&EHV
United States      Industrial Environmental Research  EPA-600/7-79-073f
Environmental Protection  Laboratory          September 1979
Agency        Research Triangle Park NC 27711
Environmental
Assessment of Coal
Cleaning Processes:
Homer City Power
Complex Testing

Interagency
Energy/Environment
R&D Program Report

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                   RESEARCH REPORTING SERIES


  Research reports of the Office of Research and Development, U.S. Environmental
  Protection Agency, have been grouped into nine series. These nine broad cate-
  gories were established to facilitate further development and application of en-
  vironmental technology. Elimination of traditional grouping was consciously
  planned to foster technology transfer and a maximum interface in related fields.
  The nine series are:

     1.  Environmental Health Effects Research

     2.  Environmental Protection Technology

     3.  Ecological Research

     4.  Environmental Monitoring

     5.  Socioeconomic Environmental Studies

     6.  Scientific and Technical Assessment Reports (STAR)

     7.  Interagency  Energy-Environment Research and Development

     8.  "Special" Reports

     9.  Miscellaneous Reports

 This report has been assigned to the INTERAGENCY ENERGY-ENVIRONMENT
 RESEARCH AND DEVELOPMENT series. Reports in this series result from the
 effort  funded  under the 17-agency Federal Energy/Environment Research and
 Development Program. These studies relate to EPA's mission to protect the public
 health and welfare from adverse effects of pollutants associated with energy sys-
 tems. The goal of the Program  is to assure the rapid development of domestic
 energy supplies  in an environmentally-compatible manner by providing the nec-
 essary environmental data and control technology. Investigations include analy-
 ses of the transport of energy-related pollutants and their health and ecological
 effects; assessments of, and development of, control technologies for energy
 systems; and integrated assessments of a wide range of energy-related environ-
 mental  issues.
                        EPA REVIEW NOTICE
This report has been reviewed by the participating Federal Agencies, and approved
for publication. Approval does not signify that the contents necessarily reflect
the views and policies of the Government, nor does mention of trade names or
commercial products constitute endorsement or recommendation  for use.

This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161.

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                                           EPA-600/7-79-073f

                                               September 1979
Environmental  Assessment of  Coal Cleaning
          Processes:  Homer City Power
                   Complex Testing
                               by

        S.E. Rogers, D.A. Tolle, DP. Brown, R. Clark, D. Sharp, J. Stilwell, and B.W. Vignon

                       Battelle Columbus Laboratories
                            505 King Ave.
                         Columbus, Ohio 43201
                         Contract No. 68-02-2163
                            Task No. 813
                       Program Element No. EHE624A
                     EPA Project Officer: James D. Kilgroe

                   Industrial Environmental Research Laboratory
                 Office of Environmental Engineering and Technology
                      Research Triangle Park, NC 27711
                             Prepared for

                   U.S. ENVIRONMENTAL PROTECTION AGENCY
                     Office of Research and Development
                         Washington, DC 20460

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                                FOREWORD
     Many elements and chemical compounds are known to be toxic to man
and other biological species.  Our knowledge concerning the levels and
conditions under which these substances are toxic is extremely limited,
however.  Little is known concerning the emission of these pollutants
from industrial processes and the mechanisms by which they are
transported, transformed, dispersed, or accumulated in our environment.

    Portions of the Federal Clean Air Act, the Resource Conservation
Recovery Act, and the Federal Water Pollution Control Act require the
U.S. Environmental Protection Agency (EPA) to identify and regulate
hazardous or toxic substances which result from man's industrial activ-
ities.  Industrial pollutants are often identified only after harmful
health or ecological effects are noted.  Remedial actions are costly,
the damage to human and other biological populations is often irrevers-
ible, and the persistence of some environmental contaminants may
endanger future populations.

    EPA's Office of Research and Development (ORD) is responsible for
health and ecological research, studies concerning the transportation
and fate of pollutants, and the development of technologies for con-
trolling industrial pollutants.  The Industrial Environmental Research
Laboratory, an ORD organization, is responsible for development of
pollution control technology and conducts a large environmental assess-
ment program.  The primary objectives of this program are:

    •  The development of information on the quantities of toxic
       pollutants emitted from various industrial processes—information
       needed to prioritize health and ecological research efforts.

    •  The identification of industrial pollutant emissions which pose a
       clearly evident health or ecological risk and which should be
       regulated.

    •  The evaluation and development of technologies for controlling
       pollution from these toxic substances.

    The coal cleaning environmental assessment program has as its
specific objectives the evaluation of pollution and pollution control
problems which are unique to coal preparation, storage, and trans-
portation.  The coal preparation industry is a mature yet changing
industry and in recent years significant achievements have been made in
pollution abatement.

    This report deals with one portion of an IERL/RTP program which is
designed to focus on the effectiveness and efficiency of coal cleaning
processes as a means of reducing the total environmental impact of
energy production through coal utilization.  Specifically, the pre-
operational environmental of the advanced physical coal cleaning
facility at Homer City, Pennsylvania, was studied for the purpose of
providing a reference point for future comparisons.

                                   ii

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                                ABSTRACT

    This report describes a preliminary, preoperational environmental
survey conducted at a newly constructed advanced physical coal cleaning
facility located near Homer City, Pennsylvania.  The work comprises a
part of a comprehensive environmental assessment of physical  and
chemical coal cleaning processes performed by Battelle's Columbus
Laboratories for the U.S. Environmental Protection Agency (EPA).
    A series of multimedia grab-sampling campaigns were conducted in the
study area to document the abundance or concentration of selected envi-
ronmental parameters.  The data collected in the campaigns were used to
evaluate the air, water, and biological quality of the study  area both
through interpretive techniques and by direct comparison with EPA
Multimedia Environmental Goals (MEG) values.
    Fugitive dust was monitored using high-volume samplers at locations
verified by a multiple source fugitive dust dispersion model, field-
calibrated to the monitoring results and source conditions at the Homer
City Station.  The model is able to predict dispersion levels at various
distances under a variety of meteorologic conditions.
    The fugitive dust chemical analysis revealed two important phenom-
ena.  First, there are uncombusted coal dusts 2,000 meters downwind of
the coal cleaning plant site that exhibit levels of lead, cadmium,
arsenic, and mercury higher than those present in the whole-coal or
disposed ash.  Cadmium and lead values are several orders of magnitude
higher than those in the whole-coal or disposed ash.  Beryllium and
vanadium were not found in the coal dusts but are quite evident in the
source coals.  Second, magnification of trace metal compounds may be
attributed to the cleavage of the coal along planes where these metal
compounds were concentrated.  The particles released by fracturing along
these planes evidently tend to become airborne due to air or vehicular
movement over the coal pile.
    Water quality in each of the basins monitored is a direct reflection
of the types of land uses involved.  The five major land uses in the
                                   iii

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study area affecting  stream water are:  agriculture, mining, urban,
construction, and power generation.
    The  stream sediments of the  study area are heavily laden with metal
compounds.  These streams exhibit high dissolved oxygen levels and, were
it not for the pH extremes and suspended solid levels, the streams could
begin a  rather rapid  recovery.   As expected in a coal region lithology,
the streams had sufficiently high levels of various forms of iron,
manganese, sulfur, and calcium to be of some concern.
    The  aquatic biota reconnaissance involved the sampling of three
groups of organisms (attached algae, bottom-dwelling invertebrates, and
fish) indicative of the streams' biological quality.  Sampling was con-
ducted at 14 locations in eight  streams.
    The  subjective  analysis of  water quality based on the aquatic biota
observed was in close agreement  with the water chemistry analysis.
     The terrestrial  habitats evaluated within a 2-mile (3.2-km) radius
of the coal cleaning  plant are quite diverse and support animals common
to all successional stages, especially those wildlife species asso-
ciated with the early successional vegetation.  Very little wetland
habitat exists, and the streams  and ponds which do occur in the area are
unsuitable for water birds.  The observation of particulate matter cov-
ering vegetation and  leaf litter within 1 mile (1.6 km) of the coal pile
suggests that plant biota in that area may soon begin to show signs of
stress.
    In summary, the ambient environment in the study area appeared to be
typical of many western Pennsylvania areas which include coal mining and
handling operations.   In many cases, stream water chemistry and biolog-
ical quality were adversely affected by pollution sources outside of the
study area, especially by acid mine drainage.   Power complex operations
had a negative impact on the chemical and biological quality of a few of
the smaller tributaries.   Levels of particulates in the air were high in
the vicinity of the coal  storage pile,  but dropped down to relatively
good air quality levels off of the power station property.   Terrestrial
vegetation is presently diverse  in the study area.  Some of the more
                                    iv

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sensitive plant species close to the coal pile, however, may begin to
show signs of stress due to the accumulation of coal dust and other
particulates.
    Both the terrestrial and aquatic ecosystems in the vicinity of the
Homer City Coal Cleaning Plant reflect varying degrees of environmen-
tal stress.   The general area has been the site of numerous coal-related
activities for decades. Old abandoned strip mines in the vicinity as
well as on-site coal-fired power plants influence the natural envi-
ronment.  Estimated permissible concentration (EPC)  values for several
elements were found to be exceeded in either air or  water media at the
site before the coal cleaning facility began operation.
                                   v

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                             ACKNOWLEDGMENT

    This study was conducted as a Task in Battelle's Columbus
Laboratories' program, "Environmental Assessment of Coal Cleaning
Processes", which is supported by the U.S. EPA IERL/RTP.  The contribu-
tions of the Program Manager, Mr. G. Ray Smithson, Jr., and the Deputy
Program Manager, Mr. Alexis W. Lemmon, Jr., are gratefully acknowledged.
    We also gratefully acknowledge the help of the Pennsylvania Electric
Company and the New York State Electric and Gas Company in permitting
the environmental measurements to be made at their facilities and pro-
viding personnel and equipment to assist us in operating the air
monitoring stations.  Their support of this program is appreciated.
Mr. James H. Tice and Mr. Raymond W. McGraw of Penelec were particularly
helpful in facilitating the field sampling program.
    The following organizations and individuals provided support:
Benedict, Bowman, Craig, and Moos, who performed the soil analysis and
hydrometer tests; Tradet Laboratories, who performed chemical analysis
on water samples, sediment samples, fish samples, and fiber glass filter
pads; Mr. Edward Zawadzki, consultant, General Public Utilities; and
Dr. Gilbert Raines, consultant.
    The advice and counsel of the EPA Project Officer, Mr. James D.
Kilgroe, and others at the IERL/RTP facility were invaluable in
performance  of this work.

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                            TABLE OF CONTENTS

                                                                     Page

 Foreword                                                            ii

 Abstract                                                             iii

 Acknowledgment                                                     vi

 List of Figures                                                      x

 List of Tables                                                       xii

 List of Abbreviations                                                xvii

INTRODUCTION 	   1

     Description of the Study Area	   2

     Data Comparison with MEG Values	   3

     Environmental Components Sampled  	   5

CONCLUSIONS AND RECOMMENDATIONS   	   7

     Environmental Quality Prior  to Cleaning Plant Operation 	   7

     Pollutant Toxicity Considerations  and
     MEG Value Comparisons	10

TERRESTRIAL ENVIRONMENT  	  14

     Fugitive Dust Monitoring  	  14

     Terrestrial Biota Survey  	  . 	  18

     Comparison of Analytical Data with MEG Values—
     Terrestrial Environment 	  26

AQUATIC ENVIRONMENT  	  33

     Water Quality Determinations   	  33

     Land Use Analysis	35


                                    vii

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                            TABLE OF CONTENTS
                               (Continued)

                                                                      Page

     Cherry Run Basin	     43

     Wier's Run	     56

     Common Ravine/Second Ravine 	     66

     Two Lick Creek Basin	     71

     Summary of Water Quality Conditions 	     77

     Comparison of Analytical Data with MEG
     Values—Aquatic Environment 	     78

     Aquatic Biota Survey  	     85

COAL CLEANING REFUSE DISPOSAL SITE 	     98

     Site Description	     98

     Facility Design 	    100

     Potential Operational Problems—Pollution Potential 	    103

     Recommendations for Future Monitoring 	    104

REFERENCES	    106

APPENDIX A.  FUGITIVE DUST MONITORING  	    110

     Location of Monitoring Sites  	    Ill

     Diffusion Model Results 	    112

     Fugitive Dust Sources	    113

     Modeling Activities 	    114

     Survey Data	    123

     References	    160

APPENDIX B.  TERRESTRIAL BIOTA OBSERVATIONS  	    161

APPENDIX C.  WATER QUALITY DETERMINATIONS  	    166
                                   viii

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                            TABLE OF CONTENTS
                                (Continued)

                                                                      Page

     Land Use Analysis	   167

     Physical Descriptions of the Drainage Basins in the
     Vicinity of the Homer City Coal Cleaning Plant	   179

     Water Chemistry	   183

     Water Quality Analyses  	   195

     References	   223

APPENDIX D.  AQUATIC BIOTA RECONNAISSANCE  	   225

     Sampling Site Locations and Descriptions  	   226

     Organisms Selected for Study  	   226

     Sampling and Analysis Procedures  	   229

     Detailed Data	   230

     References	   253

GLOSSARY	   254
                                    IX

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                              LIST OF FIGURES

                                                                       Page

 1.  MAP OF THE HOMER CITY POWER COMPLEX	   4

 2.  LOCATION OF FUGITIVE DUST SOURCES AND MONITORING SITES 	  15

 3.  VEGETATION TYPES IN THE VICINITY OF THE
     HOMER CITY COAL CLEANING PLANT	20

 4.  FUGITIVE DUST CONCENTRATIONS COMPARED TO A TRANSECT
     OF THE AREA'S TOPOGRAPHICAL RELIEF	27

 5.  STREAMS AND TRIBUTARIES SURVEYED IN THE HOMER CITY AREA	34

 6.  SURFACE WATER QUALITY SAMPLING LOCATIONS 	  36

 7.  STREAM SEDIMENT SAMPLING LOCATIONS 	  37

 8.  CHERRY RUN SAMPLING LOCATIONS—CAMPAIGN I	44

 9.  CHERRY RUN SAMPLING LOCATIONS—CAMPAIGNS II AND III	45

10.  HISTOGRAMS OF SOME IMPORTANT SOLUBILITY CONTROLLING
     INDICATOR SPECIES IN CHERRY RUN BASIN  	  46

11.  BUFFER CAPACITY—CHERRY RUN	49

12.  PHENOL, COD, AND TOC CONCENTRATIONS AT VARIOUS
     LOCATIONS IN THE CHERRY RUN WATERSHED	52

13.  CONCENTRATIONS OF PLANT NUTRIENTS AT VARIOUS
     LOCATIONS IN CHERRY RUN WATERSHED  .	54

14.  SOLIDS FRACTIONS AT VARIOUS LOCATIONS
     IN THE CHERRY RUN WATERSHED	55

15.  WIER'S RUN SAMPLING LOCATIONS—CAMPAIGN I	57

16.  WIER'S RUN SAMPLING LOCATIONS—CAMPAIGNS II AND III	58

17.  CONCENTRATIONS OF IMPORTANT SOLUBILITY-CONTROLLING
     SPECIES IN WIER'S RUN	60

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                              LIST OF FIGURES
                                 (Continued)

                                                                       Page

18.  BUFFER CAPACITY—WIER'S RUN	62

19.  NUTRIENT CONCENTRATIONS IN WIER'S RUN BASIN  	  64

20.  COMMON RAVINE/SECOND RAVINE SAMPLING LOCATIONS—CAMPAIGN I ....  67

21.  COMMON RAVINE/SECOND RAVINE SAMPLING LOCATIONS-
     CAMPAIGNS II AND III	68

22.  TWO LICK CREEK SAMPLING LOCATIONS—CAMPAIGN I	72

23.  TWO LICK CREEK SAMPLING LOCATIONS—CAMP AIGNS II AND III	73

24.  CONCENTRATIONS OF SOME IMPORTANT SOLUBILITY CONTROLLING
     SPECIES IN TWO LICK CREEK	75

25.  AQUATIC BIOTA SAMPLING LOCATIONS 	  86

26.  COAL CLEANING REFUSE DISPOSAL AREA	99

27.  DISPOSAL STAGES AND POND LOCATIONS	101

28.  RESULTS OF LINEAR REGRESSION ANALYSIS
     (PREDICTED VERSUS OBSERVED)  	 118

29.  CONCENTRATION OF FERROUS IRON AS A FUNCTION
     OF pH IN A CARBON ATE-FREE SYSTEM	186

30.  SOLUBILITY OF FERROUS IRON AS A FUNCTION OF pH IN A
     SYSTEM CONTAINING DISSOLVED CARBONATE SPECIES  	 187

31.  STABILITY RELATIONSHIPS IN THE SYSTEM—Fe-02-C02 	 188

32.  CONCENTRATION OF FERRIC IRON AS A FUNCTION OF pH	189

33.  SOLUBILITY OF FERROUS IRON IN AN OXYGENATED SYSTEM	191

34.  FIELDS OF STABILITY OF SOLIDS AND SOLUBILITY OF MANGANESE AS A
     FUNCTION OF Eh AND pH AT 25 C AND 1 ATMOSPHERE OF PRESSURE .... 192

35.  SOLUBILITIES OF SOME METALS SHOWING DEPENDENCE ON pH AT 25 C . .  . 193

36.  EQUILIBRIUM pH IN RELATION TO CALCIUM AND BICARBONATE
     ACTIVITIES IN SOLUTION IN CONTACT WITH CALCITE 	 194
                                     xi

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                               LIST OF TABLES
 1.   COMPARISONS  OF EPC VALUES  FOR AIR WITH HOMER CITY
     FUGITIVE DUST DATA	28

 2.   COMPARISONS  OF EPC VALUES  FOR SOIL WITH HOMER
     CITY FUGITIVE DUST DATA	30

 3.   COMPARISONS  OF MATE VALUES FOR SOLID WASTE
     WITH HOMER CITY FUGITIVE DUST DATA	32

 4.   WATER QUALITY PARAMETERS—HOMER CITY RECONNAISSANCE SURVEY  ....   38

 5.   LAND USE INFLUENCE ON STREAM WATER QUALITY
     AT HOMER CITY POWER COMPLEX	39

 6.   CAUSE/EFFECT MATRIX OF LAND USE CONTRIBUTIONS
     TO WATER QUALITY PARAMETER VALUES 	   40

 7.   CHEMICAL ANALYSIS—WATER YEAR 1973 YOUNG WOMAN'S
     CREEK NEAR RENOVO, PENNSYLVANIA	42

 8.   FORM OF TRACE METALS IN WATER SAMPLES OBTAINED AT  SITE CDE1 ....   50

 9.   COMPARISONS  OF EPC AND MATE VALUES FOR WATER WITH
     HOMER CITY SURFACE WATER QUALITY DATA	79

10.   COMPARISONS  OF CRITERIA RECOMMENDED FOR FRESHWATER AQUATIC
     LIFE WITH HOMER CITY SURFACE WATER QUALITY DATA	81

11.   WATER QUALITY PARAMETERS IN CLOSE AGREEMENT
     WITH BIOTA QUALITY RATING  	   82

12.   COMPARISONS  OF EPC AND MATE VALUES FOR SOIL WITH
     HOMER CITY SEDIMENT QUALITY DATA	84

13.   BIOLOGICAL QUALITY EVALUATION OF STREAMS SURVEYED
     IN THE AREA  OF THE HOMER CITY POWER COMPLEX	96

14.   SHORT-TERM AND LONG-TERM CONCENTRATIONS
     VERSUS OBSERVED CONCENTRATIONS  	  119

15.   WIND SPEED AND DIRECTION DURING CAMPAIGN II—
     FIRST 24-HOUR PERIOD	121

                                     xii

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                               LIST OF TABLES
                                 (Continued)

                                                                        Page

16.   COMPARISON OF PREDICTED VERSUS OBSERVED CONCENTRATIONS
     DURING PERIODS OF LIGHT VARIABLE WINDS DURING
     CAMPAIGN II—FIRST 24-HOUR PERIOD	122

17.   PARTICULATE CONCENTRATIONS IN THE VICINITY
     OF THE COAL CLEANING FACILITY	124

18.   DATA PRESENTATION OF PARTICLE SIZING SAMPLER  	 127

19.   RESULTS OF OPTICAL EXAMINATION OF FILTER PADS, CAMPAIGN I 	 128

20.   RESULTS OF OPTICAL EXAMINATION OF FILTER PADS, CAMPAIGN II  .... 131

21.   RESULTS OF MICROSCOPIC EXAMINATION OF GLASS-FIBER
     FILTER PADS, CAMPAIGN III 	 134

22.   BLANK ANALYSIS OF FILTER USED IN CAMPAIGN II	140

23.   BLANK ANALYSIS OF FILTER USED IN CAMPAIGN III	141

24.   TRACE ELEMENT ANALYSIS OF THE PARTICLE SIZING SAMPLER
     USED AT SITE 3, CAMPAIGN III	142

25.   COMPARISON BETWEEN TRACE ELEMENT CONCENTRATIONS
     IN 12- AND 24-HOUR SAMPLES	144

26.   COMPARISON BETWEEN TRACE ELEMENT CONCENTRATIONS AT
     SELECTED SITES (CAMPAIGNS I, II, AND III)	145

27.   TRACE ELEMENT CONCENTRATIONS AS THEY RELATE TO MASS CONCENTRATION
     RANGES FOR ALL SITES AND ALL CAMPAIGNS	146

28.   TRACE ELEMENT CONCENTRATION OF PARTICULATE ON THE FILTER PAD  ... 147

29.   COAL ANALYSIS (HELEN MINE)  	149

30.   TRACE ELEMENT ANALYSIS (HELEN MINE) 	 149

31.   COAL ANALYSIS (HELVETIA MINE)	150

32.   TRACE ELEMENT ANALYSIS (HELVETIA MINE)   	 150

33.   COAL ANALYSIS (TRUCKED-IN COAL) 	 151

34.   TRACE ELEMENT ANALYSIS (TRUCKED-IN COAL)  	 151

35.   HYPOTHESIS THAT THE MEANS OF THE SAMPLES AT
     EACH SAMPLING SITE ARE IDENTICAL	153

                                      xiii

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                               LIST OF TABLES
                                 (Continued)

                                                                        Page

36.   HYPOTHESIS THAT THE MEANS OF THE SAMPLES AT SITES 1 AND 3 ARE
     IDENTICAL TO THOSE AT SITES 4 AND 5, AND SITES 8 AND 9  ...... 154

37.   HYPOTHESIS THAT THE MEANS OF THE FOLLOWING SAMPLE GROUPS ARE
     IDENTICAL:  24-HOUR SAMPLES, 12-HOUR DAY SAMPLE, AND
     12-HOUR NIGHT SAMPLE  .......................
38.  HYPOTHESIS THAT THE MEANS OF THE FOLLOWING SAMPLE GROUPS ARE
     IDENTICAL 12-HOUR DAY AND 12-HOUR NIGHT SAMPLES .......... 156

39.  WOODY SPECIES RECORDED AROUND THE HOMER CITY POWER COMPLEX  .... 162

40.  MEDIUM AND LARGE SIZE MAMMALS RECORDED
     AROUND THE HOMER CITY POWER COMPLEX ................ 163

41.  BIRDS OBSERVED AROUND THE HOMER CITY POWER COMPLEX  ........ 164

42.  REPTILES AND AMPHIBIANS OBSERVED AROUND PONDS AND STREAMS
     NEAR THE HOMER CITY POWER COMPLEX ................. 165

43.  MINE DRAINAGE CLASSES ....................... 171

44.  CHEMICAL COMPOSITION OF COALS ................... 196

45.  ANALYSES OF ASH FROM ASH DISPOSAL AREA AT HOMER CITY COMPLEX  ... 197

46.  CONCENTRATION RATIOS FOR SELECTED METALS AND NONMETALS
     IN HOMER CITY ASH AND COAL SAMPLES  ................ 198

47.  ANALYTICAL TECHNIQUES FOR WATER SAMPLES .............. 201

48.  ANALYTICAL TECHNIQUES FOR SEDIMENT SAMPLES   ............ 203

49.  SURFACE WATER ANALYSES FOR CHERRY RUN BASIN-
     PART 1:  CHEMICAL CONTROLS ON SOLUBILITY   ............. 204

50.  GROUNDWATER ANALYSES FOR CHERRY RUN BASIN-
     PART 1:  SOLUBILITY CONTROLLING SPECIES .............. 205

51.  COMPARISON OF WATER QUALITY AT STATIONS H14  AND H16 ON  CHERRY
     RUN ABOVE AND BELOW MINE BOREHOLE DISCHARGES  (CAMPAIGN  I)  ..... 206

52.  SURFACE WATER ANALYSES FOR CHERRY RUN BASIN-
     PART 2:  TRACE MATERIALS   ..................... 207

53.  SEDIMENT ANALYSES— CHERRY RUN  ..... .............. 208

54.  GRANULOMETRY— CHERRY RUN BASIN   .................. 208

                                      xiv

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                               LIST OF TABLES
                                 (Continued)

                                                                        Page

55.  TRACE METALS IN GROUNDWATER NEAR CHERRY RUN	209

56.  SURFACE WATER ANALYSES FOR CHERRY RUN BASIN-
     PART 3:  NUTRIENTS AND SOLIDS	210

57.  SURFACE WATER QUALITY IN WEST TRIBUTARY TO WIER'S
     RUN—SOLUBILITY OF IRON, MANGANESE, AND CALCIUM 	 211

58.  SURFACE WATER ANALYSES FOR WIER'S RUN--
     PART 1:  SOLUBILITY CONTROLLING SPECIES 	 212

59.  SURFACE WATER ANALYSES FOR WIER'S RUN-
     PART 2:  TOXIC MATERIALS	213

60.  SEDIMENT ANALYSES FOR WIER'S RUN	214

61.  SEDIMENT GRANULOMETRY FOR WIER'S RUN  	 215

62.  SURFACE WATER ANALYSES FOR WIER'S RUN--
     PART 3:  NUTRIENTS AND SOLIDS	216

63.  SURFACE WATER ANALYSES FOR COMMON RAVINE/SECOND RAVINE—
     PART 1:  SOLUBILITY CONTROLS	217

64.  SURFACE WATER ANALYSES FOR COMMON RAVINE/SECOND RAVINE-
     PART 2:  TOXIC MATERIALS	218

65.  SURFACE WATER ANALYSES FOR COMMON RAVINE/SECOND RAVINE—
     PART 3:  NUTRIENTS AND SOLIDS	219

66.  SURFACE WATER ANALYSES FOR TWO LICK CREEK--
     PART 1:  SOLUBILITY CONTROLS  	 220

67.  SURFACE WATER ANALYSES FOR TWO LICK CREEK-
     PART 2:  TOXIC MATERIALS	221

68.  SEDIMENT ANALYSES—TWO LICK CREEK	221

69.  SEDIMENT GRANULOMETRY—TWO LICK CREEK	222

70.  SURFACE WATER ANALYSES FOR TWO LICK CREEK-
     PART 3:  NUTRIENTS AND SOLIDS	222

71.  AQUATIC BIOTA SAMPLING STATIONS 	.227

72.  DIATOM SPECIES AND STANDING CROPS COLLECTED
     FROM CHERRY RUN, DECEMBER 13-17, 1976	231

                                      XV

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                               LIST  OF TABLES
                                 (Continued)
73.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM
     CHERRY RUN,  APRIL 11-15,  1977	232

74.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE
     TRIBUTARY STREAMS IN THE VICINITY OF THE HOMER CITY POWER
     COMPLEX PROPOSED REFUSE AREA, DECEMBER 13-17,  1976  	  233

75.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE
     TRIBUTARY STREAMS IN THE VICINITY OF THE HOMER CITY POWER
     COMPLEX PROPOSED REFUSE AREA, DECEMBER 13-17,  1976  	  234

76.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM
     WIER'S RUN,  DECEMBER 13-17, 1976	235

77.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM
     WIER'S RUN,  APRIL 11-15,  1977	236

78.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROk THREE
     TRIBUTARY STREAMS IN THE VICINITY OF THE HOMER CITY
     POWER COMPLEX, DECEMBER 13-17, 1976 	  237

79.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE
     TRIBUTARY STREAMS IN THE VICINITY OF THE HOMER CITY
     POWER COMPLEX, APRIL 11-15, 1977	238

80.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM TWO
     LICK CREEK AND RAMSEY RUN, DECEMBER 13-17, 1976	239

81.   DIATOM SPECIES AND STANDING CROPS COLLECTED FROM TWO
     LICK CREEK AND RAMSEY RUN, APRIL 11-15, 1977	240

82.   BENTHIC MACROINVERTEBRATES COLLECTED WITH A SURBER SAMPLER
     FROM STREAMS  IN THE AREA OF THE HOMER CITY POWER COMPLEX,
     DECEMBER 13-17, 1976	241

83   BENTHIC MACROINVERTEBRATES COLLECTED WITH A SURBER SAMPLER
     FROM STREAMS  IN THE AREA OF THE HOMER CITY POWER COMPLEX,
     APRIL 11-15,  1977	2A4

84.   FISH SPECIES  SURVEYED AND  COLLECTED FROM STREAM SITES IN THE
     VICINITY OF THE HOMER CITY POWER COMPLEX, DECEMBER 13-17, 1976   . . 248

85.  FISH SPECIES  SURVEYED AND  COLLECTED FROM STREAM SITES IN THE
     VICINITY OF THE HOMER CITY POWER COMPLEX, APRIL 11-15,  1977  .... 249

86.  CONCENTRATIONS OF  FOUR HEAVY  METALS IN  FISH TISSUE SAMPLES
     FROM CHERRY RUN AND WIER'S RUN, APRIL 11-15,  1977	250

87   FISH  SPECIES  COLLECTED FROM  STREAMS IN  THE AREA
     OF  THE  HOMER  CITY  POWER  COMPLEX	252

                                      xvi

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                           LIST OF ABBREVIATIONS






BOD       biological oxygen demand




cfs       fubic feet per second




COD       chemical oxygen demand




DO        dissolved oxygen




EPA       U.S. Environmental Protection Agency




EPC       estimated permissible concentration




gpd       gallons per day




gpm       gallons per minute




IERL      Industrial Environmental Research Laboratory




MAP       moisture- and ash-free




MATE      minimum acute toxicity effluent




MEG       multimedia environmental goals




MESA      Mining Enforcement and Safety Administration




NPDES     National Pollution Discharge Elimination Systems




PennDER   Pennsylvania Department of Environmental Resources




PTMTP     U.S. EPA's Multiple Point Source Model




ROM       run-of-mine




RTP       Research Triangle Park




TDS       total dissolved solids




TKN       total Kjeldahl nitrogen




TOC       total organic carbon




TOS       total organic sulfur




TP        total particulates
                                    XVII

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                               INTRODUCTION

     Battelle's  Columbus Laboratories  has  contracted with  the U.S.
Environmental Protection Agency  (EPA)  to  perform a comprehensive envi-
ronmental  assessment  of physical  and  chemical  coal cleaning processes.
The  broad  goal  of this program (Contract  No. 68-02-2163)  is to establish
a  strong base of engineering,  ecological, pollution control, and cost
data which can  be used to determine those coal cleaning processes that
are most acceptable from the technological, environmental, and economic
viewpoints.  The analysis of methods  for  reducing overall environmental
pollution  through the use of cleaned  coal involves mathematical and
modeling techniques used for identification of optimum coal cleaning
process configurations, pollution control equipment, and  waste manage-
ment techniques.  These optimization  studies require an assessment of
the  pollution potential of coal cleaning  processes, associated facil-
ities, and—in  certain cases—the end uses of coal.
    In order to obtain the field  data necessary for the overall program,
Battelle initiated a sampling  and analysis program designed to identify
the combinations of coal cleaning processes and environmental conditions
which are  most  effective in reducing the  total impact of  coal use on the
environment. This was accomplished through the characterization of
process and effluent streams from a variety of coal cleaning facilities
and their  associated coal transportation, storage, and refuse disposal
areas.
    The recent  construction of an advanced coal cleaning  facility at a
power complex near Homer City,  Pennsylvania, provided a unique opportu-
nity to obtain  environmental data before operation of the facility for
potential comparison with similar data to be obtained after operation
begins.  Battelle conducted a  series of preoperational, multimedia,
grab-sampling campaigns in a study area which included this facility, in
order to document the abundance or concentrations of selected key param-
eters.   These data were used to evaluate the air, water, and biological
quality in the  study area.   The preoperational environmental studies,
although not sufficiently long-term to be a true baseline  analysis,  were

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conducted prior to operation of the cleaning plant as a reference point
for future comparisons.  Additionally, an engineering-oriented eval-
uation of the planned refuse disposal system for the facility was
accomplished.  The methods and results of these studies together with
preliminary interpretations are presented in subsequent chapters.

                     Description of the Study Area

    Battelle's environmental monitoring was conducted within a study
area that can be approximately bounded by a circle 4 miles (6.4 km) in
diameter.  The advanced coal cleaning plant in the center of the study
area is about 2 miles (3.2 km) southwest of Homer City, Pennsylvania.
Two of the aquatic biota sampling stations were slightly outside of the
circular study area.
    The six major habitat types within the study area are hardwood
forest, coniferous forest, cropland, grassland, water bodies, and areas
of industrial development.  The forest areas are primarily hardwoods,
dominated by oak and hickory. Isolated pockets of pine are present as
plantations rather than naturally occurring species.  Cropland is ex-
tensive in the study area, including contour and strip-cropped fields of
corn, wheat, and hay.  Grasslands include those areas that are presently
grazed and those areas that were previously grazed or farmed and are now
in a transition stage toward becoming a forest.
    Stream water quality evaluated within the study area is affected by
a number of land uses which are either included in the immediate study
area or take place at locations farther upstream.  The five major land
uses affecting stream water are:  agriculture, mining, urbanization,
construction, and power generation.  Agricultural runoff is a problem
because of the hilly terrain and includes runoff from both farmland and
pastures.  Many upstream watersheds add acid mine drainage from aban-
doned or active strip mines.  Almost the entire study area is on top of
deep mines.  As indicated earlier, Homer City, Pennsylvania, is imme-
diately adjacent to the study area on the northeast, and Indiana,
Pennsylvania, is only 5 miles (8.0 km) north of Homer City.  Both towns

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directly or indirectly add effluents from industrial and sewage treat-
ment facilities to Two Lick Creek before it flows through the study
area. During Battelle's sampling campaigns, both the coal cleaning plant
and the refuse disposal area for that facility were under construction
in the study area.  Finally, the study area includes the Homer City
Power Station, with its associated coal storage, water treatment, and
waste disposal facilities.
    The Homer City Station is one part of an integrated power complex
which includes t.jo deep coal mines; coal cleaning, storage, and
transport facilities; power generation facilities; and waste disposal
and treatment facilities (Figure 1).  Some coal used at the Homer City
Station comes from the two dedicated deep mines in the power complex;
other coal is hauled by truck from other mines.  Solid refuse from power
complex activities is deposited in three different types of disposal
areas, including an ash disposal area, mine waste or "boney" piles, and
the cleaning plant refuse disposal area. Liquid waste treatment facil-
ities in the power complex include: mine and boney pile leachate water
treatment facilities, an emergency holding pond constructed near the
coal cleaning plant, coal storage pile runoff desilting ponds, an
industrial waste treatment plant, power plant storm runoff desilting
ponds, bottom ash sluice water desilting ponds, sewage treatment
facilities, and ash disposal area leachate treatment ponds.

                    Data Comparison with MEG Values;

    Preoperational monitoring data from Battelle's study area near Homer
City, Pennsylvania, are compared with the values listed in the Multi-
media Environmental Goals (MEG) documents prepared for the U.S. EPA by
Research Triangle Institute (Cleland and Kingsbury, 1977a and b).  MEG
values represent the maximum levels of significant contaminants which
are not considered to be hazardous to man or the environment.  The MEG
methodology was developed to facilitate the evaluation and ranking of
pollutants for the purpose of environmental assessment of energy-
related processes.

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   — Ash Disposal Area
   — Mine Drainage Treatment Pond
C  - Helvetia Boney Pile (at mine)
D  - Coal  Cleaning Rant
   - Coal  Storage Pile
   — Power Plant
G  - Industrial Watte  Treatment Plant
H  - Helen Boney Pile (at mine)
                                              Coal Cleaning  ^\
                                              Refute Disposal    '
                                              Area
                                                                                        Kilometer
                                                                                0        0.5
                     FIGURE 1.   MAP OF THE HOMER CITY POWER  COMPLEX

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    MEG values have been estimated for 216 pollutants by  extrapolating
various toxicity data by means of simple models.  For most of  these
pollutants, maximum values have been estimated for each of the  three
media (air, water, and land).   For each of the three media,  separate
maximum values have been estimated which are not considered  to  be
hazardous to (1) human health and (2) entire ecosystems.
    The MEG values that are particularly appropriate for  comparison with
the environmental monitoring data from Battelle's study area  are those
designated as estimated permissible concentrations (EPC's).   EPC's  are
the maximum concentration of a pollutant which presents no hazard  to  man
or biota on a continuous long-term basis.  These EPC values are consid-
ered acceptable in the ambient air, water, or soil, and do not  apply  to
undiluted effluent streams.  The ambient application of EPC's cor-
responds to the ambient type of sampling conducted by Battelle  prior  to
operation of the Homer City Coal Cleaning Plant.
    A second type of MEG values considered in this study  are those
designated as minimum acute toxicity effluent (MATE) values.   MATE's  are
concentrations of pollutants in undiluted effluent streams which will
not adversely affect those persons or ecological systems  exposed for
short time periods.  Very little of the preoperational monitoring  con-
ducted by Battelle near Homer City involved undiluted effluents, but  in
the case of a few pollutants, this value was the only MEG value avail-
able for comparison with Battelle's data.

                    Environmental Components Sampled

    During the period from December, 1976, through April, 1977, a  series
of three preoperational grab-sampling campaigns were conducted by
Battelle in the ambient media of the study area which included the Homer
City Power Complex.  These environmental monitoring studies involved
sampling, laboratory analysis, and/or evaluation of the  following  com-
ponents of the environment.

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            •  Fugitive dust
            •  Stream water and sediments
            •  Aquatic biota
            •  Terrestrial biota
            •  Raw coal and fly ash
            •  Cleaning plant refuse disposal area
            •  Groundwater.

Only the first three were analyzed in sufficient detail to warrant com-
parison with MEG values.  Samples of fugitive dust, water, and stream
sediments were collected during three campaigns and analyzed for phys-
ical and chemical parameters. Aquatic biota were sampled during two
campaigns for determination of indicator species, standing crop, species
diversity, and chemical analysis of fish.

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                    CONCLUSIONS AND RECOMMENDATIONS

        Environmental Quality Prior to Cleaning Plant Operation

    The terrestrial and aquatic ecosystems in the vicinity of the Homer
City Coal Cleaning Plant reflected varying degrees of environmental
stress.  The aquatic ecosystems showed the greatest impact.  Some of the
streams in tho area were inhabited by small populations of a few
tolerant species.  The air quality on the plant site was poor,
containing high levels of particulate matter.
    The terrestrial flora within 1 mile (1.8 km) of the cleaning plant
were quite diverse and supported animals common to all successional
stages, especially those wildlife species associated with the early
successional vegetation.  The area did not contain good water bird
habitat.  The continuing accumulation of particulate matter in a 1-mile
(1.8 km) radius is expected to cause an environmental stress.  Ad-
ditional studies are necessary to make a detailed evaluation of impacts
on the terrestrial biota.
    The aquatic sampling and  reconnaissance program studied a  total of
14 sites in 8 streams.  Stream quality was evaluated as good to poor.
For example, the tributary north of the refuse  area, now under con-
struction, had good overall biological quality.  Similarly, the upstream
portion of the tributary south of the refuse area was judged  to be  of
good quality.
    Cherry Run was evaluated  as having fair biological quality based on
the number of species  of fish inhabiting this  stream.  However, the
quality of the biological  community inhabiting  Cherry Run  has  been
affected by both plant  and mining  operations in the area.   Small
populations of benthic macroinvertebrates  and  fishes were  clearly
a  result of the reduced water quality.
    The remaining  streams, Wier's  Run, Rager's Pond  tributary, Common
Ravine, and the downstream portion of  the  tributary  south  of  the  refuse
disposal  area were all considered  to  have  poor biological  quality.   In
all cases  poor water  quality  was  due  to aqueous releases  to the

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environment from the existing facility.  Two Lick Creek was not rated
because of the small number of biological samples collected in this
study.
    The quality of groundwater in the area was reported to be marginal
to poor and unfit for consumption.
    The water of the streams that drain the power plant site was of
marginal quality.  Within a short distance downstream, however, con-
ditions improved due to the buffering capability and dilution.
    The stream sediments of the area were heavily laden with metals.
The streams have high levels of dissolved oxygen; however, periodic low
pH levels and high suspended solids prevent recovery of a high quality
biological community. Oil sheens were present during all sampling
periods conducted in the Common Ravine area.  As expected in a coal
region lithology, the streams had high levels of forms of iron,
manganese, sulfur,  and calcium.
    Air samples collected near the coal cleaning plant contained a wide
range of particulate loadings.  The heaviest mass loadings were measured
at 200 meters downwind of the existing coal pile.  At 2000 meters down-
wind the measured levels dropped to levels consistent with a good air
quality index.
    The stations within 1000 meters of the site had a distinct diurnal
loading phase.  In the daytime the mass weights were 50 percent higher
than the contiguous nighttime values.  Obvious and significant impacts
were found to extend about 1200 meters downwind.  The snow cover
assisted in determining the fugitive dust impact area.  The average of
the coal particle sizes at all stations was measured to be between 2 to
70 microns in diameter.  The average ash size at all stations was in the
5  to 20 micron range.  Coal was the predominant material deposited on
the high-volume (hi-vol) and "Andersen" filters.
    Trace element concentrations were not directly related to variance
in mass weights.  The average trace element concentrations were higher
at 12-hour sampling sites than at the 24-hour sampling sites and were
generally  500 meters downwind of the coal cleaning plant site.  South-
west winds prevailed at the site for 70 percent of the time during

                                     8

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the three sampling campaigns.  These southwest winds generated the high-
est levels of particulate loadings.  The lowest fugitive dust values
were recorded under a northwest wind.
    To support the fugitive dust monitoring activity, a multiple source
fugitive dust dispersion model was developed. The model was field
calibrated to the sampling results and source conditions at the Homer
City Coal Cleaning Plant.  It is probable that this model will continue
to function well at other coal handling and storage facilities.  This
model can be used to select the optimum air sampling receptor locations
in addition to predicting dispersion levels with distance and
meterologic conditions.
    Results of the fugitive dust chemical analysis revealed two major
and interesting phenomena.  First, there was uncombusted coal dust at
200 meters downwind of the coal cleaning plant site that contained
higher levels of lead, cadmium, arsenic, and mercury than were present
in the whole coal analysis.  Cadmium and lead values were several orders
of magnitude higher than corresponding values from the whole coal
analysis.  Beryllium and vanadium were not found in the coal dust, but
were quite evident in the source coals.  Second, a differential and
preferential particle magnification was most likely occurring.  This may
be because the ROM Upper Freeport coals have a greater percent of
some trace metals available for wind transport on their exposed surface
cleavage planes than the percentage of these metals present in the
entire chunk of coal.
    The proposed design of the refuse disposal facility covers most of
the important potential environmental problems in coal refuse dis-
posal, such as slope stability, erosion, and leachate control.  It is a
problem, however, that the actual construction as it existed in the
field on April 21, 1977, may not completely control the migration of the
heavy metal laden leachate.  This was principally due to the intersec-
tion of the main leachate collection line with an unconsolidated
sandstone saddle bench that surfaces on the site.  Another problem with
the site was the construction of a storm drain trunk line at a lower
vertical displacement than the leachate collection pond in the first

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lift area.   This may permit the surface runoff leachates  to  bypass  the
leachate collection pond and treatment system.

      Pollutant Toxicity Considerations and MEG Value Comparisons

    Several factors confounding pollutant toxicity evaluations need to
be considered when comparisons are made between estimated permissible
concentration (EPC) values and field data on pollutant concentrations
and biological quality. First, the EPC values have not incorporated
interactive effects of pollutant combinations, such as synergism or
antagonism. (Antagonistic effects between pollutants measured in stream
water and sediments may explain how some EPC's for ecology were exceeded
in  streams that had a good biological quality rating.) Second, EPC's and
field chemical data frequently involve only total elemental concentra-
tions. Biota in the ambient environment, however, may be adversely
affected only by specific compounds or ions of an element that are
relatively stable  in the ambient media and not by other compounds that
are included in the total elemental concentration. To date, EPC values
for inorganics have been determined primarily for groups of compounds
which have a common parent element; comparatively few of the individual,
highly  toxic compounds within  these groups that are also relatively
stable  in the environment have been evaluated for an EPC. Third, some of
the water quality  parameters which are extremely important  in making an
environmental assessment of coal-related effluents on aquatic biota do
not presently have EPC's. These master parameters, including  suspended
solids,  pH, alkalinity, etc.,  are  planned  for future EPC evaluation.

Fugitive Dust and  the Terrestrial Environment

    Elemental concentrations  in fugitive dust which  were measured  in the
study area  exceeded  both EPC  and MATE values  for  air and  soil  quality.
For example,  three out  of  fifteen  elements  analyzed  in fugitive  dust had
concentrations  above  the  health-based EPC's  for air  quality.  Comparisons
with  ecology-based EPC's  for  air quality,  however,  were  very difficult
because of  the  absence of  ten EPC  values.
                                    10

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    Although no soil concentrations were determined, comparisons of
elemental concentrations in fugitive dust were made with ecology-based
EPC's for soil because of the potential problem of toxic elements leach-
ing into the soil from fugitive dust laying on the ground.  Eleven of the
fifteen elements studied had concentrations in the fugitive dust which
were above the ecology-based EPC's for soil. Thus, additional research
needs to be conducted to determine if leaching is a problem. The ex-
istence of this type of problem, however, seems to be inconsistent with
the condition of the vegetation in the area. In spite of the dust
(particularly coal dust) present on the ground for some distance around
the coal pile, the vegetation has not yet begun to show any obvious
adverse effects.
    Several recommendations can be made based on this study. First, more
field experiments are needed to validate these results. The amount of
available data is small and more extensive sampling and elemental anal-
ysis, particularly of soil and plant and animal tissues, are needed.
These steps are necessary to determine the fate of the trace metals in
the fugitive dust.

Stream Water, Sediments, and Aquatic Biota

    Of the thirty water quality parameters measured in streams, only
fifteen parameters have associated MEG values. Thus, some of the surface
watar quality data were compared with the MEG's and some were compared
with other available criteria. .The maximum and minimum of ten param-
eters exceeded the corresponding EPC's for the environment.  In fact,
maximum, and some minimum levels, of four pollutants (ammonia, vanadium,
manganese, and zinc) exceeded the appropriate EPC values, even in
streams considered to have good biological quality.  This apparent
discrepancy needs to be further evaluated both in terms of the validity
of the proposed EPC values used, and in terms of the interactions and
uniqueness of the chemical and biological conditions encountered in the
study area streams.
    Fifteen water quality parameters evaluated in Battelle's study do
not have corresponding MEG values; these parameters were compared with

                                    11

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criteria from U.S. EPA (1976) and McKee and Wolf (1963).  Values for
four of these parameters (pH, suspended solids, dissolved iron, and
total organic carbon) were in close agreement with the biota quality
evaluation.  The three groups of aquatic biota used in the subjective
evaluation of stream quality were periphyton, benthic macroinver-
tebrates, and fish.
    Elemental concentrations in stream sediments were considerably
higher than the corresponding MEG values.  Maximum and minimum con-
centrations of eight elements in sediments exceeded the associated EPC's
and MATE's for ecology.  This situation occurred for seven elements,
even in a stream with good biological quality.  Again, the field situa-
tion and proposed EPC values need to be evaluated in more detail to
determine if a discrepancy exists.

