (including printed circuit boards, electronic

components and wires) destined for direct reuse and not for recycling or final

disposal)

(b) B1115: Waste metal cables coated or insulated with plastics, not included in list

A1190, excluding those destined for Annex IVA operations or any other disposal

operations involving, at any stage, uncontrolled thermal processes, such as open

burning;

(b)(c) B1250: Waste end-of-life motor vehicles, containing neither liquids nor other

hazardous components;

(c)(d) B2060: Spent activated carbon not containing any Annex I constituents to the extent

they exhibit Annex III characteristics, for example, carbon resulting from the treatment

of potable water and processes of the food industry and vitamin production (note to the

related entry on list A A4160);

(d)(e) B3010: Solid plastic waste;152

(e)(f) B3030: Textile wastes;153

(f)(g) B3035: Waste textile floor coverings, carpets;

(g)(h) B3040: Rubber wastes

The following materials, provided they are not mixed with other wastes:

• Waste and scrap of hard rubber (e.g., ebonite)

• Other rubber wastes (excluding such wastes specified elsewhere);

(h)(i) B3080: Waste parings and scrap of rubber.;

(j) B4010: Wastes consisting mainly of water-based/latex paints, inks and hardened

varnishes not containing organic solvents, heavy metals or biocides to an extent to

render them hazardous (note the related entry on list A A4070)

(k) B4020: Wastes from production, formulation and use of resins, latex, plasticizers,

glues/adhesives, not listed on list A, free of solvents and other contaminants to an

extent that they do not exhibit Annex III characteristics, e.g., water-based, or glues

based on casein starch, dextrin, cellulose ethers, polyvinyl alcohols (note the related

entry on list A A3050).

26.31. For further information, see section II.A of the general technical guidelines.

151 This entry does not include scrap from electrical power generation. 152 Refer to Annex IX to the Basel Convention for a full description of this entry. 153 Ibid 12.

UNEP/CHW.14/INF/9

123

B. Stockholm Convention

27.32. The present document covers intentionally produced POP-BDEs, whose production and

use are to be eliminated in accordance with Article 3 and part I of Annex A to the Stockholm

Convention.

28.33. Annex A, part III (“Definitions”), to the Stockholm Convention defines POP-

BDEshexaBDE and heptaBDE as well as tetraBDE and pentaBDE as follows:

(a)“Hexabromodiphenyl ether and heptabromodiphenyl ether” means2,2',4,4',5,5'-

hexabromodiphenyl ether (BDE-153, CAS No: 68631-49-2), 2,2',4,4',5,6'-

hexabromodiphenyl ether (BDE-154, CAS No: 207122-15-4), 2,2',3,3',4,5',6

heptabromodiphenyl ether (BDE-175, CAS No:446255-22-7), 2,2',3,4,4',5',6-

heptabromodiphenyl ether (BDE-183, CAS No: 207122-16-5) and other hexa- and

heptabromodiphenyl ethers present in commercial octabromodiphenyl ether.

(b)“Tetrabromodiphenyl ether and pentabromodiphenyl ether” means 2,2',4,4'-

tetrabromodiphenyl ether (BDE-47, CAS No: 5436-43-1) and 2,2',4,4',5-

pentabromodiphenyl ether (BDE-99, CAS No: 60348-60-9) and other tetra- and

pentabromodiphenyl ethers present in commercial pentabromodiphenyl ether.”

29.34. Annex A, part IV (“Hexabromodiphenyl ether and heptabromodiphenyl ether”), to the

Convention outlines specific requirements for hexaBDE and heptaBDE, as follows:

“1. A Party may allow recycling of articles that contain or may contain hexabromodiphenyl ether and heptabromodiphenyl ether, and the use and final disposal of articles manufactured from recycled materials that contain or may contain hexabromodiphenyl ether and heptabromodiphenyl ether, provided that

(a) The recycling and final disposal is carried out in an environmentally sound manner and does not lead to recovery of hexabromodiphenyl ether and heptabromodiphenyl ether for the purpose of their reuse;

(b) The Party takes steps to prevent exports of such articles that contain levels/concentrations of hexabromodiphenyl ether and heptabromodiphenyl ether exceeding those permitted for the sale, use, import or manufacture of those articles within the territory of the Party; and

(c) The Party has notified the Secretariat of its intention to make use of this exemption.

2. At its sixth ordinary meeting and at every second ordinary meeting thereafter the Conference of the Parties shall evaluate the progress that Parties have made towards achieving their ultimate objective of elimination of hexabromodiphenyl ether and heptabromodiphenyl ether contained in articles and review the continued need for this specific exemption. This specific exemption shall in any case expire at the latest in 2030.”

30.35. Annex A, part V (“Tetrabromodiphenyl ether and pentabromodiphenyl ether”), to the

Convention outlines specific requirements for tetraBDE and pentaBDE, as follows:

“1. A Party may allow recycling of articles that contain or may contain tetrabromodiphenyl ether and pentabromodiphenyl ether, and the use and final disposal of articles manufactured from recycled materials that contain or may contain tetrabromodiphenyl ether and pentabromodiphenyl ether, provided that:

(a) The recycling and final disposal is carried out in an environmentally sound manner and does not lead to recovery of tetrabromodiphenyl ether and pentabromodiphenyl ether for the purpose of their reuse;

(b) The Party does not allow this exemption to lead to the export of articles containing levels/concentrations of tetrabromodiphenyl ether and pentabromodiphenyl ether that exceed those permitted to be sold within the territory of the Party; and

(c) The Party has notified the Secretariat of its intention to make use of this exemption.

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2. At its sixth ordinary meeting and at every second ordinary meeting thereafter the Conference of the Parties shall evaluate the progress that Parties have made towards achieving their ultimate objective of elimination of tetrabromodiphenyl ether and pentabromodiphenyl ether contained in articles and review the continued need for this specific exemption. This specific exemption shall in any case expire at the latest in 2030.”

36. Annex A defines decaBDE as follows: “Decabromodiphenyl (BDE-209) present in

commercial decabromodiphenyl ether”.

37. Annex A, part I establishes the specific exemptions for the production and use of

decaBDE as follows:

“Production: As allowed for the parties listed in the Register”

“Use: In accordance with Part IX of this Annex:

• Parts for use in vehicles specified in paragraph 2 of Part IX of this Annex

• Aircraft for which type approval has been applied for before December 2018 and has

been received before December 2022 and spare parts for those aircraft

• Textile products that require anti-flammable characteristics, excluding clothing and

toys

• Additives in plastic housings and parts used for heating home appliances, irons, fans,

immersion heaters that contain or are in direct contact with electrical parts or are

required to comply with fire retardancy standards, at concentrations lower than 10

per cent by weight of the part

• Polyurethane foam for building insulation”

38. Annex A, part IX outlines specific requirements for decaBDE as follows:

“1. The production and use of decabromodiphenyl ether shall be eliminated

except for Parties that have notified the Secretariat of their intention to produce

and/or use it in accordance with Article 4.

2. Specific exemptions for parts for use in vehicles may be available for the

production and use of commercial decabromodiphenyl ether limited to the

following:

(a) Parts for use in legacy vehicles, defined as vehicles that have ceased

mass production, and with such parts falling into one or more of the

following categories:

(i) Powertrain and under-hood applications such as battery mass

wires, battery interconnection wires, mobile air-conditioning

(MAC) pipes, powertrains, exhaust manifold bushings, under-

hood insulation, wiring and harness under hood (engine wiring,

etc.), speed sensors, hoses, fan modules and knock sensors;

(ii) Fuel system applications such as fuel hoses, fuel tanks and fuel

tanks under body;

(iii) Pyrotechnical devices and applications affected by

pyrotechnical devices such as air bag ignition cables, seat

covers/fabrics (only if airbag relevant) and airbags (front and

side);

(iv) Suspension and interior applications such as trim components,

acoustic material and seat belts;

(b) Parts in vehicles specified in paragraphs 2 (a) (i)–(iv) above and those

falling into one or more of the following categories:

(i) Reinforced plastics (instrument panels and interior trim);

(ii) Under the hood or dash (terminal/fuse blocks, higher-amperage

wires and cable jacketing (spark plug wires));

(iii) Electric and electronic equipment (battery cases and battery

trays, engine control electrical connectors, components of radio

disks, navigation satellite systems, global positioning systems

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and computer systems);

(iv) Fabric such as rear decks, upholstery, headliners, automobile

seats, head rests, sun visors, trim panels, carpets.

3. The specific exemptions for parts specified in paragraph 2 (a) above shall

expire at the end of the service life of legacy vehicles or in 2036, whichever

comes earlier.

4. The specific exemptions for parts specified in paragraph 2 (b) above shall

expire at the end of the service life of vehicles or in 2036, whichever comes

earlier.

5. The specific exemptions for spare parts for aircraft for which type approval has

been applied for before December 2018 and has been received before December

2022 shall expire at the end of the service life of those aircraft.”

31.39. Information on the register of specific exemptions for POP-BDEs is available from:

.www.pops.int.

32.40. For further information, see section II.B of the general technical guidelines.

III. Issues under the Stockholm Convention to be addressed

cooperatively with the Basel Convention

A. Low POP content

41. The provisional definition of low POP content for hexaBDE, heptaBDE, pentaBDE and,

tetraBDE154 [and decaBDE] present in commercial decabromodiphenyl ether is […] [[50

mg/kg] or [1000 mg/kg] as a sum.155]. [The provisional definition of low POP content for

decaBDE is […]] mg/kg.

33.42. The low POP content described in the Stockholm Convention is independent from the

provisions on hazardous waste under the Basel Convention.

34.43. Wastes with a content of POP-BDEs at or above 50 mg/kg or 1000 mg/kgthe values

specified in paragraph 3641 must be disposed of in such a way that the POP content is

destroyed or irreversibly transformed in accordance with the methods described in section

IV.G.2 below. They should otherwise be disposed of in an environmentally sound manner when

destruction or irreversible transformation does not represent the environmentally preferable

option in accordance with the methods described in section IV.G.3.

35.44. Wastes with a content of POP-BDEs at or below 50 mg/kg or 1000 mg/kgthe values

specified in paragraph 3641 should be disposed of in accordance with the methods referred to in

section IV.G.4 of the general technical guidelines (outlining disposal methods when POP

content is low), taking into account section IV.I.1 below (pertinent to higher-risk situations).

36.45. For further information on low POP content, refer to section III.A of the general

technical guidelines.

B. Levels of destruction and irreversible transformation

37.46. For the provisional definition of levels of destruction and irreversible transformation, see

section III.B of the general technical guidelines.

C. Methods that constitute environmentally sound disposal

38.47. See section IV.G below and section IV.G of the general technical guidelines.

154 The current limit values for tetra-, penta-, hexa-, and hepta-BDE BDEs may be kept, if an individual value for

decaBDE is agreed, or no agreement is reached with respect to decaBDE. 155 Determined in accordance with national or international methods and standards. In addition, a limit value has

been set for the sum of tetra-, penta-, hexa-, and hepta-BDE because the commercial mixtures of those substances

have varying congener composition (see subsection I.B.1 above) and to achieve analytical efficiencies. Further

work to agree on a single value will be undertaken in accordance with decision BC-12/3 by the Conference of the

Parties to the Basel Convention.

Formatted: Highlight

Commented [ACEA23]: Please take into consideration the findings of the latest EU-Study “to support the review of waste related issues in Annexes IV and V of POP-Regulation” (http://ec.europa.eu/environment/waste/pdf/Study_POPS_Waste_final.pdf): “According to the evaluation of the limitation criteria, an appropriate LPCL can be set in a range between 200 and 1,000 mg/kg.” For a value below 200 ppm no analytical method is available. For inhomogeneous waste streams very low limit values cannot be monitored and enforced. Several considerations are relevant when considering a value within the proposed range including the precautionary principle, economic, technical and practical feasibility and efficiency. To allow resource efficiency and having the newly fixed UTC of the EU POP-Regulation of 500 ppm as a sum in mind, the LPC from our perspective should be between 500 ppm – 1,000ppm

Commented [BSEF24]: We recommend the author

taking into consideration the outcome of the discussion

on the low POP content limit value for POP-BDEs that

took place during the SIWG meeting in October 2018.

During the discussions the Parties agreed to include

two options, as referred to in Table 2, page 15, of the

draft General Technical Guidelines on POP wastes.

As a result, we recommend the author to modify this

paragraph in order to make it consistent with the draft

General Technical Guidelines on POP wastes.

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IV. Guidance on environmentally sound management (ESM)

A. General considerations

39.48. For information, see section IV.A of the general technical guidelines.

B. Legislative and regulatory framework

40.49. Parties to the Basel and Stockholm conventions should examine their national strategies,

policies, controls, standards and procedures to ensure that they are in agreement with of the two

conventions and with their obligations under them, including those that pertain to ESM of POP-

BDE wastes.

41.50. Elements of a regulatory framework applicable to POP-BDEs should, among others,

include measures to prevent the generation of wastes and to ensure the environmentally sound

management of generated wastes. Such elements could include:

(a) Environmental protection legislation establishing a regulatory regime, setting

release limits and establishing environmental quality criteria;

(b) Prohibitions and/ or legal and administrative measures to eliminate on the

production, sale, use, import and export of POP-BDEs in accordance with Articles 3 and

Annex A of the Stockholm Convention, except in the case of parties that have notified the

Secretariat of their intention to use or produce decaBDE in accordance with the time-limited

specific exemptions listed in Annex A to the Stockholm Convention;

(c)

Recycling of articles containing POP-BDEs, in accordance with Articles 3 and

Annex A of the Stockholm Convention, except in the case of parties that have notified the

Secretariat of their intention to use or produce decaBDE in accordance with the time-limited

specific exemptions listed in Annex A to the Stockholm Convention;

(d) A requirement that best available technologies (BAT) and best environmental

practices (BEP) be employed in the production and use of decaBDE, in cases where parties

have notified the Secretariat of their intention to use or produce decaBDE in accordance with

the time-limited exemptions listed in Annex A to the Stockholm Convention;

(e) Measures to ensure that POP-BDE waste cannot be disposed of in ways that may

lead to recovery, recycling, reclamation, direct reuse or alternative uses of POP-BDEs ;.

(b)(f) Measures related to the recycling of articles that contain or may contain

hexabromodiphenyl ether and heptabromodiphenyl ether, or tetrabromodiphenyl ether and

pentabromodiphenyl ether (see Annex A, parts IV and V of the Stockholm Convention) in case

Parties registered for a specific exemption under the Stockholm Convention, , set to expire at

the latest in 2030;

(c)(g) Transportation requirements for hazardous materials and waste;

(d)(h) Specifications for containers, equipment, bulk containers and storage sites;

(e)(i) Specification of acceptable analytical and sampling methods for POP-

BDEs;

(f)(j) Requirements for waste management and disposal facilities;

(g)(k) Definitions of hazardous waste and conditions and criteria for the

identification and classification of POP-BDE wastes as hazardous wastes;

(h)(l) A general requirement for public notification and review of proposed

waste-related government regulations, policies, certificates of approval, licences, inventory

information and national releases and emissions data;

(i)(m) Requirements for identification, assessment and remediation of

contaminated sites;

(j)(n) Requirements concerning the health and safety of workers; and

(k)(o) Legislative measures on, e.g., waste prevention and minimization,

inventory development and emergency response.

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42.51. Legislation should include a time limit for disposal of POP-BDEs including in products

and articles, that have no clear phase-out datesBDE wastes so as to prevent the creation of

stockpiles of such substances, products and articlesthat have no clear phase-out dates.

43.52. For further information, see section IV.B of the general technical guidelines.

C. Waste prevention and minimization

44.53. Both the Basel and Stockholm conventions advocate waste prevention and minimization.

Under the Stockholm Convention, the production and use of PDBEsPOP-BDEs is to be

eliminated, with limited exemptions for their use as provided in part I of Annex A to the

Convention.

45.54. Quantities of waste containing POP-BDEs should be minimized through isolation and

source separation to prevent mixing and contamination of other waste streams.

46.55. The mixing and blending of wastes with POP-BDEs content at or above 50 mg/kg or

1000 mg/kgthe values specified in paragraph 36 41 with other materials solely for the purpose

of generating a mixture with a POP-BDEs content at or below 50 mg/kg or 1000 mg/kgthe

values specified in paragraph 3641 are not environmentally sound. Nevertheless, the mixing or

blending of materials as a pre-treatment method may be necessary in order to enable treatment

or to optimize treatment efficiency.

47.56. For further information on waste prevention and minimization, see section IV.C of the

general technical guidelines.

D. Identification of wastes

48.57. Article 6, paragraph 1 (a), of the Stockholm Convention requires each party to, inter alia,

develop appropriate strategies for the identification of products and articles in use and wastes

consisting of, containing or contaminated with POPs. The identification of POP-BDE wastes is

the starting point for their effective ESM.

49.58. For general information on identification and inventories, see section IV.D of the general

technical guidelines.

59. Detailed guidance and information on establishing inventories for POP-PBDEs is

provided in the "Guidance for the inventory of polybrominated diphenyl ethers (PBDEs) listed

under the Stockholm Convention on Persistent Organic Pollutants" (UNEP 2017b). The

objective of this document is to provide step-by-step guidance that enables Parties to establish

inventories of hexabromodiphenyl ether and heptabromodiphenyl ether, tetrabromodiphenyl

ether and pentabromodiphenyl ether listed under the Convention in 2009, and provides updated

information on known uses, information that could be useful to identify POP-BDE containing

waste.

1. Identification

50.60. POP-BDE wastes can be found in the following stages of the POP-BDEs lifecycles:

(a) BDE manufacturing and processing:

(i) Waste generated from the production and processing of BDEs;

(ii) In water, soil or sediment close to manufacturing or processing sites;

(iii) Industrial wastewater and sludge;

(iv) Landfill leachate from sites where chemical manufacturing or processing

waste was disposed of;

(v) Stockpiles of unusable or unsellable material;

(b) Industrial application of BDEs (PUR foams, plastics of electrical and

electronic equipment, of building materials, vehicles, aircrafts, trains and ships, textiles,

adhesives, sealants, coatings, inks, wires and cables, pipes, carpets, upholstery, window

blinds, curtains, matresses):

(i) Residues generated from the application of BDEs;

(ii) In water, soil or sediment close to manufacturing or processing sites;

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(iii) Industrial wastewater and sludge;

(iv) Landfill leachate from sites where waste from industrial application

was disposed of;

(v) Stockpiles of unusable or unsellable products;

(c) Use of products or articles containing BDEs:

(i) In water, soil or sediment close to sites where such products were

used;

(d) Disposal of products or articles containing BDEs:

(i) In certain facilities for the collection, recycling and recovery of textiles,

PUR foams and plastics of electronic and electrical equipment, building

materials and vehicles;

(ii) In municipal landfill leachate;

(iii) In municipal wastewater and sludge.

51.61. It should be noted that even experienced technical personnel may not be able to

determine the nature of an effluent, substance, container or piece of equipment by its

appearance or markings. Consequently, parties may find the information on production, use and

types of waste provided in section I.B of the present guidelines useful in identifying POP-BDEs.

2. Inventories

52.62. A national inventory should, as appropriate, include data on:

(a) Production of POP-BDEs within a country;

(b) Import and export of products and articles consisting of or containing POP-BDEs;

(c) Disposal of POP-BDE waste; and

(d) Import and export of POP-BDE waste.

53.63. Inventories are an important tool for identifying, quantifying and characterizing wastes.

A step-by-step approach for the development of national inventories of POP-BDEs generally

includes the following steps:

(a) Step 1: planning (i.e., identifying relevant sectors that use or produce POP-BDEs);

(b) Step 2: choosing data collection methodologies using a tiered approach;

(c) Step 3: collecting and compiling data from national statistics on the production,

use, import and export of POP-BDEs;

(d) Step 4: managing and evaluating the data obtained in step 3 using an

estimation method;

(e) Step 5: preparing an inventory report; and

(f) Step 6: periodically updating the inventory report.

