effects of coal-mine discharges on the quality of the ...

EFFECTS OF COAL-MINE DISCHARGES ON THE QUALITYOF THE STONYCREEK RIVER AND ITS TRIBUTARIES,

SOMERSET AND CAMBRIA COUNTIES, PENNSYLVANIA

by Donald R. Williams, James I. Sams III, and Mary E. Mulkerrin

U.S. GEOLOGICAL SURVEY Water-Resources Investigations Report 96-4133

prepared in cooperation with the

SOMERSET CONSERVATION DISTRICT

Lemoyne, Pennsylvania 1996

U.S. DEPARTMENT OF THE INTERIOR

BRUCE BABBITT, Secretary

U.S. GEOLOGICAL SURVEY

Gordon P. Eaton, Director

For additional information write to:

District ChiefU.S. Geological Survey840 Market StreetLemoyne, Pennsylvania 17043-1586

Copies of this report may be purchased from:

U.S. Geological Survey Branch of Information Services Box 25286 Denver, Colorado 80225-0286

CONTENTS

Page

Abstract.................................................................................... 1

Introduction................................................................................ 2

Purpose and scope..................................................................... 2Description of study area ............................................................... 3Methods of study...................................................................... 7Previous investigations................................................................. 8Acknowledgments..................................................................... 9

Coal-mine discharges....................................................................... 10

Locations............................................................................ 10Water quality and contaminant discharges............................................... 12Remediation-prioritization index ....................................................... 18Remediation by passive-treatment systems .............................................. 31

Surface-water-quality sampling sites.......................................................... 33

Locations............................................................................ 33Water quality and contaminant discharges............................................... 36

Effects of coal-mine discharge on the quality of Stonycreek River and its tributaries ................. 41

Summary ................................................................................. 48

References cited............................................................................ 50

Appendix 1. Geographic information system (GIS) datasets ................................... 542. Location coordinates and station numbers for sampled mine discharges in the

Stonycreek River Basin.................................................... 563. Field data and laboratory analyses of mine discharges ............................ 624. Prioritization index (PI) for all mine discharges................................... 785. Field data and laboratory analyses for surface-water sites.......................... 88

ILLUSTRATIONS

Page

Figure 1. Map showing the location of the Stonycreek River Basin............................ 4

2. A generalized stratigraphic column of the geologic formations in the StonycreekRiver Basin............................................................... 5

3. Geologic map of the Stonycreek River Basin ...................................... 6

4. Map showing locations of coal-mine-discharge sites in the Stonycreek River Basin .... 11

5. Graph showing coal-mine discharges that exceeded federal effluent limits for pH and concentrations of total iron and total manganese, and arbitrary indicator limits for sulfate and net acidity concentrations............................... 13

6-11. Maps showing:6. Location of the coal-mine-discharge sites in the Shade Creek Basin ............ 25

7. Location of the coal-mine-discharge sites in the Paint Creek Basin ............. 26

8. Location of the coal-mine-discharge sites in the Wells Creek Basin............. 27

9. Location of the coal-mine-discharge sites in the Quernahoning Creek Basin..... 28

10. Location of the coal-mine-discharge sites in the Oven Run Basin .............. 29

11. Location of the coal-mine-discharge sites in the Pokeytown Run Basin ......... 30

12. Diagram showing the layout of the Shade passive-treatment system in theStonycreek River Basin.................................................... 32

13. Diagram showing a typical cross-sectional view of a successive alkalinity-producingsystem treatment component .............................................. 32

14. Map showing surface-water-quality sampling sites in the Stonycreek River Basin..... 35

Figures 15-21. Graphs showing:15. Specific conductance, pH, and concentrations and discharges of dissolved solids

measured in the mainstem and in tributary streams in the Stonycreek River Basin on July 27 and 28,1993...................................... 37

16. Concentrations and discharges of alkalinity and acidity measured in the mainstem and in tributary streams in the Stonycreek River Basin on July 27 and 28,1993 ................................................... 38

17. Concentrations and discharges of total iron and total manganese measured in the mainstem and in tributary streams in the Stonycreek River Basin on July 27 and 28,1993 ................................................... 39

18. Concentrations and discharges of total sulfate measured in the mainstem andin tributary streams in the Stonycreek River Basin on July 27 and 28,1993.... 40

19. Measured total sulfate discharges in tributary streams and measured and cal culated total sulfate discharges in the mainstem of the Stonycreek River on July 27 and 28,1993 ................................................ 42

20. The effects of mine discharges 17 and 22 on Wells Creek on September 9,1993 .. 45

21. The effects of Oven Run and Pokeytown Run on the Stonycreek River onSeptember 8,1993..................................................... 47

IV

TABLES

Page

Table 1. Federal effluent limitations for coal-mine drainage................................ 10

2. Water-quality and quantity changes that occurred downstream of mine-dischargesites 17 and 22 on May 12,1994............................................. 14

3. Mine discharges that met federal effluent standards for pH and concentrations oftotal iron and total manganese ............................................. 15

4. Flows, concentrations of total iron and acidity, and iron and acidity discharges anddischarge rank for mine discharge sites in the Stonycreek River Basin ........... 17

5. Unsorted total-iron data and sorted, ranked, and scored total-iron data used for thePrioritization Index (PI) calculations ........................................ 19

6. Prioritization index (PI) for coal-mine discharges in the Shade Creek Basin........... 21

7. Prioritization index (PI) for coal-mine discharges in the Paint Creek Basin ........... 22

8. Prioritization index (PI) for coal-mine discharges in the Wells Creek Basin ........... 23

9. Prioritization index (PI) for coal-mine discharges in the Quemahoning Creek Basin ... 23

10. Prioritization index (PI) for coal-mine discharges in the Oven Run Basin............. 24

11. Prioritization index (PI) for coal-mine discharges in the Pokeytown Run Basin ....... 24

12. Surface-water-quality sampling sites in the Stonycreek River Basin ................. 34

13. Water-quality data for five coal-mine discharges and the receiving streams .......... 43

14. Water-quality data collected on September 8,1993, for Oven Run, Pokeytown Run, and the Stonycreek River above and below where each of the runs flows into the river................................................................. 44

CONVERSION FACTORS, VERTICAL DATUM, AND ABBREVIATED WATER-QUALITY UNITS

Multiply By To obtain

Length

inch (in.) 25.4 millimeterfoot (ft) 0.3048 metermile (mi) 1.609 kilometerfoot per mile (ft/mi) 0.1894 meter per kilometer

Area

square mile (mi2) 2.590 square kimometer

Volume

gallon per minute (gal/min) 0.06309 liter per second cubic foot per second (ft3/s) 0.02832 cubic meter per second

Mass

pound (Ib) 454 grams ton 0.9072 megagrams

Temperature

degree Fahrenheit (°F) °C=5/9 (°F-32) degree Celsius

Sea level: In this report, "sea level" refers to the National Geodetic Vertical Datum of 1929 a geodetic datum derived from a general adjustment of the first-order level nets of the United States and Canada, formerly called Sea Level Datum of 1929.

Abbreviated water-quality units used in report:

micrograms per liter (ug/L) milligrams per liter (mg/L)

VI

EFFECTS OF COAL-MINE DISCHARGES ON THE QUALITYOF THE STONYCREEK RIVER AND ITS TRIBUTARIES,

SOMERSET AND CAMBRIA COUNTIES, PENNSYLVANIA

By Donald R. Williams, James I. Sams III, and Mary E. Mulkerrin

ABSTRACT

This report describes the results of a study by the U.S. Geological Survey, done in cooperation with the Somerset Conservation District, to locate and sample abandoned coal-mine discharges in the Stonycreek River Basin, to prioritize the mine discharges for remediation, and to determine the effects of the mine discharges on water quality of the Stonycreek River and its major tributaries. From October 1991 through November 1994,270 abandoned coal-mine discharges were located and sampled. Discharges from 193 mines exceeded U.S. Environmental Protection Agency effluent standards for pH, discharges from 122 mines exceeded effluent standards for total-iron concentration, and discharges from 141 mines exceeded effluent standards for total-manganese concentration. Discharges from 94 mines exceeded effluent standards for all three constituents. Only 40 mine discharges met effluent standards for pH and concentrations of total iron and total manganese.

A prioritization index (PI) was developed to rank the mine discharges with respect to their loading capacity on the receiving stream. The PI lists the most severe mine discharges in a descending order for the Stonycreek River Basin and for subbasins that include the Shade Creek, Paint Creek, Wells Creek, Quemahoning Creek, Oven Run, and Pokeytown Run Basins.

Passive-treatment systems that include aerobic wetlands, compost wetlands, and anoxic limestone drains (ALD's) are planned to remediate the abandoned mine discharges. The successive alkalinity- producing-system treatment combines ALD technology with the sulfate reduction mechanism of the compost wetland to effectively remediate mine discharge. The water quality and flow of each mine discharge will determine which treatment system or combination of treatment systems would be necessary for remediation.

A network of 37 surface-water sampling sites was established to determine stream-water quality during base flow. A series of illustrations show how water quality in the mainstem deteriorates downstream because of inflows from tributaries affected by acidic mine discharges. From the upstream mainstem site (site 801) to the outflow mainstem site (site 805), pH decreased from 6.8 to 4.2, alkalinity was completely depleted by inflow acidities, and total-iron discharges increased from 30 to 684 pounds per day. Total-manganese and total-sulfate discharges increased because neither constituent precipitates readily. Also, discharges of manganese and sulfate entering the mainstem from tributary streams have a cumulative effect.

Oven Run and Pokeytown Run are two small tributary streams significantly affected by acidic mine drainage (AMD) that flow into the Stonycreek River near the town of Hooversville. The Pokeytown Run inflow is about 0.5 mile downstream from the Oven Run inflow. These two streams are the first major source of AMD flowing into the Stonycreek River. Data collected on the Stonycreek River above the Oven Run inflow and below the Pokeytown Run inflow show a decrease in pH from 7.6 to 5.1, a decrease in alkalinity concentration from 42 to 2 milligrams per liter, an increase in total sulfate discharge from 18 to 41 tons per day, and an increase in total iron discharge from 29 to 1,770 pounds per day. Data collected at three mainstem sites on the Stonycreek River below Oven Run and Pokeytown Run show a progressive deterioration in river water quality from AMD.

Shade Creek and Paint Creek are other tributary streams to the Stonycreek River that have a significant negative effect on water quality of the Stonycreek River. One third the abandoned-mine discharges sampled were in the Shade Creek and Paint Creek Basins.

INTRODUCTION

Coal is Pennsylvania's most important mineral resource. In 1993, coal production in Pennsylvania was more than 63 million tons and Somerset and Cambria Counties ranked second (5.6 million tons) and fifth (4.6 million tons), respectively in the state for total coal produced (Pennsylvania Coal Association, 1994). Much of the Stonycreek River Basin, which is primarily in Somerset County and part in Cambria County, is underlain by low-volatile bituminous coal deposits that are an important economic mineral resource. With the onset of the Industrial Revolution in the late 1800's, extensive commercial mining of these coal resources began with almost no concern for the protection of the land surface and water resources. Consequently, the water quality in the Stonycreek River and its tributaries has been severely degraded for many decades by acid mine drainage (AMD) from abandoned coal mines and coal-refuse piles. The AMD problem has been recognized as one of the most serious and persistent water-quality problems not only in Pennsylvania, but in all of Appalachia, extending from New York to Alabama (Biesecker and George, 1966). Thousands of stream and river miles in Appalachia are currently affected by the input of mine drainage from sites mined and abandoned before strict effluent regulations were implemented (Kleinmann and others, 1988).

Part of the Stonycreek River Basin received an AMD evaluation in the early 1970's in the Operation Scarlift studies (Carson Engineers, 1974). The evaluation indicated the cleanup cost (based on conventional treatment technologies) in that part of the basin would amount to several hundred million dollars, and annual operating costs also would be in the millions of dollars. However, new passive-treatment technologies pioneered by the U.S. Bureau of Mines in the late 1970's and first applied by the mining industry in the 1980's, offer effective, low-cost, low-maintenance remediation.

The Stonycreek-Conemaugh River Improvement Project (SCRIP) association is a coalition of grass roots groups and local resource agencies seeking to restore water quality in the Upper Conemaugh River Basin. This will be accomplished by the combined efforts of government, industry, and the private sectors and by use of new passive-treatment technologies. SCRIP was formed at the request of U.S Congressman John P. Murtha. Its goal is to develop and implement solutions to the AMD problem in the Conemaugh River Basin. SCRIP was instrumental in initiating the cooperative study of the Stonycreek River Basin between the U. S. Geological Survey (USGS) and the Somerset Conservation District.

Purpose and Scope

This report presents the results of a coal-mine-drainage study in the Stonycreek River Basin in Somerset and Cambria Counties, Pa., from 1992 to 1995. The report describes the locations and instantaneous contaminant loads of 270 mine discharges sampled during low flow throughout the basin and shows the effect that the discharges had on the water quality of the Stonycreek River and its major tributary streams. The report also describes the method used to prioritize the mine discharges for remediation and gives methods for remediation by use of passive-treatment systems. Base-flow samples were collected at 5 mainstem sites and 32 tributary sites in September 1992, July 1993, and May 1994. All 37 sites were sampled each year. To show the specific effect of mine discharges on the receiving streams, five mine discharges were sampled at their point of discharge into the receiving streams, and the receiving streams were sampled above and below these discharges. Also, two streams significantly affected by AMD, Oven Run and Pokeytown Run, were sampled at their point of discharge into the Stonycreek River, and the Stonycreek River was sampled above and below these tributary-stream inflows.

Description of Study Area

The Stony creek River Basin is almost entirely in northern Somerset County in southwestern Pennsylvania with only a small part of the basin in Cambria County (fig. 1). Stonycreek River drains an area of 468 mi2 . Stonycreek River Basin is in the Allegheny Mountain Section of the Appalachian Plateaus Physiographic Province (Berg and others, 1989). The eastern basin boundary is the Allegheny Front, which is a crest forming the western edge of the Appalachian Mountains of the Ridge and Valley Physiographic Province. The western border of the Stonycreek River Basin is Laurel Ridge. The headwaters of the Stonycreek River rise near the town of Berlin in central Somerset County and flow generally north to Johnstown in Cambria County where it joins the Little Conemaugh River to form the Conemaugh River. The Stonycreek River has a length of 43.4 mi and an average slope of 38 ft/mi (U.S. Army Corps of Engineers, 1994). Elevations in the basin range from more than 2,900 ft above sea level on both the Allegheny Front and the Laurel Ridge to about 1,150 ft above sea level in the city of Johnstown. Relief throughout the basin is moderate to high. A wide, low flood plain exists at the headwaters of the Stonycreek River. As the river meanders northward, it enters an area of steep flanking hills with relief of 400 to 500 ft near the town of Hooversville; relief increases to a maximum of about 600 ft in Johnstown.

The Stonycreek River Basin contains a large resource of low-volatile bituminous coal. About 14 coal beds of mineable thickness are in the basin. However, the Lower and Upper Kittanning and the Upper Freeport coals have been the most extensively mined. The earliest mining activity in the basin was during the middle to late 1800's and was limited almost entirely to the Pittsburgh Coal bed in the southeastern most part of the basin and the Lower Kittanning Coal bed in the central and northern part of the basin. In the early 1900's, extensive mining of the Upper Kittanning Coal bed began. Surface-mining activities began between 1940 and 1950 and continue to be a major industry throughout the basin.

Rock in the Stonycreek River Basin is sedimentary in origin, and the rock types are primarily sandstone, siltstone, and shale with thin beds of limestone and coal. Folding along the Allegheny Front on the east and Laurel Hill on the west exposes a considerable part of the geologic column, from the Mississippian-Devonian age Rockwell Formation to the Pennsylvania age Monongahela Group. A generalized stratigraphic column showing the units present in the basin is shown in figure 2.

The rocks are divided into eight stratigraphic units: the Rockwell Formation of the Mississippian- Devonian System; the Burgoon sandstone, Loyalhanna Formation, and Mauch Chunk Formation of the Mississippian System; and the Pottsville Group, Allegheny Group, Conemaugh Group, and Monongahela Group of the Pennsylvanian System. The distribution of stratigraphic units in the basin is shown in figure 3. The Rockwell Formation consists of sandstone, shale, and some red beds. The Burgoon sandstone consists of buff-nonmarine sandstone and conglomerate. The Loyalhanna Formation is a highly cross- bedded siliceous limestone. The Mauch Chunk Formation consists of red shale with subordinate sandstone and limestone. The Pottsville Group is composed of the Homewood, Mercer, and Connoquenessing Formations and consists predominantly of sandstone, conglomerate, and thin beds of shale.

The Allegheny and Conemaugh Groups are the two most areally extensive stratigraphic units in the basin. The Allegheny Group is composed of the Freeport, Kittanning, and Clarion Formations. The group consists of sandstone, shale, and discontinuous limestone and coal beds. The Conemaugh Group is composed of the Casselman and Glenshaw Formations and consists primarily of sandstone and shale and lesser amounts of limestone and coal. The Allegheny Group is the major coal-bearing unit in the Stonycreek River Basin, containing the thick Freeport and Kittanning coal beds. In the basin, the Monongahela Group is composed only of the Pittsburgh Formation, which consists of sandstone, limestone, shale, and coal. The Monongahela Group is confined to the hilltops just north of Berlin. This Group contains three workable coal beds the Pittsburgh coal, the Blue Lick coal (local name), and the Redstone coal. However, in the Stonycreek River Basin, this Group is sparsely represented.

/.' - -..- *79° 07' 30"//'

FERNDALE.*^- ** " 'A

_.... i

JOHNSTOWN / '

78° 45'

40° 15' > --*. V* WINDBER f PAINT

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QUEMAHONINGj \ "\ < ' RESERVOIR : > { \/ >,

^- ......^r ^i*OOVERSVILLE\ Z*" *1 ;|: a N) U; ' ' ; OITY .x :;

/BOSWELL ffj ^ ^: - S? BOSWELL ^

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EXPLANATION

MAJOR TOWNS

STREAMS

------- DRAINAGE DIVIDE

------ COUNTY BOUNDARY

02468 10 MILES I HT ,',',' '

02468 10 KILOMETERS

Figure 1. Location of the Stonycreek River Basin.

GENERALIZED STRATIGRAPHIC COLUMN STONYCREEK RIVER BASIN

PENNSYLVANIAN SYSTEM

SSIPPIAN SYSTEM

CO CO

2

DEVONIAN SYSTEM

MONONGAHELA

GROUP

CONEMAUGH GROUP

ALLEGHENY GROUP

POTTSVILLE GROUP

MAUCH CHUNK FORMATION

LOYALHANNA FORMATION

BURGOON SANDSTONE

ROCKWELL FORMATION

Sandstones, limestones, shales, and thin coal beds

4 Pittsburgh Coal

Gray and red shales and sandstones, thin coal beds, and thin units of limestone

< Freeport coal

< Kittanning coals<

Sandstones, shales,limestones, and coals

Sandstone with shale and coal beds

Red shale with sandstone and limestone

Siliceous limestone

Cross-bedded sandstone with some basal conglomerate

Sandstone and carbonaceous shale

Figure 2. A generalized stratigraphic column of the geologic formations in the Stonycreek River Basin.

79° 07' 30"

40° 15'

PENNSYLVANIANEXPLANATION

MISSISSIPPI

MONONGAHELAGROUP

CONEMAUGHGROUP

ALLEGHENY GROUP

POTTSVILLE GROUP

MAUCH CHUNK FORMATION AND LOYALHANNA LIMESTONE

BURGOON SANDSTONE

ROCKWELL FORMATION

Figure 3. Geologic map of the Stonycreek River Basin (Geology compiled by Berg and others, 1980)

The climate in the Stonycreek River Basin is humid continental, characterized by warm summers and cold winters. Prevailing winds are from the west and bring most major weather systems that affect the basin. Air currents are mainly from the polar region, but during the summer, air currents from the Gulf of Mexico are frequent and result in warm, humid weather. Annual precipitation from 1926 to 1992 averaged 45.5 in. at Johnstown and from 1960 to 1991 averaged 40.7 in. at Boswell (U.S. Army Corps of Engineers, 1994). Snowfall and resulting snow on the ground throughout the basin tend to be much greater in areas of higher elevation. Average-annual snowfall at Johnstown (elevation approximately 1,200 ft) is 49.9 in. and at Boswell (elevation approximately 1,900 ft) is 64.9 in. The mean annual temperature at Johnstown during the period 1926-92 was 51.7°F. The average monthly temperature at Johnstown varies from a low of 27.9°F in January to a high of 72.9°F in July. The last frost of the season at Johnstown usually occurs in mid-April to early May; in higher elevations in the basin it could be from mid to late May. The first frost at Johnstown can be expected about mid-September until mid-October, but at higher elevations it has occurred as early as late August.

Agricultural land and forest land collectively account for 90 percent of the total land use throughout the basin (Anderson, 1967). The eastern (Allegheny Front) and western (Laurel Ridge) parts of the basin are the most heavily forested. Surface-mining operations, which affect both agricultural and forest land, are major activities in the basin and account for 4.4 percent of the land use. Residential development, commercial areas, urban areas, light industrial areas, and community parks account for the remaining 5.4 percent. The Stonycreek River Basin is sparsely populated and predominantly rural except near the mouth of the river at Johnstown, where most of the population is concentrated. The largest communities in the basin other than Johnstown and its suburbs include Windber, Berlin, Boswell, Paint, and Central City.

Methods of Study

One of the most significant challenges of the study was to physically locate the abandoned mine discharges throughout the basin. The mine-discharge locations were determined by four principal methods: (1) from previously published reports and from abandoned mine land (AML) maps supplied by the Bureau of Abandoned Mine Reclamation of the Pennsylvania Department of Environmental Protection (PaDEP); (2) from information obtained from Mine Conservation Inspectors of the PaDEP and River Keepers of the SCRIP organization (River Keepers are local residents who volunteered periodically to walk a section of the banks of the Stonycreek River or its tributaries and provide written reports on the condition of the selected stream segment and locations of mine discharges, sewage outflows, or any other unnatural inflows to the stream); (3) from talking to local residents and farmers familiar with the area and aware of discharges on their property or adjacent properties, (4) and by physically walking along the stream banks of tributary streams and the mainstem in remote areas where mining was known to have occurred. When a mine discharge was found, its location was determined by use of a Global Positioning System (GPS) receiver to record the latitude and longitude of the site to the nearest one tenth of a second. Each mine discharge was sampled where it first came from the ground. At the end of each sampling year, all mine discharges were prioritized and ranked with respect to their loading of selected constituents to the receiving stream. In the following year, the top 30 ranked discharges were resampled.

An initial field reconnaissance of the Stonycreek River Basin was conducted in October and November 1991 to determine the sampling locations of all stream sites. Five mainstem sites were selected on the Stonycreek River and 32 additional sites were selected on tributary streams. All 37 stream sites were sampled during low base flow on September 1 and 2,1991, and July 27 and 28,1993, and during high base flow on May 24 and 25,1994.

The effect of mine discharges on receiving streams was determined by sampling five discharges at their point of inflow to the receiving streams and sampling the receiving streams above and below the mine discharges. The effect of Oven Run and Pokeytown Run on the Stonycreek River was determined by sampling the streams at their point of discharge into the river and sampling the river above and below the stream inflows.