Future Studies Recommended

    Additional research needs to be conducted on EPC and MATE values
before they can be used to evaluate and rank pollutants for the purpose
of environmental assessment.  Much of this work was recommended in the
initial MEG document (Cleland and Kingsbury, 1977a) and is now or will
soon be in progress. For example, MEG's need to be related to the
specific compounds or ionic forms of an element which are most toxic,
rather than having a single value represent all compounds and ions which
have a common "parent" element.  Synergistic and antagonistic effects
need to be considered because they may drastically change the hazard
ranking of a pollutant in a specific situation. MEG's are also needed
for many of the master parameters, such as the "totals" identified by
Cleland and Kingsbury (1977a: 155)  (e.g., total particulates) or the
water quality parameters identified in this study (e.g., pH, suspended
solids, dissolved iron, and total organic carbon).
    In another vein, the comparison of trace element concentrations in
fugitive dust to MEG values points out the need for laboratory and field
research, particularly in relation to fugitive dust that consists pre-
dominantly of coal particles.  First, the rates at which toxic elements

                                    12

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leach from coal dust into a variety of soil types need to be explored.
Second, the concentrations of toxic elements present in the soil around
a large, open coal pile need to be determined when this pile has been in
existence for a long period of time. Third, laboratory bioassay and
long-term field studies need to be conducted on the effects of coal dust
on plants and animals.
    It is important that the type of research necessary to improve and
expand the initial MEG approach to environmental assessment be completed
soon.  Once the MEG methodology has been refined it will become an
essential part of any assessment of environmental pollution.
                                   13

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                        TERRESTRIAL ENVIRONMENT

                        Fugitive Dust Monitoring

    Potential fugitive dust sources at the Homer City power complex were
investigated during a presampling site evaluation.   Some of the  dust
sources included an ash disposal area, boney piles  at both deep  mines,  a
coal storage pile, road dust, three power plant stacks, and
construction-generated dust. The coal cleaning plant with its thermal
dryers and the cleaning plant refuse disposal area  were under construc-
tion during Battelle's sampling campaigns.  Because these two areas were
considered to be future potential sources of fugitive dust, they were
considered in the selection of sampling sites.
    The fugitive dust data were collected and analyzed for comparison
with MEG values.  The samples collected during three campaigns were
analyzed for both physical and chemical parameters.  Information from
the survey of terrestrial biota conducted during one campaign was
utilized, as later described, in attempts to confirm the results of MEG
comparisons.
    Fugitive dust monitoring was conducted using high-volume (hi-vol)
ambient air samplers during the following three 48-hour sampling
periods:
    •  Campaign I:  8 p.m. December 17 to 8 p.m. December 19, 1976
    •  Campaign II:  8 p.m. January 5 to 8 p.m. January 7, 1977
    •  Campaign III:  8 p.m. April 5 to 8 p.m. April 7, 1977.
The first of these three campaigns was conducted over a weekend  when
both coal transfer and construction activities were at a low level.
    A multiple-source fugitive-dust dispersion model was used to select
and verify locations for hi-vol samplers (Figure 2).  This model takes
into account such factors as wind speed, emission rate, particle size,
and distance from selected potential dust sources located within the
Homer City power complex.  No dust sources outside of the power  complex
were incorporated in the model.  On the basis of the computer-generated
diffusion-modeling results, ten monitoring sites were established at
                                    14

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                                                       Coal Cleaning
                                                       Refuse Disposal
   Existing Ash
   Disposal Area
    Wind Speed and Direction
    Recorder
  5) Hi Vol. Sampler
                                            0
                                             fee
        0.5
                                                                   1.0
                       Kilometer

                         Mile
1/2
FIGURE 2.   LOCATION  OF FUGITIVE  DUST  SOURCES AND  MONITORING  SITES
                                      15

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distances of 175 to 2200 m downwind from various local dust sources.
One of the ten sites was on private property downwind of the power
complex property and one site was on private property upwind of  the
complex.
    Several potential dust sources, both local and regional, were not
incorporated into the diffusion model for sampling site selection.  Dust
generated by vehicular traffic, parking lots, construction activities,
several storage silos, and especially the dusty surface of the plant
grounds was not included in the model due to its erratic and non-point-
source nature.  Data for the Homer City power plant stack emissions were
not available in time to include in the model.  In addition, four other
major power stations (Keystone, Conemaugh, Seward, and Shawville) are
located in the same Chestnut Ridge sector of the Allegheny Mountains  as
Homer City.  These utilities are fed from coal mines located either
directly under or near the station sites.  The model did not include
fugitive emission data from any of these facilities.
    In order to identify the type and quantity of pollutants being
emitted from fugitive dust sources, a variety of analytical techniques
was employed.  Particulate mass was determined by weighing the 8 x 10-
inch fiberglass filters used in the hi-vol samplers before and after
each of the 12- or 24-hour sampling periods.  A microscopic analysis  was
made of particulates to provide a distinction between components such as
coal dust, fly ash, pollen, or construction dust.  An Andersen sampling
head was used at only one of the ten hi-vol sampling sites to obtain
data on the distribution of particles in five size fractions.
    Particulates on the filters from the hi-vol samplers were analyzed
for up to 22 elements.  The analytical technique used for most elements
was atomic absorption; but neutron activation, colorimetry, a specific
ion meter, a total organic carbon analyzer, an LDC mercury monitor, and
potentiometric titration were also used.  Because large amounts  of four
of these 22 elements (Na, K, Ca, and Mg) were found in the blank
filters, the values for these four elements were not reported.  Four  of
the remaining 18 elements (Sb, Ti, V, Se) were analyzed only in the
second or third campaign.  In general, the filter exhibiting the highest
                                     16

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percentage of coal or ash from each site was used for analysis.   Data
from 15 of the elements analyzed are used in the analysis and sub-
sequent comparisons.   Details of the field study are given in
Appendix A.

Fugitive Dust Field Study Results

    Battelle objectives in this field study were to identify the type
and quantity of pollutants being emitted from fugitive dust sources
associated with the power generator at the location of the future Homer
City Coal Cleaning Facility.   Detailed procedures, models, analysis
techniques, and results are given in Appendix A.  The following  con-
clusions were drawn from these analyses of the field studies.
    (1)  The ash disposal area was not a principal source of fugi-
         tive dust during these sampling campaigns, probably because
         moisture in  the ash prevented wind entrainment of ash
         particles.
    (2)  The coal storage pile was the primary source of coal dust and
         trace metal  emissions during these sampling campaigns.
    (3)  Maximum concentrations of fugitive dusts were observed  within
         200 meters of the coal storage pile.
    (4)  Site 6, which is generally upwind of the plant site, was used
         as a background site.  Total mass concentration observed at
         this site averaged 44 yg/m^, the maximum concentration  was 76
         yg/m3, and the minimum was  33  yg/m^.
    (5)  Sites 9 and  10, which are generally downwind from the fugitive
         dust sources, were used to assess the impact of fugitive dust
         emissions leaving Homer City Power Station property. The
         maximum 24-hour concentrations were 45 and 82 yg/m^,
         respectively, and the average concentrations were 40 and 51
         Ug/m-J, respectively.  The data suggest that the impact  of
         fugitive dust to the surrounding ambient air quality off the
         property is  not significant.

                                     17

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    (6)  Trace metals were measured in the coal and  the  disposed  ash  at
         the Homer City facility as well as the particulate  matter  on
         selected hi-vol filter pads.   There is an apparent  large
         magnification of trace metal  concentrations above the
         availability levels in either coal or disposed  ash.  Although
         mass concentrations were not  elevated at  the off-site  Stations
         9 and 10, trace metal magnification was apparent for these
         stations.  For example, the average concentration of the trace
         metal cadmium for the three campaigns was 31 ppm* and  11 ppm at
         Sites 1 and 3**, respectively, while the  average concentration
         was 206 ppm and 137 ppm at Sites 9 and 10,  respectively.
    (7)  The primary air quality standards for particulate matter (75
         yg/m3) were exceeded during only one of the three  sampling
         campaigns (January 5-6, 1977) at two monitoring sites  which
         were located outside of the property line of Homer  City  Power
         Station.  The upwind location measured 76 yg/m3 of
         particulates and the downwind location measured 82  yg/m3 of
         particulates.

                        Terrestrial Biota Survey

    Brief, reconnaissance-type surveys of terrestrial biota  were  con-
ducted on December 15 and 16, 1976, and during the week of April  11-15,
1977, in order to prepare a general description of selected  ecosystem
components as they existed prior to operation of the Homer City Coal
Cleaning Facility and to provide a qualitative description  for  testing
of MEG/MATE comparisons.  The preoperational description of  vegetation
and wildlife will permit future comparisons with results of  similar
surveys made during the same seasons after the cleaning plant begins
 *ppm is the concentration of Cd in the particulate matter captured on
   the filter pad.
**Sites 1 and 3 were located within 200 meters downwind of the coal
  storage pile.
                                    18

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 operation.   Surveys which included field observations within a 2-mile
 (3.6-km) radius of the cleaning plant were made  in December,  1976,  and
 April,  1977.   Both surveys  involved the listing  of habitat types  and
 plant and wildlife species,  but quantitative listing  of  all  species was
 not possible  in view of the  limited time periods and  seasons  when
 surveys  were  possible.   Scientific names of the  biota observed are  given
 in Appendix B.
     Dominant  vegetation species within a 1-mile  (1.8-km)  radius of  the
 coal cleaning facility were  plotted on topographic maps  (see  Figure 3).
 A subjective  assessment of the  plant  species encountered  most  frequently
 and an assessment  of the relative  sizes of the plants observed provided
 the criteria  used  as the basis  for determining the dominant vegetation.
 In addition,  all habitats within a 1- and  2-mile (1.8- and 3.6-km)
 radius of the cleaning  facility were  identified.

 Vegetation

     Geographically,  the  Homer City Coal Cleaning Facility  lies  within
 the  Mixed Mesophytic  Forest Region, which  encompasses a region from
 northern Alabama to  northwestern Pennsylvania. More specifically, the
 Homer City area lies  within the Low Hills  Belt of  the Cumberland  and
 Allegheny Plateaus  (Braun, 1972).  It  is an  area  typified by low relief
 and  relatively gentle slopes.   Extensive cutting  in this entire region
 has  resulted  in a pronounced increase  in the upper  slope forest types of
 oak and oak-hickory, which prevail  today.   The mixed  mesophytic forest
 type, which dominates this area, is typically composed exclusively of
 hardwood.  However, the Homer City  area lies in  close  proximity to the
Hemlock-White  Pine-Northern Hardwood  Forest Region of northern
Pennsylvania and southern New York, and thus some  pine and hemlock exist
naturally, in  addition to large areas of various  coniferous species
which have been planted in this region.
    The terrestrial vegetation within 2 miles (3.6 km) of the coal
cleaning  facility has been mapped as hardwood forest,  coniferous forest,

                                    19

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             KILOMETER
          0      .5      1
JjABITAT TYPES
|^HARDWOOD FOREST
31 COM FERGUS FOREST
[3 CROPLAND
^GRASSLAND
  J WATER BODY
  | INDUSTRIAL DEVELOPMENT
DOMINANT SPECIES

1 APPLE TREES
GRASS

2 NORWAY SPRUCE
SCOTCH PINE
\
3 NORWAY SPRUCE
SCOTCH PINE
RED SPRUCE
4 RED MAPLE
5 RED MAPLE
BLACK CHERRY
6 BLACK LOCUST
BLACK CHERRY
7 GRASS
BLACKBERRY
BLACK CHERRY

8 GRASS
BLACK RASPBERRY

9 GRASS
WEEDS

10 STAG HORN SUMAC
BLACKBERRY

11 BLACK CHERRY
YELLOW-POPLAR

12 RED MAPLE
NORTHERN RED OAK
YELLOW-POPLAR

13 BLACK LOCUST
14 WHITE OAK
BLACK OAK
1 5 PLOWED CORN FIELD
16 STAGHORN SUMAC
DOGWOOD
HAWTHORN
1 7 NORTHERN RED OAK
WHITE OAK

18 WHITE OAK
BLACK CHERRY
1 9 HEEDS
HAWTHORN
DOGWOOD
20 BLACK CHERRY
SCARLET OAK

21 BIGTOOTH ASPEN
HAWTHORN

22 WEEDS
BLACKBERRY

23 BLACK CHERRY
SYCAMORE
24 HAWTHORN
25 RED PINE
SCOTCH PINE
26 WEEDS
BLACK CHERRY
27 RED MAPLE
WHITE OAK

28 AMERICAN BEECH
29 BIGTOOTH ASPEN
RED MAPLE

30 RED MAPLE
NORTHERN RED OAK
BIGTOOTH ASPEN

31 DEVIL 5 CLUB
GRASS

32 CRABAPPLE
RED MAPLE
BLACK LOCUST

33 RED OAK
BLACK CHERRY
34 WHITE OAK
SHAGEARK HICKORY
35 SCOTCH PINE
36 RED OAK
SHAGBARK HICKORY
37 HAWTHORN
j RED MAPLE
j
: 38 HEMLOCK
NORWAY SPRUCE
WHITE PINE
39 BLACK CHERRY

j 4C VIRGINIA PINE
j <1 SHINGLE OAK
                 FIGURE  3.   VEGETATION  TYPES IN THE VICINITY OF  THE HOMER CITY COAL CLEANING PLANT

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cultivated land, or grassland (see Figure 3). Tree species observed
within this 2-mile radius are listed in Appendix B.
     Cultivated lands are those currently being utilized for agricul-
tural crops.  Corn, wheat, and hay are the dominant crops under
cultivation.  Agricultural practices in the region include strip-
cropping and contour plowing to minimize the erosion problems created by
the hilly topography.  Much of the region is too hilly for any
agricultural use other than grazing.
    Grassland areas include those areas currently being used for
pastureland as well as those that had been grazed or farmed in the past
ten to fifteen years and are now in a transition state from pure
grassland to forest, with species of both types being common.

Wildlife Observations

    General observations of four wildlife groups were made in conjunc-
tion with other biotic surveys conducted in December, 1976, and April,
1977.   Notes were taken on all mammals, birds, reptiles, and amphibians
observed during conduct of the other surveys.  However, no quantitative
transect or plot data were obtained.  December observations were con-
centrated around the existing ash disposal area and the cleaning plant
refuse disposal area; April observations were made primarily along
streams or ponds.  Emphasis in April was on terrestrial wildlife closely
associated with the streams or ponds, because the primary ecological
effects are expected to appear in the aquatic system.  Most of the
reptile and amphibian observations were made in connection with the fish
seining and stocking surveys in the smaller streams.   List of species
and observation notes are in Appendix B.

    Mammals.   Seven species of mammals were observed  around the Homer
City power complex.  Both the white-tailed deer and the raccoon appeared
to be  abundant, judging from the number of tracks found in most areas
around the complex.  The Virginia opossum, eastern cottontail, gray

                                    21

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 squirrel, and woodchuck  were  relatively  common.  The muskrat, however,
 was  surprisingly  rare  for  the number  of  streams and ponds in the area.

     Birds.  Eighteen species  of  birds were observed during a
 reconnaissance  around  the  ash disposal area and the cleaning facility
 refuse disposal area on  the afternoons of December 15 and 16, 1976.  The
 black-capped chickadee,  tufted titmouse, white-breasted nuthatch, and
 tree sparrow were relatively  abundant around the ash disposal area;
 while  the black-capped chickadee, cardinal, and American goldfinch were
 relatively abundant around the refuse disposal area.  Birds observed
 included both permanent  (year-long) residents and winter residents.
     Bird observations during  April 11-15, 1976, were restricted to water
 birds seen at streams or ponds in the vicinity of the power complex.
 The only water birds observed were five mallards and one pied-billed
 grebe.  This number of species and individuals is below that expected
 for streams and ponds in that part of Pennsylvania during April (Todd,
 1940).  The absence of marshes with emergent vegetation is probably one
 important reason  for the limited number of water birds in the area.  On
 the other hand, additional surveys in early spring or fall would
 undoubtedly have resulted in the observation of a greater number of
 migratory waterfowl.

    Reptiles and Amphibians.  Five species of reptiles and amphibians
 were recorded in or along the streams or ponds during the April field
 trip. The northern two-lined salamander was the most abundant of these
 five species, but only eight individuals were recorded.   Seven two-lined
 salamanders were captured at seven fish survey sites on Cherry Run and
 its tributaries.  One two-lined salamander was captured at one of four
sites on Weir's Run and  its tributary.  No salamanders were observed at
one site each on the Rager's Pond and Common Ravine tributaries and at
 the one survey site on Ramsey Run.  The other four reptiles and
amphibians observed were the American toad, green frog,  wood turtle,  and
queen snake.

                                    22

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Biological Field Study Interpretation

    The following discussion and recommendations concerning the December
and April reconnaissances of terrestrial biota will be helpful in
referencing existing perturbations of the plants and wildlife prior to
the operation of the Homer City Coal Cleaning Facility.  However, no
conclusions can be drawn about the environmental effects of the new
facility.  Results of the terrestrial studies are intended only as a
reference point f r r use in future comparisons with more detailed surveys
conducted after operation of the coal cleaning plant begins.   Surveys
during the other seasons of the year will also be essential in
evaluating the effects of the coal cleaning facility.
    The vegetation map (Figure 3) shows that the area around the coal
cleaning facility is composed essentially of six habitat types, in-
cluding hardwood forest, coniferous forest, cropland, grassland, water
bodies, and areas of industrial development.  The forested areas are
primarily hardwoods, dominated by oak and hickory trees.  Isolated
pockets of pine are present as plantations rather than naturally occur-
ring species.  Cropland also is extensive in the area, including con-
tour and strip-cropped fields of corn,  wheat, and hay.  Grasslands
include those areas which are presently grazed and those areas which
were previously grazed or farmed and are now in a transition stage
toward becoming a forest.  Logging, mining, farming, grazing, and
industrial development have significantly altered the vegetation and
thus the habitats available to wildlife in the area. Each of these
perturbations has induced significant changes in the local fauna by
reducing the amount of mature forest and creating habitats that have
attracted wildlife species associated with early successional
vegetation.
    Measurement and field observations on the extent of gaseous and
particulate pollution from coal storage, burning, and refuse disposal
(see the section on Fugitive Dust Monitoring) strongly suggest that the
biota, particularly the vegetation, in the immediate vicinity of the
power plant are being impacted by the power complex.  Visual inspection

                                    23

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of  the vegetation during April, when deciduous trees still were without
leaves, did not indicate any obvious injury to the vegetation within a
1-mile radius of the cleaning facility.  However, coal dust was observed
on  vegetation and in leaf litter up to 1 mile from the coal pile.  This
fugitive dust in combination with the particulate pollution from the
power plant may result in the biological accumulation, transfer, and/or
biomagnification of toxic elements associated with the coal and fly ash.
Chemical analysis of plant and animal tissue for toxic elements known to
occur in the coal used at Homer City is recommended to determine the
extent of the problem prior to the long-term changes in air pollution
expected to result from operation of the cleaning facility and burning
and storage of cleaned coal.
    Only two species of water birds were observed during the entire week
of  field surveys in April.  Lack of marshy habitat necessary for feeding
and brood rearing may be a major reason that a greater number of species
was not observed.  In addition, aquatic flora and fauna can be killed by
dilute concentrations of heavy metals (copper, lead, zinc, etc.)
(Spauling and Ogden, 1968).  Because the water, sediment, and fish-
tissue analyses on samples taken from the streams around the power
complex showed the presence of heavy metals (see the sections on Water
Quality Determinations and Aquatic Biota Survey), it is possible that
some aquatic vegetation and some water bird species have been eliminated
from these streams owing to the uptake of toxic heavy metals.  Waterfowl
habitat is often destroyed by pollution from both mining and industrial
operations by decreasing the ability of the water body to support veg-
etation and animal life upon which waterfowl feed.   For example, acid
mine water has destroyed or seriously damaged more than 4,000 miles of
streams In the United States, primarily by destroying food organisms
(McCallum, 1964).  Additional surveys during the migratory, nesting, and
brood rearing seasons are suggested to determine the current importance
to water birds of the streams and ponds around the Homer City power
complex.
    Although the survey period in early April may have been too early
for sandpipers such as the spotted sandpiper (Actitis macularia) and too
late for some of the early migrating waterfowl, several birds common
                                    24

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Co streams and ponds in western Pennsylvania were not observed.  The
wood duck (Aix sponsa). great blue heron (Ardea herodias),  and belted
kingfisher (Megaceryle alcyon) are three examples of birds  commonly
associated with small water bodies in western Pennsylvania  during early
April (Todd, 1940) which were not observed during the surveys around the
Homer City power complex.
    Of the seven species of medium- and large-size mammals  recorded
around the Homer City power complex, the muskrat was the least abundant.
This mammal is closely associated with water and is normally found along
the banks of even the smallest Pennsylvania streams (Doutt, et al.,
1973).  Peak density of these furbearers depends on, among  other
requirements,  water purity and available food.  Therefore,  it is
possible that  the low number of muskrats observed in the streams around
the Homer City power complex may be due, in part, to the polluted nature
of most of the streams and the lack of emergent aquatic vegetation.
    Many of the smaller mammals (mice, shrews, voles, etc.) not surveyed
during this reconnaissance are likely to occur in the Homer City area
(Doutt, et al., 1973).  These small mammals are often better indicators
of environmental stress than the medium- and large-size mammals because
of their large numbers and small home ranges.  An intensive snap-
trapping program along delected transects is recommended to document
population changes and to obtain tissue samples for chemical analysis of
toxic trace elements found in the coal used at the Homer City power
complex.
    Only five  species of reptiles and amphibians were recorded in or
beside water bodies around the Homer City power complex.  It was noted
that the streams and ponds had very little marshy habitat associated
with them and  that the supply of aquatic insects, which serve as food
for many of the reptiles and amphibians found along or in streams, was
only moderate  to low, except in the smallest tributaries.  This lack of
a plentiful food supply and an appropriate marshy habitat probably
accounts for the reduced numbers of individuals and species of reptiles
and amphibians in this area.  However, one species of reptile was found
along Cherry Run; this was the queen snake, which does not  require a

                                     25

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marshy  habitat  or  aquatic  insects.   In  fact,  it  is usually found along
small stony  creeks, where  it  feeds  principally on crayfish
(Conant,  1975).  Cherry Run had both the  stony habitat and crayfish this
snake requires.
            Comparison of Analytical Data with MEG Values—
                        Terrestrial Environment
    Analytical data for fugitive dust, fly ash, and raw coal sampled in
the study area have been converted  to the units used in the Multimedia
Environmental Goals (MEG) study (Cleland and Kingsbury, 1977a and b).
These data are compared with the estimated permissible con-
centrations (EPC's) and/or the minimum acute toxicity effluent (MATE)
values.
    Average concentrations of 15 elements analyzed in the fugitive dust
from the study area are compared with the EPC'c for air in Table 1.
Because most of the fugitive dust appeared to emanate from the coal
storage pile and decline in concentration within 200-300 m downwind
(Figure 4), the data have been averaged for the sampling sites located
between 150-175 m and 400-1800 m downwind from the coal pile.  The fugi-
tive dust concentrations for the upwind "control" sampling location are
also provided.  These field data are followed by the appropriate maximum
EPC's for air recommended for each element to prevent negative effects
to humans or the surrounding environment during continuous long-term
(chronic) exposure.  A difficulty in making comparisons between observed
and recommended levels of the 15 elements shown in Table 1 is that three
EPC's for human health and 10 EPC's for the environment are not
available.
    Average concentrations for three of the elements (As,  Cr, and Pb)
analyzed in fugitive dust exceeded the EPC's for human health.  These
values have been underlined in Table 1.  It is noteworthy  that two of
these elements (As and Cr) had concentrations above the health-based EPC
even at the upwind "control"  location.

                                    26

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N>
                                                                                Future
                                                                                Coal  Refuse
                                                                                Site
   Primary
   Ambient
  Air Quality
   Standard
  (75yu.g/m3)
                                 500
             1000
Meters  From Coal Storage  Pile
1500
2000
              FIGURE 4.  FUGITIVE DUST CONCENTRATIONS COMPARED TO A TRANSECT OF THE AREA'S
                         TOPOGRAPHICAL RELIEF

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                     TABLE  1.    COMPARISONS  OF EPC VALUES  FOR AIR  WITH  HOMER  CITY  FUGITIVE  DUST DATA
00
Trace Element Concentrations, gg/m
As Cd Cr Cu Fe Pb Mn Hg Ni Ti Zn Cl
F V Se
Distance from ' y *
Coal Pile Average Concentration in Fugitive Dust During 3 Campaigns at Homer City (24-hr Sampling Periods)
Downwind 150-175 m(b> 0.014 0.008 0.026 0.292 3.45 0.586 0.076 0.00056 0.015 0.44 0.35C1' 1.97(l'
Downwind 400-1,800 m(c) 0.010 0.014 0.015 0.119 1.87 0.334 0.093 0.00009 0.013(1)0. 32(i) 0.22 0.82
L'pwind Control(d) 0.009 0.005 0.014 0.223 1.65 0.258 0.041 0.00003 0.009 0.17(1) 0.13 1.05
KPC Category Estimated Permissible Concentrations (EPC's) e , Mg/m
Health 0.005 0.12(f 'o.002(f 'o. 5 — (h) 0.35 12 16(f) 0.04tf)]4 9.5
(R) (K) C E )
Ecology. — 0.04 f — — — 1 — 0.01
5.47 NI)(i' (1.0049
2.01 Nn n.on2ft(l)
1.40 o.o2(l^ n.nn3o'
1.2 n.-)
o.i n.rn
(a) All data were collected between December 1976 and April 1977.
        (b)  Average for  sampling sites  1 and 3; downwind of coal  pile.
        (e)  Average for  sampling sites  4, 8, and 9;  downwind of coal pile.
        (d)  Sampling site 6; upwind of  coal pile about 1600 m and off of the pover station property.
        (e)  From Cleland and Kingsbury  (1977a and b).
        (f)  Based on ,-i Toxic Limit Value (TLV) which  recognizes the element's carcinogenic potential (Cleland and Kingsbury, 1977a and  b).
        (R)  Based on teratogenic potential  (Cleland  and Kingsbury, 1977a and b).
        (h)  Not available.
        (i)  Concentrations were not available for some sampling sites during all three campaigns.
        (i)  N'D = not detectable.

        Note:   For  ease  of making comparisons,  EPC values which are used for  making comparisons and the  field data which exceed them are underlined.

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    Maximum and minimum concentrations of 15 elements analyzed  in
fugitive dust are compared with the appropriate EPC's for soil  in Table
2.  Again, the data are grouped to include sampling sites less  than
200 m (i.e., 150-175 m) and greater than 200 m (i.e., 400-1800  m)
downwind of the coal pile.  Concentrations of the same elements in the
raw coal are also shown. EPC's for protection of human health and the
environment are given for 12 elements; no EPC values for iron,  chlorine,
and fluorine have been determined.
    The majority of the elements analyzed showed maximum and  frequently
minimum concentrations in the fugitive dust that were far greater than
the EPC levels suggested for the soil.  Ten elements exceeded the EPC's
for human health and 11 elements exceeded the EPC's for the environment.
Both the maximum and minimum concentrations of 8 elements (As,  Cd, Cr,
Cu, Pb, Mn, Ni, and Se) in the fugitive dust exceeded the EPC's for both
human health and the environment.
    Obviously, the concentrations of toxic trace elements in  fugitive
coal dust that has settled to the ground does not mean that these same
concentrations occur in the soil.  However, studies involving soil
contamination by other types of particulate deposition have shown that
toxic trace elements in these particulates can cause ecosystem  dis-
ruption resulting in the loss of essential nutrients and can  also result
in increased concentration of these toxic elements in both plants and
animals. These types of effects have been demonstrated for lead smelter
emissions (Jackson and Watson, 1977; Kerin, 1975) and for fly ash emis-
sions from coal-fired power plants (Furr, et al., 1977). Dvorak, et al.
(1978), have speculated that long-term exposure to uncombusted  coal dust
may cause changes in vegetation community structure similar to  those
caused by particulates from coal combustion.
    Mechanisms for the movement of toxic trace elements from  particulate
emissions deposited on the ground to the root zone of the soil  are
complex (Vaughan, et al., 1975; Dvorak, et al., 1978).  A partial list  of
the factors which influence leaching of trace elements from deposited
particulates into the soil solution include (1) the size and  type of
particulates; (2) the amount and acidity of precipitation; (3)  the
concentrations and physicochemical properties of the trace elements;
                                    29

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                     TABLE 2.   COMPARISONS  OF  EPC  VALUES  FOR SOIL  WITH HOMER CITY  FUGITIVE  DUST  DATA
       M.i:< i mum


       Mini mum
                           As
                                   Cd
154


 11
264


 18
                                                                     Trace Element Concentration,  ufc/g
                                           Cr
                                                    Cu
                                                               Fe
                                                                         n
                                                                                  Mn
                                                                                                 Ni
                                                                                                         Tl
                                                                                                                   Zn
                                                                                                                              Cl
                                                                                                                                                        Se
                                          471
Concentrations in Paniculate at Sampling Sites within  200 n of Hrmer City Coal  Pile  (Sites  1 and 3)

                                                                            39,081

                                                                             4,043
J3,_6_78

  336
28,736

 6,223
17,241

   501
632

 65
3^

0.2
264

 23
                                                                                                       8,676
                                                                                                         626
3,563
   ,
o
       HIM 1th
                            10

                             2
                                                                    Estimated Permissible Concentrations  (EPC's) for Soil
          0,06(c) 0.01(C)  200
                                        70(C)   10
                                                                                        50
                                                                                          (c)
          0.01(d)10
                                                     20
                                                                        17

                                                                       aea
                                                                                                                 1.000
                                      Raw Co.il Concentrations Determined  by  Individual Analysis of Three Homer  City Coal Sources

                                     0.26   35        31     48,750         17.3
                                                                                                                               (e)
                                                                                                                             fe)
                                                                                                                             v-
                                                                                                                                          {e)
                            22
                                    <0.1
                                            30
                           n     48,750

                           20     18,000
                                                                           12
                                                _74     1.1     16.1    1,329        66      0.26

                                                35     0.34    12.»    1,125        46      0.23
                                                                                                                                                15
                                                                                                                                        ins     fo

                                                                                                                                         91     55
            Data from three sampling campaigns conducts : by Battelle in the study area.
            t rum CK'l.ind and Kingsbury  (1977a and b); all values  were multiplied by  100 based  on personal  communication with Kingsbury  (August, 1978).
            Based on i-ari-inoRi-ntc  potential  (Cleland and Kingsbury,  1977a and b) .
            Ba-;..<) on tur.itoni'niv  potential  (Cleland and Kingsbury, 1977a and b).
            Value mil available.
            ND = not Lk t ei-1 ab )u .
            Coal sources include:   Helen Mining Company and Helvetia Coal Company  (from Upper  Freeport Seam);  and trucked-in coal (from Lover  Kittanning S^am).
        Note:  For ease  of making comparisons,  EPC  values which are used for making comparisons and  the field data which  exceed them are underlined.

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(4) the texture, organic content, pH,  and other characteristics  of  the
soil; (5) the solubility of elements in the soil solution;  and (6)  the
temperature of the air and soil.
    The fugitive dust quantity and composition found during monitoring
have probably been accumulating on the ground in a reasonably similar
fashion since the power plant (including the coal storage pile)  began
operation in 1969.  Thus,  mobile elements in the settled dust may have
leached into the soil.  The quantity of toxic trace elements available
to vegetation, hjwever, needs to be determined by chemical  analysis of
the soil. In spite of any leaching of  trace elements that may have in-
creased soil concentration, the vegetation for some distance from the
coal pile has not yet shown any adverse effects that were readily
apparent during Battelle's field reconnaissance. An analysis of  soil
biota and plant diversity, however, was not conducted.
    Another basis for comparison is also possible; MATE values for
components in solid wastes have also been developed. Inasmuch as the
deposited fugitive dusts are tantamount to being a solid waste and these
deposits may contact or be absorbed or consumed by plants and animals,
comparisons with MATE values for solid wastes would appear to be valid.
Such a comparison has been made in Table 3.  The table's structure is
similar to that of Tables 1 and 2.
    In Table 3, the appropriate MATE values are judged  to be the ones
related to ecology limits.  In general, these have lower values  than
thoce for health; exceptions are mercury (Hg), chlorine (Cl), and
fluorine (F), the latter two for which there are no ecology values
available.  Twelve of the fifteen MATE values for health are exceeded by
the maximum values for both the close  in (>200 m) and the more remote
(<200 m) sampling sites.  Eleven of the ecology values  are  exceeded.
Comparisons of solid waste MATE values with the elemental concentrations
in the raw coals are also provided in  Table 3.  Elemental concentrations
in the raw coal exceed many of the same elemental EPC values exceeded by
elements in fugitive dust.  However, the levels of toxic elements in the
raw coal are generally lower than the  levels in the fugitive dust.
                                    31

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    TABLE  3.    COMPARISONS OF MATE  VALUES  FOR  SOLID WASTE  WITH HOMER  CITY  FUGITIVE  DUST  DATA
Trace Element Concentration, UR/R
As Cd Cr
Cu
Fe Pb Mn Hg Ni Ti
Zn Cl F V Se
Concentrations in Paniculate at SanplinR Sites within 200 m of Homer City Coal Pile (Sites 1 nnd 3)
Maximum 154 264 471
3,678
28,736 17,'241 632 3 264 S.676
Minimum 11 18 18 336 6.223 501 65 0.2 23 626
Concentrations in Particulate at Sampling Sites Between 200 and 2,000 m of Homer
Maximum 238 619 667
Minimum 3A ND 46
U>
S3
Health 50 10 50
Ki-oloRv U) 0.2 50
Raw Coal
Maximum 48 0.26 35
Minimum 22  --<"> 30 5
(ol
Coal Sources *'
66 0.26 108 65 til)
46 0.23 91 55 ND

(a)  Data from three sampling campaigns conducted by Battelle in  the study area.
(b)  From Cleland and Kingsbury  (1977a and b); all values were multiplied by 100 based on personal  communication with Kingsbury (August,  1978).
(c)  HATE values listed are  for  ferrous (Fe+2)_Or ferric (Fe+3) (Cleland and Kingsbury, 1977a  and b).
(d)  MATE value listed is for  chloride ion (Cl ) (Cleland and Kingsbury, 1977a and b).
(e)  Value not available.
(f)  ND « not  detectable.
(g)  Coal sources include:  Helen Mining Conpjiny and Helvetia Coal Company (from Upper Freeport Seam); and  trucked-in coal  (fr™ Lower Kittanninp
(h)  MATE value listed is for  fluoride Ion (F ).


Note:   For ease of  making comparisons, MATE values which are  used for making comparisons and the field data which exceed them are underlined.

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                          AQUATIC ENVIRONMENT

                      Water Quality Determinations

    The water quality study was designed to obtain data on the nature
and characteristics of the water resources in the vicinity of the Homer
City power complex prior to the operation of the coal preparation facil-
ity. The study was directed toward the establishment of some perspective
as to the trends and cause/effect relationships and physical/chemical
interactions between the existing land-use activities and the present
water quality on and around the facility site.
    Because water quality varies over time as well as area, a short-term
grab-sampling effort such as that conducted at Homer City can provide
only a hint as to the long-term (annual or longer) trends, even when
supplemented by data from previous studies.  Also, an additional com-
plication is introduced by the fact that the study area has been in a
state of flux. Major alterations to power plant effluent treatment
systems and changes in regional land use have made most of the histor-
ical data obsolete or usable only with caution.  The approach used was
to determine the effects of each of the land uses on water quality,
first additively and tnen in conjunction.
    Sampling was conducted during three periods:  December 14 through
19, 1976 (Campaign I); March 1 through 3, 1977 (Campaign II); and April
20 through 22, 1977 (Campaign III).  Analytical results for 30 water
quality and 9 sediment quality parameters selected for analysis in the
streams and tributaries in the study area subsequently were used for
comparison with 30 MEG values (Figure 5).

Location of Sampling Sites

    Whenever possible, a sampling point was located at a point where
historical data were available, either from previous environmental or
engineering studies or as a requirement of the National Pollutant
Discharge Elimination Systems (NPDES) permit for the Homer City power

                                    33

-------
A
B
C
D
E
F
G
H
Ash Disposal Area
Mine Drainage  Treatment Pond
Helvetia Boney Pile (at mine)
Coal  Cleaning Plant
Coal  Storage Pile
Power Plant
Industrial  Waste Treatment Plant
Helen Boney Pile (at mine)
        FIGURE 5.   STREAMS  AND  TRIBUTARIES SURVEYED IN  THE
                     HOMER CITY AREA
                                    34

-------
plant.  As previously stated, these data were generally less com-
prehensive than desired, and in several cases .they have been made ob-
solete as a result of changes in power plant operating status.   The
locations of the sampling sites for surface water and sediment  samples
are shown in Figures 6 and 7, respectively.

Selection of Parameters

    Pollutant parameters were selected on the basis of one or more of
the following criteria:
    •  Relevance to particular land uses known to be' important  in the
       various watersheds around the plant
    •  Inclusion in previous water quality surveys at Homer City Station
    •  Appropriateness to EPA Level I assessment needs
    •  Presence in the source coal or in the ash
    •  Inclusion in NPDES monitoring data
    •  Suspected or known toxicity
    •  Likelihood of being present in any discharges from the coal
       cleaning plant or associated process areas.
    Parameters selected are listed in Table 4.   Not all parameters were
monitored at every site during each campaign. In connection with
parameter selection, analyses of the source coal and ash were made which
confirmed that an appropriate set of parameters had been selected.  The
results of these analyses are given in Appendix C.

                           Land Use Analysis

    Because the watersheds at Homer City are already influenced by a
number of land uses (see Table 5) other than the proposed coal  pre-
paration plant, a cause/effect matrix was developed on the basis of the
expected interactions between the land use class and the water  quality
(Table 6).  A set of five major land use classes were identified—
agriculture, mining, urban, construction, and power generation.  Power

                                    35

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A
B
C
D
E
F
G
H
Ash Disposal Area
Mine Drainage Treatment Pond
Helvetia Boney Pile (at mine)
Coal Cleaning Plant
Coal Storage Pile
Power Plant
Industrial Waste Treatment Plant
Helen  Boney Pile (at mine)
  P =  partial data analysis
  H =  sampling site  identifier
CDE =  sampling site  identifier
  F =  sampling site  identifier
 Cherry Run
 Reservoir
                                                                      Identity
                                                                      Code for
                                                                      Sampling'
                                                                      Sites
               FIGURE  6.  SURFACE WATER QUALITY SAMPLING LOCATIONS
                                        36

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A
B
C
D
E
F
G
H
Ash Disposal Area
Mine Drainage Treatment Pond
Helvetia Boney Pile (at mine)
Coal Cleaning Plant
Coal Storage Pile
Power Plant
Industrial Waste Treatment Plant
Helen Boney Pile (at mine)
    H =  sampling site  identifier
  CDE =  sampling site  identifier
    F =  sampling site  identifier
Cherry Run
Reservoir
                                                 __.    Identity <
                                                 17 D  code for
                                                        sampling
                                                        sites
      FIGURE  7.   STREAM SEDIMENT  SAMPLING LOCATIONS(a)
                                37

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TABLE 4.  WATER QUALITY PARAMETERS—HOMER CITY RECONNAISSANCE SURVEY
          Parameter
                                          Parameter
                (a)
         Arsenic
         Beryllium
         Calcium
         Cadmium
         Chromium
         Chromium, hexavalent
         Copper
         Iron, total
         Iron, dissolved
         Iron, ferrous
         Lead
         Magnesium
         Manganese
         Mercury
         Nickel
         Potassium
         Sodium
         Vanadium
         Zinc
pH
Acidity
Alkalinity
Sulfate
Chloride
Fluoride
Suspended solids
Dissolved solids
Total solids
Volatile solids
Sulfide
Ammonia nitrogen
Kjeldahl nitrogen
Nitrate Nitrogen
Nitrite nitrogen
Total phosphorus
Phenolics
C.O.D.
T.O.C.
Specific conductance
Oil and Grease
(a)  Dissolved heavy metals and nonmetals were measured at a limited
     number of stations during campaigns II and III; total metals and
     nonmetals were monitored at all stations.
                                 38

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               TABLE 5.  LAND USE INFLUENCE ON  STREAM WATER QUALITY  AT HOMER  CITY POWER COMPLEX
VO
	 • 	 • 	 • 	 — 	 . 	 . 	 . 	 : 	 . 	 . 	 : 	 . 	
\ Land Use
Basin \v
Cherry Run - Main Stream
Cherry Run - North
Tributary
Cherry Run - South
Tributary
Wier's Run
Common Ravine
Second Ravine
Two Lick Creek

Power Generation
i-
. c cu ao H a) a)
<" 2 , 4J e to C* cc  JJ 4JQJ4JSH) U 0 M c IS
4-; y CJJCM-'-IO-O-HW
^ ^. 3 aJtdQJOOM 3 to 4-1 n)O
•* 5P „ I-1 BSBCrt rH -H in ^ ii
t> C e 4J V * ^(c) (b) (b)
* T«+ O O *
* + *
**** +** + +(b> *
     (a)  *  Indicates a land use  having a major influence on water  quality.
          +  Indicates a land use  having a minor influence on water  quality.
          o  Degree of influence on water quality is unknown.

     (b)  Indirect interaction via industrial waste treatment  facility.

     (c)  Intermittent accidental  discharge.

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TABLE 6.  CAUSE/EFFECT MATRIX OF LAND USE CONTRIBUTIONS TO
          WATER QUALITY PARAMETER VALUES
	 	 	 __ 	 	 — . 	 . 	 	 	 • 	 • 	 — — 	 	 ' 	 • 	 • 	 — — 	

\
\
\
\

\
\ Activity
\
\

Index \
Parameter \ 	
pH
Acidity
Alkalinity
Sulfate
Chloride
Fluoride
Susp. solids
Diss. solids
Total solids
Volatile solids
Sulfide
Ammonia nitrogen
Kjeldahl nitrogen
Nitrate nitrogen
Nitrite nitrogen
Total phosphorus
Phenols
Oil and grease
C.O.D.
T.O.C.
Specific con-
ductance
Arsenic
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Zinc
Vanad ium
Beryllium
Iron, total
Iron, dissolved
Iron, ferrous
Calcium
Sodium
Magnesium
Manganese
Temperature
Power Generation


c
QJ O
J-4 T"l
3 4-t

3 6C 1-
0 C w C
'H -H C/J CO
U C C J3
4f 5 5 £
x . x
X
x x
x x
X
X
X XX
x x x x
XX X
X XX
X
X x
X "
X XX
X "
X XX
X
X
xxx
X XX
xxx

X
X
X
X
X
X
X
X
X
X
X X
X
X
X X
X
X
X

c
OJ
6
iJ Ui
(TJ OJ
1 U 4J
^ ra c
t- 3 
-------
generation is further separated into water treatment (and associated
sludge disposal), wastewater treatment (industrial and domestic),
cooling water discharge, blowdown discharge, ash sluice overflow, ash
disposal, coal storage, and oil drainage and storage.  The types of pol-
lutants associated with each land use class are described in Appendix C.
In attempting to trace the fate of pollutants from these activities, the
pollutant parameters ideally should be mutually exclusive for each.  The
monitoring of water quality in a watershed containing a number of pollu-
tion sources should resolve the origin of the pollution.  Land use
patterns, and thus contributions, to study site streams are presented in
Table 5.
    The water chemistry of the streams in the vicinity of Homer City was
examined as it relates to the solubility of important elements and ions
and the susceptibility of these streams to changes in water quality.  In
addition, chemical analysis results were acquired for the U.S.
Geological Survey hydrologic and water quality benchmark station on
Young Woman's Creek near Renovo, Pennsylvania (Table 7).  Benchmark
stations are located in undeveloped drainage basins in the major phys-
iographic regions of the country.  Renovo is approximately 85 miles (136
km) northeast of Homer City.  Although this station is located in the
Susquehanna River Basin rather than in the Ohio River Basin, the topog-
raphy and lithology of this area are very similar to those in the
vicinity of Homer City.   (See Appendix C for physical descriptions of
drainage basins in the Homer City area.)
    The monitored parameters for Cherry Run Basin, Wier's Run, Common
Ravine/Second Ravine, and Two Lick Creek have been classified into three
groups according to their interactions and significance—solubility
controlling species, toxic materials, and solids and nutrients.  Anal-
ysis results for the three groups of parameters are discussed below.
Detailed data are presented in Appendix B.
                                    41

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         TABLE 7.  CHEMICAL ANALYSIS—WATER YEAR 1973 YOUNG WOMAN'S
                   CREEK NEAR RENOVO, PENNSYLVANIA


Discharge, cfs
SiOoi PPm
Ca, dissolved, ppm
Mg, dissolved, ppm
Na, dissolved, ppm
K, dissolved, ppm
Alkalinity, ppn as CaC03
304, dissolved, ppm
Cl, dissolved, ppm
F, dissolved, ppm
N03, ppm
N02 , ppm <
TP, ppm
TDS, ppm
Hard, total, ppm
Specific conductance, umhos /era
PH
Temperature, c
D . 0 , , ppm
Fe, total, ppb
Mn, total, ppb
As, total, ppb <
Cd, total, ppb
Cr, total, ppb <
Cu, total, ppb
Pb, total, ppb
Hg, total, ppb <
Zn, total, ppb <
Suspended solids, ppm
TOC, ppm
Annual
Average
108
3.8
3.9
1.0
0,9
1.2
5.8
7.3
1.4
0,1
0.025
0.01
0.01
27
22
39
6.2-6.9
9.7
11.4
180
30
1
0
10
0
2
0.5
3
6
C.5
December - April
Average
156
3.6
3.5
1.0
0.8
1.3
3.8
7.5
1.8
0.1
0.29
N.D.
0.01
26
22
37
6.2-6.9
4.5
13.0
20
20
< 1
0
< 10
0
1
< 0.5
0
5
N.D.
Source: U.S.  Department of the Interior,  1974.

                                  42

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                            Cherry Run Basin

    For reference purposes,  the  locations  of the  sampling sites on  the
main portion of Cherry Run  and on  the  two  small  tributaries are shown in
Figures 8 and 9.

Solubility Controls

    Parameters included in  this  classification were  iron  species, sulfur
species, manganese, calcium, alkalinity,  acidity, and  pH  (Figure  10).
    The water quality  at most of the sites was influenced by  the
solubility limits for  iron  and manganese,  which  are  both  strongly
controlled by pH.  At  equilibrium, both ferrous  and  dissolved iron
should be at or below  the detection limit  of the  analysis at  pH values
above 6.  The iron and manganese relationships are especially relevant
for Campaign I, which  was characterized by low temperatures,  high
dissolved oxygen levels, and a solute  transport  mode in the form  of
snow-melt runoff.  Significant quantities  of ferrous iron were found at
Sites HI, H3, and CDE1, and lesser amounts at the other sites. No
active mines are known to be presently discharging to  either  Cherry Run
or the north tributary above the sampling  locations.  The source  of the
iron was not apparent  but may be historical.
    Site CDEl below the emergency holding  pond and siltation  ponds
receives runoff from the construction  area around the  coal  preparation
plant, and surface and subsurface drainage from  a portion of  the  coal
storage pile.  The water quality at this site was therefore influenced
even more strongly by  iron  and manganese chemistry than was the water
quality at the other sites.
    A limited number of groundwater samples were obtained upgradient of
the surface water site CDEl.  Station CDE5 is located just  below  the
coal storage pile in a manhole accessing the lateral sewers constructed
to control water migration  through the coal pile. Station  CDE7,  an
industrial water well, located  further to the west and slightly north  of
the coal pile, receives inflow from the area around  the coal  preparation
plant and possibly from the coal mine mouth area. The exact  direction
of groundwater flow on this side of the coal pile has not been

                                   43

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                                                          Legend

                                                   A  Refuse  disposal area
                                                   B  Coal pile
                                                   C  Coal cleaning  plant
                                                   D  Coal pile retention ponds
                                                   E  Substation
                                                   F  Burial  yard
                                                   O  Surface water  sample
                                                      Groundwater  sample
                                                      Sediment and surface  water  sample
   SITES

 1.  HI
 2.  H2
 3.  H3,  HA
 4.  Partial
 5.  H5
 6.  H14, HIS
 7.  H16, H17
 8.  H13
 9.  H7
10.  Hll
11.  H10
12.  H9
13.  H8
14.  CDE1, CDE2
15.  H6
16.  CDE8
17.  CDE7
1R   T.DE5
FIGURE 8.    CHERRY  RUN  SAMPLING  LOCATIONS—CAMPAIGN  I

                          44

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                                                        Legend
                                                 A  Refuse disposal area
                                                 B  Coal pile
                                                 C  Coal cleaning plant
                                                 D  Coal pile retention ponds
                                                 E  Substation
                                                 F  Burial yard
                                                 O  Surface water sample
                                                    Groundwater sample
                                                    Sediment and surface water sample
 1.  HI
 2.  H3, HA
 3.  H13
 4.  H14, H15
     H7
12.  CDE1, CDE2
13.  H8
14.  H6, H12
                 FIGURE 9.    CHERRY RUN SAMPLING LOCATIONS—CAMPAIGNS II
                             AND III
                                            45

-------
 •rl
 C
 32
 (X
7

6

5

4

3
JU
40
30
20
10
—
•M


••••
-n-

rrfT 	 =Hl-r-^n j-i n-
••M
—
B
                             Vertical Scale
                                   X6
z/u
240
210
180
150
120
90
60
-
-
-
1m-.THT
••M
-
MM
••••

-
—
•••

—
•••
-
-
MM

—
••••



r-rrr
«••


•••


-Itv
t>0
e
j . ^
2.8
2.4
2.0
1.6
1.2
0.8
0.4
0
-
—
-
^M


^ I
^•B
P
i i in: IE
HI H3


— 1 — p/ifff -i —
\
6t
K^ Dissolved Iron
I
1

ill
Ei inm i n m. i n
H6 CDEl H8
i r i
-i rm ,
;~hLLL,
M IETH inm inm
H7 H13 H14
North Main South
Tributary Stem Tributary
Main
Stem
       FIGURE 10.  HISTOGRAMS  OF SOME IMPORTANT SOLUBILITY CONTROLLING
                   INDICATOR SPECIES  IN  CHERRY RUN BASIN
              I = Campaign  I,  II =  Campaign II, and III = Campaign III in
              all histograms shown  above the Roman numerals.
Note:
                                      46

-------
determined with precision.  There is a close correlation between the
shallow groundwater quality and surface water quality at CDE1.   Modest
amounts of dissolved oxygen (2.5-6.8 mg/1) are present and prevent the
build-up of sulfides, in the near-surface groundwater.  However,
sulfides may be formed in the deeper percolate.  The pH of these ground-
waters is low enough to maintain the extremely high concentrations of
iron and manganese observed.  The combination of low alkalinity  and high
sulfate means that none of these samples is saturated with respect to
calcium carbonate (as calcite), but most of the time they are saturated
with calcium sulfate.  Usage of the well water is very limited.  Little
is known about the amounts of surface or groundwater reaching Station
CDE1 from these wells or from the coal pile.  As the coal preparation
plant site returns to a stable condition, the northwest corner  of the
coal pile will likely be regraded to cause the surface runoff to
discharge into the desilting basins on the south side of the pile.
These channels have become blocked due to earth moving during
construction and because of mass-wasting from the coal pile.
    Surface water quality in this area was found to be typical  of Class
II mine drainage in which a portion of the ferrous iron has been
oxidized.  The low pH in these samples effectively maintained the levels
of soluble and ferrous iron observed.  As this water oxidized and mixed
with water from the south refuse area tributary, ferric hydroxide and
occasionally calcium sulfate were in saturation equilibrium with their
respective solid phases.
    The south tributary also has been the receptor for runoff from the
construction of siltation and treatment ponds for the refuse disposal
area. Site H8 was relocated after the first campaign upstream to a point
just below the discharge from the coal refuse disposal construction
area.  The result of this relocation was the isolation of the effects of
this activity from the coal pile and plant site runoff.
    Total iron increased markedly during Campaign II, presumably as a
result of erosion or stream scouring.  This is supported by the  fact
that the increase is entirely in the particulate fraction.  Neither
alkalinity nor suLfate concentrations were notably affected by the

                                     47

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drainage from the back pond area.  Sulfate concentrations are already
high upstream of the leachate pond construction area.  The source of
this sulfate was not determined.
    Downstream water quality in this tributary is improved by the inflow
of water from a series of seepage springs.  The springs contribute 9 to
20 percent of the flow from the south tributary.  These springs had the
best water quality in Cherry Run Basin and approach the quality of the
reference stream.
    Below the confluence of the south tributary with Cherry Run itself,
the water quality shows no effects of the land use activities along the
south tributary.  The quality of the water below the confluence is equal
or superior to that of the upstream water with respect to iron,
alkalinity, pH, and sulfates.  Water at Site H14 is nearly in
equilibrium with CaCC>3.
    Several mine discharges located on Cherry Run about 0.7 km upstream
of the discharge to Two Lick Creek resulted in the reintroduction of the
iron and sulfate which had been previously removed by precipitation
and/or reduced in concentration by uncontarainated inflows.
    One final point concerning the influences of any future development
on the pH of Cherry Run or its tributaries relates to the buffer capac-
ity.  Buffer capacity at all of the stations was highly variable and
generally low, primarily because of the lack of natural alkalinity
(Figure 11).  Discharges of low-pH water from either the emergency
holding pond or accidental spillage from the sedimentation or treatment
pond for the refuse leachate will have a relatively adverse impact on
Cherry Run water quality in view of the existing conditions.