54.64. For further information, please refer to the Revised guidance for the inventory of

polybrominated diphenyl ethers (PBDEs) listed under the Stockholm Convention on Persistent

Organic Pollutants (UNEP, 2015c2017b).

E. Sampling, analysis and monitoring

55.65. For general information on sampling, analysis and monitoring, see section IV.E of the

general technical guidelines.

1. Sampling

56.66. Sampling serves as an important element for identifying and monitoring environmental

concerns and human health risks.

57.67. Standard sampling procedures should be established and agreed upon before the start of

the sampling campaign. Sampling should comply with specific national legislation, where it

exists, or with international regulations and standards.

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68. For WEEE a sampling method is described in the Technical Specification TS 50625-3-1:

Collection, logistics & treatment requirements for WEEE - Part 3-1: Specification for de-

pollution – General (UNEP 2017d).For EEE and WEEE plastic - the major POP-PBDEs

contaminated products and material - a detailed sampling methodology and a sampling protocol

has been developed and is described in Wäger et al, 2010. This sampling strategy and protocol

can be applied (in a modified way) in other countries and regions having shredder plants with

related WEEE plastic shredder fractions. An approach of sampling of single EEE for screening

of POP-PBDEs in e.g. Cathode Ray Tube casings of TV and PC is shortly described in Annex

3-B of UNEP 2017d. Strategies of sampling along with the mechanical preparation of samples

from electrotechnical products, electronic assemblies and electronic components is provided in

IEC 62321-2:2013.

58.69. Types of matrices that are typically sampled for POP-BDEs include:

(a) Liquids:

(i) Leachate from dumpsites and landfills;

(ii) Water (surface water, drinking water and industrial effluents);

(iii) Waterborne emulsions(i) Stockpiles of products and formulations

consisting of, containing or contaminated with POP-BDEs;

(iv) (ii) Rinse solution;

(b) Solids:

(i) ABS, HIPS and other types of flame-retardedretardant polymers

(wastes from production processes);

(ii) ABS, HIPS and other types of plastics of WEEE;

(iii) PUR foam, textile, rubber (from end-of-life vehicles);

(iv) Shredding materials and residues;

(i)(v) Solids from treatment or disposal processes (fly ash, bottom ash, sludge,

still bottoms, other residues, clothing, etc.);

(iii) Equipment, containers and other packaging materials (rinse or wipe samples),

and tissues or fabrics used in the collection of wipe samples;

(ii)(vi) (iv) Soil, sediment, rubble, sewage sludge and compost;

(c) Gases:

(i) Air (indoor and outdoor);

(ii) Exhaust gas.

2. Analysis

59.70. Analysis refers to the extraction, purification, separation, identification, quantification

and reporting of POP-BDE concentrations in the matrix of interest. In order to obtain

meaningful and acceptable results, analytical laboratories should have the necessary

infrastructure (housing) and proven experience.

71. The development and dissemination of reliable analytical methods and the accumulation

of high-quality analytical data are important to understand the environmental impact of

hazardous chemicals, including POPs.

71bis. X-ray fluorescence (XRF) and sliding spark analysis can be used as inexpensive and

rapid screening methods to determine whether a material contains bromine. However, these

methods will not serve to distinguish the types of chemicals that contain bromine.

72. Chemical analysis of PBDEs is usually using gas chromatography coupled to mass

spectrometry in different variations in order to optimise the analysis according to the specific

matrix (UNEP/CHW.13/INF/14). In the toxicological profile for PBDEs, the Agency for Toxic

Substances and Disease Registry (ATSDR) provides a summary of identified and well-

established methods that are used as standard methods for analysing PBDEs. Additionally,

analytical methods are included that modify previously used methods to obtain lower detection

limits and/or to improve accuracy and precision (see ATSDR 2017). Further information on

analytical methods for POP-BDEs is provided in the UNEP Draft Guidance on Sampling,

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Screening and Analysis of Persistent Organic Pollutants in Products and Articles (see UNEP

2017d).

60.73. Standardised mMethods of analysing the various matrices for POP-BDEs have been

developed by the International Organization for Standardization (ISO) and by national

authorities such as the Environmental Protection Agency. X-ray fluorescence (XRF) and sliding

spark analysis can be used as inexpensive and rapid screening methods to determine whether a

material contains bromine. However, these methods will not serve to distinguish the types of

chemicals that contain bromine. Table 3 presents some methods that can be used for analysing

POP-BDEs in products, wastes, sediments, flue gas and wastewater.

Table 3: Analytical methods of PBDEs

Standard No. Analytical method

DIN EN 16694: 2015-12

Water quality – Determination of selected polybrominated diphenyl ether (PBDE) in whole water samples – Method using solid phase extraction (SPE) with SPE-disks combined with gas chromatography-mass spectrometry (GC-MS)

EPA Method 1614 A Brominated Diphenyl Ethers in Water, Soil, Sediment, and Tissue by HRGC/HRMS

EPA Method 527 Determination of Selected Pesticides and Flame Retardants in Drinking Water by Solid

Phase Extraction and Capillary Column Gas Chromatography/Mass Spectrometry

(GC/MS)

EPA 8270D Semi-volatile Organic Compounds by Gas Chromatography/Mass Spectrometry (GC/MS)

IEC 62321-3-1:2013 Determination of certain substances in electrotechnical products - Part 3-1: Screening - Lead, mercury, cadmium, total chromium and total bromine using X-ray fluorescence spectrometry

IEC 62321-3-2:2013 Determination of certain substances in electrotechnical products - 3-2: Screening - Total bromine in polymers and electronics by Combustion - Ion Chromatography

IEC 62321-20086:2015

Electrotechnical products – Determination of levels of six regulatedcertain

substances (lead, mercury, cadmium, hexavalent chromium, polybrominatedin

electrotechnical products – Part 6: Polybrominated biphenyls, and polybrominated

diphenyl ethers in polymers by gas chromatography – mass spectrometry (GC-MS)

ISO 22032: 20092013 Water quality – Determination of selected polybrominated diphenyl ethers in sediments and sewage sludge – Method using extraction and gas chromatography/mass spectrometry China GB/Z 21277-

2007 Rapid screening of lead, mercury, chromium, cadmium and bromine of regulated

substances in electrical and electronic equipment - X-ray fluorescence spectrometry

3. Monitoring

61.74. Monitoring and surveillance serve as elements for identifying and tracking

environmental concerns and human health risks. Information collected from monitoring

programmes feeds into science-based decision-making processes and is used for the evaluation

of the effectiveness of risk management measures, including regulations.

62.75. Monitoring programmes should be implemented in facilities managing POP-BDE

wastes.

76. Information on monitoring and analysis of POP-BDE in articles and products is

described in the Stockholm Convention “Draft guidance on Sampling, Screening and Analysis

of Persistent Organic Pollutants in Products and Articles”. This document provides a step by

step guidance on monitoring (sampling, screening and analysis) in articles, products and

recycling streams (see UNEP 2017d).

F. Handling, collection, packaging, labelling, transportation and storage

63.77. POP-BDE wastes should be handled, collected, packaged, labelled, transported and

stored so as to prevent spills and leaks leading to worker exposure, releases to the environment

or exposure of the community. The guidance on waste handling and collection contained herein

may not apply to POP-BDE wastes that are consumer or household wastes, such as WEEE,

since it has not been documented that such wastes pose significant risks to the environment or

human health during handling and collection.

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78. For further general information on handling, collection, packaging, labelling,

transportation and storage, see section IV.F of the general technical guidelines.

1. Handling

64.79. POP-BDE wastes should be handled separately from other types of waste in order to

prevent contamination of other waste streams.

65.80. Organizations handling POP-BDE wastes should have in place procedures for handling

such wastes and workers should be trained in such procedures.

2. Collection

66.81. Collection arrangements and collection depots for POP-BDE wastes should provide for

the separation of POP-BDE wastes from other wastes. In Europe, Technical Specification (TS)

50625-3- 1: Collection, logistics & treatment requirements for WEEE is currently under

developmentavailable at the National Committees of the European Committee fFor

Electrotechnical Standardization (CENELEC)156.

67.82. All POP-BDE wastes should be collected separately from those wastes that do not

contain POP-BDEs. Legal or other mechanisms may be required to ensure the efficient

collection of POP- BDE wastes, such as WEEE, from households. For example, governments,

producers of articles containing POP-BDEs and others could provide arrangements for the

collection of such wastes by local collectors.

68.83. Waste plastics containing POP-BDEs from electrical and electronic wastes recycling

facilities should be collected separately during dismantling process.

3. Packaging

84. POP-BDEsBDE wastes should be properly packaged for ease of transport and before

storage as a safety measure to reduce the risk of leaks and spills. For transporting POP-BDEs

wastes from generators’ premises or public collection points to waste treatment facilities, the

wastes should be properly packaged.

(a) Packaging of solid POP-BDE wastes

69.85. The packaging of solid POP-BDE wastes can include corrugated cartons lined with

protective anti-seepage plastic bags.

86. Special wooden pallets could be designed for use during storage to raise stored POP-

BDE wastes above ground level and thereby protect them against moisture.

(b) Packaging of liquid POP-BDE wastes

70.87. PBDE-contaminated liquids can be packaged in special anti-seepage barrels.

(c) Packaging of POP-BDE contaminated soil

71.88. PBDE-contaminated soils can be packaged in triple layered, anti-leak, high-strength

laminated bags.

4. Labelling

89. Every container carrying POP-BDE wastes should be clearly labelled with a hazard-

warning label and a label giving details of the container and a unique serial number. Such

details should include the contents of the container (e.g., exact counts of equipment, weight,

type of waste carried), the name of the site from which the waste originated so as to allow its

traceability and, if applicable, the date of repackaging and the name and telephone number of

the person responsible for the repackaging operation. The label should be indelible, clear and

plainly visible.

5. Transportation

72.90. Appropriate measures should be taken to prevent scattering or leakage of POP-BDE

156 The standard is available at https://www.cenelec.eu/dyn/www/f?p=WEB:5:1006113885681101. To

purchase the standard please use the link to a website of a national CENELEC Member.

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wastes. Such wastes should be handled separately during transport to avoid their mixing with

other materials.

73.91. Transporters should employ trained and qualified drivers, loading and unloading

management personnel and escort personnel, all of whom should carry their qualification

certificates.

74.92. Waste transporters should provide full and accurate information about their cargoes or

shipments, safely transfer wastes to their destinations and hand them over to receivers in

accordance with national regulations.

6. Storage

75.93. POP-BDE wastes should be stored in designated sites and appropriate measures should

be taken at such sites to prevent scattering, leakage and underground seepage of POP-BDEs.

76.94. Appropriate measures, such as the installation of partitions, should be taken to avoid

contamination of the POP-BDEs wastes.

77.95. POP-BDE waste storage areas should be controlled areas with defined boundaries.

Warning signs should be posted around such areas and access should be restricted to authorized

personnel.

78.96. POP-BDE waste storage areas should have adequate access roads for vehicles. Simple

roads can be constructed when necessary.

79.97. Storage sites should have structures to prevent underground leakage of POP-BDEs.

Containers should be sealable, easy to store and durable. Storage sites should be maintained and

inspected to verify whether there have been any releases of POP-BDEs into the environment.

G. Environmentally sound disposal

1. Pre-treatment

80.98. Dismantling, disassembling and mechanical separation can be used to reduce the volume

of POP-BDE wastes.

81.99. For information, see subsection IV.G.1 of the general technical guidelines.

2. Destruction and irreversible transformation methods

82.100. Destruction and irreversible transformation methods for the environmentally sound

disposal of wastes with a POPsPOP-BDE content at or above 50 mg/kg or 1000 mg/kgthe

values specified in paragraph 3641, according to the general technical guidelines, include at

least:

(a) Advanced solid waste incineration;

(a)(b) Cement kiln co-incineration;

(b)(c) Hazardous waste incineration; and

(d) Thermal and metallurgical production of metals;

(c)(e) Supercritical water oxidation (SCWO) and subcritical water oxidation. ; and

(f) Gas-phase chemical reduction.

83.101. It should be noted that PBDDs/PBDFs can be generated from combustion and

incineration of POP-BDE wastes.

84.102. For further further information, see subsection IV.G.2 of the general technical

guidelines.

3. Other disposal methods when neither destruction nor irreversible transformation is

not the environmentally preferable option

85.103. For further information, see subsection IV.G.3 of the general technical guidelines.

4. Other disposal methods when the POP content is low

Formatted: Highlight

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86.104. For information, see subsection IV.G.4 of the general technical guidelines.

H. Remediation of contaminated sites

105. Several remediation technologies are described in the literature. These include in situ

remediation such as electrokinetic and oxidation technologies and ex situ soil washing (see Wu

et al., 2012; Ye M. et al., 2015a; Ye M. et al., 2015b; Li J. et al., 2016).

87.106. For further information, see section IV.H of the general technical guidelines.

I. Health and safety

88.107. For information, see section IV.I of the general technical guidelines.

1. Higher-risk situations

89.108. For general information, see subsection IV.I.1 of the general technical guidelines.

90.109. Higher-risk situations occur at sites where high concentrations of POP-BDEs or

high volumes of POP-BDE wastes are found and a high potential for exposure of workers or the

general population exists. Potential higher-risk situations specific to POP-BDEs may occur at:

(a) Sites of former POP-BDEs production;

(b) Sites at which electrical and electronic wastes are dismantled;

(c) Sites at which waste plastic is shredded or recycled; and

(d) Storage sitesSites for storage or disposal of POP-BDE wastes.

2. Lower-risk situations

91.110. For information on lower-risk situations, see subsection IV.I.2 of the general

technical guidelines.

J. Emergency response

92.111. Emergency response plans should be in place for POP-BDEs in use, in storage, in

transport or at disposal sites. Further information on emergency response plans is provided in

section IV.J of the general technical guidelines.

K. Public participation

93.112. Parties to the Basel or Stockholm Convention should have open public participation

processes. For further information see section IV.K of the general technical guidelines.

UNEP/CHW.14/INF/9

134

Annex to the technical guidelines

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Annex IV

Compilation of comments regarding document

UNEP/CHW.14/7/Add.4 (Technical guidelines on unintentionally

produced POPs)

The Secretariat has received comments regarding document UNEP/CHW.14/7/Add.4 from the

European Union and its Member States. These comments are presented in the draft technical

guidelines themselves.

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Draft updated technical guidelines on the environmentally sound

management of wastes containing or contaminated with

unintentionally produced polychlorinated dibenzo-p-dioxins,

polychlorinated dibenzofurans, hexachlorobenzene,

polychlorinated biphenyls, pentachlorobenzene, polychlorinated

naphthalenes or hexachlorobutadiene

(Draft of 5 November 2018)

General Comments

The European Union and its Member States have a few editorial comments shown highlighted in

yellow.

UNEP/CHW.14/INF/9

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Contents

Abbreviations and acronyms ............................................................................................................... 5

Units of measurement .................................................................................................................................... 5

I. Introduction .................................................................................................................................... 143

A. Scope .................................................................................................................................. 143

B. Description, production and wastes .................................................................................. 144

1. Description ............................................................................................................. 144

(a) PCDD and PCDF ....................................................................................... 144

(b) PCB ............................................................................................................. 145

(c) HCB ............................................................................................................ 145

(d) PeCB ........................................................................................................... 145

(e) PCN ............................................................................................................. 145

(f) HCBD ......................................................................................................... 145

2. Unintentional production ....................................................................................... 145

(a) PCDD and PCDF ....................................................................................... 146

(b) PCB ............................................................................................................. 147

(c) HCB ............................................................................................................ 147

(d) PeCB ........................................................................................................... 147

(e) PCN ............................................................................................................. 147

(f) HCBD ......................................................................................................... 147

II. Relevant provisions of the Basel and Stockholm conventions ................................................... 149

A. Basel Convention ............................................................................................................... 149

B. Stockholm Convention ...................................................................................................... 151

III. Provisions of the Stockholm Convention to be addressed cooperatively with the Basel

Convention ..................................................................................................................................... 152

A. Low POP content ............................................................................................................... 152

B. Levels of destruction and irreversible transformation..................................................... 153

C. Methods that constitute environmentally sound disposal ............................................... 153

IV. Guidance on environmentally sound management (ESM) ......................................................... 153

A. General considerations ...................................................................................................... 153

B. Legislative and regulatory framework ............................................................................. 153

C. Waste prevention and minimization ................................................................................. 154

D. Identification of wastes ..................................................................................................... 154

1. Identification .......................................................................................................... 155

2. Inventories .............................................................................................................. 155

E. Sampling, analysis and monitoring .................................................................................. 156

1. Sampling ................................................................................................................. 156

2. Analysis .................................................................................................................. 156

3. Monitoring .............................................................................................................. 157

F. Handling, collection, packaging, labelling, transportation and storage ......................... 157

1. Handling ................................................................................................................. 157

2. Collection ............................................................................................................... 157

3. Packaging ............................................................................................................... 157

4. Labelling ................................................................................................................. 158

5. Transportation ........................................................................................................ 158

6. Storage .................................................................................................................... 158

G. Environmentally sound disposal ....................................................................................... 158

1. Pre-treatment .......................................................................................................... 158

2. Destruction and irreversible transformation methods ......................................... 158

3. Other disposal methods when destruction or irreversible transformation is not the

environmentally preferable option ........................................................................ 158

4. Other disposal methods when the POP content is low ........................................ 158

H. Remediation of contaminated sites ................................................................................... 158

I. Health and safety ............................................................................................................... 159

1. Higher-risk situations ............................................................................................ 159

2. Lower risk-situations ............................................................................................. 159

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J. Emergency response .......................................................................................................... 159

K. Public participation ............................................................................................................ 159

Annex I to the technical guidelines .......................................................................................................... 160

Annex II to the technical guidelines ........................................................................................................ 163

Analytical methods for the determination of unintentional POPs ......................................................... 163

1. ISO methods ........................................................................................................... 163

2. CEN methods ......................................................................................................... 164

3. United States of America ...................................................................................... 164

4. China ....................................................................................................................... 165

5. Japan ....................................................................................................................... 166

6. Germany ................................................................................................................. 166

7. Canada .................................................................................................................... 167

Commented [EU/MS26]: Adjust the table of contents

regarding the Annexes and insert the Bibliography in

the table of contents

UNEP/CHW.14/INF/9

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Abbreviations and acronyms

BAT

BATC

best available techniques

BEP

BREF

best environmental practices

CCMS Committee on the Challenges of Modern Society

CEN European Committee for Standardization

DDT 1,1,1-trichloro-2,2-bis(4-chlorophenyl)ethane (dichlorodiphenyltrichloroethane)

ESM environmentally sound management

HCBD hexachlorobutadiene

HCB hexachlorobenzene

HRGC high resolution gas chromatography

HRMS high resolution mass spectrometry/spectrometer

I-TEF international toxicity equivalency factor

ISO International Organization for Standardization

NATO

OJEU

North Atlantic Treaty Organisation

Official Journal of the European Union

PCB polychlorinated biphenyl(s)

PCDD polychlorinated dibenzo-p-dioxin(s)

PCDF polychlorinated dibenzofuran(s)

PCN polychlorinated naphthalene(s)

PCNB pentachloronitrobenzene

PeCB pentachlorobenzene

PER, PERC perchloroethylene

PFN per- or polyfluorinated naphthalene(s)

POP persistent organic pollutant

TCDD 2,3,7,8-tetrachlorodibenzo-p-dioxin

TEFs toxicity equivalency factors

TEQ toxic equivalent]

UV ultraviolet

WHO World Health Organization

Units of measurement

μg microgram

mg milligram

μg/kg microgram per kilogram

mg/kg milligram per kilogram

ppb parts per billion

ppm parts per million

Commented [EU/MS27]: Insert (see Annex III)

Commented [EU/MS28]: Insert (see e.g. Annex III)

UNEP/CHW.14/INF/9

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I.Introduction

A. Scope

1. This document supersedes the Technical guidelines for the environmentally sound management

of wastes containing or contaminated with unintentionally produced polychlorinated dibenzo-p-

dioxins, polychlorinated dibenzofurans, hexachlorobenzene, polychlorinated biphenyls, or

pentachlorobenzene or polychlorinated naphthalenes of May 20152017.

