Nitrogen in biowaste and yard waste compost: dynamicsof mobilisation and availability—a review

Florian Amlingera,*, Bettina Götzb, Peter Dreherc, Jutta Gesztia,Christof Weissteinera

a Compost—Consulting & Development, Hochbergstr. 3, 2380 Perchtoldsdorf, Austriab Environment Agency Austria, Spittelauer Lände 5, 1090 Wien, Austria

c Fraunhofer Institute Environmental Chemistry and Ecotoxicology, Auf dem Aberg 1, 57392 Schmallenberg, Germany

Accepted 6 May 2003

Abstract

According to the Austrian Water Act, the maximum permitted nitrogen load from fertilisers is 175 and 210 kg N ha–1 year–1

for arable land and for grassland, respectively. In organic farming, the maximum life stock related N load is restricted to 170 kgha–1year–1. In the regulations of theAustrian Program for Environmentally SoundAgriculture, it is assumed that 25% of the totalN in fresh manure are available to plants in the first year, a value that may be disputed. Compared to other forms of fertiliser(mineral, slurry, animal manure or sewage sludge), biowaste compost leads to an enhanced enrichment of organic (humus–)nitrogen in the soil. Depending on the cultivation system a site-specific humus content and C/N ratio will be reached. In thepresent paper, several studies on N–mineralisation from composts are compiled.As a rule the immediate N–effect in the first yearis less than 15% (5–15%) of the Ntotal–supply by compost followed by 2–8% year–1of the remaining compost-N in the followingyears. Model calculations show that the balance between compost-N supply and N–uptake and losses will be obtained withinperiods of 40–100 years when compost is applied regularly. Improved knowledge of the C– and N–turnover from composts andin the soil organic matter pools will be the key to a specific control of the system including the potential negative impact on theground water.

© 2003 Éditions scientifiques et médicales Elsevier SAS. All rights reserved.

Keywords: Compost; Nitrogen availability; Nitrogen mineralisation; Nitrogen leaching; C/N ratio; Soil organic matter

1. Introduction

The assessment of compost nitrogen dynamics under fieldconditions is discussed broadly in agricultural and environ-mental forums. In Austria, the following legal limitationsapply to this assessment:

1. According to the Austrian Water Act (National LawGazette Nr. 215/1959)[35], the application of nitrogenwithout authorisation is limited to a maximum annualload of 175 kg and 210 kg ha–1 on arable or pastureland, respectively.

2. EC Regulation No. 1804/1999 (based on RegulationNo. 2092/91/EEC)[41] for Organic Farming limits themaximum load of manure-N to 170 kg ha–1 year–1.

3. The Austrian program ÖPUL 2000[9] based on the“Richtlinien für eine sachgerechte Düngung”[7,8] as-sumes that 15–25% of the compost-N is effective in thefirst year of application.

4. The Austrian Action Program[8] for the implementa-tion of the EC Nitrate Directive (Directive91/676/EEC, 1991) limits N application through dungwith 210 kg ha–1 year–1 before and 170 kg ha–1 year–1

after 18 December 2002.

Although various site-specific factors (e.g., compost ma-terial, composting conditions, climate and soil properties,

* Corresponding author.E-mail address: f.amlinger@kabsi.at (F. Amlinger).

European Journal of Soil Biology 39 (2003) 107–116

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© 2003 Éditions scientifiques et médicales Elsevier SAS. All rights reserved.doi:10.1016/S1164-5563(03)00026-8

soil management practices) may affect N–dynamics in com-post amended soils, it can be generally assumed that theavailability of N to plants is low since the majority (>90%) oftotal compost N is bound to the organic N–pool [4]. Localrequirements and sound plant nutrition management, there-fore, need to consider the availablility and binding dynamicsof total compost N in soils during the short and long term.Nitrogen load as well as its mobilisation rate is stronglylinked to the level of soil organic matter (SOM) and to therelative magnitude of the active fraction of the total SOM, orto the more passive pool which is currently undergoingalteration [37].

Fig. 1 gives a basic scheme of the considered C–Pools andtheir resistance against degradation. Since the question of Nimmobilisation/mobilisation is predominantly linked to thedegradability and balance of soil C pools the understandingthereof is essential.

