PB82-227521
Reclamation of Toiic Mine Waste Utilizing Sewage
Sludge Contrary Creek Demonstration Project
Virginia State Water Control Board, Bridgewater
Prepared for
Industrial Environmental Research Lab.
Cincinnati, OH
Apr 82
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P£82-227521
EPA-600/2-82-061
April 1982
RECLAMATION OF TOXIC MINE WASTE
UTILIZING SEWAGE SLUDGE
CONTRARY CREEK DEMONSTRATION PROJECT
by
Kenneth R. Hinkle
Virginia State Water Control Board
BHdgewater, Virginia 22812
.Grant No. S-803801
Project Officer
Ronald D. H111
Solid and Hazardous Waste Research Division
Municipal Environmental Research Laboratory
Cincinnati, Ohio 45268
INDUSTRIAL ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
CINCINNATI, OHIO 45268
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TECHNICAL REPORT DATA
(fie e ,ead /agr cr u au m bfo . ompl.tVngj
I. SPO T NO 2.
EPA-600/2-82 O61 I ORD Report
. RUCIPIENTS ACCES8JO NQ.
PI 22752 1
4. TIlLS AND SuSTITLI
Reclamation of Toxic Mine Waste Utilizing Sewage Sludge
Contrary Creek Demonstration Project
5 RIPORT OATS
Apnl 1982
.Pt o INoouoANIzATIONcoOI
AUTHOR($)
Kenneth R. Hinkle
I. PIRPORUIIdO ORGANIZATION REPORT NO
I. PI PO MINO ORIIANIZATION NAMI AND ADORISS
Virgini. State Water Control Board
Bridgewater, VirginIa 22812
10. PNOGR M ELIl ENT NO.
t pRANTNO
S—8O38O1
12. 5PONSO ING AGeNCY NAMI AND ADORSSS
Industrial Environmental Research Laboratory
Office of Research and Development
U. S. Environmental Protection Agency
Cincinnati, OH 45268
13. TYPE OP REPORT AND PERIOD COVERED
Interim
14. SPONSORING AGENCY COOS
EPA/600/12
15. SUPPLIMINTARY NOTES
A YDn 1 -
inree a anoonea pyrite mines in central Virginia triat had been Inactive since
1923 contaIned about 12 denuded ha and caused severe acid mine drainage (AND) in a small
stream known as Contrary Creek. TL AND included heavy metals and rendered the stream
virtually void of aquatic life. The Virginia State Water Control Board (SWCB) was
prompted to seek a solution to this problem when 1 lans were announced In 1968 to con-
struct a reservoir for a nuclear power plant downstream from Contrary Creek. Two of the
mines comprising about 8 ha were reclaimed with an EPA demonstration grant with the SWCB
contributing matching funds by In-kInd services and the Soil Conservation S rvice pro-
viding technical assistance. Reclamation began in 1976 and Included the use of sewage
sludge as a soil conditioner. Severe droughts in 1976 and 1977 and the highly toxic
nature of the mine wastes necessitated a continuing maintenance program to establish
vegetation. By the fall of 1980 approximately 90 per cent of the reclaimed areas
supported fair to good grass cover.
A comprehensive monitoring program has indicated llttl€ Improvement in water quality
since reclamation began. There appeared to be slight decreases in concentrations and
loads of AND in 1979 and 1980, but it is too early to tell If a remedial trend is
begInnIng. Further Improvement Is expected as infiltration and AND formation are re-
iuc.ed by development of a soil layer and vegetative cover. Biologic recovery has been
egligible. The project has been extended until mid-1982 for continued maintenance.
7. KIY WO OS AND DOCUMENT ANAL YSIE
DESCRIPTORS
b.IOINTIPIERSIOPIN ENDED TERMS
C. COSATI FIeld/Group
Reclamation
Sewage Sludge
Surface Mining
Water Quality
Abandoned Nines
Virginia
Demonstration Project
Revegetat on
Acid Mine Drainage
Pollut ion Abatement
08/H
081G
08/1
13/B
IL DISIRISUTION StATEMENT
Release to Public
19. SECURITY CLASS (ThISR.porrf
Unclassified
21. NO. O PAGES
3 S
so. ucumrrv CLASS (Thlsp.s)
Unclassified
22. PRICI
C PA Fo, 2220.1 (9.73)
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DISCLAIMER
This report has been reviewed by the Industrial Environmental Research
Laboratory-Cincinnati, U.S. Environmental Protection Agency, and approved for
publication. Approval does not signify that the contents necessarily reflect
the views and policies of the U.S. Environmental Protection Agency, nor does
mention of trade names or co m ercial products constitute endorsement or
reconinendation for use.
Ii
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FOREWORD
When energy and material resources are extracted, processed, converted,
and used, the related pollutlonal impacts on our environment and even on
ou health often require that new and increasingly more efficient pollution
cratrol methods be used. The Industrial Environmental Research Laboratory-
Cincinnati (IERL-CI) assists in developing and demonstrating new and im-
proved methodologies that will meet these needs both efficiently and economi-
cal ly.
This report describes a demonstration project In which sewage sludge
was utilized to reclaim toxic mine waste. As noted, the sludge, with the
assistance of limestone and fertilizer, was successful in establishing
vegetati n on mine waste dumps that had bc r barren for over 50 years. In
addition, these dumps were a major source of heavy metals to a nearby streaii.
Thus, a waste from one process, sewage treatment, is a valuable asset in the
control of another environmental problem. The information contained In this
report will be of Interest to mine land reclamation specialists, regulatory
agencies, and municipal waste treatment managerc. For further Information,
contact the Industrial Environmental Research Laboratory.
David G. Stephan
Director
Industrial Environmental Research Laboratory
Cincinnati
ill
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ABSTRACT
Three abandoned pyrite mines in Louisa County, Virginia that had been
inactive since the early 1920’s contained approximately 12 hectares virtually
barren of any vegetation. The toxic nature of the mine waste resulted In the
continuous leaching of acid and heavy metals Into a small stream known as
Contrary Creek renderirg it essentially void of aquatic life. The severe acid
mine drainage problem along this stream and associated fish kills downstream
had been recognized for years. In 1968 with the announced plans to construct
a reservoir as a source of cooling water for a nuclear power plant on the
North Anna River into which Contrary Creek drained, the Virginia State Water
Control Board was prompted to seek a solution to the problem.
Two of the mine sites comprising about 8 hectares were reclaimed with
funds from a demonstration grant from the United States Environmental Protec-
tion Agency with the Virginia State Water Control Board contributing matching
funds through in-kind services and the Soil Conservation Service providing
technical assistance. The third mine site was rec1aimer by a mining firm.
Reclamation which began in 1976 consisted of regrading nine spoils, construct-
ing diversions, applying soil amendments Including wastewater sludge, lime-
stone, and fertilizer and seeding. The purpose of the reclamation was to
reduce the acid mine drainage Into Contrary Creek and stabilize the mine
waste to minimize erosion.
Severe droughts in 1976 and 1977 and the highly toxic nature of the mine
waste has necessitated a continuing maintenance program to establish vegeta-
tion. Regular application of soil amendments and reseeding augmented by more
normal rainfall In 1978 and 1979 resulted in an Increased cover of vegetation
and a pronounced decre ise In erosion. Another dry suniner in 1980 agaIn
hampered efforts to Improve the vegetative cover, but overall loss of vegeta-
tion was minimal. By the fall of 1980 approximately 90 per cent of the re-
claimed areas supported a fair to good cover of grass. Ky-31 fescue grass
is the most successful planting.
Results of a comprehensive monitoring program still in progress have
Indicated little improvement in the water quality of Contrary Creek since
reclamation began. There appeared to be slight decreases In concentrations
and loads of acidity and some metals In water years 1979 and 1980, but It
Is too early to tell If an improving trend Is beginning to emerge. Further
Improvement is expected as a result of the reduction in Infiltration and acid
mine drainage formation caused by the development of a soil layer and vegeta-
tive cover. The addition of sewage sludge and limestone should provide some
in situ treatment of the acid mine drainage. Insufficient time has elapsed
for these impacts to be seen in the stream system. Monitoring of the Contrary
Creek arm of Lake Anna showed acid mine drainage to have a pronounced in-
fluence for a short distance out into the reservoir but apparently insignifi-
lv
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cant effect elsewhere In the lake. Biologic surveys have revealed negligible
improvement in the blota In Contrary Creek since reclamat1on
Average cost of reclamation Including all maintenance for the two mine
sites funded from the demonstration grant has been $14,518 per hectare.
In late 1980 the Environmental Protection Agency approved a request from
the Virginia State Water Control Board to extend the prr ject until mid-1982
to provide for continued maintenance as needed including application of soil
amendments, seeding and erosion control.
This report covers all of the work cot 1eted In this project until the
latter part of 1980.
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CONTENTS
Foreword ill
Abstract lv
Figures ix
Tables xvi
Acknowledgments xx
1. Introduction 1
2. ConclusIons and Recoinnendations 2
3. Background 4
LocatIon 4
Climate 4
Topography and drainage 6
Geology 6
Mining history 9
Prereclamatlon conditions 11
Early studies 13
Chronology of events 19
4. JurisdictIonal Framework 22
Cognizant authority 22
Water quality standards 22
5. Prereclamatlon Work 25
Grant application 25
Feasibility study 28
Site easements 30
Plans and specifications 31
Bid advertising and award of contract 32
Acquisition of wastewater sludge 32
Monitoring program 33
vi
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CONTENTS (continued)
6. ReclamatIon Work - 1976 34
Construction 34
Application of sludge and other soil amendments 40
Seeding 47
Costs 47
Results 49
7. Maintenance 52
SprIng 1977 52
Fall 1977 56
Spring 1978 60
Fall 1978 63
Spring 1979 66
Fall 1979 71
Spring - fall - 1980 75
8. Arininlus Site Reclamation 76
9. Postreclamatlon CondItions 80
Vegetative cover 80
Erosion control 88
Soil analyses 90
WQter quality 103
Stream stations - concentration and load data 105
Annual complete analyses 135
Tributary stations 139
pH ano specific conductance transects - 1979 149
Lake stations 149
Suninary of water quality data 170
Biologic studies 179
Suninary of biologic studies 185
10. SpecIal Studies 190
Water quality study by University of Virginia 190
Biologic study of Contrary Crer k Arm of Lake Anna 192
Revegetation studies at Arninlus Site 192
Metals uptake by vegetation - November 1978 192
11. Sumary of Project Costs 196
References 199
Glossary 201
vii
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CONTENTS (continued)
Appendices
A. Generalized deed of easement 204
B. Analytical procedures 206
C. Metric conversion 208
D. Major sources of Acid and Heavy Metals which contribute 209
to the Acid Mine Waters
E. Biological Survey of The Contrary Creek Arm of Lake Anna, 276
Virginia
F. Experimental Studies at Arminius Tailings 311
viii
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FIGURES
Page
1 Location of project 5
2 Vork River Basin drainage 8
3 Geologic map of Contrary Creek area 9
4 Generalized cross — section of mining operations at
Silphur Site
5 TIpple ruins at Sulphur Site 12
6 PortIon of Sulphur Site prior to reclamation 12
7 Devastated stream banks of Contrary Creek at 14
Sulphur Site
8 ErosIonal gully at Sulphur Site 14
9 Topography of Sulphur Site before reclamation 15
10 Old mine shaft entrance at Sulphur Site 16
11 Huge tailing pile at Sulphur Site 16
12 Topography of Boyd Smith Site before reclamation 18
13 VarIous work areas of Sulphur Site 35
14 Clearing and regrading of Boyd Smith Site - 36
April 1976
15 Regrading of Large Area at Sulphur East - Spring 1976 36
16 Regradlng of tailing pile at Sulphur West - Spring 1976 37
17 Regraded tailings at Sulphur West - Sumer 1976 37
18 Construction work - Sulphur Site 38
19 Construction and seeding work - Boyd Smith Site - 39
Sunmier 1976
l x
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FIGURF3 (condnued)
Page
20 Excavation of mine wastes from stream channel along 41
Tailing Area at Sulphur West
21 Rlprap section at mouth of Tr-2 at Sulphur East 41
22 TypIcal riprap section used In diversions 42
23 TypIcal riprap section used along stream banks 42
24 DumpIng of sludge at Sulphur Site 44
25 Spreading sludge at Sulphur Site 44
26 SeedIng work — Sulphur Site - Sunrer 1976 48
27 SeedIng work — !‘ilphur Site - Spring 1977 53
28 Seeding work - Sulphur Site - Fall 1977 57
29 F-eparation of seedb d with small disc 58
30 Seeding with a grain drill 58
31 Seeding work - Boyd Smith Site - Fall 1977 59
32 SeedIng work - Sulphur Site - Spring 1978 62
33 LIme spreading by truck on Sulphur East 64
34 Sludge spread by earthmovlng pan on Tr-1 of Sulphur 64
West
35 Seeding work - Sulphur Site — Fall 1978 65
36 Seeding work - Sulphur Site - Spring 1979 68
37 Spreading lime by hand at Boyd Smith Site 70
38 IrrigatIon of Sulphur Site 70
39 Seeding work - Sulphur Site - Fall 1979 72
40 Seeding work - Boyd Smith Site - Fall 1979 73
41 Barren ar as at Arminius East prior to reclamation 77
42 MIne tailings along Contrary Creek at Anninlus West 77
prior to reclamation
x
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FIGURES (continued)
No.
43 Arminius Site after reclamation - Fall 978 78
44 Sulphur Site before reclamation 81
45 Sulphur Site in 1980 82
46 Boyd Smith Site before reclamation 83
47 Boyd Smith Site in 1980 83
48 Boyd Smith Site - Spring 1977 85
49 Same view a Figure 48 - Suniner 1980 85
50 t.arge Area of Sulphur East - Spring 1977 86
51 Same view as Figure 50 - Sumer 1980 86
52 View of Tailing Area of Sulphur West with Tipple Area 87
of Sulphur East in foreground - Spring 1977
53 Same view as Figure 52 - Sumer 1980 87
54 Vigorous growth of Ky-31 fescue on Large Area of 89
Sulphur East - Sunrer 1979
55 Weeping lovegrass on Upstream Flat of Sulphur East- 89
Fall 1979
56 Contrary Creek Monitoring Stations 104
57 pH versus time ‘In calcndar years at MS-2 compared with 118
control station
58 pH versus tIme in calendar years at MS-3 compared with 118
control station
59 pH versus time in cakndar years at MS-4 compared with 119
control station
60 pH versus time in calendar years at MS-5 compared with 119
control station
61 Sulfate concentrations versus time in calendar years 120
at 1 15-3 compared with control station
62 Sulfate concentrations versus time in calendar years 120
at MS-4 compared with control station
xi
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FIGURES (continued)
Page
63 Copper concentrations versus time In calendar years 121
at MS-4 compared with control station
64 Copper concentrations versus time in calendar years 121
at MS—S compared with control station
65 Iron concentrations versus time In calendar years 122
at MS—2 compared with control station
66 Iron concentrations versus time in calendar years 122
at MS-4 compared with control station
67 Manganese concentrations versus time in calendar years 123
at MS—3 compared with control station
68 Manganese concentrations versus time in calendar years 123
at MS-4 compared with control station
69 Zinc concentrations versus time in calendar years 124
at MS-2 compared with control station
70 Zinc concentrations versus time in calendar years 124
at MS-3 compared with control station
71 Zinc concentrations versus time in calendar years at 125
145—4 compared with control station
72 Zinc concentrations versus time in calendar years at 125
MS-5 compared with control station
73 Sulfate loads based on instantaneous flows versus 126
time In calendar years at MS-3 compared with control
station
74 Sulfate loads based on instantaneous flows versus 126
lme in calendar years at MS-5 compared with control
station
75 Copper loads based on instantaneous flows versus 127
time In calendar years at MS-4 compared with control
station
76 Copper loads based on instantaneous flows versus 127
time in calendar years at MS-S compared with control
station
xii
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FIGURES (continued)
No. Page
77 Iron loads based on instantaneous flows versus time 128
In calendar years at MS-4 compared with control
station
78 Iron loads based on instantaneous flows versus time 128
in calendar year5 at MS-5 compared with control
station
79 Manganese loads based on instantaneous flows versus 129
time in calendar years at MS-3 compared with control
station
80 Manganese loads based on instantaneous flows versus 129
time in calendar years at MS-4 compared with control
station
81 Zinc loads based on instantaneous flows versus time 130
in calendar years at MS-2 compared with control station
82 ZInc loads based on Instantaneous flows versus time 130
in calendar years at MS-3 compared with control station
83 Zinc loads based on instantaneous flows versus time 131
in calendar years at MS-4 compared with control station
84 Zinc loads based on instantaneous flows versus time In 131
calendar years at MS-5 compared with control station
85 Copper loads computed from instantaneous flows under 133
base flow conditions versus time in calendar years at
MS—4 compared with control station
86 ZInc loads computed from Instantaneous flows under 133
base flow conditions versus time in calendar years at
MS—4 compared with control station
87 Iron loads computed from instantaneous flows under 134
base flow conditions versus time in calendar years
at MS-4 compared with control station
88 Manganese loads computed from Instantaneous flows 134
under base flow conditions versus time In calendar
years at MS-4 compared with control station
89 Arminius Tributaries 142
90 Boyd Smith Tributaries 143
xlii
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FIGURES (continued)
Page
91 Sulphur Site Tributaries 144
92 pH and specific conductance transect from Lake Anna 154
to above Arminlus Site, July 30, 1979
93 SpecIfic conductance transect along Contrary Creek at 156
Boyd Smith Site, July 19, 1979
94 pH and specific conductance transect along Tr-8 at 159
Boyd Smith Site, June 19, 1979
95 pH versus time in calendar years at surface level 162
of SS-1
96 pH versus time in calendar years at bottom level 162
of SS-1
97 Copper concentrations versus time in calendar years 163
at surface level of SS-1
98 Copper concentrations versus time In calendar years 163
at bottom level of SS-1
99 Zinc concentrations versus time in calendar years at 164
surface level of SS-1
100 Zinc concentrations versus time in calendar years at 164
bottom level of SS-1
101 Iron concentrations versus time In calendar years at 165
surface level of SS-1
102 Iron concentrations versus time in calendar years at 165
bottom level of SS-1
103 Iron concentrations versus time in calendar years at 168
surface level of SS-2
104 Iron concentrations versus time in calendar years at 168
bottom level of SS-2
105 Comparison of average copper concentrations by water 173
year at affected stream stations
106 Comparison of average zinc c centratIons by water year 174
at affected stream stations
xiv
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FIGURES (continued)
No. Page
107 ompar1son of average copper loads by water year 175
at affected stream stations
108 ComparIson of average zinc loads by water year 176
at affected stream stations
109 Sources of acid mine drainage Into Coitrary Creek 177
110 Contrary Creek biological stations 180
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TABLES
Page
I Average Monthly Precipitation at Louisa Weather Statthn- 7
1941-1979
2 Monthly Precipitation at Louisa Weather Station - 1975 - 80 7
3 Monthly Precipitation at Contrary Creek Rain Gage - 1975-80 7
4 Chronology of Events 19
5 Budget by Cost Category Requested In Grant Application 27
6 Average Water Quality Analyses of Contrary Creek Prior to 29
Reclamation
7 LIme and Fertilizer Application Rates - 1976 43
8 Sludge Application Rates - 1976 45
9 Average Concentrations of Constituents in Sludge Used at 46
Contrary Creek In 1976 on Dry Weight Basis
10 Average Fertilizer Equivalents of Sludge Used at 46
Contrary Creek In 1976 on Dry Weight Basis
11 Seed Species and Application Rates - 1976 47
12 Sunmiary of Construction and Seeding Costs — 1976 50
13 Suninary of Stone Costs - 1976 50
14 Fertilizer Application Rates - Spring 1977 54
15 Seeding - Spring 19fl 54
16 Maintenance Costs - Spring 1977 55
17 Maintenance Costs - Fall 1977 60
18 Seeding - Spring 1978 61
19 Maintenance Costs - Spring 1978 61
xvi
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TABLES (continued)
No. Page
20 Ma1nt rance Costs - Fall 1978 66
21 SeedIng - Spring 1979 67
22 Maintenance Ccsts - Spring 1979 69
23 LIme and Fertilizer !‘ lcatlon - Fall 1979 71
24 SeedIng - Fafl 1979 74
25 MaIntenance Costs - Fall 1979 74
26 MaIntenance Costs - 1980 75
27 Evaluatlnn of Vegetative Cover In Late 1980 84
28 Soil Loss Equation Factors for Before and After Reclamation 91
29 SoIl Data — SCS - pH-Nutrient Availability - 1975-76 92
30 Sumary of Sludge ApplIcation 92
31 Suninary of Lime Applicdtion Rates - 1976-80 93
32 Sunlfiary of Fertilizer Types and Application Rates - 94
1976-80
33 SoIl Data - DCLS, pH — Lime Requirement by Titration Curve 96
34 SoIl Data - DCLS, pH and Metals on Dry Weight Basis 97
35 Soil Data — WVLJ, pH, LIme Requirement, Nutrient Availability, 99
Total Potential Acidity - March 1978
36 Soil Data — SCS, pH and Nutrient Availability in lbs/ac- 100
March 1979
37 SoIl Data - SCS, pH, NutrIent Availability — July 1979 101
38 Soil Data - SCS, pH, NutrIent Availability - October 1979 102
39 Soil Data — SCS, pH, NutrIent Availability in lbs/ac — 1980 103
40 Mean Annual Flows 106
41 Sunrary of Water Quality Data by Quarter at MS-i 107
42 Sumary of Water Quality Data by Quarter at MS-2 109
xvii
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TABLES (continued)
No. Pate
43 Suninary of Water Quality Data by Quarter at MS-3 LU
44 Suninary of Water Quality Data by Quarter at MS-4 113
45 Average Concentrations by Quarter at MS-5 115
46 Load Values for High Flow Days 132
47 Water Quality Data — Additional Metals Included in 136
Complete Analyses
48 Water Quality Data - Solids, Specific Conductance, Turbidity 137
49 Water Quality Data - Miscellaneous Parameters 138
50 Water Quality Data - Nutrients and Oxygen 140
Demand Parameters
51 Monthly Composite Sludge Analyses on Dry Weight Basis- 141
Blue Plains STP
52 Water Quality Data - Arminius Tributaries 145
53 Water Quality Data - Boyd Smith Tributaries 146
54 Water Quality Data - Sulphur East Tributaries 147
55 Water Quality Data - Sulphur West Tributaries 147
56 Water Quality Data — Miscellaneous Parameters- 148
Contrary Creek Tributaries
57 pH and Specific Conductance Data for 6.6 Km Transect 150
Along Contrary Creek, July 30, 1979
58 pH and Specific Conductance Data of Contrary Creek 153
Tributaries, July 30, 1979
59 Specific Conductance Data for Transect Along Contrary 155
Creek at Boyd Smith Site, July 19, 1979
60 pH and Specific Conductance Data for Transect Along Main 157
Tributary (Tr-8) at Boyd Smith SIte, June 19, 1979
61 SS—1 - Averages, Minimums, and Maximums of Water 161
Quality Data, 1975-79
xviii
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TABLES (continued)
No. Page
62 SS-2 - Averages. Minimums, and Maximums of Water 167
Quality Data, 1975-79
63 ComparIson of Averages of All Depths at SS-1 and SS-2, 1975-79 169
64 ComparIson of Solids and Sp c1f1c C3nductance at SS-1 and SS-2 169
65 Average Annual Concentrations by Water Year at Stream Stations 171
66 Average Annual Loads by Water Year at MS-i, MS-2, MS-3 and 172
MS-4
67 Comparison of Loads at MS-4 and MS-5 on Basis of Instantaneous 178
Flows August 18, 1977
68 Cursory Biologic Survey - October 1976 182
69 Cursory and Quantitative Biologic Survey - Ma y 1979 186
70 QuantitatIve Biologic Study - April 1980 188
71 Species Mix and Per Cent Cover - Metals Uptake Study - 193
November 1978
72 Metals Uptake of Vegetation 194
73 Sumary of Federal Funds Expended thru FY 1980 197
74 Sumary of SWCB Funds Expe 1 ded iY 1976—1980 198
xix
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ACKNOWLEDGEMENTS
The Virginia State Water Control Board (SWCB) expresses Its sincere
gratitude to the Soil Conservation Service (SCS) of the United States Depart-
rnent of Agriculture for preparing construction plans and specifications and
for continued technical assistance throughout the project. Special thanks
are extended to Henry Aylor of the Culpeper District Office who served as
inspector during the main phase of reclamation and to Lowry Abell and Jack
Warren o the Louisa County Field Office who have kindly continued to assist
with the maintenance work.
Ronald D Hill, Environmental Protection Agency (EPA) Project Officer,
has provided guidance throughout ftie duration of the project.
The Government of the District of Columbia was most cooperative in
arranging the free delivery of wastewater sludge to the project site for use
in reclamation.
Thomas V. Dagenhart, graduate student at University of Virginia (UVA),
was most helpful with interpretation of water quality data. Chandler Mortimer,
Consultant for Callahan Mining Corporation, willingly exchanged information
and views on his work at the Arminius Site.
The Virginia Division of Consolidated Laboratory Services (DCLS) per-
formed all analytical work on water and sludge and a major portion of the soil
analyses. The Virginia Department of Highways and Transportation (VDH&T)
provided aerial photo coverage of the project site.
The following Divisions of the SWCB contributed to the project: Valley
Regional Office (VRO), overall management and coordination; Piedmont Regional
Office (PRO), collection of water samples; Surface Water Investigations (SWI),
installation and maintenance of flow gaging stations; Division uf Ecological
Studies (DES), biologic studies; Bureau of Administration and F 4 nance (BAF),
administration of grant funds, irocessing watcr quality data, and drafting
work; Bureau of Enforcement (BE), execution of easements and Input for
Section 4 of this report.
xx
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SECTION 1
INTRODUCTION
This report describes a mine reclamation project performed with an EPA
demonstration grant In Louisa County, Virginia. The objective of the project
was to demonstrate methods by which acid mine drainage (AMD) including heavy
met&ls could be abated from two abandoned pyrite mines which had been dis-
charging for over 50 years into a stream known as Contrary Creek. This stream
empties into Lake Anna, a reservoir completed for nuclear power plant in 1972.
The project has teen a cooperative effort between the Virginia State
Water Control Board (SWCB), the Environmental Protection Agency (EPA), and the
Soil Conservation Service (SCS). Overall management of the project has been
by the Valley Regional Office (VRO) of the SWCB in Bridgewater, Virginia.
Construction and seeding costs have been funded from an EPA demonstration grant
with the SWCB providing matching funds through in-kind services consisting
of project administration, monitoring, evaluation and report writing. The
SCS has provided engineering services and technical assistance throughot the
reclamation and inaintenar ce phase of the project. A third Inactive pyrite
mine site along Contrary Creek Is being reclaimed by a mining company.
A physical description of the project site, mining history, prereclatna-
tion conditions, and early studies are given in Section 3.
Section 4 presents the legal authority for undertaking the project with
applicable SWCB regulations and water quality standards. Prereclamation work
Including grant application 1 feasibility study, site easements, plans and
specifications, bid advertising, and award of contract are sumarized In
Section 5.
Section 6 descrIbes the major reclamation phase in 1976, and SectIon 7
discusses the semi-annual maintenance that has been performed since the
Initial reclamation work. Both sections Include detailed co t Information.
Section 8 gIves a brief sumary of the reclamation of the Armlnius Site by
Callahan Mining Corporation.
PostreclamatiOn conditions in terms of vegetative cover, erosion control,
soil analyses, water quality, and stream biota are covered In SectIon 9. The
water quality discussion Includes results of regular monitoring and supple-
mental studies.
Section 10 describes four special studies associated with the project,
three of which appear In their entirety in the appendices. Section 11
suninarizes all Federal and State costs through the end of FY 1980.
1
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SECTION 2
CONCLUSIONS AND RECOt’ lENDATI Ns
Conclusions:
(1) Fair to good vegetative cover has started to establish over about
90 per cent of the reclaimed mine sites, but severe drought during
the first two years of work seriously hampered restoration efforts
necessitating a continuing maintenance program. Some highly toxic
areas along stream banks remain barren and other areas have a very
thin soil cover supporting vegetation that Is very vulnerable to
drought.
(2) The use of digested wastewater sludge along with lime and fertilizer
has been essential in promo .ing vegetation, and It Is doubtful that
a fraction of the success rtilized would have been possible without
the sludge. No health hazarø or Ill effects to the environment
are known to have resulted fron the use of sludge In the project.
Heavy application of lime has apparently resulted in a general in-
crease in soil pH and there seems to be a close relationship between
potash deficiency and the more difficult areas to vegetate.
(3) The most successful grass has been K.y-31 fescue with weeping love—
grass proving to be highly tolerant of hot dry weather. Legumes
have not shown any appreciable success.
(4) ErosIon has been reduced considerably with concomitant decrease
in surface runoff of AMD.
(5) Analytical data from a comprehensive monitoring program show little
Improvement in water quality of Contrary Creek in terms of concen-
trations and loaas since reclamation began, but continued develop-
ment of plant cover should continue to reduce infiltration and
eventually begin to abate leaching of acid and heavy metals. There
Is no way of predicting when significant improvement will occur.
(6) The principal causes of AMD are sudden flush-outs of oxidation
products locatea In the stream bed and barren mine wastes by heavy
rainstorms following extended dry periods, and continual seepaq
of mine waste leachate along the stream banks between storms.
(7) The Sulphur Site is the major contributor of AND along Contrary
Creek. but certain heavy metals appear peculiar to each mine site.
Water quality steadily deteriorates downstream as Contrary Creek
2
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passes each site, and the downstream reach between the Sulphur Site
and Lake Anna where no reclamation has been done contributes
significantly to the AND.
(8) BIologic studies have shown meager Improvement in aquatic life of
Contrary Creek since reclamation began. Those stream reaches
lnrtediately below the mine sites remain highly toxic to all but
the most tolerant organisms.
(9) The Contrary Creek arm of Lake Anna imediately below the mouth of
the stream is definitely degraded by AND, but the effect on the main
body of the lake appears negligible.
(10) Average cost to date for reclamation including all maintenance
has been $14,518 per h ctare.
Reconinendations:
(1) A project of this type will likely require several years of
maintenance to assure permanent survival of vegetation. Regular
inspections are necessary to determine maintenance needs including
reseeding of problem areas and placement of erosion control measures.
Soil tests should be conducted at least once annually to evaluate
progress and to determine what soil additives might be needed. Fall
seeding is generally more sucessful than spring seeding because of
the risk of drought during the sumer months.
(2) Whenever feasible wastewater sludge should be used In the reclamation
of lands severely affected by mine wastes. The positive effects that
sledge has in promoting vegetative growth on highly toxic areas have
been well demonstrated in this project. Large urban areas that
generate huge volumes of 1udge and have problems ot taining disposal
sites are the best source. to use. If work schedules permit and
the terrain Is favorable it Is desirable to have sludge Camped
directly upon application areas rather than stockpiled nearby be-
cause of the extra handling involved.
(3) The ongoing water quality monitoring program in conjunction with
this project should continue with strean. stations sampled monthly
for at least one year and then on a quart ’rly basis for a few more
years. One monitoring station for measuring flows and collection
of samples downstrearr from all mine sites should be maintained per-
manently. Biologic tudles should continue at least biennially.
It should be realized that the abatement of AND of such a toxic
nature as encountered In this project is by no means a short term
process.
3
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S .crIoN 3
SACKGROUND
LOCATION
The Contrary Creek Project is located In Louisa County, Virginia
approximately 65 kilometers northwest of Richmond and 120 kilometers south-
west of Washington, D. C. (Figure 1). The three reclaimed mine sites discussed
in this report are located along Contrary Creek, a sr all stream whlc ’i heads
just north of the Town of Mineral and flows northeasthard into Lake Anna, an
impoundment constructed for a nuclear power plant. The mine sites are known
as the Sulphur, Boyd Smith and Arminius.
Louisa County Is predominantly rural with a population of about 17.000.
The County has an area of 1,346 square kilometers, about 73 per cent of which
is covered with secondary growth timber with pine and oak the dominant
varieties. Lumberinq Is the primary Industry as evidenced by the numerous
sawmills and planing mills throughout the county. Of secondary importance Is
clothing manufacturing and diversified agriculture which includes production
of small grains, corn, hay, livestock, and poultry.
The recent construction of Lake Anna which lies entirely within Louisa
County and Spotsylvania County to the northeast has made the area a major
recreational attraction. This reservoir with an area of 5,261 hectares and
322 kilometers of shoreline draws boaters and fishermen from throughout
Virg 4 nia and surrounding states including the Washington, D.C. metropolitan
area. The excellent sport fishing on Lake Anna Is recognized nationally.
CLIMATE
Most of the following information was obtained from “Climatolog- cal Data”
compiled by NOAA and reported by the Louisa Weather Station located approxima-
tely 4 kIlometers west of the project area. As part of the monitoring program
the SWCB installed a rain gage at the Droject site but a continuous record is
not available due to malfunction and vandalism.
Humid sw m rs and mild winters are characteristic of the area. The
average growing season Is 173 days from April 24 to October 14. Mean annual
temperature Is 13°C and sumertime highs range from 28°C to 32°C, but higher
temperatures are not at all uncomon. Nighttime lows In the sunnier are usually
between 15°C and 20°C. DurIng the winter months daytime highs average 8°C with
nighttime lows around -3°C. Freezing temperatures usually occur between 60 and
70 days a year and temperature usually falls below OOF at least once each
winter.