2. The present technical guidelines provide guidance on the environmentally sound management

(ESM) of wastes containing or contaminated with unintentionally produced polychlorinated

dibenzo-p-dioxins (PCDD), polychlorinated dibenzofurans (PCDF), hexachlorobenzene (HCB),

polychlorinated biphenyls (PCB), pentachlorobenzene (PeCB) or), polychlorinated naphthalenes

(PCN), or hexachlorobutadiene (HCBD) pursuant to several decisions of two multilateral

environmental agreements on chemicals and wastes.157 PCDD, PCDF, HCB and PCB were listed in

Annex C (unintentional production) to the Stockholm Convention at the time of the adoption of the

Convention. PeCB was listed in Annex C to the Convention in 2009 and the amendment entered into

force in 2010. PCN, including dichlorinated naphthalenes (di-CNs), trichlorinated naphthalenes (tri-

CNs), tetrachlorinated naphthalenes (tetra-CNs), pentachlorinated naphthalenes (penta-CNs),

hexachlorinated naphthalenes (hexa-CNs), heptachlorinated naphthalenes (hepta-CNs) and

octachlorinated naphthalene (octa-CN), were listed in 2015 and the amendment entered into force in

2016. HCBD was listed in Annex C in 2017 and the amendment entered into force in 2018.

3. The present technical guidelines cover all the persistent organic pollutants (POPs) that are

formed and released unintentionally from anthropogenic sources as listed in Annex C of the

Stockholm Convention (unintentional production), i.e., PCDD, PCDF, PCB, HCB, PeCB, PCN, and

HCBD.

4. Intentionally produced POPs are not covered by the present technical guidelines but are the

subject of the following specific technical guidelines:

(a) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with polychlorinated biphenyls, polychlorinated terphenyls,

polychlorinated naphthalenes or polybrominated biphenyls including hexabromobiphenyl

(PCBs technical guidelines) (UNEP, 2017);

(b) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with the pesticides aldrin, alpha hexachlorocyclohexane, beta

hexachlorocyclohexane, chlordane, chlordecone, dieldrin, endrin, heptachlor,

hexachlorobenzene (HCB), hexacholorobutadiene, lindane, mirex, pentachlorobenzene,

pentachlorophenol and its salts, perfluorooctane sulfonic acid, technical endosulfan and its

related isomers or toxaphene or with hexachlorobenzene as an industrial chemical (Pesticide

POPs technical guidelines) (UNEP, 2017a);

(c) Technical guidelines for the environmentally sound management of wastes consisting

of, containing or contaminated with 1,1,1-trichloro-2,2-bis(4-chlorophenyl)ethane (DDT

technical guidelines) (UNEP, 2006);

(d) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with perfluorooctane sulfonic acid (PFOS), its salts and

perfluorooctane sulfonyl fluoride (PFOSF) (PFOS technical guidelines) (UNEP, 2015);

(e) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with hexabromodiphenyl ether (hexaBDE) and

heptabromodiphenyl ether (heptaBDE) or tetrabromodiphenyl ether (tetraBDE) and

157 Decisions IV/17, V/26, VI/23, VII/13, VIII/16, BC-10/9, BC-11/3, BC-12/3 and BC-13/4 of the Conference of

the Parties to the Basel Convention on the Control of Transboundary Movement of Hazardous Wastes and Their

Disposal; decisions OEWG-I/4, OEWG-II/10, OEWG-III/8, OEWG-IV/11, OEWG-V/12, OEWG-8/5, and

OEWG-9/3, and OEWG-10/4 and OEWG-11/3 of the Open-ended Working Group of the Basel Convention;

Resolution 5 of the Conference of Plenipotentiaries to the Stockholm Convention on Persistent Organic

Pollutants; decisions INC-6/5 and INC-7/6 of the Intergovernmental Negotiating Committee for an International

Legally Binding Instrument for Implementing International Action on Certain Persistent Organic Pollutants; and

decisions SC-1/21, SC-2/6, SC-4/16, SC-5/9, SC-6/11, SC-7/14 and SC-8//12) of the Conference of the Parties to

the Stockholm Convention on Persistent Organic Pollutants.

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pentabromodiphenyl ether (pentaBDE) (UNEP, 2015a);or decabromodiphenyl ether

(decaBDE) (POP-BDEs technical guidelines) (UNEP, 2019a);

(f) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with hexabromocyclododecane (HBCD technical guidelines)

(UNEP, 2015b);

(g) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with pentachlorophenol and its salts and esters (PCP technical

guidelines) (UNEP, 2017b);

(h) Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with hexachlorobutadiene (HCBD technical guidelines) (UNEP,

2019b).

(i) Technical guidelines on the environmentally sound management of wastes consisting of,

containing or contaminated with short-chain chlorinated paraffins (SCCPs technical guidelines)

(UNEP, 2019c)

5. The present document should be used in conjunction with the General technical guidelines on

the environmentally sound management of wastes consisting of, containing or contaminated with

persistent organic pollutants (hereinafter referred to as “General technical guidelines”) (UNEP,

2019d). The General technical guidelines are intended to serve as an umbrella guide for the ESM of

wastes consisting of, containing or contaminated with POPs.

6. In the present document, reference is made to the PCBs technical guidelines and, the Pesticide

POPs technical guidelines, and the HCBD technical guidelines when the information is common to

both unintentionally and intentionally produced POPs.

B. Description, production and wastes

1.Description

(a)PCDD and PCDF

7. PCDD and PCDF are tricyclic halogenated aromatic hydrocarbons consisting of two benzene

rings connected by two oxygen atoms at adjacent carbons on each of the benzene rings in PCDD and

by one oxygen atom and one carbon-carbon bond at adjacent carbons in PCDF. The basic structures of

unchlorinated compounds are shown in figure 1 below.

Figure 1: Structures of dibenzo-p-dioxin (left) and dibenzofuran (right)

8. Both groups of chemicals may have up to eight chlorine atoms attached at carbon atoms 1 to

4 and 6 to 9. Each of the compounds resulting from chlorine substitution is referred to as a congener.

The number and position of chlorine atoms around the aromatic nuclei distinguish each specific

congener. In total, there are 75 possible PCDD congeners and 135 possible PCDF congeners. The

most widely studied ofcongener among the PCDD and PCDF is 2,3,7,8-tetrachlorodibenzo-p-dioxin

(TCDD).

8.9. Congeners with up to three chlorine atoms are thought to be of little toxicological significance.

However, 17 congeners see Annex II) with chlorine atoms in at least each of the 2, 3, 7 and 8 positions

(i.e., in the lateral positions of the aromatic rings) have shown to pose a health and environmental risk.

Increasing substitution from four to eight chlorine atoms generally results in a marked decrease in

potency.

9.10. PCDD and PCDF have very low water solubility, high octanol-water partition coefficients, low

vapour pressures strong adsorption to particles and surfaces and are resistant to chemical and

biochemical degradation under environmental conditions. Consequently, they persist in the

environment and their high fat solubility preference for partitioning into fatty tissues and inherent

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stability results in their bioconcentration and accumulation in the food chain. Almost all 210 PCDD

and PCDF congeners have been identified in emissions from thermal and industrial processes and as a

result they are found as mixtures in environmental matrices such as soil, sediment, air, plants and

lower animals, although their low aqueous solubility means that they can hardly be detected in water.

Due to their chemical-physical properties, PCDD/PCDF are largely immobile in soils.

10.11. When found in the environment, biological tissues and industrial sources, PCDD and PCDF are

usually present as complex mixtures and their various congeners vary significantly in their

concentrations. The potency of PCDD and PCDF has been ranked relative to 2,3,7,8-TCDD, the most

toxic member of the dioxin class. Those rankings are known as toxicity equivalency factors (TEFs).

To be included in the TEF scheme, a PCDD or PCDF must bind to the cellular aryl hydrocarbon (Ah)

receptor, elicit Ah receptor-mediated biochemical and toxic responses, be persistent, and accumulate

in the food chain (WHO, 1998; van den Berg et al., 1998 and 2006). To estimate the toxic potency of a

given mixture of PCDD and PCDF, the mass concentration of each congener is multiplied by its TEF

and the products are summed to give the toxicity equivalence (TEQ) of the mixture.

11.12. The most recent review of TEFs was that carried out by an expert group for the World Health

Organization in 2005 (van den Berg et al., 2005). Under the WHO TEF scheme, TCDD is assigned a

TEF of 1.0 and other PCDD and PCDF have TEF values ranging from 1.0 down to 0.0001. The WHO

TEF scheme also includes those PCB congeners which are considered to exhibit dioxin-like

characteristics; their TEFs range from 0.1 down to 0.00001. Although, two publications on the WHO

TEF schemes recommend to include certain PCN, so far, no TEFs have been proposed through the

WHO experts (van den Berg et al., 2006; van den Berg et al., 2013)158. The WHO TEF scheme as of

1998 (van den Berg et al., 1998) has established three separate schemes, one for humans and other

mammals and two others for birds and fish, respectively. For human risk assessment, the

human/mammalian TEFs should of course be applied.

12.13. It should be noted that much national legislation still applies the earlier international TEF

(I-TEF) scheme, which was established by the North Atlantic Treaty Organisation Committee on the

Challenges of Modern Society (NATO/CCMS) in 1988. That I-TEF scheme includes only the

17 PCDD and PCDF congeners with chlorine atoms substituted in the 2, 3, 7 and 8 positions and does

not include dioxin-like PCB.

13.14. Under Annex C to the Stockholm Convention, concentrations should be reported commencing

with the 1998 WHO TEF scheme. It is noteworthy that this is not the most recent evaluation

coordinated by WHO.

(b)PCB

14.15. For information, see subsection I.B.1 (a) of the PCBs technical guidelines.

(c)HCB

15.16. For information, see subsection I.B.7 (a) of the Pesticide POPs technical guidelines.

(d)PeCB

16.17. For information, see subsection I.B.10 (a) of the Pesticide POPs technical guidelines.

(e)PCN

17.18. For information see subsection I.B.1 (c) of the PCBs technical guidelines.

(f)HCBD

19. For information see subsection I.B.1 of the HCBD technical guidelines

2.Unintentional production

18.20. Under Article 5 of the Stockholm Convention, Parties are required to reduce total releases from

anthropogenic sources of the chemicals listed in Annex C (i.e., unintentionally produced PCDD,

PCDF, HCB, PCB, PeCB, PCN or HCBD) with the goal of their continuing minimization and, where

feasible, ultimate elimination.

158 It should be noted that, according to the definition of WHO, the TEF value is based on the results of several in

vivo and in vitro studies. Relative potency (REP) values, however, are derived from a single in vivo or in vitro

study (van den Berg et al., 1998). Therefore, REPs and TEFs should be clearly differentiated.

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(a)PCDD and PCDF

19.21. PCDD and PCDF have never been intentionally produced or used commercially except in very

small quantities for analytical and research purposes.

20.22. PCDD and PCDF are unintentionally formed in industrial-chemical processes, such as

chemical manufacture, and thermal processes, such as waste incineration when carbon, oxygen,

hydrogen and chlorine, whether in elemental, organic or inorganic form, are present. At some point in

the synthesis process, whether present in a precursor or generated by a chemical reaction, the carbon

atoms must assume an aromatic structure.

21.23. PCDD and PCDF may occur as trace contaminants in a number of chemical products when

carbon, hydrogen, oxygen and chlorine are present. It is thought that one or more of the following

conditions favour PCDD/PCDF formation in chemical processes (UNEP, 2006; UNEP, 2013):

(a) Elevated temperatures (> 150 °C);

(b) Alkaline conditions;

(c) Metal catalysts;

(d) Ultraviolet (UV) radiation or other radical starters.

22.24. Chemical processes that may lead to the formation of PCDD/PCDF include the manufacture of

chlorophenols, such as pentachlorophenol. The propensity for PCDD/PCDF formation in the

manufacture of chlorophenols has been reported as follows:

Chlorophenols > chlorobenzenes > chlorinated aliphatics > chlorinated inorganics.

23.25. PCDD/PCDF may also be formed as unintentional by-products in combustion processes,

mainly at temperatures between 200 °C and 650 °C, with a peak around 300 °C. Consequently, they

may be formed as unintentional products in certain processes in which carbonaceous material is heated

in the presence of organic or inorganic chlorinated substances (including sodium chloride,

i.e., common salt) together with oxygen or oxygen-containing compounds under certain conditions of

temperature, residence time, humidity and catalyst presence.

24.26. In thermal processes, there are two main pathways by which PCDD/PCDF can be synthesized:

from precursors, such as chlorinated phenols, or de novo from carbonaceous structures in fly ash,

activated carbon, soot or smaller molecule products of incomplete combustion. Under conditions of

poor combustion, PCDD/PCDF can be formed in the burning process itself. PCDD/PCDF has been

reported to be present in the fly ash of both poorly operated incinerators as well as BAT incinerators.

The latter due to increasing efficiency of flue gas scrubbing equipment since the pollutants from the

gas-phase are captured into solid residues (e.g. sorption materials such as active carbon, coke) (UNEP

2013).

25.27. Among the variables and conditions that affect the formation of PCDD/PCDF in thermal

processes, the following play an important role (UNEP, 2006):

(a) Technology: PCDD/PCDF formation can occur either as a result of poor combustion

techniques or poorly managed post-combustion chambers and air pollution control devices.

Combustion techniques vary from the very simple and very poor, such as open burning, to the

very complex and greatly improved, such as incineration using best available techniques;

(b) Temperature: PCDD/PCDF formation in the post-combustion zone or air pollution

control devices has been reported to range between 200 °C and 650 °C; the range of greatest

formation is generally agreed to be 200 °C –450 °C, with a maximum of about 300 °C;

(c) Metals: Copper, iron, zinc, aluminium, chromium and manganese are known to

catalyse PCDD/PCDF formation, chlorination and dechlorination;

(d) Sulphur and nitrogen: Sulphur and some nitrogen-containing chemicals inhibit the

formation of PCDD/PCDF, but may give rise to other unintended products;

(e) Chlorine: chlorine must be present in organic, inorganic or elemental form. Its

presence in fly ash or in the elemental form in the gas phase may be especially important;

(f) PCB: PCB are also precursors to the formation of PCDF.

26.28. A comprehensive list of sources that may release PCDD and PCDF and, to a lesser extent,

other unintentional POPs listed in Annex C to the Stockholm Convention into the environment is

presented in the Toolkit for Identification and Quantification of Releases of Dioxins, Furans and Other

Unintentional Persistent Organic Pollutants under Article 5 of the Stockholm Convention (UNEP,

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2013) (hereinafter referred to as “Toolkit for unintentional POPs”), which contains guidance for

developing release inventories of unintentionally produced POPs.

(b)PCB

27.29. PCB may be unintentionally formed and released from the same sources that generate and

release PCDD/PCDF (UNEP, 2006; UNEP, 2013); these sources include the operation of incinerators

and the combustion of waste at inadequate temperatures, especially during open-air and other open

burning of wastes. Furthermore, recently PCB have been identified as unwanted contaminants in a

number of dye pigments (Grossman, 2013).

(c)HCB

28.30. HCB is unintentionally generated as a by-product of the manufacture of perchloroethylene

(also known as tetrachloroethylene, PER or PERC), carbon tetrachloride and, to some extent,

trichloroethylene. For further information, see subsection I.B.7 (b) of the Pesticide POPs technical

guidelines.

29.31. HCB is also unintentionally generated during the manufacture of some chemicals such as

chloranil (2,3,5,6-tetrachloro-2,5-cyclohexadiene-1,4-dione), which is used as a fungicide. In addition,

HCB is an intermediate in the synthesis of medicines and pesticides and is an oxidizing agent used in

organic synthesis, particularly for dye intermediates. Concentrations in samples from China were in

the g per kg range (4-391 g per kg) (Liu et al., 2012).

30.32. HCB may also be emitted from combustion-related sources when there is incomplete

decomposition of wastes resulting from the bad combustion conditions such as low temperatures, lack

of oxygen or turbulence in either incinerators or in open burning of wastes, i.e., under the same

conditions that can lead to the generation of PCDD and PCDF.

(d)PeCB

31.33. PeCB is an intermediate in the production of the fungicide pentachloronitrobenzene (PCNB,

including but not limited to Quintozene). It may be produced as an impurity during the production of

other chlorinated organic compounds.

32.34. PeCB is also unintentionally generated during the manufacture of some chemicals such as

chloranil (2,3,5,6-tetrachloro-2,5-cyclohexadiene-1,4-dione). Concentrations in samples from China

were in the same range as those for HCB (12 g per kg -54 g per kg) (Liu et al., 2012).

33.35. PeCB may also be emitted from combustion-related sources where there is incomplete thermal

decomposition of organic materials resulting from conditions known to generate PCDD and PCDF

(UNEP, 2013).

(e)PCN

34.36. PCN may be unintentionally formed similar to the mechanisms that generate PCDD/PCDF,

namely (i) de novo synthesis in thermal processes, and (ii) formation in chemical processes where

aromatic compounds and chlorination occurs. In addition, PCNs may be unintentionally generated

from organic precursors, e.g., chlorinated methanes and ethanes, in chemical processes (UNEP

BAT/BEP, 2015).

35.37. According to process (ii) above, PCN have been reported as contaminants in commercial PCB

products such as Aroclors and others (IARC, 2015).

36.38. PCNs are listed in Annex A of the Stockholm with a specific exemption for use as

intermediates in the production of polyfluorinated naphthalenes (PFNs), including

octafluoronaphthalene.

(f)HCBD

39. HCBD is produced unintentionally in the same processes as the other unintentional POPs listed in

annex C of the Stockholm Convention (UNEP Toolkit 2013 and report of BAT/BEP 2017) and in

addition (UNEP, 2016):

(i) Production of certain chlorinated hydrocarbons, particularly of perchloroethylene,

trichloroethylene, and carbon tetrachloride (Lecloux, 2004);

(j) Production of magnesium (Deutscher and Cathro, 2001, Van der Gon et. al, 2007);

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(k) Incineration processes, e.g. motor vehicle emissions, incineration processes of

acetylene, uncontrolled incineration of chlorine residues, incineration of hazardous waste, municipal

waste, clinical waste, and plastic containing waste (Lenoir et al, 2001; German Federal Environment

Agency, 2015; UNEP/POPS/COP.8/15); and

(l) Production of polyvinyl chloride, ethylene dichloride and vinyl chloride monomer,

although this is reported as unlikely from a technological point of view, according to a dossier

prepared for the European chloralkali industry (Lecloux, 2004; Van der Gon et. al, 2007).