2. General aspects of N–mobilisationand immobilisation

The microbial transformation (mineralisation, ammonifi-cation, nitrification, denitrification) of compost nitrogen insoil follows the general scheme:

[ammonification;step 1]

(humus)-R-NH2 + H2O → NH3 + R-OH

[ammonification;step 2]

↑NH3 + H2O → NH4+ + OH−

[Nitrosomonas]

[nitrification;step 1]

2NH4+ + 3O2

→ NO2− + 2H2 O + 2H+

[Nitrosomonas]

[nitrification;step 2]

2NO2− + O2

→ 2NO3−

[denitrification;general sheme]

2NO3− + 10e− + 12H+ → N2 + 6H2O

Net-immobilisation or net-mobilisation depends on thebalance of the mineral N–pool over a defined period. Both

mineralisation and immobilisation take place simultaneouslyand may not be quantified separately. Gaseous NH3–lossesalso depend on pH and temperature regime of the soil [42].Net-mineralisation (total mineralisation minus immobilisa-tion taking into consideration liquid and gaseous losses) canbe 50–150 kg N ha–1 during the vegetation period [36].

In Fig. 2, the central question of N sorption and minerali-sation processes is summarised. For judging the potentialN–release into the gas phase and the risk of leaching ofcompost-N, it would be essential to quantify the changes insoil-N-pools after compost application. A scientific view oncompost utilisation is only possible when the temporal dy-namics of the material fluxes under different site conditionscan be described.

3. Essential site and soil specific factors influencingN–mobilisation

3.1. Water content, temperature, pH value

Mineralisation is independent of water content over awide range, with significant declines only under extreme wetor dry conditions. Any increase in temperature, e.g. from 0 to10 °C may increase the mineralisation rate 2– to 3–fold [42].The pH inhibits mineralisation only at levels <5 and >8 [14].

3.2. Quality and amount of soil organic matter (SOM),C/N ratio

SOM level is a function of climate, cropping system andsoil nitrogen content [24,27]. In general, SOM level declinesas a result of soil cultivation [27]. The new balance after inputof organic material is mainly influenced by soil type, croprotation and humus management (recycling of plant resi-dues). Diez and Krauss [13] investigated the effects of com-post application in a long term field trial on yield and soilparameters on two different soils (loess loam, gravel) with

Fig. 1. Flow diagram for the SOM model (after Ref. [28]; modified).

108 F. Amlinger et al. / European Journal of Soil Biology 39 (2003) 107–116

various crops (sugar beet, winter wheat, barley, potatoes).During a 20–year compost application period, the humuslevel increased by 0.4–0.5% (yearly average compost load15 t ha–1 d.m.), whereas it decreased by 0.5% in the case ofinorganic fertilisation. A compost load of 7 t d.m. per ha andyear was found to be sufficient to maintain the initial humuslevel [13]. Husz [24] describes a clear positive correlationbetween C and N content of soils (r = 0.9). The C/N ratioplays a major role in the question of mobilisation or immo-bilisation of nitrogen (Table 1).

3.3. Soil texture (proportion of clay)

Soil texture is important for the stabilisation of SOMsince clay can complex humus and lead to decreased C and Nmineralisation. The proportion and quality of clay further-more influences the ability and amount of ammonium sorp-tion in the soil. Depending on the type of clay, Schwertmannand Niederbudde [44] calculated a total NH4

+ fixation rang-ing from 0 to 600 kg ha–1 in the 0–30 cm layer.

3.4. Soil management

The most important factors are timing and intensity ofmechanical aeration through tillage or weed control as wellas crop rotation and inter-cropping (variation of time andlevel of N demand by crops) [14]. For instance, it was shownin a field trial with sugar beet that minimal tillage systemscompared with common ploughing increased the N-net-mineralisation from 139 to 169 kg N ha–1 [23].

4. Compost nitrogen: efficiency and mineralisationrates

4.1. General factors

Apart from site and cultivation specific factors, the avail-able nitrogen of compost is predominantly dependent on thefollowing parameters:

• C/N ratio of raw material (kitchen waste, park andgarden waste, wood choppings, farm yard manure).

• Composting conditions (mainly aeration, agitation).• Decomposition/stabilisation rate, duration of compost-

ing (immature or mature compost).• Post-treatment of compost (sieving, blending).• Time of application (time before cropping or leaching

phase).• Compost quality parameters, such as C/N ratio, degrad-

able amounts of C– and N–fractions.