Toxic Materials

    The trace metals and nonmetals, phenolics, and biodegradable
organics are included in the Toxic Materials group. On the basis of
theoretical considerations, it was not expected that analyses would show
significant concentrations of any heavy metals at any distance from a
source because of solubility and adsorption phenomena.  Aqueous levels
of total metals/nonmetals were found to be very low.  Zinc was detected
                                    48

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   0.8f—
    0.6
 o-
 o>
    0.4
o
o
a.
o
o
I
CD
0.2
   O.O
           i H nt

             H3
                      n m

                     H6
i  n nr

  H8
i  n in
CDE i
x  n  m

  HI3
n m
HI4
                                    Sampling Station




                   FIGURE 11.  BUFFER CAPACITY--CHERRY RUN




         Note:  I = Campaign I, II = Campaign II,  and III  = Campaign  III  in

                all histograms shown above the Roman numerals.

-------
the most frequently; cadmium, nickel, copper, and chromium only occa-
sionally; and mercury, arsenic, vanadium, beryllium, and lead rarely.
This trend appears to be the result of the level in the source coal and
the solubility/adsorption/volatility behavior of the metal.  For
example, 47 to 69 ppm zinc was present in the coal samples tested.  Zinc
is  also relatively soluble at pH values below 7.0 and thus was found in
solution more frequently than cadmium or lead, which were at much lower
concentrations in the coal and generally form more insoluble complexes.
    Despite their low solubility, metals can become mobilized via a
number of mechanisms, physical, chemical, and biological.  As conditions
change moving downstream, coprecipitation and adsorption are the primary
modes  by which trace metal ions are again made immobile.  The result is
an accumulation of these metals in the sediments.  In the Cherry Run
Basin, metals were most often found at Site CDE1.  Levels of nickel and
zinc are the only ones which were considered higher than the analytical
detection levels.  The trace metals tend to behave similarly to iron,
manganese, and sulfate in that the effects of activities along the south
tributary are very local and do not extend downstream into the main stem
of Cherry Run.  Metals were never detected at Site H14.  The physical
form of the metals found at Site CDE1 was also of interest (see Table
8).  Samples from Campaigns II and 111 were filtered on site and tested
            TABLE 8.  FORM OF TRACE METALS IN WATER SAMPLES
                      OBTAINED AT  SITE CDEl59
>6000
       (a)  Values  in mg/1.
       (b)  Equilibrium assumed.
       (c)  n.d.  =  not detectable.
                                    50

-------
for dissolved metals.  In every case all of the total metals found in
the samples were in the dissolved fraction.
    These observed values are compared with the expected values on the
basis of solubility.   It is obvious that these dissolved metals cannot
be in equilibrium with the metal oxide or hydroxide solid phase at this
pH. Adsorption must therefore play an important role in the accumulation
of metals to the observed concentrations.
    Since adsorption takes place at surfaces, the surfaces present were
characterized by their organic content and particle size distribution.
 The mineral sediment at most monitoring locations consisted of sand and
gravel.  The downstream sites (H14 and H16) also contained some silty
organic material.
    The iron and manganese content of these sediments is perhaps the
most significant fraction in that several investigations have documented
the  effect of hydrous iron and manganese oxide precipitates on trace
metals.  Judging by the large amounts of iron and manganese in the
sediments, it is believed that precipitation of these two metals
constitutes one of the major mechanisms for removing the trace toxic
metals from solution.  As these floes, which are composed of compounds
of iron, manganese, and trace metals, settle to the bottom and age, water
is squeezed out and compression settling takes place.  The metals held
in the interstices of the floe are then effectively immobilized unless
the floe is dissolved by an acid discharge or resuspended and physically
transported.  This latter possibility may be important for dispersion of
the metals but could not be investigated in detail.
    Specific toxic organic pollutants in Cherry Run were not identified
in the preoperational monitoring.  Simple (Level I) analytical screening
tests exist for only one class of organic compounds, namely  the
phenolics.  Phenolics have been found to be  toxic  to  some aquatic life
at levels in excess of 200 yg/1.  The maximum concentrations observed
were an order of magnitude lower  than the water quality  criterion for
phenolics (Figure 12).
                                    51

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Ln
ho
                  00
                  g
                  o
                  H
                  00
                  6
                  G
                  O
                  U
                    12
                     11  -
                     10  -
                      9  -
                      8 -
                      7 -
                      6 -
COD
Detection  5 ~
Limit
TOC
Detection  1 ~
Limit
0
                   a
                                                            Legend

                                                       O  Phenols

                                                       D  COD

                                                           TOC
                               r~
                              HI
                         —r~
                         H3
                    H6
-i	1	1	r-
 H8   CDE1  H7    H13
                                                                        T
                                                                    T
                                                                                  - 0.035
                                                                                  - 0.030
                                                                                  -  0.025
                                                                                  -  0.020
                                                                                   -  0.015
                                                                                   -  0.010

                                                                                            Phenol
                                                                                     0.005  Detection
                                                                                            Limit
                                                                                   o
                                                                                   c
                                                                                     0
H14   H16
                      FIGURE 12.  PHENOL, COD, AND TOC CONCENTRATIONS AT VARIOUS
                                  LOCATIONS IN THE CHERRY RUN WATERSHED

-------
    The organic loading data suggest that these streams have a fairly
low organic load on a steady-state basis and that some of  the COD  is
contributed by the oxidation of ferrous iron to ferric iron and of
manganous (Mn~*"2) ion to manganic (MN~™) ion.  An extensive deter-
mination of the assimilative capacity of Cherry Run was not performed.
However, the dissolved oxygen saturation levels in the streams were
always greater than 70 percent at all locations.

Nutrients and Solids

    In the final category of pollutants are the nutrients  and solids.
Included in this classification were nitrogen species; phosphorus
species; organic carbon;  and suspended, volatile, dissolved, and total
solids.  Figures 12, 13,  and 14 depict these indicators.
    Although nutrients were identified in the approach section as  being
associated primarily with agricultural land-use activity,  some ammonia
can be contributed from predominantly industrial sources.
    None of the measured  ammonia concentrations were high  enough to be
considered toxic.  The maximum ammonia concentration was 0.19 mg/1
NH3~N at a pH of 3.8.  The water quality criterion for ammonia
nitrogen was not exceeded.  Ammonia is rapidly assimilated by the  stream
and within a few hundred  meters (H8) was below the detection limit.
    Concentrations of ammonia were independent of flow.
    Nitrate behaved much differently from the ammonia.  The influences
of the agricultural land  use to the north were apparent in the values at
HI and H3.  The concentrations remained high at H1A, primarily because
of the pastureland along  the east bank.  A sample was obtained during
Campaign I at Site H5 to  characterize drainage from this land.  The
N03~N concentration of 7.0 mg/1 was several times greater  than the
nitrate values in any of  the other samples.  Nitrate also  showed a
marked dependence on flow, with the values during wet weather in
Campaigns I and II being  much higher than those during dry weather in
Campaign III.

                                     53

-------
  a oo
H §5
  x   0.05
  PU
Detec-   "*
tion Limit
                                                                         H14
                                                               Benchmark
      4-1 6
   Detec-  —
   tion Limit
           0.5 -
                  HI
        H3
                               H6
H8
CDE1
H7
H13
H14   Benchmark
Detec- -  -*
tion Limit
HI
                        inrmi  rn ZK  i nm  xinr  inrin:  i TLJH.  i ILIL
                         H3       H6      H8     CDE1      H7      H13      H14
                FIGURE 13.   CONCENTRATIONS OF PLANT NUTRIENTS AT VARIOUS
                            LOCATIONS IN CHERRY RUN WATERSHED
            Note:   I = Campaign I, II = Campaign II, and III = Campaign  III
                   in all histograms shown above the Roman numerals.

                                            54

-------
    180


    160


§  140


•S  120


f  100


1   80


     60


     40


     20
                   H3
                 H6
                                  H8
                                           CDE1
                                         H7
                                                           HI 3
                                                         H14
I
I
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00
                                                          H13
                                                         H14   Benchmark
   1600


   1400


   1200


   1000

    800

-------
     Nitrate  levels  were  also  influenced  by  agricultural  and industrial
 land usage in  the  south  tributary.   Elevated concentrations of nitrate
 were found in  drainage  (CDE1)  from  the emergency holding ponds and in
 drainage  (H6)  from  some  small  cornfields.   Hence, downstream nitrate
 concentrations  at H13 just  prior  to  the  discharge to  the main stem were
 also elevated.  Only during Campaign III did the nitrate value return to
 the  baseline values as defined by the benchmark station, probably
 because of reduced  transport  from adjacent  land uses.
     Construction and agricultural runoff control the  amounts of
 suspended and  volatile solids  in  these streams.  Although most of the
 fields have been contour plowed and  strip-cropped, some  erosion may
 still be occurring.  At the site  of  construction for  the leachate ponds,
 suspended solids increased significantly.   Here and at the other
 stations, there was a notable  decrease in suspended solids as the flow
 decreased.  At CDEl the suspended solids may be largely  iron hydroxide
 precipitate, which would remain suspended longer than silt or sand.  The
 high volatile  solids may, in fact, have been the result of loss of
 hydration water, but this has not been verified.
     The suspended solids in the south tributary do not settle until the
 juncture with the main stem at H14.   Concentrations of suspended solids
 in the Cherry Run basin approached those in the reference stream during
 Campaign III.  Total phosphate was quite low except at two locations-Hi
 and  H8.  Phosphate concentrations obtained at these sites are values
 probably associated with the solids  fraction and were caused by
 agricultural and construction influences, respectively.

                               Wier's Run

    Sampling  locations  for Wier's Run are shown in Figures  15
and  16.
                                    56

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            L...   \
                      -
/
/
/
1
1
1
1
I
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\
\
\
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V.
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Watershed
Boundary












•N
•

















\
\
\
\
\
\
\
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                                                         Legend
                                                  A  Ash disposal area
                                                  B  Boney pile
                                                  O  Surface water samples
                                                  ®  Ground water samples
                                                  •  Sediment and surface
                                                     water samples
         s
       /
                                             Two Lick Creek
FIGURE 15.  WIER'S RUN SAMPLING LOCATIONS—CAMPAIGN  I

                             57

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Watershed  /
Boundary
        Legend
A   Ash disposal area
B   Boney pile
O  Surface water samples
•  Sediment and surface
    water samples
        FIGURE 16.  WIER'S RUN SAMPLING LOCATIONS—CAMPAIGNS  II AND III

                                        58

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Solubility Controls

    Reactions involving alkalinity,  pH,  and the solubility of  iron,
manganese, and calcium are again significant in relation to the control
of leaching from the ash disposal area (Figure 17).   As the percolate
emerges below the ash dump, soda ash (Na2C03) is added to artifi-
cially raise the alkalinity and pH.   Water from these collectors and the
untreated water from a small pond flows into large settling ponds.
    The water quality just below the effluent weir showed that the iron
was primarily in a soluble form.  Also, ferrous iron constituted just
over 10 percent of the total iron.  As this effluent travels downstream
and achieves equilibrium, most of the soluble iron should precipitate
and the ferrous—ferric equilibrium should cause ferrous iron
concentrations to fall below the detection limit.  Manganese should
precipitate farther downstream.  In fact, this process was taking place
and ferric and manganic hydroxides were found coating the stream bottom.
    Just below the discharge point from the sedimentation ponds, a small
tributary enters Wier's Run from the west.  This tributary drains an
area used for agriculture and cattle grazing. No activities relating to
ash disposal or acid mine drainage occur in this subdrainage, and
consequently low levels of iron, manganese, sulfates, and calcium were
observed.  No ferrous  iron was detected.  Alkalinity and pH were higher
here but  still well below the saturation for  calcium carbonate.  The
volume  of flow was small at the time  of sampling and is annually
intermittent.
    About 0.4 mile downstream  from the  effluent weir, a tributary enters
from the  east.  This  stream was  sampled upstream at a point where it
exits  from Oak Tree Pond.  The  inflow to Oak  Tree Pond  is  a conduit
which  conveys  the  treated  Helvetia Coal  Company mine water  discharged
 from the  treatment  pond  indicated at  point  B  on the site  map  (Figures  15
and  16).  Lime  is  used to  add  alkalinity  to  the mine water and  precipi-
tate the  iron.  This  treatment  is generally  successful  as  evidenced  by
                                     59

-------
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the fairly low iron values;  however,  sulfates  are  not  removed  and
calcium is added.   This effluent was  occasionally  saturated  with calcium
sulfate, but very  little precipitate  is formed,  probably because of  the
short hydraulic residence time.
    At Site F17, the farthest downstream on Wier's Run,  sulfates have
been reduced only  slightly.   A layer  of ferric hydroxide coats the
bottom along this  reach of stream and calcium  carbonate  is sometimes
capable of being precipitated.  Flow  during Campaign III was measured  at
3.1 cfs.
    Buffer capacity in Wier's Run is  very much a function of both  the
alkalinity and pH  (Figure 18).  At F12 below the ash-retaining dike, the
alkalinity added by the Na2C03 and the pH near the first ionization
constant of carbonic acid buffers the water very effectively.  At  the
downstream station, the pH changes and the buffer capacity drops.

Toxic Materials

    As in Cherry Run Basin, the toxic materials concentrations were
never very high.  The most frequently detected metal was zinc, followed
by nickel.  Lead and cadmium were occasionally found but never at  a
discharge from a known metal source.   Apparently, the metals are held
very tightly in the ash matrix.  Analysis of the ash showed high con-
centrations of sulfide, and this may provide the mechanism preventing
the  solubility of the metals.
    The reason for the presence of arsenic  in the water at Site F6 can
only be speculated upon.  This area  is in the buffer zone for future ex-
pansion of the ash disposal facility and may have historically received
coal refuse, or the spring  flowing into the drain field may percolate
through some thin coal lenses.  Arsenic-containing herbicides may also
have been used at one time.
     Sediment samples were obtained at  one  location upstream and two
locations downstream  from the ash disposal  facility (see Figures 15 and
16).   The results of  the analyses of  these  samples were  somewhat

                                     61

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       I
            1.2
            1.0
           0.8
            0.6
            0.4
            0.2
            0.0
                    Fft
            FIGURE 18.  BUFFER CAPACITY—WIER'S  RUN

Note:  I = Campaign  I,  II  =  Campaign II,  and III = Campaign III
       in all histograms shown  above the  Roman numerals.

                              62

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surprising in view of the amounts of  metals  contained  in the ash
(Appendix C).   For every toxic metal  tested,  the average concentrations  in
the sediments at F2 were greater than or equal to the  concentrations  at
F13 and F18.   However, inspection of  the data on volatile solids coupled
with sediment granulometry showed that the upstream sediment was a fine-
grained organic material, Which probably has several orders of magnitude
more adsorption capability than the downstream sediments which were
predominantly sands and gravel.  The manganese and iron precipitates may
also act as binding sites for metals, but there was not very much
difference in iron content between the sites, so the differences between
the upstream and  downstream values for metals cannot  be entirely
explained on this basis.
    Phenols,  detectable at about half the stations, have no particular
significance to the overall quality of the stream at these low
concentrations.
    Organic carbon loading and oxygen demand downstream from the ash
disposal and Oak Tree Pond were too low to cause significant dissolved
oxygen depletion.  COD values were similar at F12 and  F14 and somewhat
higher than those at F17.  TOG was less than 4 mg/1 at all three
locations and less than the detection limit (1 mg/1) at F12.  The
greatest departure from oxygen saturation  occurred at Site F12 during
the high flow of Campaign II.  Dissolved oxygen dropped to 67 percent of
saturation.  Site F17 downstream was not affected.  Dissolved oxygen
therp showed 94 percent saturation.

Nutrients and Solids

    Total phosphorus, nitrate, nitrogen, and ammonia-nitrogen species
are shown in Figure  19.  Phosphorus was present  in Wier's Run at high
concentrations only  in the small tributary below the ash disposal
facility.  As mentioned previously, this stream drains a cattle grazing
and agricultural area.  Samples  from Sites F9 and Fll  showed con-
centrations of 0.03  and 0.08 mg/1 P04-P, respectively.  As  the volume
of this  flow was determined  to be very  small the steady-state quantity
                                     63

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2000
1500
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Volatile solids



           F4 F6 FI2 FI4 FI7
Note:
        FIGURE 19.  NUTRIENT CONCENTRATIONS IN WIER'S
                   RUN BASIN
     I = Campaign I , II = Campaign II, and III = Campaign III
     in all histograms shown above the Roman numerals.

-------
of phosphorus transported is also very small.  It is likely that runoff
samples would have shown much greater concentrations of phosphate.
    Average nitrate concentrations were less than 1 mg/1 N03-N.   On
the other hand, these concentrations are about three times those
measured by the U.S.G.S. in the reference stream and show that nitrate
is not being efficiently retained in the system.  The highest con-
centrations were found during the first two campaigns.  The weather
during Campaign III was much drier than it was during the other two
sampling periods, and this probably accounts for the differences.
    Nitrate concentrations in drainage from the ash disposal area were
slightly higher than those in the mine drainage effluent from Oak Tree
Pond.  The highest concentration of nitrate measured in this basin was
1.32 mg/1 N03-N at Site Fll.
    Ammonia nitrogen shows a more interesting trend.  The reducing
environment (low Eh) in the ash dump and  in  the mine drainage water
creates favorable conditions for the maintenance of ammonia in solution.
The pH in these discharges from Oak Tree  Pond and  the  ash dump is,
however, not sufficiently high to allow a toxic concentration of
unionized ammonia to exist.  The water quality criterion of 0.02 mg/1
NH3~N as unionized NH3 was never exceeded.   Ammonia concentrations
in Weir's Run were greater than  those  in  Cherry Run.
    The distribution of the solids  fractions reflected the nature of the
activities inWier's Run (Figure 19).  In absolute  terms, the total
solids sequence moving  from upstream  to downstream  is dominated by the
leaching of ions  from the ash and  the  calcium and  sulfate  from the mine
drainage.  Both dissolved and total  solids at F9 and F9 and Fll along
the west tributary are  less than 10  percent  of  the  respective values at
F12 and F14.   Suspended  solids also  increase moving downstream, but not
as  significantly  as  the  other  solids  fractions.  The  high  suspended
solids in the  sample at F17 may  be  due  to agricultural runoff.  The
suspended solids  concentration at  Fll  was 185 mg/1.   However,  the
presence of  suspended iron and manganese  oxides cannot be  ruled  out.
                                    65

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    The percentage of total solids which is in the dissolved state
ranges from 81 at the upstream site,  F4, to 94 at the site farthest
downstream, F17.  It was not determined whether this difference is
statistically significant.  The portion of solids in the volatile
(organic) fraction did not vary significantly as a function of location.
Percentages ranged from 9.9 upstream to about 8 downstream.   Samples
from the intermediate sites, F12,  Fll, and F17, showed 7, 8, and
7 percent, respectively.

                      Common Ravine/Second Ravine

    Sampling locations for Common Ravine/Second Ravine are shown in
Figures 20 and 21.

Solubility Controls

    The pH adjustment and lime coagulation of wastewater at the indus-
trial  treatment  facility results in  high alkalinity and pH precipita-
tion of the iron and manganese, which is then settled and removed.
However, discharge of effluent with this high pH and high alkalinity
caused the calcium, manganese, and iron present in the water upstream
from the industrial waste treatment facility to precipitate  in the
stream. The resulting mixture of calcium carbonate, ferric hydroxide,
and manganic oxide or manganous carbonate settles to the bottom and in
places is very much like a layer of concrete or plaster.
    Chemical conditions in the stream were altogether different during
the third campaign.  The pH of the stream was acid and the alkalinity
was zero.  These conditions would tend  to dissolve the calcium carbonate
and probably some of the  iron and manganese as well.  Data are not
available to determine whether these wide swings in  pH are  frequent and
what their duration might be.  This precipitation/resolubilization
sequence represents a potential mechanism whereby heavy metals may be
transferred between the liquid and solid phases and moved downstream.
    The Second  Ravine is  also  the receptor of  several  industrial wastes.
Some of these are mining  wastes and some are power plant  wastes.  The
                                    66

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Watershed
Boundary
       Legend
A  Paved road
B  Coal pile
C  Power plant
D  Cooling towers
   Stack
   Ash sluice ponds
   Mine siltation ponds
H  Employees' parking lot
I   Common ravine
J  Second ravine
K  Roger's pond
O Surface water sites
  FIGURE  20.   COMMON RAVINE/SECOND RAVINE SAMPLING  LOCATIONS—CAMPAIGN I
                                    67

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Watershed \
Boundary
       Legend
A Paved road
B Coal pile
C Power plant
D Coding towers
E Stack
F Ash sluice ponds
G Mine siltation ponds
H Employees'parking lot
I   Common ravine
J Second ravine
K Roger's pond
O Surface water sites
         FIGURE  21.   COMMON RAVINE/SECOND RAVINE  SAMPLING LOCATIONS-
                      CAMPAIGNS  II  AND III
                                     68

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North American Coal Company has constructed an earthen dike across the
ravine at a point adjacent to the Homer City Unit 3 stack.   Boney coal
is filled in behind the embankment and was the chief determinant of the
chemical characteristics of the water.  The overall quality of this
water as it reached Site CDE15 was very similar to that of a partially
oxidized and neutralized acid mine drainage (Class II) stream.  Were it
not for the alkaline pH overflow from the ash sluice ponds, Site CDE12,
this water would probably be even more acidic and  contain  even higher
levels of dissolved iron.
    Overflow from  the  two coal-pile desilting basins  is also discharged
to this ravine, but flow was noted only during Campaign II.  Even  then
the combined flow  from both  the  round  and  rectangular basins was
estimated at no more than 30 gpm (0.06 cfs) and  would have contributed
less  than 2 percent of the flow  measured  at Site  CDE15.
    As leachate emerges from the boney pile,  oxidizing conditions  are
established, and  the ferrous iron which  is stable and  soluble  to  the
extent of  several  hundred ppm  in a low Eh  system will  oxidize  to  ferric
iron.   Site CDE16  is located downstream  at the effluent end  of Rager1s
Pond.   By  the  time the ravine  water reaches this  point, the  ferrous iron
has had  sufficient opportunity to oxidize  and was no longer  detectable.
    It  is  further  evident, however, that  the  ferric iron  which was found
has either not yet precipitated  (as equilibrium  conditions would require
at this  pH),  or  the  precipitate  which is formed  is too fine  to be
 trapped  by the filter.  Some visual  evidence  suggested that at least
 some  of  the  iron  was  precipitating because the  rocks and  sticks covering
 the  stream bottom were coated  with  the floe.   In a number of samples at
 CDE15,  calcium and manganese were also supersaturated with respect to
 the  sulfate and the  oxide.
     The Common Ravine  and Second Ravine join  at  a point about 0.2 km
 downstream from the  outlet of Rager1s Pond immediately before dis-
 charging into Two Lick Creek.   No samples of  this combined flow were
 obtained,  but it is expected that because of the  increased pH the
 precipitation process  would be enhanced in the short reach of stream
 before it joins with Two Lick Creek.
                                    69

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Toxic Materials

    Considering the volume and variety of trace metal- and phenol-
containing materials handled at the electric generating station, it was
not unusual for them to be present in the Common Ravine.  Peak con-
centrations of the trace metals, as found in grab samples, were
generally higher than the average concentrations in the composite
samples.  Phenolics showed the opposite trend from the heavy metals.
Phenol concentration was higher by a factor of 10 to 15 in the composite
samples than in the grab samples.  Samples were composited by an ISCO
automatic water sampler at the following rates:  Campaign I, 90-minute
intervals for 10 hours; Campaign II, 60-minute intervals for 10 hours;
and Campaign III, 60-minute intervals for 30 hours.
    Mercury and vanadium were found in the grab samples but not in the
composite samples, while beryllium and hexavalent chromium were not
found in any of the samples, grab or composite.
          •
    Oil and grease analyses were performed on a few samples.  These
confirmed the presence of fuel oil, as was suspected from the appearance
and odor of samples taken from the Common Ravine.  The source of this
oil is unknown, as are the quantities being discharged.  Whether this
oil was contributing substantially to the trace metal and phenol con-
centrations observed is a matter of speculation.  No. 2 fuel oil, as
used for the start-up of the auxiliary boilers, is generally very clean
in terms of trace metals.  The phenol content of fuel oil is variable
and dependent on the crude oil and the refining run.
    The Second Ravine also had detectable concentrations of some heavy
metals.  Nickel and zinc occurred in the highest concentrations, as was
the case in the other basins.  Chromium, lead, mercury, and vanadium
were not detected.  The concentrations at the Rager1s Pond site (CDE16)
indicate a removal mechanism which is likely a combination of dilution
and adsorption/coprecipitation with the iron.  Solubility of discrete
trace metal hydroxides should not be a major factor at the observed pH
values.  Only nickel and zinc were present in the outflow from the pond.
    Phenolics were detected at the monitoring location immediately below
the earthen dike in concentrations almost the same as those measured at
                                   70

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CDE17 on the Common Ravine.   This correlation may not be a coincidence,
because individual samples also had very similar concentrations.
Reductions in phenol between the dike and Rager's Pond were even  greater
than those for zinc and nickel.  Concentrations in the Second Ravine at
Site CDE15 and in the Common Ravine at Site CDR17 were in excess of the
1976 water quality criterion of 0.2 mg/1.

Nutrients and Solids

    The sanitary waste system  for the power plant empties into the
Common Ravine at a point above  the industrial waste  system discharge.
The major portion of phosphate, nitrate, and ammonia were attributable
to  this source.  Grab samples  taken below the sanitary system and above
the industrial system and those taken below both discharges were com-
pared for N03-N, NH3-N, total  phosphate, and TOC.  The ratios for
the concentrations of these four nutrients in sanitary waste versus the
combined waste were  1.12:1, 3.35:1,  1.66:1, 2.71:1,  respectively.
Sanitary waste, therefore, is  the major contributor  to the nutrient
leads in the ravine.  Phosphate removal would be expected  in the lime
coagulation system used at the  industrial waste  treatment  facility.
    Ammonia concentrations encountered  at Site CDE17 would be con-
sidered toxic under  normal stream quality circumstances.   Concentrations
of  COD were as high  as 231 mg/1 (Campaign III), which would  cause an
oxygen reduction downstream but probably not before  discharge to Two
Lick Creek. Total  organic carbon, suspended  solids,  and  volatile solids
concentrations were  similarly  high during Campaign III,  suggesting  a
very large  load of organic material.  This loading cannot  be totally at-
tributed to the sewage treatment  plant  because  the downstream con-
centrations of volatile  solids and  organic carbon  in several  instances
were still  substantial.

                          Two  Lick Creek Basin

     Sampling locations for  Two Lick  Creek are  shown  in  Figures 22  and
23.

                                    71

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Watershed
Boundary  /'
                                                Legend
                                        O Surface water sample
Two Lick Creek
 FIGURE 22.   TWO LICK CREEK  SAMPLING LOCATIONS—CAMPAIGN I
                             72

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Watershed   „''
Boundary  f
                                                    Legend

                                             Surface water sample


                                             Sediment and surface water sample
Two Lick Creek
                               CDEI8
   FIGURE 23.  TWO LICK CREEK  SAMPLING LOCATIONS—CAMPAIGNS  II  AND III
                                   73

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Solubility Controls

    Two Lick Creek is an acid mine drainage stream.  The charac-
teristics were typical for Class II partially neutralized and/or
oxidized mine drainage (Figure 24).  A number of strip mines are located
upstream, which probably determines the overall quantity of iron, man-
ganese, calcium, and sulfate in the water.
    Concentrations of dissolved and ferrous iron in this stream were
about as expected for the measured pH values from equilibrium
calculations. Soluble calcium concentrations were not influenced by
calcium solid phases at these low alkalinities and sulfate
concentrations.
    There are no significant differences between the upstream and
downstream sample locations for pH, sulfate, iron species, manganese,
calcium, and alkalinity.  The differences noted between Sites HIS and
H19 during Campaign I were attributable to day-to-day variation because
these could not be sampled on the  same day on this particular occasion.
Compared with the values for the reference stream, Two Lick Creek bears
almost no resemblance to undeveloped, pristine conditions.

Toxic Materials

    The water in Two Lick Creek is relatively free of heavy metals.
Zinc was the only metal detected with consistency.  Sediment analyses
were extremely limited but indicated much  the same metal  accumulations
as  the sediments in the rest of the region.  Mercury and  lead were
somewhat higher  in these  samples than  in  those  from the remainder of the
basins, and may be attributable to upstream  land uses which include
urban  and industrial classifications.
    One attribute which these sediments possessed  to a greater  de-
gree than the others was a very high organic content and  a high percent-
age of particles in the fine sand  to clay  range.
    The  high organic content also  resulted  in  the  creation of low-
Eh  (reducing) conditions  in the sediment.  The  visual appearance of  the
                                    74

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                             PH
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                       Total  Iron and
                       Dissolved Iron
                    -

                       i
I.

                                     B
                                   Wt.
                     HI8  HI9  CDE CDE Bench-
                               18   19  mark

         FIGURE 24.  CONCENTRATIONS OF SOME IMPORTANT
                     SOLUBILITY CONTROLLING SPECIES IN
                     TWO LICK CREEK
Note:  I = Campaign I,  II = Campaign  II, and III  = Campaign III
       in all histograms shown above  the Roman  numerals.

                              75

-------
sediments and the chemical analysis confirmed the presence of sulfide.
This is likely to be the solid phase controlling the soluble metals in
the sediments.  Iron, mercury, cadmium, lead, and zinc all form ex-
tremely insoluble sulfides.
    Phenolics were detected only sporadically and at concentrations that
were not significant to stream quality.

Nutrients and Solids

    Of the nutrient  fractions, only nitrate exhibited a significant
upstream-downstream  increase, especially at Cherry Run.  Values obtained
for samples  from Site HIS  were similar to the benchmark station but
increased to  several times that downstream.
    Ammonia,  if anything,  shows the opposite trend of nitrate being
diluted by the discharge  from Cherry Run.  There is no difference be-
tween  the concentrations  upstream and downstream from the ravine dis-
charge.  At  these  pH values, the ammonia concentrations observed are not
toxic.
    Phosphate concentrations were low in most samples.
    Suspended solids concentrations ranged from 1 to 7 times the
concentrations in  samples from the benchmark station. Considering  the
amount of agriculture  and pasturing activity that takes place between
the discharge points from Cherry Run to Homer City  itself,  it is some-
what  surprising  that the  amounts were not even higher.  In  any case
there was no upstream/downstream trend either to increase or to
decrease.
    The  percentage of  total  solids which are suspended ranged  from 4 to
13 and the percentage  of  total solids  which are volatile was oc-
casionally as high as  20, attesting  to  the heavy loading.   Dissolved
solids were  primarily  sulfates and cations from mine  drainage.  There
was no statistical variation between the  upstream and downstream values
for total or volatile  solids.
                                     76

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                  Summary of Water Quality Conditions

    The results of the three sets of water quality data obtained at
Homer City during the winter and spring of 1976-1977  indicate  the
following:
    •  Water quality in most basins reflects the degree of human
       activity in the region.  This is especially apparent for the
       Common and Second Ravines, Two Lick Creek, and Wier's Run below
       the ash disposal area.
    •  The flows which exhibited water quality closest to that of the
       reference stream were the discharges from the springs to the
       south tributary to Cherry Run, followed by the west tributary to
       Wier's Run and the north tributary to Cherry Run.
    •  The main channel and north tributary of Cherry Hun are influenced
       to some degree by neutralized and diluted drainage from mines or
       a similar source and by agricultural or pasture-land drainage.
    9  The south tributary of Cherry Run is affected by flow from  the
       settling ponds below the coal preparation plant from the
       standpoint of  solubility controls, metals, and  ammonia.  These
       effects are localized and do not extend into  the main channel.
    •  The primary impact of  the construction of the sediment and
       leachate collection  ponds was the increase in the suspended
       solids levels  downstream.   Some  increases in  nutrients were also
       noted.
    •  Sulfates  concentrations  are already  high  in  the south  tributary
       to Cherry Run  before  it  reaches  the  upstream  monitoring  location.
       The  source has not been  identified.
    •  Water quality  in Wier's  Run is  determined  by  two  factors—the
       migration of  rain water  through the  ash,  and  the  lime  treatment
       given  to  the  drainage  from Helvetia  Mine.   Levels  of major
        ions  and trace metals are set by these processes.   In-stream
       chemistry determines the fate of the metals.
                                     77

-------
    •  The  agricultural  drainage  from  the west  tributary and the mine
       drainage  contribute  most to  the observed organic loads.
       Agricultural  drainage  also contributes  to  the  suspended solids
       and  nutrients loads.
    •  The  ravines are receptors  for industrial wastes, and  this water
       reflects  power plant operations and  mining  activity.
    •  Water in  the  Common  Ravine contains  both nutrients and metals.
       Industrial waste  treatment provides  a mechanism  for in-stream
       precipitation of  metals.
    •  Water quality in  Two Lick  Creek is determined  by the  amount of
       acid mine drainage created upstream. Project  area influences
       were seldom noted as being significant.
            Comparison of Analytical Data with MEG  Values—
                           Aquatic Environment
Stream Water Concentrations versus MEG Values

    Maximum and minimum concentrations of 15 elements that were
analyzed in surface water are compared with the appropriate MATE and EPC
values for the environment in Table 9.  These data were organized to
correspond to the biological sampling locations for additional
comparisons.  Although data were obtained in the study area near Homer
City for 30 different parameters used to define water quality in stream
water, MEG valuer are available for only the parameters listed in
Table 9.
    EPC and MATE values suggested for the environment were exceeded by
many of the maximum and minimum values determined for the 15 water
quality parameters listed in Table 9.  Maximum values for 9 parameters
measured in surface water throughout the study area exceeded the
corresponding MATE values, and maximum values for 11 parameters exceeded
the corresponding EPC values.  Maximum and minimum values of measured
parameters exceeded EPC's in the  following 10 cases:  beryllium, lead,

                                    78

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                                     TABLE  9.    COMPARISONS  OF  EPC  AND MATE  VALUES  FOR WATER  WITH
                                                       HOMER  CITY  SURFACE  WATER QUALITY

MEC Category

Minimum
Acute Estimated
Toxiclty Permissible
Effluent Concentration
(MATE) Tcr (EPC)


Cherry
Run:


North
Tributary to


South Tributary
to Cherry Run


Wier's Run Tributary Rager's
Below Ash to Pond Common

                                                                                                 Mater Quality Evaluatlon(bi
                                            Max.    Mln.    Max.    Mln.    Max.    Mln.    Max.   Mln.    Max.     Mln.   Max.  Min.    *ax.      Min.	Max.	Kin.	.Max.    Min.

IB  Phenolic*        500        100W       -(C>    --     -      -      —      ~      -      —     10      ND      7     6   " 340        9      360       30       B     SD

J2  Eti-ryllium         55         _llJ000  H^jjOO  43,9»0  21,0(11)

4(1  ,ead              50         in'b)       ND       ND     SD      ND      ND      ND      ND      ND     SD      ND     ND    SD      ND       ND       30       20      NI)     Ni)

4?  Ammonia                        ..,
     Kitrogun         50         HT '
    ,Usfilic           10         15

    Vanadium         150

    Cliromiun         250
(d)

(d)

(d)
80
ND
ND
ND
4_60
ND
ND
20
ND
Nil
<50
SD
SD
ND
20
ND
ND
ND
ND
ND
j>g
ND
ND
SD
280
ND
ND
20
ND
ND
< 50
ND
ND
ND
10
ND
ND
20
ND
KD
50
NU
300
ND
210
ND
NI)
50
ND
N[>
' 50
ND
ND
ND
HO
ND
SD
IP.
ND
ND
T 50
ND
ND
ND
1,400
ND
ND
JO
ND
ND
'50
ND
ND
ND
<20
ND
ND
XI
NI)
ND
630
8
SD
ND
6.100
U)0
:>

                                                                                                                         I y 1
                                                                                	Biu_logical ijuaUjj  Kyaluat ion	
                                                ¥              i;              G
                                                F              r,              c,
                                                    yrt- from Clvland and KinRsbury (1977a and h).
                                                   aiti.-lL£-  in  the study art-a.
     ii.isi-J  on Host strinnL-nt  i-xisiin^ or proposed FVdural standard for wattr  quality (ClelancJ and Kin^sbury,  1977a and b).
     Uu-mical an.ilv^is during watc-r yt-ar 1^71  of Youiig Wonu-n's Creek near Renovo, Pennsylvania  (L.S. Dtparcmtnt of tlit- Interior, 1*J74).

     lln-  .-|i|ii,tt u- hiot.i i-v.i tu.i-ions .in- bnscd nn ^t.indiuj; I'rup, species diversity, and presence  tit Indicator spt-ci-i-.s or familU-s;
     :  =  :'na,l; K = lair;  and  I' =• poor nquatic  hiola ijujililv.  Uata arc- from two sampling campaigns conducted  hv BatU-ltt in  tliu study area.

    :   Vnr  ,.is,. ol nuiking < omp.ir isnns, KTC mid MAIL values wiiii li arc used for making comparisons and the field data which cxteco tln-m ar^= underlined.

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 ammonia, nitrogen, arsenic, manganese, nickel, copper,  zinc,  and
 cadmium.
     Streams considered to have good biological quality  also  had  levels
 of pollutants which exceeded EPC or MATE values for  the environment.
 Maximum and minimum levels of manganese and Einc in  streams  with good
 aquatic biota quality exceeded the EPC values  for the environment.
 Maximum levels,  alone, of two additional parameters  (ammonia  and
 vanadium)  in streams with good aquatic biota quality also  exceeded  the
 EPC values for the environment.   Similarly, maximum  and minimum  levels
 of calcium and manganese  in streams with a  good biological quality
 rating exceeded  the MATE  values  for the environment.

 Stream Water Concentrations versus Recommended Values

     MEG values have not yet been determined for 14 of the 30 water
 quality parameters measured in Battelle's study area. Therefore, com-
 parisons have been made between  these  14 parameters  and  eight values re-
 commended  by the EPA (1976)  or suggested by McKee and Wolfe (1963) (see
 Table  10).   A biological  quality evaluation of  the same  stream stretches
 that were  analyzed for water quality is  presented for comparison with
 the  chemical  data.
    All  eight  of the  water  quality  criteria concentrations recom-
 mended  by  EPA  (1976)  or McKee  and Wolf  (1963) were exceeded by one or
 more concentrations  of the  same  parameters  measured in samples from
 streams  in  the study area (Table  10). The maximum and minimum values for
 alkalinity, sulfate, and  total solids observed in one of the streams
 with a good  biological quality rating were  greater than the recommended
criteria concentrations.
    A comparison of the data  for each of the 30 surface water quality
parameters with the biological quality evaluation for the same stream
segment  suggests that values for four parameters agree  closely with the
biological quality rating (Tables 9 and 10). The maximum and minimum
values for these  four parameters (pH, suspended solids,  dissolved iron
and total organic carbon)  have been compared with recommended  or

                                    80

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               TABLE 10.   COMPARISONS OF CRITERIA RECOMMENDED FOR FRESHWATER AQUATIC LIFE
                           WITH HOMER CITY SURFACE WATER QUALITY DATA20,()00 — 44,200 13. 2OO
Totjl to 1,000 2W 1,990 140
Dissolved KH — -- 760 «20
Kf'+ — -- 760 <100
Snl l.i ti- (Sd, ) — I 1 .000 8 ),600 27,300
T..t.i i Phosphorus 100 -- 40 -10
Su-,p.-mii-il Sol ids -- 30 ,000 14 ,000 2,000
VM! n i K- Sol ids -- — 34,000 2,000
Siiriu- - N 9H, 000 -- 2,000 760
J..t.tl Ku'Id.i',1 - \ -- -- 160 HO
l.-i.r 1 on;, mi. r;irh..[! -- -- i.OOO 1 . 700
\,-,l i! s.i 1 id- -- K1J ,l)00(K) 1H J.OOO 1 Ji ,000


\l I i- !..••! ,\l ,.-.H- F
!•!•.. n. -.r-n,^ I1
1 i -h K
.•v. r.i 1 1 k.it nil' K
(.1) All valui-s -ir,- givm In «/ i-xtfnt j)H units.


("J I'" 'r^r!1^'?" po^'an^U-3!?!,,'^^,^! t,-!''"^"- ar^'f'rc
Streams In the Vicinity of Homer City Station
Trihiirdry To Cherry Run Below Ash To Pond 8. Two Lick DtL-Anr
Water Quality Evaluation
Max Hin. Max. Hin. Max. Hin. Max. Min. Max. Mtn. Max. Min. Max. Min. Max. Min.
Solubility Controls'^
7,200 1,400 t.flOO 1,400 4 . 3flO 1.400 4S.700 3.100 — 1,999.000 28.300 1H3.000 0 7a,000 11,400
44,200 21,100 19,600 12,600 _1_5J_70_0 7 , 1 OO (Sn.100 11,000 -- ^jj*P_0 __ 0 «>15.0OO 0 4 9UU 1) 3 hOH
K710 140 530 80 660 200 15.0OO 1,820 — 472.500 3,000 21 400 7 930 15 000 =, hVi ?n nnn
10 -20 90 <20 60 -20 n.OOfl 20 -- 453,000 7.900 8.200 20 12,400 3,930
*-'0 '"'I 190 MOO 170 '100 2,140 '100 — 467. 000 <100 370 ^OO 6,0 JO - 1 00
3Z.-A0-0. 27.100 26_7_,_00_0 115,fiOO 204.000 20.600 l^MT^Omj 4_6 0 .OOp -- 2.940.000 124.000 1 ,180.000 290,000 230,000 yO.OOf) 7, }ni,
Hi d s iid (f)
100 10 10 10 50 10 10 -10 -- -]0 «10 160  n^.OOO 60,nOO -- 73ft, 500 uy> 1.046,000 2 5ftn 76 nnn M nnn
1 ,420 }60 1 ,000 SOD 1 ,07D -100 1 ,260 520 -- 4 .400 2,060 1. 750 4OO ] 80O >•>() ' - ' ' '
140 -50 270 120 160 -SO 950 270 -- 17 .ROD .SQO 4. 5 SO ?.2UO ] ' So r>o
2.000 1,200 3,500 1.500 4,000 1,200 7,000 -1,000 -- 24, WHO J.OOO 97.500 7,250 6 5nd | HOI, • ;•
159,000 124,000 442,000 180,000 380,000 82,000 2,119.000 SIR, 000 -- 4.17H.500 7/4 ( (inn -. ^^r Snfl r,7(t Vin , }H ,1(1, ,,,- |(
'
.Lol^.lc.1 ,,-Uc, Ev-uauon"'"
i- K !• I c: |. ,. ,.
' (. [• I' ' [i |> |
c c (• !' f i' p ,

ri'c-k m-.ir R^nouo, Pennsylvania (U.S. Department of tl,e Interior. 1974).
pciii-s Jivurbity, and prc-sonc^ of^inclicatur species c,r lan.ili,:i; I. - nood ;

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suggested water quality criteria in Table 11.   It can be  seen  that
streams with good biological quality did not have any levels of  these
four parameters which were above the recommended criteria.  Maximum, and
frequently minimum, values of these four parameters,  however,  exceeded
the recommended criteria in streams with poor biological  quality.   The
significance of these four "master" parameters to aquatic biota  is
probably great because they affect the presence of other  potentially
toxic water pollutants.
    Several studies have described the effects of water pollutants  in
acid mine drainage on aquatic biota.  These studies found that the
master chemical factors involved one or more of the parameters listed in
           TABLE 11.   WATER QUALITY PARAMETERS IN CLOSE AGREEMENT
                      WITH BIOTA QUALITY RATING
Sampling Sites ,LV
Water Quality (units or concentrations>specif ied
Parameter
pH (6.5-9.0)(c)
Suspended Solids
{20,000 pg/l)(d'
Dissolved Fe
{1,000 ug/l)ld)
Total Organic Carbon
(4,000 Mg/l)(d)
Grand Totals
re\
Biota Quality Rating vc'
(a) Sampling site locations
at the top of Table 10.
1
1
0

0

1

2
F
2
0
0

0

10

0
G
correspond

(b) Maximum and minimum units

J
0
0

0

£

0
G
to

4
1
1

0

3,

3
P
the eight

5
1
1

1

1

4
P
6
2
2

2

1

7
P
locations

or concentrationsspecified value = 1; maximum and
     minimum units or concentrations>specified value = 2.
(c)   Criteria recommended by EPA (1976).  Maximum and minimum pH
     within recommended range = 0;  maximum or minimum pH outside
     recommended range =1; maximum and minimum pH outside recommended
     range = 2.
(d)   Criteria suggested on the basis of the chemical and biological
     data presented in this paper.
(e)   G = good; F = fair; P = poor quality.
                                   82

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Table 11.  Weed and Rutschky (1972), for example, found that pH, alkalin-
ity, and ionic concentrations of iron and sulfate were primarily re-
sponsible for altering the community structure and diversity of benthic
macroinvertebrates.  Similarly, Warner (1971) found that pH measurements
in streams seemed to provide the most reliable, as well as unique, index
of the effects of acid mine drainage on aquatic life.  A report by the
Federal Water Pollution Control Administration (1969) concluded that
acid mine drainage damages aquatic biota primarily because of the high
concentrations of mineral acids, the ions of iron, sulfate, and the
deposition of a smothering blanket of precipitated iron salts on the
stream bed.

Sediment Concentrations Versus MEG Values

    The maximum and minimum concentrations for eight of nine trace
metals (lead, arsenic, chromium, manganese, nickel, copper, zinc,
cadmium, and mercury) measured in stream sediments exceeded their
corresponding EPC values (Table 12).  Comparisons of concentrations for
the same nine elements in fly ash from the ash disposal area revealed
that maximum and minimum ash concentrations of six elements exceeded
their associated MATE and EPC values. Maximum and minimum concentrations
of all of these elements, except chromium, mercury, and cadmium, were
higher in separate grab-sample analyses of the three raw coals used in
the Homer City power complex than they were in the associated MATE or
EPC values.  Therefore, coal and fly ash from a variety of sources may
be contributing to the trace element content in the sediments of the
study area streams.
    In spite of the toxic trace elements in its sediments, one stream In
the study area still had a good biological rating (Table 12).  The
upstream portion of the south tributary to Cherry Run had good biolog-
ical quality.  This stream, however, had maximum and minimum concentra-
tions of seven elements (lead, chromium, manganese, nickel, copper, zinc
and cadmium) that exceeded the associated MATE and EPC values.

                                    83

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       TABLE 12.   COMPARISONS OF  EPC AND MATE VALUES FOR  SOIL WITH HOMER  CITY  SEDIMENT  QUALITY  DATA
                                      Streams in the Vicinity  of  Homer City Station
MEG Category
and Substance
MATE(b)
for
Ecology
EPC(b)
for
Ecology
Cherry
Run:
Main Stem
Upstream
On South
Tributary
To
Cherry Run
Wier's Run
Below Ash
Disposal Area
Two Lick
Creek
Ash / ,
Analysis1*^
Max. Min.
Analysis
of Three
Raw Coals(f)
Max. Min.
GO
                                                   Concentrations in Stream Sediments
                                                                                    (c)
                                        Max.
                                               Min.
                                                       Max.   Min.
                                                                     Max.
                                                                             Min.
                                                                                     Max.
                                                                                           Min.
46
49
68
71
76
78
81
82
83
Lead
Arsenic
Chromium
Manganese
Nickel
Copper
Zinc
Cadmium
Mercury
10
10
50
20
2
10
20
0.2
50
3>
71
90
40
0.6

17.8
49
36
76
17.5
32
69'
0.27
1.1
                                                                                                                            12. 3

                                                                                                                            12

                                                                                                                            I
13.2

11

1Z

 
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                          Aquatic Biota Survey

    Fourteen aquatic biota sampling sites were selected in seven streams
in the study area, as well as in an additional control stream, Ramsey
Run, which is about 6 miles (9.6 km) north-northeast of the study area
and about 1 mile (1.6 km) east of Indiana, Pennsylvania (Figure 25).
Sites were chosen which would provide the best data for evaluating the
impact of the existing facilities in the complex on the aquatic biota of
the receiving streams.  Sampling was conducted both upstream and down-
stream from potential sources of pollution.   Thus, the prior effect of
upstream sources of pollution on aquatic biota was included in the
assessment of the study area.  Only a minimal sampling effort was
carried out in Two Lick Creek because a survey by Environmental
Sciences, Inc., (1972) reported that this stream had poor water and
aquatic biota quality primarily due to acid mine drainage from abandoned
strip mines located upstream.
    Three groups of aquatic organisms were selected for study:
(1) periphyton (attached algae, especially diatoms), (2) benthic macro-
invertebrates (bottom-dwelling invertebrates visible to the naked eye),
and (3) fish.  These three groups of organisms were chosen because of
their relative ease of collection, usefulness as water quality
indicators, and importance in aquatic food webs.
    Attached algae were sampled in triplicate by scraping cobble-size
rocks from the stream bottom.  The preserved diatoms were prepared for
viewing on a microscope slide and then identified according to species.
Standing crop was expressed for each species in terms of number of
organisms per square centimeter.  Finally, total periphyton standing
crop and total number of species were calculated for each sampling site.
    Bottom-dwelling macroinvertebrates were collected from riffle areas
using a Surbur ® sampler.  Five replicate samples were taken at all
stations and were preserved with Formalin ® and returned to Battelle for
sorting, identification, and enumeration.  All organisms were identified
to the lowest practical taxon, and the resulting data were used to

                                    85

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A  — Ash Disposal Area
8  — Mine Drainage  Treatment Pond
C  - Helvetia Boney Pile (at mine)
D  - Coal Cleaning Plant
E  - Coal Storage Pile
F  - Power Plant
G  - Industrial Waste Treatment Plant
H  - Helen Boney Pile (at mine)
                 FIGURE  25.  AQUATIC BIOTA SAMPLING  LOCATIONS

                    (a)   Table  70 describes the locations.