In 1983-86, the USGS collected data on five headwater streams in the Laurel Hill area, three of which were in the Stonycreek River Basin, to determine the effect of acid precipitation on stream water quality (Barker and Witt III, 1990). Sulfate was the dominant precursor for acid formation in precipitation and streamflow. Nitrate was more abundant in snowfalls and contributed to streamflow acidification only during snowmelt.

Water-resources data, climatological data, and quality-assurance data were collected by the USGS in the North Fork Bens Creek Basin, a small subbasin in the Stonycreek River Basin, from 1983 through 1988 (Witt III, 1991).

In 1993, the U.S. Army Corps of Engineers, Pittsburgh District, completed a reconnaissance survey on the lower 4-mi section of the flood-reduction channel on the Stonycreek River (U.S. Army Corps of Engineers, 1993). The survey was conducted to examine the water quality, the channel sediments that might be removed or disturbed, and aquatic-life resources that might be affected by proposed rehabilitation in that section of the flood channel.

A Conemaugh River Basin Reconnaissance Study was published in 1994 by the U.S. Army Corps of Engineers, Pittsburgh District. This study considered a broad array of basin problems, one of which was water-quality degradation with respect to AMD. The study also recommended solutions for identified problem conditions.

The PaDEP publishes a water-quality assessment for Pennsylvania waters on a biennial basis in response to Section 305(b) of the Federal Clean Water Act. The PaDEP 1994 Water-Quality Assessment report for subbasin 18, which includes the Conemaugh River Basin, indicates that the single biggest source of water degradation in the subbasin is coal mining and is responsible for more than 81 percent of the degradation (Pennsylvania Department of Environmental Resources, 1994b).

Acknowledgments

The authors gratefully acknowledge the many individuals residing in the Stonycreek River Basin who took an earnest interest in this project and provided information and assistance in finding many abandoned-mine discharges. A special thanks goes to the Mine Conservation Inspectors of the PaDEP and to the River Keepers of SCRIP who provided information on the location of many mine discharges and assisted field personnel in physically locating the discharges. The authors also acknowledge the interest and cooperation of the many individual landowners, companies, and municipalities throughout the Stonycreek River Basin who provided access to private and public property for the field data collection, and commonly, provided personal escorts for locating secluded mine discharges.

COAL-MINE DISCHARGES

Coal mining can result in drainages that have a low pH and are contaminated with elevated concentrations of iron, manganese, aluminum, sulfate, and acidity. At sites mined since May 4,1984, drainage chemistry must meet strict effluent quality criteria (Code of Federal Regulations, 1994) (table 1). In an effort to meet these criteria, mining companies commonly treat contaminated drainage by use of chemical methods. In most chemical-treatment systems, metal contaminants are removed through the addition of alkaline chemicals (e.g., sodium hydroxide, calcium hydroxide, calcium oxide, sodium carbonate or ammonia). The chemicals used in these treatment systems can be expensive, especially when required in large quantities. In addition, operation and maintenance costs are associated with aeration and mixing devices, and additional costs are associated with the disposal of metal-laden sludges that accumulate in settling ponds. Water-treatment costs can exceed $10,000 per year at sites that are otherwise successfully reclaimed (Hedin and others, 1994). The high costs of chemical water treatment place a serious financial burden on active mining companies and have contributed to bankruptcies of many others.

Table 1. Federal effluent limitations for coal-mine drainage

[Code of Federal Regulations, 1994, Title 40, Part 434, Section 22; concentrations are in micrograms per liter]

Element or property

Iron, total Manganese, total pH

Maximum for any 1 day

Average of daily values for 30

consecutive days

7,000 3,500 4,000 2,000

Within the range of 6.0 and 9.0 at all times

Although the mining industry throughout the United States spends more than $1 million every day to treat effluent waters from active coal mines (Kleinmann, 1989), mine drainage continues to affect stream water quality because of the adverse effects of discharges from abandoned mines, many of which have been inactive for over a century.

The rate and direction of water movement through abandoned mines can be influenced by factors that include precipitation, the structure of the mined coal beds, overburden structure, mine tunnels, air shafts, boreholes, and local collapses. When an underground mine is abandoned, water levels rise until the water eventually overflows to another mine or at the land surface creating an abandoned mine discharge. Mine drainage from abandoned mines and coal refuse piles is the major source of water-quality degradation in the Stonycreek River. Most of the Stonycreek River and particularly the lower half of the river and many of its major tributaries are currently affected by mine drainage from both underground and surface sites. Many sites were mined and abandoned before passage of the Surface Mining Control and Reclamation Act of 1977 (Office of Surface Mining Reclamation and Enforcement, 1993). This Act sets strict compliance standards for surface coal-mining operations and for the surface effects of underground mining.

All mine discharges that were located and sampled for this study were abandoned mine discharges. Mine discharges from active mines are monitored regularly by the PaDEP to determine if the discharges comply with the current Federal and State effluent limitations.

Locations

Locations of the 270 coal-mine discharges sampled during the study are shown in figure 4 and listed in appendix 2. Methods used to physically locate most of the mine discharges are defined in the Methods of Study section on page 7. After reviewing the information from two previously published reports (U.S. Environmental Protection Agency, 1972; Carson Engineers, 1974) and the AML maps from PaDEP with mine-discharge locations, it was determined that a much more precise method than was used in previous studies was needed to locate mine discharges. A Trimble Navigation GPS Pathfinder system was used to achieve a horizontal accuracy of 3 to 10 ft. The exact location coordinates of all 270 mine-discharge locations are given in appendix 2.

10

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c^^J^K^r?V " - '^ f' ^V'-x } } . ">T"~' ^'>V % ^ -v.4^,..

EXPLANATION6 MILE

STREAMS- BASIN BOUNDARY

MINE DISCHARGE SITE

1 I I I I

2 4 6 KILOMETER

Figure 4. Locations of coal-mine-discharge sites in the Stonycreek River Basin.

11

Water Quality and Contaminant Discharges

Surface and underground coal mining exposes many earth materials to weathering. The physical- chemical breakdown of some materials is accelerated by this weathering process. Pyrite, or iron sulfide (FeS2), is commonly present in coal and the adjacent rock strata and is the compound most associated with AMD. Water is also a principal component of the AMD problem, functioning as a reactant in pyrite oxidation, as a reaction medium, and as a transport medium for oxidation products. Pyrite oxidation is described by the following reaction in which pyrite, oxygen, and water form sulfuric acid and ferrous sulfate:

2FeS2 + 7O2 + 2H2O = 4H+ + 2Fe2+ + 450^ . (1)

Oxidation of ferrous iron (Fe2+) produces ferric ions (Fe3+) according to the following reaction:

2Fe2+ + 1/2 O2 + 2H+ = 2Fe3+ + H2O. (2)

When the ferric ions react with water, an insoluble ferric hydroxide [Fe(OH)3], also called "yellow boy," and more acid are produced:

Fe3+ + 3H2O = Fe(OH)3 + 3H+ . (3)

The above reactions produce elevated concentrations of the precipitate insoluble ferric hydroxide [Fe(OH)3], dissolved sulfate (SO2̂ ), and acid (H+). Secondary reactions of the acidic water dissolve many other constituents associated with coal deposits, including manganese, aluminum, zinc, and trace metals such as arsenic, cadmium, and mercury (Tolar, 1982).

High acidities of many mine discharges also can be attributed to the action of the bacterium Thiobacillusferrooxidans on the pyrite associated with the coal. At near-neutral pH, the oxidation rates of pyrite by air and by T. ferrooxidans are comparable. This stage is typical of freshly exposed coal or refuse, and despite the high concentration of pyrite, the oxidation rate either by oxygen or T. ferrooxidans is low. When a mine discharge is sufficiently alkaline, the acidic water may persist for only a short time before neutralization occurs. However, when the neutralization capacity of the discharge is exceeded, acid begins to accumulate and the pH decreases. As the pH decreases, the rate of iron oxidation by oxygen also decreases, but T. ferrooxidans catalyze the pyrite oxidation and accelerate acid production, which serves to further lower pH. As the pH near the pyrite falls to less than 3, the increased solubility of iron and the decreased rate of ferric hydroxide precipitation significantly increase the overall rate of acid production. Most sampled mine discharges throughout the Stonycreek River Basin that had a pH less than 3 also had very high acidities in addition to high concentrations of iron, manganese, aluminum, and sulfate. The field and laboratory analyses of all samples collected at the 270 mine discharge sites are listed in appendix 3. The number of sampled mine discharges that exceeded effluent limits for pH, total iron, and total manganese concentrations (Code of Federal Regulations, 1994) (table 1) and arbitrary limits for sulfate (U.S. Department of the Interior, 1968) and acidity are shown in figure 5. A pH less than 6.0 was measured in 193 mine discharges, and a pH greater than 9.0 was measured in 1 discharge. Concentrations of total iron greater than 7,000 ug/L were measured in 122 mine discharges, and 141 mine discharges contained concentrations of total manganese greater than 4,000 ug/L. Effluent limits for pH and for concentrations of total iron and total manganese were all exceeded in 94 mine discharges. Effluent standards for 1 or 2 of those constituents were exceeded in 140 mine discharges. Sulfate is an excellent indicator of mine drainage because neutralization processes generally do not change the sulfate concentration and the sulfate ion remains in solution. The U.S. Department of Interior (1968) reported that 75 mg/L of sulfate is an indicator of AMD in streams. Sulfate concentrations exceeded 75 mg/L in 263 mine discharges.

12

MINE-DISCHARGE- SITE SCALE

263

COLJJ

LJJ O DC <

IoLJJ

oDC LJJ DO

193191

141

122

94

ocni-vjv

200

1*501 OU

100

enww

fl

FEDERAL EFFLUENT LIMITS FOR pH AND CONCENTRATIONS OF TOTAL IRON AND TOTAL MANGANESE, AND ARBITRARY INDICATOR LIMITS FOR SULFATE AND NET ACIDITY CONCENTRATIONS

SULFATE CONCENTRATION >75 mg/L

pH <6.0ACIDITY > ALKALINITY

TOTAL MANGANESE CONCENTRATION >4,000 iig/L

TOTAL IRON CONCENTRATION >7,000 iig/L

TOTAL IRON CONCENTRATION >7,000 iig/L, AND TOTAL MANGANESE CONCENTRATION >4,000 iig/L, AND pH <6.0 OR >9.0

pH >9.0

Figure 5. Coal-Mine discharges that exceeded Federal effluent limits for pH and concen trations of total iron and total manganese, and arbitrary indicator limits for sulfate and net acidity concentrations.

13

Acidity concentrations show the severity of a mine discharge. A discharge that is appreciably acidic will be highly aggressive that is, it will dissolve many minerals in coal mines. The acidity of coal-mine drainage generally arises from free hydrogen ions (H+) and mineral acidity from dissolved iron, manganese, and aluminum, which can undergo hydrolysis reactions that produce H+. When a mine discharge contains both mineral acidity and alkalinity, the discharge is net acidic if acidity is greater than alkalinity or net alkaline if alkalinity is greater than acidity. Of the mine discharges sampled, 191 were classified as net acidic and the remaining 79 were classified as net alkaline.

Natural processes commonly ameliorate mine discharges and the toxic characteristics of the discharges can decrease because of chemical and biological reactions and by dilution with uncontaminated water. Many of these processes occur as the mine discharge flows on the land surface and is exposed to the air. The data in table 2 show the changes that occurred in water quality and quantity of two mine discharges sampled on the same day at their point of discharge from the ground and at a distance downstream just before the discharges flowed into the receiving stream. Water quality of mine- discharge at site 17 showed slight improvement about 400 ft downstream. The flow of mine discharge at site 17 was about the same at both sampling points. The quality of mine discharge at site 22 was considerably improved about 1,000 ft downstream, but dilution appears to have been a significant cause.

Natural processes that ameliorate the quality of mine discharges also can occur before the discharge flows from the ground. When mine water contacts oxygen in the mine voids, iron and manganese can precipitate as hydroxides or oxides, and pH can increase if the discharge comes in direct contact with carbonate rocks. Of the 270 abandoned-mine discharges sampled, 38 met effluent standards for pH and concentrations of iron and manganese (table 3). Five of the 38 discharges met secondary drinking-water standards established by USEPA (1994) for pH, iron, manganese, aluminum, and fluoride.

Table 2. Water-quality and quantity changes that occurred downstream of mine-discharge sites 17 and 22 on May 12, 1994

[mg/L, milligram per liter; j*g/L, microgram per liter]

Site

Site 17 at point of discharge from the ground Location approximately 400 feet downstream

of site 17 Site 22 at point of discharge from the ground Location approximately 1,000 feet downstream

of site 22

Discharge (cubic feet

per second)

2.5 2.3

1.2 2.5

PH (units)

3.6 3.7

3.6 3.4

Iron, total (no/L

as Fe)

990 900

21,300 9,300

Manganese, total (ng/L

asMn)

800 760

7,100 3,700

Acidity, total heated

(ng/L as CaCO3)

32 30

172 82

Sulfate, total

(mg/L as S04)200 230

730 400

14

Table 3. Mine discharges that met Federal effluent standards forpH and concentrations of total iron and total manganese

[U.S. Environmental Protection Agency, 1994; u.g/L, microgram per liter; mg/L, milligrams per liter, <, less than]

Site number

506164666886889196

121123135136145146151152153171193

!195 !196

197199202211224229230243244245

J246 !247

257259268

1270

pH (units)

7.16.76.46.86.76.66.56.86.36.06.46.66.66.26.76.56.56.36.66.9 7.1 6.87.27.16.16.66.46.26.16.36.36.0 6.4 6.66.96.36.3 6.6

Manganese, total (ng/L)

3302,0002,90050013061010

120610760170

1,2001,800

701,6003,000

40230950

1,400 100 30

1,900230150

1,200830

2,2004,0002,000220210 20

490570180700 110

Iron, total (HQ/L)

24150

1,700260

1,4005006088

46094050140170280120260100320510130 10 107917086

1,6003,900380

2,0004317

120 240 84033190680 10

Aluminum, Fluoride total (ng/L) (mg/L)

<130 <0.2 <130 <.2

<130 <.2 150 <.2

197 .2

1 Discharges that met U.S. Environmental Protection Agency secondary drinking water standards for aluminum and fluoride.

15

The flow rate of a mine discharge is one of the most important factors when determining contaminant discharges. This is illustrated in table 4. The first set of data on the top left side of the table represents the top 10 percent (27 discharges) of the 270 mine discharges with respect to the largest total iron concentrations. The sites are sorted from highest concentration to lowest concentration of total iron. The "DISCHARGE RANK" column represents the rank of the corresponding discharge for each site from highest measured instantaneous discharge to lowest measured instantaneous discharge of all 270 mine discharges. For example, mine discharge at site 20 contained the highest measured total-iron concentration (4,750,000 ug/L) of all 270 mine discharges, but the iron discharge of 39.9 Ib/d ranked 26th of all 270 mine discharges. Mine discharge at site 122 contained the fourth highest measured iron concentration (690,000 ug/L), but its discharge of only 1.66 Ib/d ranked that mine discharge 107th of the 270 mine discharges.

On the top right side of table 4, the data are sorted with respect to total-iron discharges, with the highest measured discharge at the top of the data group in the column marked "Discharge, Ib/d" and the lowest measured discharge at the bottom. In this data group, mine discharge at site 16 contained the largest total iron discharge (1,700 Ib/d), but the concentration ranked only 41 of the 270 discharges. The reason for the highest measured total iron discharge was because of the very large flow (2,250 gal/min) in addition to a large concentration (63,000 ug/L). Mine discharges at sites 149 and 242 ranked very high in both iron discharge rank and iron concentration rank because both mine discharges contained high total- iron concentrations and high flows.

The bottom half of table 4 shows discharge ranks and concentration ranks for acidities that were sorted on the basis of acidity concentrations and acidity discharges. Site 242 ranked second of all 270 sites in acidity discharge rank and acidity concentration rank. The iron and acidity columns labeled "Discharge, Ib/d" on the right side of table 4 gives the 27 mine discharges that are contributing most of the contaminant discharges of total iron and total acidity to the receiving streams.

The next section in this report integrates discharges of total iron, total manganese, dissolved aluminum, acidity, and sulfate to prioritize all sampled mine discharges for remediation.

16

Table 4. Flows, concentrations of total iron and acidity, and iron and acidity discharges and discharge rank for mine discharge sites in the Stonycreek River Basin

[gal/min, gallon per minute; ng/L, microgram per liter; Ib/d, pound per day; mg/L, milligram perliter; <, less than]

Site

202427912216514922814124158192174180191219166142578094125225184127176148179

Site

202427912216514112514221922711712415824

18818016673118609480140208593

204

Flow(gal/min)

0.7222.0.2

18310

.1483.5

2.17.5

25518132.51.6.4

2.522560451.3

330.2

7.5

Flow(gal/min)

0.7222.0.2

1848

2252.5

187.5

2118

.53

5125131.6.3

6.42.5.4

27374

3.115560

Iron(H9/L)

4,750,0002,750,0001,300,000690,000320,000300,000220,000210,000210,000200,000190,000180,000180,000180,000160,000150,000140,000130,000130,000130,000130,000120,000120,000110,000110,000100,00095,000

Acidity(mg/L)

19,70012,2003,9403,6201,60013001,1801,120940940934866850840820820820780734720714700684680660630620

Discharge(Ib/d)

39.972631.21.66

69.11,120

.26121

7.561.204.79

16.254.010.834.623.44.202.50.62

3.9035186.464.81.72

436.24

8.55

Discharge(Ib/d)

1653,230

94.68.69

345751

3,18033.6

20384.6

235187

5.1030.2

50124612815.02.64

55.321.43.36

2223,050

24.61,170446

Dischargerank

264

31107172

1641268118764223542934819113983614201055

16561

Dischargerank

372

501212463

7932553035136831628441021616394154314887

20

Site

1614919

24217612517817311034

141812251092216515971843818020595

2482055

Site

16242125208149193414

141811891761102218810310463

20497389516516415

160

Flow (gal/min)

2,250310

1,78022

330225

1,62047044915534848

1,40060180224189619745782575

981114<145

Flow (gal/min)

2,25022

225374310

1,78015534879948

1,40053933044922451

4362002776019778

981189796171

Iron (WJ/L)

63,000300,00041,000

2,750,000110,000130,00017,00034,00030,00075,00030,000

210,0006,900

120,00039,00030,000

320,00060,00028,000

120,00066,000

180,00052,0003,500

30,0004,750,000

72,000

Acidity (mg/L)

25012,2001,18068054074

63027088

1,300441001621002008209219414062018644230

1,600260222120

Discharge (Ib/d)

1,7001,12087672643535133019216214012512111686.484.280.669.169.166.264.861.854.046.841.241.039.938.9

Discharge (Ib/d)

6,7503,2303,1903,0502,0101,5801,1701,130844751739647642539538502481466465446440414353346303256246

Concen tration rank

416

572

252193687532768

1242260745

458023401349155771

35

Concen tration rank

6127

243013226551196

15610176102661511168852771401685

566293

17

Remediation-Prioritization Index

A primary goal of the Stonycreek River Basin project was to prioritize individual mine discharges by a method that would show their relative severity with respect to all sampled discharges throughout the basin. If applicable, this method also could be used in other subbasins that are severely affected by mine drainage. A priority numbering system, or prioritization index (PI), was developed to identify the mine discharges that have the greatest effect on the receiving streams and that should be given a high priority for remediation. The remediation work would be designed to improve water quality in tributary streams and in the Stonycreek River. The PI was based on a site-to-site comparison of discharges of selected water- quality constituents. Discharges of the specific constituents were determined by multiplying the concentration in milligrams per liter or micrograms per liter times the flow rate in gallons per minute times a constant of 0.012 (for milligrams per liter) or 0.000012 (for micrograms per liter). The constant was used to convert concentration (in milligrams per liter or micrograms per liter) per flow rate (in gallons per minute) to pounds per day. Most mine discharge samples were collected during base-flow conditions. Because of funding limitations, sampling all 270 mine discharges at different flow conditions was not feasible. However, approximately 48 of the mine discharges were resampled 1 to 5 times and the data in appendix 3 show that the flow rate and constituent concentrations varied at the resampled sites. Data from the first sample collected at each mine discharge site were used for the PI calculations. When water-resource managers consider remediation at specific sites on the basis of these first-sample comparisons, they can take into consideration all data collected at each site and may want to consider collecting additional data at different flows and in different seasons to design treatment systems properly. The water-quality constituents used to calculate the PI included total iron, total manganese, dissolved aluminum, acidity, and total sulfate. The pH was indirectly used in the PI as a tie breaker for constituent discharges that were identical. These factors are related either directly or indirectly to the effects of coal-mine drainage on water quality. Low pH and high acidities are common to the most severe mine discharges. Total iron, total manganese, and pH in coal-mine drainage are limited by Federal regulations. The sulfate discharge is a reliable indicator of mine drainage because the neutralization processes that can occur in a mine discharge or stream do not greatly affect sulfate concentrations. Dissolved aluminum in waters having low pH affects fish and some other forms of aquatic life (Driscoll and others, 1980). Flow of a mine discharge is very significant because the flow and the concentration of a constituent determine the constituent discharge.

A computerized spreadsheet of the water-quality data at all sites was used to simplify the PI calculations. The spreadsheet was used to complete a primary sort on the discharges of each constituent in order of ascending or improving water quality. Table 5 shows how total-iron discharges were sorted, ranked, and scored for the PI calculations. The left four columns of table 5 show the unsorted total-iron data for sites 1 through 56. The right six columns of table 5 show how the 56 sites of all 270 sites with the highest total-iron discharges were sorted, ranked, and scored. The text below refers to the sorted total-iron data in table 5. A rank number was assigned to each total-iron discharge in a descending order, with a rank 1 for the largest total-iron discharge (1,700 Ib/d), and a rank 56 for the smallest total-iron discharge (10.2 Ib/d). Each discharge was then given a score based on the rank. A score of 1 to 10 was assigned to each discharge by subdividing the 270 sites into 10 percent groups. The first 10 percent group (rank 1-27) received a score of 10. The next 10 percent group (rank 28-54) received a score of 9, and so on. If sites had identical discharges, a secondary sort was conducted on the discharges to break the tie, using pH as the tie breaker. The discharge with the lower pH received the lower rank number. Sites 165 and 15 both had total-iron discharges of 69.1 Ib/d. The pH at site 165 was 2.7 and the pH at site 15 was 3.6, so site 165 received the lower rank number. Discharges for all five water-quality constituents were sorted, ranked, and scored by this method. The final score for each site was then calculated by adding the scores for the five water-quality constituents. The final rank or PI was determined by assigning the largest final score the number 1, the second largest score the number 2, and so forth through all 270 sites. Flow was used as a tie breaker for identical final scores. The site with the largest flow received the lower rank number. The final rank or PI shows which mine discharges have the greatest potential effect on the water quality of the receiving streams, in a descending order. The complete spreadsheet showing the individual ranks and scores for each water-quality constituent at all sampled discharges and the final PI for each mine discharge is given in appendix 4.