.3. Wastes

37.40. Wastes containing or contaminated with unintentionally generated PCDD, PCDF, PCB HCB,

PeCB, PCN or HCBD can be found in:

(a) Solids:

(i) Contaminated soils and sediments (sites contaminated by the use of certain

pesticides (see UNEP, 2013), treated wood, open burning and the chemical

industry including production of chlorinated hydrocarbons, transformer or heat

exchange fluids);

(ii) Contaminated sludge (sludge containing industrially produced chemicals, solids

and liquids);

(iii) Contaminated solid waste (paper, metal products, plastic, vehicle shredder fluff,

painted objects, demolition waste, etc.);

(iv) Residues from air pollution control systems and residues left in combustion

chambers such as sludge and bottom or fly ash resulting from high-temperature

processes (incinerators, power plants, cement kilns, sinter plants (Xhrouet et al.,

2001), secondary metallurgical industry);

(v) Drained equipment with liquid residues (electrical, hydraulic or heat transfer

equipment, internal combustion engines, pesticide application equipment);

(vi) Drained containers containing liquid residues from the equipment described in

(v) above (independent of the materials of the containers, which could be waste

oil drums, pesticide bottles or storage tanks), or absorbent materials;

(vii) Contaminated wood (PCB-contaminated or pesticide-impregnated wood);

(viii) Leather wastes;

(ix) Products/articles produced using PFNs;

(x) Materials/products where PCNs were formerly applied (often identical with PCB

in open applications) including: Neoprene/chloroprene, painted articles (e.g.,

ships, steel), cables;

(b) Liquids:

(i) Contaminated oils (contained within or drained from internal combustion

engines and from electrical, hydraulic or heat transfer equipment);

(ii) Certain pesticide formulations (herbicides, wood preservatives);

(iii) Mixed organic liquid wastes (paints, dyestuffs, oils, solvents);

(iv) Contaminated process water (industrial effluent, water from pollution control

scrubbers and curtains, quench waters, sewage);

(v) Landfill leachates.

38.41. In addition, parts II and III of Annex C to the Stockholm Convention list source categories that

have the potential to include wastes containing or contaminated with unintentionally produced PCDD,

PCDF, PCB, HCB, PeCB, PCN or HCBD. See section B of chapter II below.

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II.Relevant provisions of the Basel and Stockholm conventions

A. Basel Convention

39.42. Article 1 (“Scope of the Convention”) defines the types of waste that are subject to the Basel

Convention. Subparagraph (a) of that Article sets forth a two-step process for determining whether a

“waste” is a “hazardous waste” subject to the Convention: first, the waste must belong to any category

contained in Annex I to the Convention (“Categories of wastes to be controlled”), and second, the

waste must possess at least one of the characteristics listed in Annex III to the Convention (“List of

hazardous characteristics”).

40.43. Annexes I and II list some of the wastes that may contain or may be contaminated with

unintentionally produced PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD. These include:

(a) (a) Y4: Wastes from the production, formulation and use of biocides and

phytopharmaceuticals;

(a bis) Y5: Wastes from the manufacture, formulation and use of wood preserving chemicals;

(b) Y6: Wastes from the production, formulation and use of organic solvents;

(c) Y8: Waste mineral oils unfit for their originally intended use;

(d) Y9: Waste oils/water, hydrocarbons/water mixtures, emulsions;

(e) Y10: Waste substances and articles containing or contaminated with polychlorinated

biphenyls (PCBs) and/or polychlorinated terphenyls (PCTs) and/or polybrominated biphenyls

(PBBs);

(f) Y12: Wastes from the production, formulation and use of inks, dyes, pigments, paints,

lacquers, varnish;

(g) Y18: Residues arising from industrial waste disposal operations;

(h) Y39: Phenols; phenol compounds including chlorophenols;

(i) Y41: Halogenated organic solvents;

(j) Y42: Organic solvents excluding halogenated solvents;

(k) Y43: Any congener of polychlorinated dibenzo-furan;

(l) Y44: Any congener of polychlorinated dibenzo-p-dioxin;

(m) Y45: Organohalogen compounds other than substances referred to in this Annex

(e.g., Y39, Y41, Y42, Y43, Y44);

(n) Y47: Residues arising from the incineration of household wastes.

41.44. Wastes listed in Annex I are presumed to exhibit one or more Annex III hazardous

characteristics, which may include H6.1 “Poisonous (Acute)”, H11 “Toxic (Delayed or chronic),” or

H12 “Ecotoxic”, unless, through “national tests”, they can be shown not to exhibit such characteristics.

National tests may be useful for identifying a particular hazardous characteristic listed in Annex III

until such time as the hazardous characteristic is fully defined. Guidance papers for Annex III

hazardous characteristics H11, H12 and H13 were adopted on an interim basis by the Conference of

the Parties to the Basel Convention at its sixth and seventh meetings.

42.45. List A of Annex VIII describes wastes that are “characterized as hazardous under

Article 1, paragraph 1 (a) of this Convention” although “their designation on this Annex does not

preclude the use of Annex III [hazard characteristics] to demonstrate that a waste is not hazardous”

(Annex I, paragraph (b)). List B of Annex IX lists wastes that “will not be wastes covered by

Article 1, paragraph 1 (a), of this Convention unless they contain Annex I material to an extent causing

them to exhibit an Annex III characteristic.” The following Annex VIII waste categories are applicable

to unintentionally produced PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD:

(a) A1180: Waste electrical and electronic assemblies or scrap159 containing components

such as accumulators and other batteries included on list A, mercury-switches, glass from

cathode-ray tubes and other activated glass and PCBs-capacitors, or contaminated with Annex

I constituents (e.g., cadmium, mercury, lead, polychlorinated biphenyl) to an extent that they

159 This entry does not include scrap assemblies from electric power generation.

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possess any of the characteristics contained in Annex III (note the related entry on list B

B1110);)160;

(b) A1190 Waste metal cables coated or insulated with plastics containing or contaminated

with coal tar, PCB, lead, cadmium, other organohalogen compounds or other Annex I

constituents to an extent that they exhibit Annex III characteristic;

(c) A3180: Wastes, substances and articles containing, consisting of or contaminated with

polychlorinated biphenyl (PCB), polychlorinated terphenyl (PCT), polychlorinated naphthalene

(PCN) or polybrominated biphenyl (PBB), or any other polybrominated analogues of these

compounds, at a concentration level of 50 mg/kg or more;161;

(d) A4110: Wastes that contain, consist of or are contaminated with any of the following:

• Any congener of polychlorinated dibenzo-furan;

• Any congener of polychlorinated dibenzo-p-dioxin.

43.46. List A of Annex VIII includes a number of wastes or waste categories that have the potential to

contain or be contaminated with unintentionally produced PCDD, PCDF, HCB, PCB, PeCB, PCN or

HCBD, including:

(a) A1090: Ashes from the incineration of insulated copper wire;

(b) A1100: Dusts and residues from gas cleaning systems of copper smelters;

(c) A2040: Waste gypsum arising from chemical industry processes, when containing

Annex I constituents to the extent that it exhibits an Annex III hazardous characteristic (note

the related entry on list B B2080);

(d) A2060: Coal-fired power plant fly-ash containing Annex I substances in concentrations

sufficient to exhibit Annex III characteristics (note the related entry on list B B2050);162

(e) A3020: Waste mineral oils unfit for their originally intended use;

(f) A3040: Waste thermal (heat transfer) fluids;

(g) A3070: Waste phenols, phenol compounds including chlorophenol in the form of

liquids or sludges;

(h) A3120: Fluff – light fraction from shredding;

(i) A3150: Waste halogenated organic solvents;

(j) A3160: Waste halogenated or unhalogenated non-aqueous distillation residues arising

from organic solvent recovery operations;

(j bis) A3170: Wastes arising from the production of aliphatic halogenated hydrocarbons

(such as chloromethane, dichloro-ethane, vinyl chloride, vinylidene chloride, allyl chloride and

epichlorhydrin)

(j tris) A4030: Wastes from the production, formulation and use of biocides and

phytopharmaceuticals, including waste pesticides and herbicides which are off-specification,

outdated or unfit for their originally intended use;

(k) A4040: Wastes from the manufacture, formulation and use of wood-preserving

chemicals163;

(k bis) A4060: Waste oils/water, hydrocarbons/water mixtures, emulsions

(l) A4070: Wastes from the production, formulation and use of inks, dyes, pigments,

paints, lacquers, varnish excluding any such waste specified on list B (note the related entry on

list B B4010);

(m) A4100: Wastes from industrial pollution control devices for cleaning of industrial

off-gases but excluding such wastes specified on list B;

160 PCB are at a concentration level of 50 mg/kg or more. 161 The 50 mg/kg level is considered to be an internationally practical level for all wastes. However, many

countries have established lower levels (e.g., 20 mg/kg) for specific wastes in their regulations. 162 Category B2050 reads as follows: “Coal-fired power plant fly-ash, not included on list A.” 163 This entry does not include wood treated with wood preserving chemicals.

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(m bis) A4130: Waste packages and containers containing Annex I substances in

concentrations sufficient to exhibit Annex III hazard characteristics;

(m tris) A4140: Waste consisting of or containing of specification or outdated chemicals

corresponding to Annex I categories and exhibiting Annex III hazard characteristics;

(n) A4150: Waste chemical substances arising from research and development or teaching

activities which are not identified and/or are new and whose effects on human health and/or the

environment are not known;

(o) A4160: Spent activated carbon not included on list B (note the related entry on list B

B2060).164

44.47. List B of Annex IX to the Convention lists wastes that “will not be wastes covered by

Article 1, paragraph 1 (a), of this Convention unless they contain Annex I material to an extent causing

them to exhibit an Annex III characteristic.” List B includes a number of wastes or waste categories

that have the potential to contain or be contaminated with PCDD, PCDF, HCB, PCB, PeCB, PCN or

HCBD, including:

(a) B1010: Metal and metal-alloy wastes in metallic, non-dispersible form, in particular:

• Iron and steel scrap; and

• Aluminium scrap.165

(b) B2080: Waste gypsum arising from industry process not included on list A (note the

related entry on list A A2040);

(a bis) B1040: Scrap assemblies from electrical power generation not contaminated with

lubricating oil, PCB or PCT to an extent to render them hazardous

(b) B1110: Electrical and electronic assemblies166;

(c) B2050: Coal-fired power plant fly-ash, not included on list A (note the related entry on

list A A2060);

(d) B2060: Spent activated carbon not containing any Annex I constituents to the extent

they exhibit Annex III characteristics, for example, carbon resulting from the treatment of

potable water and processes of the food industry and vitamin production (note the related entry

on list A A4160);

(e) B2080: Waste gypsum arising from industry process not included on list A (note the

related entry on list A A2040).

(e bis) B3040: Rubber wastes

The following materials, provided they are not mixed with other wastes:

• Waste and scrap of hard rubber (e.g., ebonite);

• Other rubber wastes (excluding such wastes specified elsewhere).

45.48. For further information, see section II.A of the General technical guidelines.

B. Stockholm Convention

46.49. For POPs that are unintentionally generated as the result of human activity, Article 5 of the

Convention (“Measures to reduce or eliminate releases from unintentional production”) stipulates that

each Party must take “measures to reduce the total releases derived from anthropogenic sources of

each of the chemicals listed in Annex C, with the goal of their continuing minimization and, where

feasible, ultimate elimination”. PCDD, PCDF, HCB, PCB, PeCB, PCN, specified as dichlorinated

naphthalenes (di-CNs), trichlorinated naphthalenes (tri-CNs), tetrachlorinated naphthalenes (tetra-

CNs), pentachlorinated naphthalenes (penta-CNs), hexachlorinated naphthalenes (hexa-CNs),

heptachlorinated naphthalenes (hepta-CNs) and octachlorinated naphthalene (octa-CN) and HCBD are

listed in Part I of Annex C (“Unintentional production”).

164 Category B2060 reads as follows: “Spent activated carbon not containing any Annex I constituents to the

extent they exhibit Annex III characteristics, for example, carbon resulting from the treatment of potable water

and processes of the food industry and vitamin production.” 165 For the full entry, see Annex IX to the Basel Convention. 166 For the full entry, see Annex IX to the Basel Convention .

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47.50. Part II of Annex C lists the following industrial source categories which have the potential for

comparatively high levels of formation and release of unintentionally produced PCDD, PCDF, HCB,

PCB, PeCB, PCN or HCBD:

(a) Waste incinerators, including co-incinerators of municipal, hazardous or medical waste

or of sewage sludge;

(b) Cement kilns firing hazardous waste;

(c) Production of pulp using elemental chlorine or chemicals generating elemental

chlorine for bleaching;

(d) The following thermal processes in the metallurgical industry:

(i) Secondary copper production;

(ii) Sinter plants in the iron and steel industry;

(iii) Secondary aluminium production;

(iv) Secondary zinc production.

48.51. Part III of Annex C lists source categories from which PCDD, PCDF, HCB, PCB, PeCB, PCN

or HCBD may also be unintentionally formed and released, including:

(a) Open burning of waste, including burning of landfill sites;

(b) Thermal processes in the metallurgical industry not mentioned in part II of Annex C;

(c) Residential combustion sources;

(d) Fossil-fuel-fired utility and industrial boilers;

(e) Firing installations for wood and other biomass fuels;

(f) Specific chemical production processes releasing unintentionally formed persistent

organic pollutants, especially production of chlorophenols and chloranil;

(g) Crematoria;

(h) Motor vehicles, particularly those burning leaded gasoline;

(i) Destruction of animal carcasses;

(j) Textile and leather dyeing (with chloranil) and finishing (with alkaline extraction);

(k) Shredder plants for the treatment of end of life vehicles;

(l) Smouldering of copper cables;

(m) Waste oil refineries.

49.52. Part V of Annex C provides general guidance to Parties on best available techniques (BAT)

and best environmental practices (BEP) for preventing or reducing releases of unintentionally

produced POPs. Specific guidance is contained in the Guidelines on best available techniques and

provisional guidance on best environmental practices relevant to Article 5 and Annex C of the

Stockholm Convention on Persistent Organic Pollutants (UNEP, 2007).

50.53. For further information, see section II.B of the General technical guidelines.

III. Provisions of the Stockholm Convention to be addressed

cooperatively with the Basel Convention

A. Low POP content

51.54. The following provisional definitions for low POP content should be applied:

(a) PCDD/PCDF: [1 g TEQ/kg] 15 µg TEQ/kg;

(b) PCB: 50 mg/kg;167

(c) HCB: 50 mg/kg;168

167 Determined in accordance with national or international methods and standards.

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(d) PeCB: 50 mg/kg;169

(e) PCN: 10 mg/kg.170

(f) HCBD: 100 mg/kg171.

52.55. The low POP content described in the Stockholm Convention is independent from the

provisions on hazardous waste under the Basel Convention.

53.56. Wastes with a content of PCB, PCDD/PCDF, HCB, PeCB, PCN or HCBD above the values

specified in paragraph 5254 must be disposed of in such a way that the POP content is destroyed or

irreversibly transformed in accordance with the methods described in subsection IV.G.2. Otherwise,

they may be disposed of in an environmentally sound manner when destruction or irreversible

transformation does not represent the environmentally preferable option in accordance with the

methods described in subsection IV.G.3.

54.57. Wastes with a content of PCB, PCDD/PCDF, HCB, PeCB, PCN or HCBD at or below the

values specified in paragraph 5254 should be disposed of in accordance with the methods referred to

in subsection IV.G.4 (disposal methods when the POP content is low) and taking into account

subsections IV.I.1 and IV.I.2 (on higher and lower-risk situations, respectively).

55.58. For further information, see section III.A of the General technical guidelines.

B. Levels of destruction and irreversible transformation

56.59. For information, see section III.B of the General technical guidelines.

C. Methods that constitute environmentally sound disposal

57.60. For information, see section G of chapter IV below and section IV.G of the General technical

guidelines.

IV.Guidance on environmentally sound management (ESM)

A. General considerations

58.61. For information see section IV.A of the General technical guidelines.

B. Legislative and regulatory framework

59.62. Parties to the Basel and Stockholm conventions should examine their national strategies,

policies, controls, standards and procedures to ensure that they are in agreement with the two

conventions and with their obligations under them, including those that pertain to ESM of wastes

consisting of, containing or contaminated with PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD.

60.63. Elements of a regulatory framework applicable to substances listed in Annex C to the

Convention should include measures to prevent the generation of wastes and to ensure the

environmentally sound management. Measures and controls could include the following:

(a) Environmental protection legislation establishing a regulatory regime, setting release

limits and mandating environmental quality criteria;

(a bis) A requirement that BAT and best environmental practices (BEP) be employed in

processes that may lead to the unintentional generation of POPs listed in Annex C (Section

VI.B Part III Chapter 4 of the UNEP BAT and BEP guidelines (UNEP, 2007) and relevant EU

reference documents for best available techniques (BREFs) 172;

(b) Transportation requirements for hazardous materials and waste;

(c) Specifications for containers, equipment, bulk containers and storage sites;

168 Ibid 1011. 169 Ibid 110. 170 Ibid 110. 171 Ibid 11. 172 EU BREFs are accessible http://eippcb.jrc.ec.europa.eu/reference/. BREFs relevant for unintentional

POPs are listed in Annex III

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(d) Specification of acceptable analytical and sampling methods;

(e) Requirements for waste management and disposal facilities;

(f) Definitions of hazardous waste conditions and criteria for the identification and

classification of PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD wastes as hazardous wastes;

(g) A general requirement for public notification and review of proposed government

regulations, policy, certificates of approval, and licenses and inventory information and

national releases/emissions data;

(h) Requirements for identification, assessment and remediation of contaminated sites;

(i) Requirements for health and safety protection of workers;

(j) Other potential legislative controls, as for waste prevention and minimization,

inventory development and emergency response;

(k) Requirements for BAT/BEP to be used for destruction technologies for the POPs

content of hazardous waste and for waste management facilities and landfills;

(l) Regulations imposing restrictions on open burning of the POP content of domestic

waste;

(m) Regulations for ash disposal (including disposal of ashes from the burning of

agricultural wastes);

(n) Environmental assessment, including environmental impact assessment of new

facilities for which emission limits for PCDD and PCDF may be a consideration.

61.64. For further information, see section IV.B of the General technical guidelines.

C. Waste prevention and minimization

62.65. Both the Basel and Stockholm conventions advocate waste prevention and minimization. With

regard to PCDD/PCDF, the Stockholm Convention Expert Group on BAT and BEP (BAT/BEP expert

group) has developed Guidelines on best available techniques and provisional guidance on best

environmental practices relevant to Article 5 and Annex C of the Stockholm Convention on Persistent

Organic Pollutants (UNEP, 2007) that apply to PCDD/PCDF and were adopted by the Conference of

the Parties to the Stockholm Convention at its third meeting in 2007. The guidelines are currently

being amended by the BAT/BEP expert group to include the new POPs that have been listed in Annex

C to the Stockholm Convention since 2007.

63.66. It is likely that efforts to reduce the formation and release of PCDD and PCDF will also reduce

the formation and release of unintentionally produced HCB, PCB, PeCB, PCN or HCBD generated by

the same processes.173

64.67. The mixing and blending of wastes with a content of PCB, PCDD/PCDF, HCB, PeCB, PCN or

HCBD above the values specified in paragraph 54 with other materials solely for the purpose of

generating a mixture with a POP content at or below the values specified in paragraph 54 is not

environmentally sound. Nevertheless, the mixing or blending of materials before waste treatment may

be necessary in order to enable treatment or to optimize treatment efficiency.

65.68. For further information, see section IV.C of the General technical guidelines, the Toolkit for

unintentional POPs (UNEP, 2013) and the guidelines on BAT and provisional guidance on BEP

(UNEP, 2007).

D. Identification of wastes

66.69. Article 6, paragraph 1 (a), of the Stockholm Convention requires each Party to, inter alia,

develop appropriate strategies for the identification of products and articles in use and wastes

consisting of, containing or contaminated with POPs. It is recommended that Parties consult the toolkit

for unintentional POPs (UNEP, 2013) for the identification of unintentional POPs in chemicals and

consumer products.

67.70. For general information on identification of wastes, see section IV.D of the General technical

guidelines.