4
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‘ 0 N 1 Y
• S P • * I.
A
r
&N a
0 S
COUNTY
I
N
N
I .
(I
4
WALl
Mliii
PROJECT
0
0
D.C.
C
4
LOUISA
FIGURE 1. LOCATION OF PROJECT
C
I
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Annual precipitation averages 1( ’) centimeters and is usually fairly well
distributed throughout the year. Total snowfall averages about 50 centimeters
per year. Most of the precipitation falling on the project area results from
storm systems moving northeastward from the southern Appalachians or eastward
from the Ohio Valley. During the surner months thunderstorms nd occasional
hurricanes or other tropical disturbances account for a major portion of the
rainfall. In 1969 Hurricane Camille dumped a record 28 centimeters of ran
on the area within a 24-hour period. For the period of record from 1941 to
1979, July and August have been the months with the highest rainfall with
February and April the driest months (Table 1). The driest year on record
during this period was 1977 when only 78.2 centImeters of precipitation fell.
Table 2 gives monthly precipitation records from the Louisa Station since the
reclamation project started. Partial precipitation data from the rain gage
installed in the project area are shown In Table 3.
TOPOGRAPHY AND DRAINAGE
The Contrary Creek Project is located in the Piedmont physiographic
province which is characterized by a uniformly rolling surface with mild
relief sloping gently southeastward from the Blue Ridge to the Coastal Plain.
Elevation ranges from 90 to 120 meters above sea level in the project area.
All of the major streams draining the Piedmont and Coastal Plain provinces
flow in a southeastward direction. in the imediate project area the tribu-
taries of the major streams flow northe stward in a well developed trellis
pattern controlled by the geologic structure.
Contrary Creek lies within the York River Basin (Figure 2) and drains
approximately 18 square kilometers In the north central part of Louisa County.
Before the construction of Lake Anna, Contrary Creek flowed into Freshwater
Creek which in turn emptied into the North Anna River which drains a major
portion of the York River Basin. The length of Contrary Creek is now
spproximately 8 kilometers and average flow at the mouth of the stream Is 207
liters per second (7.3 cfs).
GEOLOGY
The Piedmont province is mostly underlain by a complex of igneous and
metamorphic rocks of Precambrian age consisting chiefly of granites, schists,
and gneisses occurring in northeastward trending belts generally paralleling
the Appalachian Mountain Range. In most places a thick layer of residual
soil covers the deeply weathered bedrock which contains a wide variety of
minerals. The pyrite mines along Contrary Creek were developed in a four-mile
wide belt of crystalline schists striking N4OE and dipping 65°SE (Figure 3).
The extensively metamorphosed schists Intruded by pegmatitles, quartz veins,
and diabase dikes have probably been altered from sedimentary rocks. This
belt of highly mineralized rocks occurring between two masses of granitic
rocks is part of the so—called pyrite-gold belt of Virginia. In addition
to pyrite a vast assemblage of minerals Including garnet, hornblende, blotite,
and magnetite occur in this region attracting many rockhounds.
6
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TABLE 1. AVERAGE MONTHLY PRECIPITATION AT LOUISA
WEATHER STATION 1941 - 1979 (crn)a
June i Q !
7.8 7.3 9.7 7.5 9.2 9.6 117 11.6 84 88 80
9.2
i !
1088
TABLE 2. MONTHLY PRECIPITATION AT LOUISA WEATHER
STATION 1975 - 1980 (cm)a
June i
I L
1975 8.4 5.9 16.4 4.6 8.5 26.7 202 7.8 24.0 4.8 5.1
9.9
142.3
1976 9.3 3.9 7.2 4 1 8.2 11 6 6. 10.9 10 7 22.3 3.7
4.8
103.4
1977 4.3 1.0 6.2 4.6 3 6 3.7 5. 5.3 5 2 11 5 14.7
12.6
1978 21.7 0.7 10.3 9.3 12.1 14.6 13.7 21.0 6 0 2.9
199 14 1 13.0 9.6 8.5 8.7 10.0 2.3 127 19 7 13.9 8.2
2.1
122.b
1980 11.5 2.7 9.7 5.3 7.9 1.4 8.4 11.0 2.2
TABLE 3. MONTHLY PRECIPITATION AT CONTRARY CREEK
RAIN GAGE - 1976 - 1980 (cm)a
June Ji !E! 9 ! ! !
!1
1976 b 9.4 9.3 127 8.3 20.4 3.3
5.1
1977 3.8 1.0 4.8 3.4 3.2 3.0 6.2 5.] 9.8 12.7
16 6
1978 8.9 10.2 8.0 6.5 11 3
1979 72 9.6 1.9 11 8 20 9 7.5 6.0
1.3
1980 11.7 1 9 10.9 4.7 8.6 0.3 7.7 17 3 2.2
aTO convert centimeters to inches multiply by 0.394
records are available wt ere no measurement appears.
7
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LAKE ANNA
CONTRARY
CREEK
WVA MD
TENN. N.C.
R.produc.d I ro*
b.s. .v.fl.bl, copy.
I
u a
FIGURE 2. YORK RIVER BASIN DRAINAGE
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LITHOLOGY
VOLCANIC ROCKS
META )RPHOSED
C$MENTARY ROCKS
METAMORPH1 ED VOLCANIC
A SED$ NTARY ROCkS
V..
—i
____ KIL IT $
FIG. 3 GEOLOGIC MAP OF CONTRARY CREEK AREA (MOD WIED FNOM GEOLCX
MAP OF VIRGINIA, 1913. VIRGINIA DIVISION OF MiNERAL NE$OL ES)
Massive lenses of pyrite ore conforming to the regional strike occur
within the enclosing schistose rocks. The ore bodies are usually 10 to 15
meters thick and up to 200 meters In length. Where discontinuous, the
pyritic lenses are often connected by stringers of ore. The ore deposits
are the typical gossan type with the pyrite weathered to iron oxides forming
the caprock at the surface, underlain by a zone of secondary enrichment which
Is in turn underlain by the unweathered pyrite ore (Figure 4). Generally
the contact between the ore bodies and the schistose rocks is sharp but some
grading Into the country rock occurs.
MINING HISTORY
The earliest mining along Contrary Creek began In 1834 when gossan iron
ore pits were excavated at the Arminius Site. Gossan was mined from open
pits at all three mine sites until about 1877 and was used to supply furnaces
at the Arminius and Sulphur Sites. These old pits as much as 20 meters deep
and extending along the strike of the ore bodies can still be seen, but they
are not believed to be a significant factor in the pollution probl n along
Contrary Creek. Copper was mined on a small scale from the enriched mineral-
ized zone beneath the gossan deposits concurrently with the Iron mining.
Around 1880 the rich pyrite deposits beneath the gossan pits along Contra-
ry Creek began to attract attention when It was determined that It was more
profitable to manufacture sulfuric acid from pyrite rather than from brimstone.
The fact that the pyrite deposits were so near the surface also favored devel-
opment. Deep shaft mining for pyrite began at all three mine sites during the
GRANITE
ANITE ONEISS
p
MSu .E$
9
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I
ill
NW
I
a
SE
BIdTOd
BOdISS
D..p
Enclosing Sdli!.t,. 1 ...
Fornistlon
FIGURE 4. GENERALIZED CROSS SECTION OF MINING OPERATIONS AT SULPHUR SITE
(NOT TO SCALE)
-------
1880’s and continued untIl 1923. PortIons of the old tipple structures are
still standing at both the Boyd Smith and Sulphur Sites (Figure 5). A total of
8 shafts ‘e believed to have been developed at the u1phur Site, and 3
were constructed at the Boyd Smith Site. The deepest shaft at the Sulphur
Site was 220 meters but none of the shafts at the Boyd Smith Site were deeper
than-90 meters. Some shafts at the Anninlus Site reportedly exceeded 300
meters In depth. All of t e shafts were on the east side of Contrary Creek.
The shafts were Inclined in the general direction of dip of the bedrock,
that Is, southeastward toward present Route 522 (rigure 4). After the shafts
were sunk, levels were run out at various elevations in both directions along
the strike paralleling Contrary Creek. The lateral extent of the levels is
unknown but surface evidence Indicates that operations extended well beyond
the ininedlate vicinity of the shafts. Ore was broken by overha id stoping,
conveyed by mule-drawn carts to shafts, and brought to the surface by skips
where it was washed and crushed to various sizes for marketing by rail. The
coarse reject material consisting mainly of schists was dumped near the shaft
entrances on the east side of the Creek at all three mine sites. At the
Sulphur Site the fine tailings were conveyed aci-c ss the Creek leaving huge
spoil piles on the west side (Figure 6). It was this Indiscriminate dumping
of mine waste that resulted in the serious pollution problem along Contrary
Creek.
The real heyday of the mining era was between 1910 and 1920 when about
2,000 men were employed at the three mine sites. At this time Virginia was
the leading pyrite producer in the U.S. Over 6 million tons of pyrite ore were
reportedly produced at all three mine sites during their operating period.
Pyrite mining in Louisa County terminated rather abruptly when the less
expensive method of producing sulfur by the Frasch process was developed In
the Gulf Coastal Plain. The mines ølong Contrary Creek could no longer operate
on a competitive basis and by 1923 al 1 . three mines had closed and have not
operated since.
Over the past 30 years tests have been conducted for various minerals at
the Arminlus and Boyd Smith Sites but results have not warranted any new
production of ore. During the mld—1970’s Callahan Mining Corporation formed a
partnership with New Jersey Zinc Company, owners of the Arminius Site, and did
some exploratory work near tne project area on the east side of Route 522.
The mining company considered using the Arminius Site for milling operations
in the event a decision was made to go into production. The plan has not
materialized to date.
PRERECLAMATION CONDITIC 1S
Over 50 years after the mines along Contrary Creek had been closed, approx-
imately 12 hectares of land remained barren of vegetation as a result of the
toxic character of the spoil at the three mine sites (Figure 7). A few scat-
tered patches of Virginia pine had been able to establish over some of the less
toxic areas but most of the waste areas supported no vegetation at all. Some
places resembled pictures of the lunar surface. Erosion had cut deep gullies
11
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Figure 5. TIpple ruins at Sulphur Site.
Figure 6. PortIon of Sulphur Site prior
to reclamation.
12
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through and around the tailing piles (Figure 8) and vast quan:ities of
pyritic material had been washed into the main stream channel and its tribu-
taries. Much of this material was carried downstream below the mine sites
towa.d .lat Is now Lake Anna.
me Sulphur Site was by far the worst of the three mine sites. Approx-
Imately 6 hectares of the Sulphur were covered with mine wastes drastically
altering the natural contours. Figure 9 depicts topography of the Sulphur
Site prior to reclamation. Four of the old shaft entrances (Figure 10) were
still evident and a deep pool of highly acidic water filled a depression
reportedly caused by a cave-in. Huge tailing piles retained by cribbing on
the west bank of Contrary Creek rose about 9 meters above the stream bed
(Figure 11). On the east side of the Sulphur most of the wastes consisted
of the coarse reject material which fanned out from the old shaft entrances.
All of this reject material was highly mineralized and consisted of boulders
up to 60 centimeters in diameter.
Conditions at the Boyd Smith Site were considerably less severe. About
2 hectares were covered with 1 to 2 meters of tailings spreading out from the
shaft entrances toward Contrary Creek, but the natural topography was not
significantly disturbed. There was no profuse amount of pyritic material
ininediately adjacent to nor in Contrary Creek, but a tributary traversing the
waste area was badly clogged with tailings. A small amount oc AND still seeps
directly from an old shaft here, but it apparently contributes insignificantly
to the overall AND problem.
The AND problem along Contrary Creek and its detrimental effect upon
aquatid life in the North Anna River had been recognized for some time. Two
fish kills investigated in 1970 by the Virginia State Water Control Board in
the North Anna River were attributed to the A7 1D problem, and even to the
casual observer it was apparent that Contrary Creek had been rendered virtually
sterile by the continuous leaching of AND into the stream.
Most of the AMD entering Contrary Creek apparently resulted from leachitig
of sulfuric acid and metallic salts from under the massive tailing piles and
from surface runoff during and imedlately after periods of heavy rainfall.
As stated above some seepage emanates directly from the old shafts during wet
periods, and there was and still is continual slow seepage from under the
stream ba”ks In the more severe areas.
EARLY SIUDIES
During the mid-1950’s landowners affected by the mine iaste areas along
Contrary Creek sought help In alleviating the problem from the SCS through the
Thomas Jefferson Soil and Water Conservation District. Between 1957 and 1968
the SCS conducted a series of soil analyses from the mine sites which re-
vealed persistent low pH’s and deficient levels of ralcium, plant nutrients
and organic matter. Using lime, fertilizer and mulch, the SCS tested various
types of grasses at the Boyd Smith and Sulphur Sites in the early 1960s. Of
the grasses tested only the Ky-31 fescue showed any degree of succçss. Con-
13
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Figure 7. Devastated stream banks of
at Sulphur Site.
Figure 8.
Contrary Creek
Erosional gully at Sulphur Site.
14
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SULPHUR SITE
- o. ce’ c I
FIGURE 9. TOPOGRAPHY BEFORE RECLAMATION
, ‘ -
I
LL LtiD
• ••
— s’
I
—
-------
FIgure 10. Old mine shaft entrance at Sulphur Site.
Figure 11. Huge tailing pile at Sulphur Site.
,‘ .
$‘:
16
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current with the SCS work the Virginia Forest Service planted several
test plots of trees and shrubs at the Boyd Smith Site (Figure 12), but only
Virginia pine and black alder had good survival rates. Some of these trees
were still growing at the Boyd Smith Site in 1980.
When the Virginia Electric Power Company (VEPCO) decided to build a
nuclear power plant on the north Anna River) the problem along Contrary
Creek began to cause more concern. It was feared that with the construction
of an Impoundment there would be danger of a buildup of cntaminants with
the continual Influx of AND into the lake. A study co ,iducted by the Comic-
slon of Game and Inland Fisheries (CGIF) In August 1968 stated that aquatic
life was virtually non—existent in Contrary Creek and that fish populations
In the North Anna River were being affected. In October 1971 the Virginia
Soil and Water Conservation Convnlssion held a meeting with interested govern-
mental agencies and VEPCO to coordinate an evaluation of previous studies
and make future reconinendations on the Contrary Creek problem. Attending
this meeting were representatives from the SWCB, CGIF, Comisslon of Outdoor
Recreation, Division of Mineral Resources, Division of State Planning and
Comunity Affairs, SCS and the Biology Department of Virginia Polytechnic
Institute and State University (VPI&SU). It was decided at this time that the
best course of action would be to seek an EPA grant which should be used to
demonstrate the feasibility of correcting the AMD problem. More data wo’ld
be required before applying for a grant and it was agreed that each represen-
tatlvr agency would provide pertinent data. Since the SWCB is the State’s
primary water quality and resource agency, it was determined that that
agency would be responsible for seeking a solution to the oroblem.
The SWCB conducted the first chemical survey of Contrary Creek in Novem-
ber 19 1. Water samples were collected above and below suspected discharges at
all three mine sites along Contrary Creek and analyzed for pH and heavy metals.
The analyses revealed that there were indeed nimerous sources of heavy
metals and acid In high concentrations at all three mine ;ites. The metals
that were found to be present in excessive amounts were iron, copper, zinc,
manganese and lead. It was also very evident that the water quality deteri-
orated steadily downstream as the stream passed each mine site. Some of the
samples taken directly from spoilbank seepage revealed extremely high ton-
centrations of metals and acid.
A pre-inipoundment biologic study completed by Dr. George M. Simons, Jr.
of VPI&SU In 1972 showed a 65 per cent reduction in the number of fish species
and a 50 to 60 per centreduction in the standing fauna crop in the North
Anna River below the mouth of Contrary Creek. The study further showed that
the North Anna River didn’t fully recover biologically for at least 22 kilo-
meters downstream from the confluence of Contrary Creek. Another study by
Dr. Simons showed a dramatic decrease in aquatic life In Contrary Creek it-
self below the mine areas. Dr. Simons concluded from the observation of
fauna in the tributaries that the potential for blotic recovery was very good
provided the water quality could be restored in Contrary Creek. However, he
predicted that if the leaching of AND continued, the concentration of heavy
metals In Lake Anna could cause fish kills within 5 to 10 years and that a
sudden flush—out of heavy metals could result In fish kills even sooner.
17
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BOYU Mi I M .i I
LEG EjtQ
S S Q*O,
- , .sT tAMS
: - I IL.c sGs o uNoaTIOss
OLD MII IH FT$
FIGURE 12. TOPOGRAPHY BEFORE
18
RECLAMATION
/
Tist Plots
3a1
CREEK
g) tsTj G TOPOGRAPI1Y
90
1 ___ 1L ’ UIT
-------
IIU IIV I! UIIII1 IS .QI £III)MA ..l.
Energy Comisslon on the proposed North Anna power station stated that AND
from Contrary Creek could have serious effects upon the aquatic life In the
lnpoundment and that heavy metal concentrations in fish flesh could render
It unfit for human consumption. The Lake Anna Reservoir was completed in
January 1972 and primarily due to Hurricane Agnes in June, the reservoir
was filled by December 1972.
cHRO::0LOGY OF EVENTS
Major events for the project prior to, during and after reclamation are
Itemized chronologically in Table 4.
TABLE 4. CHRONOLOGY OF EVENTS
1957 - 1968: Soil Conservation Service and Virginia Division of
Forestry conducted soil analyses at mine sites and
planted test plots.
April 1968: VIrginia Electric Power Company announced plans to build
a nuclear power plant on Uorth Anna River.
Nay 1968: Various State and Federal agencies including SWCB began
making assessment of AND problem and making recomenda-
tions for a solution.
August 1968: Virginia Comission of Game avid Inland Fisheries con-
ducted study.
October 1971: VarIous agencies involved decided to explore possibility
of obtaining an EPA demonstratiin grant with the SWCB
assuming responsibility for the project.
November 1971: SWCB conducted first water quality study of Contrary
Creek.
1972: Pre-impoundnient biologic studies conducted by VPI&SU.
Lake Anna reservoir completed.
September 1973: SWCB formally decided to apply for EPA grant.
December 1973: Gannett Fleming Corddvy a d Carpenter retained to con-
duct feasibility study.
February 1974: Callahan Mining Cor ...ration contacted SWCB about their
interest in Arminius Site.
March 197 : Grant application submitted to EPA.
(continued)
19
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January 1975:
February 1975:
June 1975:
July 1975:
August 1975:
October 1975:
December 1975:
January 1976:
February 1976:
March 1976:
April 1974:
June 1974:
I4ovember 1974:
TABLE 4. (continued).
Grant application rejected.
EPA advised that grant application would be
reconsidered provided costs could be reduced.
SWCB requested technical assistance from SCS.
Scope of project reduced.
SCS agreed to provide engineering services.
C allahan Mining Corporation assumed responsibility
for reclamation of Aniiinius Site.
Final text of feasibility study completed.
Revised yrant application submitted to EPA.
EPA grant awarded.
Demonstration project officially began.
Deeds of easement with property owners completed.
SCS prepared plans and specifications for bid package.
Monitoring program began.
Bid advertisement.
Site showing to prospective bidders.
Bid opening.
Construction and seeding contracts awarded.
District of C3lumbia agreed to deliver wastewater
sludge for use in reclamation at no cost.
Major reclamation phase began.
All construction and see-9ng work at Boyd Smith and
Sulphur Sites completed.
Callahan Mining Corporation began reclamation of
Arminius Site.
Spring and fall maintenance.
(continued)
April 1976:
July 1976:
October 1976:
1977:
20
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TABLE 4. (continued)
1977: Special water quality study by University of Virginia
began.
1978: SprIng and fall maintenance.
Grant period extended for one year.
1979: Spring and fall maintenance.
Grant period again extended for one year.
Special water quality study completed.
1980: Spring and fall maintenance.
Grant period extended until 1982.
21
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SECTION 4
JURISDICTIONAL FRAMEWORK
Under the provisions of Section 107 of PL 92-500 the Virginia State
Water Control Board applied for and was awarded a demonstration grant by the
United States Environmental Protection Agency to be used in reclaiming two of
the abandoned mine sites along Contrary Creek. The Coniuonwealth of Virginia
had the responsibility of managing and administering the project including
securing of easements, contracting reclamation work, performing all monitor-
ing work, and preparing reports. Tue Soil Conservation Service has provided
engineering and technical assistance.
COGNIZANT AUTHORITY
The Vi%’ginla State Water Control Board has the authority under Chapter
3.1, State Water Control Law, of the C’,de of Virginia (1950, as amended) to
protect and safeguard the waters of the State, prevent any increase of pollu-
tion and reduce existing pollution in order to permit all reasonable public
uses and provide for the health, safety and welfare of the citizens of the
Comonwealth.
Section 62.1-44.15(4) of the Code authorizes the SWCB to conduct or have
conducted scientific experiments, investigations, studies and research to
discover methods for maintaining water quality consistent with the purposes
of the Chapter. ThIs demonstration project has been performed under the
authority of this Section of the Code.
WATER QUALITY STANDARDS
Cohtrary Creek falls within Section 3 of the York River Basin and is
designated by the State Water Control Board as a Class III stream. This
classification refers to free flowing streams (Coastal Zone and Piedmont
Zone).
The following specific standards apply to all Class III streams:
Dissolved Oxygen ( mg/i )
MInimum 4.0
Daily average 5.0
6.0-8.5
22
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Temperature OC
Maximum rise above natural* 3
MaxImum 32
Maximum hourly change** 2
Naturai temperature Is that temperature of a body of water due solely to
natural conditions without the influence of any point-source discharge.
Any rise above natural temperature allowcd by the SWCB shall be determined
on a case—by-case basis and should not exceed 3 0 C except in the case of
Class VI waters where it shall not exceed bC.
**
The maximum hourly temperature change of 2°C is to apply beyond the boundary
zones and does not apply to temperatures caused by natural conditions.
In addition, the following general standards are applicable to Contrary
Creek:
“In all surface waters, except those where leased private or public
shellfish beds are present, the fecal coliform bacteria shall not
exceed a log mean of 200 fecal coliform bacteria per 100 ml of water
with not more than 10 per cent of the tot il samples during any 30-day
period exceeding 400 per 100 ml.”
All state waters shall be maintained at such quality as will permit
all reasonable beneficial uses and will support the propagation and
growth of all aquatic life, including game fish, which might reasonably
be expected to inhabit them.”
“ All State waters shall be free from substances attributable to sewage,
Industrial waste, or other waste in concentrations, amounts, or combina-
tions which contravene established standards or interfere directly or
Indirectly with reasonable, beneficial uses of such water or which are
Inimical or harmful to human, animal, plant, or aquatic life
Although neither Contrary Creek nor Lake Anna constitute a public water
supply at this time, the water quality standards adopted by the SWCB for
application tc specific drinking water sources are used as a reference for
discussing the water quality monitoring in this report.
The following standards excerpted from “Water Quality Stan 1ards,” Virginia
State Water Control Board, Richmond, Virginia, 1980 apply at the water Intake
and for a distance upstream. This distance from the intake is to be determined
on a case-by-case basis by the SWL. considering upstream wastewater volume,
23
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receiving stream volume and other appropriate physical, chemical and biologi-
cal factors. The standards will apply to both the water supply stream and
Its tributaries within the designated distance. (In case of existing water
supplies, the standards will apply at the Intake point until further change
s made.)
CONSTITUENT CONCENTRATION tMG/L )
Arsenic 0.05
Cadmium* 0.01
Chloride 250
Chromium (Total) 0.05
Copper* 1.0
Iron (soluble) 0.3
Lead 0.05
Manganese (soluble) 0.05
Mercury* 0.002
Nitrate (as N) 10
Sulfate 250
Total dissolved solids 500
Z lnc* 5.0
The numeric standards for the chemicals listed above are designed to protect
public water supplies for human consumption. The limits established for
those chemicals marked with an asterisk (*) m y not protect aquatic life.
Therefore when a request to classify a stream as a public water supply Is
received, it will be determined if more stringent limits are needed for those
chemicals in order to Insure protection of aquatic life.
Of these standards, th’. general standard, which states that “All wastes
shall at all times be free from all substances attributable to sewage, indus-
trial waste, or other wastes In concentrations, amounts or combinations which
contravene established standards or interfere directly or indirectly with
beneficial use of such water---” was the most relevant to the project. In
particular the acidity, and the heavy metallic salts of iron, copper, zinc,
manganese, and lead were and are the most significant constituents degrading
water quality in Contrary Creek and posed threats to the aquatic environment
in Lake Anna downstream.
The objective of this project has been to effectively reduce the pollu-
tional load In the Contrary Creek watershed by eliminating or reducing these
sources of pollution to enable Contrary Creek to more closely approach its
classification as a Class III stream and meet all Water Quality Standards and
Criteria.
24
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SECTION 5
PRERECLAMATION WORK
GRANT APPLICATION
At the request of the SWCB an official from EPA visited the abandoned
mine areas in June 197 to make a preliminary appraisal of the AMD problem.
At this time it was determined that the pollution along Contrary Creek would
probably q ialify for a demonstration grant, but because of pending changes in
Federal guidelines the grant was not pursued further for over a year.
In the meantime the SWCB had determined who the property owners of the
various mine sites were and had made preliminary contacts with the owners
about the proposed reclamation work. The SWCB considered taking legal action
against the landowners to alleviate the problem along Contrary Creek but it
was feared that the legal course might take longer than pursuing a grant.
None of the current property owners had been involved with the former mining
ctiv1ty.
Representatives of the SWCB met again with EPA officials in August 1973
to discuss the problem and further explore the possibilities of obtaining a
demonstration grant. Indications from EPA were that the problem should have
rio trouble meeting the requirements and that chances of a grant being awarded
were very good since it involved the control of heavy metals.
Under the provisions of Section 107 of Public Law 92-500 the SWC8
decided to apply for an EPA demonstration grant in September 1973 to be used
in reclaiming the mine waste areas along Contrary Creek by means of re-
grading the spoil areas and using wastewater sludge as a soil conditioner.
The ColTlnonwealth of Virginia would provide matching funds through In-kind
services.
In December 1973 the SWCB retained Gannett Fleriing Corddry and Carpenter
a consulting firm from Harrisburg, Pennsylvania to prepare a grant application
and a feasibility study. Attempting to take advantage of funding for the
current fiscal year. the SWCB decided to prepare the grant application using
the meager data available and submit it as soon as possible with the feasi-
bility study supporting the application to be submitted later.
A grant application for $654,757 to be used in reclaiming the three mine
sites was submitted to EPA In March 1974. the provisions of this application
were for 95 per cent Federal funding and 5 per cent State matching funds with
all engineering work contracted to a consulting firm and the biologic studies
25
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contracted to Dr. George N. Sluuions, Jr. of VPI&SU. However, the SWCB was
advised In April that the application had been rejected because funds were
not available and because energy-related projects were receiving high priority
at that time. Shortly afterwards the SWCB was advised by EPA that the grant
application might be reconsidered if ways could be found to cut the cost
and If the Coninonwealth of Virginia could share a larger portion of the cost.
In the meantime the consultants continued work on the feasibility study.
While the grant application and feasibility study were in progress
Callahan Mining Corporation who had formed a partnership with New Jersey Zinc
Company known as Piedmont Mineral Associates contacted the SWCB about an
exploration program they were conducting near the Contrary Creek mines.
Callahan was considering using the Arminius Site for milling operations pro-
vided their exploratory program warranted going Into production. Callahan
was also Interested in recovering valuable metals from the old tailings at
the other mine sites along Contrary Creek but after conducting extensive
samplings, assayings, and metallurgical tests they determined that this would
be uneconomical. However, Callahan advised the SWCB that they were still
interested in using the Arminlus Site for a milling operation provided their
nearby exploration proved successful, and they expressed a willingness to work
with the SWCB In reclaiming the Arniinius Site.
During the latter part of 1974, the SWCB explored several means of reduc-
ing the project costs. The first step taken was for the SWCB to assume re-
sponsibility for the biologic studies rather than contract this work, and
some of the property owners were approached about sharing part of the cost.
The SCS was contacted about what assistance they might be able to provide.
Since the SCS had done some earlier studies at the mine sites and because
erosion control was a major part of the problem, it was felt that that agency
could lend valuable assistance and could make reconinendations for reducing
costs. After SCS personnel toured the mine waste areas and reviewed the pro-
posed reclamation methods, they were of the opinion that the scope of the
project set forth by the consultants could be reduced considerably. They
felt that the channel work proposed downstream between the Route 522 Bridge
and Lake Anna would result in only negligible improvement in water quality
of Contrary Creek and reconinended that no work at all be doree along this 9art
of the stream. They proposed only minimal channel work ir. the ininedlate
vicinity of the mine sites and they also felt that the spoil piles could
be regraded and smoothed In preparation for seeding with less disturbance of
the existinq topography and at less cost than proposed by the consultant.
The Glatfelter Pulp Wood Company,owners of t e Sulphur Site, were asked
about sharing some of the costs of reclaiming that site but they were reluc-
tant to do so and It was the opinion of the SWCB that they could not legally
be compelled to participate. They did agree to pl t pine seedlings on the
Sulphur Site when restoration work was completed. the SWCB also asked VEPCO
about providing some financial assistance, but since they owned only an insig-
nificant portion of property at the moith of Contrary Creek they felt no
obligation to assist. VEPCO did indicate a willingness to help with the
monitoring work in the Contrary Creek arm of Lake An ia but this task was
26
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eventually assumed by the SWCB.
After Callahan Mining Corporation determined that it would not be
economical to recover the abandoned tailings along Contrary Creek, they con-
tinued their exploration work east of Route 522. In November 1974 Callahan
uormally notified the SWCB that they would take responsibility for reclaiming
the Anninlus Site regardless of whether a decision was madc to go Into pro-
duction or not. The consultants had estimated a cost of $127,000 for restor-
Ing the Arminius Site. This, of course, meant a considerable reduction In
the grant needs.
Mter several meetings between the consultants, SCS, landowners Afld EPA,
the SCS agreed in November 1974 to provide all enqineering servlr s for the
project including survey work, preparation of construction pla;is and specifi-
cations and personnel for general and resident insoection. Th* SCS kindly
agreed to provide these services at no cost. Needless to say, i.his was
another tremendous cost savings since the consultants had estimaied a total
cost of approximately $143,000 for these tasks. The EPA Project Officer
advised the SWCB that the participation by SCS did not conflict with grant
regulations and that it did not have to be cost Itemized in the grant appiica-
tion. By this time the consultants were nearly finished with the feasibility
study. The study had been revised to Include the downstream reach of Contrary
Creek but as mentioned above there was a difference of opinion between the
consultant and the SCS on the feasibility of doing this work. The consultant
estimated a cost of $221,000 to dredge and realign the downstream reach.
In early 1975 the SWCB prepared and submitted a revised grant application
requesting funds to reclaim the Boyd Smith ‘id Sulphur Sites. The total funds
requested were $225,158 with the Conmionwealt of Virginia providing $150,503
matching funds making the total budget $375,6 1. This amounted to 60 per cent
Federal funding with 40 per cent Corrvuonwealth of Virginia funding. Virtually
all of the Federal money requested was to cover construction costs with a
very small percentage for contractual personnel services. Table 5 gIves more
details on the itemized costs in the grant application.
TABLE 5. BUDGET BY COST CATEGORY REQUESTED IN GRANT APPLICATION
Federal Funds
Construction $223,718
Contractual Personnel Services 1.440
Subtotal 225,158
Coirinonwealth of Virginia Matching Funds
Personnel $70,870
Fringe Benefits 16,300
Travel 5,786
Equipment 20,417
Supplies 35,640
Indirect Costs 1,490
Subtotal 1 150.503
Grand Total $375,661
27
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The objective of the project as set forth In the grant application was
to demonstrate methods by which pollutlonal discharges containing high concen-
trations of dissolved metals may be abated from two Inactive pyrite mines and
their pyrite-laden wastes washed into the streambed and flood plain of Contrary
Creek. The approach set forth in the grant application provided for the SCS
to do the engineering work and described the proposed reclamation of the
Arminius Site by Callahan Mining Corporation. The feasibility study was sub-
mitted In support of the grant application although as has been pointed out,
the scope of the project had been reduced considerably from that proposed
in the feasibility study.
FEASIBILITY STUDY
The purpose of the feasibility study was to define the extent of the
mine drainage problem along Contrary Creek and Lake Anna, to reconnuend
appropriate abatement measures, and to make cost estimates for the proposed
restoration work. The study addressed all three mine sites along 1th the
downstream reach of Contrary Creek between the Sulphur Site and Lake Anna.
The consultant conducted several field Investigations of the project area
during 1974 and the SWCB provided them with all information available includ-
tng mining history, climatological data, biological and chemical studies, and
regulations of the SWCB. The Virginia Department of Highways and Transporta-
tion was engaged to do special aerial photography of the project area and that
agency also provided existing contour maps for use in defining areas affected
by the mine waste. Since only meager chemical data were available, weekly
sample collections were made along Contrary Creek at the various mine sites
from April until October 1974 to provide additional data to be included in
the feasibility study. Sampling continued through the inte, m period until
the regular monitoring program began in October 1975. The water quality data
collected over this period continued to show the effects that the leaching of
AND was having upon Contrary Creek. A sumary of these data is shown in
Table 6.