18

Table 5. Unsorted total-iron data and sorted, ranked, and scored total-iron data used for the Prioritization Index (PI) calculations

[gal/min, gallons per minute; ng/L, micrograms per liter; Ib/d, pounds per day]

Unsorted total-iron data

Site number

123456789

1011121314151617181920212223242526272829303132333435363738394041424344454647

Flow (gal/min)

169.0

155348341306

915.86.7

1221368652

79996

2,250284

111,780

.746

224123.03.91.51.0

84194.4

155188.4

424843

6.87863759.0

36.5

133.04

201.6

Total-iron concentration

(ng/L)46,000

3,80075,00030,000

409,900

11,00062,00038,000

7505,800

13,0008,300

88060,00063,000

3,4006,600

41,0004,760,000

6,90030,000

300210,00068,00023,00030,000

1,20030

2,1002,0001,100

33032,000

5,20013,000

1,10066,000

8204,800

78,0005,400

27,000140290

7,50038,000

Total-iron discharge

(Ib/d)8.83

.410140125

.16436.412.04.323.061.109.47

13.425.188.44

69.11,700

11.6.871

87640.0

3.8180.6

.0437.563.18

.414

.3601.21.007.111

3.72.238.033

16.13.006.71

.09061.8

.6204.328.422.33

.162

.223

.0001.800.730

Site number

16149

19242176125178173110

34

14181

22510922

1651597

18438

180205

95248

2055

6219204

7916414416614058

18824920817010417434

1216312

169

Sorted,

Flow (gal/min)

2250310

178022

330225

162047044915534848

140060

180224

1896

19745782575

981114

.745

3061860

297

1851327355141

374142200

7.542

1510277

8615

, ranked, and scored total-iron data


(HQ/L)63,000

300,00041,000

2,750,000110,000130,000

17,00034,00030,00075,00030,000

210,0006,900

120,00039,00030,000

320,00060,00028,000

120,00066,000

180,00052,0003,500

30,0004,760,000

72,0009,900

160,00048,000

1,300,00026,00013,000

150,00070,00047,00031,00036,000

3,7009,7006,800

180,00032,000

7604,100

13,00074,000


(Ib/d)1,7001,120

87672643635133019216214012512111686.484.280.669.169.166.264.861.854.046.841.241.040.038.936.434.634.631.230.328.923.422.719.719.017.716.616.516.316.216.113.813.613.413.32

Rank

123456789

1011121314151617181920212223242526272829303132333435363738394041424344454647

Score

101010101010101010101010101010101010101010101010101010

99999999999999999999

19

Table 5. Unsorted total-iron data and sorted, ranked, and scored total-iron data used for the Prioritization Index (PI) calculations Continued

[gal/min, gallons per minute; ng/L, micrograms per liter; Ib/d, pounds per day]

Unsorted total-iron data

Site number

484950515253545556

Flow (gal/min)

8.03.41.0

18.2

4.61114520


(ng/L)6,4004,800

330300

9,5001,2007,900

72,000240


(Ib/d)

.614

.196

.004

.065

.023

.06610.52338.880

.058

Site number

190160

717

18720719154

124

Sorted,

Flow (gal/min)

6017191

28436

2215

11118

, ranked, and scored total-iron data


(ng/L)18,0005,900

11,0003,400

26,0004,200

180,0007,900

47,000


(Ib/d)

12.9612.1112.0111.5911.2311.1410.8010.5210.15

Rank

484950515253545556

Score

999999988

A PI also was established for all mine discharges in certain subbasins that were moderately to severely effected by mine drainage. This was done so that water-resource managers could work on a subbasin approach in designing remediation plans. The subbasins prioritized included Shade Creek, Paint Creek, Wells Creek, Quemahoning Creek, Oven Run, and Pokeytown Run. The subbasin data are listed in tables 6-11. Locations of the subbasin sites are shown in figures 6-11

The GIS data base containing the site locations and PI provides an effective means for viewing the spatial distribution and magnitude of each sampled mine discharge throughout the basin. The GIS was also useful in viewing spatial relations of mine discharges with high quality streams, population centers, existing wetlands, land use, and land slope.

20

Table 6. Prioritization index (PI) for coal-mine discharges in the Shade Creek Basin

[gal/min, gallon per minute; Ib/d, pound per day; <, less than]

Site number

1619151438424076

221231

2075

234236

41215214232247235216

392333727

22923023843

245200265

86243

85246201237244266267239222240

PH (units)

3.35.1

3.63.63.03.13.13.43.23.42.43.33.55.45.53.03.12.76.63.75.56.22.73.63.06.26.15.33.56.04.66.36.66.34.66.44.23.66.36.86.66.05.65.8

Iron, total (Ib/d

as Fe)1,700

87669.18.44

61.82.334.327.142.09

.9239.9

1.983.22

.028.42

.35

.131.08

.39

.066.27

.62

.49

.09

.36

.63

.35

.01

.16

.03

.021.04.07.19.06

<.01<.01

.12

.01

.06

.07

.05<.01

.01


(Ib/d as CaCO3)6,750158025684441486.4

14852.947.562.2

16528.813.825.913.09.468.356.58<.015.699.65<.014.032.945.04<.01<.014.03

.83<.012.16

.46<.01<.01

.33<.01

.50

.20<.01<.01<.01

.02<.01

.03

Sulfate, total

(Ib/d as S04)

29,70010,300

1,1307,000

796562378239612478227176104421

52.953.463.429.6

6756.7

39.415920.421.210.697.925.1

1192.16

67.712.66.91

15.112.38.40

32.32.111.736.344.61

.02

.114.18

.98

Aluminum, dissolved

(Ib/d asAI)486

25.618.493.038.4

6.0512.64.123.313.281.341.22

.10

.39

.01

.38

.85

.02

.10

.18

.01

.08

.05

.19

.50

.04

.01

.04

.05

.02

.05<.01

.01

.01<.01<.01

.01<.01<.01<.01<.01<.01<.01<.01

Manganese, total (Ib/d

asMn

23285.419.664.2

6.0811.24.861.341.735.76

.501.221.14

.39

.44

.58

.29

.36

.68

.71

.33

.46

.28

.25

.14

.11

.17

.01

.06

.02

.05

.08

.05<.01

.08

.01

.01<.01<.0l<.01

.01<.01<.01<.01

Discharge, instantaneous

(gal/min)

22501780

96799

783675356048

.730

7.945

97.3

121.3

677.96.7

6316.81

247.2

14.5

127.51.297.92.53.91.6

.24.8

.8

.4

.11.2

.2

Final score

50505049494544444343424038343434333231313130292828272322222121211717171414131110101099

PI

123456789

1011121314151617181920212223242526272829303132333435363738394041424344

21

Table 7. Prioritization index (PI) for coal-mine discharges in the Paint Creek Basin

[gal/min, gallon per minute; Ib/d, pounds per day; <, less than]

Site number

8112514118810310418414011712431

2191011874428

13912646

14210011179327778

11611218529

11396

21726812733

11430

220115138218

8011810245

PH (units)

4.82.42.72.63.23.02.82.53.12.63.22.43.22.43.63.12.62.93.22.25.83.42.23.43.84.53.63.52.74.13.36.32.96.32.63.93.53.13.53.62.75.62.72.64.79.7

Iron, total (Ib/d

asFe)116351121

19.07.85

16.364.822.7

8.3210.23.72

34.62.39

11.2.22

1.219.201.221.804.20

.21

.1931.2

.24

.10

.02

.16

.061.39<.01

.04

.381.32

.341.72.03.04.11.03.05.33.27.62.22.01

<.01


(Ib/d as CaC03)

7393,180

75150248146624222223518718220313216499.0

10173.086.150.433.65.07

29.594.613.824.321.813.710.713.211.98.72<.01

10.7<.017.584.445.947.395.574.314.11<.013.362.642.16<.01

Sulfate, total

(Ib/d as S04)

12,1008,640

8641,4705,7603,8401,240

648605648670518

1100562

1150433250253118102

177021614920710067917813254.7

14194.8

43729.7

32625.086.779.224.854.756.216.7

2656.246.84

14.6.41

Aluminum, dissolved

(Ib/d asAI)

31.9232

42.661.234.031.213.010.427.719.216.92.596.609.508.629.983.128.745.281.471.863.062.381.323.10

.631.151.15

.621.62

.91

.08

.54

.14

.02

.50

.58

.74

.47

.37

.21

.06

.12

.23

.06<.01


asMn47.0

17863.425.725.633.62.27

15.617.111.410.66.702.531.343.995.856.087.491.182.792.912.34

.24

.932.69

.941.19

.75

.09

.32

.58

.29

.09

.33

.50

.57

.48

.40

.59

.51

.44

.01

.03

.12

.08<.01


(gal/min)

14002254851

43620045272118

15518

11736

13384132620

2.5352

302

183.8

651512

1.9197.9

522.5

401.38.45.54.48.63.91.6

33.4.3

15.04

Rnal score

5050494847474343434241403838373736353231303029272725252321202019191818171717161615141212

65

PI

123456789

10111213141516171819202122232425262728293031323334353637383940414243444546

22

Table 8. Prioritization index (PI) for coal-mine discharges in the Wells Creek Basin


Site number

2217101121023223

9

18

Table 9.

[gal/min,

Site number

208

176

172

173

259

174

175

209

48

258

54

53

171

47

183

92

182

52

256

257

PH (units)

3.03.33.54.4

5.8

3.4

5.6

6.1

6.4

Iron, total (Ib/d

as Fe)

80.611.61.109.47

9.43

.04

.75

3.06

.87


(Ib/d as CaCO3)

53819835.132.6

<.01

14.4

1.74

<.01

<.01

Sulfate, total

(Ib/d as S04)

2,020

1,260

571

588

524

51.8

78.0

30.6

31.7

Aluminum, dissolved

(Ib/d asAI)

25.5

17.0

2.78

1.31

.35

1.58

.06

.01

.01


asMn

20.26.48

1332.61

5.35

1.30

.90

.21

.11


(gal/min)

224284122

136

97

12

25

6.7

11

Final score

49443835

29

24

21

17

13

PI

1

2

3

4

5

6

7

8

9

Prioritization index (PI) for coal-mine discharges in the Quemahoning Creek Basin

gallon per minute; Ib/d,

PH (units)

6.2

5.9

2.8

6.2

6.3

5.0

3.2

3.5

4.5

3.8

6.7

3.6

6.6

3.2

4.2

5.8

5.2

3.8

5.8

6.9

Iron, total (Ib/d

as Fe)

16.6

436

2.38

192

1.87

16.2

2.22

6.68

.61

1.51

10.5

.07

.79

.73

.05

.02

.18

.02

<.01

<.01

pounds per day; <, less than]


(Ib/d as CaCO3)

3,050

642

93.6

<.01

<.01

30.6

7.20

<.01

4.80

6.42

<.01

3.97

<.01

3.69

1.44

.24

.20

.12

.05

<.01

Sulfate, total

(Ib/d as S04)

5,830

1,780

342

4,570

4,580

83.7

28.8

230

53.8

38.4

129

28.2

124

14.8

7.56

22.4

1.44

1.32

.30

4.09

Aluminum, dissolved

(Ib/d asAI)

539

.40

8.64

1.13

1.35

.07

.32

.15

.27

.21

.19

.43

.11

.17

.14

<.01

<.01

<.01

<.01

<.01


asMn

58.3

24.2

5.04

24.8

1.98

1.17

.66

.92

.87

.33

.84

.04

.42

.27

.10

.02

.03

<.01

<.01

<.01


(gal/min)

374

330

30

470

867

7.5

5

64

8

3.3

111

4.6

69

1.6

3

1.7

1

.2

.8

1.1

Final score

49

46

43

41

35

35

33

31

31

30

28

25

23

23

20

16

15

11

8

7

PI

1

2

3

4

5

6

7

8

9

10

11

12

13

14

15

16

17

18

19

20

23

Table 10. Prioritization index (PI) for coal-mine discharges in the Oven Run Basin

[gal/min, gallon per minute; Ib/d, pounds per day]

Site number

360

22724

72

59

71

73

158

159

pH (units)

2.8

2.9

3.0

3.0

3.7

2.9

3.8

3.5

3.8

4.6

Iron, total (Ib/d

asFe)

140.38

1.897.56

.08

2.72

.10

1.73

1.20

.09


(Ib/d as CaC03)

1,17055.384.630.2

45.4

24.6

24.3

15.0

5.10

2.54

Sulfate, total (Ib/d

as S04)

2,980384144122

144

100

100

76.8

21.6

21.2

Aluminum, dissolved

(Ib/d asAI)

1006.609.902.23

5.78

2.05

3.10

1.09

.44

.36


as Mn)

42.8

10.8

1.71

4.68

4.54

2.90

2.69

2.30

.72

.66


(gal/min)

1556.47.5

3.0

8.6

3.1

3.8

1.6

.5

2.3

Final score

503935343028221912

6

PI

1

2

3

4

5

6

7

8

9

10

Table 11. Prioritization index (PI) for coal-mine discharges in the Pokeytown Run Basin


Site number

2424

34

1

94

35

2

87

pH (units)

2.3

2.8

2.7

2.8

3.0

6.0

3.1

6.4

Iron, total (Ib/d

asFe)

726125

16.1

8.83

3.90

3.00

.41

.24


(Ib/d as CaC03)

3,2301,130

15673.021.4

<.01

9.94

<.01

Sulfate, total

(Ib/d as S04)

5,280

4,010

605

288

51.0

173

107

12.7

Aluminum, dissolved

(Ib/d asAI)

25983.510.66.14

.75

.12

.56

<.01


asMn

7.39

21.7

7.06

5.76

4.50

1.84

.95

.09


(gal/min)

22348

42

16

2.5

48

9

1.8

Final score

4946

40

35

28

24

23

15

PI

1

2

3

4

5

6

7

8

24

. 236^2k ''.

N

&

; ' J...^x~

V ,/"""<" <'

.s :\

SMILES

SMILES

EXPLANATION

STREAMS BASIN BOUNDARY 27 MINE DISCHARGE SITE

> AND NUMBER

STONYCREEK RIVER BASIN

Figure 6. Location of the coal-mine-discharge sites in the Shade Creek Basin.

25

/ *...

" %

V .. _

SMILES

EXPLANATION

STREAMS - BASIN BOUNDARY

MINE DISCHARGE SITE 220 AND NUMBER

Stonycreek River Basin

Figure 7. Location of the coal-mine-discharge sites in the Paint Creek Basin.

26

\ *'

-* . X

/I L - 210

/ 18 \

I /*

V

v

17 x-

sv% V'-\^ \10 V

« L \

SMILES

3 KILOMETERS

EXPLANATION

STREAMS

- - BASIN BOUNDARY

MINE DISCHARGE SITE 223 AND NUMBER

Stonycreek River Basin

Figure 8. Location of the coal-mine-discharge sites in the Wells Creek Basin.

27

N

1 ??, » " y -x\ U^JH l><:- " "-' % ">t ?&, ^ : / .., ?

i» . '" . I'*..; Vtt * .^* .,*' *

f I "T^vft" ' } s "" :\ : ' ./-^f-vix }"* \\ \ : ' 1--^%.. ,,. / . ' -- v,. S. , . : -^^ y4-TA " :..^\.. H !\A- \ /'-^N.^ 74 y

I s ,-^'x -- , : / , \ ; 17=^ / * "' Xs X^ 1 / f=;< ,J1

\ ** r .. ' f ....'^.. \ / .' > '; {' ../ VX'^ Xi>V f

"\. / >'"' :. \f i A .*' / ?\ /

V " ;-.....----..x \ '"i : ..... ^ / ':xt^ ^ ^.. % /"

^ . -.../"" v, , \ .. J53 V"' x- * /\.,X-----"x....,.-\^ ; - ^ ^ :'-: v^;;/ V ^ CO } ^

/ ..X---.---X x.-x,w../ ,»y x \ ' "" ) ""'^^ x ' 1454 >i .... K ^":: </'""-J

' ^ ^-,\X V ,. >-A 209^ / x * * s \ ' 'x\ f : - ( i"-x.-«<; /

. :-»:.... .. '' ' V .-i 1. . ""'"';: ,. * ;>-..- )---f' v^ ' : f \x /

» / ' .. * ''\

^ ^x..., . /- s ;rV^l x J "/""0 <:..} jyv^" °

QUEMAHONING^ CREEKBASIN /

^ $*vK ^^ /

:. Y -f ^

VI. )N fe\- :/ ""NJ:--1^-^/-^ /'

\ f ^ ' \ - ''~'* ^/^-. >--<7- / J *" ' -'"

3 6 MILES 1 1

1 6 KILOMETERS

EXPLANATION

STREAMS

_.. _ BASIN BOUNDARY

MINE-DISCHARGE SITE 208 AND NUMBER


Figure 9. Location of the coal-mine-discharge sites in the Quemahoning Creek Basin.

28

! *eo

f" *«59: 24| C 0 159

\ TS

71 72

\.. ^

1MILE

1 KILOMETER

EXPLANATION

STREAMS

- - BASIN BOUNDARY

MINE DISCHARGE 72 SITE AND NUMBER


Figure 10. Location of the coal-mine-discharge sites in the Oven Run Basin.

29

\ 2 % \ *.

\

A 35

8734

I I

/

1 MILE \ \J N -...'»

1 KILOMETER

POKEYTOWN RUN BASIN

STONYCREEKRIVER BASIN

EXPLANATION

STREAMS

- - BASIN BOUNDARY

A 35 MINE DISCHARGE SITE 9 ANDNUMBER

Figure 11. Location of the coal-mine-discharge sites in the Pokeytown Run Basin.

30

Remediation by Passive-Treatment Systems

Within the last decade, passive-treatment systems have developed from an experimental concept to full-scale field implementation at hundreds of sites (Hedin and others, 1994). Passive technologies take advantage of natural chemical and biological processes that improve the quality of contaminated water. Passive-treatment systems use contaminant removal processes that are slower than conventional treatment systems. Passive-treatment systems must retain contaminated mine water long enough to decrease contaminant concentrations to acceptable levels. The retention time for a particular mine discharge is limited by available land area, and therefore, the sizing of passive-treatment systems is a crucial design aspect. Baseline water quality and flow must be known to design AMD-treatment systems properly.

Three principal types of passive technologies are currently in use for the treatment of coal-mine drainage: aerobic wetland systems, wetlands that contain an organic substrate (compost wetlands), and ALD's. In aerobic wetland systems, oxidation reactions occur and metals precipitate primarily as oxides and hydroxides. Most aerobic wetlands contain cattails (Typha latifblia) growing in clay or spoil substrate. Plantless systems also have been constructed and function similarly to those containing plants if the influent water is alkaline. However, it is recommended that plants be included because they may help filter particulates, prevent flow channelization, and benefit wildlife. The water depth in a typical aerobic system is approximately 6 to 18 in.

Compost wetlands are similar to aerobic wetlands in form but also contain a thick layer of organic substrate. This substrate promotes chemical and microbial processes that generate alkalinity and neutralize acidic components of mine drainage. Typical substrates used in compost wetlands include spent mushroom compost, Sphagnum peat, hay bales, and manure.

ALD's are commonly used to treat AMD before it flows into a constructed wetland. The ALD raises the pH of the water to circumneutral levels (pH 6 to 7) and introduces bicarbonate alkalinity that neutralizes the acidity. When water exits the ALD, the circumneutral pH level promotes metal precipitation (Hedin and Narin, 1993). The limestone and mine water in an ALD are kept anoxic by sealing the drain to atmospheric oxygen to avoid armoring of the limestone with ferric hydroxide.

Each of the three passive technologies is most appropriate for a particular type of mine-water problem, but commonly, they are most effectively used in combination with each other. Examples are shown in figures 12 and 13. A passive-treatment system in which three ALD's, a constructed wetland, and two limestone cells are used in series to treat mine drainage from reclaimed surface mine spoils that were approximately 10 years old is shown in figure 12. This passive-treatment system is at an experimental site of the U.S. Bureau of Mines in the Shade Creek Basin, a subbasin of the Stonycreek River Basin. Kepler and McCleary (1994) have conducted research on a system called a successive alkalinity-producing system (SAPS) that combines ALD technology with the sulfate reduction mechanism of the compost wetland. A typical cross-sectional view of a SAPS treatment component is shown in figure 13. This system can be used to treat mine drainage that is extremely acidic (acidity concentration greater than 300 mg/L as CaCOa) and has high concentrations of ferric iron (concentrations greater than 1.0 mg/L). A series of SAPS is commonly utilized until the AMD either meets effluent criteria or the quality of the AMD improves to the degree proportional to the area available for treatment. Passive treatment technology is still evolving and developing as researchers continue to work on perfecting these treatment systems. Although the effluent from these treatment systems at abandoned mine sites may not meet compliance standards, passive treatment may provide the only practical means of improving the quality of the mine discharge. Hedin and Narin (1992) provide an extensive listing of passive-treatment literature for water-resource managers who may be involved in the passive treatment of contaminated mine discharges.

31

ANOXIC UMESTONE DRAINS

NOT TO SCALE

Figure 12. Layout of the Shade passive-treatment system in the Stonycreek River Basin (Modification from Narin and others, 1991).

FLUME

Figure 13. A typical cross-sectional view of a successive alkalinity-producing system treatment component (Kepler and McCleary, 1994, p. 198).

MPERMEABLE BARR.ER

32

SURFACE-WATER-QUALITY SAMPLING SITES

Locations

The 37 surface-water-quality sampling sites selected for this study are listed in table 12, and their locations are shown in figure 14. The sites were selected to include a variety of stream-quality conditions. The sites consisted of mainstem sites, tributary sites, sites affected by varying degrees of mine drainage, sites designated as high quality or exceptional value streams by the PaDEP, inflows to reservoirs, reservoir outflows, and sites where historical data are available. Five sites were established on the Stonycreek River (sites 801-805) and 32 sites were on tributary streams (sites 806-837). Sites 805 and 833 are streamflow- gaging stations where continuous streamflow data and periodic water-quality data are collected. Site 805 (Stonycreek River at Ferndale, Pa.) is 5.2 mi upstream from the confluence with the Little Conemaugh River and has been a streamflow-gaging station since 1913. This site was established as the outflow site for the Stonycreek River Basin because of its proximity to the river mouth and the availability of long-term streamflow data and periodic water-quality data. Ninety-seven percent of the Stonycreek River Basin is monitored at site 805. Site 833 (North Fork Bens Creek at North Fork Reservoir) is the main inflow to the North Fork Reservoir, a water-supply reservoir serving the greater Johnstown area. Data were collected at this site from 1984 to 1993 as part of a nationwide network to determine long-term effects of acid precipitation on base-flow stream quality (Aulenbach and others, 1996). Data collection was continued at this site in 1994 for this investigation. Site 801 is a mainstem site in the headwaters of the Stonycreek River and is, for the most part, unaffected by mine drainage. Sites 802-804 are mainstem sites at the towns of Kantner, Blough, and near Windber, respectively, and are affected by varying degrees of mine drainage. Eight tributary sites (sites 813,814,818, 824, 826,829,832 and 834) were previously sampled by the USGS during 1979-81 (Herb and others, 1981) as part of a monitoring network to collect hydrologic data in coal- bearing areas. Site 831 was previously sampled by the USGS from 1983 to 1986 to determine the effect of acid precipitation on stream-water quality (Barker and Witt III, 1990). Site 808 is a discontinued streamflow-gaging station on Clear Run operated by the USGS from 1961 to 1978. The remaining sites were near the mouth of tributary streams in the Stonycreek River Basin and at inflows to the Quemahoning Reservoir (sites 818-823), Indian Lake (sites 808 and 809), and Lake Stonycreek (site 807). Site 817 was at the outflow of the Quemahoning Reservoir and site 810 was at the outflow of Lake Stonycreek and Indian Lake.