173 For further information, see Toolkit for Identification and Quantification of Releases of Dioxins, Furans and

Other Unintentional POPs under Article 5 of the Stockholm Convention (UNEP, 2013).

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1. Identification

68.71. PCDD, PCDF, PCB, HCB, PeCB, PCN or HCBD may be found in the following industries,

equipment and locations (for details, see parts II and III of Annex C to the Stockholm Convention and

Section II.B of the present guidelines):

(a) Waste incineration;

(b) Cement kilns;

(c) Pulp and paper production;

(d) Metallurgical industries;

(e) Fossil-fuel-fired utility and industrial boilers;

(f) The production and use of certain pesticides;

(g) Motor vehicle breaking and recovery;

(h) Drained equipment with liquid residues (electrical, hydraulic or heat transfer

equipment, internal combustion engines, pesticide application equipment, shredders for end-of-

life vehicles and other consumer goods);

(i) Drained containers with liquid residues (oil drums, plastic drums, pesticide bottles,

storage tanks);

(j) Painted objects, including wood, concrete and wallboard;

(k) Mixed organic liquid wastes (paints, dyestuffs, oils, solvents);

(l) Treated or contaminated wood (PCB-contaminated, pesticide-impregnated);

(m) Contaminated soils, sediments, rock and mine aggregates;

(n) Contaminated solid waste, including demolition waste;

(o) Contaminated sludge;

(p) Contaminated oils (contained within or drained from internal combustion engines and

electrical, hydraulic or heat transfer equipment);

(q) Contaminated process water (industrial effluent, water from pollution control scrubbers

and curtains, quench waters, sewage);

(r) Open-air and other open burning of agricultural residues such as crop residues, stubble

and bagasse;

(s) Landfill leachates.

69.72. It should be noted that even experienced technical personnel may not be able to determine the

nature of an effluent, substance, container or piece of equipment by its appearance or markings.

Consequently, Parties may find the information on production, use and types of waste provided in

section I.B of the present guidelines useful in identifying PCDD, PCDF, HCB, PCB, PeCB, PCN or

HCBD.

2.Inventories

70.73. According to Article 5, paragraph (a) (i), of the Stockholm Convention, action plans have to be

developed for unintentionally produced POPs (i.e., chemicals listed in Annex C to the Convention)

that should include an evaluation of current and projected releases of those chemicals, including the

development and maintenance of source inventories and release estimates, taking into consideration

the sources of unintentionally produced POPs listed in Annex C. Such inventories are important for

identifying, quantifying and characterizing wastes.

74. The Toolkit for unintentional POPs (UNEP, 2013) constitutes the most comprehensive

available compilation of emission factors for all relevant sources of the chemicalsPCDD/PCDF listed

in Annex C to the Stockholm Convention. For countries where measurement data are limited, it

enables the elaboration of source inventories and release estimates by using default emission factors

the elaboration of source inventories and release estimates by using default. Recently, emission factors

for dioxin-like PCB (Gong et al., 2017a) as well as for HCB and PeCB (Gong et al., 2017b) have been

published. It should be noted that the number of emissions factors for the other POPs listed in annex

C is lower than for PCDD/PCDF.

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71.75. Since the formation of PCDD/PCDF is accompanied by releases of PCB, HCB, PeCB, PCN or

HCBD, releases of PCDD/PCDF are indicative of releases of the other chemicals listed in Annex C

and can be used as a basis for identifying and prioritizing sources of releases and for evaluating the

efficacy of adopted measures for minimizing and ultimately eliminating releases of these chemicals.

E. Sampling, analysis and monitoring

72.76. For general information, see section IV.E of the General technical guidelines.

1.Sampling

73.77. For information on sampling, see subsection IV.E.1 of the General technical guidelines. It

should be noted that the presence of PCB, HCB, PeCB, PCN or HCBD in a sample does not

necessarily imply that the POP has been formed unintentionally. Only in the case of PCDD/PCDF can

all concentrations be assumed to have been unintentionally formed.

74.78. Standard sampling procedures should be established and agreed upon before the start of the

sampling campaign (both matrix- and POP-specific).

75.79. The types of matrices that are typically sampled for unintentionally generated PCDD, PCDF,

HCB, PCB, PeCB, PCN or HCBD include:

(a) Chemicals and pesticides that contain chlorine or whose synthesis process involved the

use of chlorine, especially chlorophenol and its derivatives and, other chlorinated aromatic

compounds; and certain short-chain hydrocarbons (chloroethanes, -ethylenes,

fluorochlorohydrocarbons);

(b) Consumer goods known to be contaminated with PCDD or PCDF and in which PCB,

HCB, PeCB, PCN or HCBD may be present, such as chemically bleached paper, textiles or

leather; products/articles produced using PFN;

(c) Stack emissions; these are typically analysed for PCDD/PCDF only; occasionally for

dioxin-like PCB. Commonly used sampling methods include European standard 1948, EPA

TO9. For each of the other unintentional POPs – non-dioxin-like PCB, HCB, PeCB and, PCN

or HCBD – there are no such standard methods for sampling and analysis.

2.Analysis

76.80. In general, screening methods should be differentiated from confirmatory methods. Full

analysis of unintentionally produced POPs is expensive, time consuming, and requires sophisticated

equipment and experienced personnel. Capacity is therefore not always available. There are however

screening methods available for these POPs that allow for a pre-selection of samples before

undertaking confirmatory analysis with sophisticated equipment. Such screening may save time and

costs.

77.81. Screening methods can be used to indicate the presence of POPs among other chemicals and

are typically used for chemicals that require quite sophisticated instruments for analysis such as

PCDD, PCDF or dioxin-like PCB. Bioanalytical screening methods to detect Ah-receptor binding

have been developed, e.g. immunoassays or CALUX type cell-based bioanalytical methods; these are

sensitive enough to determine dioxin like-POPs at trace levels but also include other groups of

chemicals. The European Union has set criteria for the use of bioanalytical methods in official controls

for feed and food (EU 2009, EU 2014). Since 2005, the Japanese Government has also allowed the use

of bioanalytical methods for measuring PCDD, PCDF and dioxin-like PCB in emission gas from small

scale waste incinerators and ash from all the waste incinerators (Nakano et al., 2006).

78.82. In chemical-analytical laboratories, simple clean-up steps followed by GC-ECD separation and

detection of the main peak can be used as well in screening steps.

79.83. All screenings methods should not generate false negatives. If not otherwise agreed, all

samples resulting positive should undergo confirmatory measurements for final quantification.

80.84. Confirmatory methods for the unintentionally produced POPs, include separation of the POPs

on a capillary gas chromatographic column followed by detector to identify and quantify. As stated in

the Guidance for the global monitoring plan for persistent organic pollutants (UNEP, 2015c), all

methods should apply internal standards for identification and quantification.

81.85. For information on analytical methods for the determination of unintentional POPs, see annex

II to the present guidelines.

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82.86. Analysis for PCDD and PCDF and also for HCB, PCB, PeCB, PCN or HCBD174 as

unintentionally produced POPs differs from the analysis of intentionally produced POPs insofar as,

typically, the concentrations to be determined are many orders of magnitude lower than for other

POPs. This requires special expertise and equipment; for example, only mass-selective detectors are

acceptable for quantification.

83.87. Determination of unintentionally produced POPs other than the dioxin-like POPs, e.g., HCB,

PCB PeCB, PCN or HCBD, since they are also intentionally produced POPs routinely are not analysed

by the same sophisticated equipment like the PCDD/PCDF and dioxin-like PCB. Further, the six most

common PCB (often referred to as “indicator PCB”), HCB, PeCB, PCN or HCBD are not found in the

same fraction after clean-up as the PCDD, PCDF and dioxin-like PCB. HCB, PeCB and HCBD are

analysed together with POPs pesticides using capillary gas chromatography in combination with

electron capture or preferred low resolution mass-selective detectors. For details on the analysis of

PCB or PCN please refer to the PCBs technical guidelines and the Pesticide POPs technical guidelines

for HCB and PeCB. For details on the analysis of HCBD, please refer to the HCBD technical

guidelines and Pesticide POPs technical guidelines.

84.88. For further information on analysis, see subsection IV.E.2 of the General technical guidelines.

3.Monitoring

85.89. Monitoring programmes should be implemented for facilities managing wastes containing or

contaminated with PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD. For further information, see

subsection IV.E.3 of the General technical guidelines.

F. Handling, collection, packaging, labelling, transportation and storage

86.90. For general information on handling, collection, packaging, labelling, transportation and

storage, see the first two paragraphs of section F of the General technical guidelines.

1.Handling

87.91. For information, see subsection IV.F.1 of the General technical guidelines.

2.Collection

88.92. A significant fraction of total national inventories of wastes containing or contaminated with

PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD may not be adequately identified.

89.93. Collection costs may be prohibitive, and national, regional and municipal governments should

consider establishing schemes for the collection and removal of wastes containing or contaminated

with PCDD, PCDF, HCB, PCB , PeCB, PCN or HCBD (see subsection IV.I.1 below, on “higher-risk

situations.

90.94. Collection operations and collection depots for wastes containing or contaminated with PCDD,

PCDF, HCB, PCB, PeCB, PCN or HCBD should ensure that such wastes are handled and stored

separately from all other wastes.

91.95. It is imperative that collection depots do not become long-term storage facilities for wastes

containing or contaminated with PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD.

92.96. For further information, see subsection IV.F.2 of the General technical guidelines.

3.Packaging

93.97. Wastes containing or contaminated with PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD

should be properly packaged before storage or transport:

(a) Liquid wastes should be placed in double-bung steel drums or other approved

containers;

(b) Regulations governing the transport of hazardous materials often require the use of

containers that meet certain specifications (e.g., 16-gauge, made of steel, internally coated with

174 Recently, analytical standards for identification and quantification of PCNs have become commercially

available, e.g., from Cambridge Isotope Laboratories (http://www.isotope.com/corporate-

overview/newsletters.cfm?nid=The%20Standard%20July%202015&aid=New%20Polychlorinated%20Naphthale

nes%20%28PCNs%29) or Wellington Laboratories (http://well-labs.com/wellingtoncatalogue1214.html).

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epoxy). Containers used for storage should meet such specifications given that they may be

transported in the future;

(c) Large, drained equipment may be stored as is or may be placed inside large containers

(overpack drums) or heavy plastic wraps if leakage is a concern;

(d) Small pieces of equipment, whether drained or not, should be placed in drums with an

absorbent material, where appropriate, to prevent excessive movement of container contents

and enable any free liquids/spills to be absorbed. Numerous small pieces of equipment may be

placed in the same drum so long as an adequate amount of absorbent material is present in the

drum. Loose absorbents may be purchased from safety suppliers;

(e) Drums and equipment may be placed on pallets for movement by forklift truck and for

storage. Drums and equipment should be strapped to the pallets before they are moved.

94.98. For further information, see subsection IV.F.3 of the General technical guidelines.

4.Labelling

95.99. Every container carrying wastes containing or contaminated with PCDD, PCDF, HCB, PCB,

PeCB, PCN or HCBD should be clearly labelled with a hazard-warning label and a label providing

details of the container. Such details should include the contents of the container (exact weight or

volume of a liquid, type of waste carried), the name of the site from which the wastes originated so as

to allow their traceability and, if applicable, the date of waste repackaging and the name and telephone

number of the person responsible for the repackaging operation.

96.100. For further information, see subsection IV.F.4 of the General technical guidelines.

5.Transportation

97.101. For information, see subsection IV.F.5 of the General technical guidelines.

6.Storage

98.102. The storage procedures for PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD wastes should be

similar to those for other POPs, as their properties and toxicity are broadly similar to those of other

POPs.

99.103. For further information, see subsection IV.F.6 of the General technical guidelines.

G. Environmentally sound disposal

1.Pre-treatment

100.104. Techniques which separate unintentionally produced POPs from the waste matrix are

of particular relevance. Those techniques include solvent washing and thermal desorption as, in most

cases, wastes contaminated by unintentionally produced POPs are solid substances such as fly ashes

and other residues from off-gas cleaning. Oil-water separation may also be important.

101.105. For information, see subsection IV.G.1 of the General technical guidelines.

2.Destruction and irreversible transformation methods

102.106. For information, see subsection IV.G.2 of the General technical guidelines.

3.Other disposal methods when neither destruction nor irreversible transformation is not the

environmentally preferable option

103.107. For information, see subsection IV.G.3 of the General technical guidelines.

4.Other disposal methods when the POP content is low

104.108. For information, see subsection IV.G.4 of the General technical guidelines.

H. Remediation of contaminated sites

105.109. For information, see section IV.H of the General technical guidelines.

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I. Health and safety

106.110. For information, see section IV.I of the General technical guidelines.

1.Higher-risk situations

107.111. Unintentionally produced HCB, PCB, PeCB, PCN or HCBD are not covered under this

subsection because they are very unlikely to be generated in concentrations or volumes greater than

those from intentional production.

1. For further information on higher risk-situations, see subsection IV.I.1 of the General technical

guidelines. Potential higher-risk situations specific to PCDD and PCDF may include:

(a) Sites with residues from air pollution control systems;

(b) Sites with graphite electrodes;

(c) Production and application sites of chlorinated phenols and its derivatives and sludges

and other wastes from processes using elemental chlorine;

(d) Consumption of dioxin-contaminated food.

108.112. As any PCB-containing site will also have high concentrations of PCDF and be

accompanied by PCN, see also section IV.I of the PCBs technical guidelines.

2.Lower risk-situations

109.113. For information on lower-risk situations, see subsection IV.I.2 of the General technical

guidelines. Lower-risk situations specific to PCDD and PCDF may include facilities where

unintentionally produced POPs occur in low concentrations and low volumes.

J. Emergency response

110.114. Emergency response plans should be in place for wastes containing or contaminated

with PCDD, PCDF, HCB, PCB, PeCB, PCN or HCBD in storage, in transport or at disposal sites.

Further information on emergency response plans can be found in section IV.J of the General technical

guidelines.

K. Public participation

111.115. Parties to the Basel and Stockholm conventions should have open public participation

processes. For further information, see section IV.K of the General technical guidelines.

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of, containing or contaminated with pentachlorophenol and its salts and esters (PCP technical

guidelines). http://www.basel.int/Portals/4/download.aspx?d=UNEP-CHW.13-6-Add.3-

Rev.1.English.pdf175

UNEP (2017e) Draft guidance for the inventory of hexachlorobutadiene. UNEP/POPS/COP.8/INF/18.

[to be updated]

UNEP, 2019a. Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with hexabromodiphenyl ether and heptabromodiphenyl ether or

tetrabromodiphenyl ether and pentabromodiphenyl ether or decabromodiphenyl ether (POP-PBDEs

technical guidelines).

UNEP, 2019b7c. [to be updated]. Technical guidelines on the environmentally sound management of

wastes consisting of, containing or contaminated with hexachlorobutadiene (HCBD technical

guidelines).

UNEP, 2019c. Technical guidelines on the environmentally sound management of wastes consisting

of, containing or contaminated with short-chain chlorinated paraffins (SCCPs technical guidelines)

UNEP, 20197d. [to be updated]. General technical guidelines on the environmentally sound

management of wastes consisting of, containing or contaminated with persistent organic pollutants

(General technical guidelines).

Van den Berg, M. et al, 1998. “Toxic equivalency factors (TEFs) for PCBs, PCDDs, PCDFs for

humans and wildlife”, Environmental Health Perspectives, vol. 106 No. 12, pp. 775–792. Available

from: www.ehponline.org.

Commented [EU and MS30]: Correction

UNEP/CHW.14/INF/9

162

Van den Berg, M. et al, 2006. “The 2005 World Health Organization Re-evaluation of Human and

Mammalian Toxic Equivalency Factors for Dioxins and Dioxin-like Compounds”, Toxicological

Sciences, vol. 93, pp. 223-241. Available at: http://www.ncbi.nlm.nih.gov/pmc/articles/PMC2290740/.

Van den Berg M. et al., 2013. ””Polybrominated Dibenzo-p-Dioxins, Dibenzofurans, and Biphenyls:

Inclusion in the Toxicity Equivalency Factor Concept for Dioxin-Like Compounds.”, Toxicological

Sciences 133(2), 197–208; doi:10.1093/toxsci/kft070

WHO, 1998. Assessment of the health risks of dioxins: re-evaluation of the tolerable daily intake

(TDI). Executive summary of the WHO consultation, 25–29 May 1998, Geneva.

Xhrouet, C. et al. 2001. De novo synthesis of polychlorinated dibenzo-p-dioxins and dibenzofurans

ion fly ash from a sintering process. Environ. Sci. technol. 35, 1616-1623

UNEP/CHW.14/INF/9

163

Annex II to the technical guidelines

Analytical methods for the determination of unintentional POPs

The present annex contains references applicable to PCDD and PCDF only, since the other

unintentionally produced POPs, i.e., PCB, HCB and PeCB, are covered by the Pesticide POPs technical

guidelines (UNEP, 2017a) and the PCBs technical guidelines (UNEP, 2017).

1. ISO methods

1. ISO methods are available for a fee from www.iso.org and are globally applicable. The

published methods listed below, which were valid as of August 2014, may be retrieved.

Standard Language(s)

ISO 17858:2007

Water quality -- Determination of dioxin-like polychlorinated biphenyls --

Method using gas chromatography/mass spectrometry

Edition: 1,TC 147/SC 2, ICS: 13.060.50

Document available as of: 12.02.2007

English

ISO 16000-13:2008

Indoor air -- Part 13: Determination of total (gas and particle-phase)

polychlorinated dioxin-like biphenyls (PCBs) and polychlorinated dibenzo-p-

dioxins/dibenzofurans (PCDDs/PCDFs) -- Collection on sorbent-backed filters

Edition: 1, TC 146/SC 6 , ICS: 13.040.20

Document available as of: 29.10.2008

English,

French

ISO 16000-14:2009

Indoor air -- Part 14: Determination of total (gas and particle-phase)

polychlorinated dioxin-like biphenyls (PCBs) and polychlorinated dibenzo-p-

dioxins/dibenzofurans (PCDDs/PCDFs) -- Extraction, clean-up and analysis by

high-resolution gas chromatography and mass spectrometry

Edition: 1, TC 146/SC 6, ICS: 13.040.20

Document available as of: 15.05.2009

English,

French

ISO 18073:2004

Water quality -- Determination of tetra- to octa-chlorinated dioxins and furans --

Method using isotope dilution HRGC/HRMS

ISO 18073:2004 specifies a method for the determination of tetra- to octa-

chlorinated dibenzo-p-dioxins (PCDDs) and dibenzofurans (PCDFs) in waters

and waste waters (containing less than 1 % by mass solids) using high-resolution

gas chromatography/high-resolution mass spectrometry (HRGC/HRMS). The

minimum levels (MLs) at which the PCDDs/PCDFs can currently be determined

with no interferences present are specified. This method is "performance based".

The analyst is permitted to modify the method to overcome interferences or lower

the cost of measurements, provided that all performance criteria are met. The

requirements for establishing method equivalency are given.

Edition: 1, TC 147/SC 2, ICS: 13.060.50

English,

French

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2. CEN methods

2. Methods can be obtained against a fee at the following website: www.cen.eu. They are

applicable to European Union Member States. The following published methods are available.

Standard reference Title Directive (OJEU

citation*)

CEN/TC 264 - Air quality

EN 1948-1:2006 Stationary source emissions - Determination of

the mass concentration of PCDDs/PCDFs and

dioxin-like PCBs - Part 1: Sampling of

PCDDs/PCDFs

94/67/EC (No.)

89/429/EEC (No.)

89/369/EEC (No.)

EN 1948-2:2006 Stationary source emissions - Determination of

the mass concentration of PCDDs/PCDFs and

dioxin-like PCBs - Part 2: Extraction and

clean-up of PCDDs/PCDFs

94/67/EC (No.)