                                         86
                                                                      (a)

-------
calculate species diversities according  to  the  Shannon-Weaver  formula
(Shannon and Weaver, 1963).
    Fish were collected by using a 4  x 6-ft,  l/4-in.-mesh seine and/or  a
backpack shocker.  Both devices were  used during the  spring  survey,  but
only the seine was used during the winter survey.   Fishing was conducted
with approximately equal effort (1/2  hour)  at each station.  Fish were
identified, recorded, and released.  Specimens not positively  identified
in the field were placed in sample bottles, preserved,  and returned  to
the laboratory fir identification.
    Biological quality was determined for each of eight portions of
streams or  tributaries surveyed in the study area. Quality of  the biota
in the control stream (Ramsey Run) was evaluated as good and provided a
basis for comparing the other streams.  The subjective evaluation of
aquatic biota quality in each stream was determined by initially eval-
uating each of the three groups of organisms surveyed.  The  evaluations
were based  on the presence of indicator  species, standing crop of
diatoms, species diversity of bottom-dwelling macroinvertebrates, and
number of individuals per fish species.  Finally, overall biological
quality ratings of good, fair, or  poor were based on the individual
ratings for the three aquatic groups.

Stream Surveys

    Cherry  Run and Tributaries.  Cherry Run is  a medium-size  stream
which flows through areas of differing land use.  It receives  runoff
from agricultural, residential, and  pasture lands as well as  discharges
from coal mining  and  storage operations.
    Collections  of attached algal  (diatom) communities made during
December,  1976,  and April,  1977, reflect ecological  stress  conditions  in
Cherry  Run.  Dominant  species  include Melosira  distans,  Navicula
radiosa, N. cryptocephala,  N.  viridula,  and  Nitzschla  dissipata, which
have been  classified  as  indicative of mild to heavy  organic pollution
and high inorganic  and nutrient content  (Patrick  and Reiner,  1966,  and
Lowe, 1974).   Organic  enrichment  was particularly evident at  Sampling
                                    87

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 Sites 2 and 3;  (upstream and downstream of the tributary south of  the
 disposal area;  see  Figure 25)  after the stream flowed  through  pasture-
 land.  Ecological  imbalance was expressed by the relatively  large
 numbers of  only a  few species.  Species diversity indices for Cherry  Run
 and  other streams  are presented in Appendix D.
     Benthic macroinvertebrates  collected from three  sites  in Cherry  Run
 indicated the  presence of a moderately diverse community.  Dominant
 groups  of aquatic organisms included  dipteran (fly)  and  trichopteran
 (caddis fly),  larvae  and fingernail clams.   Other organisms  present
 included mayfly and stonefly naiads and beetle larvae.   Species
 diversity indices calculated from  the total of three Surber  samples  are
 presented in Appendix D.   Indices  greater than 2.0 have  been classified
 as representative of  clean stream  conditions (Wllhm, 1970).  An ex-
 ception of  0.90 was recorded for Sampling Site 2  in  the  winter.  The
 standing crop  supported  at these sampling sites was  lower  than might be
 expected.
     Fish collections  made in Cherry Run contained a  total  of 18 species.
 A variety of species  were collected including  forage fish  (minnows,
 shiners,  and dace) and  sport fish.  Only two  species of darter  the
 barred  fantail  and the  Johnny darter,  were  collected in  this area.
 These bottom-dwelling riffle species  tend to  be one of the more sen-
 sitive  groups  of aquatic  organisms.   The absence of more darter species
 may  indicate periodic poor water quality.   In  addition, relatively small
 numbers  of  fishes were  observed or  collected  from the riffle areas with
 a seine.  This  low-standing  crop of fishes, may  also reflect
 environmental stress  in Cherry Run.

     North Tributary.  The  north tributary is a  small headwater stream
which flows  along the northern edge of  the  proposed refuse area.
 Dominant numbers of Surirella ovata and  Navicula radiosa indicate a
 source of pollution,  possibly inorganic  (Lowe,  1974).  Spring col-
lections showed a relatively small  number of species.  Additionally,  the
presence of  large numbers of individuals of two or three species in-
dicated a possible environmental perturbance.  This stream was  almost
                                    88

-------
 totally shaded,  which  could  account  for  the  underdevelopment  of  the
 diatom community.   The north tributary does  not drain any  of  the
 existing plant complex and receives  little or  no  industrial or domestic
 waste.   The benthic raacroinvertebrate community here was abundant and
 diverse.  Species  diversity  indices  calculated from these  collections
 were  the highest in the area,  3.50 in winter,  and 3.98  in  spring.
 Although these were calculated  from  three combined samples, values in
 this  range are characteristic  of clean,  unpolluted streams (Wilhm,
 1970).
    Fish collections made in this stream revealed the presence of 12
 species.  Abundance of fishes  in this stream was also high.   This stream
 has a  well-balanced and diverse aquatic  community, indicating good water
 and habitat quality.

    South Tributary.   The south tributary, a small headwater  tributary,
 drains  the southern edge of  the proposed refuse area.  Site 5 was
 located upstream from  existing plant discharges (from coal pile runoff)
 and from potential  runoff (from the new  refuse area).  The tributary
 flows  through a  wooded area  and, in  the  region of the sampling station,
 was approximately  50 percent shaded.  Low numbers of species were found
 during  both sampling periods.  Dominant  species were indicative of
 pollution, high  nutrients, and inorganic content—Gomphonema  parvulum.
 Navicula crytocephala, Navicula radiosa. Navicula viridula. and
 Surirella ovata.  Upstream land use for  pasture and agriculture were
 likely  sources for  nutrient  additions.
    Runoff from  the coal pile was likely responsible for the decreases
 in standing crop and numbers of species  found  during the spring survey
 between  the upstream portion of this tributary (Site 5) and that segment
 near the  confluence with Cherry Run (Site 6).  The diatom  community at
 the downstream station was extremely depauperate during the spring
 survey,  less so during the winter.
    The headwaters of this stream were found to support an abundant and
diverse macroinvertebrate community dominated  by caddis fly larvae.
Also present were two headwater stream species of fish, the creek chub,
                                   89

-------
 and  blacknose  dace.  This  portion  of  stream  appeared  free of external
 environmental  stress.  The  site further downstream, however, clearly
 demonstrated a perturbance.   Stress was caused  by the poor water quality
 below  the  coal-pile runoff  discharge  to this stream.  Benthic macro-
 invertebrates  were almost  totally  absent  from the lower reaches as far
 downstream as  its confluence  with  Cherry  Run. Another indication of the
 poor water quality of  this  stream  was  the absence of  fishes.  Only three
 species and seven Individuals were collected from the downstream
 sampling site.
     Coal-pile  runoff and current construction activity have severely
 stressed both  the water quality and biological  communities of this
 tributary.  Apparently, dilution with  Cherry Run water reduces the
 negative impacts below detection at the level of effort of this study.
 No indication  of poor stream  quality downstream in Cherry Run could be
 attributed to  the addition  of waters from this  tributary.

     Wier's Run and Tributary.  The uppermost portion of Wier's Run
 originates below the existing ash disposal area.  No algal growth was
 apparent on any substrate in  this  portion of Wier's Run.  Analysis of
 samples showed extremely poor diatom community development, both in
 numbers of species and standing crop, during both winter and spring
 sampling surveys.
     The tributary to Wier's Run was physically very similar to the
 portion of Wier's Run below the ash disposal area.   Both are small head-
 water  streams  fitting through the  same wooded area.   Standing crops were
 relatively high during both spring and winter sampling surveys.   Spring
 collections had a relatively high number  of species.  Dominance was
 evenly distributed among several species.   However,  a few of those
 species were indicative of organic pollution and nutrient enrichment.
These conditions were likely due to, or enchanced by, the decomposition
of garbage and trash found at several spots along the banks of the
 tributary.
    Benthic macroinvertebrate samples were also collected from both
Wier's  Run just downstream from the ash disposal area and from the
                                    90

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tributary in the same area.  A relatively large and diverse community of
invertebrates was found to inhabit the triburary stream.   Species
diversity indices calculated from this tributary were 2.61 and 2.13 for
winter and spring, respectively.   However, in Wier's Run (Site 8), no
invertebrates were found in collections during either sampling trip.
Only one fish species was collected from both these areas, the creek
chub.  On the basis of the periphyton and invertebrate collections, the
segment of Wier1s Run immediately downstream from the ash disposal area
was greatly stressed by poor water quality leaching from the ash pile.
    Two additional stations further downstream in Wier's Run were also
sampled to determine the downstream extent of the ecological perturbance
observed below the ash disposal area.   At Site 9, the stream bed widens
and deepens, creating long pool areas.  Suitable habitats for attached
algal development were scarce.   The diatom populations found on
available substrates were fairly sparse—low numbers of species
(possibly seasonal variation, in the winter), and low-standing crop.
    Stream characteristics at the farthest downstream site sampled (Site
10) were similar to those found at Site 9.  Winter samples showed a
larger number of species at this site than at either of the two up-
stream sites.  Standing crops were also greater at this site during both
surveys.  The dominant organism during both surveys was Diatoma vulgare,
classified as indicative of high nutrient conditions (Patrick and
Reimer, 1966, and Lowe, 1974).   This enrichment was likely due to
domestic sewage discharges to Wier's Run upstream of this sampling
location.
    Benthic invertebrate collections from the downstream sites were also
very poor.  Few, if any, organisms were collected from the riffle areas
of the two sites.  The notable exceptions were the large number of
Hydropsyche and Cheumatopsyche collected near the confluence with Two
Lick Creek.  This almost complete dominance by two quite tolerant
organisms also indicates that Wier's Run was adversely impacted for its
entire length.
    Fish collections obtained using both seines and electrofishing
equipment further demonstrate the poor ecological quality of Wier's Run.
                                    91

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Only 5 species and 59 individuals were collected from both downstream
sites.  Extensive attempts to collect fish from these areas produced few
additional specimens.  Low-standing crop of only a few fish species
clearly demonstrates the poor quality of Wier's Run.
    Although some recovery was indicated downstream, Wier's Run was
generally adversely impacted from the ash disposal area to its con-
fluence with Two Lick Creek.

    Common Ravine.  The small tributary stream in Common Ravine receives
discharges from the sewage treatment plant, the industrial waste
treatment facility, and the cooling towers.  Substrates were covered
with a white-gray cementing material which rendered habitats totally
unsuitable for colonization of attached algae or benthic
macroinvertebrates.
    Diatom populations during both surveys were extremely de-
pauperate.  Existing organisms were only of cosmopolitan or tolerant
species (Lowe, 1974, and Palmer, 1969).  Most species were represented
by only one or two specimens.
    No fishes or benthic macroinvertebrates were found at this site
during either survey.  The biological communities investigated in this
stream were generally nonexistent due to poor water and habitat quality.

    Rager's Pond Tributary.  The small  tributary stream to Rager's Pond
receives  runoff  from both mining and power plant operation areas.
Oxidation of  ferrous material in these  wastewaters covers the  substrates
with  a bright orange precipitate.
    Diatom collections during spring and winter surveys showed ex-
tremely depauperate  algal communities in this tributary.  No growth was
apparent  except  on  isolated portions of rocks near  the banks which
protruded from the  water.  Two species  were found during the winter
survey and four  during  the  spring  survey.  These  species were
represented by only  one to  three individuals  per  sample.
    No benthic macroinvertebrates  or fishes were  found during  either
survey at this site.  Discharges from raining  and  power plant operations
                                    92

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have severely stressed this small stream.   Poor water and habitat
quality have rendered this stream inhospitable to colonization by
aquatic organisms.

    Two Lick Creek.  The portion of Two Lick Creek which was sampled
flows though industrial, residential,  and  commercial areas.   Previous
studies (Environmental Sciences, Inc., 1972) have shown this large
stream to be an extremely perturbed aquatic system.
    Surveys were conducted on only the attached algae community during
both winter and spring.  The number of species found remained fairly
constant between surveys—relatively high  in comparison with those in
the streams sampled in the area of the coal cleaning facility but very
low for a stream of this size.  Standing crops.were extremely low during
both surveys.  Dominant species were typical of mild to heavy organic
pollution and high nutrient content (Lowe, 1974, and Palmer, 1969).

    Ramsey Run.  Ramsey Run, a moderate-size stream, flows though a
wooded, lightly populated residential  area.  The stream is bounded by
steep banks which are used locally for dumping trash.  A 350- to 400
yard area adjacent to the stream had been  cleared and graded prior to
the time of the spring sampling.
    Ramsey Run was sampled in order to obtain additional data on another
stream not impacted by the Homer City power complex or other industrial
source.  Similar collections of periphyton, macroinvertebrates, and
fishes were made in this stream.  In general, these collections
contained fewer numbers than might be  expected.  However, a diverse  and
stable community of aquatic organisms did  inhabit this stream.
    Algae collections during both the  winter and spring survey showed
evidence of environmental perturbance.  The numbers of species found
were generally low.  Standing crops were high but dominated by large
populations of one or two species. Dominant species, Navicula
lanceolata, N. crytocephala. and N^ Viridula, are characteristic of
waters of high mineral content (Patrick and Reiner, 1966) and mild-to-
heavy organic pollution (Lowe, 1974, and Palmer, 1969).

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     Benthic tnacroinvertebrate collections from this stream revealed a
low  standing crop, composed of a fairly large number of species.
Species diversity indices were 3.20 and 2.58 for winter and spring,
respectively, typifying clean stream conditions (Wilhm, 1970).
     Only  seven  species of fish were found to inhabit this stream.  The
dominant  species, the mottled sculpin (Cottus bairdi), is found in high-
gradient  clean, unpolluted streams (Trautman, 1957).  The presence of
large numbers of this clean water species indicates good water quality.

Fish Tissue Analysis

     Results of  the fish tissue analyses for four metals—arsenic, copper,
nickel, and zinc—are presented in Appendix D (Table 86).  The
majority  of the fishes collected for analysis were bottom feeders, or
those whose food supply is closely associated with the sediments.  The
ranges of selected metals occurring in the sediments at the approximate
locations of the fish collections are presented in Appendix C.
     Generally,  there were few differences between sites in the levels of
the  four  selected metals in the tissues of the fish species analyzed.
In some cases,  levels found in the tissues of fish collected upstream of
the  disposal area tributary were higher than those in tissue of fish
taken downstream at Site 3—specifically, levels of all four metals in
hogsucker and white sucker tissue.
     Levels in samples of muscle tissue ranged between 0.023 Ug/g and
0.11 ug/g (wet  weight) for arsenic and 13.9 to 33.4 yg/g for zinc.
Higher values were reported for analysis of whole minnows which included
gut  contents and therefore may reflect levels found in the sediments.
     Levels of arsenic reported in the literature are generally within
the  range found in the Homer City samples.  Tong, et al., (1974)
reported 0.037  to 0.090 ppm arsenic (wet weight) for lake trout from
Lake Cayuga; Uthe and Bligh (1971) reported 0.05 to 0.15 ppm arsenic
(wet weight) for fishes from polluted and unpolluted area in the Great
Lakes region.  The levels found in the tissues of fishes from the Homer
City area fall below the 0.5 ppm concentration recommended for arsenic
in muscle tissue for human consumption (Rooney,  1973).

                                    94

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     Levels of zinc  found  In  fish  tissue  at  Homer  City were  similarly
 within ranges reported  in  the  literature—11  to 20  ppm  (wet weight) for
 fishes from polluted  and unpolluted  area of the Great Lakes region (Uthe
 and  Bligh,  1971).   Those values that were considerably  higher than 20
 ppm  were  again from samples  of whole minnows.
     Levels of nickel  and copper found in fish  tissue reported in the
 literature for fishes from clean  and polluted  waters are within the
 range  of  0.2  to  1.3 ppm (wet weight) (Tong, et al., 1974; Uthe and
 Bligh,  1971;  and Lucas, et al., 1970).   These  same  authors report the
 range  of  levels  of  copper  in fish tissue as 0.015 to 1.28 ppm (wet
 weight).   Levels found  in  fish muscle tissue at Homer City ranged from
 5.73 to 98.8  ppm (wet weight)  for copper and 1.01 to 24.9 ppm (wet
 weight) for nickel.   These values are considerably  higher than would be
 expected.   It  should  be noted  here that  two types of sample preparation
 were utilized  in making the metals determinations.  One method consisted
 of homogenizing whole fish (minnow) samples by hand using a glass and
 Teflon homogenizer.   Larger  tissue samples  were homogenized in a blender
 with blades primarily of iron, nickel, and  chromium.  Tissue samples
 prepared  by hand showed lower  copper and nickel values  than those
 prepared  by the blender method.   Hence,  little significance can be
 applied to  these copper and  nickel values.

 Stream Biological Quality

    The aquatic survey of  the  area of the Homer City power complex
 covered eight streams.  Quality in a control stream (Ramsey Run) was
 evaluated as good and provided a  base for comparison.  Stream quality
 ranged from excellent to very  poor.  A subjective evaluation of the
 streams surveyed in this study is presented in Table 13.  A subjective
 quality evaluation was made of each biological group investigated; an
 overall stream quality rating was then made for each stream.
    Three streams,  the tributary  to Cherry Run north of the refuse area,
 the tributary to Wier's Run,  and Ramsey Run, were considered to have
good overall biological quality.   Additionally, the upstream portion of

                                    95

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                           TABLE  13.  BIOLOGICAL QUALITY EVALUATION OF  STREAMS SURVEYED
                                      IN THE AREA OF THE HOMER  CITY POWER  COMPLEX
VO
ON


Biological Cherry
components
Periphyton
Benthic macro-
invertebrates
Fishes
Overall
rating
Run
F

P
F

F
Tributary to
Cherry Run north
of refuse area
F

G
G

G
Tributary to
Cherry Run south Tributary
of refuse area to Wier's
Upstream
F

G
G

G
Downstream Wier's Run Run
P G F

PGP
PGP

PGP
Rager ' s
Pond Common
tributary Ravine
P P

P P
P P

P P

Ramsey ' s
Run
F

F
G

G

G = Good
F = Fair
P = Poor



















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the tributary south of the proposed refuse disposal area was considered
to be of good quality.
    Cherry Run was evaluated as having fair biological quality based on
the number of fish species inhabiting this stream.   However, the quality
of the biological community inhabiting Cherry Run has been affected by
both plant and mining operations in the area.  Low standing crops of
macroinvertebrates and fishes clearly demonstrate this perturbance.
    The remaining streams—Wier's Run, Rager's Pond tributary, Common
Ravine tributary, and the downstream portion of the tributary south of
the disposal area—were all considered to have extremely poor biological
quality.
                                     97

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                   COAL CLEANING REFUSE DISPOSAL SITE

                            Site Description

    Refuse from the Homer City coal cleaning plant will be disposed of
on a hillside site 3600 feet northeast of the plant (Figure 26).  There
are approximately 200 feet of relief (elevation 1100 to 1300 feet) in
the disposal area, and natural slopes average about 12 percent.   Size of
the disposal site is approximately 180 acres.
    East of the site is Cherry Run, which flows south to Two Lick Creek.
North and south of the site are unnamed tributaries to Cherry Run.
Total drainage area of the two tributaries is about 2000 acres.   On the
basis of USGS flow records for Two Lick Creek, average annual discharge
from this basin is equivalent to 21.68 inches.  Therefore, combined
average discharge from the unnamed tributaries can be estimated at about
5.0 cfs or 2250 gpm.
    The site is underlain by sandstone, siltstone, and shale.  Bedding
is nearly horizontal.  Two principal waterbearing formations beneath the
site are the source of numerous small springs on the hillsides on the
southeast and west sides of the site.   The discharge from each of these
springs is generally less than 5 gpm.  The location of the springs and
the regional geology suggest groundwater flows from north-northwest to
south—southeast.
    Soils in the refuse area were examined by the disposal facility
design engineer.  The fairly shallow (1 to 10 feet) soil layers over
bedrock were found to be silt loams.   The U.S. Soil Conservation Service
has rated the erosion potential of these soils as moderate.  No
permeability tests were performed on the natural soils of the area, but
the disposal facility design engineer estimated permeability at less
than 1Q~6 cm/sec.
                                    98

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           C*    Cool cleonino/l
                      plant
                                            0       2500     50OO

                                                  SCALE, FEET
FIGURE 26.   COAL CLEANING REFUSE  DISPOSAL AREA
                       99

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                            Facility Design

Landfilling Stages

    The disposal facility was designed for a 30-year lifetime.  Refuse
disposal, by landfill, will be done in four stages (Figure 27) and
involve four fill areas.  The first refuse disposal stage is intended to
extend over a 1-year period and will fill a valley on the southwest
flank of the disposal site.  Refuse will be placed behind a non-
impounding embankment to an elevation of 1170 feet.  Stage II disposal
will be atop Stage I; this will extend the fill area and raise the
elevation to 1290 feet.  Stage II is intended to last for about 9 years.
     Stage III  refuse disposal  will  fill  a  valley on  the  southeast  flank
of the  hill, behind  a nonimpounding embankment, to an elevation of  1175
feet.   Stage III will  last  for 4  years.   Stage  IV  refuse disposal will  be
atop Stage  III;  this will  extend  the  fill  area  to  180 acres  and raise
the elevation  to a maximum  of  1290  feet.   When  completed,  the  site  will
hold 30 million tons of coal  cleaning  refuse.

Water Protection Measures

     The facility design incorporates several  water-protection measures.
Diversion ditches will be  constructed  to reduce surface  erosion on the
 site.  These  will divert all  surface drainage around the disposal  area
 into a  siltation basin. In addition,  runoff  from  the disposal surface
 itself, which might  be high in suspended solids,  will be directed  to the
 siltation basin.  There will  be separate siltation basins  for Stages I
 and III.
     Siltation basins were designed to conform to  recommendations  of the
 Pennsylvania Department of Environmental Resources (Penn DER).  The
 Stage I and Stage III ponds have storage capacities of  0.68 and 0.78
 million cubic feet,  respectively.  A 12-inch pipe has been installed for
 normal discharge of clarified water from the pond.  However, emergency
                                    100

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   'N.
            Disposal Area Limits
                                                                                           Sedementation Pond
                                                                                              (Stage HI)
                Stage I Limits

               "50-'
                                           Sedimentation Pond
                                              (Stage I
Temporary Storm Drain
                                                                                                Leachate Pond
                                                                                                 (Stage EL)
                                                                               0   200  400  6OO
                                                                                  SCALE, FEET
Leachate Pond
  [ Stage I)
               FIGURE 27.   DISPOSAL STAGES AND POND LOCATIONS

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overflow weirs have been installed to prevent overtopping the dikes in
the event of excessive storm runoff.  No treatment other than settling
is provided for sedimentation-pond discharges.
    During construction and during the earliest period of refuse
disposal in Stage I, natural surface drainage will be diverted through
the nonimpounding embankment via a 12-inch pipe (Figure 27).  This
diversion was designed to be used until the fill reaches a predetermined
elevation (1110 feet), at which time the surface diversion ditches and
sedimentation pond will be used and the pipe will be grouted.
    According to the facility design engineer, all hydraulic char-
acteristics of the ponds and ditches have been designed to conform to
Penn DER guidelines and the Mining Enforcement and Safety Administra-
tion's (MESA) design criteria for coal-cleaning refuse disposal facil-
ities.  The design storm for the surface drainage facilities was a
100-year storm, which corresponds to a 2.7-inch rainfall over a 1-hour
period.
    Surface waters will be further protected by clearing only the land
area required for each stage as it is needed and by prompt revegetation
of completed areas.
    The disposal facility design calls for groundwater in and around the
disposal area to be protected by means of a leachate collection and
treatment system.  A rock underdrain, consisting of 3- to 6-inch cobbles
wrapped in filter cloth, has been placed in the major valley bottoms.
Smaller drains of similar construction are to be installed wherever
springs are encountered.
    The design called for these drains to be constructed on the existing
natural ground surface.  The facility design engineer reasoned that the
existing soil surface, consisting principally of silts, would be
relatively impermeable and that leachate would flow preferentially into
the underdralns, thereby preventing infiltration of leachate into the
ground and eventually into the groundwater.  The main underdrains were
designed to handle an estimated peak flow of 150 gpm.
    The underdrains will carry leachates to two leachate ponds.  The
ponds serve as equalization basins to capture peak flows and provide a

                                   102

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relatively uniform feed rate to the leachate treatment  system.   The
ponds are designed for 24-hour  retention of the  estimated  150 gpm  peak
flow from the underdrains.  Collected leachate will  be pumped  to  a  treat-
ment facility.   An 8-inch pipe  has  been installed near  the crest of  the
pond dike to serve as an "emergency overflow".
    Water quality characteristics of the leachate are estimated  by the
design engineer to be as follows:

             pH                    2.0-2.5
             Acidity               5000-7000mg/l
             Iron                  5000-1000 mg/1
             Suspended Solids      250 mg/1

No estimate or mention of other possible water quality parameters  was
made by the design engineer.
    The leachate will be treated at an off-site  mine-drainage-treatment
facility of the Helvetia Coal Company.  The only treatment known or
expected to be provided by this facility is lime neutralization  and
settling.  This treatment has been approved by the  Penn DER,  which views
coal preparation refuse the same as coal ash and other mine wastes and
considers acid drainage to be the only important potential pollutant.
                   Potential Operational Problems—
                          Pollution Potential
    Certainly leachate will be generated in this disposal facility, as
the facility design engineer has anticipated.  However, evidence from
numerous investigations of various types of coal, coal ash, and coal
refuse leachates indicates that other water quality parameters than
those anticipated by the facility design engineer may be affected.
Among these are sulfate, calcium, various metals, and total dissolved
solids.
    The underdrain system is only one possible avenue of escape for
leachate.  The facility design engineer assumed that the underdrain
would be placed on top of the natural soil, which as mentioned before
                                   103

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consists primarily of silts.  The engineer expected that the silty soil
would prevent downward migration of the leachate and that the leachate
would flow preferentially into the underdrain system.   This is not
necessarily so, however.  If the underdrain should become plugged, or
hydraulically overloaded, or if differential settlement should reverse
the grade of the drain locally, a head may develop within the refuse
which would allow leachate to penetrate the silt soils and percolate
downward toward the groundwater table. More importantly, however,  the
natural soils were disturbed and in places removed during site prepara-
tion, probably to improve the grades.  In fact, the main underdrain for
Stage I has been constructed partly in bedrock, which in that area is
sandstone.  A certain amount of leachate may find its  way out of the
site and into groundwater or surface water via that path.
    Another potential point of leachate migration is the temporary storm
drain, described previously, to divert natural drainage through the
embankment during construction and early disposal.  This pipe has  been
installed at a lower elevation than the leachate collection drain  at
this point.  Therefore, any leachate formed in Stage I will flow toward
the temporary storm drain rather than the leachate collection  drain.
Water is already channeling alongside this pipe, through the embank-
ment.  Leachate will follow this same path, unless the pipe and the
embankment below the level of the leachate drain are carefully sealed.

                 Recommendations  for Future Monitoring

     To  measure  the  infiltration of  leachate  into  the  soil within  the
disposal  area,  soil  testing  should  be done before  and during operation.
This  will enable  the owners  of  the  cleaning  facility  to  measure the
rate  of migration of leachate down  through the  soil toward  the ground-
water.  Measurement  before  the  facility is in  operation  is  essential  to
establish background levels.  Tests should be  run  on  the water quality
parameters described previously in  this section, especially for metals,
which have a  tendency to be  adsorbed on the  soil  particles.
    At  least  three  deep soil  borings  should  be made for  the purpose  of
establishing  clearly the local  groundwater gradient.  These borings
could also be used  for groundwater  monitoring.
                                    104

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    Monitoring of the possible discharges described above should be
initiated.  These discharges include (1) treatment system effluent,
(2) sedimentation and overflow, and (3) the temporary storm drain
discharge. The leachate pond should also be monitored to establish the
characteristics of this particular leachate.   Stream monitoring in the
tributaries to Cherry Run north and south of the site, downstream of the
disposal area, will help detect any leachate that might get into the
sandstone bedrock and be carried laterally to a surface discharge point.
Stream monitoring will also help detect any other possible seepage.
                                   105

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Spaulding, W. M., Jr., and R. D. Ogden, 1968.  "Effects of Surface
Mining on  the Fish and Wildlife Resources of the United States",
Resource Publication 68, U.S. Department of the Interior, Fish and
Wildlife Service, Washington, D.C. (August, 1968), 51 pp.
                                   107

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Stumm, W., and J. J. Morgan.  1970.  Aquatic Chemistry—an Introduction
Emphasizing Chemical Equilibria in Natural Waters, John Wiley and Sons,
New York, 583 pp.

Stumro, W. n.d.  "The Chemistry of Natural Waters in Relation to Water
Quality".  Unpublished, 26 pp.

Stumra, W., and G. F. Lee.  1960.  "The Chemistry of Aqueous Iron".
Sonderabdruck aus schweizerische zeitschrift fur hydrologie, Birkhauser
Verlag Basel, Vo. 21, Fasc. I.

Todd, W.E.C.  1940.  Bj^rds of Western Pennsylvania, University of
Pittsburgh Press, Pittsburgh, Pennsylvania, 710 pp.

Tong, S., W. Youngs, W. Gutenmann, and D. Lisk.  1974.  "Trace Metals in
Lake Cayuga Lake Trout (Saluelinus namaycush) in Relation to Age", J.
Fish.  Res.  Bed. Can., M.(2), 238-239.

Trautman, M.  1957.  The Fishes of Ohio, Ohio State University Press,
Columbus, Ohio, 683 pp.

U.S. Department of the Interior.  1974.  Water Resources Data for Pen-
nsylvania, Part 2.  Water Quality Records, Geological Survey.	

U.S. Environmental Protection Agency.  1969.  Chemistry Laboratory Man-
ual Bottom Sediments.  Compiled by the Great Lakes Region Committee on
Analytical Methods.

U.S. Environmental Protection Agency.  1976.  Quality Criteria for
Water.  U.S. Environmental Protection Agency, Washington,  D.C., EPA
440/9-76-023.

Uthe, J., and E. Bligh.  1971.  "Preliminary Survey of Heavy Metal Con-
tamination of Canadian Freshwater Fish", J. Fish. Res. Bd. Can., 28(5)
786-788.

Vaughan, B.  G., K. H. Abel, D. A.  Cataldo, J. M. Hales,  C. E. Hane, L.
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"Review of Potential Impact on Health and Environmental Quality from
Metals Entering the Environment as a Result of Coal Utilization.  Bat-
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Warner, R. W.  1971.  "Distribution of Biota in a Stream Polluted by
Acid Mine Drainage".  Ohio J.  Sci.  71(4):202-2l5.
                                   108

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Weed, C. E., and C. W. Rutschky, III.  1972.  "Benthic Macroinvertebrate
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Note:  Appendix references appear at the end of each appendix.
                                    109

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       APPENDIX A
FUGITIVE DUST MONITORING
            110

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                               APPENDIX A
                        FUGITIVE DUST MONITORING

                      Location of Monitoring Sites

     In designing an air monitoring system,  the first  consideration is
generally given to the purpose for monitoring.   Are maximum concentrations  of
primary interest or is a spatial representation of  average concentrations of
special importance?  In monitoring fugitive dust near  the Homer City coal
cleaning facility, Battelle wanted to obtain both a spatial distribution of
the dust deposition and the magnitude of the maximum concentrations.  The
second important consideration is the nature of the emissions.   Since the
dusts in the study area are fugitive in nature, it  is  reasonable to assume
that the greatest impacts will occur within short distances downwind from the
sources; therefore, monitoring efforts should be concentrated in that area.
     Ten monitoring sites were selected, carefully  keeping in mind the consider-
ations noted above.  A Fugitive Dust Emission Model was developed by Battelle
to aid in the monitoring site selection (see section on Modeling Activities in
this Appendix).  The locations of the monitoring sites are shown in Figure  2.
Five sites (1, 2, 3, 4, and 7) are located in the immediate vicinity of the
power plant operations.  The remaining sites (5, 6, 8, 9, and 10) are well
removed from the center of these operations.
     Sites 1, 3, 4, 8, and 9 were selected to show a spatial distribution of
dust concentration (including the maximum) during periods of prevailing wind
flow from the south-southwest.  Site 3 would also provide baseline data prior
to the start-up of the coal cleaning plant.  Site 2 would show the maximum
concentrations from the coal pile when the wind was from southwest-west.  Site
5 was selected to evaluate the air quality impact of the ash disposal area
when the wind is from the west or southwest.  Site 6 served as a site for
background concentrations for any wind direction between southeast to north.
                                     Ill

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Site 7 was selected to show the air quality impact from plant operations for
a northwest wind.  Finally, Sites 9 and 10, 1800 and 2000 meters, respectively,
from the plant were chosen to indicate whether fugitive dust was being
transported to these distances.

                         Diffusion Model Results

     The results obtained from the Fugitive Dust Emission Model developed by
Battelle to evaluate potential sites for monitoring are summarized below.  The
distances given agree favorably with the locations of the monitoring sites
situated around the power complex's operations.  The term "major axis" relates
to the nonuniform shape and specifies the orientation of each source.  (See
the following section on Modeling Activities in this appendix.)
       Source
Coal Pile

Boney Pile

Ash Disposal
  Area
      Wind Direction
Perpendicular to Major Axis
Parallel to Major Axis
Perpendicular to Major Axis
Parallel to Major Axis
Perpendicular to Major Axis
Parallel to Major Axis
  Distance of Maximum
Fallout Concentrations,
	meters	__^
       250-400
       400-500
       150-300
       200-400
         0-100
         0-100
     The locations of the ten sampling sites in relation to the dust sources
are listed below:
Site 1  - Located about 175 meters northeast of coal storage pile and
          300 meters northeast of the coal cleaning facility
Site 2  - Located about 200 meters southeast of the coal storage pile
Site 3  - Located about 150 meters northwest of the coal storage pile
          and 50 meters northeast of the coal cleaning facility
Site 4  - Located about 400 meters north of the coal storage pile and
          about 300 meters east of the boney pile
Site 5  - Located about 200 meters east of the ash disposal area
Site 6  - Located on a farm about 1600 meters southwest of the coal
          cleaning facility
                                    112

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Site 7  - Located about 500 meters southwest of coal storage pile and
          adjacent to an unpaved parking lot at the property line of
          the power complex
Site 8  - Located about 1200 meters north of coal storage pile in an
          area that is being readied to handle the refuse from the
          coal cleaning facility
Site 9  - Located about 1800 meters north of the coal storage pile
          near the property line of the power complex
Site 10 - Located on a farm about 2200 meters northeast of the coal
          storage pile.

                          Fugitive Dust Sources

     Fugitive dust sources identified on the power complex property include
an ash disposal area, where fly ash and bottom ash are routinely deposited
by trucks; a boney pile, which serves as a refuse area for undesirable coal
from the mining operations; and a large coal pile from which coal is  fed into
the coal-fired boilers.  Future potential sources include the proposed coal
cleaning facility to be located adjacent to the coal storage pile, and the
proposed refuse area for this facility.  These sources are shown in Figure 2.
     The ash disposal area encompasses about 17.7 acres and is irregular in
configuration.  Bottom and fly ash are spread uniformly over the area; the
height of the ash disposal area is only slightly above ground level.
     The boney pile is also of irregular shape and covers an area of about
11.1 acres.  This pile extends well above the ground, and the average height
is 60 feet.
     The largest source of dust, with regard to both land area and amount of
airborne coal particles expected, is the coal storage pile.  It occupies an
area of approximately 20 acres and is of rectangular configuration.  The coal
pile towers well above the ground, averaging about 100 feet in height through-
out its length and breadth.
     The coal cleaning facility is a ten-story structure which will also be
a fugitive dust source.  As the plant will be enclosed with sheet metal, it
is expected that the rate of emissions will be lower than those characteristic
of older coal cleaning plants.

                                    113

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     Other fugitive sources near the coal cleaning facility operations Include
vehicular traffic and construction activities.  Construction has been ongoing
for a number of years and is projected to continue for at least two more
years.  Also, coal from two storage silos is carried by conveyor belts and
deposited onto the coal pile.  Coal particles are released during this operation.
Although the conveyor belts were not identified as a principal source of
fugitive dust since they are almost fully enclosed, coal dust does escape
from the bottoms of these belts.

                           Modeling Activities

Description of Model and Modeling Approach

                                            (A—1)
     Battelle's Fugitive Dust Emission Model      is based on U.S. EPA's
                                    (A-2)
Multiple Point Source Model (PTMTP).       It predicts hourly mass concen-
trations of fugitive dust at any number of downwind distances.  Several major
alterations were made to EPA's PTMTP.
     First, sources of fugitive dust were treated as area sources because of
the dimensions of the area occupied by these types of sources.  For example,
the dimensions of the coal pile are 1.36 x 0.6 km, or 21.5 acres.  To consider
each source as an area source, the concept of a virtual point source was
                          (A-2)
programmed into the model.       This assumes that the area sources are squared
and requires the user to input the length of one side.  In the study at the
power plant, each source was angular in configuration.  Therefore, each fugi-
tive dust source was subdivided into area sources approximately square in con-
figuration.
     To mathematically permit the deposition of fugitive dust particles, a
simple particle deposition function was incorporated in the model.  The amount
of material deposited on a receptor location is a function of wind speed,
emission rate, distance, and particle size, density, and shape.  As wind speed
increases, more dust becomes entrained in the surface circulation (i.e., the
emission rate increases), thereby creating a greater likelihood for a large
amount of dust deposition.  The smaller the size, the less dense the particles
released into the wind and the further downwind they will be transported before
settling to the ground.  The distance where the maximum amount of fallout will
occur is obviously dependent on the wind speed, particle size, density, and
shape.
                                     114

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     The particle deposition function (Vx/u)  was programmed in the  model  as
a distance.  V, the settling velocity,  was assigned a velocity which reflected
a range of particle sizes.   The coal pile at  Homer City is  believed for the
most part to be made up of granulated coal particles greater than 30 microns
in diameter.  Thus, in the modeling work, it  was assumed initially  that most
of the particles released from fugitive sources were greater than 30 microns
in radius.  Later it was found that predicted concentrations were independent
of particle sizes greater than 15 or 30 microns.  The deposition function was
applied to all receptor distances and the resulting value was assigned to
receptor height.  This approach effectively increased receptor heights at all
downwind distances for a flat terrain.   By defining a deposition function in
this manner, one does not have to manipulate plume centerline calculations,
which coincidentallyare normally not relevant where dealing with coal storage
and coal refuse sources.  The height of the local terrain is then added to
the height determined by the deposition function.
     A third modification of EPA's PTMTP involved the formulation of an
emission rate rather than a direct input of emissions for each fugitive dust
source.  First approximations of emission rates for each of the sources in the
study area were based on an article written by S. L. Vekris, M.Sc., and pub-
                                               (A_0\
lished in the Ontario Hydro Research Quarterly.    '  The study on dispersion
of coal particles from a storage pile was conducted at the Lakeview Generating
Station on the north shore of Lake Ontario.  Mr. Vekris found that for a coal
pile covering 40 acres and extending from 0 to 30 meters above the ground,
and for a wind speed of about 9 m/sec,  an emission rate of 50 g/sec was reason-
able to assume in modeling work for particles greater than 30 microns in radius.
     Subsequently, a constant was calculated which expressed the ratio of the
acreage occupied by each source of fugitive dust at the Appalachian power
station to the acreage of the coal pile at the Lakeview Generating Station.
The value of this ratio is then multiplied in the emission rate equation by
the square of the wind speed.  The amount of dust released, whether it origin-
ated from a coal, ash, or terrestrial source, has been programmed to be directly
proportional to the energy imparted by the wind, that is, to the square of the
wind speed.
     Finally, a constant, K, was formulated in the emission rate equation which
is used after the first computer run in estimating the emission rate for all of
                                    115

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 the sources.   The constant  represents  the  value of  the  slope of the regression
 line.   The general form of  the emission rate  equation is
                     _         2   Area  (acres)
                     Q = K x u  x  —. n   	-
                                    40  acres
     Additional modifications to  EPA's PTMTP  included the elimination of the
 plume  rise routine.  It was assumed that none of  the sources of fugitive dust
 considered in  this study imparted any  thermal buoyancy  to the airborne particles.

 Methodology for Determining Coefficient of Emission

     To determine  the value of the coefficient of emission, formulated in the
 emission model and discussed in a previous section, a linear regression
 analysis was performed  using the  observed data and  the model's first approxi-
 mations.   A linear regression analysis is a statistical method which correlates
 one variable to another.  It involves  the theory of the minimization of the sum
 of  least squares.
     If it is assumed that  a straight  line approximately describes the fit of
 observed data to  the model's predictions of the observed concentration, then
 this relationship  takes  the  following  form and is commonly referred to as the
 line of regression:
                    Y =  a +  bx,
where  a and b represent  the  intercept  and slope, respectively.   In determining
 the  values of a and b,   it becomes necessary to decide which line best de-
scribed the observed data and model first approximations.   The  principle of
 least  squares aids  in calculating  the  values of the intercept,  a,  and the
 slope, b.  It states that the  line of  best fit to a series of values is that
 line about which the sum of  the squares of the deviations (the difference
between the line and the actual values) is a minimum.
     The result of the sum of least squares is given in the following form
of the line of regression:
                    P - 59.5 +• 1.47 x  .
     The value of the slope of the line, 1.47, now becomes the  value of the
coefficient of emission, K.   This value was substituted  into the emission rate
equation,  and the results of Battelle's Fugitive Dust  Emissions  Model  are

                                      116

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shown in Figure 28.  A line that best fits the predicted versus observed
data has been drawn.

Results of Diffusion Modeling

     The development of a reliable diffusion model which could be applied to
fugitive dust sources was achieved.  Battelle's Fugitive Dust Emission Model
served two functions:  one, to aid in selection of monitoring sites,  and
two, to predict particulate concentrations at the monitoring sites or at
any desirable location.
     The model's output, which was studied in selecting potential sites for
monitoring, is summarized below.  The term "major axis" refers to the longest
axis of the source configuration.
     Basically, the effectiveness of Battelle's Fugitive Dust Emission Model
in predicting concentrations can be best illustrated by Figure 28.  In con-
structing Figure 28, an average concentration of all 24-hours for the three
campaigns was determined from the observed and predicted data and plotted for
each monitoring site.  A regression line has been drawn that best fits the
data points.  Perfect correlation would exist between observed and predicted
concentration if all data points would lie along the regression line.
     With any diffusion model, perfect correlation between observed and pre-
dicted concentration is seldom, if ever, achieved.  Figure 28 shows that
perfect correlation between what the model predicted and what was observed was
not achieved.  However, it is quite an accomplishment that the correlation is
good or that the scatter of data points about the regression line is minimal.
Diffusion modeling of fugitive dust sources is extremely more difficult than
modeling of point sources with stacks.  More is known about the dispersion
of effluent from stacks than the dispersion of fugitive dust (coal dust) from
unconfined sources such as the coal pile, and the ash disposal area.
     Since Battelle's Fugitive Dust Emission Model is a Gaussian diffusion model,
its sensitivity to input data is similar to most point source models.  In
particular, conclusions which have been determined from the model's response
to the input data are summarized below:
     (1)   It was found that the predicted concentrations were
          independent of particle size greater than 15 microns;
          that is, the predicted concentration remained
                                    117

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25
50         75        100
  Predicted Concent rati on,
(25
                                                       150
                                                                   175
FIGURE 28.  RESULTS OF LINEAR REGRESSION ANALYSIS
            (PREDICTED VERSUS OBSERVED)
                        118

-------
           essentially  unchanged  for any particle  size  15 microns
           or greater.
      (2)   Long-term predictions  have  less random  scatter from
           observed  concentrations  than short-term predictions
           because the  random atmospheric dispersion  processes,
           not accounted  for  by the diffusion model,  are averaged
           out in the passage of  time.  This is  illustrated  by a
           set of concentration data presented in  Table 14.   It
           should be noted that the predicted concentrations do
           not include  the background  concentration,  which has been
           estimated to be between  30  and 40  yg/m  .
      (3)   During periods of  light  (1-4 mph)  and variable winds,
           essentially  zero concentration was predicted at all
           sites. This does  not  include a background concentration
           of 30-40  yg/m .  The observed concentrations were signi-
           ficantly  greater than  those predicted at  sites  situated
              TABLE 14.   SHORT-TERM AND LONG-TERM CONCENTRATIONS
                         VERSUS OBSERVED  CONCENTRATIONS
Predicted(a)
Concentrations
2nd 24 hr
Sites Campaign III
1 100
2 55
3 3
A 11
5 4
6 0
7 0
8 8.3
9 5
10 6
Observed
Concentrations
2nd. 24 hr
Campaign I
325
250
392
144
78
38
68
145
42
57
Predicted^
24-hr average
Concentrations
All Campaigns
68
58
26
32
6
0
1.5
2
1
1
Observed
24-hr average
Concentrations
All Campaigns
141
161
152
77
60
44
68
95
40
51
                                          T
* A background concentration of 30-40 yg/m  should be added to the
  predicted concentrations.

                                    119

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          close to plant operations.   For the wind pattern  shown in
          Table 15, the predicted and observed collection are shown
          in Table 16.   With the addition of background concentrations
          to the predicted concentration, the model at some of the
          monitoring sites underestimated dust concentrations.

Possible Causes of Scatter About Regression Line

     Figure 28 shews a significant scatter about the line of regression.
This could be attributed to several factors.
     First, a number of sources were not included in the modeling work
because of their nature.  These include construction activities, vehicular
traffic, and parking lots, and the conveyance and dumping of granulated coal
from several storage silos onto the coal storage pile.  After careful examin-
ation of the observed data and the model's predictions, it is believed that
all of these sources plus the general dusty surfaces of the power plant are,
in some instances, contributing significant amounts of dust.  It is believed
that stack emissions, under certain meteorological conditions, contributed a
significant amount to the total mass particulates collected at several of the
monitoring sites.
     The results of an optical review of the sampling filters for Campaigns I
and II are given in Tables 19, 20, and 21 in the section on Microscopic
Analysis on page 128.  On numerous occasions there were at least some deposits
of soot on the sampling filters.  The soot either was released from the
stacks, was emitted as a product of combustion associated with the diesel-
fired equipment, such as coal trucks, or was reentrained off the grounds of
the power plant and onto the filters.  For example, during Campaign II at
Sites 5, 6, 9, and 10, ash constituted almost half of the total mass concen-
tration.  It is highly unlikely to expect the ash disposal area to be the
principal source of the ash since all of the filters at Sites 5, 6, 9, and
10 had a moderate-to-large amount of soot deposits.  In particular, one
filter  (at Site 10—operated for 24 hours) was reported to be sooty.
     Soot deposits were also reported at the sites located on plant property
(Sites 1, 2, 3, 4, 7, and 8).  Here soot may be originating off the plant
grounds and/or originating from vehicular traffic.  Notice too that there

                                    120

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        TABLE 15.   WIND  SPEED  AND  DIRECTION  DURING  CAMPAIGN  II--
                   FIRST 24-HOUR PERIOD
Date/Hour
Jan. 5, 1977
2000-2100
2100-2200
2200-2300
2300-2400
Jan. 6, 1977
2400-0100
0100-0200
0200-0300
0300-0400
0400-0500
0500-0600
0600-0700
0700-0800
0800-0900
0900-1000
1000-1100
1100-1200
1200-1300
1300-1400
1400-1500
1500-1600
1600-1700
1700-1800
1800-1900
1900-2000
Wind
Direction

50
315
165
150

80
135
140
85
60
50
35
225
230
242
235
230
240
230
237
225
225
225
225
220
Wind, ,
Speed ,(a)
mph

2.0
3.0
4.0
2.0

1.5
1.0
3.0
2.0
2.5
3.5
2.0
2.5
2.0
2.0
2.5
4.0
4.0
5.0
7.0
10.0
8.5
7.5
8.5
7.5
Site

1
2
3
4

5
6
7
8
9
10














(a)   Conditions were not calm through the entire 24-hour period.  The
     wind direction became more defined in the second 12-hour period.
                                    121

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     TABLE 16.   COMPARISON OF PREDICTED VERSUS  OBSERVED  CONCENTRATIONS
                DURING PERIODS OF LIGHT VARIABLE WINDS DURING
                CAMPAIGN II—FIRST 24-HOUR PERIOD
        Date/Hour
Site
   Predicted
Concentration
     yg/m3
                                              (a)
                                   Observed
                                Concentration,

2000-2100
2100-2200
2200-2300
2300-2400

2400-0100
0100-0200
0200-0300
0300-0400
0400-0500
0500-0600

1
2
3
4

5
6
7
8
9
10
January 5, 1977
23
9
12
1
January 6, 1977
7
0
0
1
1
1

95
18.3
136
67

96
76
110
96
41
82
— — — 	 „ _.__ ,.
        (a)  The predicted concentrations do not include a background
            concentration of 30-40
was no significant amount of tertiary deposits on any of the filters.  This
indicates that construction dust, in itself, is not a major source of fugitive
dust at the power plant and that most of the dust on the plant's grounds
originated from coal or ash sources.
     Third, the method used in averaging hourly wind direction and wind speed
data may account for some scatter about the line of regression.  For example
during a given hour, the direction of the wind fluctuated quite severely
and it is difficult to include these fluctuations when representing the wind
directions for a given hour with a single value.   To remedy this, wind direc-
tion data should be averaged over 15-minute intervals in any future studies
                                    122

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                               Survey Data

Particulate Concentrations

     All of the samples were collected on 8 x 10-inch fiber glass,  high-volume
filters, for periods of 12 or 24 hours.  The filters were weighed before and
after each sampling to determine the mass of the particles collected.  The
weighing of samples was performed by Battelle-Columbus personnel.
     Generally, the maximum concentrations were observed at Sites 1, 2, and
3.  These sites are located adjacent to the coal storage pile; also, the
maximum concentrations occurred during the 8 a.m; to 8 p.m. sampling periods.
During the first campaign (Friday, December 17 to Sunday, December 19, 1976),
sampling was conducted on the weekend to reduce the .impact of fugitive emissions
from construction activities.  The particulate mass concentrations found at
each sampling site for each time frame are given in Table  17.  The average
                                                                 2
(arithmetic) concentration for the 12-hour samples was 114.0 yg/tn , while the
                                           3
average for the 24-hour samples was 52 yg/m .  The maximum and minimum concen-
                                                         o
trations for the 12-hour samples were 564.0 and 30.0 ug/m  , respectively,
while the maximum and minimum concentrations for the 24-hour samples were
                   o
110.0 and 28.0 ug/m  , respectively.
     During Campaign III, a particle sizing distribution sampler was operated
at Sites 2 and 3; however, valid data were obtained only at Site 3.  Approxi-
mately 44 percent of particles were in the 0 to 1.1 micron range.  These data
are presented in Table 18.