33

Table 12. Surface-water-quality sampling sites in the Stonycreek River Basin

[°, degrees;', minutes;", seconds; -, no drainage area available]

Site number

801802803804805806807808809810811812813814815816817

818819820821822823824825826827828829830831832833834835836837

Station number1

03040000

03039200

0303930003039340

03039440

03039700

03039750

03039930

03039930030399500303992503039957

Location

Latitude40000'14"40006'11"40°10'18"40°14'37"40°171 08"39°58'36"40°00'33"40°02'50"40°03'37"40°00'56"40°00 1 58"40°04'14"40°04'11"40°05'35"40°07'06"40°08'41"40°11'21"

40°09'54"40°09'54"40°08'22"40°10'17"40°09'08"40°08'26"40°06'18"40°07'01"40°08'03"40°08'541140°10'59"

49 14'46"40°14'41"40°23'4r'40°15'02"40°15'58"400 16'58"40°18'21"40°12'43"40°07'38"

Longitude078°54'02"078°55'58"078°54'29"078°53'02"

078°5515"078°55'49"

07«°5116"078°49'58"078°51'37'078°54105"078°55'23"078°54'51"078°56'45"078°57'16"078°55'28"078°54'49"078°56'28"

079°0r51"079°04'05"079003'59"079°00'53"078058'57"078°58'04"078°47'55"078°48'16"078048'53"078°49'02"078°49'52"078°50'49"078°53'02"079°02'49"078°58'20"079001'0r'078°56'10"078°54'36"078°53'55"078°55'28"

Station name

Stonycreek River at ShanksvilleStonycreek River at KantnerStonycreek River at BloughStonycreek River near WindberStonycreek River at FerndaleGlades Creek near ShanksvilleBoone Run near ShanksvilleClear Run near BuckstownCalendars Run at BucktownRhoads Creek at ShanksvilleShrock Run near ShanksvilleLamberts Run at LambertsvilleWells Creek at MostollerBeaverdam Creek at StoystownOven Run at RowenaFallen Timber Run at HooversvilleQuemahoning Creek at Quemahoning

Reservoir OutflowQuemahoning Creek at BoswellBeaverdam Creek at JennerstownN Br Quemahoning Ck near Coal JunctionRoaring Run at PilltownTwomile Run near BoswellHiggins Run near BoswellDark Shade Creek at Central CityLaurel Run at Central CityDark Shade Creek at ReitzClear Shade Creek at ReitzRoaring Fork near HillsboroLittle Paint Creek at Scalp LevelPaint Creek near WindberSouth Fork Bens Creek near ThomasdaleSouth Fork Bens Creek near FerndaleNorth Fork Bens Creek at North Fork ResBens Creek at FerndaleSolomon Run at JohnstownShade Creek at SeanorPokeytown Run at Wilbur

Drainage area

---

451~

3.68

26.1--

16.818.5-

2.4898.2

58.5---

5.525.818.51

10.035.831.4-

12.436.8

3.2818.13.45

41.68.47

96.7-

1 For sites that have no station number listed, the station number is the 15 digit number that includes the latitude, longitude, and a 01 identifier at the end. For example, the station number for site 801 would be 400014078540201.

34

r ;

I'ao&

3 6 MILESj__i__i__i__i__I

i i i i r

3 6 KILOMETERS800

EXPLANATION

STREAM

BASIN BOUNDARY

SURFACE-WATER QUALITY SAMPLING SITE AND NUMBER

Figure 14. Surface-water-quality sampling sites in the Stonycreek River Basin.

35

Water Quality and Contaminant Discharges

In order to determine base-flow stream quality and contaminant discharges, synoptic-sampling was conducted each year from 1992 through 1994 at the surface-water sites. Because no precipitation occurred within 5 days of each sampling period, any effects of direct surface runoff to the streams were eliminated. Consequently, the data provide a basinwide coverage of base-flow water quality. Low-base-flow samples were collected on September 1 and 2,1992, and July 27 and 28,1993, at the 63- and 76-percent flow durations at the Stonycreek River at Ferndale, Pa., respectively. High-base-flow samples were collected on May 23 and 24,1994, at the 35-percent flow duration. Surface-water-quality analyses are presented in appendix 5. Samples collected on July 27 and 28,1993, were during the lowest base-flow conditions of the three synoptic runs and are used to describe base-flow water quality throughout the basin. Specific conductance, pH, and concentrations and discharges of dissolved solids, alkalinity, acidity, total iron, total manganese, and sulfate in the mainstem and tributary streams in the Stonycreek River Basin are shown on figures 15-18.

The pH at mainstem sites 801 and 802 was near neutral, but at mainstem sites 803-805, the pH was 4.2 or less (fig. 15). The pH from the mainstem corresponds with changes in the alkalinity and acidity on the mainstem (fig. 16). As the pH decreased, the alkalinity decreased and the acidity increased. Alkalinity at mainstem site 801 and tributary streams between 801 and 802 effectively neutralizes most acidity in the mainstem at site 802. However, the extremely high acidities at tributary sites 815 and 837 eliminate the neutralizing capability in the mainstem, and the mainstem remains acidic from site 803 to outflow site 805. Tributary sites 836 and 830 also contribute significant acid discharges to the mainstem. Specific conductance and dissolved-solids concentrations do not significantly change from mainstem site 801 to mainstem site 805 because of dilution from tributary streams (fig. 15). However, specific conductance and dissolved-solids concentrations vary in the tributary streams. Dissolved-solids discharges gradually increase from mainstem sites 801 to 803 and then increase significantly at mainstem sites 804 and 805. The large increases at sites 804 and 805 are the result of large dissolved-solids discharges entering the mainstem from tributary sites 830 and 836 and the increase in streamflow from site 804 to 805.

Total-iron concentrations vary considerably spacially in both the mainstem and in the tributary streams (fig. 17). Chemical reactions occurring within the stream, which promote the oxidation and precipitation of iron, contribute to the variation in concentrations of iron. The discharge of total iron increased from 30 Ib/d at mainstem site 801 to 684 Ib/d at mainstem site 805. The slight decrease in total- iron discharge from mainstem site 803 to site 804 was probably because of the precipitation of iron. Concentrations of total manganese also varied considerably in the mainstem and in the tributary streams (fig. 17). However, the discharge of total manganese increased considerably from mainstem site 802 to site 805. Very large discharges of manganese entered the mainstem from tributary sites 836 and 830. Manganese oxidation reactions and precipitation are strongly affected by pH and are very slow below pH 8.5. Therefore, the manganese entering the mainstem from the tributary streams did not precipitate and had an additive affect on mainstem discharges.

Sulfate concentrations are particularly high at tributary sites 812, 815, 830, and 837 (fig. 18). Mainstem sulfate concentrations gradually increase from sites 801 to 803 and then gradually decrease from sites 803 to 805. Neutralization reactions occurring in a stream generally do not change sulfate concentrations. The attenuation of the sulfate concentrations from mainstem sites 803 to 805 is probably because of dilution. Sulfate discharges gradually increase from mainstem sites 801 to 803 and significantly increase from sites 803 to 805 (fig. 18). The streamflow at sites 804 and 805 exceeded the streamflow at site 803 by 3.4 and 5.5 times, respectively, accounting for the large increase in sulfate discharges.

36

3,000

2,000 -

1,000 -O ZUJo-CO

11 1 1

1 1 1

MAINSTEM

III , 1 .Trim

co -t Z-J

2

4,000

3,000

2,000

§8j 1.000

C0<0-

COQQH

0

300

200

100

riHrvt tiiilil\ i i r i i

DOWNSTREAM TREND AT MAINSTEM SITES

MAINSTEM SITE

TRIBUTARY SITE

I I 1£ 8 oo oo

SITES, IN DOWNSTREAM ORDER FROM LEFT TO RIGHT

Figure 15. Specific conductance, pH, and concentrations and discharges of dissolved solids measured in the mainstem and in tributary streams in the Stonycreek River Basin on July 27 and 28,1993.

37

AC

IDIT

Y D

ISC

HA

RG

E,

IN P

OU

ND

S P

ER

DA

YA

CID

ITY

CO

NC

EN

TR

AT

ION

, IN

MIL

LIG

RA

MS

PE

R L

ITE

RA

LKA

LIN

ITY

DIS

CH

AR

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39

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Figure 18. Concentrations and discharges of total sulfate measured in the mainstem and in tributary streams in the Stonycreek River Basin on July 27 and 28,1993.

40

EFFECTS OF COAL-MINE DISCHARGE ON THE QUALITY OF STONYCREEK RIVER AND ITS TRIBUTARIES

Coal-mine discharges affected surface-water quality throughout all of Appalachia. AMD continues to flow from some underground mines and coal refuse piles that are already a century old. In 1967, the Federal Water Pollution Control Administration (U. S. Department of the Interior, 1967) estimated that 78 percent of Appalachia's mine-drainage problems were from inactive and abandoned mines and coal refuse piles. However, with the enactment of the Surface Mining Control and Reclamation Act of 1977 and the establishment of effluent limitations for coal mining (Code of Federal Regulations, 1994), the total stream miles affected by mine drainage have decreased and inactive and abandoned mine sites now account for 99 percent of AMD problems in streams (Kleinman and others, 1988). This assessment is probably accurate for streams in the Stonycreek River Basin because effluents from all active mining operations must meet current effluent limitations (table 1).

When mine spoils containing sulfides are exposed to air and water, the sulfide minerals are oxidized by a series of microbial and chemical processes. The products of these reactions are carried into surface waters where they degrade water quality via acidification, metal contamination, and sedimentation. AMD waters are characterized by high metal and sulfate concentrations, high conductivity, and low pH (Mills, 1985).

Physical properties and chemical constituents varied during low-base flow on tributary streams and mainstem sites in the Stonycreek River Basin (figs. 15-18). Mine drainage flowing into a stream will affect most of those constituents. However, because of various physical and chemical processes such as precipitation, neutralization, and adsorption, changes in concentrations of stream constituents can occur that are not related to mine drainage. Sulfate is not affected by neutralization and precipitation processes and therefore, sulfate concentrations and discharges can be used as a reliable indicator of mine drainage in streams (Tolar, 1982, p.8). Bencala and others (1987) found that sulfate was an excellent conservative tracer of AMD in a stream system in Colorado. Very few processes act to remove sulfate from solution in stream water. The concentration of sulfate in streams depends on the amount produced at the source (a mine discharge) and the subsequent dilution in the stream. Dilution depends on streamflow, which can vary with factors such as precipitation and drainage area. Because of the dilution factor, sulfate concentrations cannot be compared from stream to stream as a reliable index of mine drainage. However, the resultant sulfate discharges can be compared from stream to stream or within a stream as a reliable indicator of mine drainage. The measured sulfate discharges of tributary streams and the measured and calculated sulfate discharges of the mainstem sites are shown in figure 19. The calculated mainstem discharges were determined by adding the upstream mainstem discharge with the measured downstream tributary discharges to determine the next mainstem discharge. For example, the sulfate discharge measured at mainstem site 801 (6 ton/d) was added to the discharges from tributary site 810 (2 ton/d), tributary site 811 (3 ton/d), tributary site 812 (19 ton/d), tributary site 813 (3 ton/d), and tributary site 814 (1 ton/d) to arrive at a calculated sulfate discharge of 34 ton/d at mainstem site 802. The measured sulfate discharge at mainstem site 802 was 26 ton/d. A good correlation between the measured mainstem sulfate discharges and the calculated sulfate discharges is shown in figure 19. The calculated sulfate discharges at mainstem sites 803-805 were less than the measured discharges because sulfate discharges from some mine discharges that flow directly into the Stonycreek River were not measured. Sulfate discharges from Shade Creek (site 836) (44 ton/d) and Paint Creek (site 830) (26 ton/d) had the largest effect on sulfate discharges in the Stonycreek River.

Water-quality analyses from five mine discharges and the receiving streams above and below the mine discharges are presented in table 13. The water quality at mine-discharge site 14 did not affect Dark Shade Creek, primarily because that section of Dark Shade Creek was already severely affected by mine drainage.

41

170

160

150

140

130

120

110

100

90

80

70

60

50

40

30

20

10


MAINSTEM SITE

TRIBUTARY SITE


Figure 19. Measured total sulfate discharges in tributary streams and measured and calculated total sulfate discharges in the mainstem of the Stonycreek River on July 27 and 28,1993.

42

Table 13. Water-quality data for five coal-mine discharges and the receiving streams

[ug/L, microgram per liter; mg/L, milligram per liter]

Site


(cubic feet per second)

PH (units)

Iron, totalfog/l as Fe

Manganese, total(MQ/L

asMn)

Alkalinity (mg/L as CaCO3)

Acidity, total

heated (mg/L as CaCO3)

Sulfate, total

(mg/L as SO4)

Octobers. 1992

Dark Shade Creek above site 14Site 14Dark Shade Creek below site 14

15.21.51

17.5

3.93.73.9

21,2001,980

19,200

2,6206,8602,910

000

8410082

334678342

Octobers. 1992

Laurel Run above site 15Site 15Laurel Run below site 15

3.60.12

4.30

5.43.54.9

35857,400

1,840

33813,300

695

2.002.0

16230

22

24799

45Septembers. 1993

South Fork Bens Creek above site 178Site 178South Fork Bens Creek below site 178

1.682.143.82

7.46.56.8

6813,4602,650

454484468

46162110

000

89606344

September 9. 1993

Wells Creek above site 17Site 17Wells Creek below site 17

1.22.32

1.54

7.23.46.4

1991,860

804

4621,740

742

260

12

058

0

233499243

Mav 12. 1994


19.12.34

21.4

6.83.76.4

1,050908

1,030

303762358

1107.4

030

.8

83226

90September 9. 1993


1.52.30

1.82

6.32.93.9

80624,4005,160

7527,4101,930

1000

3.617432

243880406

Mav 12. 1994


23.42.47

25.8

6.43.45.3

1,3309,2802,240

3783,740

733

7.402.2

4.482

6.2

91399115

43

Mine discharge 15 did affect Laurel Run even though the flow of the mine discharge was only 3 percent of the flow in Laurel Run. Concentrations of total iron, total manganese, total sulfate, and acidity increased and pH decreased.

Mine discharge 178 is a treated mine discharge that had a significant effect on the South Fork Bens Creek. One positive effect was the addition of alkalinity to the stream. The discharge accounted for 56 percent of the streamflow in South Fork Bens Creek.

Mine discharges 17 and 22 flow into Wells Creek and were sampled during low- and high-base flow. Mine discharge 22 enters Wells Creek about 900 ft downstream from where site 17 enters Wells Creek. These two discharges significantly affect the water quality of Wells Creek at both low- and high-base flow (table 13). Figure 20 graphically shows how these two mine discharges affect Wells Creek during low-base flow. The pH in Wells Creek decreased from 7.2 to 3.9. Stream alkalinity was completely depleted by the acidity of the two mine discharges. Sulfate discharges increased from 0.76 to 2.0 ton/d. Discharges of total iron increased from 1.3 to 51 Ib/d. Plots of the data from sites 17 and 22 collected on May 12,1994 (not shown), show that the two mine discharges had a similar effect on Wells Creek during high-base flow as is shown on figure 20 for low-base flow. The discharges and concentrations were different, but the trends were similar. The PI in Appendix 4 shows that sites 17 and 22 are ranked 28th and 7th, respectively, for mine-discharge remediation in the Stonycreek River Basin. The PI in table 8 shows that sites 17 and 22 are ranked second and first, respectively, for mine-discharge remediation in the Wells Creek Basin.

Surface-water-quality data collected from the mouth of Oven Run (site 815) and Pokeytown Run (site 837) and from the Stonycreek River above and below where each of those runs flow into the river are given in table 14. Oven Run flows into the Stonycreek River near the town of Rowena. Pokeytown Run flows into the Stonycreek River approximately 0.5 mi downstream from the Oven Run inflow. Both Oven Run and Pokeytown Run are severely affected by AMD, and each significantly deteriorates Stonycreek River water quality. The Oven Run outflow is the first source of highly degraded water from AMD into the Stonycreek River. Both have many mine discharges but a major discharge in each basin is responsible for most of the AMD in the two streams. Mine discharge site 3 has a significant effect on Oven Run, and mine discharge site 4 has a similar effect on Pokeytown Run. Mine discharges 3 and 4 ranked 8th and 5th, respectively, on the PI for the Stonycreek River Basin (Appendix 4). The flows at mine-discharge sites 3 and 4 on August 18,1993, were 0.23 and 0.20 ft3/s, respectively. The streamflows in Oven Run and Pokeytown Run on September 8,1993, at low-base flow were 0.56 and 0.41 ft3/s, respectively. If the discharges at the mine-discharge sites and the streamflow in the streams were similar on both days, mine- discharge site 3 accounted for 41 percent of the streamflow in Oven Run and mine-discharge site 4 accounted for 49 percent of the streamflow in Pokeytown Run.

Table 14. Water-quality data collected on Septembers, 1993, for Oven Run, Pokeytown Run, and the Stonycreek River above and below where each of the runs flows into the river

[|Kj/L, microgram per liter; mg/L, milligram per liter]

Site

Stonycreek River above Oven RunOven RunStonycreek River below Oven RunStonycreek River above Pokeytown RunPokeytown RunStonycreek River below Pokeytown Run

Discharge,instantaneous

(cubic feet per second)

17.4.56

18.023.0

.4123.4

pH (units)

7.62.87.26.32.75.1

Iron,total(nO/l- as Fe

30915,900

769599

490,00014,000

Manganese,total(nO/l-

as Mn)

29628,000

1,3101,410

13,6001,860

Allolinitv

(mg/L as CaC03)

420

3832

02

Acidity, total

heated (mg/L as CaC03)

0354

00

2,18050

Sulfate,total

(mg/L as S04)

3821390

415472

4,120644

44

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150

100

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60

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20

II

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WELLS CREEK SITES

MINE DISCHARGE SITE

UJUJoct oco oct

oco oct oco cou


Figure 20. The effects of mine discharges 17 and 22 on Wells Creek on September 9,1993.

45

The pH in the Stonycreek River decreased from 7.6 above Oven Run to 5.1 below Pokeytown Run (fig. 21). The alkalinity in the Stonycreek River was adequate to neutralize the acidity from Oven Run, but the large acidity discharges from Pokeytown Run almost eliminated the available alkalinity in the river. Alkalinity in the Stonycreek River decreased from 42 mg/L above Oven Run to 2 mg/L below Pokeytown Run. Sulfate discharges in the Stonycreek River were 18 ton/d above Oven Run and 41 ton/d below Pokeytown Run. Total-iron discharges increased slightly in the Stonycreek River from the Oven Run inflow, but dramatically increased in the river because of the Pokeytown Run inflow. Total-iron discharges increased from 29 Ib/d above Oven Run to 1,770 Ib/d below Pokeytown Run.

The U.S. Department of Agriculture, Natural Resources Conservation Service, in cooperation with the Somerset Conservation District, the Somerset County Commissioners, and SCRIP as a supporting sponsor, plans to design and construct passive-treatment systems for the remediation of mine discharges in the Oven Run and Pokeytown Run Basins. A watershed plan includes six specific mine-drainage abatement projects. The design phase for the projects will be from 1994 to 1997, and the construction phase will be from 1995 to 1998. Preliminary plans suggest that SAPS, settling ponds, and chambered passive- treatment-wetlands that use composted mushroom spoil and cattails will be used to treat the mine discharges. The treatment measures are expected to improve the water quality in the Stonycreek River in a 4-mi reach from Oven Run to the Borough of Hooversville. Residents in the borough of Hooversville and surrounding areas will benefit from this project because the Hooversville Water Authority obtains its water supply from the Stonycreek River.

The effects of Oven Run and Pokeytown Run on the water quality of the Stonycreek River are shown in figures 15-19 and figure 21. Shade Creek and Paint Creek had an even greater effect on the water quality in the Stonycreek River (figs. 15-19) and these two streams contribute more acid mine-affected water to the Stonycreek River than any other tributaries in the Stonycreek River Basin. The Shade Creek and Paint Creek Basins have been heavily mined and have many abandoned-mine discharges. Water-resouce managers are considering remediation action in these two basins after the completion of the remediation work in the Oven Run and Pokeytown Run Basins.

46

MAINSTEM"

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QQ-

tr << Q

01 2

0

60

40

20

0

2,000

tr tr< HIx o-

1-500

1,000Q z

If 500

i if- - DOWNSTREAM TREND AT MAINSTEM SITES

| MAINSTEM SITE

TRIBUTARY SITE


Figure 21. The effects of Oven Run and Pokeytown Run on the Stonycreek River on Septembers, 1993.

47

SUMMARY

The Stonycreek River Basin drains an area 468 mi2 in Somerset and Cambria Counties in southwestern Pennsylvania. Fourteen different coal beds throughout the basin are of mineable thickness, however, the Lower and Upper Kittanning and the Upper Freeport coals are the three coal beds that have been most extensively mined. Commercial mining of the coal resources began in the late 1800's with almost no concern for the protection of the land surface or water resources. Consequently, the water quality of the Stonycreek River and its tributaries has been severely degraded for many decades by acidic coal-mine drainage. From October 1991 through November 1994, the USGS, in cooperation with the Somerset Conservation District, conducted an investigation throughout the Stonycreek River Basin to locate and sample abandoned mine discharges, to prioritize the discharges for remediation, and to determine the effects of the mine discharges on the water quality of the Stonycreek River and its major tributaries. The location of the 270 mine discharges that were sampled were determined by use of a GPS receiver with a horizontal accuracy of 3 to 10 ft.

The water quality of the mine discharges varied considerably from discharges that were extremely acidic with high concentrations of iron, manganese, aluminum, and sulfate to discharges whose water quality met USEPA drinking water standards for most constituents. Of the 270 mine discharges sampled, 193 discharges exceeded effluent standards for pH, 122 discharges exceeded effluent standards for total- iron concentration, and 141 discharges exceeded effluent standards for total-manganese concentration. Ninety-four mine discharges exceeded effluent standards for pH and concentrations of total iron and total manganese; 38 mine discharges met effluent standards for all three constituents. Secondary drinking water standards for pH, iron, manganese, aluminum, and fluoride were met at five mine discharges.

Streamflow was an important factor when determining the contaminant discharges of the mine discharges. Mine discharge at site 20 contained a total-iron concentration of 4,760 mg/L, highest of all 270 mine discharges, but a streamflow of only 0.7 gal/min ranked it 26th of all 270 discharges with respect to total-iron discharge. The mine discharges that contained high concentrations of contaminants in addition to large streamflows were the discharges that contributed most of the contaminant discharges to the receiving streams.