The feasibility study was completed in December 1974 and a sumary of
the conclusions drawn is as follows:
1. The demonstration project would meet the requirements of Section 107
of the Federal Water Pollution Control Act.
2. It would be feasible to reduce erosion and leaching of acid and
metallic salts originating from three abandoned pyrite mines and
from pyrite-laden wastes in the channel of Contrary Creek by re-
storing waste dumps and by reconstructing stream channels.
3. A considerable volume of pyritic waste material deposited in Contrary
Creek downstream from the three mine sites also posed a potential
threat to the downstream water quality.
4. Anticipated reductions in the pollutional load should effectively
improve the stream quality of Contrary Creek and should substantially
remove the potential for flush-outs or acid and dissolved metals
28
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TABLE 6. AVERAGE WATER QUALITY ANALYSES OF CONTRARY CREEK
PRIOR TO RECLAMATION (mg/l)a
I ’ ,
0
Monitoring
Station
pH
Acidity
(CaCO 3 )
SO 4
Cu
Fe
Pb
Mn
Zn
Above all
Mine Sites
6.8
13
9
0.02
1.1
0.01
0.06
0.2
Below Arminius
Site
6.0
12
98
0.11
2.1
0.02
0.52
4.8
Below Boyd
Smith Site
4.8
34
149
0.22
2.6
0.03
1.54
3.8
Below Sulphur
Site
3.7
126
229
0.76
24.1
0.08
1.71
4.0
Mouth of
Contrary Creek
3.3
169
67
1.20
23.1
0.05
1.45
3.5
a
Based upon the
average of
approximately 25
samples
collected
in 1974
and 1975.
-------
that could contribute to fish kills and could harm normal aquatic
biota In Lake Anna.
5. A proposed monitoring program gould define the extent of the mine
drainage problem, and the data obtained would establish the effec-
tiveness of the demonstration project and would aid in determining
any remaining pollutional loads that would have to be abated to
achieve desired stream quality.
6. Accurate cost records obtained from the project would have potential
future use for abatement methods on similar areas.
7. Existing legislation and the easements to be obtained for tnis pro-
ject would protect the restored sites.
A summary of the recoirinendatlons made In the feasibility s’udy are as
follows:
1. Regrade the pyritic waste disposal areas to maximize surface runoff,
minimize erosion and promote vegetative growth.
2. Dredge and realign portions of Contrary Creek and tributaries and
construct diversions within the mine sites.
3. Conduct soil analyses and apply lime and fertilizer as needed.
4. Place wastewater sludge on the regraded areas and seed.
5. Dredge and realign all of Contrary Creek and portions of tributaries
downstream between the Sulphur Site and Lake Anna.
6. Conduct an extensive monitoring program which would include the
construction of 5 flow gaging stations along Contrary Creek and
establish 2 sample stations in the Contrary Creek arm of Lake Anna.
Collect grab samples from all monitoring and sample stations period-
ically to be analyzed for pH, alkalInity, acidity, sulfates, turbi-
dity, suspended solids, iron, copper, zinc, manganese and lead. It
was further recommended that analyses for BOD and fecal coliform be
conducted at all stations after wastewater sludge was applied.
Continuous precipitation records were also to be compiled.
7. Cost records be compiled so that actual abatement costs could be
determined.
8. All precautions should be taken during construction to minimize
flooding, sedimentation and pollution problems.
SITE EASEMENTS
Under the provisions of Section 107(d) of PL-92-500, the SWCB secured
agreements with the owners of the mine sit s prior to beginning the reclama-
tion work. Section 107(d) states:
30
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“(1) that the State shall acquire any land or interert therein
necessary for such project; and
(2) that the State shall provide legal nd practical protection to
the project area to Insure cgalnst any activities which will
cause future acid or other mine pollution.’
As mentioned earlier, the SWCB had determined who the property owners
were and had contacted them about the proposed reclamation work during the
Initial planning stages. The Sulphur Site Is part of a 650-hectare tract
owned by the Glatfelter Pulp Wood Comp3ny and the Bcyd Smith Site is privately
owr.ed by Mrs. Otella Mallory who resides on the property.
While the grant application and feasibility study were being prepared,
the Office of the Attorney General of the Commonwealth of Virginia with the
assistance of the SWCB drafted d ds of easement to be executed with each
property owner. The deeds of ea$ement covering a period of 5 years provided
for the necessary reclamation work and the construction of flow recording
stations and stipulated that the owners would not conduct any artivity that
would adversely affect the pruject goals or objectives. The Glatfelter Pulp
Wood Company requested a special provision In their agreement which would not
prevent them from planting trees on the reclaimed areas, and the Mallory
eas ment was modified to provide for a lease agreement with Piedmont Mineral
Associates. A copy of the general provisions of the agreement appears in
Appendix A.
Separate agreements were executed with New Jersey 7inc Company to provide
for access to the Arminlus Site and with another property owner to allow for
thc construction of a flow gaging station upstream from all the mine sites.
No serious problems were encountered in securing the easements other than the
property owners asking for some addlti&r.al information and requesting that a
few minor changes be made in the agreements. Initially, a preliminary memo-
randun of understanding was proposed with the owners prioi to e cecut1on of the
fo”mal property agreement, but the owners felt that the proposed agre ient was
too broad, unclear and comitted them to signing another agreement wh t ch they
had not seen. In light of this circumstance the SWCB decided to proceed with
the execution 3f the final deeds of easement which were all signed prior to
the be 1nn1ng of the construction work. Deeds of easement were recorded In
the Louisa County Courthouse.
PLANS AND SPECIFICATIONS
In June 1975 the SWCB was notified by EPA that the Contrary Creek grant
application had been selected for award. With the aid of large scale rapping
provided by the VDH&T and by fle’d surveys, the SCS drafted plans and specs
for restoring the Boyd Smith and Sulphur Sites and prepared a bidding document.
The general outline of the reclamation plan developed by the SCS follows:
31
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(1) ClearIng of waste areas
(2) Grading and smoothing
(3) ConstructIng diversions and waterways
(4) Salvaglr g and spreading topsoil
(5) Excavating channels
(6) PlacIng loose rip ap stone
(7) Spreading wastewater sludge
(8) Seeding and planting
(9) Providing erosion control
All plans nd specs were submitted to EPA for approval and the bid docu-
ment was reviewed by the Virginia Office of the Attorney General before invi-
tations to bid were advertised. The bid package provided for all construction
work necessary to reclaim the mine sites except furnishing of riprap material
and hauling of wastewater sludge.
BID ADVERT! ING AND AWARD OF CONTRACT
Invitations to bid were advertised In 6 area newspapers and approximately
75 potential bidders were notified by mail. Interested contractors were shown
the site in January 1976. Sixteen contractors submitted bids. The bids
were opened on 3 February 1976 and ranged from a low of $87,922.50 to a high of
$180,687.50. Several of the contractors in the low bid range were asked to
submit additional information on their firm before a final decision was made.
After this review was made and the SCS had conducted equipment inspections,
the contract was awarded to Sellers Brothers, Inc. of Danville, Virginia who
had submitted the lowest bid. The ccntractor was given notice to proceed with
work at the beginning of April 1976 and to have all work completed within 150
calendar days as specified in the bid document.
A separate contract was negotiated with a local quarry for furnishing
riprap tono and bedding. In lieu of public advertising, local stofle sup-
pliers were sent invitations to quote a price on furnishing and delivering
the stone material to the project sIte. The low bid f $11,913.90 was
subriitted by A. H. Smith Stone which operates a quarry developed In granitic
rocks approxImately 4 kilometers west of the project atea.
ACQUISITION OF WASTEWATER SLUDGE
The SWCB began exploring for sources of wastewater sludge well before
the construction contract was awarded. The consultant estimated In the
feasibility study a cost of about 10 per metric ton for transporting sludge.
Several municipalities within hauling distance of the project site were con-
sidered, but only the cities of Richmond and Washington, D.C. generated
32
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digested sludge in the volumes needed. The City of Richmond made a detailed
cost analycis, and advised the SWCB that they could haul sludge to the site
for approximately $4 per tonne (metric ton). Richmond was seriously consider-
ed as a sludge source but in the meantime the SWCB had contacted officials
from the District of Columbia about obtaining sludge from the Blue Plains
Wastewater Treatment Plant in Washington, D.C. Initially, the District esti-
mated a cost of about $2 per tonne for hauling sludge but shortly before begin-
ning of Construction work the District advised the SWCB that they could provide
all the sludge needed at no cost for hauling. Needless to say, this repre-
sented another substantial cost savings. The Blue Plains Plant generates
approximately 275 tonnes of anaerobically digested sludge daily. The sludge
from this plant is concentrated by vacuum filtration to approximately 20 per
cent solids. Land costs for disposal of sludge in the Washington, D.C.
metropolitan area are so high that the District of Columbia Government incurred
little If any extra expense in hauling sludge an additional 80 or 90 miles to
the project where, of course, there was no charge for disposal.
MONITORING PROGRAM
A comprehensive monitoring program implemented prior to reclamation to
determine the effectiveness of the project continued until early 1980 when it
was reduced In scale. Monitoring stations were established as reconinended by
the consultant in the feasibility study. Five monitoring stations were estab-
lished along Contrary Creek and two sampling points were established in the
Contrary Creek arm of Lake Anna. All stream monitoring stations were equipped
with continuous flow recorders except for one station at the mouth of Contrary
Creek where channel conditions were too unstable for installing a flow gaging
station. The four automatic recording stations were installed and maintained
by the SW! section of the SWC3.
All regular sample collections were conducted by personnel from the Pied-
mont ReQional Office of the SWCB and analytical work was done by the DCLS as
part of the matching funds. In addition to the regular water quality and flow
monitoring, special studies were done to determine effects of storm runoff and
to pinpoint specific sources of AMD along the main channel of Contrary Creek
and its tributaries. Biologic studies were conducted semi-annually by the DES
of the SWCB. Various soil analyses have been performed periodically by the
SCS and the DCLS and a special study on metals uptake of vegetation was done
by a private firm contracted by EPA. Sludge samples were ccl lected daily dur-
Ing the main phase of reclamation work in 1976 and analyzed by DCLS. Results
of all monitoring are discussed in Section 9 of this report.
33
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SECTION 6
RECLAMATION WORK - 1976
Reclamation work began at the Boyd Smith and Sulphur Sites in early
April 1976. Wet ground caused some delay at the Boyd Smith Site but work
progressed more or less concurrently at both sites. The SCS provided an on-
site Inspector for the duration of the construction and seeding work along
with engineering and agronomic expertise.
For the purpose of this report the various work areas of the Sulphur Site
have been named as depicted in Figure 13.
CONSTRUCTION
The first phase of construction consisted of cl* aring the waste areas of
snags, stumps, brush, rubbish and a few unavoidable pine trees. Special care
was taken to preserve all trees possible including the test plots at the Boyd
Smith Site (Figure 14). All clearing work was done with two D-8 bulldozers.
Regrading and smoothing work was done with the two bulldozers along with
two 175 endloaders and one 9b3 loader (Figures 15 and 16). At the Sulphur
Site a considerable amount of the wastes was pushed or dumped into some of the
old pits and shaft entrances. Since not all of the exact locations of ‘e old
shaft entrances were known at the Sulphur Site, there was concern as to what
danger this might pose for heavy equipment. Fortunately, no cave-in problems
occured. Another concern was the possibility of encountering resistant
hardpan under some of the old tailing piles, but again this problem did not
materialize. A small amount of the fthe tailings frori Sulphur West was truck-
ed to the east side to add some extra fines to the predominantly coarse mate-
rial there.
The spoil areas at both sites were graded to approximately the natural
contours (Figure 17). It is estimated that approximately 67,000 cubic meters
of tailings and reject material were regraded and smoothed at both sites.
This figure is based upon the pre-construction estimate made by the SCS. The
grading and smoothing work progressed considerably faster than expected and
was completed at both sites within two months.
Construction of diversions and waterways to shorten slopes and to mini-
mize runoff infiltrating into the mine wastes and underground workings was
done concurrently with the grading and smoothing work. Locations of diver-
sions and waterways at the Sulphur Site are shown in Figure 18. At the Boyd
Smith Site the main drainageway traversing the site was excavated and realign-
ed, and a diversion was constructed on each side of the site to facilitate
drainage so that the ground would suppcrt heavy equipment (Figure 19).
34
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LEC. LP
- - - 0• £
— R r
Tr-5 Tr uty
FIGURE 13. VARIOUS WORK AREAS OF SULPHUR SITE
/
I•0
‘I
U’
V..,
4 ,
-------
FIgure 14. Clearing and regrading of Boyd Smith Site
AprIl 1976.
Figure 15. Regrading of Large Area at Sulphur East
Spring 1976.
36
-------
Figure 16. Regrading of tailing pile at Sulphur West
Spring 1976.
Flçwre 17. Regraded tailings at Sulphur West-Suniner
1976. Same view as shown In Figure 11 prIor to
reclamation.
37
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SULPHUR SITE
—
C
FIGURE 18. cONSTRUCTION WORK
Ass. mGodld A.i Gt _____
To App,o*w,i.S, Ni wI Cm
- ._ _ - (.s . s
-------
BOYD SMITH SITE
woo..
OIVU$IOMS
a,pa*p sicys s
COSTS’ ..
auDio
LVDSID
iT
l Il IjMiTiN*
FI’ I, E 19. CONSTRUCTION AND SEEDING WORK — SUMMER 1976
(N wi wits rssssdid In spring 0(1977)
4 tons of lime
pr acre on
all areas
CONTRARY CREEK
39
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Another part of the construction work at the Sulphur Site consisted of
straightening the channel of Contrary Creek and excavating toxic materials
from major portions of the streambed. All of the main channel along thc
upstream Flat of Sulphur East was relo.ated and straightened and several
hundred feet of the channel was excavated in the vicinity of the Tailing Area
(Figure 20). InitIally the channel work was attempted with a backhoe but
this machine proved unsatisfactory working from the high stream banks. At
the recomendation of the SCS engineer the backhoe was replaced with a crawler
mounted crane equipped with a dragline bucket and clamshell. The dragline
allowed for greater length of each and proved much mcre efficient. The
diversions at the Boyd Smith Site were also excavated with the dragline be-
cause wet ground limited the use of the backhoe.
Approximately 1400 tonnes of stone from a nearby granite quarry were used
at both sites to stabilize stream banks and to line diversions In the 1976
work (Figure 21). This included 1100 tonnes of Class I dry riprap and 300
tonnes of No. 25 graded aggregate for bedding. The stone size was in accord-
ance with VDH&T specifications. Stone was hauled directly to the placement
areas by the supplier and placed by the contractor. Virtually all riprap
and bedding materials were placed with the dragline. The largest section of
riprap was placed over the old cribbing adjacent to the Tailing Area of
Sulphur West and along the fufl leflgth of Tr-1 in the disturbed area (Figure
18). Additional sections of riprap were added at the Sulphur Site In 1977
and 1978. At the Boyd Smith Site sections of riprap were placed at the mouth
of each tributary draining into Contrary Creek and along the upper reach of
the main tributary near the old shafts (Figure 19). Typical dimensions of
the riprap sections used at both sites are shown in Figures 22 and 23.
APPLICATION OF SLUDGE AND OTHER SOIL AMENDMENTS
The use of municipal sludge in mine reclamation is relatively rare. Few
projects are known to have utilized sludge on th scale that has been done at
Contrary Creek. Municipal sludge has several characteristics that make it
desirable for use in mine reclamation. One of its most important constituents
is organic matter which when Incorporated into r nne spoils increases the
water holding capacity, Increases the cation absorption capacity, and improves
the supply and the availability of nutrients (Hill, 1977).
Before delivery of sludge to the project site began th SWCB provided
the Government of the District of Columbia with written authorization and all
applicable hauling regulations from the VDH&T. Guidelines for the disposal
of sludge were obtained from the Virginia Department of Health. The hauling
route was desi nated so as to minimize travel through populated areas, and
the hauling distance was approxlmna ely 275 kIlometers (170 mIles) per round
trip. Sludge was hauled In iB-tonne—capacity trucks partially covered with
tarpaulins. Usually, 10 loads of sludge were hauled each day with 5 trucks
making 2 trips each. Delivery of sludge began around mid-April and con-
tinued regularly for 2 months except tor a few occasions when wet ground
curtailed operations. ApproxImately 400 truckloads of sludge amounting to
about 7250 tonnes were delivered to both mine sites. Initially ft was anti-
cipated that some stockpiling of sludge might be necessary, but unusually
40
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Figure 20. ExcavatIon of mine wastes from stream
channe’ along Tailing Area at Sulphui West.
Figure 21. Rlprap section at mouth of Tr-2 at
Sulphur East.
41
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7
FIGURE 23. TYPICAL RIPRAP SECTION USED ALONG STREAMBANKS
(NOT TO SCALE)
I
1’
FIGURE 22. TYPICAL RIPRAP SECTION USED IN DIVERSIONS
(NOT TO SCALE)
•“BEDD$NG
Hr
1
42
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dry weather during the spring of 1976 and an agreement with the hauler to
deliver sludge on an as-needed basis minimized stockpiling. Virtually all of
the sludge was dumped directly upon the regraded areas where it was to be
Incorporated (FIgure 24).
Before sludge was spread and worked Into the regraded areas, lime and
fertilizer were applied to all areas to be reseeded. A spreader truck was
used to apply lime to all areas except on steep slopes and soft places along
the stream banks where It was necessary to hand spread. Lime was applied at
the rate of 9 tonnes per hectare (4 tons/ac), and 10-10-10 fertill:er was
applied at the rate of 1120 kIlograms per hectare (1000 lbs/ac) to all areas.
In addition to the 10-10-10 fertIlizer 38-0-0 (ureaforin) fertilizer was applied
at the rate of 448 kIlograms per hectare (400 lbs/ac) to the unsludged areas.
(Table 7).
TABLE 7. LIME AND FERTILIZER APPLICATI0 i RATES - 1976
Lime
9 tonnes/ha
Fertilizer
All areas
10-10-10
1121
kg/ha
Unsludged areas
38—0-0 (ureafonn)
448.4
kg/ha
To convert tonnes/ha to tons/ac multiply by 0.449.
bTO convert kg/ha to lbs/ac multiply by 0.892.
Sludge was generally allowed to dry for up to a week prior to spreading,
but In some cases spreading was done a day or two after delivery. It would
have been desirable for sludge to have dried longer before spreading, but this
was not feasible due to time constraints. Bulldozers were used to spread the
sludge to a thickness of approxImately 10 centImeters (Figure 25). It was
found that spreading could be done much more efficiently by backdragging rather
than pushing. A heavy-duty Rome disc drawn by a bulldozer was used to incorpo-
rate the sludge along with the other soil amendments Into the spoil material to
a depth of 8 to 16 centImeters. Where the ground was too soft to support heavy
equipment, a small disc pulled by a fan tractor was used to Incorporate sludge.
Approximately 1.2 hectares of the Sulphur Site Including the Upstream Flat of
Sulphur East and a few places along the stream banks th&t were too soft to
support any equipment were not sludged In 1976.
A total of S443 tonnes of wet sludge was applied to 4.6 hectares of
the Sulphur Site and a total of 1814 tonnes to 2 hectares of the Boyd Smith
Site. As determined by laboratory analyses, the average moisture content of
the sludge used during the sunrer of 1976 w s 78 per cent. The actual dry
tonnes applied are shown in Table B.
43
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Figure 24. DumpIng sludge at Sulphur Site.
Figure 25. SpreadIng sludge at Sulphur Site.
-
- —--
- ill _p.
44
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TABLE 8. SLUDGE APPLICATION RATES - 1076
Sulphur Site 260 dry tonnes,haa
Boyd Smith
Site 200 dry tonnes/ha
a
To convert tonnes/ha to tons/ac multiply
by 0.449.
Special care was taken during all phases of the operation to prevent
sludge from entering intc Contrary Creek or any of its tributaries. Trucks
were directed to dump a safe distance from all stream banks and in some places
low berms were constructed as a further protection. There was concern that
there might be a problem with sludge being washed into the main stream and
tributaries in the event a heavy rain fell while sludge was drying, but it was
found that sludge tended to cohere when wet and did not flow appreciably.
Where possible, some sludge was applied o stream banks but Inaccessibility
kept this to a minimum. Trucks were carefu 1 ly cleaned after each dumping
to prevent loss of sludge on public highways.
As part of the project monitoring, samples were collected from each
truckload of sludge and composited Into one daily sample during the 1976
work. There was little variation in the composition oF the sludge from day
to day but moisture content varied as much as 8 per cent. Thie variatior can
mainly be attributed to the sludge being stored in the open for a day or so
before hauling, and there is some slight variation in moisture content of
the sludge from the treatment plant. Sludge samples were analyzed by the
Division of Consolidated Laboratory Services, the same laboratory that has
conducted all of the water and soil analyses for the project. Average con-
centrations of the constituents in the Contrary Creek sludge based upon 40
composite samples collected during the 1976 work are shown in Table 9.
The heavy metals content of the Blue Plain.; sludge is within the range
of that reported for sludge from other municipal sewage treatment plants and
tends to be lower than that from highly Industrialized cities. The high iron
content of the Blue Plains sludge Is partly due to ferric chloride used in the
treatment process. The average pH of the sludge was 6.5 and volatile solids
averaged 51 per cent. Fertilizer equivalent values were also determined for
the sludoe and averages for the composite samples In the suniner of 1976 are
shown In Table 10. AdditIonal sludge data appears in Section 9 of this report.
45
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TABLE 9. AVERAGE CONCENTRATIONS OF CONSTITUENTS
IN THE SLUDGE USED AT CONTRARY CREEK IN 1976
ON D Y WEIGHT BASIS
Constituent pp
Alkalinity 17
Cl (Soluble) 8.1
Cd 17
Cr 659
Cu 765
Fe 109,000
Pb 550
Hg 5.05
Zn 2,529
NI 29
F (Soluble) ()•73
TABLE 10. AVERAGE FERTILIZER QUIVALENTS OF 5LUUGE
USED AT CONTPARY CREEK IN 1976 ON
DRY WEIGHT BASIS
Nutrient Per cent
N 3.23
7.32
K 2 0 0.32
46
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Seeding began In late June and was completed at both sites by eariy
July. WhIle it was realized that this was not the most favorable season
for planting, It was not feasible to delay the seeding since Lhe regrading
and smoothing work had progressed considerably faster tnan expected. After
all soil amendments had been incorporated, the seedbed was smoothed by
dragging heavy timbers over rough areas as a final preparation. A tractor-
drawn BrIllion cultlpacker was used to do all seeding except for steep banks
and soft spots that had to be hand seeded. The seed formula included two
grasses, Ky-31 fescue and red top, along with ladino clover for a legume.
Seed species and applicatk.”n rates are given in Table 11. Figure 26 shows
seeded and sludged areas of the Sulphur Site. Refer to F1gu e 19 for seeding
done at the Boyd Smith Site.
In addition to the specified seed formula, 24 kilograms of deertongue
grass were sown randomly over various areas of Sulphur East at the reconiiien-
dation of the SCS agronomist. Immediately after seeding, mulch comprised of
small grain straw was applied at the rate of 5 tonnes per hectare with a
mulching machine and tied down with emulsified asphalt.
TABLE 11. SEED SPECIES AND APPLICATION RATES - 1976
Species Kg/had
Tall Fescue (var. Ky-31) 67
Red Top 5.6
Ladino Clover 5.6
a
To convert Kg/ha to lbs/ha multiply by 0.892.
After all construction was completed, several straw bales were staked
In dralnageways and along stream banks to control erosion until vegetation
had a chance to establish, but by late summer it was realized that additional
erosion controls would be needed. Approximately 300 straw bales were placed
at erosion prone areas on both sides of the Sulphur Site in October, 1976.
COSTS
All Construction and seeding work was performed by Sellers Brothers,
Inc. and included the furnishing of all materials except stone and sludge.
Payment for construction was based upon the hourly rate for equipment rental
as agreed to In the contract. Payment for seeding including all lime,
fertilizer, seed, mulch and asphalt t eJown was at the rate of $600 per acre.
The SCS inspector logged eqdipment hours daily and measured acreage at the
completion of seeding. A summary of the construction and seedinq costs
appears in Table 12.
47
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•0*OS
O.VUSIOWS
lWLC: S$ ON POUNDA?IONI
coqtous
1EED O
FIGURE 26. SEEDING WORK — SUMMER 1976
SULPHUR SITE
I
AU N
4 0I
w.
I
it
LCSEND
0
4
____________ IIImS
4$
ILUOSID
-------
The original contract called for 3 0-8 bulldozers. [ ut as grading pro-
gressed more rapidly than expected it was decided by the SCS engineer that
one bulldozer could be eliminated and that the estimated hours could be re-
duced on another bulldozer. In place of these hours were added a crane, a
farm tractor with attached disc, and d water truck. As stated above, the
crane was much more effective than the backhoe for working on stream banks
and the tractor drawn disc was needed in areas inaccessible to bulldozers.
The water truck was added for dust control.
The only other contract negotiated In connection with the 1976 reclarna-
tion work was with A. H. Smith Stone for the furnishing and delivery of riprap
and bedding material. Table 13 gives a breakdown of stone costs. Total cost.
of the construction and seeding work was $64,863.90 as shown below.
Sellers Brothers $55,709.50
A.H. Smith Stone $ 9,154.40
Total $64,863.90
Sellers Brothers had bid $87,922.50 for the job and A. H. Smith Stone
had bid $11,913.90 for furnishing stone.
The contract with Sellers Brothers, Inc. included the planting of pine
seedlings at the Boyd Smith Site, but this work was carried over until the
spring of 1977 when the season would be optimum for planting.
RESULTS
The success of the 1976 see iing work was very limited. It was realized
that late June and early July we.’e not optimum times for planting and the
problem was further compounded by below average rainfall during the remainder
of the growing season. This was particularly so in July, and by the time a
few heavy thunderstorms came in August, much of the grass that had germinated
had died. Only in the more shaded areas did the grass show any degree of
success.
It came as no surprise that condItions at the Sulphur Site were by far
the poorest. The only areas that showed any significant cover of grass by
the end of the sununer were some of the shaded areas on Sulphur East. The
Large Area of Sulphur East produced a heavy growth of tomatoes during the late
sununer, but after the first frost only a few patches of vegetation remained
around the edges that had been shaded. Virtually no germination occurred on
the Tailing Area of Sulphur West even though sludge had been applied heavily.
None of the unsludged areas on either side of the Sulphur Site showed any
signs of germination.
At the Boyd Smith Site the results of the 1976 work were more encouraging.
A fair growth of vegetation established on some parts of the site, but the dry
weather took its toll here also despite the ground remaining somewhat wetter
than the Sulphur Site. Sludge had been applied to all of the Boyd Smith Site,
but of the seeds pianted, only the Ky-31 showed any success.
49
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TABLE 12. SUMMARY OF 0NSTRUCTION AND SEEDING COSTS - 1976 a
EQUIPMENT RENTAL
Type Equipment No. of No. Hours Cost Per Total
Pieces Used Hour Cost
D -8 150 dozer 1 184 $29.00 $ 5,336.00
0-8 100 dozer 1 182 22.50 4,095.00
175 loader 2 498.5 23.00 11,465.50
955 loader 1 183 21.00 3,843.00
Crane 1 312.5 40.00 12,500.00
Backhoe 1 79 35.00 2,765.00
Rome disc 1 65 2.00 130.00
Farm tractor & disc 1 43 25.00 1,075.00
Dump truck 1 32 12.50 400.00
Water truck 1 27 10.00 270.00
Power saw 1 20 6.50 130.2 _
Subtotal 12 1626 $42,009.50
SEEDING
Site No. Acres Cost per Total Cost
Seeded Acre
Sulphur 14.5 $600 8,700.00
Boyd Smith — 5 $600 3,000.00
Subtotal 19.5 $11,700.00
MOBILIZATION $2,000.OO
Grand Total $55,709.50
a
Does not include cost of stone.
TABLE 13. SUMMARY
OF
STONE COSTS
pe Stone
Riprap
No. Tons Used
Cost per ton
Cost
$8175.08
1090.01
$7.50
Bedding
240.70
71.33
3.15
3.10
TOTAL
758.20
221.12
$9154.40
50
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By late sumer It was apparent that complete reseeding would be necessary
in the spring of 1977. and an abnormally cold fall further aggravated the
problem. Overriding the weather problems was the fact that major portions
of the Sulphur Site still remained highly toxic. As an added protection
against erosion in critical areas of the Sulphur Site, approximately 285 straw
bales were staked In drainageways and along stream banks. This work was done
by a local contractor on a non-bid sole source basis at a lump sum of $845.
Maintenance work conducted since 1976 Is discussed in the next section.
51
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SECTION 7
MAINTENANCE
An ongoing maintenance program has continued since the major reclamation
work of 1976. Maintenance work has included the application of more sludge,
lime, and fertilizer; reseeding of problem areas; and the placing of addition-
al riprap and straw bales to control erosion. All of the Sulphur and Boyd
Smith Sites were reseeded in the spring of 1977 and spot seeding of problem
areas has been continued each fall and spring to date. Soil samples have
been collected and analyzed periodically from both sites to determine lime
and fertilizer requirements. A sumary of sludge, lime, nd fertilizer appli—
catior and soil analyses is presented In Section 9.
.All of the maintenance work has been done by local contractors except
for the spring 1977 work which was performed by Sellers Brothers, Inc. The
SCS has continued to assist the SWCB with maintenance work by providing
technical advice and inspection services. Virtually all of the SCS assistance
since 1977 has been provided by the Louisa County Field Office. Plans and
specifications for all maintenance work have been prc.pared with the assistance
of the SCS and approval of the EPA Project Officer.
SPRING 1977
The spring of 1977 work consisted of the application of additional lime
and fertilizer, reseeding of both sites, and placing a new section of riprap
at the Sulphur Site. Since the contract with Sellers Brothers was still open
providing for the planting of pine seedlings at the Boyd Smith Site, all of
the spring maintenance work was done under a contract modification with the
exception of furnishing stone.
Lime application rates were determi-ied by titration analyses of composite
soil samples. A discussion of analytical procedures is given in Appendix B.
lime was applied by spreader truck at rates ranging from 13.3 to 31.2 tonnes
per hectare (6 to 14 tons/ac) on the Sulphur Site (Figure 27) and t a rate
of 9 tonnes per hectare (4 tons/ac) on the Boyd Smith Site.
Four different types of fertilizer were used including the 10-10-10 and
38-0-0 types used the previous sun ner along with 907 kilograms (1 ton) each
of 16-7-12 and 18-18-6 controlled release fertilizers which were donated by
the Sierra Chemical Company to compare with other fertilizers. Each type of
controlled release fertilizer was applied to designated portions of both
sites totaling about 3.2 hectares. This Included 2.4 hectares that had re-
ceived sludge the sunniier before and 0.8 hectare along the stream banks of the
Sulphur Site that had not been sludged. Unfortunately, extensive maintenance
since 1977 has probably obscured any pronounced results the controlled release
52
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buLr uH 5 1TL
I y_ _ -Th
14 ol Si..s ,
14 —.
.- --—— /
--
p- -. --_‘\ “ --.---- .-
- -: :
iS 01 —.
1’
S _ 01 hous pus sao
(
00000
woo..
oIvu,Iow.
SYPtAN.
suI .oIsS . OS O ’0OATiON1
vs
FIGURE 27. SEEDING WO 4K — SPRIIIG 1977
Slusus 01 w.
I
p•i I
?I SI
cONT 0U..
1110(0
-------
fertilizers may have had. All remaining portions of both sites were treated
with 10-10-10 fertIlizer vith the 38-0-0 ureaform dgdlfl added to the severe
areas where sludge had not been applied. A sumary of fertilizer and applica-
tion rites Is given in Table 14.
ThBLE 14. FERTILIZER APPLICATION RATES
_____ SPRING 1977 (Kg/ha)a
Sludged Unsludged
Type Areas Are _
16-7-12 336.3 896.8
18-18-6 336.3 896.8
Sulphur Site 10-10-10 560.5 560.5
38-0-0 484.4
336.3
Boyd Smith Site 18-6-6 336.3
10-10-10 560.5
a
To convert Kg/ha to lbs/ac multiply by 0.892.
The seedbed was prepared with small disc drawn by a farm tractor and a
cultipacker was again used to incorporate seed. Weeping lcvegrass and Korean
lespedeza were added to the seed formula that had been used the previous sum-
mer. Seed types and application rates are shown in Table 15.
TABLE 15. SEEDING - SPRING 1977
Type
Kg/ha
Tall Fescue
67.3
Red top
5.6
Ladino Clover
2.2
Korean Lespedeza
11.2
Weeping Lovegrass
2.2
a
To convert Kg/ha to lbs/ac multiply by 0.892.
In fulfillment of tne original contract agreement the contractor planted
6500 pine seedlings of the species Virginia Pine ( pinus virginiana ) at the
Boyd Smith Site. The GlatfelterPuip Wood Company planted 17,000 Loblolly Pine
seedlings at the Sulphur Site after seeding work was completed. In addition
54
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to the seeding and planting work a small section of riprap was placed on the
North End of Sulphur East where Tr-2 enters Contrary Creek.