Microscopic Analysis

      The objective  of  the microscopic  analysis was  to  provide a  distinction
between the various  fugitive dusts  such  as pollen,  construction  dust,  coal
dust, and  coal ash  dust.
      Each  filter  pad was  examined under  a low-power stereomicroscope to see
whether the particulate matter  was  evenly distributed  and whether  the pads
were  smeared  during handling.   Once these conditions were ascertained,  a
small piece,  approximately  1/2-inch square, was  cut from the pad and further
analyses were conducted on  these small pieces.   The small pieces of filter
pad were placed on  a glass  slide and a drop of  lens immersion oil  (index
                                    123

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TABLE 17.  PARTICULATE CONCENTRATIONS IN THE VICINITY
           OF THE COAL CLEANING FACILITY
Sampling
Site Date
1 17-18 Dec 76
18 Dec 76
18-19 Dec 76
19 Dec 76
5-6 Jan 77
6 Jan 77
6-7 Jan 77
7 Jan 77
5-6 Apr 77
6 Apr 77
6-7 Apr 77
7 Apr 77
2 17-18 Dec 76
18 Dec 76
18-19 Dec 76
19 Dec 76
5-6 Jan 77
6 Jan 77
6-7 Jan 77
7 Jan 77
5-6 .Apr 77
6 Apr 77
6-7 Apr 77
7 Apr 77
3 17-18 Dec 76
18 Dec 76
18-19 Dec 76
19 Dec 76
5-6 Jan 77
6 Jan 77
6-7 Jan 77
7 Jan 77
Suspended participates
Time concentration, yg/m3
12-Hour Samples
8 p.m. -8 a.m.
8 a.m. —8 p .m.
8 p.m. -8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m. -8 p.m.
8 p.m. —8 a .m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p. mi
8 p.m.— 8 a.m.
8 a.m.— 8 p .m.
8 p .m.— 8 a .m.
8 a.m. —8 p .m.
8 p.m.— 8 a.m.
8 a.m.— 8 p .m.
8 p.m. -8 a.m.
8 a.m.— 8 p.m.
8 p.m. -8 a.m.
8 a.m.— 8 p.m.
8 p.m. -8 a.m.
8 a.m.— 8 p.m.
8 p .m. —8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m. -8 a.m.
8 a.m.— 8 p .m.
8 p .m.— 8 a .m.
8 a.m.— 8 p .m.
78
Invalid data
Invalid data
Invalid data
54
136
60
56
149
124
252
398
107
69
60
306
59
230
63
294
79
168
209
291
75
87
72
70
82
189
58
92
                        124

-------
TABLE 17.  (Continued)
Sampling
Site Date
5-6 Apr 77
6 Apr 77
6-7 Apr 77
7 Apr 77
4 17-18 Dec 76
18 Dec 76
18-19 Dec 76
19 Dec 76
5-6 Jan 77
6 Jan 77
6-7 Jan 77
7 Jan 77
5-6 Apr 77
6 Apr 77
6-7 Apr 77
7 Apr 77
5 17-18 Dec 76
18 Dec 76
18-19 Dec 76
19 Dec 76
5-6 Jan 77
6 Jan 77
6-7 Jan 77
7 Jan 77
5-6 Apr 77
6 Apr 77
6-7 Apr 77
7 Apr 77
8 17-18 Dec 76
18 Dec 76
18-19 Dec 76
19 Dec 76
5-6 Jan 77
6 Jan 77
6-7 Jan 77
7 Jan 77
Suspended participates
Time concentration, yg/m3
8 p.m. -8 a.m.
8 a.m.— 8 p .m.
8 p .m.— 8 a.m.
8 a.m.— 8 p .m.
8 p.m. -8 a.m.
8 a.m.— 8 p .m.
8 p .m.— 8 a.m.
8 a.m. —8 p.m.
8 p.m. -8 a.m.
8 a.m.— 8 p.m.
8 p.m. —8 a.m.
8 a.m. —8 p .m.
8 p.m. -8 a.m.
8 a.m. -8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m. -8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m. -8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m.— 8 p.m.
8 p.m.— 8 a.m.
8 a.m. -8 p.m.
8 p.m. -8 a.m.
8 a .m.— 8 p .m.
8 p .m.— 8 a.m.
8 a.m. -8 p.m.
164
149
220
564
30
48
75
100
75
59
52
50
106
46
143
145
31
47
71
45
106
86
43
46
46
49
87
69
39
58
63
59
76
115
62
45
         125

-------
TABLE 17.  (Continued)
Sampling
Site Date
5-6 Apr 77
6 Apr 77
6-7 Apr 77
7 Apr 77
6 17-18 Dec 76
18-19 Dec 76
5-6 Jan 77
6-7 Jan 77
5-6 Apr 77
6-7 Apr 77
7 17-18 Dec 76
18-19 Dec 76
5-6 Jan 77
6-7 Jan 77
5-6 Apr 77
6-7 Apr 77
9 17-18 Dec 77
18-19 Dec 77
5-6 Jan 77
6-7 Jan 77
5-6 Apr 77
6-7 Apr 77
10 17-18 Dec 76
18-19 Dec 76
5-6 Jan 77
6-7 Jan 77
5-6 Apr 77
6-7 Apr 77
Time
8 p.m. -8 a.m.
8 a.m. -8 p.m.
8 p.m. -8 a.m.
8 a.m. -8 p.m.
24-Hour Samples
8 p.m. -8 p.m.
8 p .m. —8 p.m.
8 p.m.— 8 p.m.
8 p.m.— 8 p.m.
8 p .m.— 8 p .m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m.— 8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m.— 8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p .m.— 8 p .m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
8 p.m. -8 p.m.
Suspended particulates
concentration, yg/m3
85
105
98
191
33
47
76
39
28
38
64
88
110
48
54
67
33
Invalid data
45
41
39
42
33
57
82
41
37
57
          126

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                TABLE 18.   DATA PRESENTATION OF PARTICLE
                           SIZING SAMPLER^3)
Stage
1
2
3
4
Backup Filter
Percent in
size range
33.3
13.2
5.9
3.4
44.2
Size range,
microns
7.0 and
3.3 -
2.0 -
1.1 -
0 -
above
7.0
3.3
2.0
1.1
          (a)   Sampler was  located at Site 3,
of refraction = 1.5150) and a cover slip were placed over the filter.  The
immersion oil matted the glass fibers in the pad and made them transparent.
     Optical examinations were made with two instruments:  (1) a Leitz micro-
scope using transmitted light and (2) a Zeiss metallograph using reflected
light either with dark-field or polarized-light illumination.  All optical
examinations were conducted at magnifications of approximately 500x.
     Generally, the estimates of areas covered on the filter by coal and
ash particles were made in 10 percent intervals, i.e., 0-10, 10-20, 20-30,
etc., although for the Campaign I, broader ranges were used.  An attempt
was made to estimate the percentage of the tertiary category for Campaigns
II and III by means of morphological and dark-field/polarized-light obser-
vations.  The remaining areas of the filter remained uncovered.
     Results of these microscope examinations for Campaigns  I, II, and III
are presented in Tables 19, 20, and 21.
                                    127

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TABLE 19.  RESULTS OF OPTICAL EXAMINATION OF
           FILTER PADS, CAMPAIGN I
Location,
time /date
1,
1,
1,
1,
2,
2,
2,
2,
3,
3,
3,
3,
4,
4,
4,
4,
Fri-8 p.m.
12-17-76
Sat-8 a.m.
12-18-76
Sat-8 p.m.
12-18-76
Sun-8 a.m.
12-19-76
Fri-8 p.m.
12-17-76
Sat-8 a.m.
12-18-76
Sat-8 p.m.
12-18-76
Sun-8 a.m.
12-19-76
Fri-B p.m.
12-17-76
Sat-8 a.m.
12-18-76
Sat-8 p.m.
12-18-76
Sun-8 a.m.
12-19-76
Fri-8 p.m.
12-17-76
Sat-8 a.m.
12-18-76
Sat-8 p.m.
12-18-76
Sun-8 a.m.
12-19-76
Coal, % of
area covered
0-20
0-20
0-20
0-20
0-20
(high side)
0-20
0-20
(low side)
0-20
0-20
0-20
0-20
0-20
0-20
(low side)
0-20
(low side)
0-20
(low side)
0-20
(low side)
Ash, % of
area covered
trace
>trace
> trace
>trace
> trace
>trace
1
> 1
trace
0.5-1
1
trace
1-2
2-3
1-2
< 1
Coal Particle Size
Range, microns
10-40
< 5-30
< 5-20
< 5-30/40
5-30
5-40
< 5-20
< 5-30
< 5-60/70
5-40
5-30
< 5-30
5-20
5-20
5-20
5-40
                  128

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                          TABLE 19.  (Continued)
  Location,
  time/date
                    Coal,  %  of       Ash,  %  of
                   area  covered     area covered
                 Coal Particle  Size
                   Range, microns
5, Fri-8 p.m.
   12-17-76
5, Sat-8 a.m.
   12-18-76
5, Sat-8 p.m.
   12-18-76
5, Sun-8 a.m.
   12-19-76
6, Fri-8 p.m.
   12-17-76
6, Sat-8 p.m.
   12-18-76
7, Fri-8 p.m.
   12-17-76
7, Sat-8 p.m.
   12-18-76
8, Fri-8 p.m.
   12-17-76


8, Sat-8 a.m.
   12-18-76
8, Sat-8 p.m.
   12-18-76
8, Sun-8 a.m.
   12-19-76
9, Fri-8 p.m.
   12-17-76
                      < 1-2
                      < 1-2
                        2-3
                        1-2
                        1-2
                        1-2
                        1-3
                       trace
                        1-2
                      < 1
                      < 1
    0-20
(low to med)


    0-20
(low to med)


    0-20
(low to med)


    0-20
(low to med)


    0-20
(low to med)


    0-20
(med to high)

    0-20
(med to high)
                        0-20           0-20
                   (low to med)    (low to med)


                        1              0-20
                                   (low to med)
    0-20
(low to med)


   20-40
(low to med)


    0-20
(low to med)


    0-20
(low to med)
                                                             5-10
                                                             5-20
                                                             5-15
                                                             5-15
                                                             5-15
                                                             5-15
                                                             5-20
                                                             5-40
                         5-15
                                                             5-15
                                                             5-15
                                                            5-15
                                                            5-15/20
                                  129

-------
                          TABLE 19.   (Continued)
  Location,
  time/date
 Coal, % of      Ash, % of
area covered    area covered
                Coal  Particle  Size
                  Range, microns
10, Fri-8 p.m.
    12-17-76
10, Sat-8 p.m.
    12-18-76
    <  1
    <  1
   0-20
(high side)


  20-40
(low side)
5-20
5-15/20
                                   130

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          TABLE 20.  RESULTS OF OPTICAL EXAMINATION OF FILTER PADS,
                     CAMPAIGN II
Location,
time/date
  Coal, %     Ash, %
  of area     of area
covered(a)    covered
Tertiary,   Coal Particle
% of area    Size Range,
 covered	microns
#l-Putnp House
Wed. 8 p.m.-8 a.m.      0-10
1-5-77

#1                      0-10
Thurs. 8 a.m.-8 p.m.
1-6-77

#1                      0-10
Thurs. 8 p.m.-8 a.m.
1-6-77

#1                      0-10
Fri . 8 a.m.-8 p-.m.
1-7-77
#2-Substation           0-10
Wed. 8 p.m.-8 a.m.
1-5-88

#2                     10-20
Thurs. 8 a.m.-8 p.m.   Low side
1-6-77                   <15
                         Trace      <5,20-30
                 <1      Trace      <5,30-40 (some  100)
                 <1       Trace      <5,10-20 (some  40  & 50)
                 <1       Trace      <5,10-30 (some  40  & 50)
                 <1      Trace     <5,10-20 (few larger)
                1-2      Trace     <5,10-20 (some  larger)
#2
Thurs.  8 p.m.-8 a.m.
1-6-77
      0-10      2-3      Trace     <5,10-30 (few larger)
n                     10-20
Fr. 8 a.m.-8 p.m.
1-7-77
#3-Haroilton's           0-10
  Trailer
Wed. 8 p.m.-8 a.m.
1-5-77

#3                      0-10
Thurs. 8 a.m.-8 p.m.  High  side
1-6-77                   >7

#3                      0-10
Thurs. 8 p.m.-8 a.m.
1-6-77

#3                      0-10
Fri. 8 a.m.-8 p.m.
1-7-77
#4 Pen. Trailer         0-10
Wed. 8 p.m.-8 a.m.
1-5-77
                 <1      Trace     <5,10-30 (some  larger)
                 <1      Trace     <5,10-30 (some  larger)
                         Trace     <5,10-30
                 <1      Trace
           <5,20-30 (some larger
                     ones, -100)
                 <1      Trace     <5-70
                         Trace     <5-30
                                      131

-------
                            TABLE 20.  (Continued)
 Location,
 time/date
  Coal, %     Ash,  %
  of area     of area
covered(a)    covered
        Tertiary,    Coal  Particle
        %  of  area     Size Range,
        covered	microns
#4                      0-10
Thurs. 8 a.m.-8 p.m.
1-6-77

#4                      0-10
Thurs. 8 p.m.-8 a.m.
1-6-77

#4                      0-10
Fri. 8 a.m.-8 p.m.
1-7-77

#5-Ash Disposal         0-10
Wed. 8 p.m.-8 a.m.
1-5-77
#5                      0-10
Thurs. 8 a.m.-8 p.m.
1-6-77
#5                      0-10
Thurs. 8 p.In.-8 a.m.
1-6-77
#5                      0-10
Fr. 8 a.m.-8 p.m.       Low side
1-7-777                  <5
#6 Schirf Fartn(b)       0-10
Wed. 8 p.m.-8 p.m.      Low
1-5-77                   <5

#6                      0-10
Thurs. 8 p.m.-8 p.m.    Low
1-6-77                   <5

#7 Unit #3           0-10
Wed. 8 p.m.-8 p.m.
1-5-77
#7                      0-10
Thurs. 8 p.m.-8 p.m.
1-6-77
#8 Refuse Coal          0-10
  Area                  Low
Wed. 8 p.m.-8 a.m.       <5
1-5-77
#g(b)                   0-10
Thurs. 8 a.m.-8 p.m.
1-6-77
                 <1       Trace      <5-30  (some  larger
                                          ones, -60)


                 <1       Trace      <5-30  (some  larger)
                 <1
<1
         Trace    <5,30-40
               1-2      Trace     <5, 30 (some larger)
                        Trace     <5,30-40
                        Trace     <5-20
                <5      Trace     <5-20 (some larger)
                <1      Trace     <5-40 (some larger)
                <1      Trace     <5-20 (few larger)
                1-2      Trace     <5-30
                 ~1      Trace     <5-30
                        Trace     <5,10-20
                1-2      Trace      <5~20
                                     132

-------
                            TABLE 20.  (Continued)
Coal, % Ash, % Tertiary, Coal Particle
Location, of area of area % of area Size Range,
time/date covered (a) covered covered microns
#8
Thurs . 8 p.m. -8 a.m.
1-6-77
#8
Fri. 8 a.m. -8 p.m.
1-7-77
#9 Pen. Recreation
Area(b)
Sat. 8 p.m. -8 a.m.
12-18-76
#9(b)
Wed. 8 p.m. -8 p.m.
1-5-77
#9
Thurs. 8 p.m. -8 p.m.
1-6-77
#10 Stiles Farm(b)
Wed. 8 p.m. -8 p.m.
1-5-77
#10
Thurs. 8 p.m.
1-5-77
0-10 <1 Trace <5-30 (few larger
Low ones, 70)
<5
0-10 <1 Trace <5-30 (few larger)
0-10 3-4 Trace <5, 10-15
Low
<5
0-10 1-2 Trace <5-20
Low
<5
0-10 2-3 Trace <5-10
Low
<5
0-10 5-10 Trace <5, 10-15
Low
<5
0-10 5-10 Trace <5-20
Low
<5
(a)   % reported is based upon an area/grid impact or % area of available
     filter pad.
(b)   Filter subsequently used for chemical analysis.
                                     133

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TABLE 21.  RESULTS OF MICROSCOPIC EXAMINATION OF GLASS-FIBER
           FILTER PADS, CAMPAIGN III

Sampler 1
Tues-8 p.m.
4-5-77
Sampler 1
Wed-8 a.m.
4-6-77
Sampler 1
Wed-8 p.m.
4-6-77
Sampler 1
Thurs-8 a.m.
4-7-77
Sampler 2
Tues-8 p.m.
4-5-77
Sampler 2
Wed-8 a.m.
4-6-77
Sampler 2
Wed-8 p.m.
4-6-77
Sampler 2
Thurs-8 a.m.
4-7-77
Sampler 3
Tues-8 p.m.
4-5-77
Sampler 3
Wed-8 a.m.
4-6-77
Sampler 3
Wed-8 p.m.
4-6-77
Sampler 3
Thurs-8 a.m.
4-7-77
Coal, Z
of area
covered
0-10


0-10


10-20
(low side)

10-20


0-10


10-20


0-10


0-10


0-10
(high side)

0-10


0-10
(high side)

10-20


Ash, % Tertiary,
of area % of area
covered covered
0-10


0-10


0-10


0-10
(low side)

0-10


0-10
(low side)

10-20
(low side)

10-20
(high side)

0-10


0-10


0-10

0-10
(low side)

Trace


Trace


Trace


Trace


Trace


Trace


Trace


Trace


Trace


Trace


Trace

Trace


Coal Particle -Comments-
Size Range, Observed with transmitted light;
microns ' dark field/polarized light
< 5-50
Some 200

* 5-40
Few longer

< 5-40,50 Soot
Few larger

< 5-40,50
Some larger

< 5-40


< 5-30 Soot
Few larger

< 5-20,30 Trace of soot
Few larger

< 5-40,50 (Fly ash appears to be larger in
size than usual . )

< 5-50,70
Some larger

< 5-20,30 Soot
Some larger

< 5-30,50 Soot
Few larger

< 5-30,40 Trace of soot
Some larger

                               134

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TABLE 21.  (Continued)

Sampler 4
Tues-8 p.m.
4-5-77
Sampler 4
Wed-8 a.m.
4-6-77
Sampler 4
Wed-8 p.m.
4-6-77
Sampler 4
Thurs-8 a.m.
4-7-77
Sampler 5
Tues-8 p.m.
4-5-77
Sampler 5
Wed-8 a.m.
4-6-77
Sampler 5
Wed-8 p.m.
4-6-77
Sampler 5
Thurs-8 a.m.
4-7-77
Sampler 6
Tues-8 p.m.
4-5-77
Sampler 7
Tues-8 p.m.
4-5-77
Sampler 7
Wed-8 p.m.
4-6-77
Sampler 8
Tues-8 p.m.
4-5-77
Sampler 8
Wed-8 a.m.
4-6-77
Coal, %
of area
covered
0-10
(low side)

0-10
(low side)

0-10


10-20


0-10
(low side)

0-10
(low side)

0-10


0-10


0-10
(low side)

o-io
(low side)

0-10


0-10
(low side)

0-10
(very low)
~1%
Ash, % Tertiary,
of area % of area
covered covered
0-10 Trace


0-10 Trace


0-10 Trace


0-10 Trace
(low side)

0-10


10-20 Trace
(med range)

10-20 Trace
(low side)

0-10 Trace
(high side)

0-10 Trace
(high side)

0-10 Trace

0-10 Trace


0-10
(low side)

0-10 Trace


Coal Particle -Comments-
Size Ranpe Observed with transmitted light;
microns ' dark field/polarized light
< 5-10,20
Few larger

< 5-20,30


< 5-20,30
Some larger

< 5-30,50
Some larger

< 5-10,20
Few larger

< 5-20,30
Few larger

< 5-20,30


< 5-30,40
Some larger

< 5,10-20
Few larger

< 5-20 Small metallic particles;
Some larger silica particles

< 5-20,30
Few larger

< 5-10,20
Some larger

< 5-15
Few larger

            135

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                         TABLE 21.  (Continued)

Sampler 8(1)
Wed-8 p.m.
4-6-77
Sampler 8(2)
Wed-8 p.m.
4-6-77
Sampler 8
Thurs-8 a.m.
4-7-77
Sampler 9
Tues-8 p.m.
4-5-77
Sampler 9
Wed-8 p.m.
4-6-77
Sampler 10
Tues-8 p.m.
4-5-77
Sampler 10
Wed-8 p.m.
4-6-77
Coal, %
of area
covered
0-10
0-10
0-10
(high side)
0-10
(very low)
0-10
0-10
(very low)
0-10
Ash, %
of area
covered
10-20
(low side)
10-20
(low side)
0-10
0-10
(high side)
0-10
(high side)
0-10
(high side)
10-20
Tertiary,
% of area
covered
Trace
Trace
Trace
Trace
Trace
Trace
Trace
Coal Particle -Comments-
Size Range, Observed with transmitted light;
microns dark field/polarized light
< 5-20,30 Some soot
Few larger
< 5-20,30 Some soot
Few larger
< 5-20,30 Few whites
Quite a few
larger
< 5-10
Some larger
< 5-20
Some larger
< 5-15
Few larger
< 5-30
Some larger
Trace Elements Analysis
     Analytical Procedures.
     Filter Preparation.  The clean margin area was trimmed from each filter
and the trimmed filter was weighed.  It was then divided as equally as possible
into eight pieces, each of which was weighed.  The calculations from the
individual analysis to the milligram values for the entire filter were then
done on a weight proportion basis.  A blank filter was treated and analyzed
in the same manner and the blank values were included in the final calculations.

     Chlorine Analysis (Based on ASTM D2361-66).  One-eighth filter was cut
into 1-inch-square portions and layered into a crucible with 2.5 g of Eschka
mixture.  The crucible was heated to 675 C within 1 hour and maintained at
                                    136

-------
that temperature for 1-1/2 hours.   The mixture was cooled,  dissolved in a
solution containing 8 ml nitric acid, diluted to 100 ml,  and filtered.   The
chloride was titrated potentiometrically using 0.01 N AgNO., and a Beckman
Automatic Titrator.

     Fluorine Analysis (Based on Preparation Used in ASTM D2361-66).  One-
eighth filter was cut into 1-inch-square portions and layered into a crucible
with 2.5 g of Eschka mixture.  The crucible was heated to 675 C within 1 hour
and maintained at that temperature for 1-1/2 hours.  The mixture was cooled
and then dissolved in a solution containing 8 ml of sulfuric acid.  This
solution was diluted to 100 ml.  The fluoride was measured using an Orion
electrode and specific ion meter after distillation according to Standard
Methods for the Examination of Water and Wastewater, 14th edition.


     Total Organic Carbon  (TOG) Analysis.  One-eighth filter was placed in
a Petri dish, covered with 5 ml of IN HC1, and then placed in an oven at
103 C and evaporated to dryness to remove the inorganic carbon.  The dried
filter portions were cut into small strips and placed in a Leco combustion
boat.  The Petri dishes were washed with 2 ml of deionized water and the
washings were added to the boats, which were again dried at 103 C.  Standard
organic carbon solutions were pipetted into combustion boats and dried in
the same manner.  The individual boats were fired in a stream of oxygen in
a Leco-tube-type resistance furnace.  The gas stream from the combustion
tube was scrubbed into a 50-ml solution of 0.10 N NaOH.  These solutions
were diluted to 100 ml; 30 yl of each solution and standard was injected
into the total carbon channel of a Beckman 914 TOG Analyzer.

     Metals Analysis.  The following procedures have been used successfully
for the NBS coal standard SRM1632:
     (1)  Mercury.  One-eighth filter was cut into strips and placed on edge
          in a combustion boat.  It was fired in a Leco resistance furnace
          using an oxygen stream to carry the volatilized mercury to a
          scrubber containing acidic permanganate and persulfate.  Standards
          and reagent blanks were prepaied in the same manner.  The scrubber
          solution was reduced and bubbled with nitrogen through an LDC
          Mercury Monitor.
                                    137

-------
     (2)   Arsenic.   One-eighth filter was  placed  in  an  Erlenmeyer  flask
          covered by a watch glass.  A  solution containing  2 ml  of HC10  ,
          2 ml of H-SO ,  and 1 mg of vanadium catalyst  was  added and  the
          flasks were slowly heated  through the entire  boiling range  of
          perchloric acid until the  particulates  turned white or colorless.
          The solution was cooled and  the  watch glass was washed into the
          Erlenmeyer flask.   The solution  was diluted and analyzed by the
          silver diethyldithiocarbamate chlorimetric method given  in
          Standard  Methods for the Examination of Water and Wastewater,  13th
          edition.
     (3)   All other metals.   One-eighth filter was placed in a Teflon beaker;
          HC1, HNO_, and HF were added, and the solution was slowly heated
          to dryness.  Perchloric acid was added, the beaker covered  by  a
          watch glass, and heated until the remaining material was digested.
          One ml of HNO- was added to  the  solutions  and they were  diluted
          to 50 ml  and analyzed using  a Perkin Elmer 503 Atomic  Absorption
          Spectrophotometer.

     General Chemical Analysis Procedure.

     Campaign I. The chemical analysis of the hi-vol filter pads  was designed
for coal or ash analysis, since these  are  assumed to comprise a  significant
portion of the particulate,  particularly the 12-hour samples.  Data from the
microscopic analysis of the filters  were used to  determine  which filters
would be analyzed for trace elements.   Generally, the filter exhibiting  the
highest percentage  of coal or ash from each site  was selected.
     Each candidate filter was analyzed for the following elements in Campaign
I:
     Arsenic       Chromium     Magnesium     Potassium      Chloride
     Beryllium     Copper       Manganese     Sodium         Fluoride
     Cadmium       Iron         Mercury       Zinc
     Calcium       Lead         Nickel        Total Organic Carbon
     Blank filters  were analyzed in conjunction with the other  filters.   The
filter-blank values were then subtracted from the total values.   The  blank
filter was analyzed in duplicate for metal.  These duplicate analyses were
in precise agreement with each other.   Only traces of  iron, copper,  manganese,
                                    138

-------
chromium, zinc, mercury and lead were found.  However, large amounts of sodium,
potassium, calcium, and magnesium were found in the blank filters as shown
below.

          Sodium (Na)     320     311 milligrams/filter
          Potassium (K)   304     284 milligrams/filter
          Calcium (Ca)    250     243 milligrams/filter
          Magnesium (Mg)   68      68 milligrams/filter

When these values are compared with the quantities of metals that we are trying
to measure it is apparent that the relative error makes the results for these
four metals meaningless.  Therefore these metals were not reported in Campaign
I.
     Beryllium content was below the minimum detection limits at each of the
ten sites.
      Campaign II.  Antimony,  titanium, and vanadium were  included  in  the
 elemental  analysis for Campaign  II; calcium, magnesium, potassium, and sodium
 were  not analyzed because  of  their high concentrations in the blank filters.
      Beryllium, vanadium,  and antimony were below  the minimum detectable
 limits; titanium was  observed at only two of the ten sites.

      Campaign III.  A new  filter, Spectrograde Type A glass  fiber, made by
 Gelman  Instrument Company, was used in Campaign III.
      The new fiber glass filters still showed large amounts  of  calcium,
 magnesium, potassium, and  sodium.  Therefore', analyses for these metals were
 not made on the other filters.   Also, the new filters showed larger amounts
 of zinc, chloride, and fluoride  than did the previous filters.
      The chloride analysis of the blank was high,  the value  being  2-l/2-to-3
 times higher than the total values  (blank included) for the  filters in
 Campaigns  I and II.   Therefore,  no chloride values were reported in this
 campaign.  Selenium was analyzed in this campaign  using neutron activation
 analysis.  Blank analyses  of  filters used in Campaigns II and III  are given
 in Tables  22 and 23,  respectively.
      Chemical analyses of  particle size distribution samples were  run on
 the  four stages and the backup filter.  These results are reported in Table  24.
                                     139

-------
TABLE 22.  BLANK ANALYSIS OF FILTER USED IN CAMPAIGN II

Parameter
Antimony
Arsenic
Beryllium
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Mercury
Nickel
Titanium
Vanadium
Zinc
TOC
Fluoride
Chloride
Milligrams
<0.1
0.022
<0.004
0.018
0.023
0.36
2.0
1.2
0.043
0.00013
0.0040
<0.2
<0.1
0.16
21.5
1.8
0.71
                        140

-------
TABLE 23.  BLANK ANALYSIS OF FILTER USED IN CAMPAIGN III
Parameter
Arsenic
Beryllium
Cadmium
Calcium
Chromium
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Potassium
Titanium
Selenium
Sodium
Zinc
Vanadium
TOC
Chloride
Fluoride
Milligram per filter
<0.002
<0.004
<0.0010
86
0.053
0.016
1.72
0.020
33.1
0.075
0.000053
<0.010
31.1
.25
5.3
235
1.95
< .05
4.0
11.0
19.3
                         141

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                              TABLE  24.   TRACE ELEMENT ANALYSIS  OF THE PARTICLE SIZING SAMPLER
                                          USED AT  SITE 3, CAMPAIGN III


Stage
1

2
3
4
Back-up
Filter
Size
range,
microns
(7.0 and
above)
(3.3-7.0)
(2.0-3.3)
(1.1-2.0)
(0-1.1)

Percent
loading
in size
range
33.3

13.2
5.9
3.4
44.2

















Concentration, ppm by weight of particulates
As
23.76

53.14
118.51
104.6
78.4

Cd
(a)

(a)
(a)
(a)
10.9

Ca
12,544.56

9631.4
12,592.6
2614.4
(b)

Cr
(a)

265.7
(a)
307.2
89.3

Cu
132

299
666.6
2222.2
46.7

Fe
15,077.8

14,613.1
15,555.6
14,379.1
9627.8

Pb
237.68

498.2
888.9
2614.4
2084.4

Mg
3376.86

2324.8
5185.2
(a)
(b)

Mn
198.07

166.1
296.3
392.16
228.3

Hg
3.03

7.3
11.9
11.63
(a)

Ni
39.6

99.6
(a)
130.7
(a)

K
1621.68

3985.4
7407.4
5228.8
(b)

Sc
(b)

(b)
(b)
(b)
66.5

Zn
171.7

(a)
(a)
8104.6
2580.6

Ti
1585.0

1860.0
—
(a)
(a)

V
(a)

(a)
(a)
(a)
(a)

(a)  Below minimum detectable limit.
(b)  Element not analyzed.

-------
     In order to provide a general indication of the trace element level
encountered, brief summaries have been prepared.  However, these summaries
are insufficient to establish a sufficient data base.   The average values
for 12-hour and 24-hour samples, as well as minimum and maximum levels  for
each time frame, are given in Table 25.   The average values for Campaigns I,
II, and III for selected sites are given in Table 26.   These sites are  generally
in a line from the coal pile at distances of 175 to approximately 2200  meters.
Site 6 is off property and generally not affected by emissions from the coal
piles or power plant stacks and therefore serves as a background or control
site.
     The trace element concentrations as they relate to mass concentration
ranges are shown in Table 27.  Data in this table indicate that trace element
concentration is not always directly proportional to the mass concentrations.
     Trace element concentrations in ppm by weight of particulate matter
captured on the filter pads are shown in Table 28.

Chemical Analysis of Coal

     Coal  Source.  The Homer  City power plant receives its coal  from three
sources, namely  the Helen mine, Helvetia mine,  and  trucked-in coal  (Josephine).
The  Helen  and Helvetia mines  are part of the Upper  Freeport Seam, while the
trucked-in coal  is from  the Lower Kittanning Seam.

     Analytical  Procedures.   Samples of the coals were air-dried, pulverized
to -60 mesh, split with  an enclosed  riffle, placed  in glass jars, and mixed
on a blending wheel for  1/2 hour.
     Routine analyses were carried out by  the  following methods:
Analysis
% Moisture
% Ash
% Sulfur
Btu
Fixed Carbon
Carbon
Hydrogen
Nitrogen
ASTM Method
D3173-73
D3174-73
D3177-75
D2015-66
D3172-73
D3175-73
D3178
D3179
                                                  (1972)
                                    143

-------
                                 TABLE  25.   COMPARISON BETWEEN TRACE ELEMENT CONCENTRATIONS
                                            IN 12- AND 24-HOUR SAMPLES
3
Concentrations, yg/m
Average
Arithmetic
Maximum
i— i
** Minimum
Average
Arithmetic
Maximum
Minimum
As Cd Cr Cu Fe Pb Mn
12 -Hour
0.14 .009 .0261 0.217 3.56 0.442 .088
.053 .039 .064 0.484 16.55 1.50 .804
.005 .001 .007 0.011 1.04 0.160 .031
2 4 -Hour
.011 .006 .015 0.189 1.88 0.308 .036
.022 .020 .022 0.310 0.80 0.500 .063
.002 .001 .007 0.112 1.40 0.144 .022
Hg
Samples
.00017
.00041
.00002
Samples
.00005
.00010
.00002
Ni Ti(a)
.018 0.58
.028 1.53
.006 0.58
.008 0.14
.018 0.17
.001 0.09
.Zn Cl(b)
0.30 1.45
0.70 3.40
0.08 0.20
0.13 1.84
0.21 1.92
0.06 0.19
F V
-------
                         TABLE  26.   COMPARISON BETWEEN  TRACE ELEMENT CONCENTRATIONS AT SELECTED SITES
                                     (CAMPAIGNS I, II, AND III)
Distance from
eoal pile.
Site
1
3
-. 4
" 8
9
10
6(c)
meters
(175)
(150)
(400)
(800)
(1800)
(2200)
(1600)
As
.015
.014
.011
.011
.007
.015
.009
Cd
.006
.011
.005
.016
.007
.008
.005
Cr
.027
.026
.014
.017
.015
.014
.014
Cu
0.184
0.400
0.146
0.045
0.165
0.174
0.223
Fe
3.65
3.25
2.22
1.81
1.57
1.99
1.65
Pb
0.529
0.644
0.228
0.498
0.277
0.350
0.258
Concentrations,
Mn
0.058
0.095
0.217
0.026
0.036
0.034
0.041
Hg
.00087
.00024
.00008
.00013
.00005
.00008
.00003
Ug/cu m
Ni
.014
.016
.018
.007
.011
.006
.009
Ti
0.71
0.18
0.33
(a)0.46(a)
0.13(a>
0.17(a)
0.17(a>
Zn
0.41
0.33
0.28
0.25
0.12
0.10
0.13
Cl
0.95(a)
2.31
0.98
0.73
0.74
0.58(a)
1.05
F
7.48
3.46
2.0
2.53
1.56
0.67
1.40
V
(b)
(b)
(b)
(b)
(b)
(b)
.02(a>
Se
.0051
.0047
.0026
.0002(a)
.0051(a)
.0049(a)
.0030(a)
(a)  One observed value.
(b)  Below minimum detectable  limit.
(c)  Site 6 is off property and serves as a background site.

-------
                  TABLE 27.   TRACE ELEMENT CONCENTRATIONS AS  THEY RELATE TO  MASS CONCENTRATION RANGES
                               FOR ALL SITES AND ALL  CAMPAIGNS
Mass Concentration Range,
ug/m3 No. of Sanpli

0-50

51-100






101-150



151-200
_i
£ 201-250

251-300


301-450
451-600

0-50




51-100





101-150

5
4
5
8
8
5
4
3
5
2
1
4
4
3
8
2
3
2
1
2
1
3

6
9
9
6
9
6
7
10
10
10
7
7
	
28 As

.007
.005
.017
.015
.012
.015
.011
.008
.019
.006
.021
.018
.009
.024
.006
.053
.017
.007
.019
.025
.006
.006

.011
.006
.008
.002
.006
.015
.007
.013
.022
.011
.009
.021
Concentrations, u^/ra3
Cd

.030
.003
.002
.039
.007
.021
.012
.023
.004
(a)
.006
.003
.002
.005
.002
.005
.005
.001
.005
.002
(a)

-------
                            TABLE 28.   TRACE ELEMENT  CONCENTRATION OF  PARTICULATE  ON THE  FILTER PAD
Site
1
1
1
2
2
2
2
3
3
3
3
4
4
4
4
£ 5
5 5
5
5
8
8
8
6
6
6
7
7
7
9
9
9
10
10
10
Campaign
II
III
III
I
II
II
III
I
II
III
III
I
II
III
III
I
I
II
III
I
II
III
I
II
III
I
II
III
I
II
III
I
II
III
Sampling
period,
hours
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
12
24
24
24
24
24
24
24
24
24
24
24
24
Participate
concentration
136
252
398
107
230
294
291
87
189
220
564
100
50
143
145
47
71
106
87
63
62
191
33
76
38
64
110
67
33
45
42
57
82
57
, Trace Element Concentration, ppm by weight
As
154
74
15
56
230
24
85
92
127
76
11
110
100
130
65
149
211
160
217
238
194
34
333
197
52
109
190
136
181
177
135
228
268
191
Cd
44
18
(a)
(a)
22
3
7
264
26
24
(a)
120
60
21
10
638
296
19
45
619
113
12
303
39
67
187
27
31
393
(a)
19
351
37
23
Cr
471
43
18
561
196
139
182
230
228
81
38
130
380
109
46
468
296
217
206
317
258
74
424
211
285
313
200
143
667
356
166
228
244
173
Cu
1,787
695
336
1,215
1,900
837
1,168
3,678
2,561
2,154
572
840
220
1,367
2,016
1,894
3,239
1,538
4,126
794
645
235
5,455
2,342
7,957
3,594
1,245
3,211
6,061
2,489
4,356
4,035
1,988
2,252
Fe
18,824
18,281
9,557
16,822
35,174
13,197
56,962
28,736
16,561
17,501
6,223
17,000
24,800
27,468
13,718
46,809
33,803
26,321
34,419
34,921
16,774
11,477
42,424
25,263
42,637
28,125
21,273
34,106
57,576
31,333
33,392
33,333
24,878
35,433
Pb
4,397
2,215
1,085
2,150
2,670
1,255
826
17,241
3,095
942
501
2,800
5,700
1,162
1,235
6,809
10,282
4,717
1,846
12,857
566
1,745
9,696
4,079
3,801
5,312
4,436
3,140
12,727
5,955
3,422
8,772
4,545
3,119
Mn
523
304
65
561
404
197
427
632
534
287
81
2,400
680
5,603
6
979
648
491
706
540
500
74
848
737
974
859
573
714
1,818
578
529
456
500
615
Hg
3
1
.2
1
1
.4
1
3
1
2
.4
2
(a)
(a)
1
1
2
1
1
2
2
(a)
1
1
1
.3
1
1
2
1
1
1
1
2
Ni
51
78
(a)
187
91
34
88
264
74
45
23
270
160
(a)
(a)
1,064
(a)
57
239
(a)
113
(a)
394
92
202
16
100
107
545
67
(a)
175
24
121
Ti
8,676
1,954
1,135
(b)
2,522
(a)
5,269
(b)
(a)
2,109
626
(b)
(a)
2,733
1,885
(b)
(b)
(a)
4,560
(b)
(a)
2,416
(b)
(a)
4,513
(b)
(a)
1,356
(b)
(a)
3,007
(b)
(a)
2,946
V
(a)
(a)
(a)
(b)
(a)
(a)
199
(b)
(a)
(a)
(a)
(b)
(a)
(a)
(a)
(b)
(b)
(a)
(a)
(b)
(a)
(a)
(b)
(a)
594
(b)
(a)
(a)
(b)
(a)
(a)
(b)
(a)
(a)
Zn
3,015
(a)
(a)
2,336
1,783
374
2,421
3,563
2,275
-
465
2,000
1,600
2,870
2,796
5,532
4,085
943
4,343
3,175
3,548
1,678
4,848
1,184
5,463
2,188
1,364
(a)
5,152
1,333
(a)
2,982
1,585
(a)
F
55,000
(a)
(a)
23,364
6,870
11,599
(a)
37,931
19,206
(a)
(a)
15,000
45,600
16,809
12,483
53,191
42,553
3,679
23,127
34,921
40,161
15,235
1,818
22,237
21,496
37,500
10,182
(a)
42,424
38,889
(a)
16,491
4,879
(a)
Cl
6,985
(c)
(c)
14,019
4,043
4,184
(c)
39,081
6,402
(c)
(c)
8,200
22,800
(c)
(c)
59,574
42,553
30,849
(c)
17,460
5,806
(c)
10,000
2,526
(c)
20,313
3,818
(c)
27,278
12,889
(c)
10,175
(a)
(c)
Se
6
26
9
(b)
(b)
(b)
30
(b)
(b)
33
4
(b)
(b)
33
3.0
(b)
(b)
(b)
91
(b)
(b)
1
(b)
(b)
77
(b)
—
49
(b)
(b)
122
(b)
(b)
86
(a)  Below minimum detectable limits.
(b)  Element not analyzed.
(c)  Element not reported because of high background  concentration in blank filter.

-------
              Chlorine                D2361-66
              Oxygen                  D3176-74
              Sulfur Forms            D2498-68   (1974)

     Fluorine.  The coal was fired in an oxygen bomb containing a small quantity
of one normal sodium hydroxide.   The bomb contents and washing were then
analyzed by the method of known addition using a fluoride-specific ion probe.

     Mercury.  Coal samples were fired in a resistance furnace using an oxygen
gas stream to carry the volatilized mercury to an acidic permanganate-persul-
fate scrubber solution.  This solution was then analyzed for mercury using
flameless atomic absorption spectrophotometry.

     Arsenic.  Samples were digested using a mixture of perchloric acid,
sulfuric acid, and vanadium catalyst; the arsenic was determined colorimetri-
cally using the silver diethyldithiocarbamate method.


     Selenium.  Neutron activation.

     Other Metals.  Q.5 gram samples of coal were ashed by bringing the temper-
ature to 500 C over one hour and then to 750 C over a second hour.  The ash
was washed into Teflon beakers and dried.  HF (4 ml) was added and the samples
taken to dryness.  A solution containing 0.5 ml HC1 and 1 ml HN03 was added
and the solutions heated to expel chlorine and solubilize the residue.  The
solutions were diluted to 50 ml and analyzed by atomic absorption spectro-
photometry using reagent blanks and standards in the same acid matrix.  NBS
standard 1632 was analyzed in conjunction with these samples and excellent
agreement was found with all metals except vanadium.  The NBS certified value
for vanadium is 35+3 ppm; our analysis value was 50 ppm.  (An ASTM draft proce-
dure shows that four laboratories analyzed NBS 1632 in quadruplicate by a
procedure similar to the one above.  They found good agreement with NBS
values except for vanadium; their average value was 45.7+4 ppm.)

     Results.  The composition and trace elements contents of the coals from
all three sources are given in Tables 29 through 34.
                                    148

-------
       TABLE 29.  COAL ANALYSIS  (HELEN MINE)
                     As Received,
                       Dry  Basis,
Moisture
Ash
Sulfur
Btu
Fixed carbon
Volatile matter
MAF Rt~ii \"'
L 1A.L 1J L. U
Carbon
Hydrogen
Nitrogen
Chlorine
Oxygen
Sulfur Forms:
Pyritic
Sulfate
Organic
2.58
23.68
2.94
11,274
50.41
23.32
-
63.00
4.02
1.10
0.25
2.42

2.45
0.09
0.41
—
24.31
3.02
11,573
51.75
23.94
15,290
64.67
4.13
1.13
0.26
2.48

2.51
0.09
0.42

(a)   Btu measurements are not given in percentages.
(b)   MAF = moisture- and ash-free.
 TABLE  30.   TRACE ELEMENT ANALYSIS (HELEN MINE)
                                yg/g
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Calcium
Chromium
Cobalt
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Titanium
Vanadium
Zinc
Fluorine
As Received

    26,700
    <25
    26
    102
    2.5

    3,000
    35
    15
    26
    27,600
    12.0
    1,470
    63
    0.46
    15.8
    1,165
    60
    46
    98
Dry Basis

   27,420
   <25
   27
   105
   2.6

   3080
   36
   15
   27
   28,350
   12.3
   1,510
   65
   0.47
   16.2
   1,200
   62
   47
   101
                       149

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      TABLE  31.   COAL ANALYSIS (HELVETIA MINE)
                    As  Received,
                        %<*>
Dry Basis,
Moisture
Ash
Sulfur
Btu
Fixed carbon
Volatile matter
MAF Btu (b)
Carbon
Hydrogen
Nitrogen
Chlorine
Oxygen
Sulfur Forms:
Pyritic
Sulfate
Organic
3.97
22.44
1.91
11,277
49.80
23.79
—
63.29
4.32
1.13
0.26
2.91

1.44
0.03
0.44
—
23.37
1.99
11,743
51.86
24.77
15,324
65.91
4.50
1.18
0.27
3.03

1.50
0.03
0.46

(a)   Btu measurements are not given in percentages,
(b)   MAF = moisture- and ash-free.
 TABLE  32.  TRACE ELEMENT ANALYSIS  (HELVETIA MINE)
                                  ug/g
                                       (a)

Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Calcium
Chromium
Cobalt
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Titanium
Vanad ium
Zinc
Fluorine
Selenium
As Received
28,050
<25
22
116
2.5
<0.1
1520
33
14
31
18,000
14.9
1345
35
0.34
16.8
1125
65
66
108

Dry Basis
29,200
<25
23
121
2.6
<0.1
1580
34
15
32
18,740
15.5
1400
36
0.35
17.5
1170
68
69
112
2.9+. 6 (-a>
-J T 1 -J «.«
 (a)   Selenium given in parts per million.

                         150

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            TABLE 33.   COAL ANALYSIS (TRUCKED-IN COAL)
                     As Received,
Dry Basis,
Moisture
Ash
Sulfur
Btu
Fixed carbon
Volatile matter
MAF Btu (b)
Carbon
Hydrogen
Nitrogen
Chlorine
Oxygen
Sulfur Forms:
Pyritic
Sulfate
Organic
3.00
24.52
5.67
11,037
50.99
21.49
—
60.94
3.95
1.12
0.23
0.57

4.95
0.15
0.57
—
25.28
5.85
11,378
52.57
22.15
15,228
62.82
4.07
1.15
0.24
0.59

5.10
0.16
0.59

 (a)  Btu measurements are not given  in percentages,
 (b)  MAF = moisture- and ash-free.
  TABLE 34.  TRACE ELEMENT ANALYSIS  (TRUCKED-IN  COAL)
                                       (a)

Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Calcium
Chromium
Cobalt
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Titanium
Vanadium
Zinc
Fluorine
Selenium
As Received
25,300
<25
48
250
2.5
0.26
760
30
14
20
48,750
17.3
975
74
1.1
12.8
1329
55
64
91
—
Dry Basis
26,080
<25
49
258
2.6
0.27
784
31
14
21
50,260
17.8
1005
76
1.1
13.2
1370
57
66
94
6.4(+1.2)(a)

(a)   Selenium given in parts per million.
                          151

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Statistical Analysis

     Purpose.  A statistical analysis is necessary because the measurements
of concentrations are subjected to processes which cause fluctuations, or
variations in the measurements.  Wind direction, wind speed, distance, and
types of measurements all contribute to the observed variations.
     As a result, the average value of a small set of samples is likely not
to be the true mean value.  Thus, if one took samples one day under a certain
set of conditions and took samples another day under identical conditions,
the means of the samples would be different, although they would be expected
to be identical.
     For the same reason, if the means could be expected to be different,
they might coincidentally turn out to be identical.
     It is therefore necessary to use the variation within the samples to
determine the tolerance in the estimated value of the sample mean.  Such a
procedure is conducted in an analysis of variance.