A primary goal of the Stonycreek River Basin study was to develop a system that would prioritize all mine discharges for remediation. A PI was developed that ranked the severity of each mine discharge by use of seven specific constituents. The constituents included pH, streamflow, and discharges of total iron, total manganese, total heated acidity, total sulfate, and dissolved aluminum. The PI can be used by water-resource managers as a guide to determine which mine discharges have the greatest effect on stream-water quality and should be considered for remediation. A PI was developed for all mine discharges throughout the Stonycreek River Basin and for mine discharges in six subbasins that were moderately to severely effected by mine drainage. The subbasins were the Shade Creek, Paint Creek, Wells Creek, Quemahoning Creek, Oven Run, and Pokeytown Run Basins.

Water-resource managers propose to remediate the abandoned mine discharges by constructing passive-treatment systems that include aerobic wetlands, compost wetlands, and ALD's. Each of the three passive technologies is most appropriate for a particular type of mine water, but commonly, they are most effectively used in combination with each other. For mine discharges that are extremely acidic (acidity concentration greater than 300 mg/L as CaCO3) with high concentrations of ferric iron (concentrations greater than 1.0 mg/L), the use of a SAPS would be most effective in treating the AMD. A SAPS combines ALD technology with the sulfate reduction mechanism of the compost wetland. A series of SAPS is commonly necessary until the AMD either meets effluent criteria or the limit of the area available for treatment is reached.

48

A network of 37 surface-water sampling sites was established to identify stream water quality during base flow. Water samples collected on July 27 and 28,1993, are used to describe base-flow quality throughout the basin. From mainstem site 801 to mainstem site 805, water-quality degradation occurred that is attributed to the inflows of acidic mine discharges from affected tributaries in addition to inflows of mine discharges directly into the river. Shade Creek, Paint Creek, Oven Run, and Pokeytown Run are tributaries that significantly affect river water quality. From mainstem site 801 to 805, pH decreased from 6.8 to 4.2, alkalinity was completely depleted, and discharges of total iron increased from 30 to 684 Ib/d. Very large discharges of manganese entered the mainstem from Shade Creek and Paint Creek. Manganese oxidation reactions and precipitation are strongly affected by pH and are very slow below pH 8.5. The manganese entering the mainstem from the tributary streams did not precipitate and had an additive affect on mainstem discharges. The attenuation of sulfate concentrations from mainstem sites 803 to 805 is because of dilution, but the significant increase in sulfate discharges from sites 803 to 805 is the result of increased streamflow. A good correlation existed between the measured mainstem sulfate discharges and the calculated mainstem sulfate discharges. The sulfate discharges were calculated by adding the sulfate discharges of the previous upstream mainstem site to the sulfate discharges of all sampled tributary streams entering the river between the two mainstem sites.

Mine discharges 17 and 22 had a major effect on the water quality of Wells Creek. Mine discharge 22 enters Wells Creek about 900 ft downstream from where mine discharge 17 enters Wells Creek. Data collected in Wells Creek above mine discharge 17 inflow and below mine discharge 22 inflow on September 9,1993, show that pH decreased from 7.2 to 3.9, stream alkalinity was completely depleted by the two mine discharge acidities, sulfate discharges increased from 0.76 to 2.0 ton/d, and total-iron discharges increased from 1.3 to 51 Ib/d. The PI for mine discharges 17 and 22 rank them 28th and 7th, respectively, for mine-discharge remediation in the Stonycreek River Basin. Oven Run and Pokeytown Run had a similar effect on the water quality of the Stonycreek River. Both streams are significantly affected by AMD and are the first major sources of AMD flowing into the Stonycreek River. The Pokeytown Run inflow is about 0.5 mi downstream from the Oven Run inflow. Both basins contain many mine discharges, but one major discharge in each basin is responsible for much of the AMD in each stream. Mine discharge at site 3 has a large effect on Oven Run, and mine discharge at site 4 has a similar effect on Pokeytown Run. Mine discharges at sites 3 and 4 ranked 8th and 4th, respectively, on the PI for the Stonycreek River Basin. Data collected in the Stonycreek River above Oven Run and below Pokeytown Run during low-base flow on September 8,1993, show a decrease in pH from 7.6 to 5.1, a decrease in alkalinity from 42 to 2 mg/L, an increase in sulfate discharges from 18 to 41 ton/d, and an increase in total-iron discharges from 29 to 1,770 Ib/d. The U.S. Department of Agriculture, Natural Resources Conservation Service, in cooperation with the Somerset Conservation District, the Somerset County Commissioners, and SCRIP as a supporting sponsor, plans to design and construct passive-treatment systems for the remediation of mine discharges in the Oven Run and Pokeytown Run Basins. The design phase for the projects will occur during 1994-97, and the construction phase will occur during 1995-98.

49

REFERENCES CITED

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Aulenbach, B.T., Hooper, R.P., and Bricker, O.P., 1996, Trends in the chemistry of precipitation and surface water in a national network of small watersheds: Hydrological processes.

Barker, J.L., and Witt III, E.G., 1990, Effects of acidic precipitation on the water quality of streams in the Laurel Hill area, Somerset County, Pennsylvania, 1983-86: U.S. Geological Survey Water-Resources Investigations Report 89-4113, 72 p.

Bencala, K.E., McKnight, D.M., and Zellweger, G.W, 1987, Evaluation of natural tracers in an acidic and metal rich stream: Water Resources Research, v. 23, no. 5, p. 827-836.

Berg, T.M., Barnes, J.H., Sevon, W.D., Skema, V.W, Wilshusen, J.P., and Yannacci, D.S., 1989, Physiographic provinces of Pennsylvania: Pennsylvania Geological Survey, 4th ser., Map 13,1 p.

Berg, T.M., Edmunds, W.E., Geyer, A.R., and others, comps., 1980, Geologic map of Pennsylvania: Pennsylvania Geological Survey, 4th ser., Map 1, scale 1:250,000,3 sheets.

Biesecker, J.E., and George, J.R., 1966, Stream quality in Appalachia as related to coal-mine drainage, 1965: U.S. Geological Survey Circular 526,27 p., 1 pi.

Carson Engineers, 1974, Operation Scarlift, Stony Creek Mine Drainage Pollution Abatement Project, SL-179.

Code of Federal Regulations, 1994, Title 40, Part 434, Section 22.

Driscoll, C.T., Baker, J.P., Bisogni, J.J., Jr., and Schofield, C.L., 1980, Effect of aluminum speciation on fish in dilute acidified water: Nature, v. 284, p. 161-164.

Fishman, M.J., and Friedman, L.C., eds., 1989, Methods for determination of inorganic substances in water and fluvial sediments: U.S. Geological Survey Techniques of Water Resources Investigations, book 5, chap. Al, 545 p.

Hedin, R.S., and Narin, R.W., 1992, Designing and sizing passive mine drainage treatment systems, in Proceedings, Thirteenth annual West Virginia surface mine drainage task force symposium: Morgantown, W Va., 11 p.

___1993, Contaminant removal capabilities of wetlands constructed to treat coal mine drainage, in G.A. Moshiri, ed., Constructed wetlands for water quality improvement: Boca Raton, Fla., Lewis Publishers, p. 187-195.

Hedin, R.S., Narin, R.W., and Kleinmann, R.L.P., 1994, Passive treatment of coal mine drainage: U.S. Bureau of Mines Information Circular 9389,35 p.

Herb, W.J., Shaw, L.C., and Brown, D.E., 1981, Hydrology of area 3, eastern coal province, Pennsylvania: U.S. Geological Survey Water-Resources Investigations Report 81-537,88 p.

Kepler, D.A., and McCleary, B.C., 1994, Successive alkalinity-producing systems (SAPS) for the treatment of acid mine drainage: International Land Reclamation and Mine Drainage Conference and Third International Conference on the Abatement of Acidic Drainage [Proceedings], v. 1, Mine Drainage, p. 195-204.

50

REFERENCES CITECUcontinued

Kleinmann, R.L.R, 1989, Acid Mine Drainage: Engineering Mining Journal, v. 190, p. 16I-16N.

Kleinmann, R.L.P., Jones, J.R., and Erickson, RM., 1988, An assessment of the coal mine drainage problem: 10th Annual Conference of the Association of Abandoned Mine Land Programs, Pennsylvania Bureau of Abandoned Mine Lands Reclamation {Proceedings}, p. 1-9.

Mills, A.L., 1985, Soil Reclamation Processes, in Klein, D., Tate, R.L., eds.: New York, Marcel Dekker, Inc., p. 35-81.

Nairn, R.W., Hedin, R.S., and Watzlaf, G.R., 1991, A preliminary review of the use of anoxic limestone drains in the passive treatment of acid mine drainage, in 12th Annual West Virginia Surface Mine Drainage Task Force Symposium: West Virginia University [Proceedings], 15 p.

Office of Surface Mining Reclamation and Enforcement, 1993, Surface mining control and reclamation act of 1977: Public law 95-87,239 p.

Pennsylvania Coal Association, Pennsylvania Coal Data 1994, table 16.

Pennsylvania Department of Environmental Resources, 1994a, Methods manual: [Harrisburg, Pa.], Bureau of Laboratories, v. 1, [n.p.].

___1994b, Commonwealth of Pennsylvania 1994 water quality assessment: Harrisburg, Pa., 186 p.

Rantz, S.E., and others, 1982, Measurement and computation of streamflow, vol. 1 and 2: U.S. Geological Survey Water-Supply Paper 2175,631 p.

Toler, L.G., 1982, Some chemical characteristics of mine drainage in Illinois: U.S. Geological Survey Water-Supply Paper 1078,47 p.

U.S. Army Corps of Engineers, 1993, Johnstown, Pennsylvania local flood protection project,reconnaissance report on water and sediment quality and aquatic life resources pertinent to rehabilitation of the flood reduction channel: Pittsburgh District, 67 p.

___1994, Conemaugh River Basin Pennsylvania, Reconnaissance Study: Pittsburgh District, 67 p.

U.S. Department of the Interior, 1967, Stream pollution by coal mine drainage in Appalachia: Federal Water Pollution Control Administration, prepared in 1967 and revised in 1969, 261 p.

___1968, Stream pollution by coal mine drainage upper Ohio River Basin: Federal Water Pollution Control Administration, p. 110.

U.S. Environmental Protection Agency 1971, Water supply and water quality control study, Conemaugh River Basin, Pennsylvania: Wheeling Field Office.

___1972, Cooperative mine drainage survey, Kiskiminetas River Basin: Wheeling Field Office, p. 251-313.

___1994, Drinking water regulations and health advisories: Washington, D.C., Office of Water, 11 p.

U.S. Geological Survey 1976-81, Water resources data for Pennsylvania, v. 3, Ohio River and St. Lawrence River Basins: U.S. Geological Survey Water-Data Reports PA 76-3 to PA 81-3 (published annually).

51

REFERENCES CITED^Continued

Ward, J.R., and Harr, C.A., eds., 1990, Methods for collection and processing of surface-water and bed- material samples for physical and chemical analyses: U.S. Geological Survey Open-File Report 90-140,71 p.

Witt III, B.C., 1991, Water-resources data for North Fork Bens Creek, Somerset County, Pennsylvania, August 1983 through September 1988: U.S. Geological Survey Open-File Report 89-584,61 p.

52

APPENDIXES

53

Appendix 1. Geographic information system (GIS) datasets

Hydrography - Two sets of stream data were compiled for the study at 1:24,000 and l:100,000-scales. Both have line and polygon topology. A stream layer was extracted from the Pennsylvania Department of Transportation (PennDOT) county line files using attributes for water features. This dataset was originally in the Intergraph format. The second dataset is from the Digital Line Graph (DLG) series l:100,000-scale data from National Mapping Division (NMD). Specific infomation for the creation, accuracy, topological consistency, and attributes of these datasets can be found by contacting PennDOT and NMD.

Roads - This line dataset was extracted from the PennDOT county line files using attributes fortransportation features. Specific information for the creation, accuracy, topological consistency, and attributes of this dataset can be found by contacting PennDOT.

Municipal boundaries - This dataset was created by digitizing county and township lines from paper7.5-minute topographic quadrangles. Root Mean Square (RMS) errors were below 0.006 inches. Both line and polygon topology are present. The only attribute added to the line attribute table is CLASS and is defined as a character type with input and output size of one. CLASS is a code for distinguishing township lines from lines which are both township and county lines. Valid codes for this attribute are C and T which represent county and township, respectively. Attributes added to the polygon attribute table include: FIPPST, FIPPSCO, and CENSMCD. These attributes are defined as integer type with an input and output of two, three, and three, respectively. FIPPST is the state code, FIPPSCO is the couny code, and CENSMCD is the Census MCD code obtained from the Geographic Identification Code Scheme.

Drainage basin boundaries - In 1989, the Pennsylvania Department of Environmental Resources (PaDER), in cooperation with the USGS, published the Pennsylvania Gazetteer of Streams. This publication contains information related to named streams in Pennsylvania. Drainage basin boundaries are delineated on 7.5-minute series topographic paper quadrangles in Pennsylvania, a total of 878 quadrangles. These boundaries enclose catchment areas for named streams that flow through named hollows, using the hollow name, e.g., "Smith Hollow." This was done in an effort to name as many of the 64,000 streams as possible. RMS errors were below .006 inches and both line and polygon topology are present. Two attributes were added to the polygon attribute table; WRDS# and HUC. The WRDS# is the water resources data system number for streams from the PaDER water use database. This attribute is defined as an integer type with an input and output size of six. Valid codes are 45084-45804, which define the Stonycreek watershed. The HUC attribute is the USGS hydrologic unit code (HUC) number and is an integer type having an input and output size of eight. The valid HUC code is 05010007. Further information about this dataset can be found by contacting the USGS in Lemoyne, Pennsylvania.

Geology - The 1980 Geologic Map of Pennsylvania, by T.M. Berg and others (1980), is the source map for this dataset. This map shows surface geology, fomational contacts, faults, and several glacial advances, and is printed at a scale of 1:250,000 in the Transverse Mercator projection. A stable-base separate of geologic formation boundaries was scanned using a drum-type scanner. Only geologic contact lines and faults between different geologic formations are delineated on this dataset with some fault lines extending into areas of identical formations. The attribute FM was added to the polygon attribute table and is defined as a character item having an input and output value of two. This attribute is a two-letter abbreviation defined by the USGS Bulletin 1200, Lexicon of Geology Names of the United States for 1936-1960. Some positional errors exist in the dataset, therefore, the positional accuracy is 508 meters, or a scale of 1:1,000,000. The Geologic Map of Pennsylvania was never made to be a digital product and although this dataset has been used by the USGS, no warranty, expressed or implied, is made by the USGS as to the accuracy and functioning of the dataset nor shall the fact of distribution constitute any such warranty, and no responsibility is assumed by the USGS in connection herewith.

54

Land use/land cover - This dataset is a product of NMD and is called the Geographic InformationRetrieval and Analysis System (GIRAS). This dataset has been attributed with the Anderson Level-II land use/land cover classifications for 1973-1977 and has line and polygon topology. Specific information for the creation, accuracy, topological consistency, and attributes of this dataset can be found by contacting NMD.

State game lands - This dataset was created by digitizing state game land lines from paper 7.5-minute topographic quadrangles. Root Mean Square (RMS) errors were below .006 inches. Both line and polygon topology are present. Attributes were not added to the dataset.

Special protection waters - Using the existing 1:24,000 and l:100,000-scale hydrography layers, linearfeatures were manually split and attributes were added to the line attribute tables. The only attribute added, QUAL, a character type with an input and output value of two, defines the stream reaches with a special protection code. Valid entries are HQ, for High Quality, and EV, for Exceptional Value. Since the linear topology has been altered, this dataset is a separate layer from the hydrography datasets. Only line topology is present.

Wetlands - This dataset was created by digitizing 7.5-minute quadrangles delineated with areasdesignated by the U.S. Fish and Wildlife Service (USFWS) for wetlands and combining existing 7.5-minute quadrangle datasets already digitized by USFWS into a single layer. Only eight quads were digitized by USGS: Bakerstown, Boswell, Johnstown, Ogletown, Rachelwood, Somerset, Stoystown, and Windber. RMS errors were below .006 inches. Both line and polygon topology are present. Attributes were not added to the line attribute table. Attributes added to the polygon attribute table are MAJOR1 and MINOR1, defined as integers with inputs and outputs of six for each. Valid codes and definitions are numerous and range in order, but can be obtained from the USFWS.

Mine discharges - This dataset contains information on all mine discharges sampled from April 1992through November 1994 throughout the Stonycreek River Basin. Only point topology is present in the dataset. The point location was determined in the field using a Global Positioning System (GPS) receiver with differential correction from base station data. Attributes added to the dataset include: PRI_SCORE, PRI_RANK, and PRIJNDEX. These numeric values were determined by a program designed to prioritize the mine discharge sites for remediation based on comparative water quality data.

Surface-water-quality data - This dataset contains information on surface-water sites sampled on the mainstem of the Stonycreek River and major tributaries. Only point topology is present. The locations of the sites were determined from paper 7.5-minute topographic quadrangles. Attributes include all water quality data collected during the investigation.

Ground water site inventory (GWSI) data - The GWSI data for the Stonycreek River drainage system was retrieved from the GWSI database and imported to ARC/INFO. The dataset contains point information only, neither line nor polygon topology are present.

Pennsylvania water well inventory (PWWI) data - The PWWI data for the Stonycreek River drainage system was retrieved from the PWWI database and imported to ARC/INFO. The dataset contains point information only, neither line nor polygon topology are present.

DEM - DEM data for the project area were obtained from the NMD and clipped to the basin boundary. Specific information regarding the DEM data can be obtained by contacting NMD.

55

Appendix 2. Location coordinates and station numbers for sampled mine discharges in the Stonycreek River Basin

Site number

usestopographic quadrangle

Latitude LongitudeStation number

21

I m&

6789

10

12m,m

1617

181920V

23

2627282930

HooversvilleHooversvilleHooversvilleSomersetSomerset

Central City Stoystown Stoystown Central City Central City

Stoystowrt

Stoystown Central City Windber Windber Windber

II Witdbefm

3637383940Ir

m

45

430M8J 40064807^*1201

4GG9ome400849.0

400930.2

400927.4400105.3

400121.8

785318.6

785439.4785441.3790046.4790039.5

40Q9QQ828S42603 400849078531901 400930078543901 400927078544101 400105079004601 400122079004001

4QOTO7 78S95&0 400104078505601

mm® mmm400626.4400159.1400222.7400648.1400522.7

784816.3785947.7785928.5784847.3784756.4

400626078481601400159078594801400222078592801400648078484701400523078475601

48Q2Q&3

46(112567814^101

400357.0400308.8401242.9401301.9401218.9

785337.1784744.2784924.5784945.0784924.4

400357078533701400309078474401401243078492401401302078494501401219078492401

Stoystown Central City Central City Windber Windber

JPPpi 400653.1400714.3400407.1400737.0400920.1

785530.0785034.8784814.6785125.3784914.4

400653078553001400714078503501400407078481501400737078512501400920078491401

':4iiiiiiii|pii

56

Appendix 2. Location coordinates and station numbers for sampled mine discharges in the Stonycreek River Basin Continued

Site number

USGS topographic quadrangle

Latitude LongitudeStation number

4647484950

5657585960w

lip-7677787980

m

8687888990

OgletownHooversvilleHooversvilleHooversvilleHooversville

BosweU BbsvveH

BerlinBerlinNew BaltimoreStoystownStoystown

6667686970

StoystownStoystownStoystownStoystownStoystown

Central CityWindberWindberGeistownWindber

WindberStoystownHooversvilleHooversvilleHooversville

401417.9400906.2400903.2400823.5400819.0

395751.7395745.3395817.3400528.5400532.0

400029,0maim

400122.7400553.4400540.2400500.2400451.9

400405,7401428.8400706.1401238.2401423.1401507.3401502.5

400236*1

400752.0400707.8400914.2400916.8400918.0

784408.0 401418078440801785945.5 400906078594601785926.8 400903078592701785612.7 400824078561301785539.9 400819078554001

785236.0 785242.9 785217.2 785450.4 785449.4 785124$:

395752078523801395745078524301395817078521701400528078545001400532078544901

785502.5785634.2785554.2785555.2785557.6

400123078550201400553078563401400540078555401400500078555501400452078555801

785038.1784844.0785114.8785000.9785154.2

400706078503801401238078484401401423078511501401507078500101401503078515401

78S2M 78582^2

784900.0785402.7785525.6785529.1785539.0

4007M07S512401 400752078490001 400708078540301 400914078552601 400917078552901 400918078553901

57


Site number


Latitude Longitude Station number

'

96979899

100Ey0£!

m

106107108109110

\ i"i:::::: I IcJ

116117118119120

126127128129130

HiDoversville Hiooyersville

Windber Hooversville Central City Central City Windber

Pitdber

Central CityJohnstownJohnstownJohnstownGeistown

Windber

WindberBeaverdaleBeaverdaleHooversvilleHooversville

WM&erWindberWindberStoystownStoystownJohnstown

ISli^P I 4QOM9L3: WSW&j? me@88& ?8PPJ7

28S52&?

401408.2401335.8400248.1400245.8401417.6

785022.9785422.3785005.5785007.9784849.8

401408078502301 401336078542201 400248078500501 400246078500801 401418078485001 401415078485001 4014fl067«4736&l

400323.0 785202.8401847.6401846.2401844.0401848.2

785344.3

785348.2785257.4

785224.5

400323078520301401848078534401401846078534801401844078525701401848078522401

mmmrn^Mi40*463 J401401,9 784o43jO401409.2 784648;! 401409078464801

401414.7401516.5401517.6400857.4400859.7

784641.5784414.6784413.6785403.2785414.178S»4

401415078464101 401516078441501 401518078441401 400857078540301 400900078541401 40U85507S534001

401451.4401500.0400521.0400519.6401527.7

784612.5784552.0785613.2785614.1785248.5

401451078461201401500078455201400521078561301400520078561401401528078524801

785622,4

^85759,5

58


Site number



136137138139140Ml"

HooversvilleHooversvilleGeistownGeistownGeistownciitetoMn,

1341IM:

146147148149150

Stoystown Johnstown Johnstown Johnstown Johnstown

iPif.156157158159160

SioyStownStoystownStoystownStoystownStoystownStoystown

P, M

y3.W*t~&:W ::¥**¥Jifc¥:::;

166 Hooversville167168169170

mm

176177178179180

400828.0400841.9401502.3401503.1401504.7

BerlinNew Baltimore New Baltimore Berlin

Soswell

BoswellHooversvilleHooversvilleHooversvilleHooversville

«2$l 400552.5 401947.7 401932.7 401941.9 401840.9

400541.4 400548.3 400530.2 400510.6 400603.3 M62&4 fQ0617J

401328.4395752.4395821.3395920.4395950.8

4018M 400840.2 401319.1 401321.4 401330.9 401320.0

785536.7785449.5784540.6784539.9784538.1

1PM1F

400828078553701400842078545001401502078454101401503078454001401505078453801

4S3 5808784522*]!