Under the contract modification with Sellers Brothers, Inc. all of the
seeding work was done at both sites at a cost of $1,000 per acre which included
the furnishing and planting of pine seedlings at the Boyd Smith Site. The
only other cost Item involving the work Sellers Brothers performed was equip-.
ment rental for a luacier to place riprap. All mobilization costs were includ-
ed In each cost item. Stone was again furnished and hauled to the site under
a separate contract with A. H. Smith Stone. A cost breakdown appears in
Table 15.
TABLE 16. MAINTENANCE COSTS - SPRING 1977
Seeding and Construction (Sellers Brothers, Inc. )
Seeding 13.5 acres of Sulphur Site @ $1,000/ac $13,500.00
Seeding 5 acres at the Boyd Smith Site @
$1,000/ac 5,000.00
44.5 hours of u awler tractor time @ $36/hr 1,602.00
Subtotal $20, 102.00
Stone (A. H. Smith Stone )
75.28 tons of riprap @ $7.50/ton $564.60
45.14 tons of bedding @ $3.15/ton 142.19
Subtotal $706TT9
Grand Total $20,808.79
The sprig of 1977 reseeding work was almost a complete failure primarily
due to the severe drought which followed. Rainfall for the months of June
thru September was 22 centimeters below normal (Page 7 ) and by late summer
some of the upper reaches of Contrary Creek, itself, had completely ceased
flowing. The extreme drought not only negated the spring seeding but also
destroyed some of the meager patches of Ky-31 grass that had survived from
the previous summer. The one encouraging note was the weeping lovegrass which
came on in late July at the height of the drought. This drought-tolerant
grass which had been sown for the first time in the sprinci of 1977 exhibited
a vigorous growth on most of the Large Area of Sulphur East and the Boyd
¶mlth Site. The lovegrass was most successful In the same general areas tnat
scatte c” patches of Ky-31 had managed to take root in 1976. The lovegrass
was the only vegetation from the spring seeding that survived the summer,
and it shows good survival a ter three years. Sulphur West remained practi-
cally barren as well as several other smaller areas of Sulphur East. Virtually
all of the pine seedlings that had been planted at both sites died before the
end of summer and most died within two weeks after planting. Lt was obvious
by mid-summer that a major reseeding program would be necessary in the fall.
55
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FALL 1977
With acslst3nce from the SCS the SWCB prepared plans and specifications
for the fall of 1977 maintenance work and arranged with the Blue Plains
Wastewater Treatment Plant for delivery of aoditional sludge. The maintenance
work consisted of (1) spreading and Incorporation of sludge on designated
areas; (2) liming, seeding, and mulching portions of both sites; and (3)
modification of an existing beaver dam for a source of irrigation water at
the Sul—hur Site. Plans and specifications for the work were submitted to
two local contractors who were asked to submit bids. The contract was award-
ed to W. C. raylor of Mineral. The contractor did not submit the low bid,
but the other bidder could not guarantee completion of the work within the
prescribed time schedule. W. C. Taylor has done the major portion of all
subsequent maintenance on a sole source non-hid basis.
All maintenance work W3S done during September and October. Seeding
work was to be finished by the end of eptemher, but a delay in the delivery
of sludge forced completion of seeding to nid-October.
Sludge was applied only to the Sulphur Site. Approximately 1770 tonnes
(wet weight) of sludge was applied to 1.1 hectares on Sulphur West and to 0.5
hectare on Sulphur East (Figure 28) which amounted to approximately 220 dry
tonnes per hectare (99 tons/ac). Sludge was applied to the Upstream Flat of
Sulphur East for the first time. This area where the stream had been straight-
ened was too soft to support heavy epuipment when the 1976 work was done, but
the extremely dry con’iitions of 1977 allowed the sludge trucks to dump direct-
ly on the areas of application. The sludge was again spread with a bulldozer
and worked in with a heavy duty disc. The sludqed areas were further smoothed
by a small disc which was also used to prepare the unsludged areas for seeding
(Figure 29).
The only area limed at this time was the Tailing Area of Sulphur West.
Lime was applied at the rate of 22 t nnes per hectare ( O tons/ac). At the
recomendation of the EPA Project Officer approximately 0.2 hectare had the
lime sandwiched between two applications of sludge (Figure 28). After sludge
and lime had been applieo, seed was incorporated with a grain drill drawn by
a farm tractor (Figure 30). ThIs method of seeding was used for all subsequent
maintenance except for inaccessible areas that were hand seeded. The same
types of seed and application rates were used as in the spring of 1977 seeding
with the exception of ladino clover which was dropped from the formula. A
total of 3 hectares was reseeded at the Sulphur Site as shown in Figure 28.
Mulch comprised of small grain straw was hand spread on approximately 2
hectares of newly seeded areas of the Sulphur Site and tied down by discing.
The only work done at the Boyd Smith Site was the reseeding or approximately
0.2 hectare as Indicated in Figure 31 usIng the same seed types and applica-
tion rates.
Prior to application of sludge and the seeding work an exising Impound-
ment which had been formed by a beaver dam was modified slightly for a source
of irrigation water. This impoundment is approximately 200 meters upstream
of Tr-1 from Sulphur West and contains good quality water. Since the dry
56
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SULYPIUII SI I t
1 -
10
ThN
—. —_n..
U, -
a
a
/
(ç
11(ANS
III.OINII 0 POUND*YION$
SIEOID -
/
‘a
JJ1L R. I’.
•Z ‘UT
moos
— o.vc i.ows
-
pilj_f
FIGURE 28. SEEDING WORK — FALL 1977
Il.uo.I.
-------
Figure 29. PreparatIon ‘f seedbed with small disc.
FIgure 30. SeedIng with a grain drill.
58
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BOYD MTH SITE
.E GEND
WOODI
p—-* $TNE*M$
CONTOURI
ICEDED
UT
FIGURE 31. SEEDING RK — FALL 1077
CONTRAR’ ’ CREEK
59
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weather had continued up tc the time of se i ing, arrancjenients were made with
another local contractor to provide equipment and apply irriqdtiol water as
needeu. However, heavy rains !n eatly November broke the drought, and It was
not necessary to Irrigate at this time.
Under the terms of the contract, payment far the spreading of sludge
and the modification of the existing impoundment was on a lump sum basis.
Payment for seeding which Included furnishing all lime, seed, mulch, equipment,
and labor was at the rate of $740 per acre. Anc’ther contract wa liter
arranged with the same contractor to place some additional straw bales at the
Sulphur Site for erosion control. A sunuiary of costs appears in Table 17.
TABLE 17. MAINTENANCE COSTS - FALL 1977
Spreading 2,000 tons of sludge
$1300
Seeding 8.1 acres @ $740/ac
4957
Modification of impoundment
400
Placing 56 straw bales @ $4.50/bale
252
Total
$6909
The results of the 1977 fall seeding were the most encouraging so far for
the project. The heavy rains durirg the first week of riovenber caused grass
to germinate in places that no germination had occurred before. The heavy
application of sludge on the Upstream Flat of Sulphur East and the Tailing
Area of Sulph ir West was undoubtedly also a major factor. Particularly note-
worthy was the Tailing Area of Sulphur West. Unfortunately. with the onset
of CO .J temper?tures so near, the grass did not have a chance to get a good
start.
Despitc’ the successes, some of the same old troublesome areas at the
Sulphur Site remained bare or showed meager growth of .jrass. It was obvious
that more spot setding would he necessary tne followi’ig year.
SPRING 1978
During the winter of 1978 s3il samples were coflected from the barren
areas at the Sulphur Site to determine lime requirements. Re t’lts are discus-
sed in Section 9. With the assistance of the SCS it was determineo tt’at ap-
proximately 1.6 hectares of the Sulphur Site would be reseeded during the
spring season. It was decided that seeding work would not be attempted on the
stream banks where the ground was very soft arid because a major reseeding
program was planned foi the fall of 1978. While then was risk that another
severe drought would make this work f .tile, it was felt that gains could be
made if a more normal season of rainfall followed. The same contractor who
had done the fall of 1977 work did the seeding; seed types and application
rates are shown In Table 18. Note that red top was dropped from the s .ed
60
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formula. FIgure 32 depicts the areas seeded.
T LE 18. SEEDING - SPRING 1978
Species
Tall Fescue
67.3
Korean Lespedeza
11.2
Weeping Lovegrass
2.2
To convert Kg/ha to lbs/ac multiply by 0.892.
A second contract was negot ated with a local supplier to furnish and
spread lime over the reseeded areas at the rate of 22.25 tonnes per hectare
(10 tons/ac), and a third contract was negotiated with another contractor
to furnish and spread straw mulcn over approximately 0.6 hectare of the
Upstream Flat of Sulphur East. All liming and seeding work was done in early
May and mulching was completed by mid-May. The seeding contract provided for
the furnishing of all seed, equipment, and labor at a cost of $106 per acre.
SCS officials certified that a total of 1.66 hectares was seeded. Table 19
gives a sumary of costs.
TABLE 19. MA!NTENW CE COSTS - SPRING 1978
Seeding 4.1 acres @
$106/ac
$434.60
38.42 tons of
lime @ $14/ton
537.88
Mulching 1.5
acres
Total
250.00
$1222.48
A more normal season of rainfall during the sumer of 1978 made the spring
seeding quite successful. For th small amount of money spent on the spring
seeding the returns were great, l t some of the same problem areas persisted
along the stream banks at the Sulphur Site. As indicated above no attempt
had been made to reseed some of the ctter areas at this time. One of the
more encouraging signs was the increasing grass cover that was apparently
establishing on the Tailing Area of Sulphur West. The Ky-31 grass was still
showing a vigorous growth and for the first time Korean lespedeza germinated.
Also numerous volunteer weeds began to invade the LargeArea of Sulphur East
and the Boyd Smith Site. By this time it appeared that the Boyd Smith Site
would require little additional seeding. The weeping lovegrass again made a
good showing durinq the hot sumer months, and it did very well in the Upstream
Flat of Sulphur East where lit ..le other vegetation had ever germinated.
61
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‘Ii
• _
-
- — --- -
‘— - T - L cT -’
( T
—
0 ooos
—.. DIVERIIONI
,. symt s
SUR.O N $ O FOUNDATIONS
FIGURE 32. SEEDING WORK — SPRING 1978
SULPHUR SITE
1O nsof Sii p
SC ’S t
——
(
/
, ‘?/ COUTOUSS
*110(0
-------
Plans were underway early in the summer of 1978 for the fall maintenance.
Additional soil samples were collected in the problem areas to determine lime
requfrements and arrangements were made with the Blue Plains Sewage Treatment
Plant for delivery of more sludge. At the recommendation of the SCS plans
were made to place some additional riprap at the Sulphur Site. The contract
provided for all maintenance including (1) construction of berms to retain
sludge, (2) spreading sludge, (3) seeding, (4) riprap work, and (5) placin9
additional straw bales.
Delivery of sludge began In late July and was completed in August. A
total of 540 tonnes was stockpiled at three locations on the Sulphur Site.
This was the first time that sludge was stockpiled for any appreciable time
before application. The reason was primarily because most of the application
areas were inaccessible to the sludge trucks. Sludge handles much better
the longer it dries, but there is of course extra work involved in transporting
it from stockpiles to areas of application and there is some risk of heavy
rain washing it out of stockpile areas.
Spreading of lime and sludge began in mid-September. Lime was applied
with a spreader truck (Figure 33) at rates ranging from 11 to 33 tonnes per
hectare (5 to 15 tons/ac) as shown in rigure 35. Sludge was hauled from
stockpiles with an earthiroving pan aid partially spread as it was released
from the pan (Figure 34). Further smoothing was done with a bulldozer before
sludge was disced in. Approximately 0.8 hectare or about one acre on each
side of the Sulphur Site was sludged (Figure 35) with approximately 138 dry
tonnes per hectare (60 tons/ac).
The seedbed of the unsludged areas was prepared with a small disc and
seeding was again done with a grain drill. The same seed formula was used
as the previous spring except that rye was planted at the rate of 22 kilo-
grams per hectare (20 lbs/ac) for a nurse crop.
All seeding work was completed during September, and straw mulch at the
rate of 4.45 tonnes per hectare (2 tons/ac) was placed by hand on all newly
seeded spots. A total of 1.62 hectares was seeded.
A 50-meter section of riprap was placed on the east side of Contrary
Creek along the Upstream Flat where inflow from a tributary from the opposite
side was beginning to erode the stream bank. Another small section of riprap
with bedding was placed in a gully that was starting to develop in the Tailing
Area of Sulphur West. Riprap sections are shown In Figure 18. Forty-seven
new straw bales were placed for continued erosion control.
After the seeding was completed, a small amount of rainfall in early
October germinated the new seed, but another dry spell followed and threatened
the survival of the new grass. It was quickly decided to irrigate all the
seeded areas feasible. The beaver pond that had been modified for this purpose
a year earlier was still intact, and the same contractor that had agreed to
do this work the previous year was hired to irrigate all of the areas
accessible to piping. Water was pumped from the impoundment west of the
63
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Figure 33. Lime spread by truck on Sulphur East.
Figure 34. Sludge spread by earthmoving pan on Tr-1
of Sulphur West.
64
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SULPHUR SITE
•
U,
zp
LEGEND
ROADS
w000S
DIVERSIONS
STREAMS
SUILDINGS OR FOUNDATIONS
CONTOURS
SE WED
StUOGED
FIGURE 35. SEEDING WORK — FALL 1978
T, s
-------
Sulphur Site and sprayed by a system of 30 sprinklers. Between October 23 and
November 13 water was applied to about 1 hectare on S different occasions.
Approximately 2.54 cm of water was applied each time. All of the newly seeded
areas were irrigated except the Upstream Flat and the North End of Sulphur East.
Payment was by the acre for seeding including lime, seed, mulch, equip-
ment, and labor. The contractor was paid for an additional 5.875 tons of lime
required above the contract estimate. Payment for riprap was by the ton for
furnishing and placing stone. Payment for placing straw bales was by the bale
and payment for construction of bernis to retain sludge was on a lump sum basis.
The total cost of the irrigation work was $325 which included $150 for setting
up equipment and $35 per application. Itemized costs for the Fall of 1978
maintenance appear In Table 20.
TABLE 20. MAINTENANCE COSTS - FALL 197C
Construction of berms to retain sludge $200.00
Spreading and discing in sludge 3000.00
Seeding 4 acres 0 $740/ac 2960.00
5.875 tons of additional lime @ $15/ton 88.12
100.39 tons of riprap @ $9/ton 903.51
18.82 tons of bedding 0 $7/tori 131.74
47 straw bales $2.25/bale 105.75
Setup of irrigation equipment 150.00
5 applications of irrigation @ $35/application 175.00
Total 7714.12
The results of the fall irrigation work were most beneficial. Grass
germinated on some portions of the stream banks of Sulphur East and Sulphur
West where no grass had ever sprouted before. The Ky-31 fescue which is a
cool weather grass showed th most success. It was again obvious that the
sludge was a major factor in promoting the growth of vegetation. Some of the
same old problem areas remained barren despite the success of the fall seed-
ing indicating need for continued maintenance.
SPRING 1979
The maintenance program was continued in the spring of 1979 with spot
seeding and application of lime and fertilizer. A total of 0.85 hectare was
seeded at the Sulphur Site the last week of April. Seed species and rates
66
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are given In Table 21 and seeded areas are designated in Figure 36. Wheat
straw was hand spread over all seeded areas for mulch.
TABLE 21. SEEDING - SPRING 1979
Species K Jhaa
Tall Fescue 67.3
Korean Lespedeza 11.2
Sericea Lespedeza 11.2
Weeping Lovegrass 2.2
Oats 35.9
a
To convert Kg/ha to lbs/ac mL•ltiply by 0.892.
Because continued soil tests by the SCS had begun to suggest a strong
association between bareness and potash deficiency, it was decided that a
high potash fertilizer of the formula 6-6—12 would be used. In the initial
reclamation work a high nitrate fertilizer of the formula 38-0-0 had been
used. A total of 9.07 tonnes of 6-6-12 fertilizer was appl 4 ed to ill of the
Sulphur and Boyd Smith Sites at the rate of 1121 kilograms per hectare (1000
lbs/ac).
Lime was applied at rates rangin9 from 8.9 tonnes per hectare (4 tons/ac)
to 17.8 tonnes per hectare (8 tons/ac) on reseeded areas of the Sulphur Site
as determined by soil tests (Figure 36). All remaining portions of both sites
were limed at the rate of 4.45 tonnes per hectare (2 tons/ac). In areas
inaccessible to a spreader truck, lime and fertilizer were spread by a tractor
drawn whirlybird spinner or by hand (Figure 37). All lime and fertilizer
application was done in May except for a few truckloads of lime delayed until
early June by wet ground.
Other work done as p4rt of the spring maintenance included reconstruc-
tion of a diversion at the Sulphur Site and placement of additional straw
bales for erosion control. The contractor furnished all materials and labor
and was paid at the rates shown 1 n Table 22.
A continuing improvement in vegetative cover was apparent over most of
the reclaimed areas during the sun iier of 1979. Notable areas of improvement
resultin 9 from the spring seeding were the lipple Area of Sulphur East and
in the vicinity of Tr-1 on both sides of the creek. Numerous varieties of
weeds continted to invade the Large Area of Sulphur East along with at least
two species of trees. Of the grasses sown, the Ky-31 fescue continued to be
67
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SULPHUR SITE
LEGEND
RoaDs
WOODS
— DIvr ks.oNs
STREAMS
BUILDINGS OR FOUNDATIONS
CONTOURS
SIEDED
FiGURE 36. SEEDING WORK — SPRING 1979
-. -.
__ I.s ’ 3
S .1 ___ - — — —
—. s Iisd1OOO p
—
t
4 .I .
/
‘
-------
the mainstay with the lovegrass making its usual good shoring in mid-sumer.
Both varieties of lespedeza showed only moderate succers. Parts of the
Tailing Area of Sulphur West, the North End of Sulphur Edst and some of the
stream banks still supported 1ltt1e or no vegetation and obviously remained
highly toxic.
TABLE 22. MAINTENANCE COSTS - SPRING 1979
10 tons fertilizer 0 $16.50/ton $1165.00
46.46 tons lime @ $18/ton (truck spread) 836.28
9.7 tons lime @ $30/ton (hand spread) 291.00
2.1 acres seeded and mulched 0 $395/ac 829.50
43 ctraw bales 0 $2.50/bale 107.50
Regrading diversion (lump sum) 150.00
Total $3379.28
Although precipatation was generally abundant throughout Virginia during
most of 1979, only 1.88 centimeters of rain fell on the project site in July.
When the dry weather threatened the survival of the new grass and began to
take its toll on some of the established parts of Sulphur West, the SCS recom-
mended irrigation at once. The same contractor who had done the fall of 1978
irrigation was hired, and five applications of water were made to critical
areas during August (Figure 38). The irrigation along with itiore normal rain-
fall during late summer maintained mi ch of the grass on Sulphur West that
would probably have died. Cost of irrigation was as follows:
Setup of equipment $225
5 applications 0 $45/application 225
TOTAL $450
69
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Figure 37. Spreading lime by hand at Boyd Smith Site.
FIgure 38. IrrIgation of Sulphur Site.
70
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FALL 1979
Essentially the same maintenance was performed in the fall as had been
done in the spring except that sludge was again applied to some of the problem
areas that persisted. A small portion of the Boyd Sniith Site which had re-
mained barren and had started to encroach upon established vegetation was
reworked. No seeding had been done at this site since the fall of 1977. Lime
and fertilizer were applied in early September to all of the Sulphur
Site and that portion of Boyd Smith Site seeded as indicated in Table 23.
TABLE 23. lIME AND FERTILIZER APPLICATION - FALL 1979
Lime tonnes/bad
Sulphur East
Upstream Flat 17.8
Large Area 8.9
Tipple Area 17.8
North End 17.8
Sulphur West
Tailing Area 22.25
Tr-1 8.9
Boyd Smith 22.25
Total 82.18
Fertilizer
Formula 6-0-12 b
Rate 1121 Kg/ha
Total 6.35 tonnes
a
To convert tonnes/ha to tons/ac multiply by 0.449.
b 10 convert Kg/ha to lbs/ac multiply by 0.892.
Approximately 308 tonnes of sludge were delivered from the Blue Plains
SIP and stockpiled at t ie Sulp iur Site during August. After liming and
fertilizing was complete, sludge was hauled with a dump truck to areas to
be reseeded at each site and spread with a loader (Figures 39 and 40).
Although this did not incorporate the sludge to the depth normally desired
and In fact left much of It at the surface, it appeared that the seed ger-
minated quite well. Also the limited amount of sludcjr used at this time
minimized its possibility of being washed into the stream. An estimate
of the rdte per hectare over the widely scattered small areas is difficult
to make, but based upon the 0.73 hectare seeded, it would be about 82 dry
tonnes per hectare (37 tons/ac). Seeding and mulching was completed in
early October and dilapidated straw bales were replaced. Seed species
and rates are given in Table 24.
71
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SULPHUR SITE
-., ‘4
--.
r%) -
/
LIG(NO
ROADs
WOODs
DIVERSIONS
STREAMS
BUILDINGS OR FOUNDATIONS
CONTOURS
SI I D(D
SLUOGID
-
“p
I -
I
- -
- (S
FIGURE 39. SEEDING WORK — FALL 1979
—
.. ‘-
-.-.--.
-;: — - -
•1
a-
/
IIUUI ___ .r—IL ___ IIIIuI ’•I ,
S
-------
BOYD SMITH SITE
WOODS
p— e STREAMS
CONTOURS
SEEDED
SLUDGED
FIGURE 40. SEEDING WORK FALL 1979
230
IIIIIIIIUL.. J IIIUUIIUL....JUIIUUIIJ FIET
‘ TENS
0 4S
,,#1’
CONTRARY CREEK
73
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TABLE 24. SEEDING - FALL 1979
Species
g/ha 8 _
T I1 Fescue
67.3
“Tolerant” Red Fescue
11.2
Weeping Lovegrass
2.2
Wheat
67.3
a
To convert Kg/ha to lbs/ac multiply by 0 892.
The ?tolerart° red fescue was added to the seed formula because it rod
been used in the reclamation work at the Arminius Site and had appeared çuite
successful. At the recomend3tjon of the SCS, no legume was include.J, but
Korean’ lespedeza was nand sown over the same areas in February of H80.
Itemized costs of the maintenance work are presented in bole 25
TABLE 25. MAINTENANCE COSTS - FALL 1979
88.6 tons lime @ $20/ton (truck spread) 1772.O0
2 tons lime @ $40/ton (hand spread) 80.00
7 tons fertilizer @ $116.50/tort 815 50
1.8 acres seeded @ $500/ac 900.00
Spreading sl .dge @ $45/hr 990.00
36 straw bales $2.50/bale 90.00
Repairing access road 40.00
Towing sludge truck 30.00
TOTAL $ 717.50
The fall of 1979 maIntenance was one of the more successful endeavors in
the project. By late fall the g -ass cover over the entire Sulphur Site looked
as good as t ever had and new grass had sprouted on most of the reseeded are’s.
One notable area of pronounced impro en ent was the North Ei id of Sulph’jr East.
The continued use of sludge was undoubtedly a factor along with abundant
rainfall in germinating the new grass and the high potash fertilizer may have
74
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begun to have some effect.
SPRING-FALL - 1980
lime and fertilizer were again applied to all of the Sulphur and the
north side of the Boyd Smith Site In April and September of 1980. On both
occassions lime was applied at the rate of 8.9 tonnes ‘er hectare (4 tons/ac)
and fertilizer was applied at the rate of 1121 kilograms per hectare (1000
lbs/ac). Fertlizer of the type 6-0-12 was used in the spring work, but
after soil tests In August showed a decline in phosphate availability, 6-6-12
fertilizer was again used In the fall maintenance.
Abundant rainfall during April and May promoted a vigorous growth of vegetation
aver most of the reclaimed areas, but the sudden oiset of another drought in
June necessitated resumption of irrigation. Six applications of irrigation
during July were essential in preserving vegetation on critical portions of
the Sulphur Site. The 1980 drought did minimal damage to the overall project,
but prohibited any significant gains in establishing vegetative cover during
this growing season. A suniiiary of the 1980 maintenance costs is presented in
Table 26. At the request of the SWCB In the suniuer of 1980, the EPA ap-
proved an extension of the project until 1982 to provide for furthur mainte-
nance.
TABLE 26. MAINTENANCE COSTS -1980
Spring
78.25 tons of lime @ $22! ton $1721.50
8 tons of fertilizer @ $16.50/ton 932.00
Hand seeding 30 lbs. lespedeza (lump sum) 33.0O _
Subtotal $2686.50
Sumer
Setup of irrigation equipment $250.00
Six applications @ $60/application 360.00
Subtotal $610.00
Fall
77.52 tons of lime @ $22/ton $1705.44
8.5 tons of fertilizer 0 $26.65/ton 1076.52
Subtotal 2781.96
Grand Total $6078.46
75
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SECTION 8
ARMINIUS SITE RECLAMATION
In terms of size and disturbance of natural conditions, the Arminius
Site was intermediate to the Boyd Smith and Sulphur Sites. Approximately 4
hectares were disturbed at this site. Tailings covered the denuded areas on
both sides of Contrary Creek, but the natural topography was not altered
significantly (Figures 41 and 42). For purposes of this report the part of
Arminius Site on the east side of Contrary Creek shall be known as Arminlus
East and that on the west as Arrninlus West. Four old settling ponds remain
on the north side of Arminius East (Figure 43).
As stated earlier In this report, Callahan Mining Corporation had agreed
to reclaim this site and reclamation was expected to start more or less con-
currently with the work at Boyd Smith and Sulphur. After there was some delay
In Initiating the work at Arminius, the SWCB Issued a Consent Order to Callahan
requiring that steps be taken to abate the AMD from the Arminius Site.
Callahan began work on Arminlus West which consists of about 1.2 hectares
in the fall of 1976 and work began on Arminius East in the spring of 1977 which
Involved approximately 2 hectares. No reclamation work was done on the old
settling ponds at Arminius. All of the reclamation work at the Arininius Site
has been under the direction of a private consultant who had begun test plot
studies at that Sitd in 1974 using various application rates of soil additives
and seed types. The results of these experimental test plots are discussed
in Appendix D. The original reclamation work and postreclamation maintenance
was performed by local contractors and a major portion of the work was perform-
ed by the same contractor that did the maintenance work at the Sulphur and
Boyd Smith Sites.
The reclamation measures implemented at the Arminius Site have been
essentially the same as those used at the other two sites downstream with
the exception of some variation In application rates of soil additives and
seed types. As at the Sulphur and Boyd Smith Sites, spoil areas were regraded,
stream banks riprapped, and soil additives were applied including lime,
fertilizer and wastewater sludge. Sludge for this site was hauled from the
same source, the Blue Plains SIP in Washington, D.C. Sludge was applied at a
considerably lower rate per hectare and lime application rates varied from
those used at the Boyd Smith and Sulphur. Only a few small portions of the
site were fertilized.
The results of the reclamation work at the Arminius Site have been very
similar to that at Boyd Smith and Sulphur. The drought of 1977 of course had
its narsh effects on this site too, and there were some very toxic areas to be
76
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Figure 41. Barren areas of Anninius East prior to
reclamation.
FIgure 42. Mine tailings along Contrary Creek at
Anninius West prior to reclamation.
77
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-
Figure 43. Arminlus Site after recla.atlon-FalI 1978.
-------
dealt with here as at the Sulphur Site. A maintenance program consisting
of spring and fall seeding similar to that at Boyd Smith and Sulphur along
with application of additional lime and sludge and placement of riprap for
erosion control has been carried out at this site. By late 1980 most of the
reclaimed areas had a fairly good cover of vegetation Including some of the
same grass species used at the other two sites along with other plantings
which have been quite successful. However, the hot dry sumer of 1980
seriously affected some parts of this site and It is likely that some further
reseeding will be necessary. It is anticipated that a detailed report of the
reclamation at this site will be prepared by the consultant for Callahan
Mining Corporation.
79
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SECTION 9
POSTRECLANATION CONDITIONS
This section presents an evaluation of postreclamation conditIons at the
project site from the standpoint of vegetative cover, erosion control, soil
analyses, water quality, and biologic studies. Vegetative cover has been
evaluated by periodic Inspections by SCS and SWCB personnel along with aerial
photography by the VDH&T. The SCS used the universal soil loss equation to
estimate degree that erosion had been reduced, and soil tests have been con-
ducted regularly by the SCS and SWCB. All water quality data except a special
study by the University of Virginia have been generated by a comprehensive
monitoring program still being conducted by the SWCB. Biologic studies have
been conducted by the SWCB and are still in progress.
VEGETATIVE COVER
As related in Sections 6 and 7 the establishment of vegetation on the
reclaimed mine sites has been slow and difficult, especially at the Sulphur
Site, and the droughts of 1976 and 1977 could not have come at a less opportune
time. There was really no appreciable success until the sumer of 1978.
Another dry sumer in 1980 continued to hinder vegetative growth.
The aerial photos In Figures 44 — 47 compare conditions at both sites
before reclamation started and in the sumer of 1980. The photos show that
the potential f ’r erosion was reduced considerably. A general evaluation of
conditions in late 1980 Is presented In Table 27. The Boyd Smith Site (Figures
48 and 49) supports the most dense grass mat of any of the SWCB reclaimed areas
and the Large Area of Sulphur East had the most diverse vegetation (Figures 50
and 51). The more difficult areas have been the Tailing Area of Sulphur West
(Figures 52 and 53), the North End of Sulphur East, and the stream banks at
that site.
The Ky-31 fescue grass has been the mainstay of the vegetation. This
cool—weather grass has established quite well over about 75 per cent of the
Sulphur Site (Figure 54) and covers better than 90 per cent of the Boyd Smith
Site. As would be expected it makes its best showing in the spring and fall,
but becomes dormant during hot dry weather and begins to die out If prolonged
drought occurs. However, It usually greened up within a few days after
substantial rainfall or when Irrigation was applied. The ability of the
fescue to reach maturity and reseed itself has undoubtedly contributed to its
success on the reclaimed mine sites.
The second most successful species has been the weeping lovegrass which
is drought tolerant and has proven invaluable during the dry weather that has
plagued the project. Dunng the sumer of 1977, the first year it was planted,
80
-------
FIGURE 44. SULPHUR SITE — BEFORE RECLAMATION
-------
FIGURE 45. SULPHUR SITE IN 1000
-------
FIGURE 41. BOYD SMITH SITE-BEFORE RECLAMATION
FIGURE 47. BOYD SMITH SITE IN 1980
83
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TABLE 27. EVALUATION OF VEGETATIVE COVER IN LATE 1980
Per Cent of
Werk Area Size (haja Grass Cover General Conditions
Sulphur East
Upstream Flat 0.55 90 moderate cover, weeping lovegrass dominant,
some areas difficult to establish because
of poor drainage
Large Area 2.20 95 good cover exc ’t along stream banks • Ky-31
dominant, nIm, rous varieties of weeds and some
trees Invading
Tipple Area 0.75 90 moderate cover. Improved during 1979 and 1980,
y 3 1 dominant
North End 0.85 90 wnderate cover, considerable improvement In
1q80
Sulphur West
Tailing Area 1.15 85 good cover on northwest half of area, moderate
cover on romainder, some bare spots rear banks
very toxic, Ky-31 dominant with scattered
patches of lespedeza
Tr-1 0.41 85 moderate cover, much Improved in 1979,
X 31 dominant
Boyd Smith 2.03 98 heavy cover except for small areas on southeast
end of site, y-31 dominant, weeds and trees
lnvad,rg
a
To convert hectares to acres multiply by 2.471
-------
Figure 48. Boyd Smith Site - Spring 1977.
Figure 49.
Same view as Figure 48. - Suimier 1980.
85
-------
Figure 50. Large Area of Sulohur East - Spring 1977.
Figure 51.
Same view as Figure 50 - Sumer 1080.
86
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Figure 52. View of Tailing Area of Sulphur West with
Tipple Area of Sulphur East In foreground - Spring 1977.
FIgure 53. Same view as Figure 52 - Sumer 1980.
Compare both figures wIth Figure 6.
87
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It was virtually the only planting that showed any degree of success and it
undoubtedly prevented considerable erosion on large portions of Sulphur East
until other vegetation could become more established. Even wJien the lovegrass
became dormant in winter, the dry tussocks continued to abate erosion (Figure
55). The lovegrass has been retained in the seed formula since 1977 and the
established growth continues to thrive over much of the Large Area and Up-
stream Flat of Sulphur East.
Both Korean and sericea lespedeza have been u:ed in the seed formula
at various times since the reclamation began. These legumes have been moder-
ately successful in a few scattered spots but neither h s yet matured enough
to reseed Itself during a growing season. Red top and ladino clover were
tried during the first few years of reclamation, but they were dropped from
the seed formula after they failed to show any appreciable degree of success.
Numerous varieties of weeds including foxtail, fall panicum, and smart—
weed began to invade the Large Area of Sulphur East a, ,d the Boyd Smith Site
In 1978 and continued to flourish in the sumers of 1979 and 1980 and spread
to other areas. One of the more encouraging notes was the appearance In the
suniner of 1979 of at least two species of trees In significant numbers on the
Large Area of Sulphur East and the Boyd Smith Site. The most abundant species
s a variety of poplar which attained heights of about 0.5 meter the first
year.
The general appearance of the stream channel along the upper reach of
the Sulphur Site has improved since the reclamation began mainly due to the
expanding growth of white grass along the water’s edge each sumer. This
grass grows naturally and is apparently highly ac’d-tolerant. A few clusters
of cattails also began growing in 1978.