Fig. 2. The still sparely known fate of compost-N in SOM-pools. – min N = without supplementary mineral N; + min N = with supplementarymineral N; SB = sugar beet. (1) Gagnon et al. (1997) [17]; (2) Schlegel (1992) [43]; (3) Asche et al. (1994) [5]; (4) Frei Ming et al. (1997) [16];(5) Ebertseder and Gutser (1995) [15]; (6) Gutser (1996) [18]; (7) Buchgraber (2000) [10]; (8) Diez and Krauss (1997) [13].

Table 1Trends for N–mobilisation and immobilisation related to C/N ratio[25]

C/N–ratio pastureland

C/N–ratio arableland

Trend

<7.5 <8 N–release distinct7.5–8.5 8–9 N–release8.5–9.5 9–11 Balanced9.5–10.5 11–14 N–binding>10.5 >14 N–binding distinct

109F. Amlinger et al. / European Journal of Soil Biology 39 (2003) 107–116

To evaluate the mineralisation (availability) of compost-Nand to estimate the amount available for plants over a certainperiod several experimental and calculation methods are pos-sible:

• Laboratory incubation tests under constant conditions(temperature, water content of the substrate with andwithout cultivation of crops) with or without periodicalpercolation of the mineralised N.

• Field trials to evaluate the N–efficiency in terms ofcomparative yield or N uptake, respectively, relative tocontrol or mineral fertilised plots.

• N–leaching tests on field scale with lysimeter installa-tions or suction cups as well as regular measurements ofmineral N in the leaching horizon.

• Model based calibration of N–mineralisation kinetics.

4.2. Incubation tests

Mattingly [33] investigated the characteristics of 23 typesof composts amended to top soil (4 g d.m. compost in 200 gsoil) and incubated in 600 ml flasks under greenhouse condi-tions, frequently shaked and kept at a continous moisturelevel. The NO3–N contents measured after 5 and 13 weeksshowed that (1) –2.5% to +20.4% of total N was nitrified and(2) 88% of the nitrified N was mineralised during the first5 weeks. In another experiment (10% compost, 40% loamysoil, 50% perlite, 20 °C, 12 weeks), Berner et al. [6] demon-strated that 50% of the N content of 38 yard waste compostswas immobilised, and 13% of the samples induced N immo-bilisation under field conditions. On average, 2.1% of totalcompost N (between +8% and –11%) was mineralised.

Cheneby et al. [11] evaluated the CO2–evolution and theN–mineralisation in 2 organically managed soils amendedwith 15N–labelled composted farm yard manure. The miner-alisation model for carbon and nitrogen showed typical min-eralisation dynamics for a more loamy and a more sandy soil,repectively. CO2–C mineralisation curves resembled asymp-totic regression curves with an exponential CO2–evolutionduring the first 50 d of incubation followed by linear evolu-tion during the final period of incubation. The soil type had a

marked effect; with the labile fraction representing 31% ofcompost-C in the more sandy soil and 20% in the more loamysoil. The labile N–fractions represented 34% (sandy soil) and25% (loamy soil) and were in the same order of magnitude ascorresponding values of labile C fraction. Nevertheless, theauthors point out that laboratory results reflect only thepotential and not the real dynamics under field conditions.

In pot experiments, Hadas and Portnoy [20] showed thatthe rates for inorganic N release depends on the availabilityof C and N (quantity and solubility) and the C/N ratio of thesefractions, but is independent of the soil type and the compostapplication rate. The rate of mineralisation amounted to 15%of N added by compost. The cumulative N–release after33 weeks of incubation was 22% of added N for municipalwaste compost and 23% for cattle manure compost.

In Table 2, some citations with key results of incubationtests are assembled. Even under optimised temperature andwater conditions, the mineralisation rates exceeded 15% oftotal compost-N only in one experiment with FYM compost.Even immobilisation during the initial stages was observedupon application of compost rich in C.

4.3. Field trials

Based on several field and lysimeter experiments N avail-ability ranges from 0% to 10% for biowaste compost in thefirst year, and around 3.5% for each of the following years[18]. Similar results were obtained in pot experiments withbarley where the N–uptake of compost was 15% lower com-pared to the N–efficiency of mineral fertiliser [26]. In a9–year field experiment (loamy silt; SOM: 1.9%; pH: 6.8;crop rotation: grain maize-summer wheat-winter barley)Aichberger et al. [2] found a declining N–efficiency of com-posts depending on input material in the sequence cattlemanure > yard waste > biowaste. Over an observation periodof 9 years, the mineralisation rate of compost N with yearlycompost applications varied between 21 and 62 kg ha–1

year–1, corresponding to an average of 20% ha–1 year–1 of theyearly total N load. In 5–year crop rotations treated withbiowaste compost and supplementary mineral fertiliser,

Table 2N–mineralisation of different compost types as found in incubation tests: N–availability in per cent of Ntot supply

Source Incubation(weeks, °C)

Compost (type, amount orconc.)