785632.3785533.0785534.2785534.1785459.2

400552078563201401948078553301401933078553401401942078553401401841078545901

785556.6785555.2785450.6785447.5785613.4

400541078555701400548078555501400530078545101400511078544801400603078561301

490626^8553801

785914.3785236.2785218.4785139.8785241.3

401328078591401395752078523601395821078521801395920078514001395951078524101mmimmm

790246.2785926.9785924.1785915.7785959.0

400840079024601401319078592601401321078592401401331078591601401320078595901

59


uses _ .Slte topographic Latitude Longitude Stat!°n

quadrangle number

itPtlf182 Ligonierm.

186 Johnstown 401839.3 785459.2 401839078545901187 Windber 401500.0 784637.7 401500078463801188 Windber 401441.6 784617.7 401442078461801189 Johnstown 401807.1 785426.9 401807078542701190 Johnstown 401729.0 785454.1 401729078545401

IIBI! fyte&xmrft IQlFPi- ?!$43&i

196 Johnstown 401709.0 785433.8 401709078543401197 Johnstown 401704.9 785434.5 401705078543401198 Johnstown 401810.5 785519.8 401810078552001199 Johnstown 401741.9 785510.3 401742078551001200 Windber 400817.2 784957.7 400817078495801

CenttdtCMrKjveap t|9p#?p!<

206 Hooversville 401229.2 785451.0 401229078545101207 Hooversville 401228.5 785454.8 401229078545501208 Hooversville 400524.7 790451.4 400525079045101209 Somerset 400644.4 790427.3 400644079042701210 Stoystown 400231.1 785911.6 400231078591201

fas? d£| in $|pit$i3$T|||i I 78523M smg&iraw-i

4600m6

216 Windber 406942.7 784931.9 400943078493201217 Windber 401332.4 784939.6 401332078494001218 Windber 401406.0 785019.0 401406078501901219 Ogletown 401331.6 784428.9 401332078442901220 Windber 401249.4 784757.0 401249078475701

iS*S*7Tf> WinrfJSoT &C¥l 1 fifl ^> :::::::::-.-Jilili VVUltiUtfT ^iUllWUi^:

|l|g| Somerset 4GQCM«^ ?9somi mm$®Mmm$HIB i!6p&&**i 4l!6011il tSiSmiS 40QOHS785526D3

60


Site number



226227228229230

m246247248249250

256257258259260wlies-im

266267268269270

StoystownStoystownHooversvilleWindberWindber

23*?33&2362372382392405HF"

lM

WindberSVMdberteste-WindberWindberWindberWindberWindber

:::> Jt4iBd**ieiip?

Huovetsw

WindberWindberJohnstownHooversvilleHooversville

SomersetSomersetSomersetHooversvilleHooversville

sirair&y Central City Windber Geistown Hooversville Hooversville

400559.5 785539.3400642.2 785444.7400901.0 785416.3401058.1 785204.6401054.9 785208.9

401206.6401213.0401906.8400944.1400941.2

S810S42

4810M

400651.0400707.5400706.2400838.7401122.7

400715.0400742.4

401507.1401238.1401231.2

400600078553901400642078544501400901078541601401058078520501401055078520901

401245.2 785140.1401246.5 785139.8401248.7 785135.9401243.9 785147.9401237.5 785147.1

401245078514001401246078514001401249078513601401244078514801401237078514701

W97&3 mmmmmm

785224.7785219.0785450.5785450.1785446.7

401207078522501401213078521901401907078545001400944078545001400941078544701

wwm78S424J 7854233 78S43&6 790413.0 790410.4 790318.4 785908.1 785446.3

wimmmmm400651079041301400708079041001400706079031801400839078590801401123078544601

784828.3785026.5785038.4785424.2785519.8

400715078482801400742078502601401507078503801401238078542401401231078552001

61

Appendix 3. Field data and laboratory analyses of mine discharges

[ft3/s, cubic foot per second; gal/min, gallon per minute; °C, degrees Celsius; nS/cm, microsiemen per centimeter at 25 degrees Celsius; mg/L, milligram per liter; <, less than; --, no data available]

Site number

Localidentifier

(Topographicquadrangle)

Date Time

Discharge, instan

taneous (ft3/*)

Flow rate, Temper- Specific pH, water

instan taneous (gal/min)

ature, water <°Q

conduc-field

Alkalinity, Residue at Carbon, water 105 °C, inorganic,

(mg/L as dissolved total CaCO3) (mg/L) (mg/L

asC)

Illf^lPi^pWll

II 2

m^m^m^ mm u

4 Hooversville

5 HooversvilleSSHij?;': ?S" '6

im m mm II:

S2: 40Wm Central r%:

1.1&*

08-18-93 171005-03-94 1040

17 Stoystown 06-25-92 084009-09-93 092008-31-93 0840

f^^^^^f^^^^^!^^^ 1Q&3&M

3.48.3

.63

.33

.34

ilU£250;1,5103,750

284

146151

W®

11.010.59.5

10.59.5

16-06-92 is,ms

1,780 3.11,760 2.9

728 3.3

780 3.4

774 3.3

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M.

m900

0

0

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0

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4614m if

2, 180

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04-21-94 1100ille 06-17-92 1330

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62

Appendix 3. Field data and laboratory analyses of mine discharges Continued

[ft3/s, cubic foot per second; gal/min, gallon per minute; °C, degrees Celsius; nS/cm, microsiemen per centimeter at 25 degrees Celsius; mg/L, milligram per liter; <, less than; --, no data available]

Date

Iron, Manganese,Sulfate, Iron, total Iron, ferrous, total Manganese,

dissolved Fluoride, recoverable dissolved dissolved recoverable dissolved(mg/L total (ng/L (ng/L (ng/L (ng/L (ng/L

asSO4) (mg/Las F) asFe as Fe as Fe asMn asMn)

Aluminum, Acidity,total Aluminum, total

recoverable dissolved heated(ng/L (Mg/L (mg/L asas Al) as Al) CaCO3)

Acidity, mineral (methyl orange) (mg/L as CaCO3)

04-21-94 06-17-92 08-18-93

05-09-94

06-17-92

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880

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750 700 5,800 5,000

iliiiiiii^Ds

, 84$ 4:M30320 1,600

8,200

2,600

91,000

1,600

- irpa

M6G1,600 8,200

2,600

900

1,400

I5$p 2,800

43^00013,000 62,000

280 2,000 1,000

25®

:4&$qfc::.

12,000

62,000 170

1,900

800

aea

363, 138 560

0 24 20a

::IM

34 210

0

5

0

il

88

6870

5614

130116116201616

63


Sitenumber

202122

Localidentifier

(Topographicquadrangle)

Central CityStoystownStoystown

D

05-03-9406-29-9206-29-9206-30-9209-09-93

Time

13151300140008451025

ww

|:23;: - - - - - '";!" *

Sfcjvstdwtt

&> MZ^.:m$>& ;01o

Discharge,instan

taneous(ffrs)

9.2.71.10.50.30

.34I'vl

m

Flow rate,instan

taneous(gal/min)

4,130.7

46224135

55312

Temperature,water(°C)

9.529.021.010.012.0

mm$

Specificconductance

(nS/cm) '

63212,9001,1701,410

950

IWi*iS8>:

660

'h 1

fiplrillt?IU

f standardunits

4.82.43.33.02.9

£2;£4

Alkalinity,water

(mg/L asCaCO3)

80000

W08

Residue at105°C,

dissolved(mg/L)

53635,100

1,4801,1001,090

366;588

Carbon,inorganic,

total(mg/LasC)

23<1.0<1.0

2.5<1.0

43.9*3; i&«

26 Stoystown27 Central City28 Windber

29 Windber

07-01-92 113007-01-92 160007-13-92 104509-01-93 150007-13-92 1215

: ; :3T33 Windber34 Stoystown

35 Stoystown

07-14-92 102007-15-92 113008-18-93 153604-21-94 093007-15-92 1225

mmm mm

J44S,18.

39 Windber40 Windber

41 Windber

: 42 Windber

05-03-94 093007-16-92 103507-16-92 123508-30-93 150007-16-92 1405

145S

44 Windber45 Ogletown46 Ogletown

47 Hooversville

51

gss&gsg

.19

.27

.04m mm

.02

.09

.10

.35

.11

m2Q

W.37 .14 .17

.10

* JS

|pgiPJ||i^g|s;;y!;!^|.,:,.3007-17-92 0900

07-17-92 1015 <.0108-18-93 1100 1207-17-92 1100 .0508-13-92 1015 <.01

m m

1.51.0

84120

194,4&7

15.021.010.510.512.0DiM

3,0001,360

838953

1,040U6Q

999

3.13.03.13.04.1mMl

IS8.4

4245

15648

$B&17.511.011.010.015.5

ysii1,4102,2302,5301,390

810

i*3.92.73.43.16.0

1676375

42.2

J

133.04

201.6m

10.5 13.0 17.5 20.5 15.5 MS

J&fi

yep1,380

5601,020

727460

4138

M

2.6 6.23.13.2 3.6

10.5 21.5 11.5 16.0 14.5 PSm.

$&1,240 '3.6 1,950 9.7

934955

1,420960

6.1 3.2 3.2

531 XI450 4J993 3iB

0 0 0 0 0

0 0 fe

do000

30

H

P

0

64000

E)

P

""o"

19830

00

PW

(S

i

3,9001,400

800852950m®

III

1,3502,0402,6501,300

540

1,210462796566374 S6T

1,300824856

1,200

371

3.2

4.9 6.1 2.9

1.68.9

10159.9

19166.6

1.1

if36:

,, '

3315

2.3

21

H?

64


Date

05-03-94

06-29-92

06-29-92

06-30-92

09-09-93

;i;p8J3H93;piila: ;6fe-i30?W:

l||||p

07-01-92

07-01-92

07-13-92

09-01-93

07-13-92

Sulfate,dissolved

(mg/LasSO4)

370

27,000

630

750

880:^iBm360

3400

ii?.2,200

880

430

690

620

Fluoride,total

(mg/L as F)

0.2

4.2

<.2

.4

.4i:

#|;

&&*&£i.i

.4

.3

.3

.2

Iron, totalrecoverable

(ng/LasFe

16,000

4,760,000

6,900

30,000

24,000

Mil!nnr

380!;2 KMKJ$|0g>:

23,000

30,000

1,200

1,700

30

Iron,dissolved

(ng/Las Fe

14,000

4,360,000

7,600

30,000

23,000

111 ̂ SjilGP12%OD0

2W

J;^Bp$Pi>23,000

30,000

1,200

1,700

30

Iron,ferrous,

dissolved(ng/LasFe

220-

-

-

-

66Q

610^

^.~-

-

-

170-

Manganese,total

recoverable(ng/LasMn

2,700

60,000

7,100

7,500

7,400

wm2M:o--/\fvp(:' f-AKKJ

mfaim4i?i):

56,000

12,000

5,800

5,700

1,400

Manganese,dissolved

(ng/LasMn)

2,700

60,000

7,700

7,500

7,200

;8,7QQ

5p!0:

ijj3?Q&

*Hiij4jm

56,000

12,000

5,700

5,700

1,400

Aluminum,total

recoverable(ng/LasAI)

1,400

160,000

1,100

9,600

9,500

ujmmm*I2ip0&*sj|»

<&m55,000

42,000

10,000

12,000

7,100

Aluminum,dissolved

(nQ/LasAI)

910

160,000

1,200

9,500

9,200

11JPB

11,0198

rpQl

B^ljips*\m

55,000

42,000

9,900

12,000

7,100

Acidity,total

heated(mg/L asCaCOg)

52

19,688

62

200

174

23®

S2EJOSH40

JJP

490

420

100

114

52

Acidity,mineral(methylorange)(mg/L asCaCO3)

-

8.170

38

130

94

126

80m :|B$

100

120

32

28

0

&mm

07-17-9207-17-9208-18-9307-17-9208-13-92

m

05-03-94 84007-16-92 21007-16-92 42008-30-93 45007-16-92 200

85$

720860480490770spPS200206«

_ MK:|g|

pop mm

mm

34,000820

4,8003,4003,000

~ 0,500:34,000 25,000 4,400

390 - 6104,800 - 5,4003,200 400 13,0001,200 - 3,200

fiOfi

4,400600

5,40013,0003,200

31,000 <100

14,000 8,600 6,400

31,000 <100

14,000 8,300 4,500mm

140290

57,0007,500

38,000

-13JG

338308

m230

u*$

J48

Ip-wd07-14-9207-15-9208-18-9304-21-9407-15-92

J^MT

9&0860

1,2001^00

900300" iw:-r-

- 3

.3

.8

.9

.5

.2

?>l^330

32,00045,00012,0005,200;«;r'-- ^Jp::-

9W290

32,00044,00011,0004,800 pili-

--

2,8001,100

-*

4JKK?:5,700

14,00016,0006^003,200

42,000:

4.2QP5,700

14,00016,0006,5003,200

4;p0on

SJQ®5,000

21,00028,00010,000

1,600

ip^ii^

4100!5,000

21,00028,00010,000

200:-:.:-:-:.:.:-:-:-:o:-:»-,:|jj;Sjrt- -. . .-. . . . . .

£yS\J(t

M44

310404

--

0- ma

si.0

15020452

084:,

232

384 0

16410262

12G

1120

44289

"22

2fe>000;140<10

41,0007,300

37,000pso

m ; Q$@&?2^005,5004,7004,900

14,000- rtp-:

...9i$DD;s::sTsoo

1,5004,6004,900

14,000WO

;,.:;«K;s^j80l&*5,4004,200<130

22,0009,2003,200

m: :^$jj(j&mm5,400

730<130

22,0008,900ilif

xm$Mjysm:m$........ _.................

056

210 4192 6

II

mm i/200

65


Local Site identifier

number (Topographic quadrangle)

5354555657

isa

isUrntea

63

646566

BoswellBoswellBerlinBerlinBerlin

Mfe^ BalttHtotfiStovstowrv

^y^evwiSfcjystown:;Stoystown

StoystownStoystownStoystown

Date

09-14-9209-14-9205-19-9305-19-9305-19-93

mm$$mmm

pg-2(*.Q3m^m05-25-9304-20-9405-25-9305-26-9305-26-93

Time

14501615102010451115

Ti33ft164S

Q92&1!QM11300940130008300920

Discharge, Flow rate, instan- instan

taneous taneous (frVs) (gal/min)

.01

.25

.10<.10<.01

.DP

t,33J&.62

1.8.04.13.13

4.61114520

1.6

M

fi*

es32

277805

195858

Temper ature, water (°C)

14.511.08.0

10.014.095

MOoisM

14.59.5

18.510.515.0

:» W&|,_

iS;.. ! '

Z?:%Q

1^1;72

73

74

75

76

llP^

f|' $8

Stoystown$&y#f&»$

S^5^0S!^B

Sfoysfow

StoystownStoystownStoystownCentral CityCentral City

,.S&ystdSwnWitidkef

&&&&&OMS .$$

OMJ1 *9-?:

8&&M®06-01-9306-01-9306-02-9307-12-9307-12-93

GfcftlsSStffiMM

IMSm&

3i33&:3i3&16001700083010001030 isp:368ti

,ua

<J33rP£:

J9L

.02<.01

.01

.07

.08S* m?-"*"-"

*l&

*&

&41

3J:|8.61.62.4

3035

srpg;;;fig

i&a

10,02@iS:12.011.09.5

24.012.5

:T'SiK|:::r

^|J:

Specific conduc tance

(nS/cm)

900333

1,080439937

L38Q

sS3D?506977881608345343

IP*

|y2pysiQj

165^'EJ211,9004,200

359830776

";;s3|p|01jd5?0:

pH, water whole field

(standard units)

3.66.75.74.25.5-*S

1*J

&7m3.43.16.45.86.8

Alkalinity, water

(mg/L as CaC03)

07246

042

52

f

% «

00

261138

Residue at 105°C,

dissolved (mg/L)

780212864372

1,140L240

IS21432i742562494284200

Carbon, inorganic,

total (mg/L asC)

<1.010381926

2^111

m ' " "

$&9.34.87.86.48.6

,.&& >|; :^g|p;;5pisss;^2||;s

^

4,0m3.73.56.53.33.4

"""'33|""';;:;:;s

4J<

^9:"0:

£00

3000;';r';.pr "'

si

) u'ili'i1fi ?iNTyT

L2403piE2,3205,430

394628740

:3jP& :

1*$

*«-sLS

;6>3333.9

<1.09.91.3

303;5s;

11

Hi82 83 84 85 86

. S'Smdbiet: ............................Central City Central City Central City Windber Windber

as

9293949596

P*8 08-18-93 1100 08-18-93 1310 08-30-93 1050 08-30-93 1230 08-30-93 1345

Wffi

<m£3

.03

2320: 2.7

.01

.02fe$

12.8.5

2.59.0

11.514.09.0

14.018.0

9342,0802,490505336

6.14.56.14.66.6

300

840

15

1290 irJ3

Hooversville Hooversville Hooversville Hooversville Windber

09-22-93 170009-23-93 091509-23-93 102005-11-94 083005-17-94 1315

mmm

mm

2.2 .12J4- m m

1.7 2.2 2.5

981 52

J9f

im

14.5 1,8209.5 860

16.5 3,67010.0 1,06010.0 1,120

m

sj

5.8 3.6 3.0 4.6 6.3il4:1

6.1

3 0 0 0

26 I

8242,3103,230

462284

XlvIv.vSSTOv:

1,920720

4,630986

1,070

594

152.7

332.43.2

is

13

20

5.6 7.5

66


Date

09-14-92

09-14-92

05-19-93

05-19-93

05-19-93

iiysMpi

Sulfate,dissolved

(mg/Las SO4)

510

97

630

230

630

79®

Fluoride,total

(mg/L as F)

0.3

<.2

<.l

<.2

<.2

&


(PO/LasFe

1,200

7,900

72,000

240

130,000

il$fc

Iron,dissolved

fcg/LasFe

1,200

7,700

72,000

220

120,000

S&IP

Iron,ferrous,

dissolved(^g/LasFe

-

-

-

-

-

~

Manganese,total

recoverablefug/las Mn

680

630

10,000

5,300

20,000

M09

Manganese,dissolved

fag/LasMn)

650

620

10,000

5,300

19,000

fe4QQ

Aluminum,total

recoverable<w/LasAI)

7,800

<140

<130

3,600

<130

®*0

Aluminum,dissolved

fag/las Al)

7,700

<140

<130

3,500

<130

Sifi

Acidity,total

heated(mg/L asCaCO3)

72

0

94

32

204

46


11

0-

-

-

~

Iplpaliiip:05-25-93

04-20-94

05-25-93 05-26-93 05-26-93

08-18-93 08-18-93 08-30-93 08-30-93 08-30-93

21

9260460300140120

m

6,200

in.480

1,5002,100

280140wa

600

J3| 09-22-93 1,100 09-23-93 460 09-23-93 1,700 05-11-94 690 05-17-94 700

U30D

mm

1.4 1,2

^:.

.4

.3

06-01-9306-01-9306-02-9307-12-9307-12-93

1,4004,000150490570

.71.3<.2.2.2

.2

m4,1002,3002,900

170500

80090,00011,0005,500

17,000

m

Plili

57,000620

40,0001,900

610

1,000490

130,,0003,500

610

733300 22,000 ISaJDD 4480;

55,000

4,100 3,000 7,8002,300 1,600 5,6001,400 - 1,700

<10 - 120110 - 260

!40,n(X) hh,000

^9007,8005,6001,600

120250

iiliir1,400

19,00017,000

<100<130<130

19,000 17,000

<100 <130 <130 1800

wornliDJD 1,400

600 520 44,00090,000 260 120,00011,000 0 3,8003,900 - 3,400

17,000 8,000 3,200

44,000120,000

3,7003,4003,100

56,00057,000

2003,4009,800

*te# mm68.00056,00057,000

<1303,4009,800

m

I -JH;UEto

ijm

26,000

41,000490

38,0001,200

52

4,7001,5009,9002,600

500

17004,6001,5009,9002,300

490%2oa

Hf)

<1301,100

240130

<130

2-P

<130 1,100 <130 <130 <130

13W

140176

000

0

440780

8.080

126

M32

2160

2436

lip

44Q

56180

110

m

<10470 150

130,000 96,000 2,300

530

1,2002,400

150,0002,000

460

wm

1,2002,300

150,0002,000

450

4801,100

26,0003,000

230

2401,000

25,0002,900<130

poo; 2286,100£136:

1234

71430

0186204

7

200

44

memm L2

67


Site number

101102103

104si

iflS;

J%IP

109110

111112

P3:

fl!4:

||||:Ifc1117

118119120121122g»' :-^

Local identifier

(Topographic quadrangle)

WindberWindberWindber

Windber

Stoystown:C5erttraJ<^rmmvm

JohnstownGeistown

WindberWindberWINfoerWindber6V$P$befWinclberBeayetdkleBeaverdaleHooversvilleHooversvilleHooversvilleHooversvilleJKiiSi^ei'!^^

Date

05-25-9405-25-9405-25-9411-17-9405-25-94t>l7**J4

lOS^fe&i;86<$&*|

06-14-9406-14-9411-21-9406-20-9406-22-94

3M-94:fle^2^4fyij&mwm+mMr^M4:

06-27-9406-27-9406-27-9406-28-9406-28-94

:'-''"''''':.::®6^N*i

Discharge,Time tinstan-

taneous(ftVs)

100012301310104514001110Uft401305

IQBi 11201300125010501115meIM*

H»*13QPmo11301550164508100840

10930? '""

.26

.03

.97

.07

.4485mjii

m,.40

1.0.88.07.03

Flow rate, instan

taneous (gal/min)

11715

43633

200mM

-Sj

180449396

3012

Temper- Specific ' Alkalinity, Residue at Carbon, ature, conduc- .. . .e water 105°C, inorganic, water tance . ' . (mg/L as dissolved total (°C) (jiS/cm) . . CaCOs) (mg/L) (mg/L

units) asC)

10.513.010.510.011.0ma.1:21

^

15.513.012.512.010.0

1310186

13503,1102,4002p0-

£B&tH

1,2301,2201,420

9921,430

3.24.73.22.73.03J:

Wn7m5.94.53.03.43.5

000000d^4

440000

1,180270

1,2503,7802,270Mm.

2p!W528 542

1,20013101,2601,0001,530

3.51.53.32.43.62JJ?Pbj

12 2.34.6

112.13.1

;02;i M:; £&& 1-jpD &&iuisi

J@;05

<.01.01.02

3.4<.01M

MW

15;£l

.34.07.5

1,510.2

s&ff

Piimw®M&19.015.520.012.018.0J&0 v

y?!QIJ^Q3.41Q2i4^02,380

177810718

5,010ip;rs0iw«

%5a*Mr

:-SJ

2.65.03.26.02.9

§:6&x

«i9QQ030

180

3.^10289S1,490$MQ3,150

140474662

10,880

<^M3$Mm&m1.45.91.09.42.7^ ,,,., :,.