89/429/EEC (No.)

89/369/EEC (No.)

EN 1948-3:2006 Stationary source emissions - Determination of

the mass concentration of PCDDs/PCDFs and

dioxin-like PCBs - Part 3: Identification and

quantification of PCDDs/PCDFs

94/67/EC (No.)

89/429/EEC (No.)

89/369/EEC (No.)

EN 1948-4:2010 Stationary source emissions - Determination of

the mass concentration of PCDDs/PCDFs and

dioxin-like PCBs - Part 4: Sampling and

analysis of dioxin-like PCBs

-

EN ISO 16000-12:2008 Indoor air - Part 12: Sampling strategy for

polychlorinated biphenyls (PCBs),

polychlorinated dibenzo-p-dioxins (PCDDs),

polychlorinated dibenzofurans (PCDFs) and

polycyclic aromatic hydrocarbons (PAHs) (ISO

16000-12:2008)

89/106/EEC (No)

* Official Journal of the European Union, accessible in languages from: http://eur-lex.europa.eu/

3. United States of America

3. The U.S. Environmental Protection Agency has produced various methods that can be retrieved

from http://www.epa.gov/waste/hazard/testmethods/sw846/online/index.htm. Several series of

wastewater methods have been published under 40 CFR Part 136, including the 200, 600 and 1600

series. All series are available at http://water.epa.gov/scitech/methods/cwa/methods_index.cfm. In

addition to wastewater methods, the EPA has produced methods for air (300 series, MACT standards),

drinking water (500 series) and solid waste (8000 series).

Method (including

updates) Title

8280, 8280A, 8280B The Analysis of Polychlorinated Dibenzo-p-Dioxins (PCDDs) and

Polychlorinated Dibenzofurans (PCDFs) by High-Resolution Gas

Chromatography/Low Resolution Mass Spectrometry (HRGC/LRMS)

8290, 8290A SW846 Method 8290, "Polychlorinated Dibenzodioxins (PCDDs) and

Polychlorinated Dibenzofurans (PCDFs) by High-Resolution Gas

Chromatography/High Resolution Mass Spectrometry (HRGC/HRMS)",

Revision 0, November 1992. Available at:

http://www.epa.gov/osw/hazard/testmethods/sw846/pdfs/8290a.pdf

0023A (Up. III) Sampling Method for Polychlorinated Dibenzo-p-Dioxins and

Polychlorinated Dibenzofuran Emissions from Stationary Sources (Note:

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Method (including

updates) Title

This method is a revision of Method 23, 40 CFR Part 60.)

Method 23 - Determination of Polychlorinated Dibenzo-p-dioxins and

Polychlorinated Dibenzofurans from Municipal Waste Combustors.

Available at:

http://www.epa.gov/ttn/emc/promgate/m-23.pdf

613 Methods for organic chemical analysis of municipal and industrial

wastewater method 613—2,3,7,8-Tetrachlorodibenzo-p-dioxin

EPA Solid Waste. Available at:

http://www.epa.gov/waterscience/methods/method/organics/613.pdf

TO-9 Determination oOf Polychlorinated, Polybrominated And

Brominated/Chlorinated Dibenzo-p-Dioxins And Dibenzofurans In

Ambient Air

1613B Tetra- through Octa-Chlorinated Dioxins and Furans by Isotope Dilution

HRGC/HRMS, October 1994; EPA Office of Water

Isomer-specific determination of the 2,3,7,8-substituted, tetra- through

octa-chlorinated, dibenzo-p-dioxins and dibenzofurans in aqueous, solid,

and tissue matrices by isotope dilution, high resolution capillary column

gas chromatography (HRGC)/high resolution mass spectrometry (HRMS)

It is approved by Federal Register 1997 under Clean Water Act and

applicable to (waste)water, soil, sediment, biota/ tissues

http://www.epa.gov/ost/methods/1613.pdf, Tetra-through Octa-

Chlorinated Dioxins and Furans by Isotope Dilution High Resolution Gas

Chromatography/High Resolution Mass Spectrometry Revision B

23 Method 23 - Determination of Polychlorinated Dibenzo-p-dioxins and

Polychlorinated Dibenzofurans from Municipal Waste Combustors.

Available at:

http://www.epa.gov/ttn/emc/promgate/m-23.pdf

4. China

4. China’s national standards for environmental monitoring can be retrieved from

http://kjs.mep.gov.cn/hjbhbz/ and are available in Chinese only; an unofficial translation of the titles of

the standards is provided below.

5. The Chinese national standards for PCDD/PCDF analysis (HJ-77.1-2008, HJ-77.2-2008, HJ-

77.3-2008, HJ-77.4-2008) are a mix of international methods, including EN 1948, EPA methods 1613,

8290 and 23A and Japanese Industrial Standard (JIS) methods K0311 and K0312, but they most

resemble EN 1948. The Chinese national standards for PAH analysis are different from those of other

counties; however, the target 16 PAHs in HJ478-2009 are the same chemicals as those covered by EPA

method 610.

Standard reference Title

HJ-77.1-2008 Water quality - Determination of polychlorinated dibenzo-p-dioxins

(PCDDs) and polychlorinated dibenzofurans (PCDFs) by isotope dilution

HRGC-HRMS

Document available as of: 31.12.2008

HJ-77.2-2008 Ambient air and waste gas - Determination of polychlorinated dibenzo-p-

dioxins (PCDDs) and polychlorinated dibenzofurans (PCDFs) by isotope

dilution HRGC-HRMS

Document available as of: 31.12.2008

HJ-77.3-2008 Solid waste - Determination of polychlorinated dibenzo-p-dioxins

(PCDDs) and polychlorinated dibenzofurans (PCDFs) by isotope dilution

HRGC-HRMS

Document available as of: 31.12.2008

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Standard reference Title

HJ-77.4-2008 Soil and sediment - Determination of polychlorinated dibenzo-p-dioxins

(PCDDs) and polychlorinated dibenzofurans (PCDFs) by isotope dilution

HRGC-HRMS

Document available as of: 31.12.2008

5. Japan

6. JIS K 0311:2005 standard serves to determine tetra-through octachlorodibenzo-p-dioxins, tetra-

through octachlorodibenzofurans and dioxin-like polychlorinatedbiphenyls in stationary source

emissions.

7. The standard specifies the method of analysis for tetra-through octachlorodibenzo-para-dioxins,

tetra-through octachlorodibenzofurans and dioxin-like PCBs in exhaust gas that are generated by

combustion and chemical reactions and are discharged to flues, stacks or ducts in stationary source

emissions using gas chromatography instruments coupled with mass spectrometers.

8. Date Established: 1999-09-20, Date Revised: 2005-06-20, Date Published: 2005-06-20; 2008-01-

20 (Revised).

9. The standard is available in Japanese and English and can be obtained for a fee from

http://www.webstore.jsa.or.jp/webstore/Com/FlowControl.jsp?lang=en&bunsyoId=JIS+K+0311%3A20

05&dantaiCd=JIS&status=1&pageNo=0.

6. Germany

Method Title / Description

DIN ISO 16000-13 Indoor air - Part 13: Determination of total (gas and particle-phase)

polychlorinated dioxin-like biphenyls (PCBs) and polychlorinated

dibenzo-p-dioxins/dibenzofurans (PCDDs/PCDFs) - Collection on

sorbent-backed filters (ISO 16000-13:2008)

Published in 2010-03; available in German, English and French.

DIN ISO 16000-14 Indoor air — Part 14: Determination of total (gas and particle-phase)

polychlorinated dioxin-like biphenyls (PCBs) and polychlorinated

dibenzo-p-dioxins/dibenzofurans (PCDDs/PCDFs) — Extraction,

clean-up and analysis by high-resolution gas chromatography and

mass spectrometry.

Published on 2009-05-15; available in German, English and French.

DIN EN ISO 16000-12 Indoor air - Part 12: Sampling strategy for polychlorinated biphenyls

(PCBs), polychlorinated dibenzo-p-dioxins (PCDDs),

polychlorinated dibenzofurans (PCDFs) and polycyclic aromatic

hydrocarbons (PAHs) (ISO 16000-12:2008)

Published in 2008-08; available in German, English and French.

DIN ISO 16000-13 Indoor air - Part 13: Determination of total (gas and particle-phase)

polychlorinated dioxin-like biphenyls (PCBs) and polychlorinated

dibenzo-p-dioxins/dibenzofurans (PCDDs/PCDFs) - Collection on

sorbent-backed filters (ISO 16000-13:2008)

Published in 2010-03; available in German, English and French.

VDI 3498 Blatt 1 Ambient air measurement - Indoor air measurement - Measurement

of polychlorinated dibenzo-p-dioxins and dibenzofurans; Method

using large filters

Published in 2002-07; available in German and English.

VDI 3498 Blatt 2 Ambient air measurement - Indoor air measurement - Measurement

of polychlorinated dibenzo-p-dioxins and dibenzofurans; Method

using small filters

Published in 2002-07; available in German and English

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Method Title / Description

DIN38414-20 German standard methods for the examination of water, wastewater

and sludge - Sludge and sediments (group S) - Part 20:

Determination of 6 polychlorinated biphenyls (PCB) (S 20)

Published in 1996-01; available in German and English.

7. Canada

Report EPS 1/RM/19, February 1992

Reference Method for the Determination of Polychlorinated Dibenzo-para-dioxins (PCDDs) and

Polychlorinated Dibenzofurans (PCDFs) in Pulp and Paper Mill Effluents. Available at:

http://www.ec.gc.ca/lcpe-cepa/default.asp?lang=En&n=89496F4E-1.

Report EPS 1/RM/23, October 1992

Internal Quality Assurance Requirements for the Analysis of Dioxins in Environmental Samples.

Available at: http://www.ec.gc.ca/lcpe-cepa/default.asp?lang=En&n=5ED227EE-1.

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Annex II to the technical guidelines

Congener Abbreviation Mammalian WHO-TEF (1998)

WHO-TEF (2005)

Molecular structure

Polychlorinated dibenzo-p-dioxins

2,3,7,8-Tetrachlorodibenzo-p-dioxin 2,3,7,8-TeDD 1 1

1,2,3,7,8-Pentachlorodibenzo-p-dioxin 1,2,3,7,8-PnDD

1 1

1,2,3,4,7,8-Hexachlorodibenzo-p-dioxin

1,2,3,4,7,8-HxDD

0.1 0.1

1,2,3,7,8,9-Hexachlorodibenzo-p-dioxin

1,2,3,7,8,9-HxDD

0.1 0.1

1,2,3,6,7,8-Hexachlorodibenzo-p-dioxin

1,2,3,6,7,8-HxDD

0.1 0.1

1,2,3,4,6,7,8-Heptachlorodibenzo-p-dioxin

1,2,3,4,6,7,8-HpDD

0.01 0.01

Octachlorodibenzo-p-dioxin OCDD 0.0001 0.0003

Polychlorinated dibenzofurans

2,3,7,8-Tetrachlorodibenzofuran 2,3,7,8-TeDF 0.1 0.1

1,2,3,7,8-Pentachlorodibenzofuran 1,2,3,7,8-PnDF

0.05 0.03

2,3,4,7,8-Pentachlorodibenzofuran 2,3,4,7,8-PnDF

0.5 0.3

Commented [EU/MS31]: Insert a title for this annex,

e.g. “The 17 PCDD/PCDF congeners that pose a health

and environmental risk”

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Congener Abbreviation Mammalian WHO-TEF (1998)

WHO-TEF (2005)

Molecular structure

Polychlorinated dibenzo-p-dioxins

1,2,3,4,7,8-Hexachlorodibenzofuran 1,2,3,4,7,8-HxDF

0.1 0.1

1,2,3,7,8,9-Hexachlorodibenzofuran 1,2,3,7,8,9-HxDF

0.1 0.1

1,2,3,6,7,8-Hexachlorodibenzofuran 1,2,3,6,7,8-HxDF

0.1 0.1

2,3,4,6,7,8-Hexachlorodibenzofuran 2,3,4,6,7,8-HxDF

0.1 0.1

1,2,3,4,6,7,8-Heptachlorodibenzofuran

1,2,3,4,6,7,8-HpDF

0.01 0.01

1,2,3,4,7,8,9-Heptachlorodibenzofuran

1,2,3,4,7,8,9-HpDF

0.01 0.01

Octachlorodibenzofuran OCDF 0.0001 0.0003

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Annex III to the technical guidelines

Reference documents under the IPPC Directive and the IED (http://eippcb.jrc.ec.europa.eu/reference/)

BREF document title Adopted/Published Document

Ceramic Manufacturing Industry BREF (08.2007)

Common Waste Water and Waste Gas Treatment/ Management Systems in the Chemical Sector

BATC (06.2016) BREF

Ferrous Metals Processing Industry BREF (12.2001)

Iron and Steel Production BATC (03.2012) BREF

Large Combustion Plants BATC (07.2017) BREF

Manufacture of Glass BATC (03.2012) BREF

Manufacture of Organic Fine Chemicals BREF (08.2006)

Non-ferrous Metals Industries BATC (06.2016) BREF

Production of Cement, Lime and Magnesium Oxide BATC (04.2013) BREF

Production of Chlor-alkali BATC (12.2013) BREF

Production of Pulp, Paper and Board BATC (09.2014)BREF

Refining of Mineral Oil and Gas BATC (10.2014)BREF

Smitheries and Foundries Industry BREF (05.2005)

Surface Treatment Of Metals and Plastics BREF (08.2006)

Surface Treatment Using Organic Solvents (including Wood and Wood Products Preservation with Chemicals)

BREF (08.2007)

Tanning of Hides and Skins BATC (02.2013) BREF

Textiles Industry BREF (07.2003)

Waste Incineration BREF (08.2006)

Waste Treatment BATC (08.2018) BREF

Commented [EU/MS32]: Insert a title for this annex,

e.g. “Best available techinques reference (BREF)

documents relevant for unintentional POPs”

Commented [EU/MS33]: Explain abbreviation

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Annex V

Compilation of comments regarding document

UNEP/CHW.14/7/Add.5 (Technical guidelines on HCBD)

The Secretariat has received comments regarding document UNEP/CHW.14/7/Add.5 from the

European Union and its Member States. These comments are presented in the draft technical

guidelines themselves.

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Draft updated technical guidelines on the environmentally

sound management of wastes consisting of, containing or

contaminated with hexachlorobutadiene

(Draft of November 2018)

General Comments

The European Union and its Member States have only one comment on para. 18(b) shown

highlighted in yellow.

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Contents

Abbreviations and acronyms .................................................................................................................... 174

Units of measurement ............................................................................................................................... 174

I. Introduction .................................................................................................................................... 175 A. Scope .................................................................................................................................. 175 B. Description, production, use and wastes .......................................................................... 175

1. Description ............................................................................................................. 175 2. Production .............................................................................................................. 176 3. Use .......................................................................................................................... 178 4. Wastes..................................................................................................................... 178

II. Relevant provisions of the Basel and Stockholm conventions ................................................... 182 A. Basel Convention ............................................................................................................... 182 B. Stockholm Convention ...................................................................................................... 183

III. Issues under the Stockholm Convention to be addressed cooperatively with the Basel

Convention ..................................................................................................................................... 183 A. Low POP content ............................................................................................................... 183 B. Levels of destruction and irreversible transformation..................................................... 184 C. Methods that constitute environmentally sound disposal ............................................... 184

IV. Guidance on environmentally sound management (ESM) ......................................................... 184 A. General considerations ...................................................................................................... 184 B. Legislative and regulatory framework ............................................................................. 184 C. Waste prevention and minimization ................................................................................. 185 D. Identification of wastes ..................................................................................................... 185

1. Identification .......................................................................................................... 185 2. Inventories .............................................................................................................. 186

E. Sampling, analysis and monitoring .................................................................................. 186 1. Sampling ................................................................................................................. 186 2. Analysis .................................................................................................................. 187 3. Monitoring .............................................................................................................. 187

F. Handling, collection, packaging, labelling, transportation and storage ......................... 187 1. Handling ................................................................................................................. 187 2. Collection ............................................................................................................... 187 3. Packaging ............................................................................................................... 187 4. Labelling ................................................................................................................. 188 6. Storage .................................................................................................................... 188

G. Environmentally sound disposal ....................................................................................... 188 1. Pre-treatment .......................................................................................................... 188 2. Destruction and irreversible transformation methods ......................................... 188 3. Other disposal methods when destruction or irreversible transformation is not the

environmentally preferable option ........................................................................ 188 4. Other disposal methods when the POP content is low ........................................ 188

H. Remediation of contaminated sites ................................................................................... 188 I. Health and safety ............................................................................................................... 188

1. Higher-risk situations ............................................................................................ 188 2. Lower-risk situations ............................................................................................. 188

J. Emergency response .......................................................................................................... 189 K. Public participation ............................................................................................................ 189

Bibliography .............................................................................................................................................. 190

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Abbreviations and acronyms

APHA American Public Health Association

BAT best available techniques

BEP best environmental practices

BREF best available techniques reference document

CAS Chemical Abstracts Service

EPA United States Environmental Protection Agency

ESM environmentally sound management

EU European Union

HCBD hexachlorobutadiene

LVOC large volume organic chemicals

NIOSH National Institute for Occupational Safety and Health

PBBs polybrominated biphenyls

PCBs polychlorinated biphenyls

PCTs polychlorinated terphenyls

PCDD(s) polychlorinated dibenzo-p-dioxin(s)

PCDF(s) polychlorinated dibenzo-furandibenzofuran(s)

POP persistent organic pollutant

UNEP United Nations Environment Programme

WEEE waste electrical and electronic equipment

Units of measurement

µg/l microgram(s) per liter. Corresponds to parts per billion

µg/kg microgram(s) per kilogram. Corresponds to parts per billion by mass

mg/kg milligram(s) per kilogram. Corresponds to parts per million by mass

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I. Introduction

A. Scope

1. This document supersedes the Technical guidelines for the environmentally sound

management of wastes consisting of, containing or contaminated with hexachlorobutadiene of May

2017.

1.2. The present technical guidelines provide guidance on the environmentally sound

management (ESM) of wastes consisting of, containing or contaminated with hexachlorobutadiene

(HCBD), pursuant to several decisions adopted by the bodies of two multilateral environmental

agreements on chemicals and wastes.176

2.3. HCBD was listed in Annex A (elimination) to the Stockholm Convention in 2015, through an

amendment that entered into force in 15 December 2016. The current guidelines also address

unintentionally produced HCBD. It should be noted that unintentionally produced HCBD, however,

is currently not subject to the Stockholm Convention provisions.on 15 December 2016.

3bis. Unintentionally produced HCBD listed in Annex C to the Stockholm Convention

(unintentional production) are not covered by the present technical guidelines. They are covered

instead by the Technical guidelines on the environmentally sound management of wastes containing

or contaminated with unintentionally produced polychlorinated dibenzo-p-dioxins, polychlorinated

dibenzofurans, hexachlorobenzene, polychlorinated biphenyls, pentachlorobenzene, polychlorinated

naphthalenes or hexachlorobutadiene (Unintentional POPs technical guidelines) (UNEP, 201XXX

[to be updated]).

3.4. The present technical guidelines should be used in conjunction with the General technical

guidelines on the environmentally sound management of wastes consisting of, containing or

contaminated with persistent organic pollutants)” (UNEP, 2017a) [to be updated]) (hereinafter

referred to as “General technical guidelines”). The General technical guidelines are intended to serve

as an umbrella guide for the ESM of wastes consisting of, containing or contaminated with

persistent organic pollutants (POPs).