Net-mineralisation(% of Ntot )

Remarks

Berner et al. (1995) [6] 12 weeks Yard waste 8–11% 50% short term20 °C 38 composts 13% med. term

100% compost ImmobilisationCheneby et al. (1994) [11] 52 weeks FYM 25% → Loamy soil

28 °C 60 t f.m. ha –1 34% → Sandy soilHadas and Portnoy (1997) [20] 32 weeks FYM and MSW 15%

30 °C 5% and 15% compostHébert et al. (1991) [22] 16 weeks 4 FYM 0–14% At high C/N

22 °C 0.05%, 0.1%, 0.2% N → ImmobilisationInsam and Merschak (1997) [25] 29 weeks SS and biowaste =control Undisturbed soil cores

15 °C 300 kg N Measured as N–release in percolate

Compost from: FYM, farm yard manure; SS, sewage sludge; MSW, municipal solid waste; f.m., fresh matter.

110 F. Amlinger et al. / European Journal of Soil Biology 39 (2003) 107–116

N–availability ranged from 14% (cereal dominated, pasture)to 32% (maize dominated) of total compost N [10]. Diez andKrauss [13] in the first year of a 21–year field experimentwith waste compost found 16% of the compost nitrogen inthe yield and in the final year this figure rose to over 40% ofthe applied total N. This amount probably is the effect of theenhanced mineralisation potential after 20 years of compostamendment and the actual compost effect. The calculatedN–mineralisation was 5–8% for the first year, 3–5% for thesecond year and 1.5–2% in each of the following years.Schlegel [43] found that 13% of compost N was converted to

the grain at sorghum, and 30–36% was mineralised at appli-cation rates of 17.8 t ha–1 year–1. As observed by Diez andKrauss [13], mineralisation rate is diminished by using addi-tional mineral fertilisers.

Figs. 3 and 4 summarise the results of a number ofcompost trials in terms of N–recovery related to N uptake oryield. Fig. 3 demonstrates the N–recovery in the year ofapplication. The last five columns represent the yearly N–ef-ficiency from compost during a 5–year crop rotation. Fig. 4shows mean results for several crop rotations of differentexperiments. Columns 1–4 are 5–year crop rotations domi-

Fig. 3. N–recovery from compost in the year of application (CR, crop rotation) LSU, livestock unit ha–1;YWC, yard waste compost; FYM, farmyard manure; +min N = with supplementary mineral N. (7) Buchgraber 2000 [10]; (9) Pötsch (2000) [40]; (10) Berner et al. (1997) [6]; (11) Diezand Krauss (1997) [13].

Fig. 4. N–efficiency from compost within crop rotations.

111F. Amlinger et al. / European Journal of Soil Biology 39 (2003) 107–116

nated by maize, cereal or pasture, respectively, and show thetendency that for maize an increased N–efficiency can beachieved. In contrast, the pasture showed a low N–efficiencyof 9–14% (columns 4–6). Columns 8–14 indicate a continu-ous increase of N efficiency through organic N accumulationin the soil when compost is applied continuously over aperiod of 21 years.

These examples indicate that (i) N–effect of compostapplication in general does not exceed 15–20% of totalN–supply in the first year, (ii) the residual compost N–pool ismineralised at rates of 3–8% in following years, (iii) continu-ous compost amendments and crop rotations with high nutri-ent demand may increase N–minerlisation, and (iv) maturecomposts may mineralise in a shorter time period than freshcompost.