[W

1*42Illl-:

Windber

WindberWindberStoystownStoystownJohnstown

m126127128129130

Ip4-

136 Hooversville137 Hooversville138 Geistown139 Geistown140 Geistown

M

mm

07-06-94 110007-06-94 115007-06-94 162007-06-94 170007-07-94 0840

ww

.06

.06

.04

.56

1026

1.32817

250°m43

17.5 1,43022.5 234012.5 1,52014.5 2,06012.0 1,170JTyj : ' :ggi|

m

2.9 2.63.63.7 3.9

07-14-94 075007-14-94 084007-21-94 101007-21-94 110007-21-94 1130

Geistown

.02

.40

.03

.06

m m

7.5180

1.61327

m

10.0 288 6.69.5 360 5.3

18.0 1,280 2.716.5 2,520 2.616.5 3,090 2.5

m3^20

86 6 0 0 0 P-

i 0

mmIPP137023701,6902,5501,150

234352

13602,6003,270

msM

1.2 8.0 7.5 1.2

5.6 5.5 5.3 4.6 5.6

22,0* He

68


Date

05-25-94

05-25-94

05-25-94

11-17-94

05-25-94

liiiklirOlia|plii#4m^m06-14-94

06-14-94

11-21-94

06-20-94

06-22-94

.^U% $$fM$&

06-27-94

06-27-94

06-27-94

06-28-94

06-28-94

Sulfate, dissolved

(mg/L as SO4)

780

81

1,100

1,900

1,600y*P

248;

336

430

650

780

1,200

600

920

%2D&;S90:

1,900

74

350

400

6,100

Iron, total Fluoride, recoverable

total (ng/L (mg/L as F) as Fe

0.2

<.2

.3

.7

.4J

«£2

ll-si<.2

<.2

<.2

.4

.4

: «

3.

.7

<2

<.2

.3

2.0

1,700

60

1,500

12,000

6,800

fittlilpf*

490*%

39,000

30,000

45,000

530

380

4%

640

S!

j%0po60,000

150

5,700

760

690,000

Iron, dissolved

asFe

1,700

48

1,500

12,000

6,500

Illl^iofi^ £800

MS

4i-39,000

28,000

39,000

510

330

640

mJfojaOQ

54,000

56

5,400

71

650,000

Iron, ferrous,

dissolved(H9/L asFe

170-

250

920

500

PSP

~

~:

-

-

43,000

410

150

Aim

24i$00:32,000

-

840-

230,000

;;:G]^28M. .^^^^W3^^^^^^^^" ' ~8i " 3s

Manganese, total

recoverable

asMn

1,800

440

4,900

20,00014,000

i&(3t$:4,000

m

44

2,100

2,300

3,000

6,500

5,200

S£68;000

33,000

330

2,100

940

37,000

5MHM

Aluminum, Acidity, Manganese, total Aluminum, total

dissolved recoverable dissolved heated (ng/L (n9/L (n9/L (mg/L as

asMn) asAI) asAI) CaCO3)

1,800

420

4,900

20,000

14,000

283300

|P

ft:2,100

2,300

2,700

6,300

5,000

12Tra$W

:§>60Q

MjBOP

33,000

310

1,900

880

36,000

m&m

4,800

330

6,500

28,000

14,000

mmipa

200

170

3,800

4,800

8,700

8,300

MB

w&lm67,000

180

770

2,400

320,000. . . . . . .-.-. . . . . . . .;*j/jrt>v

'tiii fifiri-'O-T^t-JiAJ

4,700

310

6,500

27,000

13,000

23P0®5

JS*rm.

170

3,500

4,200

8,500

8,,000:^0Q

6,400110,000 65,000

<130

770

330

310,000

tfetito

94

12

92

350

194

Wt

0

isP

62

100

102

82

74

m m92

934:

734

32

112

7.6

3,620

*/

Acidity, mineral (methyl orange) (mg/L as CaCOs)

40-

26

122

72

108

12

»

-

-

-

19

12

m148

260--

60--

1,580

T

Mil^:

07-14-94 07-14-94 07-21-94 07-21-94 07-21-94

07-06-94 81007-06-94 1,60007-06-94 1,00007-06-94 1,50007-07-94 640

5RB)

1100

&1 .5

1.6 .4 .5 .2

3,900 3,900 770 24,000110,000 110,000 27,000 32,000

230 220 200 11,000810 880 430 18,000

80 60 60 1,600

24,00032,00011,00018,000

1,500

28,0001,2006,400

8,600

2,500

28,0001,2006,400

8,600

2,500ipa

WM

,.,..M,58

170870

1,6002,000

1,800 50

17,000

59,000

70,000

&0,Q0G

1,30017

17,000 1,70059,000 2,50070,000 3,300

140,000

170310

23,00039,000

48,000

160300

23,00039,000

48,000

<130I,300

II,000 20,000 33,000

<130I,000

II,000 20,000 32,000

imp72$90;MBS

mm*

276486

66

9230

W:

030

214468

684

m.

m

J80

126306388m-55i

336

m

69




144145

146147

148I49:

*||Sff;l|Sil

StoystownCentral City

StoystownJohnstown

JohnstownJohnstown

JoJ>nsKM*nStoystown

Date

08-01-9408-01-94

08-01-9408-10-94

08-10-94

d&$&,$4IIHZli-94;mmmfi?T2.M2

Discharge,T. instan- Time .

taneous(ffrs)

11501415

10500920

1010

JI3&1:QOP124?1L4S

.41

.01

<.01<.01

<.01;&9

m-d&

My|2- y& m

153154155156

rpri;'i§8(;Jss; 1601

161

162

163164

Stoystown

Stoystown

Stoystown

Stoystown

' ;ig5y^tif3wJK^iii^|;

Sfa$YStOWR

StoystownStoystown

Stoystown

Stoystown

StoystownHooversville

07-21-92

07-21-92

07-21-92

07-22-92

08-17-93

W-ZZ&'Sii*MM&0^*22^1W-&v$05-09-94

07-22-9207-23-92

07-23-9207-23-92

1320

143516001130

1135

i&iyist&IS!§*&

mm1635

1620

0945

1025

1130

<.01

.06

.04

.08

.10

m^J3S;

,8*

m

.60

.04

.01

<.01

.22

Flow rate, Temper- Specific instan- ature, conduc-

taneous water tance (gal/min) (°C) (nS/cm)

1854.9

1.1.5

.2

10S84

LeIMass

.3

2820

36

45

mJS

IfIF!!no272

20

5.0

2.097

11.013.0

25.021.0

21.5|gi:j)

11;$

2<p

NPIBp9.5

17.0

14.012.5

14.0

ilvSlil&§tub10.5

15.5

16.0

16.0

11.0

1,5902,600

1,0301350

1,480

&4:80

mm&m'W

W9700

1,640

2,200

2,2002,220

pH, water

field (standard

units)

6.06.26.76.86.3If£7mf&

&&

6.33.53.23.53.8

Alkalinity, Residue at Carbon, water 105°C, inorganic,

(mg/L as dissolved total CaCO3) (mg/L) (mg/L

asC)

100140

3888

70

4B

66412l*$§&:26

0

0

00

1,8503,410

9561,300

1,770

2,840O10p60

MPw676

1,170

2,390

2,210

2,4202P0P-:

4>616y?w1,836ysis13701,3802,1701,9901,680

Sift

fcfrJil

M2.9

3.2

3.1

3.02.8

u

SP0fl0

0

0

0

0

E^tiOu

U?9L460i^TS1,1801,1602,1701,8601,500

9.412

6.74.6

3.0

3.F3i;lli|

**;

3612

1.2

1.1

31

14?P

2<S^y ̂«s

10

<1.0

<1.0

2.7

2.9

lannstoivit

166 Hooversville

167 Berlin

168 New Baltimore Qua

£5

07-24-92 0940

09-01-93 1000

05-09-94 1100 08-03-92 1025 08-03-92 -

ggiQ^ag^ iffQwm&- mm

P Berlin J3^| BipsweiJ:

.03

.01

.17

.03

.01 Mm

.If

134.0775.02.3

12.016.010.512.012.5

2,2702,5201,960665

1,180

2.72.62.53.56.0

0

0

00

38

m31

173 Boswell174 Boswell

175 Boswell

176 Boswell

09-02-93 0830 <.01 <.l 18.6 1,460 2.9 0

08-05-92 111508-05-92 1155

08-05-92 1315

08-05-92 1530

09^02^93 0928Mi-.t&"54 t)$2t!i

1.0.02

.01

.73

M

Mi

470

7.5

5.0330

39!

1$

10.513.0

15.5

11.0

t£0

n&

1,4601450

1,060

890967

3UJO»

6.25.0

3.2

5.9SJ:

&z

10012

034

mm

7m:|,620

mm 2JOO

:-:->i^^^:-:- x-^SFWSL--;*

mtwM

5^80 2,420

2,660

1,710 574

1,070

fern

288

1,070

1,1801,200

708

760

1.6

5.9

4.818If :

16

1,4

8.123135.7

15

m

70


Date

08-01-94

08-01-94

08-01-94

08-10-94

08-10-94

OliMt^Mt

INPH

ltth$ii

Sulfate,dissolved

(mg/Las SO4)

1,0002,000

600610

1,100jygjpjQ;

J3I&ism

Fluoride,total

(mg/L as F)

<0.2

<.2

.4

.3

.5.&£

*J

A


(ng/LasFe

13,000

70

1,600

81,000

100,000

:300fji000>

39&00f«p&:

Iron,Iron, ferrous,

dissolved dissolved(ng/L (ng/Las Fe as Fe

12,0002979

60,00098,000

~t

TMl!B

%Z0D *

Manganese,total

recoverable(ng/LasMn

35,000

280

120

1,600

2,000

mm4,4001p3ii

Manganese,dissolved

(ng/LasMn)

35,000

260

120

1,200

2,000

2il90D:

1P&

t>IP

Aluminum,total

recoverable(no/las Al)

150

170

300

260

390

?9$

(Mw$

Aluminum,dissolved

(ng/LasAI)

<130160140

<130<130

580<m*$&

Acidity,total

heated(mg/L asCaC03)

0000

92540b34

¥

Acidity, mineral(methylorange)(mg/L asCaCO3)

-----±*

r-_.

,

*

09-02-93 08-05-92 08-05-92 08-05-92 08-05-92

07-24-92 1,50009-01-93 2,10005-09-94 1,10008-03-92 28008-03-92 670

910810930

480

450

640

648

07-21-9207-21-9207-21-9207-22-9208-17-93

J^2j2&f21|SM22r92IN

05-09-9407-22-9207-23-9207-23-9207-23-92

330690

1,4001,4001,400mmmm

776

jy$900770

1,4001,200

840

""""<.2

<.21.2

.8

.7

2302,2003,9004,4003,100

<102,2003,9004,4002,800 660

*i

o;5

<l<.2<.2

.8

.3

.8

2CJ0i00&!P0&

l^4,4003,6002,5007,100

26,000

2S00iQ0 ^M

S urn4,400 1,0003,5002,4007,100

25,000

3208,0005,0002,8002,500wm

WMMU#t&

t2»11,00011,00017,00021,0005,100

JZ

150,000140,000120,000

1,70033,000

i®^150,000130,000 130,000120,000 44,000

940

21,000

1,9002,4001,5006,6003,400

950

.3

110,00034,000

180,00037,000

110,000m00s

110,00034,000

180,00037,000

110,000

88,000 11,0004,400

13,00011,0006,100

120,000: 120,000: 7^380

im* m480

3008,0005,0002,8002,500

11,00011,00017,00021,0004,900

1,9002,3001,5006,6002,300lios

11,0004,400

13,00011,0006,100

1,700

4BO

%m2,600

70013,00012,0009,200

<100700

13,00012,0009,200

mm

5,6002,600

12,0007,000

17,000

5,6002,600

12,0007,000

16,000

45,00058,00034,000

7,300<130

45,00058,00034,000

7,200<130

2,000 <100 1,000 5,400 <100

200

050

15010098

015441410

8

12012410482

130140260

820806596

7619

t20

30404264

130

440436332

17

2,000200800

5,300<100<!&<T3G

3&00Q

2840

340120162

186232S21

11000

680 *~

240Itm>

71


Site number

179

180

181

|p2083

tN

Localidentifier


Hooversville

Hooversville

Hooversville

jLlgomer

] :learti£JiVaibr

Date

05-11-94

08-06-92

09-01-93

05-09-94

07-14-93

tW M

®7-%$jjf$

wj&rn.

Time

1050

1115

1100

1145

1535

&%

wm085G

Discharge,instan

taneous (frVs)

.02

.06

.07

.38

.01«m

.01

,30

Flow rate,instan

taneous (gal/min)

7.5

25

30

171

5.0

1,0;

3Mm

Temperature, water (°C)

10.5

11.0

11.0

11.0

8.5

I5.p

imm

Specificconduc tance

(nS/cm)

1,180

2,350

2,590

1,630

1,220

2323BS

1P>

pH, waterwholefield

(standard units)

3.8

2.7

2.4

2.3

3.3

M4$

is

Alkalinity,water

0

0

0

0

0

mf

Residue at105°C,

dissolved (mg/L)

1,020

2,420

2,480

1,350

1,110

PJfeiiS

aS

Carbon,inorganic,

total (mg/L asC)

3.6

3.1

<1.0

3.3

<1.0

l||;ji j?: !m

209210211212

IIPlib

m

186 Johnstown187 Windber

188 Windber

IIP :;! J||i|!bS1K ^;Jl

&*''?£.. j&f^i-iz-- Ji3 m$3$$il$Mii$

08-10^94 133007-15-93 114004-19-94 143007-15-93 124004-19-94 1330

II|fOs^9g

Johnstown Johnstown Johnstown Johnstown Johnstown

s|p TfiftndberJ|pt WiShJiber202 Central City203 Central City204 Hooversville

205 Hooversville

StHnerset

SomersetBerlinBerlinNew Baltimore

Windber tVindb^r

.05

.081.0

.11

.053iJE1,1

2236

4705124

53$5pi

15.511.511.518.016.01i2ii&&

2,3501,7401,9402,2701,770ipo:y^

4.82.42.52.62.83$&i

40000

©

2,5201,6301,3903,0701,620

m

101.6

<1.01.3

<1.01$£

4J6$4 W

wwti&MM

08-03-92 120008-03-92 154008-04-92 111005-09-94 094508-04-92 1445

lose

0820 08-05-92 1130 08-05-92 1535 08-06-92 1000 07-07-93 0945

14201520

.12

.13

.35

.17

M

m81

Yi.14 .22

1.2 .66 M

M,

54

6015875

:/«

m

14.0 2,09015.0 3,10012.0 2,45010.5 62011.5 1,280

j^p «EJ?rip s»zp

. ^ »w_ .

mmm

475649748726

m m

m

10.0 19.5 1,670 10.5 872 16.5 1090 18.5 1,940

HP 1,780 814mm

6.1 3.8 2.7 3.1 6.3

m

5.8 3.5 5.8 6.6 3.3

m

138000

150

H

i

404638840

8:00

2,3504,1002,510382

1,080

mmSI8;

m14

tfM-NS 31\§08-15-94 120008-15-94 124508-15-94 134008-15-94 140008-15-94 1445

m<.01<.01

.03

.01

.03

ifr2.12.0

136.4

12

16.515.015.511.514.512.5

SMQ3,1201,1101,720

765903

m3.36.96.87.16.8

(]0

194132168224

lift).4,2801,0601,740

580704

1*2034303240

m

18167.05.144

m m m

534746744

1,950

24151917

72


Date05-11-9408-06-9209-01-9305-09-9407-14-93

H^'&ilpISN&sii|(|Z_fFjJ9i

Sulfate,dissolved

(mg/Las SO4)

8001,4002,000

960900*P

2li2,300

Fluoride,total

(mg/L as F)

<0.2.5.4.3

<.2<>2

J

&3


(ng/LasFe

95,000180,000120,00080,00028,000

?i,efi|w>

i2o;00t

Iron,dissolved

fog/las Fe

85,000170,000120,00079,00026,000

lllfllPI

&SPBQ

Iron,ferrous,

dissolvedfug/las Fe

80,000-

1,400900900

~.<~.

IIMS

Manganese,total

recoverable(Mg/LasMn

6,0002,0002,4001,100

13,000

lil*4-z%g®£280

Manganese,dissolved

(ng/LasMn)

5,9002,0002,4001,100

12,000

mm&JBQODD

Aluminum,total

recoverablefog/las Al)

70044,00051,00025,0003,300*>P0

&3B02&£08

Aluminum,dissolved

(MQ/LasAI)

70043,00051,00025,0003,200<i3B3»

2%006

Acidity,total

heated(mg/L asCaCO3)

172820780476146

w40

MS


247043827696«

41*4

08-10-94 07-15-93 04-19-94 07-15-93 04-19-94

08-15-94 08-15-94 08-15-94 08-15-94 08-15-94

08-03-92 08-03-92 08-04-92 05-09-94 08-04-92

05-04-94 08-05-92 08-05-92 08-06-92 07-07-93

1,6001,3001,1002,4001,400

&ji-

2,900470960120220

; *!!§'

i&j

M.1,3002,1001,400

320610

550

330300450430

1,300wm

440

.5

.3

.4

.6

.6ill 1'

.6

1.4 .2 .3

mm

j

<.2 .7 .3

J

15,00026,00033,00031,0005,900

8,00025,00033,00031,0005,500

-

980680

7,0001,500

?SJ5;:S;ia^:J?iSKiSS-:1H«|i|Sri: 1 JIA :»S:?:¥S-jB$^.::>:>:>S:;::&:: :.lf4\j\f -1 BU

3,8003,1002,500

42,00023,000

m

3,8003,0002,500

42,00023,000

13,00022,00015,000

100,00065,000

6,10022,00015,000

100,00065,000

80380306820512

2161721686811

IP 6-600mms

190,0001,400

28,00010030

l^OjOE* 190,000 160,000

980 26,000

8J8Q9,500

1302,900

10

9,400100

2,900

1507,000

48,0001,900

52,0004W

1,2064408

:2JDS 2^300 720m r, m

150 - 866,400 - 24,000

48,000 - 3,1001,900 200 270

51,000 - 1,100

4pj

4122,000

3,100270

1,100

MO

p&iy#$3MMJ

12,000<130<130<130<130

psffiwm1100

12,000<130<130<130<130

|4ut"«J

45B:526

0000

mm

314100-- ~

.^^^^mm^^^m^mrn^f^m^ff^^

64017,00055,0004,800

200»

22016,00054,0004,800<100mm

6

3*

016062080

0

II

7256

280

- w$m.3

.3

.2

.6

.4&

6,1008,7008,1001,2002,400

2,1663,7007,500

502,000

£JD&&*&

~---

990O00

226:

1,1001,2004,6001,600

53,0001JMJ8D:2,8tM

1,1001,2004,3001,600

51,000t0,8Q02,006

2,3003,600

200<130

33,0003%@Q8§ni

440200300

<13032,000mms

1^1)

'"""""6"""""

000

252m&IP

0

0

24

IPm

4J08 296:

4JQS 168;

Wl:

73




218219

220221

\$&\*£&;!ltlx8l1226227

228229

p*0

ffcf|32liasHP*

235236237

238I.J3I

WindberOgletown

WindberWindberWi^berSomerset

:fic|)ier;56&vrgtowft

StoystownStoystown

HooversvilleWindber\%dfeerVyiiSdfeefWtndberWindberW&yfeerWindberWindberWindber

Windber'-'-' : :î|a|^^T WKKWX-^HK -

07-08-9307-08-9305-03-9407-08-9307-08-93

*ErM*yI^HP-N«PtP?38&KM®SSHMJ08-17-9308-18-9304-21-9408-19-9308-22-94

f#H22HN09^36^d&iforM

tjuîgÎ*Mfe«4

09-06-9409-12-9409-06-9409-12-9409-12-94

IpSKSgl 5

Time

101011301530130014401523itgP1438mmi M15251200101511151600P$*

HBH&yy*1256

lit14201015142011151215

sHJia '"

Discharge, Flow rate, instan- instan

taneous taneous (frVs) (gal/min)

0.07.04.15.02.13;p06

.67mm

.02

.02

.19<.01

.05&Mi

<ms&Oi;

,01.02.10.02

<.01.03

iiiils

331868

8.660

UZ5

:30*

&D7.57.5

85<.l

24I$M

48titS'

TUl^? -0:

7.945

7.9.2

14iiiilP^lslf

Temper- Specific ature, conduc- water tance (°C) (nS/cm)

10.527.011.010.016.5

3 III16DmuipIP12.519.59.0

10.015.0m&i;Qi§jp21,016.515.09.5

15.010.510.0

r:1ii:iiii::s:;;

1,3503,2701,500

7821,280llir460

im&yt^j*s

1,1802^901,8901,760

628605

l£&^?ffi;«at*1.430;

7001,120

700938

1,060?::2ife"

whole field

5.62.42.63.53.2&&Mi6.4SIS;efel5.53.02.85.56.2 &1

MPZW-

liS3.75.43.73.65.3mwr-^

Alkalinity, Residue at water 105°C,

(mg/L as dissolved CaCO3) (mg/L)

800000

24to

180mP40

00

2420mMm0P0

1500

40r-""M"'

1,1003,5301,310

5141,190

662503

1,490~

M364

2,9901,7601,990

638sm

IMtiism*1,7®Pyj3@.

6721,130

672884

1,080:.>:.x.x.x,.x.:-:.x-x.||||x,.>x.

Carbon, inorganic,

total (mg/L asC)

281.01.01.41.1

tep»

117.9

<1.0<1.025

3.8

%& '"""

m^33$

m1.3

181.36.3

24:':'xHa;x":':':':'w':'!