The overall assessment of the vegetative cover Is that gains continue
to be made each year, but it must be realized that there have been only two
normal growing seasons since reclamation began. Some of the better areas
appear on their way to reverting back to the natural wildlife habitat of the
surrounding environs, but other sparsely covered areas with a very thin soil
layer supporting vegetation will remain highly vulnerable to drought. Lime
and fertilizer should be applied for at least two more years and some of the
more toxic areas may need spot seeding. It will probably be several years
before a full evaluation of the vegetative cover can be made. It Is antici-
pated that the Glatfelter Pulp Wood Company will again plant pine seedlings
on the Sulphur Site once vegetation is more stabilized.
EROSION CONTROL
The Louisa County SCS Field Office used the universal soil loss equation
to estimate the degree to which soil loss In tons per acre per year has been
reduced on the grassed areas since reclamation began. The soil loss equation
was developed by the SCS from rainfall, runoff, and soil loss data collected
from 37 research stations over 21 states and has been adapted for use In Vir-
ginia as a method for predicting soil loss from sheet erosion. The equation
is as follows:
88
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Vigorous growth of Ky-31 fescue on Large
Area of Sulphur East - Suniner 1979.
FIgure 55. Weeping lovegrass on Upstream Flat of
Sulphur East Fall 1979.
FIgure 54.
89
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A KRI.SCP
where
A average annual predicted soil loss In tons per acre per year
K soil erodibility factor
R rainfall factor
L length of slope factor
S per cent of slope factor
C cropping management factor
P erosion control practice factor
The following are constants for both before and after grass establishment:
K .49
R 175
P = 1.0
The following values are used for the cropping management factor (C) according
to the cover condition:
No vegetation — 1.0
Fair — 0.01
Good - 0.006
Excellent - 0.004
I and S values were determined by field measurements. The average annual
predicted soil loss (A) computed from the above equation for the various
reclamation areas along with the slope factors (L S) and cropping manaqement
factor (C) are shown In Table 28. On the basis o these computations, It
appears that soil loss has been reduced In excess of 99 per cent at all of the
reclamation areas.
SOIL ANALYSES
As part of the monitoring program various soil analyses have been conduct-
ed to determine lime and fertilizer requirements and to compare prereclamation
and postreclacnation conditions. Initially, composite samples were collected
only from Sulphur West, Sulphur East and Boyd Smith, but as specific problem
areas became apparent, additional samples were collected to compare covered
areas with bare spots and at various depths. Refer to Figure i3on Page 35
for locations of various collection areas at the Sulphur Site.
The SCS collected composite samples for determiniation of pH and nutrient
availability prior to reclamation and have repeated the tests periodically
since reclamation. Samples were collected with a soil auger at a depth of
around 5 centimeters unless Indicated otherwise. All of the SCS samples were
analyzed by t Cooperative Extension Service at VPI&SU inBlacksburg, Virginia.
Table 29 shows pH and nutrient status of samples collected In 1975 before any
reclamation and In 1976 after initial reclamation.
The tests conducted in September 1976 a few months after the first soil
90
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additives had been applied Indicated dramatic increases In pH and same Im-
provement In nutrient availability 1 but another test in November 1976 showed
a sharp drop in pH. Tables 30-32 gIve sumarles of sludge, lime, and ferti-
lizer applications at the project site since reclamation began. Subsequent
tests by the SCS are discussed later in this section.
TABLE 28. SOIL LOSS EQUATION FACTORS
FOR BEFORE AND AFTER RECLAMATION
Area
I. S Factora
Before After
C Factors
Before After
A (tons/ac/yr)
Before
After
Sulphur West
0.35
0.35
1.0
0.006
30.01
0.18
Tailing Area
Tr—1
0.75
0.75
1.0
0.006
64.31
0.39
Sulphur East
Upstream Flat
0.10
0.10
1.0
0.004
8.58
0.05
Large Area
2.2
1.55
1.0
0.006
188.65
0.53
Tipple Area
3.80
3.80
1.0
0.006
325.85
1.96
North End
0.30
0.30
1.0
0.006
25.73
0.15
Boyd Smith
0.65
0.65
1.0
0.004
55.74
0.22
a
Determined by multiplying length of slope by per cent of slope. It Is
assumed that these factors were the same before and after reclamation
except in the Large Area of Sulphur East where a diversion was constructed.
b 1 • 0 no vegetation, 0.006 good cover, 0.004 = excellent cover.
91
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TABLE 29. SOIL DATA - SCS
pH - NUTRIENT AVAILABILITYa - 1975-76
Area - Date p 11 CaO
MgO
P Oc
K 2 0
Sulphur West
11-75 2.4 1-
9-76 6.0 VH
11-76 3.8 VH
I i
VH
VH
L-
VH
VH
L-
H-
M
Sulphur East
11-75 2.2 VH
9-76 5.6 VH
11-76 3.1 VH
VH
H
H
1-
VH
VH
1-
H
II-
Boyd Smith
11—75 3.1 1—
9-76 6.1 VH
11—76 5.4 VH
H+
VH
VH
1-
VH
VH
L-
I
L—
a
VH - very high H - high M- medium
L-low
TABLE 30. SUMMARY OF SLUDGE
APPLICATION
Total tonnesa Avg.% Total tonnes
Year (wet) Solids — (dry)
1976
Sulphur 5443 22 1197
Boyd Smith 1814 22 399
Total ha
Sludged
4.6
2.0
Tonnes/hab
...Jdrv)
260
200
1977 1769 19.9 352
1.6
220
1978 544 20.3 110
0.8
138
1979 C 308 19.5 60
TOTAL 9878 2118
0.7
82
a
To convert tonnes to tons multiply by 1.1023.
bTo convert tonnes/ha to tons/ac multiply by 0.449.
CIncludes a very small portion of Boyd Smith Site, but no breakdown Is made.
92
-------
TABLE 31. SU U4ARY OF LIME APPLICATION
RATES - 1976 - 80 (tonnes/ha)a
Area
Size b
(ha)
Si er
1976
Spring
1977
Fall
1977
Spring
1978
Fall
1978
Spring
1979
Fall
1979
Spring & Fall
1980
Total
Sulphur East
Upstre Flat
0.41
8.9
31.2
11.1
8 9 d
17.8
8.9
95.7
Large Area
2.23
8.9
13.4
22 . 3 c
33 4 C
8.9
8.9
109.2
Tipple Area
0.57
8.9
13.4
22.3
22.2
17.8
17.8
8.9
120.3
North End
0.72
8.9
13.4
22.3
22.3
89 d
17.8
8.9
111.4
Sulphur West
Tailing Area
1.17
8.9
22.3
22.3
22.3
11.1
8.9d
22.3
8.9
135.9
Tr-1
0.32
8.9
31.2
33.4
17.8
8 9
8.9
118.0
Boyd SmIth
2.03
8.9
13.4
2 • 3 e
8 9
56.9
a
To convert tonnes/ha to tons/ac iltiply by 0.449.
bTO convert hectares to acres multiply by 2.471.
CStre si banks only.
dBare spots only. r ,inder of each area receIved 4.5 tonnes/ba.
0 Seeded areas only.
iorth side only.
-------
TABLE 32. SUMMARY OF FERTILIZER TYPES AND APPLICATION
RATES — 1976 - 80 (Kg/ha)a
a
To convert Kg/ha to lbs/ac multiply by 0.892.
bTo convert hectares to acres multiply by 2.471.
CStre banks only.
d 0 4 05 hectare (1 ac) of each area was treated with 16-7-12 and 18-18.6, respectively.
0
Area
Size
(ha)b
Simmer
1976
Spring
1977
Spring
1979
6-6-12
Fall
1979
6-0-12
Spring
1980
6-0-12
Fall
1980
6—6—12
10-10-10 38-0-0
10-10-10
38-0-0
16-7-12
18-18-6
Sulphur East
Upstream Flat
0.41
1121 448
897
1121
1121
1121
1121
Large Area
2.23
1121 448
561
448 c
336 d
336 d
1121
1121
1121
1121
Tipple Area
0.57
1121
561
1121
1121
1121
1121
North End
0.72
1121 448 c
561
1121
1121
1121
1121
Sulphur West
Tailing Area
1.17
1121 448
561
448 c
335 d
336 d
1121
1121
1121
1121
Tr-1
0.32
1121 448
897
1121
1121
1121
1121
Boyd SmIth
2.03
1121
561
33 (
336 d
1121
1121
1121
1121
-------
Composite soil samples were also collected in the same manner by the
SWCB and analyzed by the DCLS to determine lime requirements by titration
and metals content using special tests prescribed by the EPA Project Officer.
Procedures are described in Appendix B. Table 33 shows initial pH and lime
requirements for the various work areas from 1976 to 1979 as determined by
titration.
The results of the soil analyses were used as guidelines for developing
the specifications for lime application rates during each period of mainte-
nance. Where repetitive samples were collected from the same area, It can
be seen that lime requirements varied considerably. Note that the sample
collected from the Tailing Area of Sulphur West in March 1979 was from the
barren or most severe area and did not necessarily represent conditions over
the entire area. From the pH and lime requirement data, it appears that soil
conditions Improved appreciably at Tr-1 on Sulphur West during 1978. rhl
has been one of the most severe areas to work with since the project begun.
In general, the pH of the soils as been raised and lime needs appear to have
declined, but some areas, particularly the Tailing Area and the North End
of the Sulphur Site, will probably require heavy liming for sometime to main-
tain vegetation.
Table 34 shows metal analyses of composite soil samples collected over
the entire project area. It can be seen that there Is a wide range In metals
content over the various areas, but a very pronounced decrease in metal con-
centrations occurred in some of the worst areas in 1978 and 1979. This un-
doubtedly resulted from the continued heavy application of soil additives and
indicates less toxic soil at the surface over much of the reclaimed areas,
but it is likely that the underlying material is still heavily laden with
metals.
At the request of the EPA Project Off ic r a special se of samples was
collected In March 1978 and sent to the soil testing laboratory at West Vir-
ginia University to determine total potential acidity, lime requirements, and
nutrient availability. The results are shown in rable 35. See Table 33 for
a comparison of lime requirements. Note the extremely low availability of
potassium In some areas of the Sulphur Site.
During 1979 the SCS collected three sets of composite soil samples for
continued study of nutrient availability. The first collection made in March
(Table 36) was concurrent with a collection made by the SWCB for titration
tests and metal analyses (Tables 33-34), and samples were split from the
same borings. Numerical values of nutrient availability in pounds per acre are
Included in Table 36. Note the extremely low availability of potash (1(20) in
all areas except the Large Area of Sulphur East and the Boyd Smith Site. The
lowest potash availability was on the Tailing Area of Sulphur West and on the
stream bank opposite Tr-1 and the North End of Sulphur East, all of which
have been difficult to vegetate.
Another set of samples collected by the SCS in July 1979 (Table 37)
showed the same general trend in potash deficiency, and comparisons between
grassy and barren spots of the Tailing Area and the Tipple Area revealed
slightly higher potash where grass was growing. This was after the applica-
95
-------
TABLE 33. SOIL DATA - DCLS
pH, LIME REQUIREMENT BY TITRATION CURVE
Accumulative total
Lime Required to of lime applied
attain pH of 6 5 prior to each test
Area - Date Initial pri ( tonnes/ha) ( tonnes/ha )
SULPHUR WEST
Tatflno Ar
11-76 4 1 21.6 8 9
6-77 3.1 40.1 31 2
3-78 5.1 240 53 5
6-78 5.9 46 758
4.5 40.1 84 i
Tr-1
11-76 3.7 30.5 8.9
11 _7 6 b 3.9 50.1 8.9
3-78 3.6 34.3 40 1
3-79 6.5 11.1 40 1
SULPHUR EAST
Opposite Tr-1
6-78 2.7 42.7 44 6
Stream Bank of
Large Area
-79 4.5 31.2 66.9
pstream Flat
11-76 7.3 0 8.9
3-78 6.7 0 40 1
7—78 5.7 5 3 40.1
3-79 5.4 18.5 51 2
Large Area
11-76 5.5 13.4 8.9
3-78 7.3 0 22.3
Tipple Area
3-78 3.2 36.6 22.3
6-78 3.0 40.7 44.6
3-79 5.9 22.3 66.9
North End
3-79 5.7 28.9 66.9
BOYD SMITH
11-76 5.4 7.8 8.9
a
bBare spots only.
Dark material only.
96
-------
TABLE 34. SOIL DATA - DCLS, pH AND
METALS ON DRY WEIGHT BASIS (mg/kg)
Area-Date pH Cu Fe Pb Mn Zn Al
SULPHUR WEST
Tailing Area
11-76 4.1 50 30 ND 6 74 262
6-77 3.1 62 34 .- 17 82 132
3-78 5.1 0.1 7.8 0 2 6.8 6.6 1 0
6-78 5.9 1.0 24 0.2- 3.6 1.5 2 4
3_79C 4.5 3.2 7.6 0 01 6.4 28 0 1.0
2-80 4.9 0.2 0.4 0.2- 2.6 3.4 1.0-
Tr- 1
1T-76 3.7 288 220 4.6 152 3940
1176 d 3.9 820 160 5.4 236 5200
3-78 3.6 226 340 2 4 7.4 366 32
3-79 6.5 0 9 0.2- 0.002 2 9 1.6 1 0-
2-80 5.3 0.6 0.6 0.2- 4.8 17.8 2.0-
SULPHUR EAST
Opposite Tr-1
6—78 2.7 66 1600 2.4 7.2 252 324
3-79 5.9 0.9 0.2 0.011 3.8 11.0 1.0-
2-80 4.7 1.1 1.2 0.2- 6.0 18.6 2.0-
Stream Bank of
Large Area
3—79 1.2 3.6 0.011 0 6 21.6 1.0
2-80 3.8 4.6 10.4 0.2- 3.8 15.4 4.0
Large Area
11-76 5.5 8.6 4.2 MD 31.4 18.8
3-78 7.3 0.3 6.2 0.2 0.5 0.1 2.0
3-79 5.9 0.3 3.6 0.005 1.9 1.2 1 0-
2-80 5.2 0.2 0.8 0.2 1.7 3.4 2.0-
Upstream Flat
11-76 7.3 2 ND MD 31.6 54
3.78 6.7 0.1 5.0 0 2 6.6 4.0 1.0-
7-78 5.7 1.0 5.0 0.2- 14.4 3.2 3.2
3.79 5.4 1.9 0.6 0.014 25.9 150 1.0-
2-80 5.5 0.6 0.8 0.2- 12.2 12.8
(continued)
97
-------
TABLE 34. (contInued)
Area-Date pH Cu Fe Pb
Mn
Zn Al
Tipple Area
3-78 3.2 5.0 80 0.2
0.8
6.2 6.6
6.78 3.0 28 620 0.2-
3.0
24 100
3-79 5.9 0 1 0.6 0.001
3.9
2.0 1-
2-80 4.7 1.1 4.8 0.2-
4.6
10.2 2-
North End
3-79 0.2 0.8 0.008
2.2
3.8 1.0
2-80 4.9 0.1 0.4 0.2-
7.2
0.7 2-
BOYD SMITH
11-76 5.4 0 7 0.6 ND
30.6
19 6
6-78 7.1 0.3 1.0 0.2-
1.6
0.8 1.2
3-79 5.7 1.1 0.2 0.011
7.0
19 6 1-
2-80 5.0 1.0 0.4 0.2-
6.0
12.6 2-
a
kND-None detected. Detection Limit is 0.2 mg/kg
A (.) sign indicates that the concentration was
below
the
Indicated leve’
of
detect Ion.
Bare spots only.
dThjs sample consisted primarily of dark material
only.
98
-------
a
Pjltiply K by 1.2 to obt6in (20.
TABLE 35. SOIL DATA-WVU,
pH, LIME REQUIREMENT, NUTRIENT AVAILABILITy, TOTAL POTENTIAL ACIDITY - MARCH 1978
Maximum
S le Area L.Ra Kb
Amount
Max inxm
‘.O
0
Tailing Area
5.3
2.0
75
11.200
405
5.225
163.28
7.85
Sandwich Area
Tr-1
6.8
4.4
0
6.0
178
184
12,200
4,800
435
165
3.150
2.600
98.44
81.25
26.48
-9.55
155.43
71.96
Sulphur £e t
Upstream Flat
6.8
0
75
10,400
375
0.850
26.56
14.23
Large Area
6.7
0
164
13,600
450
2.450
76.56
29.90
12.33
46.66
Tipple Area
3.9
Lime requirement in tons/ac to acquire a pH of 6.5.
bAmonnt of acid extractable K in san le in lbs/1000 tons of material.
C unt of acid extractable Ca in san le in lbs/bOO tons of material.
of acid extractable Mg In san le In lbs/bOO tons of materiaL
eper cent sulfur in s le as detected by LECO induction furnace.
fp axig m amount of acid that can be produced from % sulfur present in sau 1e expressed in terms of CaCO 3
equivalents in tons/1000 tons of material. Derived by multiolying % S by 31 25.
9Amo mt of neutralizers present in sauple expressed in CaCO 3 equlvaler.ts In tons/bOO tons of material as
determined by the neutralization potential. Negative nunt)ers indicate the presence of free acid.
of neutralizers required to neutralize the maximun acidity possible from t S in tons/1000 tons of
material.
-------
TABLE 36. SOIL DATA - SCS, pH AND
NUTRIENT AVAILABILITY IN LBS/AC - MARCH 1979 a
Area
pH
CaO
Mgo
P 2 0 5
K 2 0
Sulphur West
3.7
3358
(VH)
207
(M+)
250+(VH)
12
(L-)
Tailing Areab
Tr-1
5.5
3358
(VH)
398
(VH)
247 (H+)
41
CL)
Sulphur East
4.9
3358
(VH)
398
(VH)
250+(VH)
26
(L)
Opposite Tr-1
Stream Bank
of Large Area
4.6
3358
(VH)
398
(VH)
224 (H+)
8
(L-)
Large Area
5.3
3358
(VH)
398
(VH)
137 (H)
154
(M)
Upstream Flat
Tipple Area
North End
4.8
5.1
4.6
3358
3358
3358
(.VH)
(VH)
(VH)
255
398
398
(H-)
(VH)
(VH)
250+(VH)
250+(VH)
250+(VH)
60
26
1
(L)
(L)
CL-)
Boyd Smith
6.0
3358
(VH)
398
(VH)
231 (H+)
298
(H)
a
VH—very high, H-high, M-medium, L-low.
baare spots only.
100
-------
tion of 6-6-12 fertilIzer in the spring of 1979 (Table 32) which was the first
fertilizer that had been applied since the spring of 1977. Note that pH was
around two units higher in the grassed areas than in the bare spots.
TABLE 37. SOIL DATA - SCS
pH 1 NUTRIENT AVAILABILITY - JULY 1979
Area CaO
Sulph’ir West
Tailing Area
Grass 4.4 VH VH H I
Barren 2.2 VH VH VH I-
Sulphur East
Large Area 5.9 V I I VH
Upstream Flat 3.7 VH VH VH L+
Tipple Area
Grass 4.6 VH VH VH
Barren 2.8 VH VH VII
North End 3.8 VH VI I L
Boyd Smith 5.9 VII VII H H
a
VH - very high, H - high, M — medium, I - low.
In October 1979 after application of more lime and 6-0-12 fertil 4 zer
(Tables 31—32) samples were collected on the Tailing Area of Sulphur West
and the Large Area of Sulphur East to compare soil conditions near the
surface and at depth in grassed and barren areas (Table 38). In the Tailing
Area it can be seen that pH was somewhat higher in the topsoil where there
was ground cover, but at depth the pH was Identical In grassed and barren
spots. Most of the nutrients tended to be lower at depth, but potash was
very low regardless of cover or depth. The Large Area of Sulphur East show-
ed the same general pattern of pH, but nutrient availability was generally
higher near the surface. The sample collected along the stream bank opposite
Tr—1 with the extremely low pH of 1.1 consisted primarily of pyritic material,
but Interestingly It was not the most nutrient deficient.
Continued soil analyses conducted In 1980 showed a marked improvement
between March and August (Table 39) In pH and potash availability over all
areas, but there was a decrease in phosphate (P 2 05) availability. Fertilizer
101
-------
TABLE 38. SOIL DATA - SCS, pH
NUTRIENT AVAILABILITY - OCTOBER 1979 a
Area
Depth
(cm)
pH
CaO
MgO
P 2 0 5
K20
Sulphur West
Tailing Area
Grass
5
61
3.6
2.5
VH
VH
11+
M-
VH
M-
L-
L—
Barren
5
46
2.9
2.5
VH
VH
L
H-
VH
L+
1-
1—
Sulphur East
Large Area
Grass
5
30
5.0
3.2
VH
L+
11+
1-
N
L
H-
L+
Barren
46
2.9
L+
VH
L
L
Opposite Tr-1
Barrenb
0
1.1
N-
V I I
L
M
a
b VH-very high, H-high, N-medium, L-low.
Consisted primarily of pyritic material.
of the type 6-6-12 was again used in the fall of 1980.
In sumary, it appears that a viable soil cover is gradually being
established over most of the reclaimed areas, but there are still some very
toxic spots supporting no vegetation and in other areas the soil horizon
that does support vegetation is indeed very thin. A major unvegetated area
is the steep banks along the creek. Not only are they toxic, but lime,
fertilizer, sludge, and seed are difficult to apply and they erode easily.
Without the heavy application of lime, fertilizer and especially the sludge,
there would unquestionably be little If any vegetation growing on thetre—
claimed sites. It appears that potash availability Is a key limiting factor
in the e!tablishmeflt of vegetation In areas with adequate lime and sludge.
A high potash fertilizer should be used for any future maintenance. The
thin mantle of growth supporting media overlying the toxic mine wastes
102
-------
TABLE 39. SOIL DATA - SCS, pH AND NUTRIENT
AVAILABILITY IN LBS/AC - l 98 O
Area
pH
P 2 05
K20
Mar
Aug
Mar
Aug
Mar
Aug
Sulphur West
Tailing Area
3.0
6.1
275(VH)
32(M-)
7(L-)
124(M)
Barren Spots
3.1
275(VH)
38(L)
Tr-1
4.4
6.3
275(VH)
32(M-)
75(L+)
155(M)
Sulphur East
Large Area
4.1
6.6
275(VH)
32(M-)
117(M-)
124(M)
Upstream Flat
4.9
6.3
275(VH)
60(M)
147(M)
186(M+)
Tipple Area
5.5
5.7
160(VH)
209(M)
80(L+)
11O(M-)
North End
3.9
6.0
275(VH)
32(M)
34(L)
41(L)
Boyd Smith
4.1
6.2
275(VH)
128(H)
94(M )
275(H)
a
VH-very high, H-high, M-medlum, L-low
presents a condition that is very drought sensitive. Since the plant root
sy .cem is very shallow, short periods without precipitation result in plant
damage. Soil tests will continue to be conducted periodically to evaluate
progress toward a soil profile that will support permanent vegetation.
WATER QUALITY
A detailed water quality monitoring program began in October 1975 six
months prior to start of reclamation work and is still In progress. Until
early 1980 water samples were collected semi-monthly from five stream stations
and two lake stations except when inclement weather or manpower constraints
curtailed operations. In April 1980 the stream sampling was reduced to once
monthly and all lake sampling was discontinued. A brief .iescriptlon of each
monitoring station Is given below, and Figure 56 shows locations of the
stations.
103
-------
1 ; : /
S MS-CO MOI ITORING STATION
SSS-OO SAMPLING STATION.
A
1•. •
. I.!
4:
. ç
-)
,. . ..
-w /
1
_) .-•v
)
:
• - -‘
,• ‘r ‘— \ • - J • <4
; i r /’ t
NS-5 :\
/•
• -•
-‘S
I
I
FIGURE 56. CONTRARY CREEK MONITORING STATIONS
7, -I
-I
,1
I-
‘ S. ‘. .
“4
:
•
‘4 .
,,__ .1*t
V
-------
Stations Located on Contrary Creek —
MS—i Control station above all mine sites
MS-2 Below Arminlus Site
MS-3 Below Boyd Smith Site
MS-4 Below Sulphur Site
MS-5 Mouth of Contrary Creek just above Lake Anna
Lake Stations —
SS—i Contrary Creek arm of Lake Anna
SS-2 Juncture of Contrary Creek arm with main body
of Lake Anna
Surface, middle, and bottom samples were collected from each lake station
making a total of Ii samples for each collection. A list of the parameters
analyzed from the regular sampling follows.
pH Manganese
Acidity Zinc
Sulfate Suspended Solids
Copper Turbidity
Iron BOD (5-day)
Lead Fecal Coliform
SOD and fecal coliform analyses were included in the regular analyses to ascer-
tain if the use of wastewater sludge had any effects upon the water of the
stream. Analyses were conducted on the sludge itself during the main phase of
construction. For results see Table 9 on Page 46. Additional parameters in-
cluding some less coninon metals and some nutrients were analyzed at all sta-
tions at least once annually, and grab samples were collected periodically
from various tributaries at each mine site. A special study funded from the
EPA grant was conducted by the University of Virginia in 1978 to identify
specific sources and magnitude of AND along the stream and to determine the
effects of heavy rainstorms on stream chemistry. The SWCB followed this
study up with pH and specific conductivity transects during the suniner of 1979.
Results of the water quality monitoring will now be presented.
Stream Stations - Concent n and Load Data
All stream stations were equipped with automatic flow recorders except
MS-5 where flows were measured with a current meter. Mean annual flows for
the stations with continuous records covering five water years from 1976 to
1980 are shown In Table 40.
105
-------
TABLE 40. MEAN ANNUAL FLOWS (i/ 5 )a
Water
Year
MS-i
MS-2
MS-3
MS-4
1976
48.7
54.9
94.3
147.8
1977
32.6
36.3
62.6
94.6
1978
73.9
87.2
140.2
206.5
1979
66.6
82.4
140.5
198.8
1980
50.8
68.2
115.5
153.1
a
To convert 1/s to cfs multiply by 0.0353.
Tables 41 - 44 show average values of flows, concentrations, and loads
for key parameters at stream stations MS-i thru MS-4 by quarter for water years
1976 thru 1980. Table 45 gives average concentrations only for MS-5 where no
continuous flow data are available. Concentration values from the semi-
monthly samplings were averaged, and loads were computed by multiplying
average concentrations by the quarterly average daily flows. While this
method 0 f averaging loads does not fully reflect the effects of sudden flush—
Ings of AMD loads from the mine sites, it gives a general picture of seasonal
trends. It can be seen from the concentration and load averages that there
has been little overall change in water quality during the five—year period.
Concentrations and loads for some pollutants tended to e somewhat lower in
water years 1979 and 1980, but it Is too early to discern If an Improved trend
Is beginning to emerge. Some of the apparent decreases in loads may be more
attributable to lower flows during the dry suniner mor ths. The sharp Increases
in concentrations during the last quarter of water year 1980 were primarily
due to he very low flows during the sumer drought.
Comparing the quarterly concentration averages with the water quality
standards presented in Section 4, it Is apparent that acid and heavy metals
have consistently exceeded SWCB limits at most stream stations. For any
given quarter, pH usually averaged below the standard of 6.0 at MS—2, only e-
ceeded 6.0 once at MS-3, never exceeded 4.4 at MS-4, and only once averaged
as high as 4.0 at MS-5. Sulfate concentrations usually averaged above the
limit (250 mg/l) at all affected stations during low flow, and copper usually
exceeded the 1.0 mg/l limit at MS-4 and MS-S during the last quarter of each
water year. Lead often exceeded the limit of 0.05 mg/l at MS-4 and some-
times was above the standard at the other affected stations during low flows.
Zinc regularly exceeded the limit of 5.0 mg/l at MS-2 and MS-4 during low
flow periods and occasionally did so at MS-3 and MS-5. Iron and manganese
concentrations almost always exceeded standards, 0.3 mg/l and 0.05 mg/l,
respectively, at all stations Including the control MS-i Indicating the ubiq-
uity of these metals, but obviously the Sulphur Site Is the major contributor
of Iron. Manganese appears to increase most abruptly at t e Boyd Smith Site.
For a more detailed picture of pH and concentration;, a series of graphs
were constructed from the data In STORET to show ind1vI’ ual pH values and
concentrations determined from the semi-monthly sampling at each station.
106
-------
TABLE 41. SUMMARY OF WATER QUALITY
DATA BY QUARTER AT MS-i
2 j _ 2 3 4
Quarter _ _1
3 4
Flow (us)
pH
51.8
91.8
42.8
8.8
6.5
6.1
6.0
7.6
72.8
37.4
20.1
0.6
6.7
6.9
7.2
7.9
62.6
129.4
84.4
20.7
7.5
6.1
7.1
6.8
21.8
16i.4
68.3
17.3
6.4
5.6
6.6
6.9
62.4
95.3
37.9
6.5
6.6
6.1
6.7
6.9
Concentration
(mg/i)
Load
(kg/d)
15
9
10
26
10
6
4
27
119
5
10
38
291
9
5
65
112
59
7
15
363
12
ii
38
82
Sulfate
Water
Yeara
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
22
9
66
348
39
3
1
9
10
6
9 7 4
7 6 18
17 11 15
20 8 14
15 9 10
6
6
12
8
7
8
8
19
11
11
0.02
0.01
0.04
0.02
0.05
0.9
0.8
0.6
1.5
1.7
36
50
103
21
59
71
23
55
279
124
26 3
10 1
80 27
47 21
29 6
0.03
0.01
0.09
0.16
0.03
0.01
0.06
0.03
0.06
0.04
0.22
0.45
0.03
0.03
0.04
1.39
0.03
0.03
0.27
0.41
Iron
0.02
0.01
0.04
0.10
0.05
0.5
0.7
0.5
0.6
0.6
1.5
1.6
1.5
2.2
1.6
0.11
0.05
0.44
0.18
0.10
5.5
2.8
10.9
13.0
5.2
1.6
0.5
2.5
2.2
1.4
0.01
0.00
0.07
0.04
0.02
1.2
0.0
4.5
3.3
0.8
4.0
5.0
3.2
2.8
9.2
4.0
2.3
5.6
8.4
4.9
107
(continued)
-------
TABLE 41. (contInued)
Quarter
1
2
3
4
1
2
3
4
Water
Year
a
Concentration
(mg/i)
Load
(kq/d)
1976
1977
1978
1979
1980
0.009
0.016
0.003
0.008
0.007
0.004
0.010
0.007
0.018
0.006
Lead
0.03
0.02
0.05
0.04
0.02
0.03
0.00
0.02
0.01
0.01
0.007
0.012
0.007
0.006
0.005
0.039
0.003
0.013
0.005
0.011
0.04
0.10
0.02
0.02
0.04
0.03
0.03
0.08
0.25
0.05
1976
1977
1978
1979
1980
0.04
0.14
0.20
0.04
0.16
0.08
0.10
0.11
0.17
0.12
Manganese
0.6
0.2
0.8
0.7
0.3
0.0
0.0
0.3
0.1
0.0
0.16
0.12
0.11
0.12
0.08
0.04
0.24
0.17
0.07
0.07
0.2
0.9
1.1
0.1
0.9
0.6
0.3
1.2
2.4
1.0
1976
1977
1978
1979
1980
0.1
0.1
0.2
0.1
0.3
0.1
0.1
0.2
0.4
0.2
Zinc
0.3
0.2
1.2
1.8
0.3
0.0
0.0
0.3
0.2
0.1
0.1
0.1
0.2
0.3
0.1
0.0
0.2
0.2
0.1
0.2
0.2
0.4
1.1
0.2
1.6
0.6
0.2
1.9
5.6
1.6
a
A water year begins October 1 and ends September 30. 1st quarter, Oct. - Dec;
2nd quarter, Jan — March; 3rd quarter, April - June; 4th quarter, July — Sept.