5. Leaching of nitrogen in compost amended soils

Hartl [21] demonstrated in a mono-cropping system withrye on a loamy silt that even with high compost applicationrates (130 t f.m. in different intervals within 5 years) theincrease of NO3–N at a depth of 0–90 cm did not exceed49 kg ha–1 as compared to the control (without fertiliser). Inanother field experiment [21], compost amendments be-tween 14 and 37 t f.m. ha–1 over an the average of 6 years leadto an increased NO3–N level at 0–90 cm of 5–23 kg ha–1

from the third year with no significant differences betweenthe compost levels. Petersen and Stöppler-Zimmer [39] iden-tified sandy soils as highly sensitive to nitrate leaching, whileKranebitter and Insam [29] did not find any significant dif-ference in nitrate leaching of compost amended soils com-pared to the control in alpine soils. Insam and Merschak [25]showed that for forest soils, composted materials can consid-erably lower the risk of a groundwater contamination incomparison with unstabilised materials or with mineral fer-tilisers. In a 3–year experiment of Schlegel [43], compostapplications up to 17.8 t d.m. ha–1 year–1 did not affect thenitrate content in the soil at 1.5 and 3 m depth, respectively,whereas mineral fertilisers led to an elevated nitrate contentin the subsoil. Li et al. [31] applied five composts (sugarcanefiltercake, biosolids and mixtures of municipal solid wastesand biosolids) on the surface of sandy soil at 100 t ha–1 inleaching columns and leached with deionised water. Nitrateleaching was negatively correlated to C/N ratio of the com-post, with the amount of N leached accounted for 3.3–15.8%of total N in the compost. Peaks in NO3 leaching occurredafter a simulated rainfall of only 6.8–7.9 cm. Maynard [34]showed that the nitrate concentrations in the groundwaterunder compost amended plots (four levels: 0, 25, 50, 100 td.m. ha–1) did not exceed 10 mg l–1 and did not show anysignificant differentiation between the variants. Diez et al.[12] demonstrated in a 3–year experiment that compost treat-ment combined with efficient irrigation (according to plantconsumption) showed positive effects in controlling nitratedischarge in comparison to other fertilisers and over-wateredplots. Leclerc et al. [30] demonstrated the high efficiency of

manure compost and the beneficial reduction of nitrate leach-ing elicited by organic fertilisers during a 5–year rotation ona sandy soil in lysimeters. Calculated mean nitrogen lossesdue to leaching were the highest in the case of mineralfertilisers (124 kg N ha–1 year–1). The mean values ofleaching/supply ratio was 47% for mineral fertilisers, 35%for manure compost, 8.5% for urban compost, and zero forbrushwood compost.

Effects of compost and N fertiliser management on cornyield and NO3–leaching were evaluated by Mamo et al. [32]in a 3–year study on a loamy sand soil. Two composts wereeach applied at very high rates either 90 t ha–1 year–1 in threesuccessive years or at 270 t ha–1 year–1 at once. Over thisperiod, the NO3–N leaching with the high compost rates was1.8 times higher compared to the annual application plots.However, it has to be considered that such an excessivecompost use does not meet requirements of good agriculturalpractice.

It may be concluded that under practical compost appli-cation rates, the site-specific leaching for NO3–N is en-hanced compared to variants without fertilisation between0 and 50 kg N ha–1. Furthermore, some papers indicate thatthe biggest amount of NO3 is found in the upper soil layer(0–60 cm). Despite these findings, high amounts of compostin one or repeated applications are not recommended, at leastfor well drained soils (sand). Data on N–release after com-post application are summarised in Table 3.

6. C and N accumulation models

Biowaste compost (separately collected garden and do-mestic wastes) shows the highest humus reproduction poten-tial compared to sewage sludge, slurry and manure. Gutser[18] describes the enrichment of the organic N–pool follow-ing the sequence compost > farm yard manure > liquidmanure > mineral fertiliser. On the basis of several fieldexperiments [19], it is estimated that with continuous com-post amendment on the basis of 100 kg N ha–1 year–1 totalcompost N input will balance the plant uptake within 40–80 years (Fig. 5).

Computer simulation of long term compost management(loamy soil, compost: 30 t d.m. ha–1 3 year–1; crop rotation:sugar beet—winter wheat—winter barley, followed by rapeas intercrop) vs. mineral fertilisation over a period of50 years found that N– and C–levels decline in the case ofinorganic fertilisation and increase with compost fertilisa-tion. The C/N ratio increases upon continuous compost ap-plication (Fig. 6, [45]).

A computation on the basis of a 9–year compost field trialresulted in the estimate that the total N application by com-post would balance the yearly mineralisation potential after100 years (Fig. 7; [1,2]). However, N mobilisation kineticshave to be evaluated critically in relation to N demand bycrops during the year with alternating vegetation andfallow/leaching periods. This leads to the demand that thespecific humus accumulation by compost amendments has to

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be balanced with site–(climate and soil) and cultivation-specific conditions. Actual mineralisation potentials must beinvestigated regularly.