4.5. In addition, the use of HCBD as a pesticide is addressed in more detail in the Technical

guidelines on the environmentally sound management of wastes consisting of, containing or

contaminated with the pesticides aldrin, alpha hexachlorocyclohexane, beta hexachlorocyclohexane,

chlordane, chlordecone, dieldrin, endrin, heptachlor, hexachlorobenzene, hexachlorobutadiene,

lindane, mirex, pentachlorobenzene, pentachlorophenol and its salts, perfluorooctane sulfonic acid,

technical endosulfan and its related isomers or toxaphene or with hexachlorobenzene as an industrial

chemical (UNEP, 2017b).

B. Description, production, use and wastes

1. Description

5.6. HCBD (CAS No: 87-68-3) is a halogenated aliphatic compound (see structural formula in

Figure 1). It is a colorless liquid with a mild odor. HCBD is insoluble in water and denser than

water. It is not very volatile or flammable (ATSDR, 1994). Synonyms for HCBD include

perchlorobutadiene; 1,1,2,3,4,4-hexachloro-1,3-butadiene; 1,3-hexachlorobutadiene (USEPA, 2003).

Figure 1: Structural formula of HCBD

6.7. HCBD is detected in abiotic and biotic media, even in remote areas such as the Arctic (Hung,

2012). HCBD was found in surface waters, drinking water, ambient air, aquatic and terrestrial

organisms (Lee et al., 2000; Kaj and Palm, 2004; Lecloux , 2004). HCBD levels in water and fish

176 Decision BC-12/3 and BC-13/4 of the Conference of the Parties to the Basel Convention on the Control of

Transboundary Movements of Hazardous Wastes and Their Disposal; decision OEWG-10/4 and OEWG-11/3

of the Open-ended Working Group of the Basel Convention; and decision SC-7/12 of the Conference of the

Parties to the Stockholm Convention on Persistent Organic Pollutants.

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from European rivers (Rhine, Elbe) have decreased significantly over the last decades (RIWA,

2004). Due to the scarcity of data it is difficult to identify a temporal trend for remote areas.

Although recent (i.e. within the past 15 years) data on biota are very infrequent, HCBD

contamination has been reported for beluga blubber in 2003 (of up to 278 μg/kg lipid weight) and

for polar bear fat (1–9 μg/kg wet weight) from 2002. Based on the available evidence, HCBD is

persistent, bioaccumulative and very toxic to aquatic organisms and toxic to birds

(UNEP/POPS/POPRC.8/16/Add.2).

7.8. HCBD bioaccumulates strongly in rice and vegetables (Tang et al, 2014). In mid-1970s

levels of HCBD in beverages, bread, butter, cheese, eggs, fruits, meats, milk, oils and potatoes

ranging from non-detectable to 3.7 μg/kg (grapes) were reported in the United Kingdom. High

concentrations were found in eels from the river Rhine in 1993 (average concentration 55 μg/kg). In

the 1970’s concentrations around 1 mg/kg were found in fish in a lake fed by the river Rhine in

Holland (cited by Jürgens et al., 2013). Concentrations of HCBD in chicken, eggs, fish, margarine,

meat and milk ranged from non-detectable to 42 μg/kg (egg yolk) in Germany in the 1970s

(Environment Canada, Health Canada, 2000).

9. HCBD is easily absorbed and metabolized via conjugation with glutathione. This conjugate

can be further metabolized to a nephrotoxic derivative. Kidney tumours were observed in a long-

term oral study in rats. HCBD has not been shown to be carcinogenic by other routes of exposure.

IARC has placed HCBD in Group 3 (not classifiable as to its carcinogenicity to humans) in 1999

(IARC, 2017).

10. WHO has established a drinking water guideline value of 0.0006 mg/l (0.6 μg/l) (WHO,

2004, WHO, 2017) based on a tolerable daily intake of 0.2 µg/kg bodyweight and day.

2. Production

2.1 Intentional production

8.11. Parties to the Stockholm Convention must prohibit and/or eliminate the production of HCBD

and there are no exemptions under the Convention for HCBD production. HCBD is not known to be

currently intentionally produced in Europe, Japan, the United States of America (USA) or Canada.

9.12. HCBD was first prepared in 1877 by the chlorination of hexyl oxide (IARC 1979). The

commercial production in Europe stopped in the late 1970s and in Japan in the 1980s. HCBD is also

suspected to have been produced in the former USSR. Reported common trade names were Dolen-

Pur; C-46, UN2279 and GP-40-66:120 (Lecloux, 2004). HCBD has never been manufactured as a

commercial product in the USA or Canada, (USEPA, 2003; van der Honing, 2007; Canada, 2013).

However, possible remaining intentional production (particularly in quantities below the limits for

high-production volumes) in other regions cannot be excluded (UNEP/POPS/POPRC.9/13/Add.2).

There are no natural sources of HCBD in the environment (Environment Canada, Health Canada,

2000).

10.13. Intentional production of HCBD is already prohibited in Canada, the European Union,

Mexico (UNEP/POPS/POPRC.9/13/Add.2), and in Japan (MoHLW, 2018).

2.2 Unintentional production

11. HCBD is produced unintentionally in the:

(i) Production of certain chlorinated hydrocarbons, particularly of perchloroethylene,

trichloroethylene, and carbon tetrachloride (Table 1; Lecloux, 2004;

UNEP/POPS/POPRC.9/13/Add.2177);

(j) Production of magnesium (Deutscher and Cathro, 2001, Van der Gon et. al, 2007).

Fifteen to twenty grams of HCBD arise per tonne of manufactured magnesium (German Federal

Environment Agency, 2015);

(k) Incineration processes e.g. motor vehicle emissions, incineration processes of

acetylene, uncontrolled incineration of chlorine residues, incineration of hazardous waste, municipal

waste, clinical waste, and plastic containing waste (Lenoir et al, 2001; German Federal Environment

Agency, 2015; UNEP/POPS/COP.8/15);

(l) Production of polyvinyl chloride, ethylene dichloride and vinyl chloride monomer,

although this is reported as unlikely from a technological point of view, according to a dossier

177 Revised draft evaluation of new information in relation to the listing of hexachlorobutadiene in Annex C to

the Stockholm Convention (Unintentional Production)

UNEP/CHW.14/INF/9

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prepared for the European chloralkali industry (Lecloux, 2004; Van der Gon et. al, 2007).

12. Information on unintentional HCBD production is scarce. High volumes were produced

unintentionally in chlorination processes involving organic compounds during the 1970s and 1980s.

The worldwide unintentional production of HCBD in heavy fractions was estimated at 10,000

tonnes in 1982 (Lecloux, 2004). In the USA alone, the estimated annual HCBD generation was

3,600 tonnes in 1975, and 12,000 tonnes in 1982 (USEPA, 2003). In 2000, 15,000 tonnes of HCBD

was produced unintentionally in the USA (Lecloux, 2004). The unintentionally produced HCBD has

been regarded as waste, although it is known to have also been sold partly for commercial uses

(BUA, 1991/2006; UNEP/POPS/POPRC.9/13/Add.2).

13. The reported European volumes of unintentionally produced of HCBD were in the same

range as in North America. In the European Union in 1980 (EU-10), about 10,000 tonnes of HCBD

were generated. In Germany, 4,500 t/year of HCBD was produced during the low-pressure

chlorolysis for combined production of perchloroethylene and tetrachloromethane in1979 ( German

Federal Environment Agency, 2015). In early 1990s the total amount of HCBD produced in

Germany was estimated at 550 – 1,400 t/year, which was partially directed back into the production

process (German Federal Environment Agency, 2015). In 1990, an HCBD formation quantity of

2,000 to 49,900 tonnes was estimated based on the production volumes of perchloroethylene and

tetrachloromethane in Western Europe (BUA, 1991/2006).

14. Processes relevant for the unintentional production of HCBD in the production of chlorinated

chemicals are shown in Table 1. Many countries have introduced requirements to reduce

unintentional production e.g. via use of best available technologies (BAT)

(UNEP/POPS/POPRC.9/13/Add.2). Chlorinated solvents are produced in many countries in the

world in large quantities. Information on the amounts of HCBD in waste from one European

producer of chlorinated solvents including perchloroethylene is shown in Table 2.

Table 1: Processes relevant for the unintentional production of HCBD in chlorinated chemicals

production (BUA, 1991/2006; UNEP/POPS/POPRC.9/13/Add.2).

Process HCBD concentration

in the raw product

Remarks

Low pressure chlorolysis

for the manufacturing of

perchloroethylene and

carbon tetrachloride

5%

(50 000 ppm)

HCBD is fed back into the process

together with other high-boiling by-

products to carbon tetrachloride and

perchloroethylene (Lecloux, 2004) or

residues containing HCBD are directly

incinerated on site (German Federal

Environment Agency, 2015).

Optimised low pressure

chlorolysis for the

manufacturing of

perchloroethylene and

carbon tetrachloride

0.2 to 0.5%

(2000 to 5000 ppm)

The HCBD containing residue is treated

by distillation which results in a residue

containing 7 to 10% HCBD (70 000-

100 000 ppm). The latter residue is

incinerated.

Manufacturing of

hexachlorocyclopentadiene

0.2 to 1.11 %

(2000 to 11 100 ppm)

Manufacturing of

tetrachloride and

trichloroethylene from

acetylene and chlorine and

subsequent decomposition

to carbon tetrachloride and

trichloroethylene

0.4%

(4000 ppm)

Table 2: Volumes of HCBD in waste by a producer of chlorinated solvents including

perchloroethylene (Spolchemie in Ústi nad Labem) as reported in the Czech PRTR system. (Source:

http://www.irz.cz, 2016)

2004 2005 2006 2007 2008 2009 2010

HCBD in t/year 161 178 194 175 140 66 162

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3. Use178

15.14. Parties to the Stockholm Convention must prohibit and/or eliminate the use of HCBD, and

there are no exemptions under the Convention for the use of HCBD. The same provision (Article 3)

applies to the use of unintentionally produced HCBD. There is no information on on-going uses of

HCBD available. In the past HCBD has been used, for example, as a solvent (for rubber, elastomers

and other polymers, for carbon-tetrachloride (C4) and higher hydrocarbons), intermediate in the

production of fluor-containing lubricants, a “scrubber” to recover chlorine-containing gas or to

remove volatile organic components from gas, hydraulic fluid, heat transfer liquid (in combination

with trichloroethene) or a non-flammable insulating liquid in transformers, fluid in gyroscopes, in

the production of aluminium and graphite rods, and as a plant protection product. There is no

specific information available on any existing applications of HCBD and all applications seem to

have ceased, but cannot be fully excluded. (Environment Canada, Health Canada, 2000,

UNEP/POPS/POPRC.9/13/Add.2, German Federal Environment Agency, 2015).

16.15. Prior to 1975 the largest use of HCBD in the USA was for the recovery of “snift” (chlorine

containing gas in chlorine plants). HCBD is no longer used for this process, however (ATSDR,

1994). HCBD was mainly used as a chemical intermediate in the manufacture of rubber compounds

and that lesser quantities were used as solvent, fluid for gyroscopes, heat transfer liquid, hydraulic

fluid, chemical intermediate in the production of chlorofluorocarbons and lubricants, laboratory

reagent (ATSDR, 1994). In Canada HCBD is no longer used as a solvent (Environment Canada,

Health Canada, 2000).

17.16. HCBD was used as a seed-dressing fungicide or insecticide in vineyards in the former USSR

(application rate of 100-350 kg/ha), in Mediterranean European countries and in Argentina

(Lecloux, 2004; Van der Honing, 2007; German Federal Environment Agency, 2015). In France the

fumigant use was extensive and discontinued in 2003 (European Commission, 2011). It is unclear

whether HCBD is still used as a plant protection product anywhere.

18.17. A method using HCBD to synthesize graphite sheets has been developed relatively recently.

Graphite flakes are used as electronically conducting fillers in the production of conducting polymer

composites in various fields such as fuel cell electrodes, corrosion resistant materials, batteries etc.

(Shi et al., 2004). However, there is no information on whether HCBD is actually used for this

purpose anywhere.

4. Wastes

19.18. Action aimed at waste streams of importance in terms of volume and concentration will be

essential to eliminating, reducing and controlling the environmental load of HCBD from waste

management activities. In that context, the following should be recognized:

(a) The uses of HCBD have apparently ceased, although there are uncertainties related to

plant protection use as vineyard fumigant in the former USSR;

(b) HCBD releases can arise from the disposal of old HCBD-containing products that

have become waste. Some of the HCBD applications (e.g. hydraulic, heat transfer or transformer

fluids) have a long service-life and despite the uses being ceased, HCBD may still enter the waste

management stage. HCBD can still be present in rubber compounds in marginal amounts according

to the national association on rubber and polymers in France (Syndicat National du Caoutchouc et

des Polymères according to German Federal Environment Agency, 2015). There is no further

information on possible HCBD residues when used as a chemical intermediate in rubber, elastomer,

or lubricant production. However, in a recent study by German Federal Environment Agency

(2015), HCBD was not found relevant in any waste streams in Germany;

(c) Landfills may be a source of HCBD from disposal of HCBD containing products that

have become waste (e.g. hydraulic, cooling and absorbent liquids, HCBD waste from chemical

production (typically containing 33-80% HCBD), lining (ebonite) and graphite electrodes removed

from chlorine electrolysis cells containing traces of HCBD) (Lecloux, 2004). There is no insight into

the total amount of waste sites worldwide, nor on their releases (UNEP/POPS/POPRC.9/13/Add.2).

In Europe disposal practices of HCBD wastes from unintentional production from chemical and

magnesium production have shifted from landfilling to incineration (ATSDR, 1994);

(d) Sites where HCBD pesticides have been used may be highly contaminated. Soils in

vineyards infected with Phylloxera were treated with 250 kg/ha HCBD, were contaminated to the

178 “Use” covers the use of HCBD for the production of products and articles, as well as the use of those

products and articles.

Commented [EU and MS34]: Part of this sentence is

shown deleted in the document, preventing it from

being understood. We prefer that this text is kept.

UNEP/CHW.14/INF/9

179

level of 7.3 mg/kg after 8 months and 3 mg/kg after 32 months (Vorobyeva (1980) - – the original

reference is only available in Russian). However, after 24 months HCBD could not be found in the

study;

(e) Old chemicals industry sites may be contaminated by HCBD. In the United States, soil

concentration of up to 980 mg/kg were found at chemicals industry sites (Li et al., 1976). Examples

of such contamination can also be found in Europe (Barnes et al. 2002);

(f) HCBD can be unintentionally produced during waste incineration (e.g. incineration of

municipal waste, clinical waste and hazardous waste) and could be found in incineration residues

(ashes and slag). However, HCBD was not found in two slag samples above the detection limits in

Germany in 2015 (German Federal Environment Agency, 2015).

20.19. Historical landfilling of heavy fractions from the production of chlorinated organic

substances and perchloroethylene use can also lead to secondary HCBD emissions or leachates to

water and soil via sewage sludge (ASDTR, 1994, Staples, 2003, Lecloux, 2004, European

Commission, 2011). Concentration of HCBD in waste depends on the quantities in which HCBD

was originally present in specific products and the quantities released during product use and waste

management. However, based on the known uses wastes consisting of, containing or contaminated

with HCBD (hereinafter referred to as “HCBD wastes”) may potentially be found in:

(a) HCBD chemical, including intentionally produced HCBD and unintentionally

produced HCBD from chlorinated solvent production and magnesium production;

(b) Residues (ashes and slag) from incineration of unintentionally produced HCBD from

chlorinated solvent production, incineration of municipal, clinical and hazardous waste;

(c)(b) Electrical transformers;

(d)(c) Heat exchangers;

(e)(d) Electrical hydraulic fluids, cooling and absorbent liquids;

(f)(e) Other industrial electrical equipment, including removed lining (ebonite) and graphite

electrodes from chlorine electrolysis cells;

(g)(f) Rubber compounds;

(h)(g) Sludge from municipal and industrial sewage treatment;

(i)(h) Contaminated soils and sediments from use or disposal of HCBD;

(j)(i) Agricultural insecticides and fungicides.

21.20. The most important HCBD waste streams in terms of potential volume are expected to be:

(g) Waste gas and liquid from the production of chlorinated solvents and magnesium

(unintentional production of HCBD);

(h)(g) Soils and sediments contaminated from substandard HCBD disposal;

(i)(h) Soils and sediments contaminated from HCBD applied as plant protection;

(j)(i) Obsolete insecticides and fungicides;

(k)(j) Transformer fluids;

(l)(k) Heat exchanging fluids.

22.21. The most important HCBD waste streams in terms of potential releases or concentration of

HCBD are expected to be:

(k) Waste gas and liquid from the production of chlorinated solvents and magnesium

(unintentional production of HCBD);

(l)(k) Sludge from municipal and industrial sewage treatment;

(m) Ashes and slag from waste incineration;

(n)(l) Obsolete HCBD insecticide and fungicide waste;

(o)(m) Transformer, heat exchange and hydraulic fluids.

23.22. HCBD wastes can be generated in a diverse range of applications, at different stages of the

life cycle and through different release media. Knowledge of release media guides the analysis and

UNEP/CHW.14/INF/9

180

choice of methods that may be used to manage such wastes. Many of these applications are assumed

to have been phased out. Table 3 provides an overview of relevant information regarding the life

cycle of HCBD wastes.

Table 3: Overview of the production and application of HCBD and their release media into the environment

(Based on Van der Honing, 2007; UNEP/POPS/POPRC.8/16/Add.2 and UNEP/POPS/POPRC.9/13/Add.2).

UNEP/CHW.14/INF/9

181

Group Source materials

/Substance used

Applications

/Processes

End Product Release Media

HCBD PRODUCTION

Ch

em

ical

Pro

du

cti

on

Chlorine, hexyl

iodide (original

intentional

production process)

Chemical synthesis HCBD

• Solid waste

• Industrial waste

water

• Sludge from

waste water

treatment

• Air

Production of

perchloroethylene,

trichloroethylene and

carbon tetrachloride

Chlorinated hydrocarbons (e.g.

tetrachloromethane,

Halon 104, Freon 10 etc.),

residual HCBD

Optimised low-pressure

chlorolysis for the

production of

tetrachloroethene and

tetrachloromethane

0.2-0.5% HCBD in the raw

product. The residue finally

obtained from the process

contains after distillation 7-

10% HCBD

Acetylene, chlorine Production of 1,1,2,2-

tetrachloroethane (no

longer used according

to UNECE, 2007)

0.4% HCBD

Production of polyvinyl

chloride, ethylene

dichloride and vinyl

chloride monomer

Production of articles containing HCBD

Ch

em

ical

ap

pli

ca

tion

s

HCBD + unknown Production of

transformer fluids

Transformer fluids

• Solid waste

• Landfill leachate

• Industrial and

municipal

waste water

• Sludge from

waste water

treatment

• Air

HCBD + unknown Production of heat

exchange fluids

Heat exchange fluids

HCBD + unknown Production of fluor-

containing hydraulic

fluids

Hydraulic fluids (HCBD

residues unknown)

Unknown Solvent in production

of rubber and

elastomers

HCBD residues unknown

HCBD + unknown Production of HCBD

plant protection

products

HCBD insecticides and

fungicides

USE OF PRODUCTS AND ARTICLES CONTAINING HCBD

(The boxes below include articles that have become wastes. Such wastes may also be generated at production sites)

Ele

ctri

cal

equ

ipm

ent

Transformer fluids Transformer fluid waste,

contaminated transformers • Solid waste

• Landfill leachate

• Liquid industrial

waste

• Sludge from

waste water

treatment

• Air

•

Hydraulic fluids Hydraulic fluid waste,

contaminated hydraulic

equipment

Gyroscopes Gyroscope fluid waste,

contaminated equipment

Agri

cult

ur

al

chem

icals

Agricultural

insecticides and

fungicides

Obsolete pesticide waste (see

UNEP, 2017b)[…])

Incineration processes

UNEP/CHW.14/INF/9

182

II. Relevant provisions of the Basel and Stockholm

conventions

A. Basel Convention

24.23. Article 1 (“Scope of the Convention”) defines the waste types subject to the Basel

Convention. Subparagraph 1 (a), of that Article sets forth a two-step process for determining if a

“waste” is a “hazardous waste” subject to the Convention. First, the waste must belong to any

category contained in Annex I of the Convention (“Categories of wastes to be controlled”). Second,

the waste must possess at least one of the characteristics listed in Annex III of the Convention (“List

of hazardous characteristics”).