108
-------
TABLE 42. SUMMARY OF WATER QUALITY
DATA BY QUARTER AT MS-2
Quarter 1 2
3 _4 1 2
3 4
Flow
(us)
pH
64.3
95.4
47.9
12.2
5.9
5.4
5.8
4.8
78.5
41.1
24.1
1.1
5.7
6.2
5.8
3.3
6 .9
156.6
102.5
26.3
4.9
5.6
6.6
5.8
2L’ 9
204.8
78.2
20.1
6.0
5.5
6.2
5.8
71.1
135.9
56.9
8.5
6.3
6.0
6.2
4.7
Concentration (mg/i)
Load
(kg/d)
Acidity
16 20 8 44
12 14 32 309
60 18 18 14
19 41 71 18
18 13 13 70
Sulfate
Water
Year
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
89
81
336
47
111
72
50
48
200
400
85
65
161
1052
577
93
42
64
115
521
114
49
57
109
285
61
45
68
491
375
Copier
165
50
244
725
152
412
231
568
867
529
0.91
0.36
1.49
1.95
0.94
10.7
6.7
17.6
17.7
21.1
33
167
159
480
64
199
335
567
385
334
0.37
0.52
0.97
0.54
0.29
9.5
5.0
12.4
12.8
4.9
0.09
0.30
0.56
0.25
3.02
1.15
0.11
0.13
1.1
0.08
0.09
0.27
0.06
0.36
0.55
46
30
32
32
51
211
100
261
189
361
0.32
0.29
0.30
0.16
0.26
3.9
0.7
3.9
2.3
1.2
0.10
0.17
0.20
0.11
0.09
2.0
3.0
1.9
1.7
1.8,
0.11
0.10
0.11
0.11
0.08
1.3
1.9
1.3
1.0
1.8
Iron
2.3
2.4
1.4
1.9
1.0
3.7
7.1
1.7
1.3
1.7
11.1
20.3
10.7
4.2
11.1
109
(continued)
-------
TABLE 42. (continued)
Quarter 1 2 3 4 1 2 3 4
Water
Year Concentration (mg/i) Load (k /d )
Lead
1976 0.013 0.018 0.019 0.075 0.07 0.15 0.08 0.08
1977 0.102 0.057 0.048 0.625 0 9 0.20 0.10 0.06
1978 0.030 0.015 0.020 0.029 0.17 0.20 0.18 0.06
1979 0.022 0.028 0.012 0.O1C 0.06 0.50 0.20 0.03
1980 0.019 0.006 0.014 0.096 0.12 0.07 0.07 0.07
Manganese
1976 0.52 0.39 0.43 1.57 2.9 3.2 1.8 1.7
1977 1.04 0.59 1.38 7.68 7.1 2.1 2.9 0.7
1978 0.47 0.36 0.59 0.86 2.6 4.9 5.2 2.0
1979 0.61 0.40 0.63 0.92 1.5 7.1 4.3 1.6
1980 0.51 0.41 0.59 1.49 3.1 4.8 2.9 1.1
Zinc
1976 4.4 2.8 3.1 12.9 24.4 23.1 12.8 13.6
1977 8.8 4.3 8.9 54.7 59.7 15.3 18.5 5.2
1978 3.5 2.7 3.5 8.6 19.6 36.5 31.0 19.5
1979 7.3 2.7 4.4 5.7 18.2 47.8 29.7 9.9
1980 5.1 2.7 3.4 21.0 31.3 31.7 16.7 15.4
110
-------
TABLE 43. SUMMARY OF WATER QUALITY
DATA BY QUARTER AT MS-3
Quarter 1 2 3 4 1 2 3 4
Concentration (mci/i)
Load (kci/d)
Flow (ifs)
PH
158.3
76.5
233.6
342.4
226.8
89.2
36.8
167.7
137.6
86.4
27.2
4.5
47.6
43.0
21 0
5.0
5.3
4.7
5.4
5.8
4.9
6.3
4.9
4.8
5.6
5.3
5.8
5.1
5.1
5.3
4.3
3.7
4.8
4.6
4.5
Water
Year
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
103.9
132.8
113.8
42.8
126.0
16
23
41
20
14
127
78
136
173
88
0.15
0.20
0.18
0.36
0.13
2.2
2.4
2.2
1.3
1.7
Ai..idity
10
31
27
75
17
40
81
20
23
27
144
264
403
74
152
233
132
404
1420
314
Sulfate
76
153
92
98
110
2 8
476
h2
125
269
1140
895
1337
640
958
1012
595
1251
1834
529
copper
17
20
20
48
16
74
90
62
62
27
0.15
0.16
0.16
0.15
0.12
1.7
1.9
1.8
1.5
1.8
0.39
0.15
0 1’
0.10
77
99
391
892
127
586
486
1333
11’
—a
3.0
0.5
2.4
1.7
0.7
57.8
4.5
21.7
23.8
11.9
94
31
82
85
49
583
185
790
464
488
0.8
0.3
0.5
0.5
1.1
3.3
0.5
5.3
4.1
1.8
0.32
0.74
0.13
0.14
0.58
I ron
1.4
2.3
1.8
1.3
1.4
2.1
1.1
3.2
4.4
2.4
7.5
1.4
1.5
2.0
1.6
1.4
1.2
1.3
1.0
1.0
19.7
27.5
21.6
4.8
18.5
23.3
12.6
36.3
44.4
35.3
[ contThued)
111
-------
TABLE 43. (contInued)
Quarter
1
2 3 4
1
2
3
- 4
Water
Year
Concentration (mg/i)
Load
(kg/d)
1976
0.026
Lead
1.50
0.10
0.25
0.05
0.015 0.200 0.105
0.23
0.21
1977
0.037
0.018 0.032 0.124
0.43
0.12
0.52
0.12
1978
0.033
0.023 0.036 0.029
0.32
0.46
0.27
0.10
1979
0.019
0.028 0.023 0.027
0.07
0.83
0.10
0.03
1980
0.021
0.015 0.014 0.019
0.23
0.29
976
1.50
Manganese
17.0
6.3
10.2
3.2
0.94 2.20 4.32
13.5
12.9
1977
1.33
1.40 1.97 8.16
15.3
9.3
18.1
7.8
1978
2.00
0.81 1.25 1.90
19.7
16.3
14.4
3.6
1979
2.25
0.50 1.21 2.32
8.3
14.7
11.0
6.9
1980
1.29
0.93 1.48 3.80
14.0
18.2
1976
1977
1978
1979
1980
3.9
4.0
4.2
4.0
3.4
Zinc
32.4
12.7
49.3
40.4
18.7
18.8
4.7
18.9
14.5
10.0
2.6 4.2 8.0
3.7 4.0 12.2
2.4 3.4 4.6
2.0 3.4 3.9
2.3 2.5 5.5
35.0
45.9
41.3
14.8
37.0
35.6
24.5
48.4
59.2
45.1
112
-------
TABLE 44. SUMMARY OF WATER QUALITY
DATA BY QUARTER AT MS-4
Quarter 1 2 3 4 1 2 3 4
244.7
147.0
43.6
4.0
4.0
4.4
3.2
109.3
59.8
14.2
4.1
4.4
3.7
2.9
355.4
239.3
72.5
3.5
4.1
3.8
3.4
478.6
181.2
66.3
3.6
3.9
3.7
3.3
287.2
123.8
37.1
4.0
4.3
3.8
3.0
Concentration
(mg/i)
Load
(kg/d)
Water
Year
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
1976
1977
1978
1979
1 8O
157.2
194.3
162.6
75.0
160.9
83
112
198
191
121
187
167
179
319
178
0.5
1.1
1.8
0.9
0.6
62
315
1127
171
621
1880
131
214
2782
292
200
1238
134
381
1682
Sul fate
141
483
2540
288
966
2804
212
400
2515
168
166
2067
200
525
2474
Copper
67
84
93
140
74
123
144
116
121
117
0.5
0.6
0.8
0.6
0.5
1187
762
1340
1146
1221
1819
1185
2506
951
1682
1417
793
2856
5789
1837
2600
1360
3562
5003
2903
10.4
5.5
24.9
23.2
12.4
787
884
2708
4571
1433
1791
1488
4384
2630
2139
8.1
5.7
18.4
11.0
5.3
0.6
1.1
0.9
0.7
0.5
2.1
4.3
1.1
1.0
1.5
Iron
7.2
18.5
25.3
6.0
8.3
1976
1977
1978
1979
1980
1976
1977
1978
1979
1980
24
37
43
37
16
16
26
18
18
20
340
244
559
736
496
253
469
606
269
214
7.9
5.3
6.9
5.5
4.8
327
157
207
172
192
20
37
29
17
20
87
128
33
30
60
331
613
600
242
222
I.contlnued)
113
-------
TABLE 44. (continued)
Quarter
1
2 3
4
1
2
3
4
Water
Year
Concentration
(mg/i)
Load
(kg/d)
1976
0.023
Lead
0.6
1.1
0.5
0.027 0.085
0.121
0.3
1977
0.170
0.039 0.085
0.203
2.9
0.4
0.4
0.2
1978
0.070
0.109 0.053
0.064
1.0
3.3
1.1
0.4
1979
0.039
0.048 0.039
0.157
0.3
2.0
0.6
0.9
1980
0.014
0.033 0.013
0.092
0.2
0.8
0.2
0.3
1976
1.6
Manganese
17.4
15.3
1.0 1.4
4.1
21.1
20.0
1977
1.6
1.4 1.8
5.6
27.5
13.2
9.3
6.8
i’78
1.8
1.2 1.4
2.1
25.4
26.9
29.6
13.0
19
2.2
0.8 1.5
2.3
14.2
32.5
22.9
13.1
1980
1.3
1.0 1.5
3.8
18.1
24.8
16.0
12.2
1976
3.6
Zinc
43
35
2.7 3.4
9.2
49
57
1977
5.8
4.0 6.0
16.6
97
38
31
20
1978
7.0
3.6 4.5
7.6
98
111
93
48
1979
5.8
2.7 3.6
4.8
38
112
56
1980
4.3
2.8 2.9
7.8
60
69
31
25
114
-------
TABLE 45. AVERAGE CONCENTRATIONS BY QUARTER AT MS-S (mg/i)
Water Year
& Quarter
1976
pH AcIdity 504 Cu Fe Pb Mn Zn
1 3.6 111 197 0 8 24 0 04 1.3 3 4
2 3.7 69 117 0.6 14 0 03 0.9 2.3
3 3.6 112 120 0.7 18 0 07 1.3 3.2
4 2.9 390 523 3.0 78 0 19 3.8 9.4
1977
1 3.7 140 170 1.6 40 0 09 1 4 4 5
2 4.0 88 143 0.8 24 0 04 1 3 3.6
3 3 3 184 271 1.1 29 0 09 2 2 4 7
4 2.6 912 1346 97 143 028 6 1 21
1978
3.3 259 273 3.6 59 0 08 1 9 7.5
3 3.7 123 188 0.9 22 0 06 1 3 3.9
4 3.3 175 340 1.2 27 0 01 1.6 4 7
1979
1 3.2 225 344 1.4 33 0 06 2.0 5.5
2 3.6 243 105 0.7 13 0 07 0.7 2.4
3 3.4 235 107 0 8 18 0 02 1.4 2 9
4 3 0 245 141 1.8 34 0 11 2.3 4 8
(continued)
-------
TABLE 45. (contInued)
Water Year
8 Quarter
pH
AcIdity
SO 4
Cu
Fe
Pb
Mn
Zn
1980
a
3
4
7
3.6
2 8
118
121
409
170
192
622
0 8
0.6
2 6
28
15
38
0.03
0 04
0 14
1.2
1.4
4.0
3 5
2 S
7.9
-a
-a
Mo san 1e collections this quarter.
-------
FIgures 57-72 show plots of pH and selected concentrations at various stream
stations with MS-i shown as control on each plot. The dramatic increases in
the concentrations and associated drops in pH during the suniners of 1976 and
1977 reflect the extreme low flows caused by the severe droughts of those
years. The difference In amplitude of the peaks gives a good indication
of the relative severity of the two droughts. Some of the extremely low con-
centration values resu’t from samples being taken on high-flow days. Again,
there appears to be little overall Improvement in the AND problem since
reclamation began.
The plots shown In Figures 73—84 depict loads In kilograms per day for
key parameters computec: from the semi-monthly concentration data and the
instantaneous flows rec .rded 3t the time of sample collection at the particu-
lar station. The computed loads are nearly always directly proportional to
the magnitude of the flows. The pronounced peaks in the load plots usually
reflect high flows that happened to be concurrent with sample collections,
and the low points generally coincide with reduced flows during the late sumer
months. The dramatic rise in manganese and zinc loads at MS-3 in early 1976
Is concurrent with the beginning of regradin at the Boyd Smith Site when all
metal concentrations rose sharply.
Several sample collections were made on dates when there were significant
Increases in flow. Unfortunately, most of these collections were made some-
time after the peak flow for a given storm event and none were made prior to
the peak. Table 46 shGws load, instantaneous flows, and the maximum flows re-
corded for the particular storm event at stations MS-2, MS-3 and MS-4 for six
days on which high flows occurred. Only the sample collections of 11-29-76
and 1—24—79 were made near peak flow levels. The collections at MS-4 or’ these
dates were approximately at peak levels and those at MS-2 and MS-3 occurred
slightly past the peaks. The sample collection of 1-26-78 happened to occur
on the same date as the highest flow ever recorded at MS-4 during the period
of record which began in 1975. This was 19,852 lIters per second (704 cfs)
which was well above the Instantaneous flow of 3766 liters per second (133 cfs)
recorded at the time of sampling. The loadings on this date were also maximal.
The special study conducted by the University of Virginia showed that
there are significant increases in loads and concentrations during the early
stages of a storm that are not reflected in the quarterly averages or semi-
monthly sampling data. This study revealed that loads usually reached a maxi-
mum level slightly before flows peaked, but there are several factors control-
ling the magnitude of the loads Including the length of dry spell preceding
the storm, temperature, and the amount of rainfall and duration. The reader
Is referred to pages 36-60 of this study in Appendix D for details of the
rainstorm studies.
To portray stream loads during base flow conditions, a series of plots
were generat2d with sample collection dates of all significant instantaneous
flow increases above normal seasonal levels deleted. Plots of the base flow
loads for MS-4 are shown in Figures 85-88. The criterion used for deletion
of collection dates was based upon analysis of precipitation and discharge
data to determine when the base flow of the stream was augmented by overland
runoff or shallow subsurface flow after a rainstorm. Some of the deleted
117
-------
S
a
V
1975 1976 1977 1978 1979 1980
FIgure 57.
station.
pH versus time In calendar years at MS—2 compared with control
S
a
S
0
1915
FIgure 58.
station.
1976 1977 1978 1919 1990
p11 versus time In calendar years at MS-3 compared wlth control
118
-------
1978
FIgure 59.
station.
1916 1977 1978 1979 1980
pH versus time In calendar years at MS-4 compared with control
1978
Figure 60.
station.
1976 1977 1978 1979 1980
pH versus time In calendar years at MS—5 compared with control
S
0
119
-------
C
3
2
0
1975 1976 1977 1978 1979 1980
Figure 61. Sulfate concentrations versus time in calendar years at 16-3
compared with control station.
1975 1976 1977 i r e 1979 1 o
FIgure 62. Sulfate concentrations versus time in calendar years atMS—4
comparei with control station.
1’
2
§
0
120
-------
C
C
1975 1976 1977 1978 1979 1980
FIgure 63. Copper concentrations versus time in calendar years at MS-4
compared with control station.
r
a
a
1915 1976 1977 1976 1979 1980
FIgure 64. Copper concentrations versus time in calend ‘ years at MS-5
compared with control station.
a
V.
0
a
C
S
121
-------
S
C
1916 1976 2977 2978 1979 1980
FIgure 65. Iron concentrations versus time in calendar years at MS-2 compared
with control station.
C
a
C
S
073 1976 077 2979 1979 2980
FIgure 66. Iron concentrations versus time In calendar years at MS-4 compared
with control station.
122
-------
0
S.’
r
0
C
0
1975 1976 1977 1978 1979 1980
Figure 68. Manganese concentrations versus time in calendar years at MS-4
compared with control station.
123
.
.
0
‘s,ThLA_
1915 1976 1977 1918 1979 1980
FIgure 67. Manganese concentrations versus time in calendar years at MS-3
compared with control station.
0
a
0
0
S
0
p.
-------
2
Figure 69. Zinc concentrations versus time in calendar years at MS-2
compared with control station.
FIgure 70. Z 4 nc concentrations
compared with control station.
versus time In calendar years at MS-3
8
C
1973 1976 1977 1978 1919 1980
F
S
1975 1976
1977
1975 1979
124
-------
-
1975 1976 1977 1978 1979 198C
Figure 71. Zinc concentrations versus time in calendar years at MS-4
compared with control station.
a
2
1’
C
S
S
!“5 1976
1977
Figure 72. Zinc concentrations
compared with control station.
1978 1979
versus time In calendar years at MS-5
125
-------
I
0
Figure 73. Sulfate loads based on instantaneous
years at 11S-3 compared with control station.
FIgure 74. sulfate loads based on Instantaneous flows versus
years at MS-5 compared with control station.
time in calendar
§
1975 1976 1977 1978 1979 1980
flows versus time in calendar
0
x
a
a
1975 1976
1977
1978 1979
126
-------
FIgure 75. Copper loads based on Instantaneous flows versus time in calendar
years at MS—4 compared with control station.
FIgure 76. Copper loads based on instantaneous flows versus
years at 115-5 compared with control station.
197$ 1976 1977
1976 1979
2
2
1975 1976
1977
1916 1919
time in calendar
127
-------
FIgure 77. Iron loads based on 1ns 4 tntaneous flows versus
years at MS-4 compared with control station.
time In calendar
8
k
£ P6-S
P 6- i
1979 1960
Figure 78. Iron loads based on Instantaneous flows versus time in calendar
years at JIS—5 compared wIts’ control station.
g
C
C
1975 1976 1977 1978 1979 1980
§
a
S
a
1975 1916 1977
128
-------
3
C
Figure 79. Manganese loads based on instantaneous flows versus time in
calendar years at MS-3 compared with control statIon.
C
‘V
C
1975
FIgure 80. Manganese loads based on instantaneous flows versus time In
czulendar years at MS-4 compared with control station.
9
C
1975 1976
1977
1918 1919 1980
9
0
9
1976
1977
1979 1980
129
-------
a
Figure 81. Zinc loads based on instantaneous flows versus time in calendar
years at MS—2 compared with control station.
I
FIgure 82. Zinc loads based on instantaneous flows versus time In calendar
years at MS-3 compared with control station.
C
1975 1976 1977 1978 1979 1980
8
8
8
0
a
1915 1976 1977 1978 1979 1980
130
-------
Figure 83. Zinc loads based on Instantaneous flows versus time In calendar
years at MS-4 compared with control station.
Figure 84. Zinc loads based on instantaneous flows versus
years at MS-5 compared with control station.
time in calendar
8
a
1978
1976
1977
1978 1979
U
0
1975 1976
1977
1978 1979
131
-------
TABLE 46. LOAD VALUES FOR HIGH FLOW DAYS (Kg/d)a
Date
Flow (l/s)
Hrs.C
Instdntaneousd
Flow (us)
S0
Cu
Fe
Pb
I
Zn
‘6—2
1-28-76
10—21-76
11-29-76
1-26-78
5-09-78
1-24-79
1388
4871
453
9346
1303
1586
I ?
21
3
9
11
2
292
186
365
1331
397
1246
948
717
687
2795
1031
3115
2.3
2.8
2.2
8 0
4 8
7.5
20
24
51
146
24
112
0 4
4.1
1.0
1.7
0.6
5.6
7.8
7.6
12 4
26 6
9.1
34 9
44
45
40
75
48
116
‘6- 3
1—28-76
10—21-76
11-29-76
1-26-78
5-09-78
2-24-79
2294
5551
765
10139
2804
2577
16
20
3
9
11
2
453
262
600
2945
821
2352
1771
1070
1531
4712
2381
4519
4.5
5.5
4.8
23.6
10.7
10 8
45
39
96
530
58
194
0 7
I 0
3 4
7 4
1 I
8 0
17.7
15 7
21.0
56.0
23 0
SI.?
59
55
59
112
80
106
‘ 6—4
1-28-76
10—21-76
11-29-76
1—26—78
5—09-78
1—24-79
3257
8326
793
19852
2549
3059
12
20
0
7.5
9.5
1
753
453
804
3766
991
3200
4715
39)5
6064
15818
5947
11519
27.9
38.5
55 5
177.0
33 1
73 6
527
129
1206
4143
595
1568
2 5
3 7
38 1
137 1
3.5
31 7
29.4
31 3
79 6
116.8
34 7
92 8
98
136
82
407
139
313
b To convert ag/day to lbs/day multiply by 2 205
Peak flow recorded this storm event, to convert liter/sec to cfs multiply by 0 0353
C hours after peak flow that sample was collected.
d Instantaneous flow recorded at time sample was coflected.
-------
Figure 85. Copper loads computed from instantaneous flows under base flow con-
ditions versus time in calendar years at MS-4 compared with control station.
Figure 86. Zinc loads computed from instantaneous flows under base flow con-
ditions versus time In calendar years at MS—4 compared with control station.
1976
1976 1977 1978 1979
1977
1978 1979
133
-------
Figure 87. Iron loads computed from instantaneous flows under base flow con-
ditions versus time in calendar years at MS-4 compared with control station.
Figure 88. Manganese loads computed from instantaneous flows under base flow
conditions versus time in calendar years at MS-4 compared with control station.
I
1975 1979 1977 197* 1979
p
a
134
-------
flows were low to moderate discharges following a dry spell, but most were
higher than normal base flow. Approximately 30 per cent of the collection
dates from October 1975 thru September 1979 were deleted. The instantaneous
flows used In this portrayal averaged 64 liters per second (2.3 cfs) at MS-4.
The base flow curves present a clearer seasonal pattern of loading with peaks
generally reached In the fall and winter months and minimum loading during
the suniner.
The relative load contributions from each site can be deduced from the
various means used to present the load data. It is obvious that loads in
crease as Contrary Creek passes each mine site, and apparently certain minerals
are peculiar to each site. Without question the Sulphur Site contributes the
major bulk of the AMD load as Indicated by the dramatic increases in acidity,
sulfate, Iron, copper and lead at MS—4. Generally during periods of low flow
in late sumer and early fall there was about a sixteen-fold ircrease in
acidity, eleven—fold Increase in copper, nine-fold increase in iron, and
thirty-fold increase in lead loading between MS-3 and MS-4 which bracket the
Sulphur Site. On a year-round basis the zinc load increased about fifty times
between MS-i and MS-2 indicating that the Aruiinius Site is a major source of
that metal, and the Boyd Smith Site appears to be the principal contributor of
manganese. From the instantaneous flow data collected at MS-5 it is apparent
that all pollutant loads Increased in the reach of Contrary Creek between the
Sulphur Site and Lake Anna where no reclamation work was done. In this section
of the stream the bed Is full of mine wastes washed from the upstream mine
sites.
An overall comparison of the AMO loads for water year 1980 with loads
from previous quarters when flows were of similar magnitude shows little change
at MS-2 and MS-4 over the monitoring period, but there was a pronounced de-
crease in most metal loads at MS-3. There are undoubtedly many statistical
analyses that could be made of the load data presented, but no further iuter-
pretation is attempted here.
Annual Complete Analyses
As stated earlier a complete analysis of additional parameters was
conducted at all sampling stations at least once annually. The results of
these analyses for the stream stations with flow data are presented in Tables
47-49. Of the additional metals analyzed, only cadmium was found to equal or
slightly exceed the SWCB limit of 0.01 mg/I on a few occasions in the affected
reach of the stream. The total and dissolved solids and specific conductance
values reflect the same trend In concentrations as the regular metals data.
The regular semi-monthly sampling included fecal coliform and BODç analy-
ses to determine If any effects of wastewater sludge used in the project could
be detected In the stream and lake samples. Fecal coliform counts virtually
never exceeded 100 organisms per 100 ml of sample at any stream station during
the five-year period of monitoring,* The BOD 5 usually ranged from I to 2 mg/I
The bacterial standard for non-shellfish waters In Virginia is 200 organIsms
per 100 ml of sample.
135
-------
TABLE 47. WATER QUALITY DATA-
ADDITIONAL METALS INCLUDED IN COMPLETE ANALYSES 1 a
Flow
Sped f IC
Conductance
Station Oate (l/s) pH ( thos/c i) Al As Cd Cr Hg Na
10—27-75 22.9 6.5 47 0.5- 0.003- 0.01- 0.01— 0.0005- o.o I- 3.3
5-19-76 30.9 6.2 44 0 2— 0.002- 0.01- 0.01- 0.0005- 0 01- 1-
5-24-77 5.1 6.9 60 0.5 0.002- 0.01. 0.01- 0 0005- 1.8 6.0
5-25.78 17.3 7.4 49 0.6 0.002- 0.01- 0.01 0.0005- 1.9 2.0
6-12-79 22.1 7.4 59 1.0 0.001- 0.01- 0.01- 0.0003- 0 8 6.0
5-14-80 19.3 6.8 63 2.0 0.001- 0.01- 0.01 0 0003- 0.9 5.0
P6-2 10-27-75 34.0 5.8 170 4.5 0.003- 0.02 0.01- 0.0005- 0.1- 3.5
5-19-76 36.8 6.3 120 0.7 0.002- 0.01- 0.01- 0 0005- 0.1- 1.0
5-24-77 6.2 5.9 350 0.6 0 002- 0.01 0.01- 0.0005- 2.2 5.0
5-25-78 27.5 7.0 180 1.0 0.002- 0.02 0.01- 0.0005- 2.2 1.0
6-12-79 25 5 6.8 174 0.2 0.001- 0.01- 0.01- 0 0003- 0.5 4.0
5-14-80 23.5 6.4 195 4.0 0.001- 0.01- 0.01 0.0003- 1.3 6.0
10-27-75 59.5 4.9 240 2.4 0.003- 0.01- 0.01— 0.0005- 0.1— 4.2
5-19-76 69.4 5.6 156 1 2 0.002- 0.01- 0.01- 0.0005- 0.1- 1-
‘4-77 16.1 4.1 365 1.9 0.002- 0.01 0.01- 0 0005- 2 3 4.0
‘5-78 50.1 5.0 252 1.6 0.002- 0.02 0.01 00005- 22 1.0
2-79 40.5 5.2 267 1 8 0.001- 0.01- 0.01- 0 0003- 1 6 6.0
.-14-8 0 45,3 5.5 288 1.0 0.001- 0.01- 0.01 0.0003- 1.3 5.0
P6-4 10-21-75 84.4 4.0 390 6.3 0.006 0.02 0.01- 0.0005- 05 7.8
5-19-76 158.6 6.0 56 3.5 0.002- 0.01- 0 01- 0 0005- 0.1 1-
S-24-77 28.6 3.3 680 15.0 0.002 0.02 0.01- 0 0005- 2 6 4.0
5-25-78 99.4 3.6 583 8.6 0.002- 0.02 0.01 0 0005- 2 4
6-12-79 76. 3.8 568 7.3 0.002 0.01- 0.02 0.0003- 1.0 4.0
5-14-8( 76.5 3.8 447 5.0 0.003 0.01- 0 01 0.0003- 1.3 7.0
P6-5 10-27-75 3.6 630 6.4 0.006 0.01- 0.01- 0 0005- 0.1- 4.3
5-19-7 - — 160.9 3.7 330 3.7 0.002- 0.01- 0.01- 0.0005- 0.1- 1-
5-24-7 35.7 3.0 820 20.0 0.002- - 0.01 0.01- 0.0005- 2.9 8.0
5-2—78 3.6 589 7.6 0.002- 0.02 0.01 0 0005- 2 5 4.0
6-12-79 100.0 3.5 613 7.0 0.001 0.01- 0.01 0,0003- 1 0 4.0
5-14-80 80.1 3.5 476 5.0 0.002 0.01- 0.01 0.0003- 1.4 6.0
a A 4—) sign Ind Icates that the concentration was be’ow the incidated ‘evel of detection.
-------
TABLE 48. WATER QUALITY DATA -
SOLIDS, SPECIFIC CONDUCTANCE, TURBIDITYa
Tota)
Dissolved Specific
ROW Total Solids ( m gil ) j p dnd Solids (mg/i ) Sohds Conductance Turbidity
Station Date (lj’S) (Total) (YoU (Fix) (Total) (Vol) (fix) (mg/I) (j,nhos/cm) (NTIj}
NS-1 10—27-75 22.9 68 37 31 0 0 0 68 47 3.5
5-19-76 30.9 110 58 52 2 0 108 44 5.0
5—24-77 5.1 739 412 327 8 8 0 7)1 60 3.2
5-25-76 17.3 64 20 44 12 5 7 52 49 6.7
6-12-79 22 1 61 16 45 2 1 1 59 59 6.1
5-14-80 19.3 80 28 52 12 5 7 68 63 7.0
S-2 10—27-75 34.0 176 21 155 4 2 2 172 170
5-19-76 36.8 121 39 88 30 16 14 97 120 7.5
5-24-77 6.2 289 74 215 1 1 0 288 350 3.1
5-25-78 21.5 151 25 126 14 5 9 137 160 7.6
6-12-19 25 5 168 31 1)7 8 4 4 160 174 6.2
— 5-14-80 23 5 166 46 120 17 8 9 149 195 7.0
MS-3 10-27-75 59.5 254 78 176 6 2 4 248 240 5.9
5-19-76 69.4 204 65 139 14 6 8 190 156 7.2
5-24 77 18.7 348 136 212 3 3 0 345 365 1.1
5-25-78 50.1 227 48 179 8 1 1 219 252 6.4
6-12-79 40.5 242 45 197 7 0 1 235 267 6.2
5-14-80 45.3 245 61 184 24 11 13 221 288 8.8
MS-4 10-27-75 84 4 368 19 289 14 6 8 354 390 4.0
5-19-76 158 6 85 43 42 20 14 6 55 56 5.2
5-24-77 28.6 576 173 403 17 6 11 559 680 1.6
5-25-78 99.4 511 149 362 31 5 26 470 583 12.0
6-12-79 76 5 458 102 356 9 3 6 449 568 9.7
5—14—80 76.5 357 71 286 14 1 7 343 447 8.3
WS—5 10—27-75 392 85 307 10 4 6 382 630 1.3
5-19-76 1609 299 91 208 26 4 22 213 330 100
5-24-71 35.1 508 191 31/ 1- 1- I- 508 820 0.4
5-25-78 485 1)9 306 23 5 18 462 589 7.9
6-12-79 100 0 434 123 311 2 1 1 432 618 2.6
5-14-80 80.1 351 91 260 9 5 4 342 476 1.0
a A (-) sign Indicates that the concentration was below the Indicated level of detection.
-------
TABLE 49. WATER QUALITY DATA -
MISCELLANEOUS PARAMETERS (mg/i)
Flow
Hardness
Station Date (us) Ca
Mg (CaCO 3 ) Cl F Cyanide
MS—i 10-27—75 22.9 4 2.3 22 3 0.1-
5-19-76 30.9 4 2.3 24 4 0.1- 0.01-
5-24-77 5.1 6 3.0 28 2 0.01-
5-25-78 17.3 5 2.5 18 3 0.01-
6-12-79 22.7 14 8.3 26 1
5-14-80 19.3 5 2.4 24 2 0.1-
11 5—2 10-27-75 34.0 15 8.0 54 3 0.5
5-19-76 36.8 Ii 5.5 44 3 0.0 0.01-
5-24-77 6.2 28 12.4 100 3 0.01-
5-25-78 27.5 14 7.9 62 2 0.01-
6—12—79 25.5 4 2.5 81 2
5-14-80 23.5 15 7.5 68 2 0.1
115-3 10-27-75 59.5 21 12.7 116 3 0.1
5-19—76 69.4 16 9.5 79 5 0.1 0.01-
5-24—77 18.7 31 14.0 134 3 0.01—
5-25-78 50.1 18 11.0 78 3 0.01—
6-12—79 40.5 19 12.0 103 2
5-14-80 45.3 22 12.0 100 2 0.1
1 15-4 10-27-75 84.4 18 13.6 116 3 0.3
5-19-76 158.6 15 9.8 26 4 0.1- 0.01-
5-24-77 28.6 31 16.0 100 1 0.01-
5-25-78 99.4 20 14,0 68 4 0.01-
6-12-79 76.5 21 21,0 95 3
5—14—80 76.5 20 12.0 93 2 0.3
MS—S 10-27-75 16 12.4 120 2 0.24
5-19-76 160.9 13 9.0 60 4 0.16 0.01-
5-24-77 35.7 26 13.0 110 3 0.01-
5-25-78 17 13.0 64 4 0.01-
6-12-79 100.0 1 13.4 86 3
5-14-80 80.1 17 13.0 82 2 0.2
a
A (-) sign Indicates that the concentration was below the Indicated level
of detection.
138
-------
at MS-2 and flS-3 which was generally the same as background at MS-i. At MS-4
the 6005 ranged from 1 to 2 mg/i during the first year of monitoring, but In-
creased to a range of around 3 to 6 mg/i over the next four years with a few
higher values recorded In the fall of 1977. 6005 at MS-5 closely paralleled
that at 115-4 with values generally being 1 mg/I or less during the first year
and ranging from 2 to 5 mg/i the 1ast four years. The slight Increases In
BODE at 115-4 and MS-5 from late 1976 until 1980 presumably result from the
large volumes of sludge that have been Incorporated at the reclaimed mine
sites. For a further check on the effects of sludge, nutrients and other
oxygen demand parameters were Included In the annual complete ter anaiyses
which are shown in Table 50. ComposIte monthly an ’iyses of the Blue Plains
SIP sludge provided by the District of Columbia are shown in Table 51. For
a comparison of sludge analyses conducted by the DCLS ii 1977, see Table 9 on
Page 46. On the basis cf all analyses performed, it is believed that the
use of sludge has had insignificant effect on the water of Contrary Creek or
Lake Anna.
Tributary Stations
Various tributaries of Cor trary Creek have been sampled periodically at
each mine site for the same AMO parameters as in the regular semi-monthly
sampling. At the Armlnius Site (Figure 9) Tr-12 and Tr-13 drain the major
portion of Arminlus East, Tr-i4 drains a series of settling ponds where no
reclamation has been done, and Tr-15 is an old diversion along the northeast
side of the site. At the Boyd Smith Site (Flgu—e 90) Tr-4 is the unaffected
portion of the main tributary draining the site. Tr-6 is a very small seep
from an old shaft and Tr-7 Is just below the co.fluence of Tr-6 with the main
tributary. The entrance of the main tributary into Contrary Creek is known as
Tr-8, and two diversions constructed in 1976 are designated Tr-9 and Tr-10,
respectively. At Sulphur East (Figure 91) Tr—2 drains from an old shaft
entrance, Tr-2A. It is believed that drainage from Tr-2A originates from the
large mine pool abo t 30 meters south of the shaft entrance. At Sulphur West
Tr-1 flows from the beaver pond used for irrigation water, and Tr-1A drains a
portion of the Tailing Area.