7. Conclusions and lack of knowledge

Depending on compost properties as well as soil andcultivation conditions, the N–effect of compost amendmentsranged from 5% to 15% in the first year, and from 2% to 8%in the following years as a percentage of total compost-N.This has to be considered by computing mid term compost-Nefficiency. Nitrogen mineralisation dynamics are predomi-nantly determined by the soil properties such as Ctot and Ntot,

Table 3Changes in soil mineral-N after compost application (selected data)

Source Horizon (cm)soil

Compost type amount ha–1

applic. periodN min ha–1

compared to controlRemarks

Pape and Steffens (1998)[38]

0–90 Biowaste ∅ 20 kg After second compost appl.2 × 30 t in 5 years Above mineral N Max: D = 70 kg

Hartl (2000) [21] 0–90 Biowaste Max 49 kg Permanent rye rotationLoamy silt 130 t in 5 y >“0” Varied application rhythm

Hartl (2000) [21] 0–90 Biowaste Max 5–23 kg → cereals & potatoesLoamy silt 14–37 t y–1 >“0”

Over 6 yStöppler-Zimmer andPetersen (1995) [46]

0–90 Biowaste ± No differences at moderateLoam and sand 30 t + min N 100 t Compared to NPK Amounts of 30 t + supplement mineral N

Schlegel (1992) [43] 0–150/300 FYM No effect In ‘ leaching horizon’ (150–300 cm)Silty loam 0–17.8 t d.m.

Amlinger and Walter(1993) [3]

0–60 Biowaste ∅ 34% Max: 120 kg in 0–60 cm in springLoamy silt 80 t f.m. ha–1 >“0”

2 × in 5 y

y, year; FYM, farm yard manure; d.m., dry matter; f.m., fresh matter.

Fig. 5. N–accumulation in the soil through mineral fertiliser, slurryand biowaste compost application assuming an annual application of100 kg N ha–1 year–1 ([10]; modified).

Fig. 6. Model (DAISY) for C and N performance during 50 years without and with compost application (30 t f.m. ha–1 3 year–1) [45].

113F. Amlinger et al. / European Journal of Soil Biology 39 (2003) 107–116

C/N ratio, soil texture and water holding capacity. Maturityof compost in the long run is of minor significance. However,initial immobilisation is more likely with less mature com-post and with high C/N ratio, since in mature compost N–im-mobilisation had already taken place during the compostingprocess. Under sandy soil conditions, an adapted N–con-sumption by crop rotation, or diminished application rates ofcompost, have to be considered. On silty and loamy soils, thedanger for nitrate leaching is clearly reduced. Combining theyearly supplies in 2 to 3-year-loads (e.g. 25–30 t d.m. every3 years instead of 10 t ha–1 year–1) lead to an improvedN–utilisation. These experimental results suggest a criticalview on nitrogen related spreading restrictions. For authori-sation schemes and N limitations in the framework of e.g.,the Nitrates Directive (676/91/EEC), the Regulation2092/91 EEC [41] on organic production of agriculturalproducts and indications referring thereto on agriculturalproducts and foodstuffs or national water conservation rules,the reduced immediate N availability of composts must beaccounted for. Otherwise, agronomically and environmen-tally sound SOM management in compost fertilised farmsystems become impractical.

Further investigations are necessary to develop satisfac-tory approaches for controlling the release of accumulatedorganic nitrogen in soil resulting from compost amendment.Accordingly, long term compost fertilisation has to be con-sidered in the framework of (i) space and time dependentdemand by crops, (ii) farming system (livestock, supplemen-tary fertilisers, soil cultivation, crop rotation) and (iii) soiland site conditions. Regular measurements of critical soilparameters (SOM, nitrogen, at total and soluble amounts) aswell as specified product design in terms of feedstock com-position, and maturation schemes are recommended for pro-fessional compost management.

Above all, knowledge on the transfer dynamics betweenthe N–pools of the soil is essential. Nitrogen and organic

matter balance for evaluating the mineralisation dynamics ofthe active humus pool under organic (compost) fertilisingsystems will play an important role for sustainable soil man-agement.

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Fig. 7. N accumulation (yearly compost rates at the basis of 175 kg N ha–1 year–1 in a compost amended soil compared to model estimation [2]).

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