     Analysis of Variance—Background and Approach.  The purpose of the
analysis of variance is to test whether the mean of a group of samples (i.e.,
samples of trace element concentrations) differs significantly from the mean
of another group of samples measured under different conditions.  In essence,
the data are examined to determine whether the effect of a set of conditions
(day/night, or site location) is real or likely to have arisen as a result
of random variation.  The normal statistical assumptions have been made to
permit this analysis:  concentrations of trace elements and total mass
represent random samples independent of each other; and all variations
have normal distributions.
     Data used in the analysis are shown in Tables 17 and 18 presented in
the section on particulate concentrations.  The trace elements studied in
this analysis are arsenic (As), cadmium (Cd), chromium (Cr), copper (Cu),
iron (Fe), lead (Pb), manganese (Mn), mercury (Hg), nickel (Ni), zinc (Zn),
fluoride (F), and chlorine (Cl).
     Four hypotheses were considered in the analysis:  (1) the means of sample
concentrations for a particular element are identical at all sampling sites;
(2)   the concentration means of sample groups, Sites 1 and 3, 4 and 5, 8 and
9   for a particular element are identical;  (3) the concentration means of
                                    152

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the 24-hour samples, 12-hour day samples, and 12-hour night samples are
identical; and (4) the 12-hour day and 12-hour night samples are identical.
     The levels of confidence with which a particular hypothesis is rejected
are expressed as a percentage.  The hypothesis is stated in the table caption
(see Tables 35-38).  With a level of confidence of 90 percent or greater,
the hypothesis may be rejected as not true.  A level of confidence that is
less than 90 percent indicates that the data for the particular element
contain a significant amount of random fluctuations as opposed to systematic
fluctuations.  Therefore, the stated hypothesis may not be rejected.
     A discussion of the outcome of these hypotheses follows in the order
just stated.
           TABLE 35.   HYPOTHESIS  THAT THE  MEANS  OF  THE  SAMPLES  AT
                      EACH SAMPLING SITE ARE  IDENTICAL
Element
Total Mass
Arsenic
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Mercury
Nickel
Zinc
Fluoride
Chloride
Level of confidence (%)
with which hypothesis is rejected
*99
*90
33
40
*99+
*92
34
76
60
74
50
30
75
        ^Denotes a level of confidence high enough to reject the
         hypothesis.
        (a) Values in table are rounded to nearest integer.
                                    153

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   TABLE 36.   HYPOTHESIS  THAT  THE  MEANS  OF  THE  SAMPLES AT
              SITES  1  AND 3  ARE  IDENTICAL TO  THOSE  AT
              SITES  4  AND 5, AND SITES  8 AND  9
Element
Total Mass
As
Cd
Cr
Cu
Fe
Pb
Mn
Hg
Ni
Zn
F
Cl
Level of confidence (%)
with which hypothesis is rejected^3)
*99+
*96
60
68
29
*92
52
79
69
69
60
51
60
*Denotes a level of confidence high enough to reject the
 hypothesis.

(a)  Values in table rounded to nearest integer.
                            154

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  TABLE  37.   HYPOTHESIS  THAT  THE  MEANS OF THE FOLLOWING
              SAMPLE  GROUPS  ARE  IDENTICAL:  2A-HOUR
              SAMPLES,  12-HOUR DAY SAMPLE, AND 12-HOUR
              NIGHT SAMPLE
Element
Total Mass
As
Cd
Cr
Cu
Fe
Pb
Mn
Hg
Ni
Zn
F
Cl
Level of confidence (%)
with which hypothesis is rejected^3'
*97
*99+
14
62
*9 9+
*94
52
53
43
67
76
14
26
"'Denotes a level of confidence high enough to reject the
 hypothesis.

(a) Values in table are rounded to nearest integer.
                            155

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          TABLE 38.  HYPOTHESIS THAT THE MEANS OF THE FOLLOWING
                     SAMPLE GROUPS ARE IDENTICAL 12-HOUR DAY AND
                     12-HOUR NIGHT SAMPLES
Element
Total Mass
As
Cd
Cr
Cu
Fe
Pb
Mn
Hg
Ni
Zn
F
Cl
Level of confidence (%)
with which hypothesis is rejected'3'
88
*95
37
31
43
29
34
69
70
67
79
28
9
        *Denotes a level of confidence high enough to reject the
         hypothesis.
        (a) Values given in table are rounded to nearest integer.
     First Hypothesis.  It was hypothesized that the arithmetic means of the
sample concentrations for a particular element (total mass and trace element
concentration) obtained at each of the monitoring sites originated from the
same hypothetical population and therefore were identical.  The results of
the analysis of variance performed on this hypothesis are shown in Table 35.
     For any high level of confidence, the hypothesis would be rejected.
Thus, when applied to the total mass measurements, the hypothesis is rejected
because of a 99 percent value.  In other words, the concentrations of total
mass significantly vary between some or all of the monitoring sites.  This
is a reasonable finding since the greatest fugitive dust concentrations
were observed at the monitoring sites closest to the sources.  It is
also shown in Table 35 that the hypothesis is rejected as not true for
                                    156

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concentrations of arsenic, copper, and iron.  Thus, the concentrations of
these trace elements vary significantly among some or all of the monitoring
sites.
     For those trace elements which had a level of confidence less than 90
percent, the hypothesis cannot be statistically rejected.  Random variations
in the concentration measurements were too large to allow rejection of the
hypothesis.

     Second Hypothesis.  It was also hypothesized that the concentration
means for a particular element were identical between the following groups
of monitoring sites:  Sites 1 and 3, 4 and 5, and 8 and 9.  The results
shown in Table 36 are consistent with earlier findings.  The hypothesis is
rejected for the total mass concentrations, arsenic, and iron.  Their confi-
dence levels were all greater than 90 percent.  It can be inferred from these
results that there is a significant variation in arsenic, iron, and total
mass concentrations among the groups of monitoring sites specified in the
hypothesis.

     Third Hypothesis.  An analysis of variance was also performed in comparing
the 24-hour samples and the 12-hour day and 12-hour night samples.  The 24-hour
monitoring sites during the three campaigns were Sites 6, 7, 9, and 10.
Sites 6 and 7 were generally upwind of the fugitive dust sources during the
three monitoring campaigns, while Sites 9 and 10 were located farthest
downwind from the sources.  The 12-hour day and night samples were obtained
from Sites 1, 2, 3, 4, 5, and 8 closest to the sources.  It was hypothesized
that the means of these three samples groups were identified.  Thus, for a
particular element, u- (24-hour samples) = Tu (12-hour day samples) = u~
(12-hour night samples).
      As  shown  in Table 37,  the  hypothesis  is  rejected for the total mass
particulate  concentration with  a  97 percent  level of  confidence.   Likewise,
as  in the  first  two tests,  the  hypotheiss  is  rejected for arsenic,  copper,
and iron whose confidence levels  are greater  than 90  percent.   The results
of  the first three  analysis of  variance tests begin to indicate an interesting
conclusion;  namely,  that  in addition to total particulate concentrations,
arsenic,  copper, and iron concentrations  appear to have significant variation
with respect to time and distance from the sources.
                                     157

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     Fourth Hypothesis.  A final hypothesis analyzed was that for a particular
element, the mean concentration of the 12-hour day samples is identical to
that of the 12-hour night samples.  The results are shown in Table 38.   Here,
the hypothesis is convincingly rejected only for arsenic with a 95 percent
confidence level.  The hypothesis is not true for total mass concentrations
with a confidence level (88 percent) slightly below the criteria percentage
of 90 percent.

     Campaign I - 8 p.m. December 17 to 8 p.m. December 19. 1976.

     December 17, 1976—Friday.  Light snow fell throughout the day, accumu-
lating 1 to 2 inches by nightfall.  Cloudy skies prevailed throughout most
of the night; temperatures were well below freezing throughout the day  and
night.

     December 18, 1976—Saturday.  By dawn, skies had cleared and some  warming
occurred throughout the day.   The snow that fell the previous day melted by
noon and by midafternoon much of the surface moisture had evaporated.  Skies
remained clar throughout the day and temperatures rose to about 32 F.
Temperatures fell to the mid-twenties during the night.   Wind speeds were
especially low because of the influences of a high-pressure area situated
100 miles south of the power plant and also because of a nighttime temperature
inversion which developed from radiational cooling.

      December 19,  1976—Sunday.   Warm air advection began before  sunrise and
 continued throughout  the day,  causing an increase in wind speed and
 temperature.   Skies were mostly  sunny.   Temperatures rose into the  50's
 by  late afternoon.  A good deal  of  soil drying  had occurred during  the
 past  two days.   The first campaign  ended at 8 p.m.  Sunday.

      Campaign II -  8  p.m.  January 5 to  8 p.m. January 7,  1977.

      January  5,  1977—Wednesday.  Variable cloudiness and cold temperatures
were  the  agenda  for the day.   About 6 inches  of snow covered  most of the study
area.   However,  some  earlier drifting of snow had left  some areas exposed,
especially within  the grounds  of the power plant.   Temperatures rose to
a tropical 15 F.   Skies were partially  overcast during  the night,
                                    158

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     January 6, 1977—Thursday.  It continued very cold today and skies
became increasingly overcast, with a threat of precipitation appearing in
the west horizon by darkness.  Temperatures, however, rose to about freezing.
Snow began at 7 p.m. and persisted throughout .the night.

     January 7, 1977—Friday.  Snow continued to fall steadily until about
9 a.m.  About 5 inches had fallen during the night.  A period of snow squalls
occurred during the late morning and early afternoon hours.  Winds were very
strong, gusting to about 40 mph throughout the daylight hours and causing
blowing and drifting of snow.  Temperatures dropped to 15 F by evening.
Campaign II came to an end at 8 p.m.

     Campaign III - 8 p.m. April 5 to 8 p.m. April 7, 1977.

     April 5, 1977—Tuesday.  Rain which fell during the previous two days
created saturated soil conditions.  Soil evaporation occurred this day,
associated with partly cloudy skies through late afternoon.  Temperatures
were unseasonably cold, reaching only 44 F.  Showers began in the late
afternoon, and these later changed to snow flurries.  Snow flurries and snow
squalls continued throughout the night.


     April 6, 1977—Wednesday.  A snow blanket about 1 inch deep covered the
ground during the morning hours.  Heavy snow squalls lasting 5 to 30 minutes
each and accompanied by strong gusty winds persisted throughout the day.
Intervals of sunshine melted any accumulation of snow resulting from the
snow squall.  Flurries continued into the night.

     April 7, 1977—Thursday.  Clear skies gave way  to cloudy conditions by
late morning.  Temperatures were slightly above freezing.  Showers began
around noon and persisted until the early evening hours.  Winds continued to
be gusty as they had been throughout the monitoring  period.  Campaign  III
ended at 8 p.m.
                                    159

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                               References
A-l.  Thomas, T. J., and Ambrose, D. P., Battelle's Fugitive Dust Model.
      Battelle's Columbus Laboratories (1976).

A-2.  Multiple Point Source Model (PTMTP), DBT 51, U.S. Environmental
      Protection Agency, UNAMAP Tape (PB 229-771), Research Triangle Park,
      North Carolina (November 29, 1974).

A-3.  Vekris, S. L., "Dispersion of Coal Particles from Storage Files",
      Ontario Hydro Research Quarterly, Second Quarter, 23 (2), (1971).
                                     160

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          APPENDIX B
TERRESTRIAL BIOTA OBSERVATIONS
              161

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               TABLE 39.   WOODY SPECIES RECORDED AROUND THE
                           HOMER CITY POWER COMPLEX
      Common Name
       Scientific Name
 Alder
 Apple
 Ash,  green
 Ash,  white
 Aspen, big tooth
 Basswood,  American
 Beech, American
 Blackgum
 Boxelder
 Crabapple
 Cherry, wild black
 Devil's walkingstick
 Dogwood, flowering
 Dogwood, round  leaf
 Fir,  balsam
 Hawthorn
 Hemlock, eastern
 Hickory, shagbark
 Hickory, shellbark
 Hornbeam,  American
 Larch, subalpine
 Locust, black
 Maple, red
 Oak,  black
 Oak,  blackjack
 Oak,  chestnut
 Oak,  chinkapin
 Oak,  northern red
 Oak,  pin
 Oak,  scarlet
 Oak,  shingle
 Oak,  shumard
 Oak,  white
 Pine,  red
 Pine,  Scotch
 Pine,  Virginia
 Pine,  white
 Redcedar,  eastern
 Sassafras
 Spicebush
 Spruce,  blue
 Spruce,  Norway
 Spruce,  red
 Sumac,  staghorn
 Sycamore
Walnut, black
Willow, black
Witchhazel
Yellow-poplar
Alnus  sp.
Malus  sp.
Fraxinus pennsylvanica
Fraxinus americana
Populus grandidentata
Tilia  americana
Fagus  grandifolia
Nyssa  sylvatica
Acer_ negundo
Malus  sp.
Prunus serotina
Aralia spinosa
Cornus florida
Cornus drummondii
Abies  balsamea
Crataegus spp.
Tsuga  canadensis
Carya  oyata
Carya  laciniosa
Carpinus ^aroliniana
Larix lyalli
Robinia pseudoacacia
Acer rubrum
Quercus velutina
Quercus marilandica
Quercus prinus
Quercus muehlenbergii
Quercus rubra
Quercus palustris
Quercus coccinea
Quercus imbricaria
Quercus shumardii
Quercus alba
Pinus resinosa
Pinus sylvestris
Pinus virginiana
Pinus strobus
Juniperus virginiana
Sassafras albidum
Lindera benzoin
Picea pungens
Picea abies
Picea rubens
Rhus typhina
Platanus occidentalis
Juglans nigra
Salix nigra
Hamamelis virginiana
Liriodendron tulipifera
                                   162

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           TABLE 40.   MEDIUM AND LARGE SIZE MAMMALS RECORDED
                      AROUND THE HOMER CITY POWER COMPLEX(a)
  Common Name
  Scientific Name
Estimated
Abundance
Virginia Oppossum
Eastern Cottontail
Gray Squirrel
Muskrat
Raccoon
White-tailed Deer
Woodchuck
Didelphis virginiana
Sylvilagus floridanus
Sciurus carolinensis
Ondatra zibethicus
Procyon lotor
Odocoileus virginianus
Marmota monax
Common
Common
Common
Rare
Abundant
Abundant
Common
(a)  Records include mammals observed and/or their sign noted.
     Mammal sign involves tracks, droppings, nests, burrows, etc,
     Observations were made on December 15-16, 1976 and April
     11-15, 1977.
                                   163

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                    TABLE 41.  BIRDS OBSERVED AROUND THE HOMER CITY
                              POWER COMPLEX
-------
      TABLE 42.   REPTILES AND AMPHIBIANS OBSERVED AROUND
                  PONDS AND  STREAMS NEAR THE HOMER CITY POWER
                  COMPLEX
  Common Name	Scientific Name	

                          Reptiles
Queen Snake                                Natrix septemvittata
Wood Turtle                                Clemmys insculpta

                          Amphibians
American Toad                              Bufo americanus
Green Frog                                 Rana clamitans
Northern Two-lined Salamander              Eurycea bislineata
                                                      bislineata
(a)  Observations made during April 11-15, 1977.
                               165

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         APPENDIX C
WATER QUALITY DETERMINATIONS
             166

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                                APPENDIX C


                       WATERjQUALITY DETERMINATIONS


                             Land Use Analysis

     Because the watersheds at Homer City are influenced by a number of land
uses other than the proposed coal preparation plant, a cause-effect matrix
was developed based on the expected interactions between the land use class
and the water quality.  A set of five major land use classes was identified—
farming, mining, urban, construction, and power generation.  Power generation
is further separated into water treatment and associated sludge disposal;
wastewater treatment, industrial and domestic; cooling water; blowdown
discharge; ash sluice overflow; ash disposal; coal storage; and oil storage.
In attempting to trace the fate of pollutants from these activities, the
pollutant parameters ideally should be mutually exclusive for each.
     The monitoring of water quality in a watershed containing a number of
pollution sources should resolve the origin of the pollution.  Each source
can be monitored, but the downstream impact would remain unknown.  The distance
from a particular source to the point of discharge to the stream also plays
a role in influencing the quantity of material (yield) actually entering the
stream from the water shed.  Variations of distances from sources having
similar chemical characteristics will complicate the task of making accurate
predictions.  Finally, pollutants are generally nonconservative as they
travel from the source to the discharge point.  Individual pollutant species
may change radically over a distance and interactions between pollutants from
different sources may occur to produce a pollutant with another set of chemi-
cal and physical attributes.  This new species may be more or less toxic,
more or less soluble, and so forth, than its precursors.
                                     167

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Agricultural Activities

     The pollutants  resulting  from agricultural discharges include sediments,
nutrients,  pesticides, oxygen-consuming organic loads, and pathogens.  Pesticides
and  pathogens were excluded  from the water  quality monitoring survey because
of  the low  potential for  these pollutants to  be present  in any of the effluent
streams from  the  coal preparation plant.  Cropland is  responsible for about
50  percent  of the total sediment yield  in inland  waterways.  Sediment also
carries with  it significant  quantities  of organic and  inorganic matter including:
plant  nutrients,  pesticides, pathogens, and other water  pollutants.
     Pasturelands are also included in  this use classification.  Cattle and
sheep, even though grazing over relatively  large  areas,  may cause sediment
increases by breaking down the  streambanks while  drinking.  Additional sediment,
organic matter, and  nutrients  are contributed by  run-off water flowing through
and  around  grazing areas, feeding troughs, hayracks, and other areas where
a higher than average animal density occurs.  Nutrients  from cropland and
pastureland may be carried by water in both dissolved  and particulate forms.
Leaching can occur from both commercial fertilizers and  animal manure.  Commer-
cial fertilizers  consumed during 1972 amount  to about  37 million metric tons
(41  million tons) in the United  States.  These fertilizers contain roughly 20
percent nitrogen, 5.2 percent phosphorus, and 8.8 percent potassium.  Nutrients
from animal manure are an especially serious problem when manure is spread
on frozen ground  during the winter and early spring.   Snowmelt and spring
rains  cause the nutrients to be  transported to nearby  streams.  Some of these
nutrients can also be .transported to groundwater.

Mining Activities

     Mining activities are a potential source of several pollutants.  However
the  most serious  pollutant arising from mining activities is the mine drainage
generated by oxidation of pyritic materials with air in  the presence of water-
this drainage is  an  acidic mixture of iron salts, other salts, and sulfuric
acid.  Mine drainage  arises from  both underground and surface mining sources.
Coal deposits are commonly associated with pyrite and marcasite,  which are
disulfides  of iron.  Acid mine drainage can find its way into surface waters

                                    168

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where the acid and sulfate may result in severe deterioration in stream
quality.  The acid can react with clays to yield aluminum concentrations
sufficient for fish kills and with limestone to yield very hard waters which
are expensive to soften.  The acid can also selectively extract heavy metals
present  in trace quantities  in mineral and  soil formations, and this
ultimately results in  toxic  conditions in lakes and streams.
     Mining  refuse—waste materials  left near  the mining  site  after raw
minerals have been cleaned or concentrated—is another  source  of pollution.
Much of  this refuse contains pyritic material  which can be oxidized to
acidic  substances.  The  resultant acid water may remain in the pile until a
rainstorm, at which time it  is flushed into nearby watercourses.  Mine
drainage "slugs" during  storms are very detrimental to  aquatic life in
surface  waters.
     Many chemical reactions produce acid mine drainage.   The  most  important
 reactions, however,  are those involving the oxidation of  pyrite.  Mine drainage
 from pyrite  oxidation is generally  shown as occurring in three steps:  (1)
 oxidation of pyrite  to ferrous  sulfate and  sulfuric  acid; (2)  oxidation of
 ferrous sulfate to  ferric sulfate;  and (3)  hydrolysis of ferric sulfate.
      The oxidation of  pyrite to  ferrous  sulfate and  sulfuric acid is  rapid  if
 the pyrite is  exposed to moist  air:

                 FeS2(s)  + 3~1/2  °2  + H2° **  2S°42 + Fe+2 + 2H+      '        (1)

      Moisture condensation,  flooding,  and natural  drainage processes flush
 the ferrous  sulfate-acid mixtures into watercourses,  where dissolved oxygen
 in the water will slowly oxidize the ferrous iron  to ferric  iron.   This oxida-
 tion may be  catalyzed by other  metals (i.e.,  manganese, copper,  and aluminum)
 or by bacteria (Ferrobacillus ferroxidans):

                      Fe2+ + 1/4 02  + H+ -*• Fe3+ + 1/2 H2
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                        Fe3+ + 3H20 -> Fe(OH)3+ + 3H+                      (3)

     Reaction (1) does not represent the only possible reaction between pyrite
                                  -2   +        2+
and an oxidizing agent to yield SO, , H , and Fe  .   It has been demonstrated
       n.                         ^                ff1— fil
that Fe   can also be an effective oxidizing agent.     '  The kinetics and
reaction mechanisms of pyrite oxidation are extremely complicated and are
not examined in greater detail here.
      It  has long been recognized  that  the above  reactions  are  insufficient
to  characterize mine drainage.  For  example,  if  the  drainage passes  through
a calcareous  shale or limestone region,  the acid will be neutralized and
converted  into calcium  (or magnesium)  sulfate salinity  [Reaction  (4)]:

                      H2S04  + Ca(Mg)C03  •*• Ca(Mg)S04  + H2C03  .              (4)

      Carbonic acid generated by the  neutralization of acid mine drainage
vill  continue to dissolve limestone  to produce calcium  bicarbonate  [Reaction
 (5)], the  material which provides the  natural alkalinity of practically all
surface  and subsurface  waters:

                      H2C03  + Ca(Mg)C03  -»• Ca(Mg)(HC03)2     .              (5)

      The presence  of bicarbonate  alkalinity in neutralized mine drainage  has
important  ramifications.  Some of this alkalinity may be attributed to ferrous
bicarbonate.  Ferrous bicarbonate can  react with oxygen to form ferric hydroxide
and carbon dioxide,  thus providing a mechanism for  iron oxidation without the
formation  of  sulf uric acid  [Reaction (6) ] :
                  Fe(HC03)2  +  1/2  02  + H + Fe(OH)3* + 2CO^      .          (6)

      If  mine  drainage  passes  through noncalcareous clays  and  shales,  it  may
extract  aluminum  as  aluminum  sulfate.   Aluminum sulfate can hydrolyze to
precipitate aluminum hydroxide  and liberate sulfuric  acid, through reactions
analogous  to  those with ferric  iron.
     Many  clays contain alkali  oxides (potassium or sodium oxide)  in  signifi-
cant quantities.  A  representative chemical analysis  of a Pennsylvania clay
                                    170

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indicates 6.09 percent K-0 and 0.17 percent Na~0.   The presence of alkali
oxide in clays provides a neutralization path for acid mine drainage other
than reactions with limestone or calcareous shales.
     Mine drainage has been categorized into four  classes.  Data for these
classifications are presented in Table 43.  Distinctions among the various
classes are derived from drainage pH  (hence acidity) and from the oxidation
                             / *-i  -j \
state of the dissolved iron.
     Mining operations also generate wastes, commonly called spoil, in the
form of disturbed rock and soil.  If this spoil is left in piles, erosion
and run-off will carry sediment into streams.  This sediment is capable of
destroying life in streams, results in decreased capacity of streams and
reservoirs, and destroys fish and wildlife habitats.
                      TABLE 43.   MINE  DRAINAGE  CLASSES

Class II,
Partially Class III, Class IV,
Class I, Oxidized Oxidized Neutralized
Acid and/or and Neutralized and Not
Discharges Neutralized and/or Alkaline Oxidized
PH
Acidity,
mg/1 as CaC03
Ferrous iron,
mg/1
Ferric iron,
mg/1
Aluminum,
mg/1
Sulfate,
mg/1
2 - 4.5 3.5 -
1,000 - 15,000 0 -

500 - 10,000 0 -

0 0 -

0 - 2,000 0 -

1,000 - 20,000 500 -

6.6
1,000

500

1,000

20

10,000

6.5 - 8.5 6.5 - 8.5
0 0

0 50 - 1,000

0 0

0 0

500 - 10,000 500 - 10,000


   Source:   Reference C-7.
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Construction Activities

     Temporary activities are included in this discussion.  During the oper-
ational phase, the influence of construction activities on the measured water
quality will be minor.
     The two major categories of pollutants associated with construction are
sediments and, to a lesser extent, chemicals.  Sediment consists of deposited
particulates which have been transported by rainfall runoff and the wind.
Particulates carried by the wind are usually deposited in places where the
wind motion is obstructed by trees, grass, and buildings, i.e., where the wind
energy of motion vanishes.  Particulates picked up by rain runoff from
construction sites are deposited downstream in receiving water bodies such
as ponds, reservoirs, and dams.  Sediment deposition occurs when the sediment
load requires more energy to carry than the runoff can furnish.
     Sediment has physical, chemical, and biological effects on the
receiving stream and water bodies.  Sediment deposition can cause physical
damage.  For example, it can reduce water storage capacity; fill harbors
and navigation channels; cause more frequent flooding, resulting in increased
bank erosion; increase the suspended solids content (turbidity), thus reducing
light penetration; damage fish eggs and gills; destroy and cover organisms on
the beds of streams; reduce the flowing speed and the capacity of streams;
destroy and impair drainage ditches, culverts, and bridges; alter the shape
and direction of stream channels; destroy water recreational areas; and impart
an undesirable taste to drinking water.
     In addition, sediment deposition leads to an increase in the cost of
water treatment as well as in the cost of maintenance through the requirement
for frequent dredging.
     Chemical pollutants are generated from various operations and materials
used throughout various construction activities.  Chemical pollutants
originate from inorganic and organic sources.  These sources may be in
solid form in such construction materials as boards and  fibers and in  liquid
form as in paints, oils, and glues.  Organic materials have been gaining
wider use in the manufacture of construction materials.
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     Synthetic and nonsynthetic organic liquid chemicals are widely used for
surface treatment of walls,  for sealing cracks in roofs and floors, for gluing
materials together, and in liquid and spray paints.   Fuels are used as energy
sources in construction activities.   They include oils, gasoline, and diesel
fuel as used in trucks, power generators, backhoes,  bulldozers, and other
construction equipment.  Other organic materials used in construction activi-
ties include fertilizers, pesticides, plastics, rubbers, and curing agents.
     Construction operations at Homer City are capable of generating many
types of water pollutants.  The amount and type of pollutants generated during
construction will depend upon the type and time duration of the various
construction practices; the location and size of the construction site; the
rainfall distribution and frequency; pest control measures; the resistance
of the soil or land surface to erosion by gravity, water, and wind; the
chemical properties and geology of subsurface soils; and the number of
people and machines linked with each construction site.
     Construction practices typical of a given site will involve the following:
clearing, grubbing, and pest control, rough grading, facility construction,
and the restoration of staging and stockpile areas on completion of the job.
These practices constitute the prime source of various types of water pollu-
tants resulting from construction.
     Petroleum products are the largest group of materials consumed in
construction activities.  Petroleum products consist of oils, grease, fuels,
certain solvents, and many others.  Pollutants from construction activities
may include crank case oil wastes, oil leakage from storage containers, oil
solvents, dust control oils, minor oil spills during transfers and transpor-
tation, oil-laden rags, and degreasers.
     A majority of these materials float over the surface of the water and
spread easily over a wide area.  Oils and other petroleum products are
readily absorbed by sediment, which is the main carrier of these materials.
Sediment contaminated with oil is carried in runoff to receiving streams.
The inherent properties of petroleum products make them extremely difficult
to control after they enter water bodies.
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     The extent  of water pollution  caused by petroleum products at construc-
tion sites is dependent on the occurrence of spills from storage tanks, the
quantity of crank case oil wastes disposed of, the number of trucks and con-
struction equipment operated as well as the state of their maintenance, and
the magnitude of the construction activity.
     Some petroleum products impart a persistent odor and taste to water and
to  fish flesh.   Many oils have the  ability to block the transfer of air from
the atmosphere into water, which results in the suffocation of aquatic plants,
organisms, and fish.  Some petroleum products contain quantities of organo-
metalic compounds  (nickle, vanadium, lead, iron, arsenic) and other organic
components which can be toxic to fish and other organisms.

Urban  Activities

     Runoff  and  domestic sewage effluent are the two major causes of urban
water  quality degradation.
     Urban  runoff  is largely the result of storm water striking impervious
rooftops, driveways, and streets  and flowing into gutters.  During its
passage across surfaces loaded with atmospheric fallout or automobile
emissions, the runoff picks up and  transports a variety of pollutants into
the storm sewer  system.  Frequently, sewage treatment plants are not sized
to  treat the extremely large volumes of water represented by urban runoff
so  that storm sewers are designed to discharge directly into streams and
rivers.
     The most significant pollutant in terms of quantity is sediment.  During
periods between  rains, large amounts of solids from lawns, vehicles, atmos-
pheric fallout,  and other sources can accumulate on hard surfaces.  A subse-
quent  rainstorm  will wash off a large fraction of these pollutants in the early
stages of the storm.  Since the rate of wash-off is roughly exponential and
because the peak in the amount of water lags the movement of solids, a large
slug of highly polluted water is introduced to the receiving water in the
initial stages of runoff.  This is  the so-called "first flush" phenomenon.
     In addition to suspended solids, urban runoff contains varying quantities
of other pollutants such as organic materials (oxygen demand), nutrients,
and heavy metals.  Chlorides from street salting are also washed into receiving
waters during winter and spring snowmelt.
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      The second component of urban pollution, domestic sewage, is of
 concern primarily for its relatively continuous inputs of organic materials.
 Most wastewater plants afford adequate treatment and considerable amounts
 of dilution to a waste so that lack of dissolved oxygen is generally not a
 problem; however, during rainy periods infiltration and hydraulic overloading
 may occur, resulting in poor plant efficiency.  Some small communities in the
 study area do not treat their wastes before discharging to the receiving
 waters.
      Domestic wastewater treatment plants are generally not designed for
 removal of nitrogen and phosphorus and these, too, may be distributed to a
 receiving water bcdy along with the organic material.  This land use consti-
 tutes only a minor portion of the area in any of the watersheds.

 Power Generation Activities

      The power generation land use category is further subdivided into its
 component waste streams-water treatment effluent,  wastewater treatment
 effluent,  cooling tower blowdown,  discharge ash sluice water,  ash disposal
 leachate,  coal pile  runoff,  and oil storage leakage.
      Make-up water for  boilers and cooling towers  must be  of  high purity to
 prevent  scaling or corrosion problems.   Water treatment generally consists
 of  lime-soda softening  followed by an  ion  exchanger train  treatment  or
 reverse  osmosis.  Lime-soda  softening  removes  hardness by  precipitating
 calcium  as CaC03  and magnesium as  Mg(OH)2.   Solubility considerations
 suggest  that other cations such as Fe2+ and  Mn2+ may  also  be removed as
 hydroxides or  oxides.  To speed precipitation,  lime and soda ash  are some-
 times added in  greater than  stoichiometric quantities.   To aid in settling
 and dewatering, coagulants such as  alum, activated  silica, or polyelectrolytes
 may be added.  The resulting  sludge is, in some instances, dried  and calcined
 to recover lime and reduce the volume of sludge wasted.  In most  cases,
 however, the sludge is dewatered and landfilled.  At Homer City,  this sludge
 is transported to the ash-settling ponds for dewatering.   It is then removed
 to the ash disposal area.
     To produce the extremely high quality water such as that needed for
 supercritical steam cycle boilers,  nearly all of the ionic constituents must
be removed to yield an essentially deionized finished water.
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     Boiler water condensate is also polished via ion exchange after a number
of steam cycles.  After a certain period, the exchange sites on the resin
become saturated and must be regenerated.  At Homer City Station, the cationic
and anionic exchangers are regenerated with sulfuric acid and sodium hydroxide,
respectively.  Regeneration of the demineralizers is a constant activity at
the station.  The spent solutions, primarily sulfate salts and unreacted
regenerants, are piped to the industrial wastewater treatment plant for neutral-
                               ( C—8^
ization and lime precipitation.
     Wastewater treatment at the Homer City power plant consists of industrial
waste treatment and sanitary waste treatment.  Industrial wastes include
demineralizer and softener regenerants,  clarifier filter backwash, ash
settling pond filter-bed underflow, coal pile and yard runoff, and
miscellaneous station operating wastes.  The industrial waste treatment plant
is designed to remove both dissolved and suspended pollutants.  Suspended
solids are removed by a grit chamber.  The wastewater is then dosed with a
lime slurry and settled in a sedimentation tank.  The sludge is trucked to
the ash disposal area.  Provision is also made for the skimming and removal
of oil and grease.  Design capabilities  of this system are <7 ppm total iron
                               (C-9)
and <200 ppm suspended solids.       However, because of increasing hydraulic
loads, the treatment system has not performed as expected and modifications
have been and are continuing to be made.  Because of these changes, the
historical data are not necessarily representative of present conditions.
     The Water Management Task Force report of Fall, 1976, recommended the
                                                                           f Q_ y\
expansion of the system to provide additional capacity and improved design.    '
Changes in effluent quality undoubtedly will occur and must be accounted for
in future monitoring.
     Sewage  treatment  capabilities  for  the power plant are  provided by  two
package systems rated  at a  total  capacity of 19,000  gpd.  Each unit consists
of an aeration  activated sludge  tank and a clarifier.  The  units are  designed
                                          (C-9)
to achieve an 85  percent reduction  in BOD.       The sanitary effluent  is
chlorinated  to  1  to  2  ppm residual  before discharge.  Both  units are  apparently
                                                / p_O\
operating at or near  their  design capabilities.  ~    A separate 15,000-gpd
sewage treatment  plant has  been  installed to handle  the wastes from the
construction offices  for Unit  3.
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     The cooling water used in the wet draft type towers at Homer City still
contains enough impurities after treatment to cause a potential problem with
scale formation, if left in the system for an excessive number of cooling
cycles.  Discharges of water from the towers occur because of the need to
dilute these salts in the recirculating cooling water or because of plant
shutdown.  A portion of the blowdown water is returned to the system for
ash sluicing and the excess is discharged.  Water entering the cooling towers
has been pretreated to remove iron and turbidity and to adjust the pH.
A sedimentation stage is also provided.  Even so, the blowdown water still
contains sufficient suspended and dissolved solids to affect the quality
of the receiving body.
     The cooling water blowdown is also considerably warmer than the ambient
receiving water temperature.
     Ash sluicing is a major water-demanding activity at Homer City Station.
Bottom ash is sluiced directly from the boiler to the ash hydrobins.  The
pyrites removal system sluices the rejects from the pyrites hopper to a
holding bin and finally to the ash hydrobins.   Economizer ash is continuously
drained into water-filled storage tanks from which it is periodically removed
to the ash hydrobins.   Thus, the hydrobins serve as temporary storage sites
for all three heavy waste fractions.  The stored ash and pyrite are then
trucked from the hydrobins to the ash disposal area.  The fly ash is collected
from the precipitators and transported by conveyor into one of two storage
silos.  From these, the fly ash is loaded into trucks and taken to the ash
disposal area.
     The sluice water supernatant from the hydrobins is discharged to a pair
of settling ponds where solids are removed.  Extensive changes to this system
have been made; hence, many of the old data are unusable.  Since 1974, most
of the water for ash handling has been taken from the overflow of the ash
settling ponds instead of from cooling tower blowdown.  Pond underdrains are
used to dewater the sludge during pond cleanout.  Water in excess of recycle
needs is allowed to overflow to a ravine for discharge.     '  Plans are to
reduce the overflow volume by diverting the storm drainage and washdown water
from the ash pile and hydrobin areas to a separate treatment facility.
     Ash is disposed of on station property about 1/2 mile west of the
generating plant.  The valley fill method is used for impoundment of the ash,

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 and an earthen embankment downgradient contains the material.  Underdrainage
 is controlled by the use of a French drain collector system which discharges
 to catch basins below the retention embankment.  Layering of bottom ash
 fly ash, and pyrites is practiced to control subsidence and prevent channelling.
 Surface flows are controlled by grading and covering the ash with soil.  Grass
 is then planted to prevent erosion.
      In the catch basins, soda ash is added to raise the pH to a point where
 dissolved iron and other heavy metals will precipitate.  The water then flows
 to a series of settling ponds where the solids are allowed to settle.
      A large (500,000 tons)  supply of coal is stockpiled at the station to
 maintain generating capacity in the event of a mine shutdown.  Because this
 coal is not protected or enclosed in any way, runoff and leachate are
 produced whenever precipitation falls on the pile.   The runoff has the same
 characteristics as acid mine drainage owing to the pyrite in the coal  and,  in
 addition,  carries fine  coal  particles.   Most of the drainage from the  coal
 pile is impounded in two desilting basins which are equipped with pumps to
 transfer the impounded  runoff to the waste treatment plant for neutralization
 and solids  removal.
      Oil is stored at the station to provide fuel  for  firing the auxiliary
 boilers.  One tank contains  150,000  gallons  of No.  2 fuel oil and the  other
 two tanks 200,000 gallons.   Other than  the obvious  contamination potential
 from the oil itself,  trace amounts of phenols may  also  be present in the  oil.
 In addition, several  drainage  pits for  transformer  oil  are located in  the
 substation  area.

 Conclusions

     From the above land use analysis, a  cause-effect matrix was  developed
which shows  the various existing activities and their potential  pollutant
characteristics  (Table  6).   It is  not possible  to identify unique water
quality indicator parameters for each land use because  of  overlap.  Fortun-
ately, not all land uses prevail in each watershed  (Table  5).  Only Two
Lick Creek is affected by the majority of activities.
     Analysis of the relationships between the various  land uses  and water
quality should be ultimately extended to include the matrix entries devoted
to coal preparation and its interactions with the environment.
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                    Physical Descriptions of the Drainage
                     Basins in the Vicinity of the Homer
                          City Coal Cleaning Plant
General
     The principal geologic structure of the entire plant region is the
Latrobe Syncline.  The trend of its axis is northeast-southwest, and it
falls gently about 35 feet per mile toward the southwest.  The McKee Run
Anticline lies about 4 miles northwest, and the Chestnut Ridge Anticline
lies about 3.5 miles southeast.  Surface elevations in the study area
range from 960 to 1650 feet.
     The region is underlain by the Conemaugh formation to an elevation
of about 650 feet.  The outcropping members are the Connelsville sandstone,
which occurs from elevation 1200 to 1260 feet, and the Morgantown sandstone
which occurs from 1075 to 1200 feet.  These are thin-bedded, fine-grained
sandstones interbedded with red and green shales.  The sandstones are moder-
ately weathered to 10 to 20 feet deep; the shales are severely weathered to
40 to 50 feet deep.
     Beneath the Conemaugh formation is the Allegheny formation.  The upper
member of the Allegheny is the Upper Freeport coal; the middle members are
the Kittanning coals.  The Upper Freeport member has been extensively mined
throughout the region.
     Locally, the underlying strata are characterized by minor synclinal and
anticlinal features, all part of the Latrobe Syncline.  Bedrock strikes N 25° E
and dips a nearly flat 30 feet per mile to the southeast.  There are no known
faults in the region.  Joints are parallel and perpendicular to the axis of
the Latrobe Syncline and are generally tightly closed.
     Geologic information on the area is available in References C-l and C-2.
Data on precipitation and stream flows are from the NOAA weather station at
Blairsville, approximately 8 miles away, and from the USGS gaging station on
Two Lick Creek at Graceton, 1 mile southeast of the plant.
     Precipitation in the region has averaged 47.58 inches per year.  Maximum
precipitation was 64.31 inches.  Maximum monthly precipitation was 11.13 inches
and minimum monthly was 0.39 inch.
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     Stream discharge for the region which is measured at the USGS gaging
station on Two Lick Creek has averaged 21.68 inches per year.  (Stream flow
rates are converted to areal net discharge by dividing by watershed area.)
This includes runoff and groundwater.  Groundwater generally flows northeast
to southeast.  Groundwater levels are usually highest in spring and lowest
in early fall.
     Most of the groundwater data presented here are for various permit appli-
cations prepared by Gilbert & Associates for the Pennsylvania Electric Company
and from Reference C-2.  Data on soil types and locations come from the USDA
Soil Conservation Science Soil Surveys at Indiana County, Pennsylvania.

North Tributary to Cherry Run

     The unnamed tributary to Cherry Run north of the refuse disposal area
drains an area of approximately 1150 acres.  Relief in the drainage basin is
about 400 feet (from approximately an elevation of 1000 feet at Cherry Run
to a high point of 1388 feet), according to the USGS Indiana, Pennsylvania,
quadrangle topographic map, revised in 1973.  Maximum slope is about 35 percent,
with most of the drainage basin sloping at 10 to 15 percent.  The tributary
falls fairly gradually at 88 feet per mile.
     On the basis of the average discharge in the Two Lick Creek basin above
Graceton, 21.68 inches per year, discharge from the north tributary should
average 2.8 cfs.  However, actual streamflow is known to be intermittent.
     The Morgantown and Connelsville sandstones are major water-bearing
formations in the area and create numerous springs where they outcrop.  The
springs occur between elevations of 1050 feet and 1175 feet in the refuse area.
     Soils in the area are all silt loams or sandy loams, with erosion
potential rated by the Soil Conservation Service as moderate.  Thickness of
the soil layer is generally 10 to 102 feet.

South Tributary to Cherry Run

     The unnamed tributary to Cherry Run north of the refuse disposal area
drains an area of approximately 860 acres.  Relief in the drainage basin is
about 320 feet (from approximately 1000 feet at Cherry Run to a high point
of about 1320 feet), according to the USGS topographic map of the Indiana,
Pennsylvania, quadrangle.  Maximum slope is about 45 percent near the valley
                                      180

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bottom in the lower reaches.   This occurs over about 5 to 10 percent  of the
basin.  Most of the basin slopes at 10 to 20 percent.   The tributary  falls
at about 100 feet per mile.
     On the basis of average  discharge of the -Two Lick Creek basin above
Graceton, 21.68 inches per year, discharge from the south tributary should
average 2.1 cfs.  However, actual stream flow is known to be intermittent.
     The Morgantown and Connelsville sandstones are major water-bearing
formations in the area and create numerous springs where they outcrop.   The
springs occur between an elevation of 1050 feet and 1175 feet in the  refuse
area.  The springs are estimated by the designer of the refuse disposal
facility to flow at a maximum of 5 gpm.  The total contribution of the springs
to stream flow is estimated at not more than 100 gpm.^c~2)
     Soils in this basin are all silt loams or sandy loams, with erosion
potential rated by the Soil Conservation Service as moderate, except  for
occasional pockets of a shaley silt loam with severe erosion potential.
Thickness of the soil layers  is generally 10 to 102 feet.

Cherry Run

     Cherry Run drains an area of approximately 11,000 acres, including the
tributaries immediately north and south of the refuse area.  Relief in the
drainage basin is about 670 feet  (from approximately 980 at Two Lick Creek to
a high point of 1650 feet), according to the USGS topographic map of the
Indiana, Pennsylvania, quadrangle revised in 1973.  Maximum slope is about
50 percent and occurs at a constriction in the valley now used as a small
reser/oir about 2-1/2 miles upstream from Two Lick  Creek.  Most of the basin
slopes at 10 to 20 percent.  Cherry Run falls at about 20 feet per mile just
upstream of the reservoir.  Downstream it falls at  about 10 feet per mile.
     On the basis of average discharge of the Two Lick Creek basin above
Graceton, 21.68 inches per year, discharge from Cherry Run should average
28 cfs.
     Soils in this basin are silt loams, shaley silt loams, channery silt
loams, and channery sandy loams.  All are rated by  the Soil Conservation
Service as having moderate erosion potential, except for occasional isolated
pockets of a shaley silt loam with severe erosion potential.  Thickness of the
soil layer ranges from 5 to 120  feet.

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Common Ravine

     The Common Ravine drains an area of approximately 230 acres.   Relief in
the basin is about 240 feet (from approximately 970 feet at Two Lick Creek
to a high point of about 1210 feet), according to the USGS topographic map
of the Indiana, Pennsylvania, quadrangle.  Maximum slope is about 30 percent.
Most of the basin slopes at 15 to 20 percent.  The stream falls at 200 feet
per mile.
     On the basis of average discharge of the Two Lick Creek basin above
Graceton, 21.68 inches per year, natural discharge from the Common Ravine
should be about 0.6 cfs.  However, several of the generating station facilities
discharge into the Common Ravine.  These discharge points and their volumes
are:
     (1)  Two sanitary sewage treatment plants - 17,000 gpd capacity total
     (2)  Industrial waste treatment plant - 1000 gpm capacity
     (3)  Surface drainage for the generating station.
If all treatment plants operated at capacity, the additional flow in the
Common Ravine would be 2.2 cfs.
     Soils in this basin are all silt loams or sandy loams, with erosion
potential rated by the Soil Conservation Service as moderate.   Maximum thick-
ness of the soil layer is unreported.  Bedrock is exposed in this basin.
Second Ravine
     The Second Ravine drains an area of approximately 460 acres.  Relief in
this basin is 280 feet  (from approximately 970 feet at Two Lick Creek to a
high point of 1254 feet), according to the USGS topographic map of the
Indiana, Pennsylvania, quadrangle.  Maximum slope is  30 percent; most of the
basin slopes at 10 to 15 percent.  The upper reaches  of the basin have been
extensively modified by construction of portions of the generating plant and
settling ponds.  Slopes in the upper reaches are 10 percent or less.  The
stream falls at 140 feet per mile.  A small impoundment known as Rager's
Pond lies about 1000 feet upstream from the confluence of the Second Ravine
with the Common Ravine.
     The natural discharge of the Second Ravine, based on the average discharge
of the Two Lick Creek basin above Graceton, 21.68 inches, should average 1.2
cfs.   However, discharges from several settling basins will add an average
of 2.6 cfs.
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     Soils in this drainage basin are silt loams and sandy loams with moderate
erosion potential, according to the Soil Conservation Service.   Minimum
thickness of soil cover is 12 inches, and maximum thickness is  3 feet or more.
     Groundwater levels have been reported only for the upper reaches of the
basin in the vicinity of the settling ponds.   These levels range from a mini-
mum depth to groundwater of 2.9 feet to a maximum depth of 16.0 feet.  However,
these depths are expected to be highly seasonally variable.

Wier's Run

     Wier's  Run driins an area of approximately 2250 acres.  Relief  in the
drainage basin is about 440 feet (from approximately 960 feet at Two Lick
Creek to a high point of 1402 feet).  Maximum slope is 25 percent.   Most of
the basin slopes at 10 to 20 percent.
     An ash disposal facility has been constructed in a small valley off
the main channel of Wier's Run.  Above the point of entry of drainage from the
ash disposal area, Wier's Run falls at 240 feet per mile.  Below that point,
it falls at about 50 feet per mile.
     On the basis of average discharge of the Two Lick Creek basin above
Graceton, 21.68 inches per year, discharge from Wier's Run will be about 5.6
cfs.  The ash disposal area is not considered to be large enough that its
relatively higher infiltration rate and lower evapotranspiration rate will
significantly affect the average stream flow.  There are no significant water
discharges into the ash disposal area.
     Groundwater has been reported at the 0- to 6.8-foot depth in the basin.
Soil thickness is not known for the entire basin but was reported as greater
than 108 inches near the ash disposal area.  Soil types are all silt loams
rated as having moderate erosion potential.
     The Morgantown and Connelsville sandstones are major water-bearing
formations in this basin and occasionally create springs where they  outcrop.
Flow of these springs has not  been measured.
                              Water Chemistry

     This  section  includes a discussion of  some  equilibrium water  chemistry
 concepts related to  the  interpretation of data obtained  at Homer City.   Most
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water quality constituents behave nonconservatively, i.e., simple dilution
models are inadequate to predict the observed distribution of soluble species.
Although some parameters are not amenable to interpretation via an equilibrium
approach,  this  technique is still useful not only as a starting point in
understanding the  existing chemical controls but also in predicting responses
of  a  stream  to  changes  in land use and  topography.
      For this analysis, the following assumptions have been made:
      •  The  major  solubility controls on ferric iron are the
        amorphous  hydroxide and the aquo-hydrolysis products.
      •  The  solubility  of calcium and the levels of dissolved
        carbonate  and sulfate are controlled by their solubility
        products and alkalinity relationships.
      •  Iron and manganese oxides may be important  factors in
        determining the behavior of trace metals.
      •  Trace metals are controlled by  the  solubility of  the
        hydroxide, oxide, or carbonate, and/or by adsorption
        equilibria.
      •  Competition between cations for available ligands is of
        limited importance.
      •  Activity effects are not considered.
      •  Fluoride and phosphate anions exert a negligible
        influence  on the system composition.
      •  The  effects of  organic chelates are not included.
      These assumptions  and the lack of  precision in some of the equilibrium
constants  mean  that the resulting numerical solutions are a first approximation
to  an exact  and rigorous treatment.