25.24. Annex I lists some of the wastes which may consist of, contain or be contaminated with

HCBD:

(a) Y4: Wastes from the production, formulation and use of biocides and

phytopharmaceuticals;

(b) Y6: Wastes from the production, formulation and use of organic solvents;

(c) Y9: Waste oils/water, hydrocarbons/water mixtures, emulsions;

(d) Y10: Waste substances and articles containing or contaminated with polychlorinated

biphenyls (PCBs) and/or polychlorinated terphenyls (PCTs) and/or polybrominated biphenyls

(PBBs);

(e) Y18: Residues arising from industrial waste disposal operations;

(f)(b) Y41: Halogenated organic solvents.

(c) Y45: Organohalogen compounds other than substances referred to in this

Annex (e.g. Y39, Y41, Y42, Y43, Y44).

26.25. Annex I wastes are presumed to exhibit one or more Annex III hazard characteristics, which

may include H6.1 “Poisonous (acute), H8 “Corrosive”, H11 “Toxic (delayed or chronic)”; H12

“Ecotoxic”; or H13 (capable after disposal of yielding a material which possess a hazardous

characteristic)”, unless, through “national tests,” they can be shown not to exhibit these

characteristics. National tests may be useful for identifying a particular hazard characteristic in

Annex III of the Convention until such time as the hazardous characteristic is fully defined.

Guidance papers for Annex III hazardous characteristics H11, H12 and H13 were adopted on an

interim basis by the Conference of the Parties to the Basel Convention at its sixth and seventh

meeting.

27.26. List A of Annex VIII of the Convention describes wastes that are “characterized as hazardous

under article 1, paragraph 1 (a), of this Convention.” However, “[d]esignation of a waste on Annex

VIII does not preclude, in a particular case, the use of Annex III [List of hazardous characteristics]

to demonstrate that a waste is not hazardous” (Annex I, paragraph (b)). List A of Annex VIII

includes a number of wastes or waste categories that have the potential to contain or be

contaminated with HCBD, including:

(a) A1180: Waste electrical and electronic assemblies or scrap containing components

such as accumulators and other batteries included on list A, mercury-switches, glass from cathode-

ray tubes and other activated glass and PCB-capacitors, or contaminated with Annex I constituents

(e.g. cadmium, mercury, lead, polychlorinated biphenyl) to an extent that they possess any of the

characteristics contained in Annex III (note the related entry on list B B1110);

(b) A3040: Waste thermal (heat transfer) fluids;

(c) A3160: Waste halogenated or unhalogenated non-aqueous distillation residues arising

from organic solvent recovery operations;

Inci

nera

tion

of

wa

ste

Incineration of HCBD

waste from production

of chlorinated solvents

Incineration of

municipal, clinical and

hazardous waste

• Air

• Solid waste (slag

and ashes)

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(d) A3170: Wastes arising from the production of aliphatic halogenated hydrocarbons

(such as chloromethane, dichloro-ethane, vinyl chloride, vinylidene chloride, allyl chloride and

epichlorhydrin);

(e) A4030: Wastes from the production, formulation and use of biocides and

phytopharmaceuticals, including waste pesticides and herbicides which are off-specification,

outdated or unfit for their originally intended use;

(f) A4060: Waste oils/water, hydrocarbons/water mixtures, emulsions;

(g) A4100: Wastes from industrial pollution control devices for cleaning of industrial off-

gases but excluding such wastes specified on list B;

(h (a) A4130: Waste packages and containers containing Annex I substances in

concentrations sufficient to exhibit Annex III hazard characteristics;

(ib) A4140: Waste consisting of or containing of specification or outdated chemicals

corresponding to Annex I categories and exhibiting Annex III hazard characteristics;

(jc) A4160: Spent activated carbon not included on list B (note the related entry on list B

B2060).

28. List B of Annex IX lists wastes that will not be wastes covered by Article 1, paragraph 1 (a),

unless they contain Annex I material to an extent causing them to exhibit an Annex III

characteristic. List B of Annex IX includes a number of wastes or waste categories that have the

potential to contain or be contaminated with HCBD, including:

29. B1040: Scrap assemblies from electrical power generation not contaminated with lubricating

oil, PCB or PCT to an extent to render them hazardous;

B1110: Electrical and electronic assemblies;179

30.27. B2060: Spent activated carbon not containing any Annex I constituents to the extent they

exhibit Annex III characteristics.;

(a) B3040: Rubber wastes

The following materials, provided they are not mixed with other wastes:

• Waste and scrap of hard rubber (e.g., ebonite);

• Other rubber wastes (excluding such wastes specified elsewhere).

31.28. For further information, see section II.A of the General technical guidelines.

B. Stockholm Convention

32.29. The present guidelines cover intentionally- produced HCBD, whose production and use are

to be eliminated in accordance with Article 3 and part I of Annex A to the Stockholm Convention.

33.30. For further information, see section II.B of the General technical guidelines.

III. Issues under the Stockholm Convention to be addressed

cooperatively with the Basel Convention

A. Low POP content

34.31. The provisional definition of low POP content for HCBD is 100 mg/kg.180

35.32. The low POP content described in the Stockholm Convention is independent from the

provisions on hazardous waste under the Basel Convention.

36.33. Wastes with a content of HCBD above 100 mg/kg must be disposed of in such a way that the

POP content is destroyed or irreversibly transformed in accordance with the methods described in

subsection IV.G.2. Otherwise, they may be disposed of in an environmentally sound manner when

179 Refer to Annex IX to the Basel Convention for a full description of this entry. 180 Determined according to national or international methods and standards.

UNEP/CHW.14/INF/9

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destruction or irreversible transformation does not represent the environmentally preferable option

in accordance with the methods described in subsection IV.G.3.

37.34. Wastes with a content of HCBD at or below 100 mg/kg should be disposed of in accordance

with the methods referred to in subsection IV.G.4 of the General technical guidelines (outlining

disposal methods when POP content is low), taking into account section IV.I.1 below (pertinent to

higher-risk situations).

38.35. For further information on low POP content, refer to section III.A of the General technical

guidelines.

B. Levels of destruction and irreversible transformation

39.36. For the provisional definition of levels of destruction and irreversible transformation, see

section III.B of the General technical guidelines.

C. Methods that constitute environmentally sound disposal

40.37. See section IV.G below and section IV.G of the General technical guidelines.

IV. Guidance on environmentally sound management (ESM)

A. General considerations

41.38. For further information, see section IV.A of the General technical guidelines.

B. Legislative and regulatory framework

42.39. Parties to the Basel and Stockholm conventions should examine their national strategies,

policies, controls, standards and procedures to ensure that they are in agreement with the two

conventions and their obligations under them, including those that pertain to ESM of HCBD wastes.

43.40. Elements of a regulatory framework applicable to HCBD should include measures to prevent

the generation of wastes and to ensure the ESM of generated wastes. Such elements could include:

(o) Environmental protection legislation establishing a regulatory regime, setting release

limits and establishing environmental quality criteria;

(p) Prohibitions on the production, sale, use, import and export of HCBD;

(q) A requirement that BAT and best environmental practices (BEP) be employed in the

unintentional production and use of HCBD. Relevant BAT is specified e.g. in the BREF Document

on production of Large Volume Organic Chemicals (EC BREF LVOC, 2003 (currently being

updated) and Section VI.B Part III Chapter 4 of the UNEP BAT and BEP guidelines (UNEP, 2007);

(r)(q) Measures to ensure that HCBD wastes cannot be disposed of in ways that may lead to

recovery, recycling, reclamation, direct reuse or alternative uses of HCBD;

(s)(r) Adequate ESM controls to separate HCBD-containing materials from materials that

can be recycled (e.g., non-HCBD containing hydraulic fluids);

(t)(s) Transportation requirements for hazardous materials and waste;

(u)(t) Specifications for containers, equipment, bulk containers and storage sites for HCBD

wastes;

(v)(u) Specification of acceptable analytical and sampling methods for HCBD;

(w)(v) Requirements for waste management and disposal facilities;

(x)(w) Definitions of hazardous waste and conditions and criteria for the identification and

classification of HCBD wastes as hazardous wastes;

(y)(x) A general requirement for public notification and review of proposed government

waste-related regulations, policies, certificates of approval, licences, inventory information and

national releases and emissions data;

(z)(y) Requirements for identification, assessment and remediation of contaminated sites;

(aa)(z) Requirements concerning the health and safety of workers;

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(bb)(aa) Legislative measures on, e.g., waste prevention and minimization, inventory

development and emergency response.

44.41. For further information, see section IV.B of the General technical guidelines.

C. Waste prevention and minimization

45.42. Both the Basel and Stockholm conventions advocate waste prevention and minimization. The

production and use of HCBD are to be eliminated under the Stockholm Convention.

46.43. Quantities of waste containing HCBD should be minimized through isolation and separation

of those wastes from other wastes at source in order to prevent their mixing with, and contamination

of, other waste streams.

47.44. The mixing and blending of wastes with HCBD content above 100 mg/kg with other

materials solely for the purpose of generating a mixture with a HCBD content at or below 100

mg/kg are not environmentally sound. Nevertheless, the mixing or blending of materials as a pre-

treatment method may be necessary in order to enable treatment or to optimize treatment efficiency.

48.45. For further information, see section IV.C on waste prevention and minimization of the

General technical guidelines.

D. Identification of wastes

49.46. Article 6, paragraph 1 (a), of the Stockholm Convention requires each Party to, inter alia,

develop appropriate strategies for the identification of products and articles in use and wastes

consisting of, containing or contaminated with POPs. The identification of HCBD wastes is the

starting point for their effective ESM.

50.47. For general information on identification and inventories, see section IV.D of the General

technical guidelines.

1. Identification

51.48. HCBD wastes can be found in the following stages of the HCBD life cycle:

(a) HCBD manufacturing and processing:

(i) Waste generated from the production and processing of HCBD, including as

unintentional production;

(ii) In water, soil or sediment close to manufacturing, processing sites;

(iii) Industrial wastewater and sludge;

(iv) Leachate from landfills where chemical manufacturing or processing waste

was disposed of;

(v) Stockpiles of unusable or unsellable material;

(b) Industrial applications of HCBD (production of rubber and elastomers, manufacture of

transformer, heat exchange, and hydraulic fluids, use as a chemical in chlorine capture):

(i) Residues generated from the application of HCBD;

(ii) In water, soil or sediments close to manufacturing or processing sites;

(iii) Industrial wastewater and sludge;

(iv) Leachate from landfills where waste from industrial applications was disposed

of;

(v) Stockpiles of unusable or unsellable products;

(c) Use of products or articles containing HCBD (e.g. HCBD insecticides and fungicides,

transformers, hydraulic systems, gyroscopes):

(d)(c) In water, soil or sediments close to sites where such products were used;

(e)(d) Disposal of products or articles containing HCBD:

(i) In certain facilities for the collection, recycling and recovery of electronic and

electrical equipment, and;

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(ii) In municipal and industrial landfills and leachate;

(iii) In municipal and industrial wastewater and sludge.

52.49. It should be noted that even experienced technical personnel may not be able to determine the

nature of an effluent, substance, container or piece of equipment by its appearance or markings.

Consequently, Parties may find the information on production, use and types of waste provided in

section I.B of the present guidelines useful in identifying articles and mixtures containing HCBD. It

is believed, however, that intentional use of HCBD has ceased.

2. Inventories

53.50. When developing HCBD inventories, it is important to consider the service lives of HCBD-

containing articles and the timing of their placement on the market. While there have been diverse

industrial uses for HCBD, it appears that it is not present in consumer articles, excluding agricultural

pesticides. In addition, several industrial uses have been phased out at least 10-20 years ago. It is

possible, however, that obsolete products and articles with long service-life still enter the waste

stage.

51. A draft guidance document for the development of HCBD inventories is available (UNEP

2017e).

54.52. The first step that should be taken when developing HCBD inventories is the identification of

the types of industries that may have been producing HCBD. Large quantities of HCBD are formed

unintentionally in chlorinated solvents and magnesium production. It has also been used in the

production of e.g. rubbers, elastomers, hydraulic and transformer fluids or agricultural pesticides.

Inventories should, as appropriate, be based on information on:

(a) Production of HCBD within a country;

(b) Industrial use of HCBD;

(b) Imports and exports of products and articles containing HCBD;

(c) Use of products and articles containing HCBD in the country;

(d) Current and past regulatory requirements e.g. regarding electronic equipment,

transformer and hydraulic fluids;

(e) Disposal of HCBD wastes, including incineration;

(f) Imports and exports of HCBD wastes.

55.53. The preparation of inventories requires cooperation between those producing the inventories

and relevant actors, such as the industry producing chlorine solvents; electricity companies; rubber

and elastomer producers; customs officials; agricultural experts; personnel at waste disposal and

recycling facilities; and national focal points under the Basel and Stockholm Conventions. In some

cases, government regulations may be required to ensure those who hold HCBD wastes report their

holdings and cooperate with government inspectors.

E. Sampling, analysis and monitoring

56.54. For general information on sampling, analysis and monitoring, see section IV.E of the

General technical guidelines.

57.55. Sampling, analysis and monitoring procedures should be established for articles that may

contain HCBD.

1. Sampling

58.56. Sampling serves as an important element for identifying and monitoring environmental

concerns and human health risks.

59.57. Standard sampling procedures should be established and agreed upon before the start of the

sampling campaign. Sampling should comply with specific national legislation, where it exists, or

with international regulations and standards. Documented sampling methods exist for HCBD in air

(NIOSH Method 2543).

60.58. Types of matrices that are typically sampled for HCBD include:

(a) Liquids:

(i) Leachate from dumpsites and landfills;

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(ii) Water (surface water and groundwater, drinking water, and industrial and

municipal effluents);

(iii) Biological fluids (blood, in the case of worker health monitoring);

(b) Solids:

(i) Sewage sludge;

(ii) Biological samples (adipose tissue);

(iii) Stockpiles of mixtures and articles consisting of, containing or contaminated

with HCBD;

(c) Gases:

(i) Air (indoor and outdoor);

(ii) Exhaust gas.

2. Analysis

61.59. Analysis refers to the extraction, purification, separation, identification, quantification and

reporting of HCBD concentrations in the matrix of interest. In order to obtain meaningful and

acceptable results, analytical laboratories should have the necessary infrastructure (housing) and

proven experience.

62.60. The development and dissemination of reliable analytical methods and the accumulation of

high-quality analytical data are important to understand the environmental impact of hazardous

chemicals, including POPs.

63.61. HCBD can be analysed together with organochlorine pesticides (see Pesticides technical

guidelines, UNEP 2017, xx [to be updated]). Methods to analyze HCBD with gas chromatography

with electron-capture (GC-ECD) as well as gas chromatography with mass spectrometer (GC-MS)

have been developed for biota (at least fish, vegetable, eggs, milk extracts, vegetables), wastewater

and soils (e.g. EPA Method 612, APHA Method 6410B, APHA Method 6200B) (HSDB 2016,

Majoros et al., 2013).2013) and water (WHO, 2004). EPA Methods 612 and 625 can be used for

analysis of HCBD in industrial and municipal wastewater. The Drinking Water Guideline of WHO

reports limits of detection of HCBD in drinking water of 0.01 μg/l by GC-MS; 0.18 μg/l by GC with

ECD (WHO, 2017).

3. Monitoring

64.62. Monitoring and surveillance serve as elements for identifying and tracking environmental

concerns and human health risks. Information collected from monitoring programmes feeds into

science-based decision-making processes and is used for the evaluation of the effectiveness of risk

management measures, including regulations. The control of the WHO drinking water quality

guideline limit value may serve as an orientation in drinking water programmes (WHO, 2017).

65.63. Monitoring programmes should be implemented in facilities managing HCBD and HCBD

wastes and on sites that have been contaminated by HCBD (e.g. water bodies, landfills and

dumpsites).

F. Handling, collection, packaging, labelling, transportation and storage

66.64. For information, see section IV.F of the General technical guidelines.

1. Handling

67.65. Organizations handling HCBD wastes should have in place a set of procedures for handling

such wastes and workers should be trained in such procedures.

2. Collection

68.66. Collection arrangements that include depots for HCBD wastes should provide for the

separation of HCBD wastes from other wastes.

69.67. Collections depots should not become long-term storage facilities for HCBD wastes.

3. Packaging

70.68. In cases where HCBD wastes are considered hazardous wastes, they should be properly

packaged before storage in accordance with the applicable provisions of national legislation.

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4. Labelling

71.69. In cases where HCBD wastes are considered hazardous wastes, every container carrying

HCBD waste should be clearly labelled with a hazard warning label and a label providing details of

the container and a unique serial number. Such details should include container contents (e.g., exact

counts of equipment, volume, weight, type of waste carried), the name of the site from which the

waste originated so as to allow its traceability, the date of any repackaging and the name and

telephone number of the person responsible for the repackaging operation.

5. Transportation

72.70. In cases where HCBD wastes are considered hazardous wastes, they should be transported in

accordance with applicable provisions of national legislation.

6. Storage

73.71. HCBD wastes should be stored in designated sites and appropriate measures should be taken

to prevent the scattering, release and underground seepage of HCBD, and to control the spread of

odors.

74.72. Appropriate measures, such as the installation of partitions, should be taken to avoid

contamination of other materials and wastes with HCBD.

75.73. Storage areas for HCBD wastes should have adequate access roads for vehicles.

76.74. Large amounts of HCBD wastes in storage should be protected from fire.

G. Environmentally sound disposal

1. Pre-treatment

77.75. For information, see subsection IV.G.1 of the General technical guidelines.

2. Destruction and irreversible transformation methods

78.76. For information, see subsection IV.G.2 of the General technical guidelines.

3. Other disposal methods when neither destruction nor irreversible transformation is not the

environmentally preferable option

79.77. For information, see subsection IV.G.3 of the General technical guidelines.

4. Other disposal methods when the POP content is low

80.78. For information, see subsection IV.G.4 of the General technical guidelines.

H. Remediation of contaminated sites

81.79. For information, see section IV.H of the General technical guidelines.

I. Health and safety

82.80. For information, see section IV.I of the General technical guidelines.

1. Higher-risk situations

83.81. For general information, see subsection IV.I.1 of the General technical guidelines.

84.82. Higher-risk situations occur at sites where high concentrations of HCBD or high volumes of

HCBD wastes are found and a high potential for exposure of workers or the general population

exists. Direct dermal exposure to and inhalation of fine dust or particles containing HCBD in the

workplace are of particular concern.

85.83. Higher-risk situations specific to HCBD may occur:

(a) At sites where HCBD is unintentionally produced;

(b) At sites where HCBD wastes have been disposed of;

(cb) At sites where HCBD is used:;

(dc) At waste electrical equipment management facilities.

2. Lower-risk situations

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86.84. For information on lower risk situations, see subsection IV.I.2 of the General technical

guidelines.

J. Emergency response

87.85. Emergency response plans should be in place at sites where HCBD is produced, used, stored,

transported or disposed of. Further information on emergency response plans is given in section IV.J

of the General technical guidelines.

K. Public participation

88.86. Parties to the Basel or Stockholm Convention should have open public participation

processes. For further information see section IV.K of the General technical guidelines.

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