Concentrations and available flaws for the tributaries are given in
Tables 52-55. It is again apparent that certain metals are characteristic of
each site. Note at Tr-12 and Tr-14 of the Arminius Site (Table 52) that de-
spite the high concentrations of sulfates and most metals p 11 is near normal.
At the Boyd Smith Site the pronounced increase in concentrations between Tr-7
and Tr-8 show that most of the AND from this site seeps from along the main
tributary rather than originating from the old shaft at Tr-6 (Table 53).
Concentrations were found to be much higher from the Sulphur East tributaries
than on the west side (Tables 54 and 55). A comparison of the tributary data
with Tables 42-45 IndIcates that concentrations from the tributaries are
generally much higher than in the main stem of Contrary Creek for each respec-
tive site.
Besides the regular parameters, a few of the tributary samples were ana-
lyzed for some of the other parameters Included in the complete analyses and
these are presented in Table 56. The high calcium and magnesium values at the
Arninius Site suggest the presence of carbonate minerals which may be a factor
139
-------
1 6-1
TABLE 50. WATER ( ALITY DATA -
FHJTRIENTS AND OXYGEN DEMAND PARAIIETERS (mg/i)
Flow P N
Station Date (T) (YoU 10r J ) ( T rkje1)
NH 1
(asN)
N02 + NO)
( s N)
NO 2
(as N) COD TOC 8005
0.1-
01
0.1-
01
0 1-
0.1-
O 1-
O 1-
O 1-
02
o oi-
0.01-
O 01-
O 01
0 01
O 01-
0 01-
0 01-
O 01-
O 01
0.4
02
0.1-
0.3
0.4
9.4
0 1-
0.1-
0.3
0.4
0.01-
0.01-
0.1-
0.1-
0.1-
0.1-
O 1-
O 1-
0.1
0.1
0.2
O 1-
o i-
01
0.1-
0.14
0.1
O 05-
0.05
0.05-
0.11
0.1
0.1
0.07
0.05-
008
0.05-
0.1
0 06
O 05-
16-2
1 15-3
115-4
P6-S
a
5-19-76
30.9
28
7- 1—76
4.3
0.01-
20
12
5
5-24-77
5 1
0.01-
5-25-78
17.3
2
6-12-79
22.7
24
7
1
5-14-80
19.3
01-
0 91-
19
14
14
9
1
2
10-27-75
34.0
5-19-76
36.8
8
10
1
7-1-76
4 0
0.01-
32
11
1
5-24—77
6 2
1-
5-25—78
27.5
0 01-
4-
5
1-
6-12-79
25.5
0 01-
16
3
1
5-14-80
23 5
0 01
0 05-
13
7
8
11
1—
1
10-27-75
59 5
5-19-76
69.4
3
1-
- 1-76
18 7
0 1-
0 01-
0.4
0 01-
6
1
5-24-77
187
01-
001-
01
1-
5-25-78
501
01-
001-
01-
4-
3
1-
6-12-79
40.5
0 1-
0 01-
0.3
001-
16
3
1
5-14-80
45.3
0 1-
0 01-
0.1-
0 01-
0 01-
13
6
7
6
1
1
10-27-75
84 4
5-19—76
158 6
4
4
1
7- 1-76
28.6
0.1-
0 01-
1 0
0.21
8
6
1
5-24-77
28.0
0.1-
0 01-
0.2
0 2
1-
5-25-78
99 4
0 I-
0 01-
0 1
0.1
0 01-
8
3
1-
6-12—79
765
01-
001-
0.4
0 01-
16
3
5
5-14-80
765
01-
001-
0.2
02
0.01
0.05-
001-
001-
11
10
3
6
4
3
10-27—75
5-19-76
160.9
3
1
7- 1-76
32.3
0.1-
0.01-
0.4
0.05
0 01-
6
1
5-24-77
5.7
0.1-
0 01-
0.1
0.1
0.05-
0.01-
4
4
5-25-78
0.1-
0 01-
0.2
0.2
0.1
0.01-
1-
6-12-79
100.0
0.1-
0 01-
0.3
0.05
0 01-
11
4
5
5-14-80
80.1
0.1-
0 01-
0.1
0.1
0.05-
0 01-
6
4
3
2
A (-) sign indicates that the concentration was below the indicated level of detection.
-------
TABLE 51. MONTHLY COMPOSITE SLUDGE ANALySES ON DRY
WEIGHT BASIS FROM B1’JE PLAINS SIP (ppm)
Month/Year Zn Ni Cd Pb Cu Cr
April 1976 6.6 1710 37.6 16.6 461 4.8 472 455
May 1976 7.1 1805 36.9 17.2 451 5.6 559 587
June 1976 7.5 2020 42.9 17.9 428 2.3 676 668
July 1976 7.1 1535 30.8 11.1 344 2.0 458 476
August 1976 7.3 1770 40.3 15. 416 3.6 640 744
Sept. 1977 4.3 1825 54.2 18.1 695 5.2 1025 1045
August 1978 5.1 1277 45.4 13.7 510 4.1 768 938
Sept. 1978 5.2 1275 25.5 11.8 390 2.9 750 795
August 1979 4.9 1220 64.0 12.0 600 750 745
Average 6.1 1604 42.0 14.9 477 3.8 678 737
DCLS 1976
analyses 6.5 2529 29.0 17.0 550 5.05 785 659
Source: District of Columbia Environmental Services
-------
P-’ -
I 1 3URF 89. ARMINIUS TRIBUTARIES
(MODIFIED AFTER MIORIN ET AL, 1974)
LEGEND
SHAFT
Ii] STRUCTURE
TR.b TRIBUTARY
142
-------
BOYD SMITH SITE
o WOODS
DIVE’ SIOP1S
_ STREAMS
• RIPRAP SECTIONS
cONTOURS
SEEDED
SLUDGED
TRB TRIBUTARY
FIGURE 90. BOYD SMITH TRIBUTARIES
250
FEET
___________METERS
0 4S
TP4
/
MS3
cONIRAR’! CREEK
143
-------
C”
: : •
— r.
1,-S Tributary
--
-Th
‘ . 5
____, -—--—- ‘- . -
•TippIe
‘5, 1 ‘ — I
t POOL
I
\
FIGURE 91. SULPHUR SITE TRIBUTARIES
1
1
MS4 Ii 700 FEET
DOWNSTREAM
“V, North
, End...
5 1ST
ri. _ il __ rl
• 5$
1 ,/
SULPH
or ge
2- T ::
WEST
4
nQ
ea
7
)
I
/
/
(
g
/
-------
TABLE 52. WATER QUALITY DATA -
ARMINIUS TRIBUTARIES (mg/1)a
Station
Date
Flow
(ifs)
pH
A kal1nity
(CaCO 3 )
Acidity
(CaCO 3 )
SO 4
Cu
Fe
Pb
Mn
I
Zn
urbidity
(NTU)
Tr-12
7-14-76
8-12-76
8-25-76
5-24-77
8-18-77
7-07-77
0.113
0.110
0.102
0.130
7.2
6.4
6.4
6.0
6.0
6.3
66
63
32
75
2
58
54
87
200
225
120
2054
2004
1961
1900
2300
2150
0.68
0.15
0.20
0.01-
0 11
0.01
70
37
68
63
78
77
0.422
0.1-
0 1
0.031
0.326
0.066
12 0
11.1
10 7
12
12.0
11.0
6.0
14.4
14.4
14.0
20
9.6
225
206
240
38
390
44
lr-13
7-14-76
8-12-76
8-25-76
0.014
0.017
0014
5.5
4.5
4.3
257
267
244
2855
2631
27 3
0.26
0.34
053
100
120
105
0.211
0 1-
0 3
16 0
15 8
16.7
31.0
24
29
225
200
220
Tr-14
6-12-79
10-18-79
0.078
6.9
6.5
28
17
101
88
42
1176
0.70
0 41
0 3 0.261
0 2 0 1b3
5.6
3 4
81
60
7.2
7.1
Tr-15
10-18-79
0.120
3.4
1289
3512
9 8
6 0 0.127
2 9
148
0.4
a
U i
A C—) sign indicates that the concentration wds below the Indicated level of detection.
-------
TABLE 53. WATER QUALITY DATA -
BOYD SMITH TRiBUTARIES (mg/i)
Station
Date
Flow
(l/s)
pH
Alkalinity
(CaCO 3 )
Acidity
(CaCO 3 )
504
Cu
Fe
Pb
Itn
in
(NTU)
Tr-4
9-15-74
4-05-76
0 353
2.975
6.4
5.9
27
13
15
18
3
9
0.01-
0.01-
3.4
3.0
0.010
0.003
0.43
0.30
0.05
0.53
5.8
Tr-6
9-15-75
4-05-16
6-12-19
0.010
0.031
3.0
3.0
3.0
1589
1245
0
432
1040
1895
72
2.3
7.4
1.5
40
13.0
19
0.17
0 064
0.059
11.5
6.3
1.8
17.0
32.0
4.9
0.4
0.4
Tr-7
9-15-li
4-05-76
6-12-79
0.488
3.258
4 1
4 5
4 5
44
125
0
75
103
58
77
0.60
0.25
0 30
32
32.0
9.7
0.25
0.570
0.074
1.16
0.52
0.52
2 0
0.91
11.4
64
9.5
Tr-8
9-15-75
4-05-76
5-19—76
7-14-76
6-12-79
0.657
3.258
1.263
0.442
3 1
3.4
3.7
2.9
3.1
233
440
0
266
420
302
728
394
540
780
71
6 7
0.11
2 1
2.7
1.7
230
1.4
42
15.0
12.5
0.013
0.293
0.391
0 193
4 1
0.72
11.2
15.0
8.1
18.0
1.8
9.0
16.0
10.9
85
17
1.2
2.9
Tr-9
5-19-76
7-14-76
6-12-79
0.119
0.110
3.6
4.9
3.1
254
55
855
i4 0
1211
41
8.0
0.09
9.4
3.2
9 0
1.5
0.353
0 042
0.311
3.6
20 0
6.6
23.0
12.0
42
17
40
1.0
Tr-10
5-19-76
7-14-76
6-12-79
0.561
0
3.9
3.3
3.7
195
450
70
42
945
25
1.1
10.0
0.19
22
23 0
0.6
0.546
0.509
0.096
12.5
8.4
15
1.5
42.0
0.96
74
27
0.7
A (-) sign indicates that the concentration was below the indicated level of detection.
-------
TABLE 54. WATER QUALITY DATA -
SULPHUR EAST TRIBUTARIES (mg/i)
Station
Flow 8
Date (ifs)
p 1 1
Alkalinity Acidity
(CaCO 3 ) (C C0 3 ) S04
Cu
Fe
Pb
Mn
in
Turbidity
(NTU)
Tr-2
9-15-75
4-05-76
6-12-79
2.7
2.8
3.1
961 1640
1000 1630
1435 268
2.1
2 3
2.3
72
138
0.016
0.045
0.023
11 9
14.0
14
11.3
6.0
12.3
0.2
5 4
Tr-2A
6-12-79
4.0
1280 228
2.1
162
0 050
14
2.5
2.5
Mine Pool
7-14-76
6-12•-79
2.9
3.0
825 1106
539 64
4.5
1.9
35
1.2
0.098
0.034
10.8
5.9
12.7
6.3
8
1.5
a No flow
data available.
TABLE 55. i ATER QUALITY
SULPHUR WEST TRIBUTARIES
DATA -
(mg/i)
Station
Flow
Date (ifs)
pH
Alkalinity Acidity
(CaCO 3 ) (CaCO 3 ) SO 4
Cu
Fe
Pb
Mn
Zn
Turbidity
(NTU)
Tr-1
9-15-75 2 513
4-05-76 9 093
7-14-76 2.635
6-12-79
5.3
4 8
5.5
5.9
5 20 31.8
23 2 32.4
12 23.9
4 22 37.
0 50
0.38
0.21
0 23
15
100
70
98
0.004
0 003
0022
0 004
0 40
0 10
034
0 43
0 30
043
033
0.56
9.2
13
36
Tr-IA
6-12-79
4 0
32 69
0 26
2 3
0.027
0 38
027
3.7
-4
-------
MISCELLANEOUS
TABLE 56. WATER QUALITY DATA - a
PARAMETERS CONTRARY CREEK TRIBUTARIES (mci/i)
Total Specific
Total Dissolved Conductance
Al As Cd Ca Cr 14q K Na Solids Solids ( Psos/ )
Tr-6
— Tr-7
Tr-8
Date
Arminlus Site
Tr- 12
5.24-77
8-18-77
10.0
0.6
0.002-
0.012
0.02
0.04
590
550
0.01
0.02
138
156
0.0005-
0.0005-
12
18
9
9
3577
3602
3473
3470
2700
2600
Tr-14
6.12-79
2.5
0.001-
0.18
194
0.01-
114
0.0003-
7.4
12
1979
1967
1848
Boyd Smith
Site
6-12-79
35
0.043
0.01-
18
0.02
11
0.0003-
0.8
5
989
989
978
6-12-79
5.6
0.001
0.01-
7
0.02
5
0.0003-
0.7
S
192
181
196
5-19-76
6-12-79
22 2
30
0.002-
0.030
0.01-
0.04
54
45
0.01-
0.03
41
35
0.0005-
0.0003-
2.1
2.8
1-
6
1013
1104
975
1099
860
1141
Tr—9
5-19-76
6-12-79
22.8
83
0.002
0.115
001-
0.29
29
48
0.01-
0.05
37
69
0.0006
0.0003-
1 1
4.9
1-
4
902
1894
848
1894
760
1848
Tr-10
5-19-76
6-12-79
11.9
3 2
0.002-
0.001-
0.01-
0 02
139
157
0.01-
0.01-
98
113
0.0005-
0 0003-
7.5
4 7
4
12
1696
1716
1406
1716
1300
1576
Sulphur Site
Tr-1
6-12-79
1.6
0 003
0.01-
9
0 01-
3
O.0003
1 2
4
161)
142
132
Tr-1A
6-12-79
1.6
0.001-
0.01-
9
0 01-
3
0.0003-
2 0
13
168
164
196
Tr-2
6-12-79
102
0.132
0.04
98
0.01.
103
0.0003
6.6
6
3486
3479
2366
Tr-2A
6-12-79
98
0.125
0.04
91
0.03
105
0.0003.
7.9
6
3504
3494
2527
Mine P001
6-12-79
63
0.095
0.03
43
0.03
46
0.fl003-
4.5
4
1395
1394
1517
a A (-) sign indicates that the concentration was below the indicated level of detection.
-------
contributing to the lower acidity at this site than would be expected.
pH and Specific Conductance Transects - 1979
In the sumer of 1979 a pH and specific conductance transect was run for
6.6 kilometers at 100-meter Intervals along the entire length of Contrary
Creek from Lake Anna to above the Arminius Site. Tables 57 and 58 and Figure
92 present the results of this transect which includes the only water quality
data available for the stream reaches between the mine sites and the downstream
reach of Contrary Creek to Lake Anna. The increasing conductivity and declin-
ing ph In the downstream direction again showed how water quality is degraded
as it passes each mine site. The abrupt drop in pH at the Boyd Smith Site
occurs where Tr—8 enters the main channel, but the magnitude of the drop is
difficult to explain considering the prevailing pH’s recorded below the Boyd
Smith Site over the course of the monitoring program. Note that the ph made
a slight recovery between the Boyd Smith and Sulphur Site but there was a
dramatic drop from 4.5 to 2.9 as the stream passed through the Sulphur Site,
and there was a continued decrease downstream to Lake Anna. The specific
conductance predictably increased downstream with sharp rises at the Arminius
and Sulphur Sites. The sudden decrease in conductivity and slight improvement
in pH between the Arminius and Boyd Smith Sites may be due to a fresh water
tributary entering Contrary Creek in that vicinity. The conductivity curve
also reflects an improvement between the Boyd Smith and Sulphur Sites, but it
is obvious that metal concentrations steadily increase between the Sulphur Site
and Lake Anna.
A close-interval transect for conductance only was run at the Boyd Smith
Site to compare conditions along each side of the stream and at mid-stream. A
pronounced increase in conductance below the confluence of Tr-8 was noted on
the southeast side of the stream adjacent to the mine site. Results of this
transect are shown in Table 59 and Figure 3. A pH and conductance transect
was also run along Tr-8 at the Boyd Smith Site (Table 60 and Figure 94). This
transect revealed that most of the AND seeping into this tributary is along an
80-meter stretch in the uppermost affected reach. Refer to Table 53 for ana-
lytical data from Tr-8.
A pH and conductance transect through the entire length of the Sulphur
Site appears in the special study by UVA in Appendix D.
Lake Stations
Two stations in the Contrary Creek arm of Lake Anna were sampled concur-
rently with the stream stations from October 1975 until early 1980 and were
analyzed for the same parameters. There were significant gaps in the lake
data during the winters of 1976-77 and 1977-78 when ice and inclement weather
prohibited sampling. The stations are designated SS-1 and SS-2 and are shown
on Figure 56. SS-1 is 1.7 kilometers from the mouth of Contrary Creek where
depth is about 3 met rs. SS-2 is at the juncture of the Contrary Creek arm
with thc main body of Lake Anna approximately 5 kilometers from MS-5. Depth
at SS-2 is about 9 meters. Samples were collected at surface, middle, and
bottom depths at each station as indicated below
149
-------
TABLE 57. pH AND SPECIFIC CONDUCTANCE DATA FOR 6.6 KM TRANSECT ALONG
CONTRARY CREEK, JULY 30, 1979
Meters upstream
from Creek mouth Specific Conductance
at Lake Anna pH ( jmhos/cm) Remarks
0 2.6 1200 Began at tree stump on lake
100 2.6 1180 shore.
200 2.6 1150
300 2.7 1130
400 2.7 1140
500 2.7 1140
600 2.7 1100
700 2.7 1080
800 2.7 1090 Fresh tributary enters from
south @ 825 rn.
900 2.7 1100 Broad floodplain from 900 m
to 1200 m with laminated beds
of pyrite and quartz sand.
1000 2.7 1040
1100 2.7 1020 Fresh tributary enters from
north @ 1190 m.
1200 2.7 1050
1300 2.8 1010
1400 2.8 974 Broad floodplain from 1400 to
1700 m with laminated beds of
pyrite and quartz sand.
1500 2.8 944
1600 2.8 917
1700 2.9 907
1800 2.9 887
1900 2.9 865 Pyrlte sand and iron hydroxide
precipitate seen in creekbed
all the way to lake.
2000 2.9 887
2100 2.9 925 MS-4, gaging station at 2100 m.
2200 3.0 909 Fresh tributary enters from
west @ 2198 m, downstream limit
of major Sulphur Site tailings
at 2175 m.
2300 3.1 870
2400 3.2 773
2500 3.4 695
2600 3.7 610 Fresh tributary (Tr-1) enters
from west at 2635 m.
2700 3.9 438
2800 3.9 438
2900 4.5 372 U t m 11m ’ “f i’i:jor Sulphur
Site tailings at 2900 m .
150 (continued)
-------
TABLE 57. (continued)
Meters
upstream
from Cr
eek mouth
Specific
Conductance
at Lake
Anna pH
( mhos/crn) Remarks
3000 4.6 3Th Fresh tributary enters from
west @ 3025 m.
3100 4.5 389
3200 4.6 387
3300 4.7 386
3400 4.8 387
3500 4.8 389
3600 4.8 415
3700 4.6 433 Tributary enters from east @
3730 m, dtaining a swamp.
3800 4.5 441
3900 4.5 437
4000 4.4 461
4100 4.4 459
4200 4.5 463
4300 4.5 450
4400 4.6 452 MS-3, gaging station at 4475 m.
4500 4.7 428 Fresh tributary enters from
west and mine seepage enters
from east (Tr-10) at 4522 m,
marking the downstrc.am limit
of Boyd Smith Site tailings.
4600 4.4 496
4700 4.5 496 Fresh tributary enters from
west and mine drainage enters
from east (Tr-8) at 4702 m,
marking the upstream limit of
Boyd Smith Site tailings.
4800 6.2 470
4900 6.3 471
5000 6.4 470
5100 6.4 465
5200 6.5 457
5300 6.4 233
5400 6.5 231 Large rock outcrop and rapids
@ 5400 m, fresh tributary
enters from west at 5430 m.
5500 6.1 343
5600 6.1 354 MS-2 gaging station at 5613 m.
5700 6.2 352
5800 6.2 346 Downstream limit of Arminlus
Site tailings @ 5850 m.
5900 6.3 338
6000 6.3 292 MIne seepage trickles from
Arminius West tailings.
(continued)
151
-------
TABLE 57. (continued)
Meters upstream
from Creek mouth
at Lake Anna
pH
Specific Conductance
( mhos/cm)
Remarks
6100
6.9
193
Small mine tributaries enter
from east at 6198 and 6175 m
(Tr-12 and Tr-13) respective’y.
6200
7.1
69.1
Upstream Hmit of Arunnius
Site taiHngs @ 6225 m.
6300
7.2
63.3
MS-i, gaging station @ 6257
m, fresh tributary enters from
west at 6245 m.
6400
7.1
62.8
6500
7.0
62.2
6600
6.9
62.2
End of transect, very low
flow near headwaters.
Source: Dagenhart (1980).
152
-------
TABLE 58. pH AND SPECIFIC CONDUCTANCE DATA OF CONTRARY CREEK
TRIBUTARIES, JULY 30, 1979
Meters from
Contrary Creek
mouth to con-
!luence w/trib pH
825
1190 6.5 48.5
2198 6.6 33 7
2635 6.5 101
3025
7.1
29.7
3730
6.6
118
4522
7.1
38.3
4522
3.4
1891
4702
7.0
31 6
4702
2.9
1424
5430
7.2
30.6
6175
6.6
3181
6198
6.5
3757
37.1
Remarks
Very low flow from south.
sample lost, clean looking
Low flow from north, clean
looking
Medium flow from west, clean
looking
Medium flow from west, known
as Tr-1, flows through 100 m
of tailings from beaver pond
Medium flow from west from a
pond, clean looking
Very low flow from east, drain-
ing a swamp, dirty irridescent
water.
Medium flow from west, Ci Can
looking.
Extremely low flow from east,
polluted tributary (Ir-lO) from
Boyd Smith Site
Very low flow from west, clean
looklnq
Low flow from east, polluted
tributary (Tr.8) from Boyd
Smith Site
Med 4 urn flow from west, clean
looking
Very low flow from east, p 01 .
luted tributary (Tr-13) from
Arininlus Site.
Very low flow from east, pol-
luted tributary (Tr-12) from
Ameinlus Site
Medium flow from west, clean
looking.
Specific Conductance
( 1 ,mhos/cn
6245 7.0
Source: Dagenhart (1980).
153
-------
I
a
I-
‘7’
FIgure 92. pH And Specific Conductance Transect From Lake Anna to Above Arminius Site, July 30,
1979 (Source: Dagentart, 1980).
Arminius Boyd Smith
Mine Mine
I Ii
I S II
Sullu r
Mine
U
S.
U
a
Ln
(kilorn eters)
-------
TABLE 59. SPECIFIC COND CTANCE DATA OR TRANSECT ALONG CONTR.ARY CREEK AT
BOYD SMITH MINE SIT, JULY 19, 1979
Specific Conductance
Meters
(pmhos/cm)
North-
South-
Upstream
west Mid-
east
from MS-3
side stream
side
Remarks
0
312 315
322
—
At gaging station, MS-3, beginning of
Bc’yd Smith Site.
25
207 298
339
Tr-1O trickles frori east @ 49 m, fresh
tributary with moderate flo from west
@ 49 m.
50
327 328
335
75
332 329
331
100
327 330
343
125
327 328
333
1/ O
328 329
336
Tree down in creek and ponding water
at 150 m interval.
175
323 329
328
200
322 350
350
225
193 321
410
Tr-8 enters from east with mw flow
at 240 m, fresh tributary wit low
flow enters from west at 22 [ ’
250
311 318
316
Upstream from all Boyd Smith Site
tailings.
275
313 321
321
300
319 320
321
350
317 321
317
Source: Dagenhart
(1980).
155
-------
-s
E40 0
U I
o E E
E
-3
a)
U
C
2300 LI
o sream flow >
LI C
-o -
o osE
U,
0 . U a )I I
I l
0 LOU IU
-— ‘I II
QI L fti+..
El -
0200 I I I I I I I
300 200 100 0
DIst3nce upstream from MS-3 (meters)
Figure 93. Spec1 lc Conductance Transect Along Contrary Creek At Boyd Sniitn Site, July 19, 1979
(Source: Dagenhart, 1980).
-------
TABLE 60. p11 AND SPFCIFIC CONDUCTANCE DATA FOR TRANSECT ALONG MAIN TRIBUTARY
(Tr—8) FROM BOYD SMITH SITE, JUNE 19, 1979
Meters Upstream
from Tr-8 con-
Specific
fluence with
Cor ductance
Contrary Creek pH
( imhos/cm) Remarks
0
3.08
1160
First 10 m of tributary lined
with granite riprap.
5
3.10
1160
10
3.09
1160
15
3.10
1170
20
3.15
1170
From 20 m to 180 m, a greenish
blue-yray clavey sub—soil is
visible along much uf Tr-R’s
bank and bed.
25
3.11
1160
30
3.13
1150
35
3.10
1160
40
3.10
1160
Wooden gaging post at 43 m,
station known as Tr-8.
45
3.10
1150
50
3.09
1160
55
3.02
1160
60
3.05
1160
65
3.04
1150
70
3.05
1140
75
3.04
1140
80
3.00
1180
85
3.00
1180
90
3.00
1160
95
3.01
1160
100
3.01
1160
105
3.05
1170
110
3.06
1170
115
3.07
1150
120
3.09
1160
125
3.09
1140
130
3.10
1160
135
3.08
1170
140
3.11
1150
145
3.06
1190
150
3.10
1170
155
3.15
1140
160
3.15
1140
165
3.15
1160
170
3.17
1150
175
3.19
1140
180
3.18
1140
(continued)
157
-------
TABLE 60. (continued)
Meters Upstream
from Tr-8 con-
Specific
f uence with
Conductance
Contrary Creek pH
(umhos/cm) Remarks
185 3.19 1130
190 3.23 1130
195 3.25 1110 Visible acid seepage along
banks from 195 to 215 in.
200 3.26 1090
205 3.25 1040
210 3.28 964
215 3.30 904 Granite riprap lining banks
begins at 218 rn.
220 3.30 898
225 3.31 875
230 3.33 831
235 3.35 801
240 3.35 773 GrGIiftc rip’-ap lininq banks
ends at 242 m.
245 3.40 715
250 3.40 708
255 3.48 641
260 3.50 624
265 3.51 612
270 3.54 621
275 3.64 519
280 3.65 510
283 3 71 457
286 3.83 359
290 3.87 332
295 4.15 245 V—notch weir at 298 in known
as Tr-7.
300 4.50 177
305 4.01 30 Tributary is poorly mixed here;
Tr-6, a polluted tributary
ente, s at 308m.
315 5.20 65 Background level of the tri-
butary tjefore entering mine
tailir 1 ys, sample taken above
V-notcn weir known as Tr-4.
Source: Dagenhart (1980).
158
-------
I
U i
‘ 0
Figure 94. pH And Specific Conductance Transect Along Tr-8 At Boyd Smith Site, June 19,1979
(Source: Dagenhart, 1980).
80
Distance to Mouth of Boyd Smith lributary (meters)
-------
SS-1 SS-2
Surface - 0.3 m (1 ft) Surface - 1.2 m 4 ft)
Middle - 1.5 m (5 ft) Middle - 4.6 rn 15 ft)
Bottom - 3.0 m (10 ft) Bottom - 9.1 m (30 ft)
S ’ice much of the lake data is highly erratic and difficult to explain,
a det ‘ .j Interpretation has not been attempted, and all of the factors af-
fecting the lake chemistry is beyond the scope of this report. Summaries of
the data comparing conditions at SS-1 and SS-2 are presented along with several
concentration curves that reflect seasonal variation. It should be kept in
mind that the Contrary Creek arm of Lake Anna covers the former stream bed
which was laden with mine wastes all the way Out to the present site of SS-2
(see sediment data in the biologic survey included in Appendix D).
Table 61 shows average, minimum, and maximum values of pH and concentra-
tions recorded at SS-1 from October 1975 to October 1979. Figures 95-102 are
plots of individual pH and concentrations determined from the semi-monthly
sampling at the surface and bottom levels of SS-1. The data gaps during the
winters of 1976—77 and 1977—78 tend to present somewhat misleading trends in
the plots for the cold weather season. The influence of seasonal stratifica-
tion in the shallow part (3 m) of the lake at SS-1 is probably slight, but
there was a tendency for all concentrations to be higher at the bottom level
during the summer months which apparently resulted from lower dissolved oxygen.
However, it appears that the influx rate of AMI) loads from Contrary Creek
exerts m’ich more influence at SS—1 than effects of stratification. A study
of the stream hydrographs did not show any significant effects of any one
storm increasng the concentrations at SS-1, but it must be realized that the
sampling represents only chance conditions ar 1,0 deliberate effort was made
to collect lake samples to determine effects of storms. The quality data
does reflect uniform conditions at all three levels after a few storms indicat-
ing a mixing of the water column.
Zinc concentration reached the SWCB limit of 5.0 mg/i only once at SS-1
(bottom level), and copper exceeded the limit of 1.0 mg/l only a few times
over the monitoring period. The extremely low concentrations of copper and
zinc during the summer of 1977 apparently resulted from negligible metal loads
being carried into Lake Anna by the meager flows during the prolonged drought,
but sharp increases in zinc and copper concentrations occurred at each depth
when rains came in the fall and began flushing out rnetals that had built up
to high concentrations upstream during the hot dry weather (Figures 97-100).
A similar pattern, though more subdued, can be seen associated with the less
severe drought of 1976. The pH curves also see n to reflect this pattern with
values in the 6 to 7 range In the summer months when flows were low and then
falling to the 3 to 5 range when higher flows were entering from Contrary
Creek. This pattern is well pronounced at the surface and middle levels, but
the curve for the bottom level (Figure 96) is more erratic where stratifica-
tion is probably a factor.
On the other hand, iron concentrations tended to be much higher at the
bottom level during the hot summer months of 1977 when dissolved oxygen was
160
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TABLE 61. SS-1 - AVERAGES, MINIMUMS, AND
MAXIMUMS OF WATER QUALITY DATA, 1975-79 (mg/i) 8
a
A (-) sign indicates that
detection.
the concentration was below the Indicated level of
Depth (m) Avg. Mm. Max.
0.3
1.5
3.0
0.3
1.5
3.0
0.3
1.5
3.0
0.3
1.5
3.0
0.3
1.5
3.0
0.3
1.5
3.0
0.3
1.5
3.0
pH
5.1
5.3
5.0
3.8
3.9
3.3
7.5
8.5
7.8
Acidity (CaCO
)
20
16
24
1
2
1
138
146
160
SO 4
34
30
42
10
9
8
129
52
205
Cu
0.11
0.12
0.27
0.01-
0.01-
0.01-
0.39
1.00
2.60
Fe
1.3
1.1
3.1
0.1-
0.1
0.3
8.0
5.8
40.0
Mn
0.33
0.32
0.57
(‘.01
0.05
0.07
1.03
0.92
14.0
Zn
0.49
0.47
0.73
0.01-
0.01
0.02
1.90
0.97
5.00
161
-------
1Q75 77 1978 1979
Figure 95. pH versus time in calendar years at surface level of SS-1.
1976 1977 197d
Figure 96. pH versus time In calendar years at bottom level of SS-1.
162
-------
2
0
0
0
6
S
1975 1976 1976 1979
Figure 97. Copper concentrations versus time in calendar years at surface
level of SS-1.
0
1:
1975 1976 1977 1978 1979
Figure 98. Copper concentrat cns versus time in calendar years at bottom level
of SS—1.
163
-------
1’
S
: Il
I I
1976 1976 1977 1978 1979
Figure 100. Zinc concentrations versus time in calendar years at bottom 1e el
of SS-1.
1975 .976 1977 1979 1979
Figure 99. Zinc concentrations versus time in calendar years at surface level
of SS-1.
164
-------
•1’
S
197i
Figure 101. Iron
of SS-1.
1g76 1977
concentrati)flS versus
1978 1S19
t ie in calendar years at surface 1 evel
1915 i976 1977 1978 979
Figure 102. Iron concentrations versus time in calendar years at bottom level
of SS-1.
165
-------
very low suggesting the influence of sut rer stratification. Manganese showed
the same trend but to a lesser degree. There appeared to be a similar trend
of higher concentrations of iron and manganese at the bottom evels during
the sumers of the other years, but none are as pronounced as In 1977. Both
Iron and manganese concentrations consistently exceeded SWCB standards at SS-
1. Sulfate and lead concentrations tended to be even more erratic than the
other parameters but they still showed the influence of the flushing out after
the buildup of concentrations during the sun ner of 1977. Lead concentrations
occasionally exceeded the SWCB limit of 0.05 mg/i at all levels. The reason
for the abrupt rise in concentrations with lowering of pH in the spring of
1976 is not clear. This spike could be associated wit 1 ’ the warmer tempera-
tures during the spring turr.over u it possibly may have resulted from the
initial disturbance of the mine wastes upstream when the reclamation work be-
gan. However, the latter posslb lity is considered remote, because a similar
pattern and much more pronounced was observed at SS-2 on the same date.