Aqueous Iron Chemistry

      Iron may exist  in solution in either  the bivalent  or trivalent oxidation
 state.   Bivalent  or  ferrous iron solubility is controlled at low pH values by
 the solubility product  of ferrous carbonate,  FeC03(s),  provided alkalinity is
greater than 10   moles per liter.   The solubility product of  FeCO- is about
200 times smaller  than  the solubility product of  CaC03(s).   Ferrous iron
concentrations in  a  water saturated with CaC03 are, therefore, much lower
than its  soluble  calcium content.
                                   184

-------
     In waters lacking carbonate ion activity and not containing reduced
sulfur species (t^S, HS , S ), the solubility of ferrous iron is controlled
by the precipitation of ferrous hydroxide, Fe(OH)2(s).  However, the solubility
product expression alone is insufficient to determine the maximum soluble
ferrous iron concentration.  Reactions between the solid phase Fe(OH)~ and
the soluble hydroxo complexes must also be included.  The distribution of
ferrous iron as a function of pH with and without significant concentrations
of alkalinity present is shown in Figures 29 and 30.
     In the presence of dissolved oxygen, ferrous iron is thermodynamically
unstable and is converted to the trivalent oxidation state (Figure 31).
The rate of oxidation of ferrous iron is a function of the pH and dissolved
oxygen (D.O.) concentration.  At low pH and small D.O. values, considerable
amounts of ferrous iron may persist in solution because of the sluggish
kinetics.  Ferric iron solubility is controlled by the amorphous oxide
(Fe(OH3)) and hydrous oxide (FeOOH2).
     The soluble hydroxo complexes of ferric iron must be included in the
solubility expression to obtain valid concentrations of soluble iron.
The distribution of ferric iron species with pH is shown in Figure 32.
Ferric iron also forms strong phosphate complexes which influence the solubi-
lity at phosphorus concentrations exceeding 10   M.        A complicating
factor in examining the agreement of predicted and measured solubilities and
ferric/ferrous iron ratios is the stabilization of iron in solution by
naturally occurring humic or fulvic acids and/or the formation of hydrosols.
These stabilized iron colloids may have particle diameters on the order of
0.01 ym which will easily pass the 0.45 ym pores of the Millipore filter used
to operationally separate the dissolved and particulate fractions.  ~  '
     The concentration of soluble ferrous iron in equilibrium with ferric iron
may be determined from the standard half-cell potential for this half-cell
and the Nernst Equation:

                     Eh-I  +£iElogU*'-».
                                          fr
                                          f[
Soluble ferrous iron can react with hydroxyl ion and be oxidized according
                              2+                      _
to the following reaction:  Fe   + 30H  -* Fe(OH) I -I- e .
     Substituting the standard potential EQ and the concentration of ferric
iron as a function ferrous iron and hydroxyl ion concentration in the Nernst
Equation yields:
                                     185

-------
   10
    -2
   10
     -4
co
at
iH
O
rt
t-i
u
C
0)
u

o

0    -8
   10 8
  10
    -10
                                                                        14
            FIGURE 29.   CONCENTRATION OF FERROUS  IRON AS  A FUNCTION

                         OF pH IN A CARBONATE-FREE SYSTEM
                                        136

-------
   10
     -8
en
0)
iH    _?
o  10
e
o
•H
•U
(0
J-i
OJ
a

o
u
   10
     -4
   10
     -6
   10
     -8
   10
     -10
y////////////
      FeC03(s) V
                                    /X//////1

                                    Fe(OH)2(s)
     FIGURE  30.
SOLUBILITY OF FERROUS IRON AS  A FUNCTION OF pH IN A

SYSTEM CONTAINING DISSOLVED CARBONATE SPECIES
                                  187

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    0.8
    0.4
 o
 >
 X
w
 Ifl
•rl
 O
o.

 0)
TD
 O
 k-i
i-l
 u
 0)
r-\
W
   -0.4
  -0.8
                                                H° = "  °  + 2H  +  2e
J[Fe(OH)4]'
                                                                           [Fe(OH)3]-
                                                                         14
          FIGURE  31.   STABILITY  RELATIONSHIPS IN THE SYSTEM—Fe-02-C02


                                        188

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10
                                                                           14
          FIGURE 32.  CONCENTRATION OF FERRIC IRON AS A FUNCTION OF pH
                                       189

-------
                    Eh = -1.31V. + 0.059 log
                                              [Fe2+][OH ]3
 Figure 33 is a plot of ferrous iron concentration versus pH, assuming an
 upper and lower bound for the Eh of oxygenated waters of 0.7 and 0.5 volts,
 respectively, when measured against a standard calomel electrode.

 Manganese Chemistry

      The behavior of manganese in natural waters  is  somewhat similar to  the
 behavior of ferrous iron.   The solubility of  manganese in water  is  controlled
 by the solid phases MnC03  or Mn02,  depending  on the  Eh and concentration of
 dissolved carbonate species.  The Eh-pH diagram in Figure 34 has  been
 constructed for a total  concentration of dissolved carbonate of  100 mg/1
 as bicarbonate.   Near a  pH of 7,  manganese in solution is predominantly  Mn
 ion;  however,  in water containing very high bicarbonate  concentrations,  the
 manganese bicarbonate complex cation,  MnHCO ,  can significantly  contribute
                             (C—20)
 to the dissolved Mn species.v       In addition,  manganese tends  to form ion
 pairs of the form MnSO.  in solutions containing more  than 1000 mg/1 of sulfate
 ion,  and these  influence the solubility of manganese/C~2°)   It  should be
 noted that  the  relationships depicted  in the  previous  figure  are  valid only
 for equilibrium  conditions and that  manganese  equilibria  are  established
                                            (C-3)
 relatively  more  slowly than  iron  equilibria    .  Therefore, manganese  tends
 to stay  in  solution further  from  a source than iron does.
      Manganese  concentrations  between  1.0 and  10.0 mg/1 are  stable  under  Eh
 conditions  of oxygenated water.   Soluble manganese precipitates as  anhydrous
 oxide, which can  exert considerable  influence  on  the concentrations  of toxic
              (C -1)
 trace metals.

 Other Heavy Metals

     Control of divalent transition metal  ion  solubility by the carbonate or
hydroxide and hydroxo  solids and  soluble hydroxo  complexes is not limited to
ferrous iron.  The maximum concentrations  of copper,  zinc, lead, and nickel
that can exist in solution are similarly  determined by the solubility of their
respective complexes.  The solubility  relationships of these trace metals as
a function of pH are shown in Figure 35.  Solubility products and formation
                                            (C-19»C-20)
constants were obtained from the  literature.
                                     190

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    -2
    -4
    -6
+
CN
 00
 O
   -10
   -12
   -14
   -16
                                              Analytical Detection


                                                     Limit
              FIGURE 33.  SOLUBILITY OF  FERROUS  IRON  IN

                          AN OXYGENATED  SYSTEM
                                   191

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                 1.40
                 1.20
                 1.00
               -0.60
               -0.80
                     1   I   I   I  I   I   I  1   i   T I   I
        FIGURE 34.   FIELDS OF STABILITY OF SOLIDS AND  SOLUBILITY OF
                    MANGANESE AS A FUNCTION OF Eh AND  pH AT
                    25  C AND 1 ATMOSPHERE OF PRESSURE
Note:  Activity of  dissolved carbon dioxide species  100 mg/1 as HCOo.
       Sulfur species  absent.
                                     192

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                                                              	.X\X-_'-t-2  _\.X_
10
                                                                                       11      12       13       14
                 FIGURE  35.   SOLUBILITIES OF SOME METALS SHOWING DEPENDENCE ON  pH  AT 25  C

-------
 Calcium Chemistry

      In a system open to the  atmosphere  and containing less than 400 mg/1
 of sulfate,  the solubility of  calcium is  usually controlled by the precipi-
 tation of calcium carbonate.  As mentioned previously, the solubility of
 calcium is much greater than  the solubility of  iron.   Figure 36 can be used
 to determine whether a given  water is in saturation  equilibrium with calcium
 carbonate.  Waters undersaturated with respect  to CaC03 at a given pH and
 bicarbonate concentration* fall in the lower left side of  the saturation
 lines and waters which tend to precipitate calcium carbonate fall in the
 upper right portion of the figure.  Competition effects between cations for
 the carbonate ion have not been considered in the construction of the
 diagram.
                    1000
                      1-0
HCOJ. IN MILLIGRAMS PER LITER
  10          100
                  i
                  0)
                  i
                  2
                    100
                     10
                     1.0
                                                            1000
                          • 'v i i 11 PU   i   i  i i iw   i ^ i TIM ii
                  FIGURE 36.  EQUILIBRIUM pH IN RELATION TO CALCIUM
                              AND BICARBONATE ACTIVITIES IN SOLUTION
                              IN CONTACT WITH CALCITE
                Total pressure 1 atmosphere; temperature 25 C.
*  At pH values less than  9,  [alkalinity]    [HCO~],
                                       194

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Buffer Capacity

     The ability of a natural water to resist large changes in pH as a result
of inputs of acidic or basic wastes is of fundamental importance to an
assessment of quality.  In quantitative terms the buffer capacity is defined
as the amount of fully dissociated acid, C^, to produce a unit change in pH.
If the major buffering species in the system are the carbonates, then the
buffer capacity, 6, can be defined in terms of species contributing to alka-
linity and electroneutrality considerations  [Reaction (7)]:
              B * 2.3
               C (H+/K
(if)  + (OH~)  + —	±
                                                     K2/H+)2
where C  refers to the total carbonate concentrations and K  and K  are,
respectively, the first and second ionization constants of carbonic acid.
Reaction 7 can be rearranged to yield an expression  [Reaction (8)] for buffer
capacity  in  terms of the alkalinity (in milliequivalents/liter) and pH:
                        (Alk - OH~ + H+)(H+ + K K /H+ + 4K,)
               3 = 2.3	    :.• '	—     •        (8)
                           (1 + 2K2/H )(H  + K-j^/H  + t^)

It should be noted that alkalinity contributing species may also include
silicates and borates; however, these should be minor contributors in this
system.
                          Water Quality Analyses
Parameters Monitored
      The parameters monitored  are  listed  in  Table  4.   Not  all  parameters were
monitored  at  every site  and  during every  campaign.   Sites  are  identified and
located in Figure 6.
      Samples  of  the source coals and  the  material  at  the ash disposal  area were
analyzed and  the results confirmed the  belief  that an appropriate  set  of
parameters had been selected (Tables  44 and  45).   The coal analyses  indicate
that  the coal presently  used at Homer City exhibits generally  higher contaminant
levels, both  trace and macro,  than the  average of  the 101  coals analyzed by the
                            (C— 3)
Illinois Geological Survey.        Of  interest  are  the high concentrations  of
                                      195

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                                    TABLE 44.  CHEMICAL COMPOSITION OF COALS
vo

Analyses, percent
Element
Al
Sb
As
Ba
Be
Cd
Cr
Co
Cu
Fe
Pb
Mg
Mn
Hg
Ni
Ti
V
Zn
F
Se
TOS(f)
Cambria,
2.66
0.9
27.0
—
1.1
0.5
18
7
26
1.06
18
0.06
14
0.28
16
0.15
52
35
72
6.6
1.53
Wash . Co . ,
1.14
0.9
6.7
—
1.3
0.2
18
12
11
0.93
7
0.04
12
0.14
20
0.07
46
21
52
1.3
1.29
All
Coals 
1.29
1.26
14.0
— —
1.6
2.5
13.8
9.5
15
1.92
34.8
0.05
49.4
0.20
21.1
0.07
32.7
272.3
61
2.1
3.27
Upper
Freeport^0)
tmmm
(1.28) W)
32.8 (43.7)(d)
44.1
0.4
—
19.8
15
8
—
4
—
13
((.27)W)
12
—
23
19
88.7
—
™
Helen 
2.74
25
27
105
2.6
0.1
36
15
27
2.83
12.3
0.15
65
0.47
16.2
0.12
62
47
101
2.1
3.02
Helvetia (e)
2.92
25
23
121
2.6
0.1
34
15
32
1.87
15.5
0.14
36
0.35
17.5
0.12
58
69
112
2.9
1.97
Trucked
Coal^
2.61
25
49
258
2.6
.27
31
14
21
5.03
17.8
0.10
76
1.1
13.2
0.14
57
66
94
6.4
5.85

     (a)  Reference C-3.
     (b)  Washed  coal.
     (c)  Reference C-4 (ash analysis  back calculated  to  yield whole  coal  concentrations).
     (d)  Reference C~5.
     (e)  This  study.
     (f)  Total sulfur.

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     TABLE 45.  ANALYSES
                         (a)
OF ASH FROM ASH DISPOSAL AREA AT HOMER CITY COMPLEX

Moisture,
percent
Volatile solids,
percent
Oil and grease
COD
TOC
S04
S=
B
As
Cd
Cr
Cu
Fe
Hg
Ni
Zn
Pb
PH
Campaign I
11.9
0.59
<100
35,000
10,900
98
480
9.7
5.0
<1.0
112
126
112,500
0.14
71
40
12
8.74
Campaign II
12.6
3.6
97
13,626
21,600
156
405
1.4
3.8
0.6
144
90
112,000
<0.10
71
59
14
8.12
Campaign III
11.9
3.8
209
98,180
19,782
439
424
—
5.4
<1
117
92
11,200
<0.005
75
73
12
7.44
Mean
Weight
Arithmetic
—
2.14
135
48,935
17,427
231
436
5.55
4.7
0.9
124
103
78,567
0.0815
72
57
13
—
(Dry
Basis)
Geometric
—
2.00
127
36,043
16,700
189
435
3.69
4.7
0.8
124
101
52,063
0.0398
72
56
13
—
(a)   Values given in parts per million  (yg/g  dry weight) unless otherwise indicated.

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arsenic, beryllium, chromium, mercury, vanadium, and fluorine.  Selenium is
also relatively high in the Josephine coal.  On the other hand, zinc, cadmium,
and lead occurred in Homer City coals in lower concentrations than the Illinois
Geological Survey average.
     Grab samples of material from the ash disposal area were also analyzed.
This material was the ash from recently combusted coal, not the ash from whole
coal.  It is doubtful that these analyses are truly representative of the
entire ash emplacement because of its large volume, but the standard deviation
for the trace toxic metals and nonmetals indicates a small variation in
composition over a 5-month period.  Table 46 shows the ratio of the concentration
in the ash to the concentration in the coal for seven trace components.  The
least volatile elements, Cr, Cu, and Ni, tend to be concentrated in the ash,
while the more volatile ones such as Hg and As are depleted relative to the
raw coal.  The washed coal is expected to show a different distribution of
trace elements, with some of the elements now appearing in the ash in high
concentrations being transferred to the coal refuse disposal area due to their
                                                  ( C-3")
affinity for the sink fraction of the washed coal.
    TABLE  46.   CONCENTRATION RATIOS FOR  SELECTED METALS AND NONMETALS  IN
               HOMER CITY ASH AND  COAL SAMPLES

Element
As
Cr
Cu
Pb
Hg
Ni
Zn
Coal, ppm
32.2
33.8
26.9
15.1
0.62
16.4
60.4
Ash, ppm
4.7
124
102.7
12.7
< 0.08
72.3
57.3
Concentration Ratio
0.14
3.8
3.8
0.84
< 0.13
4.4
0.95
                                     198

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Sampling and Analysis Techniques

     Field Sampling Techniques.   Sites for water quality and sediment  analyses
were determined in advance of field monitoring.   Watersheds were sampled from
downstream to upstream.  All sites within each watershed were sampled  on the
same day or on two consecutive days.  A total of 50 surface and groundwater
sites were visited during Campaign I and 27 during Campaigns 11 and III.
     Samples were collected hy two two-man teams.  As each site was visited,
the location number, date, time, field analyses, and other pertinent obser-
vations were recorded.
     All samples were collected in prewashed polyethylene hottles and glass
jars.  The two methods.used to obtain the samples were  (1) grab sampling and
(2) the use of an automatic sampler.
     The grab sampling technique consisted of submerging each of the containers,
yet keeping them as close to the surface as poosible to prevent disturbing
the bottom sediment, as most streams were very shallow.
     At two of the sites, automatic composite samplers were used (Instrumen-
tation Specialties Company, Model  1580).  Due to the location of these  sites,
the  quality  of  the water  is more variable  than  at  the  other  sites.  In  order
to obtain  a  representative  specimen,  an approximately  750-tnl  sample of  the
water was  withdrawn  from the  stream at  60- to 90-minute intervals  for 6,  12,
or 24 hours.  During  the  winter (Campaigns I  and II) the ambient temperature
was  low enough  to keep the  sample  cold,  but  during Campaign III it was  necessary
to pack the  outer jacket  of  the sampler in ice.
      At each site while the sample was  being collected, additional data were
recorded.  A Yellow Springs Instrument  Company  polarographic D.O.  meter was
used to measure the  dissolved oxygen  content and temperature.   A Beckman Solu-
Bridge was used for  specific  conductance determinations.  Current  measurements
were taken with a Price-type  current  meter (Pygmy meter) at selected  surface
water sites.  Flow  was calculated using the velocity-area method.   Area deter-
 minations were made reading the depth off the current  meter rod and measuring
 the  width.  Flow values should be considered estimates.
      Depending on the location, three types of samples were obtained:   surface
water,  groundwater, and/or sediment.   Surface water sampling included grab
 sampling  and on-site analysis.   During surface water sampling, ancillary data
 regarding the physical conditions of  the stream and surrounding area were also
                                      199

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recorded.  Groundwater samples were obtained  from several piezometers emplaced
by D'Appolonia Engineering or from wells,  using a small plastic hand pump.
     Sediment samples were obtained from  several stream beds around the site.
Sediment was defined as any material  that  would pass through a 10-mesh screen.
There was some difficulty in obtaining an  adequate sample at some sites because
the stream bed was composed largely of gravel  (see Analytical Techniques).
     Preservative was added to each collected  sample immediately following the
morning or afternoon period of their  collection.  With the exception of ferrous
Iron, water samples were preserved using  the procedures suggested by the U.S.
Environmental Protection Agency.        Ferrous iron samples were preserved
with 4 ml HC1/100 ml sample.  Sediment samples were maintained at 4 C until
analyzed.

     Analytical Techniques.  The methods used  to analyze the parameters in the
water and sediment samples collected  during Campaigns I, II, and III are listed
In Tables 47 and 48.
     The  iron, nickel, and chromium values for the sediment samples composed
mostly of gravel may be biased high due to the possibility of contamination
from the  blender blades used to homogenize the sample.  This is probably not
significant for iron.
     Cation/anion balances were run to check the laboratory results.  Dupli-
cate analyses were routinely run on every  tenth sample to assure continued
good precision.

Data

     Data obtained for water and sediment samples from Cherry Run Basin,
Wier's  Run,  and Two Lick Creek are given in Tables 49 through 70.
                                      200

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              TABLE 47.  ANALYTICAL TECHNIQUES FOR WATER  SAMPLES
Parameter
pH
Acidity
Alkalinity
Sulfate
Chloride
Fluoride
Solids
Suspended
Dissolved
Total
Volatile
Sulfide
Reference
(a)
(a)
(a)
(a)
(a)
(a)
(a)

(b)
Method
Electrometric
Potentiometric
Potent ioinetric
Turbidimetric
Potentiometric

Titration
Titration

Titration
Distillation and Ion Selective
Electrode
Gravimetric

1. Methylene


Blue - Colorimetric
Ammonia Nitrogen
Kjeldahl Nitrogen
Nitrate Nitrogen
Nitrite Nitrogen

Total Phosphorus
Phenol
C.O.D.
T.O.C.
Specific Conductance
Chromium
Mercury

Ferrous Iron
Metals

  Arsenic
  Beryllium
  Calcium
  Cadmium
  Copper
(c)
(a)
(a)
(c)

(c)
(a)
(c)
(a)
(a)
(a)
(c)

(a)
(a)
2.  Titration
Ion Selective Electrode
Ion Selective Electrode
Brucine Sulfate
N-(l-naphthyl)-ethylene diamine
  dihydrochloride
Ascorbic Acid
4-Amino Antipyrene
Dichromate Oxidation
Beckman T.O.C. Analyzer/IR
Conductivity Bridge
Diphenylcarbazide
Persulfate/Sulfuric Acid Digestion
  Flameless AAS
1-10 Phenanthroline
Persulfate/Sulfuric Acid Digestion
  Silver Diethyl Dithiocarbamate
                                       201

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                            TABLE 47.   (Continued)
Parameter
                           Reference
                 Method
Metals (continued)
  Lead
  Magnesium
  Manganese
  Nickel
  Potassium
  Sodium
  Vanadium
  Zinc
                               (c)
                              (c)
Dissolved Metals
  (except Hg)

Total Metals (except Hg)
  (except Hg)

Oil and Grease                (a)

Samples Containing Coal Fines (d)
Filtered
Flameless AAS

Digestion
AAS

Liquid/Liquid Ether Extraction

Digestion with Perchloric Acid/
  Hydrofluoric Acid Mixture
(a)  Reference C-13.
(b)  Reference C-1A.
(c)  Reference C-12.
(d)  Referencec-18.
                                       202

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TABLE 48.   ANALYTICAL TECHNIQUES FOR SEDIMENT SAMPLES
Parameter
% Water
Volatile Solids
Oil and Grease

C.O.D.
Sulfide
Sulfate
PH
T.O.C.
Total Inorganic Carbon
Boron

Mercury

Metals
Magnesium
Potassium
Calcium
Sodium
Cadmium
Chromium
Coppsr
Nickel
Zinc
Lead
Iron
Manganese
Arsenic
(a) Reference C-16.
(b) Reference C-17.
(c) Reference C-13.
(d) Reference C-ll.
Reference
(a)
(a)
(a)

(a)
(a)
(b)
(c)
(c)
Cc)
(b)

(c)

(c)
















Method
Gravimetric
Gravimetric
Freon-Soxhlet Extraction after
Drying with MgSO -H 0
Potassium Bichromate Digestion
Distillation and Colorimetric
Extraction and Turbidimetric
pH meter
Beckman T.O.C. Analyzer
Beckman T.O.C. Analyzer
Na CO Fusion and Curcumin Color-
imetric
Acid Persulfate, Permanganate
Digestion: Flameless AAS
Nitric, Perchloric and Hydrofluoric
Acid Digestion Followed by AAS















                         203

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TABLE 49.
Site(b)
Acidity
as CaCO
3 PH
Total
Fe
SURFACE
PART 1:
WATER ANALYSES FOR CHERRY RUN BASIN-
CHEMICAL CONTROLS ON SOLUBILITY (a)
Dissolved
Fe Fe2+
Mn
Alkalinity,
Ca as CaCOo SO,
J 4
Campaign I
HI
H3
H6
CDE 1
H8
H7
H13
H14
7.2
1.8
3.8
175
6.2
1.7
3.6
7.8
6.7
6.1
6.7
3.8
6.1
6.5
6.5
6.1
1.71
1.50
0.26
3.20
1.20
0.20
0.66
0.95
0.10
0.76
0.09
2.93
0.12
0.05
0.06
0.27
0.42
0.76
0.19
0.80
0.17
0.17
0.14
0.14
0.28
0.28
0.21
22.0
2.24
<0.02
1.40
0.46
18.2
19.8
37.2
162
40.8
7.20
31.2
23.6
32.0
16.3
16.3
0
6.0
9.8
8.9
18.3
37.5
64.9
244
901
258
22.6
189
83.6
Campaign II
HI
H3
H6
H8(C)
CDE 1
H7
H13
H14
3.3
4.3
1.4
1.8
13.2
1.4
2.0
4.5
7.0
7.0
6.6
6.7
4.5
6.5
6.4
6.7
0.54
1.99
0.53
1.27
1.30
0.30
0.59
0.98
<0.02
0.44
0.03
0.03
1.20
0.04
0.02
0.18
0.38
<0.10
<0.10
<0.10
<0.10
<0.10
<0.10
<0.10
0.07
0.20
0.13
0.16
14.1
0.02
0.90
0.29
17.4
16.5
19.2
19.7
122
7.70
23.2
17.3
21.1
13.2
12.6
14.2
0
7.1
7.1
14.0
32.2
44.2
115
97
630
26.4
111
51.2
Campaign III
HI
H3
H6
H8(C)
CDE 1
H7
H13
H14
1.4
3.9
3.3
3.7
56.3
4.3
3.7
1.4
7.6
7.1
7.9
6.7
4.8
6.6
7.5
7.2
0.14
0.36
0.08
0.17
1.93
0.27
0.27
0.14
<0.02
<0.02
<0.02
<0.02
1.34
<0.02
<0.02
<0.02
<0.10
<0.10
<0.10
<0.10
<0.10
<0.10
<0.10
<0.10
0.02
0.27
0.16
0.09
13.5
0.02
0.87
0.02
20.3
22.2
38.9
35.0
13.8
7.2
37.2
20.3
44.2
25.4
19.6
23.4
2.2
10.5
15.7
44.2
27.3
73.6
267
208
1586
20.6
204
27.3
(a)   Values in mg/1 except pH.
(b)   See Figure 6 for water sampling site locations.
(c)   Relocated upstream from discharge of emergency holding pond.

                                          204

-------
                   TABLE 50.   GROUNDWATER ANALYSES FOR CHERRY RUN BASIN-
                              PART  1:   SOLUBILITY CONTROLLING SPECIES(a)
Site
PH
Total
Fe
Dissolved
Fe Fe2+
Suspended
Solids
Mn
Alkalinity
Ca as CaCO_ SO,
3 4
Campaign I
CDE 5
CDE 7
H9
Hll
4.1
2.7
7.1
4.8
9.6
1300
380
680
9.2
1720
0.12
88.0
1.76
373
5.60
5.70
16.8
25.4
-
5876
10.5
229
9.16
10.90
99.8 2.6
497 0
315
49.2 12.6
509
7353
_
29.4
Campaign II
CDE 5
CDE 7
H 9
H 11
3.9
2.3
7.5
6.1
11.8
620
454
810
-
620
0.13
1.67
1.42
56.7
2.03
2.46
3.2
72.0
20,100
13,960
17.3
76
10.4
19.1
159 0
329 0
306 563
80 67.4
722
3812
36.9
32.8
Campaign III
CDE 5
CDE 7
H 9
H 10
H 11


2.7
6.9
7.9
5.4


1300
143
153
47.5


1300
0.05
0.03
1.92

JNO
213
3.10
1.62
0.99

Sample — -
4.0
1,370
-
5,105


96
3.35
5.23
2.03


298 0
82 71.4
94.5 -
12.8 5.6


5574
22.8
-
35.1
(a)   Values in mg/1 except pH.
(b)   See Figure 6 for water sampling site locations.
                                          205

-------
    TABLE 51.   COMPARISON OF WATER QUALITY AT STATIONS H14
               AND H16 ON CHERRY RUN ABOVE AND BELOW MINE
               BOREHOLE DISCHARGES (CAMPAIGN l)(a>
Parameters
pH
Acidity, as CaCc>3
Alkalinity, as CaCo3
Sulfate
Iron, total
Iron, dissolved
Iron, ferrous
Calcium
Manganese
Site H14
6.1
7.8
18.3
83.6
0.95
0.27
0.14
23.6
0.46
Site H16
6.9
7.2
19.5
114.
4.40
4.38
0.77
29.2
0.49
(a)  Values in mg/1 except pH.
                             206

-------
                    TABLE 52.   SURFACE WATER ANALYSES FOR CHERRY RUN BASIN--
                               PART 2:  TRACE MATERIALS
Site(C>
HI
H3
H6
H8
CDEl
H7
H13
H14
H16
Reference
Stream
(a)
Concentrations
As
n.d.(b)
n.d.
n.d.
n.d.
n. d.
n. d.
n.d.
n.d.
n.d.
n. d.
Cd
n.d.
n.d.
n.d.
n.d.
0.003
n.d.
n.d.
n.d.
n.d.
n. d.
Cr
n. d.
n. d.
n. d.
n. d.
n. d.
n. d.
n.d.
n.d.
n.d.
n.d.
Cu
n.d.
n.d.
n.d.
n.d.
0.03
n.d.
n.d.
n.d.
n.d.
n.d.
Pb
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
Hg
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
Ni
n. d.
n.d.
n.d.
n.d.
0.34
n.d.
n.d.
n.d.
n.d.
n. d.
Zn
0.02
0.02
0.05
0.04
0.63
0.03
0.05
n.d.
n.d.
n.d.
V
n.d.
n.d.
n.d.
0.30
n.d.
n.d.
n.d.
n.d.
n.d.
—
Be
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d. .
n.d.
n.d.
—
(a)  Concentrations are means in mg/1;  values less than the analytical detection limit were
     averaged as one-half the detection limit.
(b)  n.d. = not detected.  Detection limits in  mg/1 are:  As 0.005;  Cd 0.001; Cr 0.02; Cu 0.02;
     Pb 0.005; Hg 0.0005; Ni 0.005; Zn 0.02; V 0.25; Be 0.02; and Phenols 0.005.
(c)  see Figure 6 for water sampling site locations.

-------
                                      TABLE  53.   SEDIMENT ANALYSES(a)—CHERRY RUN
Copalgo I



Campaign II




Campaign lit



H4 (H3)
CDE2 (CDE1)
H15 (H14)
H17 (H16)
H4 (H3)
H12 (H6)
CDE2 (CDE1)
HIS (H14)
H17 (H16)
H4  4.76 ran)
.42-4.
Fine sand (0.
Silt (0
Clay (<
.002-0
0.002
76 ram)
074-0.42 mm)
.074 nan)
tun)
11.1 0
43.8 27.3
35.5 64.2
J9.6 6.5
CDEl
II
37.3
37.3
10.8
14.6 /
H14

5
9
52
25
8
11
.2
.8
.0
.0
.0
H16 H3 H6 CDE1 HU

2
21
44
26
5
ii in in m in
.1 10.0 29.1 35.5 0
.7 74.9 52.7 33.3 55.7
.0 10.3 15.7 20.7 42.2
1 4.8 2.5 10.5 2.1
•1 \
H16
III
0
0.3
6.4
c
      (a)   See Figure 6  for water sampling site locations.

-------
                        TABLE 55.  TRACE METALS  IN GROUNDWATER NEAR CHERRY RUN
                                                                               (a)
N>
O
CDE5
-------
             TABLE  56.   SURFACE WATER ANALYSES FOR CHERRY RUN BASIN--
                         PART 3:  NUTRIENTS AND SOLIDS(a)
Station^

HI
H3
H6
CDE1
H8
H7
H13
HU

HI
H3
H6
H8
CDE1
H7
HI 3
HU

HI
H3
H6
H8
CDE1
H7
H13
H14
TP

0.10
0.02
0.03
<0.01
<0.01
0.02
0.04
0.03

0.06
0.04
0.02
0.08
0.01
0.02
0.05
0.04

0.01
0.01
0.01
0.02
<0.01
0.01
0.01
<0.01
SS

9.6
8.8
7.6
7.6
31.2
12.4
17.2
7.2

10.0
9.6
10.8
31.6
14.8
8.4
29.8
14.0

1.2
2.0
1.2
2.4
13.2
11.6
6.8
2.4
VS N03-N
Campaign
43
31
50
169
41
20
45.0
34
Campaign
48.0
28.0
36.0
53.0
182
19.0
42.5
4.0
Campaign
7.0
17.0
30.0
24.5
122
5.0 <
9.0
2.0
I
1.42
2.0
0.75
0.62
0.50
0.40
0.57
1.63
II
1.32
1.85
1.0
1.08
0.88
0.50
1.07
1.58
III
0.36
1.1
0.50
0.34
0.68
0.1
0.44
0.76
TKN

0.34
0.20
0.16
0.37
0.25
0.15
<0.05
0.14

0.21
0.31
0.27
0.20
0.41
0.10
0.12
0.25

<0.05
0.14
0.12
0.4
0.24
0.16
<0.05
0.36
TOG

1.2
2.4
2.8
6.0
2.5
2.2
1.2
1.7

1.4
2.8
1.5
2.0
4.5
2.0
1.7
2.0

2.0
3.5
3.5
4.4
2.5
3.5
4.0
4.0
NH3-N

<0.05
0.08
0.05
0.19
<0.05
<0.05
<0.05
0.08

0.06
0.05
<0.05
<0.05
0.17
<0.05
<0.05
0.06

<0.05
<0.05
<0.05
<0.05
0.17
<0.05
<0.05
<0.05
Total
Solids

159
178
430
1500
450
82
352
181

124
133
180
224
1087
82
233
156

124
183
442
378
1232
112
380
124
(a)   Values in mg/1.   TP = total phosphorus,  SS = suspended solids,
     VS = volatile solids, NO -N = nitrate nitrogen,  TKN = total
     Kjehldahl nitrogen, TOC = total organic  carbon,  NH -N = ammonia
     nitrogen.
(b)   See Figure 6 for water sampling site locations.
                                210

-------
TABLE 57.   SURFACE WATER QUALITY IN WEST TRIBUTARY TO WIER'S
           RUN—SOLUBILITY OF IRON, MANGANESE, AND CALCIUM
                                          Site
      Parameter	F9	Fll

      PH                              7.6        7.3

      Alkalinity, mg/1 as CaC03      54.2       31.2

      Sulfate, mg/1                  30.4       33.9

      Calcium, rag/1                  26.2       18.2

      Iron, ferrous, mg/1            <0.10      <0.10

      Iron, total, mg/1               0.27       2.45

      Iron, dissolved, mg/1           0.10       0.10

      Manganese, mg/1                 0.02       0.18
                               211

-------
                                  TABLE 58.  SURFACE WATER ANALYSES FORWIER'S RUN—
                                             PART 1:  SOLUBILITY CONTROLLING SPECIES
Total Dissolved

Campaign I



Campaign II



Campaign III



site(b)
F4
F6
F12
F14
F17
F4
F6
F12
F14
F17
F4
F6
F12
F14
F17
Acidity.
as CaC03
7.0
92.7
42.2
19.4
9.5
1.6
91.4
45.7
0
7.1
15.3
72.4
17.2
3.9
3.1
PH
7.3
4.9
5.9
6.7
7.0
5.6
5.0
4.9
7.1
5.8
6.5
4.9
6.5
8.0
7.6
Fe
0.19
19.5
15.0
11.1
7.73
0.24
16.9
12.8
1.02
3.80
1.37
16.6
8.40
2.19
1.82
Fe
0.77
17.7
13.0
6.90
4.04
0.03
16.2
12.2
0.02
2.00
0.08
15.8
7.10
<0.02
0.02
Fe2+
0.11
2.85
2.14
0.12
0.19
1.67
0.91
0.1
0.14
2.05
0.64
<0.1
<0.1
Mn
0.09
5.70
6.10
2.27
2.52
0.43
4.47
4.67
0.43
1.47
0.13
4.62
4.00
0.38
1.40
Ca
3.99
148
174
224
208.5
4.70
124
124
198
86
3.71
145
151
226
166
Alkalinity
as CaC03
10.5
5.6
34.4
14.2
18.0
6.5
2.4
11.0
42.2
20.5
7.7
3.8
60.1
31.0
49.2
S°4
14.3
789
836
1713
1360
17.3
540
555
1305
460
14.2
696
670
1450
905
(a)   Values in mg/1 except pH.
(b)   See Figure 6 for water sampling site locations.

-------
                     TABLE 59.  SURFACE WATER ANALYSES FOR WIER'S RUN—PART 2:  TOXIC MATERIALS
U)
Site
F3
F4
F6
F7
F8
F12
F9
Fll
F14

F17
(c)
Ash Analysis
As
n.d.(b)
0.005
0.014
0.013
n.d.
0.008
n.d.
n.d.
n.d.
n.d.

4.7
Cd
n.d.
n.d.
0.001
n.d.
0.004
n.d.
n.d.
n.d.
n.d.
n.d.

0.9
Cr
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.

124
Cu
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.

103
Pb
n.d.
0.005
n. d.
n.d.
n.d.
n.d.
n.d.
n. d.
n.d.
n.d.

13
Hg
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.
n.d.

.081
Ni
n.d.
n. d.
0.13
n.d.
0.26
0.10
n.d.
n.d.
0.06
0.07

72
Zn
n.d.
0.02
0.16
0.04
0.49
0.12
0.04
n.d.
0.08
0.09

47
V
—
n.d.
n.d.
—
—
n.d.
—
—
n.d.
n.d.

— —
Be
—
n.d.
n.d.
—
—
n.d .
—
—
n.d.
n.d.

—
Phenols
n.d.
0.013
n.d.
n.d.
0.009
n.d.
0.006
0.007
n.d.
0.010

	
    (a)  Values in mg/1.
    (b)  n.d. = not detected; see  Table  52 for metal and non-metal detection limits;  detection limits  for
        phenol = 0.005 mg/1; values less than detection were included in mean as  one-half  the detection
        limit.
    (c)  Ash analysis in mg/kg dry weight basis.
    (d)  See Figure 6 for water sampling site locations.

-------
                                   TABLE 60.   SEDIMENT ANALYSES  FOR  WIER'S  RUN
Sediment Site Number
(Associated Water
Sampling Site Number)*

F2(F4)
F13(F12)
F18(F17)

F2(F4)
F13(F12)
F18(F17)

F2(F4)
F13(F12)
F18(ri7)
z'

3.88
4.15
3.71

4.67
4.13
3.29

3.78
4.10
3.33
T.O.C.,
Z

1.94
1.28
1.44

0.35
0.21
0.20

1.97
2.56
0.18
pH,
units

6.34
6.73
7.11

6.63
6.93
6.65

5.72
7.16
7.15
«**
s

<46
<15
50

<26
<5
<5

<5
<5
5
Volatile
-** Solids,
S04 Z

139
298
931

1840
444
267

948
1420
953
Campaign I
8.17
4.06
5.89
Campaign II
8.08
3.71
3.13
Campaign III
6.63
6.38
2.55
Mn**

1095
349
500

1700
630
1000

550
450
825
As** Cd**

9.25 <1.0
19 <1.0
11.2 <1.0

8.0 0.3
9.2 0.2
7.6 0.4

41 <1
12 <1
8.4 <1
Cr**

66
156
105

383
197
102

128
172
136
Cu**

39
25
45

194
48
27

178
169
270
Pb**

20.5
2.0
19

47
29
21

30
26
28
Hg**

0.24
0.14
0.15

0.20
<0.1
<0.1

0.045
0.034
0.024
Ni**

41
79
105

210
115
71

89
117
97
Zn**

109.5
65
88.8

170
87
85

172
147
210
 * Associated water sampling site at same  location in parentheses.  See Figure 6.



** mg/kg.

-------
                TABLE 61.  SEDIMENT GRANULOMETRY FOR WIER'S
Grain Size, mm
Gravel (>4.76)
Sand (0.42-4.76)
Fine Sand (0.076-0
Silt (0.002-0.074)
Clay (<0.002)
Campaign II
F4
4.0
25.7
42)27.4
} 42.9

F12
10.2
22.3
43.1
18.4
6..0
Campaign III
F17 F4
0 0
65.3 2.8
22.9 14.9
} 11.8 16'7
14.6
F12 F17
0.1 10.3
50.7 42.6
45.4 . 40.6
} 3.8 } 6.5

(a)   Percent contained in each size range.
                                      215

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                         TABLE 62.   SURFACE WATER ANALYSES FOR WIER'S RUN—
                                    PART 3:  NUTRIENTS AND SOLIDS(a)
INJ
M
CT-

Campaign I




Campaign II




Campaign III




Site
F4
F6
F12
F14
F17
FA
F6
F12
F14
F17
FA
F6
F12
F1A
F17
Total
P
0.02
<0.01
<0.01
<0.01
<0.01
0.01
<0.01
<0.01
<0.01
0.01
0.01
0.01
<0.01
<0.01
0.01
Susp.
Solids
6.0
17.6
20.7
2A
35.3
1.2
13.2
15.0
13.2
29.3
20.8
1A.5
18.0
1A.A
11.2
Volatile
Solids
3
109
93
157
115
15.
95.
103
132
88.
1.
30.
60
83.
81.





0
0


0
0
0

0
0
N03-N
1.
0.
0.
0.
0.
0.
1.
0.
0.
1.
0.
0.
0.
0.
0.
14
72
74
54
66
84
04
90
54
26
54
50
52
28
58
TKN(b)
0.31
0.57
0.47
0.88
0.95
0.33
0.25
0.60
0.68
0.27
0.10
0.12
0.36
0.40
0.40
T.O.C.
2.85
<1.0
<1.0
1.9
2.A5
1.0
<1
-I
1.0
3.1
3.5
3.5
7.0
3.0
3.0
NH3-N
<0.05
0.31
O.A1
0.71
0.63
<0.05
0.21
0.21
0.59
0.18
<0.05
<0.05
0.21
0.35
0.28
Total
Solids
55
1,287
1,351
2,719
2,119
56.0
928
924
2,112
818
80.0
1,129
1,163
2,307
1,521
      (a)  Values in mg/1.
      (b)  Total Kjeldahl nitrogen.
      (c)  See Figure 6  for water sampling  site  locations,

-------
                                TABLE 63.   SURFACE WATER ANALYSES  FOR COMMON RAVINE/SECOND RAVINE-
                                             PART  1:  SOLUBILITY CONTROLS(a)
, , Composite Sampllnx Conditions
Slte^ pH
No. Campaign Acidity (unite)
Total Dies.
Fe Fe Fe
Hn
Ca
Alk.
Frequency
S04 mln
, Duration, Instantaneous
hr Flow, eft
A. CoBBon Ravine




J1




Ath Sluice Weter Overflow
Coal Pile Runoff
(before treatnent)

Cooling Tower Slowdown
Overflow (accidental)
Industrial Waete Treat-
ment Plant (IWT)f«>
CDE 17
CDE 17
CDE 17

CDE 15
CDE 15
CDE 15
CDE 16

CDE 12
CDE 8
CDE 8
CDE 8




I
II
III

I
II
III
I

I
I
II
III

I


0
0
183

140
605
1.
28.

0
7,410
10,588
7,1487

5.

0
8.9
11.4
4.8

4.7
4.3
999 4.9
3 4.8

9.4
2.4
1.9
,1 2.6

2 7.4

9.4-12.1
7.93
21.4
11.0
B. Second
47.5
191
472.5
8.00
C. Loading
1.73
2,420 2.
2,670 2,
2,300 2,

12.8

2.59
0.02
0.04
8.20
Ravine
45.7
188
453
7.90
Sources
0.70
450 1
800
2SO 1

0.03

0.09
< 0.10
0.37
< 0.10

4.05
1.10
467
< 0.10
0.68
1.12
1.76

6.70
14.7
45.2
2.21
102.5
485
215

133
148
209
113
51.0
615
0

2.4
0
0
0
290
1,180
920

664
1,237.5
2,940
424
90
60
60

90
60
60

10
12
20

10
10
6

2.5
	
2.5

_._
3.3
3

Receiving Water
< 0.1
.595
576
,301

< 0.1


0.15
668
211
56

0.89


118
417
41C
355

103


34.2
0
0
0

31.8


357
9.188
10,246
9,180

346


Second

Common


CoBoon

CoBBon
Ravine

Ravine/Second


Ravine

Ravine


Ravine





(a)  Values  in nig/'  unless otherwise  noted.
(b)  V.ilues  obtained by Pent-lee 9/7f>  -  11776.
(c)  See Figure 6 for water sampling  sice locations.

-------
                        TABLE 64.  SURFACE WATER ANALYSES FOR COMMON RAVINE/SECOND RAVINE—
                                   PART 2:  TOXIC MATERIALS^
oo
Site No.(d) As
Cd
Cr
Cu
Pb
Hg
Ni
Zn V
Oil &
Be Phenols Grease Cr
A. Common Ravine
CDE13
CDE10
CDE17
0.21
0.06
0.02
0.003
0.002
0.003
0.14
0.04
0.02
0.14
0.05
0.03
0.09
0.03
0.02
0.0006
n.d.
n.d.
0.14
0.06
0.06
0.
0.
0.
69 0.36
29 n.d.
23 n.d.
n.d. 0
n.d. 0
n.d. 0
.020 — n.d.
.030 — n.d.
.360 853(c) n.d.
B. Second Ravine
CDE12
CDE15
CDE16
0.47
0.02
n.d.
0.002
0.002
n.d.
n.d.
n.d.
n.d.
n. d.
0.06
n.d.
0.005
n. d.
n. d.
n.d.
n.d.
n.d.
n.d.
0.64
0.08
0.
1.
0.
10
73 n.d.
10
0
0.02 0
0
.013
.340
.009

     (a)  Values in mg/1.
     (b)  Not detected; see Table  52  for detection  limits.
     (c)  Single determination.
     (d)  See Figure 6 for water sampling site locations.

-------
                    TABLE 65.   SURFACE WATER ANALYSES FOR COMMON RAVINE/SECOND RAVINE-
                               PART 3:  NUTRIENTS AND SOLIDS

Site(c)
CDE17


CDE12
CDE15


CDE16
Campaign
I
II
III
I
I
II
III
I
Total
P
0.14
< 0.01
0.16
0.17
< 0.01
< 0.01
< 0.01
< 0.01
Susp.
Solids
61.25
64.0
968
31.6
45.6
156
63.15
23.6
Volatile
Solids
74.0
2.58
1,046
59
123
229
738.5
83
N03-N
3.08
3.75
0.40
3.3
4.4
4.35
2.06
3.5
TKN^
4.55
3.32
2.2
0.21
0.50
1.56
17.8
0.51
' TOG
19.9
7.25
97.5
4.4
5.0
24.8
21.5
3.0
NHs-N
4.2
2.4
1.6
0.17
0.45
1.0
14.4
0.36
Total
Solids
579.5
2260.5
2,441
685
1145
2,569
4978.5
743

(a)  Values in mg/1.
(b)  Total Kjeldahl Nitrogen.
(c)  See Figure 6 for water sampling site locations.

-------
                           TABLE 66.  SURFACE WATER ANALYSES FOR TWO LICK CREEK--
                                      PART 1:  SOLUBILITY CONTROLS
HI 8
H19
CDE18
CDE19
HIS
HI 9
CDE18
CDE19
HIS
HI 9
CDE18
CDE19
> Acidity
34.8
37.8
62.3
57.5
31.4
18.6
35.1
33.7
75.1
48.0
79.0
65.4
PH
5.3
4.1
3.2
4.1
5.2
4.8
4.7
5.2
3.6
4.1
3.6
3.9
Total
Fe
8.75
14.3
14.5
15.0
7.50
5.67
7.70
8.90
12.9
10.2
11.0
11.0
Diss .
Fe
8.20
10.0
12.4
12.3
4.72
3.93
5.23
5.32
11.0
7.3
8.7
6.9
Fe2+
1.36
1.36
2.06
0.49
1.17
0.24
0.58
0.42
0.27
0.23
<0.1
6.03
Mn
0.77
1.20
1.30
1.28
0.64
0.55
0.67
0.77
1.21
1.12
1.23
1.30
Ca
27.7
50.6
37.2
41.4
21.7
21.0
22.7
26.2
34.9
39.1
35.9
43.9
Alkalinity
2.7
3.8
0
2.2
4.9
3.7
3.2
2.8
0
0
0
0
so4
134
230
209
219
93
90
100
112
207
195
202
213
(a)   Values in mg/1 except pH.
(b)   See Figure 6 for water sampling site locations,

-------
                        TABLE 67.   SURFACE WATER ANALYSES FOR TWO LICK CREEK—
                                    PART 2:  TOXIC  MATERIALS^
N)
Site No. (c) As Cd Cr Cu Pb Hg Ni Zn V Be Phenols
His n.d.(b) n.d. n.d. n.d. n.d. n.d. n.d. 0.08 n.d. n.d. n.d.
H19 n.d. n.d. n.d. n.d. , n.d. n.d. n.d. 0.09 n.d. n.d. 0.008
CDE18 n.d. n.d. n.d. n.d. n.d. n.d. n.d. 0.10 n.d. n.d. 0.005
CDE19 n.d. n.d. n.d. n.d. n.d. n.d. n.d. 0.11 n.d. n.d. n.d.
(a) Values in mg/1
(b) n.d. = not detected; detection limits are given in Table 52.
(c) See Figure 6 for water sampling site locations.
TABLE 68. SEDIMENT ANALYSES — TWO LICK CREEK
site Fe, TOO, pH, S" Volatile Mn A« Cd Cr Cu Pb Hg
No. (a) Z Z units mg/kg S04" Solids, t mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
Campaign I No Sample
Campaign II CDE20 (CDE19) 8.05 11.3 5.26 < 9 5.925 17.72 210 10 0.55 152.5 94 48 0.42
Campaign III H17 (H18) 8.80 4.96 6.76 636 1,080 17.05 240 20 < 1 90 146 85 0.47
CDE20 (CDE19) 1.08 4.63 6.01 1,470 3,385 17.72 251.5 21.5 < 1 108 230 62.5 0.53





Ni Zn
mg/kg mg/kg

79 108
33 207
40 185

   (a)  See Figure 6 for water sampling site locations.

-------
             TABLE  69.   SEDIMENT GRANULOMETRY—TWO  LICK  CREEK
                                                                      (a)
Grain Size, mm
Upstream (H17)
 Campaign III
   Downstream (CDE 20)
Campaign II     Campaign III
Gravel (>4.76)
Sand (0.42-4.76)
Fine Sand  (0.074-0.42)
Silt (0.002-0.074)
Clay (<0.002)
      0
      0.3
      6.4
      68.7
      24.6
     0
     8.7
    47.9
    38.9
     4.5
16.5
 4.0
15.6
45.9
18.0
 (a)  Percent contained in each size range.
                   TABLE 70.   SURFACE WATER  ANALYSES FOR TWO  LICK  CREEK
                                PART 3:   NUTRIENTS AND SOLIDS

Campaign I



Campaign II



Campaign III



Site
No.(b)
H18
H19
CDE18
CDE19
H18
HI 9
CDE 18
CDE 19
H18
H19
CDE18
CDE19
Total
P
0.17
0.02
0.02
0.03
0.01
<0.01
<0.01
0.01
0.01
0.01
0.01
0.01
Suspended
Solids
11.0
34.5
14.5
20.0
30.7
27.0
25.0
26.0
5.6
8.8
14.0
27.3
Volatile
Solids
36.5
56.0
67.
76.
63.0
50.0
37.0
30.
24.0
28.0
47.
24.
H03-N
0.27
1.16
0.83
1.80
0.22
1.44
1.34
1.64
0.46
1.14
1.02
1.02
T*VM IS I
IMt *
0.48
0.98
1.0
1.25
0.52
0.71
0.35
0.41
0.56
0.6
0.75
1.02
TOC
2.65
3.2
3.5
4.0
3.3
1.8
1.8
2.5
2.5
2.5
3.0
6.5
....
0.84
0.68
0.77
1.03
1.28
0.19
0.18
0.19
0.94
0.48
0.68
0.62
Total
Solids
246
438
382
387
230
205
215
233
329
346
353
372
    Total KJeldahl Nitrogen.
(b)  See Figure 6 for water aanroling  site locations.
                                             222

-------
                                  References
 C-l.   Richardson,  George  B.,  "Structure  and Economic Geology of Pennsylvania,
       Indiana  Quadrangle",  USGS Folio No.  102  revised  1973  (July 1903).

 C-2.   D'Appalonia  Consulting  Engineers,  Inc.,  "Design  Plan  and Operation
       Plan—Proposed  Coal Refuse  Disposal  Facility—Homer City Coal Cleaning
       Plant",  prepared  for  the Pennsylvania Electric COrapany  (August  1976).