243244245246247

Hoover«!$Ue HoeversveOte

HooversvilleHooversvilleHooversvilleWindberWindber

I {oosersvilie 1 looversviHe

111,253254255256257

HooversvilleHooversvilleHooversvilleSomersetSomerset

MboversviHe

M MM

tm&m

09-19-94 132009-19-94 140009-19-94 173009-19-94 175009-19-94 1820

m

.02

.01

.30

.01

.15

M7.94.8

123.9

67114

Bi.11.010.016.515.515.5ms-

.ilfe353313834

1,1201,350tJNS:

%£-6.36.36.06.46.6&2

12832363054

mm 413:4 Eflifli

14;J W8&

09-21-94 150009-21-94 160009-21-94 174009-26-94 103009-26-94 1200

<.01 <.01

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m, 11 ipom

268316788

1,1801,500l$il

mm

128.36.9

12

M1.91.0

24.8

1.1£3

{#£>

IS

JS;5i16.516.510.510.014.0i||.iistie

J^Q; ......1,430

820560133671

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353

iM3.73.45.75.86.918k&bM

............. ,..-®L , .........00

642884&

3$

38

.....1^31®:,,1,920

690480102576

!ii89i:748

m

-^lis<1.0<1.030

9.421

m24

?M

74


Date

07-08-93

07-08-93

05-03-94

07-08-93

07-08-93

w&$&?j&ÎMM1|fH<&93^Mms*JJM&$&08-17-93

08-18-93

04-21-94

08-19-93

08-22-94

Sulfate, dissolved

(mg/L as SO4)

670

2,400

910

530

850

260

7M

120

II170

1,600

1,100

1,300

340

Fluoride, total

(mg/L as F)

<0.2

.8

.3

.3

.2

.3-

.<y1*

<.2

1.1

.7

.2

««£

Iron, total recoverable

asFe

690

160,000

69,000

310

2,900

BM:

%,&P

lH&P

16,000

21,000

12,000

220,000

2,200

mmîi:

Iron, dissolved

as Fe

220

140,000

69,000

290

2,700

2J0fr«PJ

pp1 î?yil?:

1,900

21,000

12,000

170,000

Iron, ferrous,

dissolved

asFe

-

10,000-

110

800

*-

:+**

-

1,500

1,300-

Manganese, total

recoverable

asMn

33

31,000

13,000

5,700

2,400

4i

3£JQU:

lilN*6,601,1

5^00

19,000

14,000

8,300

27 - 380

Manganese, dissolved

asMn)

81

30,000

13,000

5,700

2,400

M

'!?$&isefr6,600

2,300

19,000

13,000

8,300

95

Aluminum, total

recoverable

asAI)

310

13,000

5,600

4,600

4,600

w&l*e:

&58Q;

540

110,000

71,000

1,400

270

Aluminum, dissolved

asAI)

150

12,000

5,600

4,600

4,600

3&&<W®mv

<130

110,000

69,000

640

<130

<am

Acidity, total


0

940

328

54

66

¥Pm0

940

536

324

0


-

608

208

13

22

~~~-

**>

-

258

142-

H*:W;SS*!g;;si

3K30&SliD®;1,900

7301,900

150240

3361466048608224

296:

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11-

75


Sitenumber

263

264

265

266

267

DP].$£&

Localidentifier


Stoystown

Stoystown

Central City

Central City

Windber

%&*&*&lipo^ej-svlle

Date

10-03-94

10-03-94

10-11-94

10-11-94

10-11-94

&>-$-&!

fIFW-94;

Time

1630

1710

0930

1010

1110

m&1/45

Discharge,instan

taneous (frVs)

0.01

<.01

<.01

<.01

<.01

mM

Flow rate,instan

taneous (gal/min)

4.8

1.6

1.2

.8

.4

m4.8

Temperature,water

15.5

13.5

9.5

8.0

10.5

1*.?&L-8

Specificconductance

(nS/cm)

1,290

2,570

1,270

2,160

210

1>2SPmm

pH, water

field(standard

units)

6.5

6.4

6.3

6.8

6.6

&3It?

Alkalinity,water

(mg/L as CaC03)

54

340

84

168

90

640

Residue at105°C,

dissolved (mg/L)

1,340

3,090-

1,650

148

PSBi;$M

Carbon,inorganic.

total (mg/L asC)

14

97

9.2

44

26

^111

^yilllmm

76


Date

10-03-94

10-03-94

10-11-94

10-11-94

10-11-94

mmm

mmm

Sulfate,dissolved

(mg/Las SO4)

910

1,400

480

480

4.5

680*»ia

. . 318..

Fluoride,total

(mg/L as F)

<0.2

<.2

.3

.2

<.2

*M£<£'

M


(M9/LasFe

16,000

2,900

72,000

6,500

15,000

m290

................IK*,.

Iron,dissolved

(M9/Las Fe

14,000

2,400

63,000

4,200

12,000

m188;

13

Iron,ferrous,

dissolved(M9/LasFe

-

-

-

-

-

»

100

,,.,.,,,.:*::.,.,

Manganese,total

recoverable(M9/LasMn

1,700

14,000

5,400

310

3,000

680

m::,:::,:;,,,JPs:::::;:::::::::

Manganese,dissolved

(M9/LasMn)

1,500

13,000

5,100

310

3,000

J68Q

500

::::..K<i&Q..«

Aluminum,total

recoverable(ng/LasAI)

<130

<130

480<130

<130

888

12,000

m^m&s^

Aluminum,dissolved

(ng/LasAI)

<130

<130

<130<130

<130

3M

12,000

.^Sllfe;::.:.,

Acidity,total

heated(mg/L asCaC03)

0

0

32

0

0

8rf&

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189

3.4

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5.9

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Appendix 5. Field data and laboratory analyses for surface-water sites

[ft3/s, cubic foot per second; °C, degrees Celsius; uS/cm, microsiemen per centimeter at 25 degrees Celsius; mg/L, milligram per liter; ug/L, micrograms per liter; <, less than; --, no data available]

DateDischarge, Temperature, Specific pH

Time instantaneous water conductance (standard(ftVs) (°C) (j^S/cm) units)

, (mg7Las dissolved (mg/L)

. Carbon ' S"lffafm°tr9ta"ic' /ota'

total (mg/L

asC)

m

C30393QC Wfalls Greek at Mostoller. Pa.. Site i!13 ( LAT 4C C4 11N

September 2,1992 0820 2.6 12.0 665

July 27,1993 1015 3.9 19.5 689

May 24,1994 0840 12 13.0 385.,,...,,.,,,,.....,..,.........,.......... ...........,..............^__

m178 56 45W1

$M& K "x --:^t " ':':';s" X;:":! '1-8^ " :;:2D9 ::;!":';^' :': :';;3:;8

L4 M& 231

.|| :,, ft 3fe,|«:- ^ 03039750 Dark Shade Crook at Heilz. >>a.. Site 826 (LAT 40 08 03N LONG 078 48 53W)

September 2,1992 0815 21 11.0 682 3.8 0July 28,1993 1015 13 15.0 1,130 3.3 0May 23,1994 1050 53 13.0 550 3.8 0

612 1.6

990 1.4

468 2.6

03J39925 Noitfi Fcrk AT 4C 15 58N LONG 073 C1 01VV

September 1,1992 0910 1.3July 27,1993 1350 .86

May 23,1994 1215 6.4

13.0

18.0

11.5

61

64

50

6.7

7.0

6.9

90

78

58

80

<1.0 <1.0

<1.0

03039950 South Fork Sens Creek near Femdale. Pa.. Site 832 /LAT 40 15 Q2N LONG 078 58 2QW1

September 1,1992 1015 7.0 13.5 773 5.6 92 668

July 27,1993 1035 6.6 18.0 840 7.3 100 654

May 23,1994 1430 33 16.0 383 6.9 46 312

19

2310

350

770

330

m

9.0

7.7

9.2

m

rnJix

320

320140

88

Appendix 5. Field data and laboratory analyses for surface-water sites Continued

[ft3/s, cubic foot per second; °C, degrees Celsius; uS/cm, microsiemen per centimeter at 25 degrees Celsius; mg/L, milligram per liter; ug/L, micrograms per liter; <, less than; --, no data available]

_ . Date

,-, . . . . . . .Fluonde, Iron, total Iron,total recoverable dissolved

<molL ML (M9/LasF) asFe) as Fe)

Manganese, a . ..Manganese,

dissolved

Aluminum, .

.. Aluminum,dissolved

. .... Acidity, Acidity,

. ,mineral

sCaC03)

pj ........ 120 SP*

Q303930C Wolls Crook at Mostoller. Pa.. Site 813 (LAT 4<J 04 11N LONG 078 56 45\M

September 2,1992 <.2 320 31 800 780 <130

July 27,1993 <.2 240 90 1,900 1,900 1,400

May 24,1994 <.2 770 150 1,000 950 1,000

aggjgj^j^

<130

1,400

150

C3j3d.W

September 1, 1992

July 28, 1993

May 23, 1994

< 2 ^rS?*1: i^r-y'

i'lv Gfdt;k at iioswel

<.2 3,300

<.2 4,500

<.2 3,100

|0 8$ 50

24 W 3$

ra.. Situ bid I LAT 4J jj 54.N LCNG 379 '1 51 Wi

2,400 720 720

2,700 1,700 1,600

2,100 940 900

400

<130

190

<130

<130

<130

<130

0

14

5.2

&

0

0

0

581

yn,03039750 Dark Shade Creek at Hertz. Pa.. Site 826 (LAT 40 08 03N LONG 078 48 53W)

September 2,1992 .3 18,000 16,000 3,100 3,100 4,900

July 28,1993 .2 24,000 21,000 5,000 4,900 8,800

May 23,1994 .2 8,300 5,500 2,500 2,400 4,400

^^^^^^^^^^^^^^^^SBîl^^S^S^.v . :: :¥:-x?S.:-!*-:w:7:-:-Xx' ' 1--^ T

3&&

'5*300

G3U3j^25 North Fcrk Liai:s Crtsuk at N^r

September 1,1992 <.2 20

July 27,1993 <.2 2,300

May 23,1994 <.2 30

Fcrk. rs... Sits 833 (LAT 40 15 5B.\ LL'NG L'7'd 'J1 LJ1WI

<10 <10 <10 <130 <130

20 460 <50 3,100 <130

<10 32 22 <130 <130

Ig^ls^î^îjtg^

6.0

2.4

5.6

50 ^0

^. ^ ^î;::^:,,:;:;*^^

Q3Q3995C South Fork Bens Cmak naar Farndale^ Pa.. Site 832 (LAT 40 15 Q2N LONG 078 58 2flWl

September 1,1992 <.2 900 <10 230 230 370 <130

July 27,1993 .2 950 490 -

May 23,1994 <.2 1,300 120 200 200 510 <130

89


DateDischarge,

Time instantaneous (frVs)

Temperature, water (°C)

Specific conductance

(nS/cm)

pH (standard

units)

Alkalinity, total

(mg/L as CaCO3)

Residue at105°C, dissolved

(mg/L)

Carbon, inorganic,

total (mg/L asC)

$*!&§s8$®sîlpieS&et i, TWw mm w£ ** isl

2 %m «M s

u

N

Sulfate, total (mg/L

as SO4)

190-

rj4Co'UL: Stjnvcr^-k MJv^-r at Fi-rrvJaL-. Pa.. Situ L'j5 (LAT -',L- 17 'jSM LONG .7b 55 15W1

September 1,1992

July 27,1993

May 23,1994

40301407854Q2Q1 StonvcrBek River at Shanksvilb. Pa.. Site BC1 (LAT 40 00 14N LONG 078 54 02W)

September 1, 1992

July 27, 1993

May 24, 1994

0850

1245

1225

11

11

21

16.0

23.5

18.0

557

740

446

6.8

6.8

6.4

58

100

50

532

596

360

1019

11

190

220

140

mm^mmmmmm^mmmmm^^^m1489 JS,P

I-heads Creek at ShanksvUlu. fa.. Site bl. (LAT 4j Ju 56 N LONGi54 U5W)

September 1,1992

July 27,1993

May 24,1994

1030

1110

1045

14

2.5

23

18.5

22.5

16.5

610

535

412

6.8

6.3

6.6

24

48

15

134

540

538

352

5.1

6.4

3.4

m

280

230

170

4CQ337Q785137Q1 Calendars Run at Buckstown. Pa.. Site 809 (LAT 4C 03 37N LONG 078 51 37W1

September 1,1992 1300 .11 13.0 224 7.1 30 180

July 28,1993 1440 <.01 18.5 250 6.1 20 190

May 23,1994 1715 .87 15.5 160 7.1 10 144

3.6

5.3

2.1

30

19

40

imt

400611C7h555HC1 Stonvcrebk River at Kantnsr. i a.. Site bu2 (LAT 4^ J6 11N LONG J78 55 58Wi

September 2, 1992 1000 35 13.5 650 6.0 42

July 27, 1993 1140 23 23.5 884 7.2 42

May 23, 1994 1620 91 20.0 567 7.6 22

564

678

470

8.3

9.1

4.5

3710 73 ? MB

i'fci

260

420

260

wfifi;.-t\- .-.-:-:-.-.-.-.-.- -.-.-.-.-. .-.-.-.-.-.-.-.-.-. £Jttt:'-- '. f.-.-.-.-.-.-.-.-.-.-.-.--,-.-.-;1S£:-Ji.-.- v.w.-.w.'.v.-.-.v.-.'. tt-.-.-.-.v -. --. - -" î?Si-- " .-.-i-.^'.^.-'jAi;-.-.-.-.-;'.-.-.-.---:-.---.-. '.^(ff>.-. .-- ,

LOiM^gpîpiigHj??::;:;:^;!^

90


Fluoride,

« «£asF)


asFe)

Iron, dissolved

asFe)

Manganese, total

recoverable (H9/L

asMn)


asMn)

Aluminum, total

recoverable (H9/L asAI)

Aluminum, dissolved

(MO/L asAI

Acidity, total

heated

CaCO3)


^^^tiSilS&Siri^^ " "

^pteoPerl, W& <3O

lpiii» <3 £*>.*

5 2 IS "2&

0

03Q4QOQQ Slanvcreek iivcr at F^rncfaL. Pa.. Site fciJS (LAT 4u 17 OtiM LCNG :7S 55 15Wi September 1,1992 <.2 1,200 630 1,300 1,200 990

July 27,1993 <.2 1,000 340 2,600 2,500 4,700 May 23,1994 <.2 1,700 630 1,400 1,400 1,800

640 154,400 341,100 16

a

40UG l4C7b54C2(J1 Stonvcroak reiver at Shanks vite. Pa.. Situ ti(J1 ^LAT 40 QC UN LUNG C78 54 G2W1

September 1,1992 <.2 1,000 83 450 210 820 130 0 0

July 27,1993 <.2 500 40 500 440 330 <100 0

May 24,1994 <.2 390 220 820 780 <130 <130 0

72P 290.

_^»-:^:: IDiCifV TfOlli1 ^'i*-" : 7f?f\f- '*-''£&?'

-hoads Creek at Shanksvife. Pa.. Situ

340:

L20D

tLAT 4i .. 56N LONG 078 54 05Wi

430:

8.6

m

September 1,1992

July 27,1993 May 24,1994

;;4^Q58078Sg23^l1^n:

400337078513701 C

September 1, 1992

July 28, 1993May 23, 1994

ialendars Run at LJuckstDwn. Pa.. Site 809 (LAT 40 03 37N LONG 078 51 37W)

<.2<.2

.2

160

40310

45

10100

170

60820

160<50

730

<130

<100

600

<130<100

180

00

0

0--

Slcnvcreek Ftiver at Kantnbf. i'a,. Sitd h'^2 (LAT 40 CG UN LONG C7h 55 5GW)

September 2, 1992

July 27, 1993

May 23, 1994

<.2

<.2

<.2

160

240

180

61

20

<10

75

170

450

65

100

400

240

240

370

mm 2,K)Q poo ^009

440

I

0

0

0

Ny

150

200

290

91


Date TimeDischarge,

instantaneousTemperature,

water(°C)

Specificconductance

(nS/cm)

pH(standard

units)

Alkalinity,total

(mg/L as CaCO3)

Residueat105°C,dissolved

(mg/L)

Carbon, Sulfate, inorganic, total

total (mg/L (mg/L as SO4) asC)

40Q7Q6Q7a552fiQl Qvon Run at Rowena. Pa.. Site 815 (LAT 40 07 C N LONG 073 55 28W)

September 2, 1992 1100 0.57 13.0 1,930 2.7 0

July 27, 1993 1700 .55 23.5 2,350 2.8 0

May 24, 1994 1020 3.1 12.5 1,320 3.2 0:'frp$^

'"'~ "'" 1610 ^ --- --- -"££--- pp 2$ i

,40 m& 3M& m &

2,130

2,740

1,240

<1.0

<1.0

<1.0

1,100

2,000

820sis

11G0 m - -^~- vM£, , pm ^sfc .... .Sl H ... ..$P& . >y«>;S^*.< 400822079035931 North Branch Quemahonin Creek near Caal Junction. Pa.. SKe 820 (LAT 40 08 22N LONG 079 03 59W1

September 1, 1992

July 27, 1993

May 23, 1994

0830

0845

0840

6.9

1.8

30

15.0

21.0

13.0

124

135

87

6.4

6.3

5.5

13

15

6

148

116

90

' " "M

3J0

WO86

d544aul Fallen Timter Run at H-juvarsvillL-. Pa.. Sito 81G (LAT 40 ud 41N LONG 078 54 49W1

September 1, 1992 July 27, 1993 May 24, 1994^085407849020*:lefHember &, 1992

1815 1500 1200

mm mm

.32

.30 1.2

ii&S&i&i:34

13.5 17.0 12.0

i&ssffifcss&^TssiBS

2501

502 457 310

timmmm4257

5.3 5.05.5

3 2 4

^J^^S078:*S: Q2WOis

w4

498

422

294

3.3

4.7

2.0

2,1

1.6

1.0

2.9

30

35

25

4On9QHQ7p585701 Tw.Tmik Run nuar L^swull. Pa.. Site -22 (LAT 4C j9 Q^N L'JNG :J7J 5d 5"Wl

September 1,1992

July 28,1993

May 23,1994

1600

1315

1410

.52

.48

4.3

401C17C79QQ53C1 Rcarine Hun at PilHcwn. Pa.. Site 821 (LAT 43 1C 17N LONG G79 00 53W)

September 1, 1992 1200 3.5 16.5 282 6.1 24

July 28, 1993 1230 1.0 22.5 872 6.1 46

May 23, 1994 1250 17 19.5 250 6.8 20

64

292

706

206

1.2

m

5.6

12

5.5

270

320

160

10

240

320

230

m

97

430

91

^ycre^^ilpMaQp^^

401C59G734952'J1 iicarin;

September 2,1992 1025

July 28,1993 0730

May 23,1994 1240

122:

Fork near HiUsbcrc. Pa.. Site

1.2.AT 4>: 1 w1 59N LONG 07d 4i> 52Wi

4.8

1.8

13

13.5

19.0

13.5

142

203

80

4.5

3.5

5.0

162

142

74

50

120

28

92


Date

400706078552801

Fluoride,total

(mg/LasF)


(nO/l-as Fe)

Iron,dissolved

asFe)

Manganese, total

recoverable

asMn)

Manflanese,dissolved

fog/las Mn)

Aluminum, A .

recTrable di^

£% -*total

heated

CaCO3)

Acidity, mineral(methyl orange)

CaCO3)

Oven Run at Rowena. Pa.. Site 815 (LAT 40 07 06N LONG 078 55 28W)

September 2,1992 0.8 23,000 23,000 21,000 21,000 26,000

July 27,1993 .5 21,000 19,000 39,000 36,000 46,000

May 24,1994 .5 15,000 15,000 15,000 15,000 19,000

Ipl^ffi^^^JSiiV''23£ I^JiS i: 1 '(BiRJStK'- J^D^di^? Jî£i0jD: I4JMW? M&iJCfif

lîj^ytSM.................. _.v-&;.........s,%ffi$®4Q0822Q79Q359Q1 North Branch Quemahonlna Creek near Coal Junction. Pa!. Site 820 (LAT 4 j

26,000 350 124

42,000 450 136

18,000 190 66

I4&88® USQ 6256

2,180 650

22N LONG 079September 1, 1992

July 27, 1993

May 23, 1994

1,100

1,700

580

40

160

250

380

320

330

370

320

350

210

200

180

S2 m m

im218; 24? 88 m 2p**0; <tp see im. 2&a w&

Fallun Timbtir t^n at HooversvJUe. i ja.. Sito 816 (LAT 40 03 41N LONG C78 5449WJ

September 1, 1992

July 27, 1993

May 24, 1994

.3

.3

<-2

490

100

250

50

90

52

710

570

280

670

570

240

1,300

1,200

740

720

600

260

<130 0

<100 0

<130 4.0

B

0

20

9.6

1.4

0

@featSM:W^^<J 1411 4:£; 53 * 43

1993

Twjr-iiliJ nu'i nu'ar ôswoll. ra.. Site i>22 iLAT 40 09 Q8N LONG C7r 5- 57V/1

September 1, 1992 <.2

July 28, 1993 <.2

May 23, 1994 <.2

120

140

390

50

40

<10

2,900

2,200

2,100

2,800

2,200

2,100

860

760

800

730

700

<130

13

7.6

6.2

grdaj^;Q^^'a.t:âWnfeMS^':>:^-:a'?i!;

3m: 200

4C1317079C0530I Roaring Run at PJUtowr. Pa.. Site 521 (LAT 40 10 17N LONG Q79 CO 53W1

September 1,1992

July 28,1993

May 23,1994

.2

2,600

4,500

2,100

1,500

1,200

890

820

2,200

620

820

2,200

600

180

200

370

<130

<130

<130

tixW^faMs^^tglSfaMmi^^-2 ii!^J9^ 27£) ^; JOX)^ 1100: ÎG 140 7S

4Clu5a::-7a495201 Roarino Fcfk n^ Pa.. Site 828 (b\T4L- 1u 5jN LONG 078 4a 52Wi

September 2,1992

July 28,1993

May 23,1994

500

1,000

240

380

750

170

1,100

1,400

440

1,100

1,400

450

680

700

540

680

700

510

15

16

11

93


Discharge, Date Time instantaneous

^B-jtZI tJ785S23"3^''yPî''^5it^ !?Irl5*S'?e$j?8ti'

Temperature, water

p^S^MI

Specific conductance

PH (standard

units)

Alkalinity, total

(mg/L as CaCO3)

dissolved (mg/L)

Carbon, inorganic,

total (mg/L asC)

total (mg/L

as SO4)

m^mmîmmi^mmm^m^^^^mm^m^'""'^25;D m S$ m 268 3,4: S4

IP |y^ J?P ^1 5® Wfe H 35

m M & m4C124307c;5355Ul SâJ^ Cru-uk at Sua:ijr. Pa.. Situ t^3g iLAT 40 12 -',3N LONG 'J7J 53 55Wi

September 1, 1992 1610 80 18.5 322 4.5 0 282 <1.0 140

July 28, 1993 1700 40 27.5 670 3.5 0 474 <1.0 410

May 24, 1994 1030 137 13.5 300 3.8 0 228 <1.0 130

1704C1441 0785302U1 Paint Crook noar Windbor. Pa.. Sito &3Q (LAT 40 14 41N LONG 078 53 Q2W)

September 2, 1992 1105 14 14.0 1,220 3.6 0 1,210 <1.0 720

July 28, 1993 1420 9.9 24.5 1,380 3.4 0 1,210 <1.0 960

May 24, 1994 1400 43 17.0 800 3.6 0 732 3.0 510

^î

1994 184? 6,8; |J& Wn ^ 24 jy

94


Fluoride,

Date total Uate (mg/LasF)


asFe)

Iron, dissolved

asFe)

Manganese, total

recoverable

asMn)


asMn)

Aluminum, total

recoverable (ng/LasAI)

Aluminum, dissolved

as Al

Acidity, total



4P^tSif£l§£^^ 2ii^i^$S^^iii£<^ ...............

;!$!%< 27v 1993 *i,2 260 ZiSQ ^S0: I2& 4500 g$00 Si

40124307^535501 Sl.adc GroLk at SL-a-ur. Pa.. Situ 83G fLA.T -ID 12 -;3N LONG J73 53 55Wi

September 1, 1992

July 28, 1993

May 24, 1994

<.2

<.2

<.2

1*1994

401441Q7553C2C1 Paint Creek near Windber. Pa.. Site 83Q (LAT 4C14 41N LCNG 078 53 Q2W)

September 2, 1992

July 28, 1993

May 24, 1994

14,000

8,800

7,200

8,100

5,200

3,600

6,700

10,000

5,100

6,700

10,000

4,800

15,000

13,000

9,100

15,000

13,000

8,200

138

104

70

22

9

3

mm& mm *ntm

95

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