 C-3.   Ruch, R.  R.,  Gluskoter, H.  J., and Shimp,  N.  F.,  "Occurrence and
       Distribution of Potentially Volatile Trace Elements in Coal:  A Final
       Report",  Environmetnal  Geology Notes, No.  72, Illinois State Geological
       Survey,  Urbana, Illinois  (August 1974),  96 pp.

 C-4.   Chen, S.  Y.,  Nebgen,  J. W., Aleti, A.,  and McElroy, A. D., "Methods  for
       Identifying  and Evaluating  the Nature and  Extent of Non-Point Sources
       of  Pollutants", EPA 43019-73-014,  U.S.  Environmental  Protection Agency,
       Washington,  D.C.   (October  1973),  261 pp.

 C-5.   Environmental Sciences, Inc.,  "The Environmental Status  of Operations
       at  the  Homer City Generating  Station",  report to Pennsylvania Electric
       Company,  Pittsburgh,  Pennsylvania  (September  1972),  80  pp.

 C-6.   Pennsylvania Electric Company,  "Homer City EPA Discharge Permit Applica-
       tion //0720YJ20000885",  Johnstown,  Pennsylvania (May 1974), various
       pagination.

 C-7.   Landers,  D., "Report  on the Activities  of  the Water Management  Task
       Force",  prepared  for  Pennsylvania  Electric Company (October  1976),
       15  pp.

 C-8.   American Public Health Association,  American Water Works Association,
       and Water Pollution Control Federation, Standard Methods for the
       Examination  of Water  and  Wastewater, edited by M. C.  Rand,  14th Edition,
       Washington,  D.C.  (1976).

 C-9.   U.S. Environmental Protection Agency,  "Methods for the Chemical Analysis
       of  Water and Wastes", (1974).

C-10.   Smith,  G. F., The Wet Chemical Oxidation of Organic Compositions
       Employing Perchloric Acid With-or-Without Added  HN03-H5I06-HSO/.
       The G.  Frederick Smith Chemical Company, Inc.,  ColumbusYOhio  (1965).

C-ll.   U.S. Environmental Protection Agency,  Chemistry  Laboratory Manual
       Bottom Sediments, compiled by the Great Lakes Region Committee on
       Analytical Methods (December  1969).

C-12.   American Society of Agronomy and ASTM,  Methods of Soil Analysis,  edited
       by C. A. Black, Madison,  Wisconsin  (1965).
                                       223

-------
C-13.  Stumm, W., and Lee, G. F,, "The Chemistry of Aqueous Iron", Sonder-
       abdruck aus Schweizerische Zeitschrift fur Hydrologie, Birkhauser
       Verlag Basel, Vol. XXII  (1960), Fasc. I.

C-14.  Hem, J. D., "Study and Interpretation of the Chemical Characteristics
       of Natural Water", Water  Supply Paper 1473, U.S. Geological Survey
       (1970), 363 pp.

C-15.  Jenne, E. A., "Controls on Mn, Fe, Co, Ni, Cu> and Zn Concentrations
       in Soils  and Water; the Significant Role of Hydrous Mn and Fe Oxides",
       in Trace  Inorganics in Water, Am. Chem. Soc. Adv. in Chemistry Series
       21, 337-387 (1968).

C-16.  Stumm, W., and Morgan, J. J., Aquatic Chemistry—An Introduction
       Emphasizing Chemical Equilibria in Natural Waters, John Wiley and Sons
       New York  (1970), 583 pp.

C-17.  Stumm, W., "The Chemistry of Natural Waters in Relation to Water
       Quality", unpublished, 26 pp.

C-18.  U.S. Department of the Interior, "Water Resources Data for Pennsylvania,
       Part 2.  Water Quality Records", Geological Survey (1974).

C-19.  Personal communication, T. Clista, Commonwealth of Pennsylvania,
       Department of Environmental Resources, to B. Vigon, Battelle's Columbus
       Laboratories (June 1977).

C-20.  U.S.  Environmental Protection Agency,  "Quality Criteria for Water"
       EPA 440/9-76-023 (1976),  501 pp.
                                     224

-------
         APPENDIX D
AQUATIC BIOTA RECONNAISSANCE
             225

-------
                                APPENDIX D
                       AQUATIC BIOTA RECONNAISSANCE


                Sampling Site Locations and Descriptions

     Sampling sites were selected in seven streams in the vicinity of the
Homer City power complex:  Cherry Run and its north and south tributaries,
Wier's Run, Common Ravine, Rager's Pond tributary, and Two Lick Creek.  An
additional site was sampled in Ramsey Run, a stream some distance from the
complex.  Fourteen locations were sampled in these streams.  Sites were chosen
that would provide the best data for evaluating the impact of current plant
discharges on the aquatic biota of the receiving streams.  Cherry Run and
Wier's Run, which are intermediate-size streams, receive most of the drainage
from the plant area.  These and two small tributary streams, Common Ravine
and Rager's Pond tributary, flow into Two Lick Creek, a major tributary to
Blacklick Creek.  A survey conducted in 1972(D~D reported poor water quality
in Two Lick Creek due to low pH and high sulfates, iron, and total solids.
Mine drainage was the probable source of this contamination.  On the basis
of this report, only a minimal sampling effort was carried out in Two Lick Creek.
     A description of the areas sampled and their locations is given in
Table 71.  The precise locations of these sampling sites are shown on a map
of the area surrounding the Homer City power complex (Figure 25).  Ramsey
Run is not shown on this map.  It is a tributary of Two Lick Creek several
miles upstream east of Indiana, Pennsylvania, and flows in a southerly direction.


                      Organisms Selected for Study

     Three groups of aquatic organisms were selected for study.  Periphyton,
benthic macroinvertebrates, and fishes were investigated because of their
relative ease of collection, usefulness as indicators of  water quality, and
importance in the trophic structure of the aquatic community.
                                    226

-------
                TABLE 71.  rj AQUATIC 'BIOTA SAMPLING  STATIONS
Site
    (a)
-Location
.Description
        Chcvry Run north of refuses
          disposal urea
       'Cherry Run upstream from-
          disposal area tributary-
        Cherry Run downstream from
          disposal area tributary
        Tributary to Cherry Run north
          of refuse area
        Tributary to Cherry Run.south
          of refuse area (upstream)
        Tributary to Cherry Run south
          of refuse area (near mouth)
        Tributary to-Wier's Run below
          ash disposal area
        Wler'a  Run downstream from
          ash disposal area
       Wier'a  Run 1.0 km south of
          ash disposal area
                      Riffle arms 3 to 4 meters wide,  up to 0.3
                       - meter deep with cobble-rubble substrate.
                        Pool areas 5 to 6 me.tcirs wide 
-------
                             TABLE 71.     (Continued)
   Si
                      Location
                Description
    10    Wier's  Run at Mahan-School
             Road
    11     Rager's  Pond tributary
    12     Common Ravine
    13      Two Lick Creek at Coral
    14     Ramsey's  Run
Stream flows through wooded swamp.   Banks lined
  with alder, oak, willow, sycamore, dogwood,
  shingle oak.   Riffles 2 to 3 neters wide and
  C.2 to 0.4 neter deep; pools up to 0.7 meter
  deep.  Substrate cobble-rubble with occasional
  bouldar.

Stream has riffles and small pools.   Area sampled
  was 1 to 2 neters wide ar.J C.2 meter deep.   Sub-
  strate was pebble-cobble-rubble with some shale.
  All rocks were covered with a soft reddish or-
  ange precipitate.  Wooded with cherry,  oak,
  n.aple, hickory, and willow.

Area sampled was mostly riffle, 1 to 1.5 meters
  wide and 0.2j meter deep.  Substrate was pebble-
  cobbl-s-rubble.  Rocks were coated  with white
  precipitate which cemented them together,
  Stream flowed through powerline cut, lined with
  srr.ail willows.

Large stream over 30 meters wide.  Substrate was
  cobble-rubble with some boulders.   Substrate
  was covered with ferric hydroxide(?).
  Periphyton only collected near shore.

Stream, was  generally 2 to 4 meters wide;  riffles
  were 0.1  to 0.2 meter deep; pools  were  up to
  0.5 rr.eter deep.  Substrate was gravel-pebble
  with occasional cobble-rubble. Stream flowed
  through wooded area with a closed  canopy. Trees
  were alder, ironwood, cherry, and  maple.   Brown
  algae present on rocks.
(a)   See Figure 25  for  aquatic biota  sampling  locations.
                                           228

-------
                    Sampling and Analysis  Procedures

Periphyton

     Natural substrates were sampled in triplicate for hard-bodied periphyton.
Knife scrapings taken from a 3.14-sq cm area on cobble-sized rocks were
funneled into a sample bottle and preserved with an algal preservative composed
of 60 percent water, 30 percent alcohol, and 10 percent formalin.
     Quantitative procedures were utilized in the analysis of the  periphyton
samples.  All samples were adjusted to a constant volume (20 ml)  to normalize
resultant data.
     Diatoms in the samples were analyzed according to the following procedure:
     •  Half the sample was removed from each sample bottle with a
        pipette and treated with 30 percent I^C^ and I^C^Oy to dissolve
        extraneous organic matter (including nondiatomaceous algae).
     •  Residue was washed with tap water; the supernatant liquid
        was decanted three to five times at 3-hour intervals until
        the sample cleared.
     •  0.5 ml of sample was placed on a cover slip; water was
        evaporated from the cover slips on a slide warmer; cover
        slips were then placed on a hot plate for a minimum of 2 hours
        to combust any organic material which may have remained
        in the diatom frustules.
     •  Cover slips were fixed to slides using Hyrax mounting
        medium.
     •  Diatoms on each slide were identified to species under oil
        immersion with the aid of appropriate taxonomic keys.    'D~ '
     •  Counts were made and recorded for 40 microscope fields or
        more, depending on sample density.

Benthic Macroinvertebrates

      Benthic macroinvertebrates in  and on natural substrates were  collected
from riffle areas with a Surber sampler.   Five replicate samples  were taken
at  all stations.   These samples were placed in individual bottles,  preserved
with formalin,  and returned to BCL  for sorting,  identification, and enumeration.

                                     229

-------
     Organisms from unsorted Surber samples were separated from silt and
debris by passing the sample through a U.S. 30-mesh sieve.  The remaining
materials were then sorted, taking only those organisms remaining on the
screen.
     All benthic organisms were identified with the aid of a stereoscopic
microscope.  Identification was made to the lowest practical taxon utilizing
appropriate taxonomic keys.    *      Midge larvae were mounted on slides
and identified under a compound microscope according to the procedure
                       *  Spe(
                       (D-10)
presented by Mason.        Species diversities were calculated using the
Shannon-Weaver formula.

Fishes

     Fishes were collected during the winter survey utilizing a 4x6-foot,
I/4-inch mesh seine.  Spring collections were made using the seine and/or
a back pack shocker.  Fishing was conducted with approximately equal effort
(1/2 hour) at each station.  Fishes were identified, recorded, and released.
Specimens not positively identified in the field were placed in sample bottles,
preserved, and returned to the laboratory for identification.
     Fishes were collected at selected sites during the spring survey for
tissue analyses of nickel, copper, arsenic, and zinc.  The whole fishes
were held on wet ice, filleted (or in the case of the shiners and minnows,
left whole), frozen on dry ice, and shipped to Tradet, Inc., for analyses.

                              Detailed Data

     The types and numbers of species collected for all three organisms are
given in Tables 72 through 87.
                                    230

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TABLE 72.  DIATOM SPECIES AND STANDING CROPS COLLECTED
           FROM CHERRY RUN, DECEMBER 13-17, 1976
Upstream of Downstream of



Achnanthes linearis
Amphipleura pellucida
Amphora ovalis
Cocaoneis plaoentula v.
euglypta
Cymbella tumida
C. ventricosa
Fragilaria vaucheriae
Frustulia rhomboides v.
amphipleuroides
Frustulia vulgaris
Gomphonema acianinatvm
G. angustatum v. producta
G. sphaerophorim
Hantssoh'a amphioxys
Melosira distans
Meridian circulare
Navicula anglica v.
subsalsa
N. aryptoaophala
N. miniscula
N. radiosa
N. rhynoooephala
N. tripunatata
N. viridula
Nitzschia amphibia
N. apiculata
N. clausii
N. dissipate
K. .ignorata
K, palea
Surirella angustata
S. ovalis
Synedra acus
S. pu lohe I la
S. rumpens
S. ulna
S. ulna v. danioa
S. ulna v. subaequalis
S. sp.
Total standing crops
plant outfalls railroad
Sample 1 Sample 2 Sample 1
Standing crops,
9,000 41,000


70

70

100



5,000

18,000

46,000
100


5,000
5,000

200

500







400
70

32,000 14,000 70

100
5,000

46,000 134,000 1,680
bridge
Sample 2
orj»anisms/ci


9,000


18, (00
5,000
5,000
9,000

5,000

5,000


37,000



41,000 .

28,000

9,000

138,000
5,000
9,000
32,000

9,000
5,000
18,000


18,000




405,000
Downstream of
disposal
Sample 1
.2
51,000





5,000
9,000




5,000




5,000



18,000





18,000
9,000
5,000




5,000




9,000
139,000
area tributary
Sample 2

87,000
5,000





9,000






5,000
60,000



18,000

28,000


9,000


32,000
5,000
32,000
37,000

5,000


41,000
5,000



378,000
Number of Species
                                                       11
15
                           231

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TABLE 73.  DIATOM SPECIES AND STANDING CROPS COLLECTED FROM CHERRY RUN,
           APRIL 11-15, 1977





Achnanthes linearis
Aivphipleura pellucida
Baoillaria paradoxa
Cynbella prostrata
C. turgida
C. ventficosa
Fragilaria vaucheriae
Frustulia vulgaris
Gomphoneria angustatum
v. pro due ta
C. ccnstriatuvt
G. parvulun
Melosira distans
Meridion circulare
Navioula aryptoaephala
?i. minscula
U. radiosa
N. tripunatata
il. virdula
Nitzschia dissipata
N. ignorata
N. linearis
N. palea
Pinnularia sp.
Rhoiaosphenia curvata
Surirslla ovata
S. sp.
Synedi'a rwrrpens
S. ulna
S. sp.
Total standing crops

Cherry Run
Upstream of Downstream of
plant outfalls railroad bridge
Sample 1 Sample 2 Sample 3 Sample 1 Sample 2 Sample 3
Standing crops, organisms/cm^
3,000
2,000
1,000

No
organisms 900
2,600 2,000

2,000 4,000 3,500 8,000

6,000
2,000 1,000 4,000
7,000 3,500 8,000

3,000 4,000 900
2,000
18,000 13,000 11,000

14,000 29,000 23,000
1,000

1,700 2,000



4,000 900
1,000 2,000

1,700
2,600
34,000 28,000 0 48,000 31,300 56,000
Number of species


Downstream of disposal
area tributary
Sample 1

11,000



4,000

4,000

14,000


7,000
21,000
4,000

4,000


63,000



11,000

4,000
4,000

4,000


155,000

Sample 2 Sanple 3

3,000 3,000


3,000

3,000

3,000
10,000 27,000


900
3,000

2,000

21,000
3,000
12,000
3,000
900


3,000

900




32,700 60,000

                                                                13

-------
         TABLE 74.  DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE TRIBUTARY STREAMS IN
                    THE  VICINITY OF THE HOMER CITY POWER COMPLEX PROPOSED REFUSE AREA,
                    DECEMBER 13-17, 1976
Aehnanthes  linearis
Caloneis bacillum
Fragilaria  vaucheriae
Gomphonema  acttminatwn
Melosira ambigua
M. distans
M. va.ria.ns
Navi-oula salinamm v.
  intermedia
N. radiosa
N. viridula
N. sp.
Nitzsohia amphibia
N. fontioola
N. palea
Supivelta angustata
S. ovalis
Synedra pulchella

  Total Standing Crops
                               Tributary north  of
                             	refuse area	
                             Sample  1     Sample 2     Sample 1    Sample 2
                           Tributary  south of
                              refuse  area
                                     Standing crops, organisms/cm^
  9,000
110,000
             41,000
 46,000      37,000
110,000
              5,000
                           9,000
  9,000


284,000      83,000

           Number of species

      536
 Mouth of tributary
south of refuse area
Sample 1    Sample 2
543,000
  9,000
  9,000
              800
64,000
9,000
28,000 28,000
23,000

14,000
92,000
9,000 9,000
5,000
5,000 18,000 9,000

79,000 60,000 744,000




70


40


40
950

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K3
         TABLE 75.  DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE TRIBUTARY STREAMS
                    IN THE VICINITY OF THE HOMER CITY POWER COMPLEX PROPOSED REFUSE AREA,
                    DECEMBER 13-17, 1976

Tributary
Samp] - 1

north of refuse area
Saaple 2 Sample 3

Tributary
Sample 1

south of
Sample
Mouth of tributary south
refuse area of refuse area
2 Sample 3 Sample 1 Sample 2 Sample 3
Standing crops, organisms /cm2
Achna.nt.hes lanceolata 12,000
Cymbella amphicephala
C. sp.
Fragilaria itaucheriae
Prustuiia vulgar-is
Gomphonema angustatwm v.
produata
G. paruulum
Gyrosigma sp.
Melosira ambigua
M. distorts
Meridian eirculare
Naviaula cryptocephala 22,000
iV. radiosa 16,00
N. salinamm v. intermedia
/V. viridula 105,000
AT. sp.
flitzschia linearis
N. palea
Pinnularia sp.
Rhoicosphenia cupvata.
Surirella angustata
S. ovata 90,000
S. ovata v. pinnata
Synedra mnrpens
S. ulna
Tabellaria fenestrata
Total standing crops 245,000

5

6,000



1,000 3,000

8,000

6,000
12,000
3,000
3,000
17,000 42,000


3,000
1,000
6,000



13,000 45,000

5,000

8,000
49,000 133,000

6 11
3,000









13,000

6,000
80,000
10,000
3,000



3,000


64,000




182,000
Number of
8




11,000


39,000



6,000
28,000
72,000








413,000
11,000



580,000
species
7


8,000
8,000



8,000
10 5
90
20

23,000 5 30
105,000 30 90
210





20
8,000
315,000 5

8,000
5 10

483,000 40 250 240

8265

-------
     TABLE  76.  DIATOM  SPECIES AND STANDING CROPS  COLLECTED FROM WIER'S RUN, DECEMBER 13-17,  1976
                                                             Wier's Run
Aehnanthes Zinearis
Amphora ovalis v. ped-ioulus
Diatoma vulgare
Gomphonema angustatwn
  v. produeta
G. parvutwn
Melosira distorts
M. varians
Navicula aryptoaephala
N. pellioulosa
N. saHrianim v. intermedia
N. radiosa
Nitzseh-ia amphibia
N. apiculata
N. dissipata
N. palea
Pinnularia sp.
Synedra pulehella
S. ulna

  Total Standing Crops
                                Downstream  of ash
                              	disposal  area
                              Sample 1    Sample 2
                       1.0 km south of ash
                       	cli-gposal area
                       Sample 1    Sample 2
            .                       o
      Standing  crops,  organisms/cm

                        23,000

                        83,000      41,000
                         5,000       5,000
300
300
                         5,000
 40


100

140        116,000

 Number of species

  2              4
                                     5,000
51,000
                                             At
                                     Mahan School Road
                                    Sample 1    Sample 2
                                     28,000

                                     23,000
                                      9,000

                                      5,000
                                                  5,000
                         64,000
                          5,000
                        120,000
                          5,000
                         28,000

                         14,000
5,000
37,000
5,000
14,000
131,000
78,000
46,000
5,000
18,000
23,000
406,000
                                                                                                 11

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TABLE 77.  DIATOM SPECIES AND  STANDING CROPS COLLECTED FROM WIER'S RUN,
           APRIL 11-15, 1977





Achnanthea lanceolate
A . linearis
Cyirbella amphicephala
C. ventricosa
Diatoma vulgare
D. vulgare v. breve
Fragilaria vaitcheriae
Gorrpkonema parvulum
G. tergestimm
l-'eridicn circulate
!-'elosira aribigua
M. dis tans
Havicula aryptocephala
!•'. radiosa
N. salinarw v. intermedia
IS. Tripunatata
11, viridula
//. sp.
Kitzsahia igncrata
//. linearis
N. palea
Pinnularia braunii
v. amphicephala
P sp.
Stauroneis ancepe
Swirella cvalis
S. sp.
Synedra pulahella
S. ulna
S. sp.
Total Standing Crops


Wler's Run
Downstream from ash 1.0 km south of ash At
disposal area disposal area Mahan School Road
Sample 1 Sample 2 Sample 3 Sample 1 Sample 2 Sample 3 Sample 1 Sample 2 Sample 3
Standing crops/organisms cm

3,000
40 20 70 70
20
1,200
10
30 20
6,000 40
3,000
1,000
50
180 60 90 250 4,000
20 80 50 50 3,000
20 210 20 2,000 40 30
10
30 20
30 40
100
270 180 290
20 20
20
20

10
20 30
20 1,000
20
90 60 60
40 430 10,000 40
70
350 120 200 540 940 990 45,000 200 90
Number of species
75 36 12 9 10 52

-------
NJ
           TABLE 78.  DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE TRIBUTARY STREAMS
                      IN THE VICINITY OF THE HOMER CITY POWER COMPLEX, DECEMBER 13-17, 1976
Tributary to



Aehnanthes linearis
Cymbella tumida
C. turgida
Diatoma vulgare
Pragilaria vaueheriae
Gomphonema angustatum
v. product a
G. parvulwn
Melosira ambigua
M. distans
Navioula radiosa
Nitzschia amphibia
N. dissipata
N. fontiaola
N. palea
Synedva nanpens
Total Standing Crops
Wier's
Sample 1

856,000

18,000


28 , 000

18,000





9,000

92,000
1,021,000
Run
Sample 2
Standing
110,000
9,000


74,000
37,000





9,000
18,000


64,000
321,000
Rager ' s Pond
Common Ravine Tributary
Sample 1 Sample 2 Sample 1 Sample 2
crops, organ isms /cm



40 200 No organisms

40


740
590
40



110

40 1,480 240 0
                                              Number of species
                                                                                                0

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TABLE 79.  DIATOM SPECIES AND STANDING CROPS COLLECTED FROM THREE
           TRIBUTARY STREAMS IN THE VICINITY OF THE HOMER CITY
           POWER COMPLEX, APRIL 11-15, 1977
Tributary to Wler's Run Common Ravine Rager's Pond tributary


Achnanthes linearis
Cymbella amphioephala
C. ventriaosa
Eunoti-a exigua
Fragilaria leptostauron
v. dubia
F. vauoheiriae
Gomphonema anguAtatum
v. pioducta
^ G. parvu lum
to Melosira ambigua
00 M. distans
M. vafians
MericKon circulare
Navicula cryptocephala
N. radiosa
A/, tripunotata
N. sp.
N-itzaohia amphibia
N. dissipata
N. linearis
N. palea
N. tryblionella v. debilis
Surirella sp.
Stauroneia anoeps
Stephanodiscus astraea
Vynedr"a naapene
S. u Ina
Total standing crops

Sample 1

7,000
137,000
7,000



7,000
4,000










4,000

4,000





4,000
4,000
178,000

Sample 2 Sample 3 Sample 1 Sample 2 Sample 3 Sample 1 Sample 2 Sample 3
Standing crops L organlsms/ca2
56,000
51,000 202,000
41,000 3,000
60
5,000

5,000 26,000
10,000 3,000

168,000 3,000
60 530 120
140 160 60 180
10,000
20
30
30
20 50 30 30 60
60

10

5,000 3,000
5,000
30
30
5,000
13,000
6,000
357,000 263,000 260 760 270 30 30 360
Number of Species
                  11

-------
       TABLE 80.  DIATOM SPECIES AND STANDING CROPS COLLECTED
                  FROM TWO LICK CREEK AND RAMSEY RUN,  DECEMBER
                  13-17, 1976
Two Lick Creek Ramsey
Sample 1
Standing
Asterionella formosa
Caloneis baaillion
CymbeZia turgida
C. ventvieosa
Eunotia sp.
Fragilaria vaucheriae
Frustulia vulgar-Is
Gomphonema angustatum v.
produota
Melosira ambigua
M. distans
Navioula aryptoaephala
N. minisculla
N. sa.1ina.Twn v. intermedia
N. radios a
N. wiridula
N. sp.
Nitzsohia amphibia
N. dissipata
N. fontioola
N. palea
Pinnularia sp.
Stephanodisous astraea
Surirella ovalis
Tabellar-ia quadrisepta
crops,
160

AO
40
40

40
80


480


40





40

40

40

Sample 2 Sample 1
organisms/cm^

40


40
9,000



900
320
40

18,000
120
285,000
9,000

40

80 9,000

80
40 9,000
40
Run
Sample 2








9,000



83,000
9,000

64,000
239,000

9,000
9,000

18,000




Total Standing Crops
 1,040      1,740

Number of species
                              11
               11
339,000    440,000
     61
                                 239

-------
            TABLE  81.  DIATOM SPECIES AND STANDING CROPS  COLLECTED  FROM TWO LICK CREEK
                        AND  RAMSEY RUN, APRIL  11-15, 1977
Two tick Creek


Achnanthes lanaeolata
Amphipropa omata
Cymbella. amphicephala
Eunotia exigua
E. sp.
Frustulia vulgaris
Gonphonema parvulum
Melosira ambigua
M. distans
Meridian circulare
tiavicula cryptocephala
*** K. lanaeolata
O N~ minis eula
N. radioed
N. salinanw v. intermedia
H. tripunctata
Nitzchia diesipata
N. ignorata
». palea
Pinnularia braunii v.
amphicephala
P. sp.
Surirella anguetata
S. linearis
S. orata
Synedra nmpens
S. sp.
Sample 1

20
20 .
100




100
260
20



70

. 20



20



120

20

Sample 2
Standing
50


300



120
180




90





70


50

20


Sample 3 Sample 1
crops/organisms on



120
30
30
6,000

120 40,000
30
60 23,000
542,000



30

30
30 6,000
30

30


40,000

30
Ramsey Run
Sample 2 Sample 3











43,000
389,000 682,000
4,000
68,000
10,000

4,000







7,000 7,000


Total standing crops
                           770
                            11
880            570

  Number of specleg

  8             12
657,000
482,000
732,000

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TABLE  82.   BENTHIC MACROINVERTEBRATES  COLLECTED WITH A SURBER SAMPLER FROM  STREAMS
            IN THE AREA OF THE HOMER  CITY POWER  COMPLEX,  DECEMBER  13-17, 1976
Site:(a
DIPTERA
Chironomidae
Pentaneura sp.
Miovotendipee sp.
CricotopeuB sp.
Snrittia sp.
Diamesa sp.
Unidentified sp.
Tipulldae
Tipula sp.
Hexatoma sp.
Antoaha sp.
Dicranota sp.
Tabanidae
Chrypops sp.
SimuUidae
Simuliton sp.
Ceratopogonidae
Palpomyia sp.
Empidldae
Sp. A
Sp. B
) I 1


1
4 2
1 6


1

1
3





1



2
1
11567891011


1 2

138
9 14
133
1

9 10 9
1 1
1 4
3

15 4 1

1

1

1 11
20 1
12 13 14




11




1




5







EPHEMEROPTERA
  Baetidae
   Caeni.8 sp.
   Ephemerella sp.
   Paraleptophlebia sp.
  Heptageniidae
   Stenonema sp.
                                        11
                                                             1


                                                         4    1

-------
                                                   TABLE 82.    (Continued)
S3
Site:(a) 1 2
PLECOPTERA
Pel toper lidae
Feltoperla sp.
Nenouridae
Taeniopteryx sp.
Alloaapnia sp. 12
Perlldae
Acroneuria sp.
Chlotop«r lidae
Isoperla sp.
TRICHOPTERA
Rhyacophi lidae
Agapetus sp.
Rhyacophila sp.
Gloesoeoma sp. 1
Hydropsy chidae
Hydropsyehe sp. 1 1
Cheumatopeyche sp. 20-3
Unidentified sp.
3 <»





3

1




21
1 1


27
2 55
2
1 1 1 1 1 IS


1


2 2



6


20 3
3
1

26 5 5 101
48 3 65 7 424
25 4
ii 12 .13 li




1
1






2



20
9

               Limnephilidae
                 Astenophylax sp.                                1
               Philopotamidae
                 Chimarra sp.                             26     3
               Leptoceridae
                 Athripscdea sp.

             MEGALOPTERA
               Sialidae
                 Sialis sp.               2                       2
               Corydalldae
                 Chaittoides sp.                            1

-------
                                    TABLE 82.   (Continued)
0, (a)
Site:
COLEOPTERA
Elmidae
Stenelmia sp.
Opti-oservus sp.
Unidentified sp.
Psephenldae
Psephenus sp.
Ill


4
2
2


k_


1
4
5
3
3
1 .i 2. 1 1 10 II


13
1
4


11 11 M


11




PELECYPODA
  Sphaeriidae
    Sphaeriian sp.           24   104     1     1

CASTKOPODA
  Ancylidae
    Fervissia sp.             2           2                                                                    3

DECAPODA
  Asiacidae
    Cambarus sp.                                                1
    Or>(?o«eates  sp.                 1           1

OLICOCHAETA
    Unidentified sp.               2                                                                         23

NEMATODA
Total No. Individuals
Total No. Species
Species Diversity Index
88 120
19 8
3.28 0.90
10
7
2.72
204 186
26 16
3.50 3.32
7
5
2.13
121
16
2.61
0
0
0
23
9
2.73
542
7
0.95
0
0
0
0
0
0
100
15
3.20
(a)   See Figure 25  for aquatic biota  sampling locations.

-------
TABLE 83.  BENTHIC MACRO INVERTEBRATES COLLECTED WITH A SURBER SAMPLER FROM STREAMS IN THE  AREA OF  THE HOMER
           CITY POWER COMPLEX, APRIL 11-15, 1977


DIPTERA
Chironomidae
Pentanewca sp.
Microtendipes sp.
Cricotopus sp.
Diamesa sp.
Tipulidae
Tipula sp.
Hexatoma sp.
Dicranota sp.
Tabanidae
Tabanus sp.
Ceratopogonidae
!> Palpomyia sp.
Empididae
Sp. A
EPEMEROPTERA
Ephemeridae
Ephemera sp.
Baetidae
Baetis sp.
Ephemerella sp.
Paraleptophilibia sp.
Heptageniidae
Heptagenia sp.
Stenonema sp.
(a)
Site r a 23456789



4
15 6 1
25

1
2 2


1



11 3


1 1

3
6 1
1

2
12 10 3 3

10 11 12 13 14


1

22
1



1



1

3











-------
                                             TABLE  83.  (Continued)
                              Site:
                                                                                 10    11
12
13    14
N5
PLECOPTERA
  Nemouridae
    Allocapnia sp.
  Perlidae
    AcToneuria. sp.
  Chloroperlidae
    Isoperla sp.

TRICHOPTERA
  Rhyacophilidae
    Agapetus sp. A
    Agapetus sp. B
    Rhyaoophila sp.
    Protoptila sp.
  Hydropsychidae
    Hydropsyche sp.
    Cheumatopsyehe sp.
    Unidentified sp.
  Philopotamidae
    Chimarra sp.

ODONATA
  Gomphidae
    Hagenius sp.

HEMIPTERA
  Veliidae
    MioTove 1i,a sp.

MEGALOPTERA
  Sialidae
    Sialis sp.
                                                    13




9
2

11

10

2 13
11
1
26



34
19

2
3

2
32 7
2 30 4
1


1

1
1


-------
                                            TABLE 83.  (Continued)
                             Site:(a)l     2     3     A     5    6     7    8    9    10    11    12    13    14
  Corydalidae
    Chavloides sp.

COLEOPTERA
  Elmidae
    Stenelmi-s sp.
    Optioservus sp.
    Cleptelmis sp.
  Psephenidae
    1'sephenus sp.
    Unidentified sp.
                                                      14    1
                                                      26    2
                                                            2

                                                       8
114
N)
.C-
PELECYPODA
  Sphaeriidae
              sp.

GASTROPODA
  Ancylidae
    Fcrrissia sp.

DECAPODA
  Astacidae
    Cambarus sp.

ISOPODA
  Asellidae
    Aseltus sp.

OLIGOCHAETA sp.

-------
                                             TABLE  83.  (Continued)
                             Site:(a) 1     2     3     4     5     6     7     8     9     10    11    12    13    14
NEMATODA sp. !
Total number of Individuals 13 25 5 152 117 3 202 0 0 17 0
Total Number of Species 6 6 4 24 12 2 16 0 0 6 0
Species Diversity Index 2.19 2.25 1.92 3.98 2.57 0.92 2.13 0 0 2.23 0

0 0 47
0 0 12
0 0 2.58
(a)   See Figure 25 for aquatic biota sampling  locations.

-------
NJ
4S
OO
                     TABLE  84.   FISH SPECIES  SURVEYED AND COLLECTED FROM STREAM SITES IN  THE
                                  VICINITY OF THE HOMER CITY  POWER COMPLEX, DECEMBER 13-17,  1976
Species
Silver jaw minnow
(Erioymba bucaata)
Stoneroller minnow
(Campostoma anamalum)
Bluntnose minnow
(Pirnephalea notatus)
Creek chub
(Semotilus atromaculatue)
Blacknose dace
(Rninichtnys atratulus)
Number of individuals surveyed at sites indicated (a)(b)
1 2 3 4 5 6 7 8 9 10 11 12 13
1

337

253 1

3381 45

58 1

14


1



4

7
Silver shiner
  (Hotropis photogenis)
Striped shiner
  (Hotropis chrysocephalus)
Hogsucker
  (Eyper.telium nigriaans)
Common white sucker
  (Catostomus commersoni)
Golden redhorse sucker
  (Koxostoma erythrurnon)
Barred fantail darter
  (Etheostoma flabellare)
Johnny darter
  (Etheostoma nigrum)
Mottled sculpin
  (Cottus bairdi)
Smallnouth bass
  (Kicropterus dolomieui)
Rock bass
  (Anibloplites mpestris)
Pumpkinseed sunfish
   (Lepom-is gibbosus)
                                          111
                                          1     3
                                          8   20     3   11
                                                                                                            35
       (a) A visual appraisal of the stream habitats  at  Sites 7, 8, 11, 12, and 13 indicated that seining  for
          fish would not be worthwhile.
       (b) See Figure 25 for aquatic biota sampling locations.

-------
                 TABLE  85.   FISH SPECIES SURVEYED AND COLLECTED  FROM STREAM
                               SITES  IN THE VICINITY OF THE HOMER CITY  POWER
                               COMPLEX, APRIL  11-15, 1977
Species
                                          Number  of  individuals surveyed at  sites  indicated
Site:1
                                                                8
                                             10
                               11
                     12
                                                                     13UT
                                                                                                    14
Least brook lamprey
  (Okkelbergia aepyptera)
Silverjaw minnow
  (Ericymba bucaata)
Stoneroller minnow
  (Campostoma anomalum)
Bluntnose minnow
  (Pimephales notatits)
Creek chub
  (Semotilus atromaculatue)
Blacknosc dace
  (fthinichthys atratulus)
Silver shiner
  (Notropis photogenis)
Striped shiner
  (Notropis chrysocephalus)
Hogsucker
  (Ilypenteiium ni.gri.cans)
Common white sucker
  (Catoetomus commersoni)
Golden redhorse sucker
  (Moxostoma erythrurum)
Barred fantail darter
  (Etheostcma flabellare)
Johnny darter
  (Etheostoma nigrum)
Mottled sculpin
  (Cottus bairdi)
Smallmouth bass
  (Mioroptevus dolomieui)
Rock bass
  (Ambloptites rupestris)
Pumpkinsced sunfish
  (Lepomis gibbosus)
Bluegill
  (Lepomis macoochirus)
Yellow perch
  (Peraa flavescens)
32   18
20
14   10
          26   16
          12   44
          22    12
     16   13   28
               12
12
               17   35
6   20

     2
                                                    14
12

20
                                                    1

                                                    2


                                                    2

                                                    30
(a) No fish collections were attempted.
 (b) See Figure  25 for aquatic biota  sampling locations.
                                                249

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TABLE 86.  CONCENTRATIONS  OF  FOUR HEAVY  METALS  IN  FISH TISSUE  SAMPLES
           FROM CHERRY  RUN AND  WIER'S RUN,  APRIL  11-15,  1977
Concentration, ppm

Cherry Run — Upstream
(a)
Sediment
Tissue
Hogsucker - 3; 3-5 in.
Hogsucker - 1; 8 in.
Hogsucker - 3; 2-5 in.
White Sucker - 1; 5 in.
Bluntnose Minnow - 6; 2-4 in.
Bluntnose Minnow - 6; 2-4 in.
Bluntnose Minnow ' -7; 2-4 in.
Pumpkinseed Sunfish - 2; 3 in.
Rockbass - 2; 5-6 in.
Cherry Run — Downstream From

Hogsucker - 2; 10 in.
White Sucker- 2; 10 in.

of
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Wet
Dry
Arsenic
Disposal Area
4.1-8.97
6.5-15
<0.04
<0.3
0.023
0.16
<0.051
<0.37
0.055
0.26
0.22
0.90
0.26
0.96
0.10
0.50
<0.11
<0.70
0.070
0.31
Copper
(Site 1)
14-263
30-440
35.0
196
44.3
299
13.7
99.5
24.1
113
1.04
4.20
2.32
8.41
1.84
8.90
44.2
274
98.8
433
Nickel
43-89
90-140
11.7
65.9
3.48
23.5
10.1
73.1
24.9
117
0.93
3.78
0.86
3.12
<0.4
<2.0
6.84
42.4
14.6
63.9
Zinc
36-231
75-387
33.4
187
20.7
140
26.0
189
18.4
86.4
74.3
301
8.84
32.0
64.1
311
15.1
110
17.7
77.5
Disposal Area Tributary (Site 3)
Wet
Dry
Wet
Dry
Wet
Dry
3.0-3.6
4.8-13.3
0.029
0.13
0.053
0.28
15-152
23-225
6.32
27.3
14.3
76.0
46-55
71-207
3.15
13.6
2.01
10.7
24-128
107-190
26.6
115
15.1
80.5
                                   250

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                        TABLE 86.  (Continued)
Sediment
Tissue
White Sucker - 3; 14 in.

White Sucker - 2; 12 in.

Bluntnose Minnow ' - 2; 2.5

(b)
Stoneroller Minnow - 4; 2-4

Stoneroller Minnow - 4; 2-4

Stoneroller Minnow '
- 3; 2-4 in.
BluegilL - 1; 8 in.

Wier's Run — at


White Sucker - 3; 7 in.



Wet
Dry
Wet
Dry
in . We t
Dry

in. Wet
Dry
in. Wet
Dry
Wet
Dry
Wet
Dry
Arsenic

<0.07
<0.32
0.047
0.25
<0.28
<1.4

0.20
1.0
0.26
1.4
0.24
0.85
0.087
0.48
Mahan School Road
Wet
Dry
Wet
Dry
4.8-5.4
7.6-11.
<0.09
<0.42
Copper

8.37
37.9
5.73
31.1
1.91
9.56

131
663
87
464
2.33
8.41
53.2
291
(Site 10)
19-154
2 27-270
61
275
Nickel

2.08
9.27
1.01
5.55
<0.9
<4.5

2.98
15.1
11.2
59.8
1.37
4.85
14.8
80.9

49-55.4
71-105
9.4
42.3
Zinc

18.7
79.7
13.9
75.7
72.4
362

88.7
450
66.7
357
39.0
138
18.8
103

59-120
85-210
23
104
(a)  Whole.
(b)  Homogenized by hand with teflon and glass.
(c)  Sample  was taken approximately 2 stream miles upstream from fish tissue
    collection site.
                                     251

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TABLE 87.  FISH SPECIES COLLECTED FROM STREAMS IN THE AREA OF THE HOMER
           CITY POWER COMPLEX



Least brook lamprey
Silver jaw minnow
Stoneroller minnow
Bluntnose minnow
Creek chub
Blacknose dace
NJ Silver shiner
Oi
ho Striped shiner
Hogsucker
Common white sucker
Golden redhorse sucker
Barred fantail darter
Johnny darter
Mottled sculpin
Smallmouth bass
Rock bass
Pumpkinseed sunfish
Bluegill
Yellow perch
Cherry
Run
X
X
X
X
X
X
X
X
X
X
X
X
X

X
X
X
X
X
North tributary South tributary Tributary Wier's
to Cherry Run to Cherry Run to Wier's Run Run

X
X
X X
X X XX
XX X
X
X
X
X X
X
X
X
X





Rager's Fond Treatment Ramsey's
tributary plant tributary Run


X

X
X



X
X

X
X






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                               References

 D-l.   Environmental Sciences,  Inc.,  The Environmental  Status  of  Operations
       at the Homer City Generating Station,  Environmental Sciences,  Inc.,
       Pittsburgh,  Pennsylvania (1972).

 D-2.   Die Susswasser Flora Mitteleurapar,  A.  Pascher,  G.  Fischer,  Jena (1930),
       "Bacillariophyta" (F. Hustedt),  466  pp.

 D-3.   Patrick,  R., and Reimer, C.  W.,  The  Diatoms of the  United  States,  Vol.  1,
       Philadelphia Academy of  Natural  Sciences,  Philadelphia, Pennsylvania
       (1966), 700  pp.

 D-4.   Mason, W., An Introduction to the Identification of Chironomid Larvae,
       Federal Water Pollution  Control  Adm.,  U.S. Dept. of the Interior,
       Cincinnati,  Ohio (1968), 89 pp.

 D-5.   Pennak, R.,  Freshwater Invertebrates of the United  States, Ronald Press
       Company,  New York, New York (1953),  769 pp.

 D-6.   Usinger,  R., Aquatic Insects of  California, University  of  California
       Press, Berkeley, California (1971),  508 pp.

 D-7.   Ross, H., "The Caddis Flies, or  Trichoptera, of Illinois", State of
       Illinois, Natural History Survey Division Bulletin, _23, 1-326 (1944).

 D-8.   Burks, B.,  "The Mayflies or Ephemeroptera of Illinois", State of Illinois,
       Natural History Survey Division  Bull., 26, 1-216, (1953).

 D-9.   Prison, T.,  "The Stoneflies, or  Plecoptera, of Illinois",  Natural History
       Survey Division Bull., 20, 281-471 (1935).

D-10.   Shannon,  C.  E.,  and Weaver, W.,  The  Mathematical Theory of Communication,
       University of Illinois Press, Urbana,  Illinois  (1963).
                                      253

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                                GLOSSARY
acidity:  The base-neutralizing capacity of a water measured as the
     amount of sodium hydroxide required to titrate a sample gener-
     ally to a pH of 8.3 and expressed as mg/1 of equivalent CaC03«
     Strong mineral acids, weak acids such as carbonic and acetic, and
     hydrolysable metal salts such as ferrous or aluminum contribute to
     the acidity depending on the analytical method used.

alkalinity!  The acid-neutralizing capacity of a water measured as the
     amount of 0.1 N acid required to titrate the sample to a pH of 4.5
     and expressed in mill equivalents or in milligrams as equivalent
     CaC03-  The major contributors to the alkalinity in most natural
     waters are the carbonates.

benthic macrojnvertebrates:  (benthic) Relating to or occurring at the
     bottom of a body of water,  (invertebrate) Lacking a spinal column.

buffer capacity:  The ability of a natural voter to resist changes in
     pH.  The buffer capacity,  , is defined as the amount of a fully
     dissociated acid such as hydrochloric required to decrease the pH
     by one unit or the amount of strong base, for example, sodium
     hydroxide, to increase it by one unit.

colloids;  Substances that, in contrast to crystalloids, are not
     distributed as individual molecules or ions in a liquid but rather
     as larger aggregates of molecules; hence, they are intermediate
     between true solutions and suspensions.

depauperate:  Falling short of natural development or size.

diatom;  Any of a class (Bacillariophyceae) of minute planktonic
     unicellular or colonial algae with silicified skeletons that form
     diatomite.

dipteran;  Of, relating to, or being a two-winged fly.

Eh:  A measure of the oxidizing or reducing tendency of a water or
     sediment.  More positive Eh values indicate a system in which
     oxidized products such as sulfate, nitrate, and ferric iron are
     favored over their reduced counterparts—sulfide, ammonia, and
     ferrous iron, respectively.

fugitive dust emissions;  As used in this study, particulate matter
      that becomes airborne due to forces of wind, man's activity, or
      both.  Fugitive dust emissions may include traffic-generated
      particulate matter from unnaved roads, exposed surface areas at
      construction sites, and exposed storage piles.

                                    254

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Gaussian distribution:  A normal distribution described graphic-
     ally by a bell-shaped curve where 68 percent of the pollutant
     molecules are found within one standard deviation and 96 percent
     within 2 standard deviations.

hi-vol air sampler;  An instrument in which a relatively large volume of
    air (1.5-2.0 cubic meters per minute) passes through a filter and
    the suspended particulate is captured in the process on the filter.
    Concentration of the suspended particulate in the atmosphere is
    reported as micrograms per cubic meter of air.

hydrolysis:  The partial splitting caused by water of a neutral salt
    into its component-free acid and base; according to the strength of
    these products the solution reacts acidic or alkaline.

indicator species;  An organism associated with particular environmental
    conditions whose presence is indicative of the existence of these
    conditions.

microscopic analysis;  As used in this study, involves the examination
    of the high-volume filters under a microscope to determine particle
    type such as coal, ash, or soot and to quantify the coal or ash
    particles.

particle-sizing sampler;  A four-stage multi-orifice, high-volume
    impactor with a back-up filter, which can be operated as a component
    of a standard high-volume sampler.  The sampler separates the
    particulates in five size ranges:   7 microns or larger, 3.3 to 7
    microns, 2.0-3.3 microns, 1.1-3.0 mocrons, and 0.01-1.1 microns.

periphyton;  Organisms (as some algae) that live attached to underwater
    surfaces.

plume centerline;  That hieght which is the midway between the top and
    bottom edges of the plume.  The maximum pollutant concentrations are
    assumed in diffusion modeling to be found along the plume
    centerline.

scatter about line of regression;  A measure of the variability of data
    points about the line of regression.

standing crops;  The instantaneous living population.  The biomass
    present in a body of water at a particular time.

Taxa (Plural of taxon);  A classification of plants or animals according
    to their presumed natural relationships.

Trichopteran;  Any of an order (Trichoptera) of insects.
                                   255

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virtual point source;  A mathematical technique which combines all the
    emissions within a given area to an imaginary point source located
    upwind of the area source.  A virtual distance, Xy, is determined
    by approximating the initial horizontal standard deviation as
    S/A.3 where S is the length of a side of the area.
                                   256

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                                  TECHNICAL REPORT DATA
                           (Please read Instructions on the reverse before completing)
 1. REPORT NO.
  EPA-600/7-79-073f
                           3. RECIPIENT'S ACCESSION NO.
 4. TITLE AND SUBTITLE
  Environmental Assessment of Coal Cleaning Processes:
  Homer City Power Complex Testing
                           5. REPORT DATE
                           September 1979
                           6. PERFORMING ORGANIZATION CODE
 7. AUTHOR(S)
 S.E.  Rogers,  D.A.  Tolle,  D.P.  Brown, R. Clark, D. Sharp
 J.  Stilwell.  and B.W.  Vignon
                          8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
 Battclle  Columbus  Laboratories
 505 King  Ave.
 Columbus,  OH   43201
                           10. PROGRAM ELEMENT NO.

                              EHE 624A
                           11. CONTRACT/GRANT NO.

                            68-02-2163, Task 813
 12. SPONSORING AGENCY NAME AND ADDRESS
 EPA,  Office  of Research and Development
 Industrial Environmental Research Laboratory
 Research Triangle Park, NC 27711
                           13. TYPE OF REPORT AND PERIOD COVERED
                           Final:  17/77 - 7/7Q
                           14. SPONSORING AGENCY CODE
                            EPA/600/13
 15. SUPPLEMENTARY NOTES
 541-2851.
                     IERL-RTP  project officer is James D. Kilgroe, Mail Drop 61, 919/
 16. ABSTRACT                                                     ~~	—	
           The report describes  a  preliminary,  preoperational environmental survey
 conducted at a newly constructed  advanced physical coal cleaning plant near Homer
 City, PA.  The work is part of  a  comprehensive environmental assessment of
 physical and chemical coal cleaning  processes  performed by Battelle's Columbus
 Laboratories for the EPA.  Multimedia  grab-samples were gathered in the area to
 document the abundance or concentration  of selected environmental parameters.
 Collected data were used to evaluate the air,  water,  and biological quality of the
 area both through interpretive  techniques and  by direct comparison with EPA
 Multimedia Environmental Goal  (MEG)  values.  The ambient environment appeared to
 be typical of many western Pennsylvania  areas  which include coal mining and
 handling operations.  The general  area has been the site of numerous coal-related
 activities for decades.  Old abandoned strip mines and on site coal-fired power
 plants influence the natural environment.   The terrestrial and aquatic ecosystems
 near the Homer City plant reflect  varying degrees of  environmental stress.  Often
 stream water chemistry and biological  quality  were adversely affected by pollution
 sources outside the study area, especially by  acid mine drainage.  Estimated permis-
 sible concentration values for  several potentially hazardous elements were found
 to be exceeded at the plant before operations  started.
 7.
                               KEY WORDS AND DOCUMENT ANALYSIS
                 DESCRIPTORS
                                             b.IDENTIFIERS/OPEN ENDED TERMS  C.  COSATI Field/Group
 Pollution
 Coal
 Coal Preparation
 Assessments
 Strip Mining
 Electric Power Plants
Coal Storage
¥egetation
Coal Dust
Pollution Control
Stationary Sources
Coal Cleaning
Environmental Assessment
Acid Mine Drainage
Particulate
13B
08G
081
14B

10B
06C,08F
21D
 9. DISTRIBUTION STATEMENT
 Release to Public
                                             19. SECURITY CLASS (This Report)
                                             Unclassified
                                        21. NO. OF PAGES
                                            274
              20. SECURITY CLASS (This page)
              Unclassified
                                                                       22. PRICE
EPA Form 2220-1 (9-73)
            257

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