The concentration data collected at SS-2 indicated that AMO from Contrary
Creek may still be of some slight influence in this part of the lake, but
there does not appear to be nearly as much of a direct relationship to the
influx of loads dS at 5S-1. The effect of seasonal stratification is undoubt-
edly much more of a factor at SS-2 than at SS-1. A comparison of Table 61
with Table 62 gives an Indication ,f the relative concentrations at the two
stations. Concentrations were generally more erratic at the bottom level (2 m)
and exhibited some abrupt increases nich orobably resulted from oxygen deple-
tion during the sunrer moiths. The oH was the lowest in early spring ranging
from 4.5 to 5.0 and tended to reach alkaline values exceeding 7 In the sumer.
Copper and zinc concentrations reflected the same trend being lowest in the
suimuer with a gradual rise in the fall and then sharp increases in late winter.
Iron (Figures 103-104) and manganese concentrations showed a very consistent
seasonal pattern with quite uniform conditions at each level during fail dnd
winter and then a well-defined sumer stratification with concentrations In-
creasing downward. As at SS-1 the sulfate and lead values tended to be more
irregular with less defined patterns. There were seve,-al abrup’ increases in
various concentrations, the cause of wHch is not entirely clear, but same
were likely due to seasonal turnover and stratification.
Further comparisons of conditions at SS-1 and SS-2 are shown by averaging
the data from ll three deotns in Table 63 and by the solids and conductivity
data in Table 64 for five sample dates when the annual complete analyses were
run. The complete analyses also included tests for arsenic, cadmium, chromium,
and mercury. None of these metals were found above the limit of detection at
the lake stations exce t for arsenic on one occasion, and it was within SWCB
water quality standards. From all of the lake data analyzed it appears that
normal seasonal concentrations remained near the same levels.
166
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TABLE 62. SS-2 - AVERAGES, MINIMUMS, AND
MAXIMUMS OF WATER QUALITY DATA - 1975-79 (mg/1).a
Avg .
Mi n .
Max .
Depth (m )
1.2
4.6
1.2
4.6
9.1
1.2
4.6
9.1
1.2
4.6
9.1
1.2
4.6
9.1
1.2
4.6
9.1
6.7
6.6
6.5
4.2
4.4
3.7
8.3
8.4
8.2
Acidity
(CaCO 3 )
11
12
15
1
1
1
7
70
67
S04
14
13
14
2
4
4
43
42
76
Fe
0.4
0.5
1.2
0.1-
0.1-
0.1-
3.1
7.0
12.6
Mn
0.22
0.01-
3.30
0.41
Zn
0.13
0.13
0.18
a A (-) sign
detection.
0.01-
0.01-
0.01-
1.0
0.96
1.05
indicates that the concentration was below the indicated level of
I 67
-------
1’
1975 1916 1977 978 1919
Fi u’ 103. iron concentrations versus time in calenac .r years at surface level
of -2.
1975 1976 1977 1978 19 7
figure 104. Iron concentrations ver5us time In calendar years at bottom level
of SS-2.
1 6P,
-------
TABLE 63. COMPARISON OF AVERAGES OF ALL
DEPTHS AT SS-1 AND SS-2 - 1S75-79 (mg/i)
Stati i
pH
Act lity
(CaCO 3 )
SO 4
‘i
Fe
Mn
Zn
SS-1
5.1
20
35
0.17
1.8
0.41
0.56
SS-2
6.6
13
14
0.03
0.3
0.26
0.15
TABLE 64. COMPARISON OF SOLIDS AND SPECIFIC CONDUCTANCE AT SS-1 AND SS-2
Specifc
Total Total Conductance
Date ,e 2 tha Solids (mg/i) Solids (mg/i) (‘imhosjcinj
SS-1 SS-2 SS .1 SS-2 SS-1 SS-2
10-27-75 S 102 70 9 62 110 54
M 103 78 97 74 110 57
B 120 81 116 73 130 62
5-19-76 S 299 124 251 122 250 104
M 98 6 76 76 88 56
B 108 101 84 91 84 54
5-24-77 S 165 83 161 81 75 56
M 74 73 69 69 90 55
B 106 84 100 8 75 65
5—25-78 S 7? 45 75 41 103 58
M 71 49 68 45 9i 60
B 56 53 49 47 73 67
6-12-79 S 7 41 7 39 94 52
M 64 42 63 40 89 52
B 83 50 21 7 150 56
a
S-surface M-mlddle B-bottom See Page 160 for depths.
169
-------
Surmiary of Water Quality Data
A general overview of the monitoring data indicates that there has been
little improvement in the water quality In the project area since rcclamation
began. Concent.-atior.s and loads tend to be near the same seasonal levels as
before reclamation and the same general problem areas continue to persist.
T ables65 and 66 and Figures 105—108 show a comparison of ccncentratioiis and
loads by water years. The Sulphur Site is obviously still the major source
of MD with the Boyd Smith Site presenting the ledst problen anJ the Arminius
Site of intermediate consequence. ihis project has included no abatenir nt
measures on the downstream reach of Contrary Creek betwecri the Sulphur Site
and Lake Anna, and no reclamation work is contemplated on this reach of the
stream.
It must be realized that the droughts of 1976 and 19 7 whch were each
followed by abnormally cold winters came at a most critical tiny ’ and serious-
ly hampered efforts to establish vegetation on the iormerly den. d areas.
Thi3 undoubtedly delayed any chance oi reali7ing any significant ducticn
of AND entering Contrary Creak. In fact, considering the Jevastatid c ndi-
tions that existed before reclamation, it was probably unrealistic to expect
any improvement within such a shnrt period even with normal seasons. More
abundant rainfall in 1978 and 1979 courled with milder falls and winters
greatly improved vegetative growth on the reclaimed sites Lut minimal gains
were realized in 1980 due to another dry summer.
Figure 109 illustrates thc sources of AMO to Cont3ry Cree¼. The major
contribution during dry periods Wã the leaching of the mine waste by water
percol ting through the waste aid the leaching of the waste deposited in the
stream bed. A smaller source was AMO flowing from nderground wcrk rigs.
During precipitation events, runoff carried AMD and mine iste from the waste
piles.
The reclamation of tie mining waste was expecten to reduce the AND loe
in Contrary Creek in several ways:
1. Removal of toxic mining waste from the stream beu at the Sulphur
Site would remove this source of AMO.
2. Grading to facilitate rapid runoff and minimize infiltration would
reduce the volume of water leaching the mine waste.
3. Development of a vegetative stabilized cover over the toxic mine
waste would:
a. Eliminate the erosion and transport of mine waste into the
stream.
b. Reduce the water available for leaching of the mine waste
as a result of plant transpiration.
c. Reduce oxygen contact with the pyrite in the mine waste and
170
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TABLE 65. AVERAGE ANNUAL CONCENTRATIONS BY WATER YEAR
AT STREAM STATIONS (mg/i)
Water Flow Acidit
Station Yi. r (l/ )a p44 (CeC0 3 504 Cu Fe Pb Mn Zn
1976 48.7 6.6 8 7 0.02 1.1 0.02 0.1 0.1
1977 32.6 7.2 8 10 0.02 09 0.01 0 2 0.1
1978 73.9 6.9 9 16 0.04 1 3 0.01 0.2 0.2
1979 66.6 6.4 25 13 0 05 1.6 0.01 0.1 0.2
1980 50.8 6.6 10 11 0.04 1.3 0.01 0.1 0.2
1976 54.9 5.4 22 93 0.15 2 3 0 03 0.8 5.9
1977 36.3 5.3 89 321 0.82 3.5 0 20 2.5 18.3
1978 87.2 5.7 27 80 0.14 1.6 0.02 0 6 4.6
1979 82.4 5.9 38 81 0.09 1 5 0 02 0.7 5.0
1980 68.2 5.8 29 166 0.15 1.6 0.03 0.8 8.1
1976 94.3 4.9 21 131 0.26 3.3 0.09 2.3 4.7
1977 62.6 5.3 38 192 0.30 1.7 0.05 3.1 5.8
1978 140.2 4.9 28 120 0.22 1.7 0.03 1.5 3.7
1979 140.5 5.0 41 116 0.14 1.4 0.02 1.6 3.4
1980 115.5 5.3 19 124 0.23 1.5 0.02 1.9 3.4
NS-4 1976 147.8 3.9 134 240 0.95 37.3 0.07 2.1 4.8
1977 94.6 3.8 238 376 1.73 54.9 0.13 2.5 7.9
1978 206.5 3.7 160 224 1.17 31.3 0.07 1.6 5.7
1979 198.8 3.6 217 196 0.79 25 5 0.07 3.7 4.3
1980 153.1 3.8 178 255 0.78 29.0 0.04 1.9 4.5
MS—S 1976 3.4 173 241 1.28 33.8 0.08 1.9 4.6
1977 3.4 322 468 3.22 58.0 0.13 2.7 8.3
1978 3.4 183 246 2.11 38.6 0.07 1.6 5.6
1979 3.3 236 178 1.19 24.9 0.07 1.7 4.0
1980 3.4 216 328 1.15 21.0 0.47 2.2 4.6
I
No continuous flow records available for MS-S.
171
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TABLE 66. AVERAGE ANNUAL LOADS BY WATER YEAR
AT MS-i, MS-2, PG—3, and MS -4 (kg/d)a
Vater F1o Acidity
Station Year (us) (CaCO3) S04 Cu Fe Pb Nn Zn
1976 48.7 43 34 0.09 3.7 0.03 3.4 0.3
1977 32.6 85 21 0.03 2.5 0.04 0.4 0.2
1978 73.9 63 66 0.30 6.1 0.04 0.9 2.1
1979 66.6 184 97 0.41 6.9 0.08 0.8 1.9
1980 50.8 41 55 0.20 5.0 0.03 0.6 0.9
P -2 1976 54.9 83 306 0.54 8.8 0.10 2.4 18.5
2977 36.3 82 311 0.58 8.2 0.26 3.2 24.7
1978 87.2 193 479 0.97 11.2 0.15 3.7 26.5
1979 82.4 321 432 0.73 9.3 0.20 3.6 26.4
1980 68.2 96 400 0.51 9.6 0.09 3.0 23.8
1976 94.3 137 830 1.8 26.0 0.55 13.4 30.5
1977 62.6 132 540 1.1 11.3 0.18 8.5 22.0
1978 140.2 320 1177 2.0 21.2 0.36 15.5 39.5
1979 140.5 617 1026 2.0 19 3 0.32 15.1 32.2
1980 115.5 160 699 1.4 16.9 0.16 12.5 27.5
NS-4 1976 147.8 1130 2188 8.4 323 0.6 18.5 46.0
1977 94.6 1080 1709 8.8 371 1.0 14.2 46.5
1978 206.5 2421 3242 18.9 493 1.4 26.2 87.5
1979 198.8 3186 2663 11.4 354 1.0 20.7 58.5
1980 153.1 1543 2300 7.7 281 0.4 17.8 46.3
a
No continuous flow records available at ) S-5.
172
-------
Figure 105. Comparison of average copper concentrations by water
year at affected stream stations.
173
-------
FIgure 106. ComparIson of average zinc concentrations by water year
at affected stream stations.
C
174
-------
10.0
Figure 107. ComparIson of average copper loads by
water year at affected stream stations.
1.0
V
0’
0.1
0.01
175
-------
oo.o
C
NS-2 MS-3
Figure 108. ComparIson of average
year at affected stream stations.
zinc loads by water
176
-------
RUNOFF OF AMD
AND MINE WASTE
FIGURE 109. SOURCES OF ACID MINE DRAINAGE INTO CONTRARY CREEK
(NOT TO SCALE)
INFILTRATION
.1-
-4
LEACHING OF AMD
FROM MINE
WASTE
CONTRARY CREEK
LEACHING OF AMD
FROM MINE WASTE
MINE WASTE
-------
thus reduce the formation of AND by development of a soil
cover with vegetation.
4. The sludge and limestone added to the mine waste would neutralize
and treat the AND previously generated in the mine waste and reduce further
generation.
The reduction of erosion and transport of mine waste into the stream
and the reduction of overland flow of AND to the stream has been accomplished.
Erosion control was discussed on page 88. Since the surface soil now has a
higher pH and lower concentration of heavy metals (Table 34. P.97), the runoff
quality is undoubtedly Improved. Thus, the remaining major sources of AND
are the mine waste in the stream bed and the leaching of the mine waste mate-
rial. There is no way to measure the contributions each of these AND sources
has to the overall problem. Some Indication of the contribution that the
mine waste deposited in the stream bed has on water quality can be seen by
comparing the load data from MS-4 and MS-5 on a date when flows were extremely
low in the suniner of 1977 (Table 67). The only source of AND in this section
of the stream is the deposited mine waste. Although some mine waste was re-
moved from the stream In the vicinity of the sulphur Site, large quantities
still remain and the reducton from this source of AND is probably Insignifi-
cant if at all.
TABLE 67. COMPARISON OF LOADS AT MS-4 AND MS-5 ON BASIS
OF INSTANTANEOUS FLOWS ON AUGUST 18, 1977 (Kg/d)
Station
Flow(l/s)
Acidity
(CaCO3
S04
Cu
Fe
Pb
Mn
Zn
MS-4
3.40
6489
411
1.4
44
0.07
1.8
4.7
MS-S
5.66
18490
979
5.4
98
0.18
3.8
17.6
The impact of regrading, vegetation establishment, and addition of sludge
and limestone on the leaching e the mine waste will require several years to
document. There Is no way to a cually measure the quality and quantity of
leachate reaching the stream thus the impact must be measured by monitoring
the stream. As noted, to date the monitoring data Indicates there has been
little improvement in the water quality. This result may mean that the stream
bed source is the overriding factor. However, if we look at Table 57, we see
that the specific conductance Increases 125 units between 1200 and 2100 meters
or an increase of 0.14 unit per meter of stream. The only contribution in
this area Is mine waste In the stream bed. If we assume this to be the rate
of release by stream bed material then the release for the 800 meters of
stream through the Sulphur Site would be 112 units. However, the actual
Increase is 553 units. Thus, we can conclude that the major source Is the
AND leaching from the mine waste banks. (See Study by Nordstrom in Appendix
9).
Because of the long existfnce of the mine waste banks, we can assume that
178
-------
they are saturated with pyrite oxidation products — AND. Thus, even if all
new production of AND was eliminated, a significant tlniew3uld be required to
leach the AMP material from the mine waste. The reduction in Infiltration
will only extend this time pe—iod. The effectiveness of the soil cover in
reducing acid production is surely debatable, and several years will be re-
quired to collect the information needed to make any conclusions based on
stream water quality. The sludge and limestone applied to the mine waste
should neutralize some of the AND In place. Several years may be required
for this chemical front to move through the mine waste and be reflected In
stream water quality.
So far as can be determined, fron BOD and fecal coliform analyses, the
extensive use of wastewater sludge at all three mine sites has not affected
the water of Contrary Creek or Lake Anna in any adverse manner nor created
any health hazards. The Contrary Creek arm of Lake Anna is obviously degraded
by AND as far out as SS-1 in the lake, but the main body of the reservoir
appears to be unaffected. The lake abounds in sport fish, anJ there have been
no known detrimental effects by AMD on the nuclear power plant wh ch uses the
reservoir for cooling water.
In conclusion, rapid changes in water quality cannot be expected to
show up in Contrary Creek. Severa 1 more years of mDnitoring will be re-
quired to evaluate the efPectiveness of the remedial action.
BIOLOGIC STUDIES
Both prereclamatlon and postreclamatlon biclogic studies have been con-
ducted and are continuing semiannually. As stated in Section 3, ecological
surveys of Contrary Creek and the North Anna River were performed by VPI&SU
prior to the construction of Lake Anna which show€d aqu t1c life to be severe-
ly affected by AND, and reveai d that the North Anna River did not fully re-
covtr for at least 8.7 k1lon ” ters (14 miles) downstream. All subsequent
biologic studies have been conducted by the DES of the SWCB. A prereciama-
tion survey of the Contrary Creek arm of Lake Anna by the DES in the spring
f 1974 is surmiiarized in Section 10 and the complete report appears in
s ppendix 0.
After the reclamation wo 1 ’k in 1976 the DES conducted cursory benthic
surveys of Contrary Creek each fall and spring except for the fall of 1977.
Quantitative samplings were done each spring from 1978 to 1980. The cursory
investigations consisted of walking the stream and qualitatively appraising
the kinds and numbers of benthic Invertebrates preseri ‘n rocks, twigs, leaves,
and other vegetative debris In riffle areas at each station. For the quanti-
tative samplings a Surber square foot sampler was used to collect benthics
at each station and organism counts were made. Tests for pH and dissolved
oxygen along with temperature readings were made during each survey. Figure
110 shows locations of the sampling stations. BS-1A was not included In the
first survey.
The first cursory survey was conducted In October 1976. No benthic life
was found In Contrary Creek at BS-1 below the Sulphur Site. This sterile
179
-------
I T T. e’ f -‘
- r 7 ‘ /Zk t, V/A
/
•BS 0 BIOLOGICAL STATiON / V 7
t4. SITE /J4 f7j <75, —
?
C , . ..
—
r v
‘2 _____
_ J? 4 :
‘)
FIGURE 110 .cONTRARY CREEK BIOLOGICAL STATIONS
-------
condition was In part attributed to the heavy coating of ferric hydroxide
(Fe(OH) 3 ) that covers the substrate throughout much of the stream as It flows
through the Sulphur Site. Ferric hydroxide smothers benthic organisms which
breathe throt gh gills and covers the habitat of others. Of course tne high
acidity alone Is enough to render the stream sterile.
At BS-2 which is located within the Sulphur Site, a few tolerant and
facultative forms of benthics were observed, but most were on vegetation
hanging down into the water rather than In the stream bed. Colonies of fila-
mentous bacteria were found in pools butlack of periphytic algae gave the
rocks a sterile appearance. The prevalance of toxic conditions was evidenced
by the low density and moderate diversity of organisms.
A low-density population of benthos was found at BS-3 which is in a wide
gravel bar just upstream of the Sulphur Site. Caddisflies were 3bserved here,
but most organisms were still on leaves rather than on rocks, and filamentous
bacteria were again abundant in pool areas. At BS-4 ininedlately below the
tsoyd Smith Site more facultative forms were found along with a few sensitive
types. Although the density of populations was still low, the shift toward
more sensitive organisms was encouraging.
BS-5 is apprpxinately midway between the Arminius and Boyd Smith Sites
In a shaded reach of the stream. Here benthic populations were considered t
be a step closer to normal conditions for a clean stream. Diversity of orj -
isms remained high and sensitive forms were more abundant. lowever, the
density of the population was still far below normal and the lack of periphyton
still gave the substrate a sterile look. Most organisms were found on vegeta-
tive matter.
At the control station BS-b just upstream from the Arminius Site and
above all of the affected reach of Contrary Creek, the most iotable change
was the dense growth of periphytOn on rocks in the stream. Periphytic lire
was non-existent at all stations at and downstream from the Arninius Site.
Both density and diversity of benthic life increa3ed at the control station
and more sensitive types were found. This was the only part of the stream
where minnows were seen and neither hydroxide ror filamentouS bacteria were
present.
In sumary there was a gradual progressive improvement in benthic oopu-
lations upstream to the control station but even BS-5 below Amnlus was
seriously degraded. The change from tolerant a .d facultative forn to rr.ore
sensitive forms was most apparent, and only at the control station did the
density of benthics Increase enough to assume that they represented a repro-
ducing resident co,nnunity. Absence of periphyton In the affected part of
the stream was a clear Indicator of toxicity resu 1 tlng from AND. Result of
the October 1976 survey are shown in Table 68.
The second cursory survey conducted in April 1977 began with an addition-
al station BS-1A, at the mouth of Contrary Creek. Here the stream Is bordered
by a wide barren floodplain of sediments that have been washed downstream.
Riffle areas are poorly developed and pools are shallow with hydroxide cover-
Ing much of the substrate. Low numbers of tolerant organisms comprise the
181
-------
TABLE 68. CURSORY BIOLOGIC SURVEY - OCTOBER 1976
Do
Station mg/i
T . St earn Size
p 11 °C WaD
Nacrobenthic
Substrate 1 .vertebrates a
Cocments
8 5-1
2.2 4.5 19 5. a 10cm Fe(OH) 3
Sand
Rocks
6.6 4.3 19 4. a 15cm Sand
Gravel
Roots
Rocks
Fe (011)3
one bloodwor.
Hellgr ites C
flragonffles F
Hemiptera F
Whirlegig beetle F
Midges F
Caddisflies C
Flatworms F
I4ellgr uamiteS F
Wo er pennies F
Riffle beet’es F
Midges F
Fe(OH ) 3
cnverlng bottc,
only life fo md
In runoff pool
below sludge bank.
Very little Fe(OII) 3
much more bentii$c
life, mostly on
roots not rocks,
filainentous
bacteria in pools.
Poor riffle, most
benthics on leaves,
filamentous
bacteria i i pools.
Good riffle.
benthic density
still low but
more sensitive
forms present.
55—3 8.0 5.0 22 2m a 10cm Rocks Whirleqig beetle C
Gravel Caddlsflies F
e. s 0—agonflies F
Hellgraaillites F
Hemiptera F
Midges F
BS-4
8.8 5.0 19 n a 10cm Bedrock
Rocks
Gravel
Leaves
Tcontinued)
-------
TABLE 68. (contInued)
00
Station mg/i
pH
T irp. Stream Size
W D
Macrobenthic
Substrate Invertebrates a
Ccrmients
8.4 5.3 16 2.6in a 8cm Bedrock
Rocks
Gravel
Roots
Leaves
9.6 6.8 16 2m a 10cm Bedrock
Rocks
Gravel
Leaves
H igraimiites F
Water pennies F
Hemi ptera F
Cadd isflies F
Bloodworu’s F
Stonefiles F
Nidges F
Caddisfiles C
Water pennies C
Leeches F
Crayfish F
Stoneflies F
I4ayflies F
Riffle beetles F
Midges F
a
Letters denote relative abundance: U - dominant
A — abundant
C-ccsiTlon F-few
-a
CA )
Woodland area.
most benth lcs on
leaves, density
still low, bacteria
in pools.
Good riffle, more
periphyton. benthics
on rocks, density
increased Minnows
seen.
-------
benthic coninunity here. The conditions at BS—1 thru BS-5 were generally the
same as those observed during October 1976. Benthlc populations were domi-
nated by tolerant and facultative forms with a few sensitive types noted at
BS-4 and BS-5. Fewer dragonfly nyi phs and caddisfly larvae were observed
than the previous October, but more bacteria growth was observed. Compared
to the first survey there was a pronounced decline in the benthic coninunity
density at BS-5 below the Arniinlus Site. This decline may have been partly
due to seasonal changes. A healthy stream biota was again observed at the
control station.
The first quantitative sampling by the DES in conjunction with a cursory
survey in April 1978 indIcated that the status of aquatic life in Contrary
Creek had actually deteriorated since the spring of 1977. The study revealed
a decline in density of organisms at all stations in the affected reach of
the stream, and there was even a reduction In dern,ity and diversity of macro-
invertebrates and In periphyton growth at the control station. It is likely
that the extreme low flow during the severe drought of the previous season
was a factor because this would have reduced the number of organisms drifting
downstream and would have reduced the habitat available for colonization.
The October 1978 cursory survey showed some increases In aquatic life in
Contrary Creek for the first time, but toxicity was still having a severe
effect along much of the stream. A dense population of bloodworm midge larvae
were found to have established at BS-1A just above the confluence of Contrary
Creek with Lake Anna. These organisms are pollution tolerant, but It was
the first time any kind of life had been found at this station.
At BS-1 filamentous algae and diatoms were observed on a few rocks and
green algae were present i shallow pools along the stream banks. Bloodworin
midges were also found at this station In sand and gravel bars and on the
hydroxide-coated rocks. The presence of bloodworms may have resulted from
the nutrients contributed by the sludge used in the reclamation work. BS-2
within the Sulphur Site was found to have more aquatic life than during
earlier investigations. A few facultative forms were present in low numDers
and the benthic con nunity was again dominated by bloodworms. At BS-3 the
benthics appeared much healthier than In earlier surveys. Facultative and
tolerant organisms were dominant but a few sensitive forms were also found.
Below the Boyd Smith Site at BS-4 facultative forms dominated the benthic
coninunity and bloodworm populations were found to be lower than at the down-
stream 3 tations. An encouraging note was an increase in caddisfly populations.
The benthic conmiunity at BS-5 below the Arminius Site was not as diverse as
at BS-3 or BS-4, and bloodworms were again the most abundant organism.
Heavy deposits of Iron bacteria were found In pools and noted to be thicker
than in previous surveys. The control station was dominated by facultative
and sensitive organisms and a moderate diversity of forms. Benthics were
much more abundant than in the previous survey in April 1978.
The spring of 1979 study consisted of another quantitative sampling with
the regular cursory survey. Although the cursory survey revealed more types
of organisms than the quantitative sampling, there was really no improvement
noted in the biota of the affected portion of Contrary Creek since the pre-
184
-------
vious year. Results of both surveys appear in Table 69.
Another cursory benthic survey was conducted in October 1979. At this
time, as before, the upstream control station appeared to be In good condi-
tion. The aquatic life coninunity was similar to past observation with sen-
sitive organisms dominating a diverse assemblage of macroinvertebrateS. At
BS-5 below the Arminius site, water quality was poor with a few facultative
and tolerant organisms present. The dissolved oxygen and pH were not pro-
hibitively low at this station but the AND was definitely limiting the
benthic life. The benthic coninunity at BS-4, below the Boyd Smith mine site,
was more diverse than it had been previously but the populations were still
lower than at the control. Water quality at BS-4 was rated fair to poor, an
improvement over BS-5 and earlier BS-4 results.
The diversity of benthic types at BS-3 upstream from the Sulphur Site
was higher than it had been the previous spring and compared favorably with
conditions observed in the fall of 1978. The density of organisms and the
relative abundance of sensitive forms were not comparable to conditions at
BS-6 however, and water quality was rated fair. From BS-2 downstream, the
substrate remained covered with a thick ferric hydroxide precipitate which
fiUs in the benthic habitat and smothers all but the most tolerant species.
There was also a 2.0 mg/l drop in dissolved oxygen and a 1.1 unit drop in
pH observed at this station. Most of the organisms observed at BS-2 were
found among the streambank grasses rather than on the bottom Itself. There
were facultative forms which seem to be able to tolerate the poor water
quality found in this area. These poor water quality and habitat conditions
persisted downstream through the area of BS-1.
A third quantitative survey conducted in the spring of 1980 showed that
macroinvertebrateS were still very sparse in the affected portion of th
stream. Although no significant improvement In biologic conditions was noted,
there was an increase in dissolved oxygen and pH at stations BS-1A, BS—1, and
BS-2, which was encouraging. There was also less ferric hydroxide precipitate
observed on the substrate in the vicinity of the Sulphur Site. Results of
the 1980 spring survey are shown in Table 70.
SuiNnary Of Biologic Studies
The overall assessment of the biologic studies to date is that the toxic
conditions that have apparently prevailed In Contrary Creek for nearly one
hundred years rendering it virtually devoid of aquatic life have remained
essentially unchanged within the relatively short time interval that has
elapsed since reclamation began. There have been slight improvements In the
benthic coninunities between the Boyd Smith and Sulphur Sites, but most of the
other stream reaches below the mine sites, especially the lower end, remain
highly toxic to all but the most tolerant organisms.
185
-------
TABLE 69. CURSORY AND QUANTITATIVE BIOLOGIC SURVEY - MAY 1979
briber
Station
00
mq/%
pH
Temp
°C
Stre
W
em Size
x 0
Substrate
Nacrobenthic
Invertebrates a
Nacrobenthic
Invertebrates b
coements
OS-iA
5.2
4.0
27
Sm x
8i i
Boulders
Rocks
Gravel
Sand
Fe(OH) 3
Ilemiptera
Bloodworias
Whirlegig Beetle
Alderfly
C
F
F
X
None
Light growths of filwuen-
tous algae and periphyton.
less Fe(OH)3 than it OS-I.
Fewer midges than previous
year, poor water quality.
OS—i
4.8
4.3
24
Sm x
10c r
Bedrock
Boulders
Rocks
Gravel
Sand
Fe(0 14) 3
Hemiptera
Bloodworms
Whirlegig Beetle
C
F
F
Diptere Bacteria and green algae
Ptychopterldae I in side pools. Fe(0H) 3
coats entire substrate,
poor water quality.
BS—2
5.0
4.5
29
Sm x
15cm
Rocks
Gravel
Leaves
Roots
Clay
FeC 014)3
Hemiptera
Hellgra ites
Bloodworia
F
F
X
Diptera Very little algae.
Chlronoimas sp. I bacteria thick in pools,
Negaloptera poor water quality.
Corydalus
cornutus 1
BS-3
6.6
6.3
2?
Sm *
1 5cm
Bedrock
Boulders
Rocks
Gravel
Sand
Mel lgraam$ tes
Hemiptera
Whirlegig Beetle
F
F
F
P4egaloptera Filamentous algae moderate
Corydalus In riffle. Bacteria thick
cornutus 2 in pools. Poor water quality.
Dlptera pM & 00 higher than d n-
Ch ronosmjs sp. 1 stream.
85—4
7.1
6.5
24
Sm *
10cm
Bedrock
Boulders
Rocks
Gravel
Sand
Heimiptera
Hellgraemites
Water Penny
Alderf ly
Beetle
Nidge
C
F
I
I
1
I
None
Filamentous algae and
bacteria amderate. Fe(0I4) 3
thin coating on rocks.
a
cm
U ,.
D - deminant A - abundant C -
b Each sample is frem one Surber square foot %ampler
F - few - present
-------
TABLE 69. (contInued)
Strea. Size
Nacrobenthic Macrobenthic
00 T
Station mq/l 01 OC
W x 0 Substrate Invertebrates Invertebrates Ca ntS
BS-5 1.1 7.0 22 x 15om Bedrock
Boulders
Rocks
Gravel
Sand
85-6 8.0 7.5 19 4m x 10cm Bedrock
Rocks
Gravel
Sand
Detritus
F Diptera
F Ptychopterida
F Plecoptera
F Acroneuria sp.
X unIdenT [ ?Ted
X Heniiptera
unidenti fled
Coleoptera
Brychius sp.
-J
Ilemiptera
Caddisf ly
Stonefly
Di ptera
Dragonfly
Water Penny
Stonef 1 Ic;
Caddisflie s
Blackf lies
Water Pennies
Crayfish
Nayf lies
Riftle Beetles
Midges
Heniptera
Dragonfly
Fl.itwor 1
Cranefly
Light filonentous algae
1 In riffles, thick bac-
teria in pools. Fe(OH)3
2 thin coatIng on rocks
1 Poor water quality.
Light filonentous algae.
Diatom coating on rocks.
Low density, high dive’-
sity. Fair to good ter
quality.
C-F
F-C
F-C
F
F
F
F
F
F
x
x
x
Diptera
Siailitn’
venUstum 47
Sinailitan
vittatum I
TTpula sp. I
[ imnophilia s 1
Polypedilum si.. I
Orthocladin ! 2
ChIronoinina 1
C 1iItera
( lmidae 4
p T c e 1
Plecoptera
Nenioura_vencsa 12
Acroneuria
arenosa 2
Tn choptera
H dro !y.s! sp. 1
Mega optera
ç 1 ajus
cornutuS I
Hemi ptera
te!i iS Sp. I
(phenieroptera
PseudocloeOn sp.1
L !!ic! !! sp.
-------
TABLE 70. QUANTITATIVE BIOLOGIC STUDY - APRIL 1980
Station
00
pq/l
pH
T .
OC
Stream Size
W x 0
Substrate
ISacrobenthi c
Invertebratesa
Co.. *nts
aS-lA
8.0
4.7
16
6. x
8cm
Gravel
Rocks
Sand
Silt
Fe(OH)3
None
(Adult Dipter.) 2
Some algae on rocks.
Slight algae.
BS-1
‘.8
4.7
18
5. x 10cm
Gravel
Sand
Rocks
Some Fe(OH) 3
Side tributary
85-2
9.2
5.0
18
6. x 15cm
Gravel
Rocks
Sand
Roots
Fe(OH) 3
Stmulii sp. 1
Negaloptera
Nigronia sp. 1
Diptera
pH 4.7.
Moderate algae.
85-3
10.5
6.5
13 5. x 15cm
Boulders
Rocks
Gravel
Sand
Heterotrissocladius
— sp. 1
willows 6 pines,
riffle/pool.
Moderate algae.
Megaloptera
Nigronla sp 4
85-4
9.8
6.1
14
5.
a 10cm
Bedrock
Gravel
Rocks
Acroneuria sp. 1
Some algae.no
85-5
10.0
6.5
12
3.
a 15cm
Bedrock
Rocks
Gravel
Sand
Megaloptera
Nigronia sp. I
Sialis sp. 1
diatoms.
-------
TABLE 70. (contInued)
Ni er of
I X ) Te. . Stre Size Nacrobenthlc
Station mg /I p11 °C V s D Subs rate Invertet,rates Ccents
85-6 10.2 7.0 11 4 a 10cm Bedrock Diç era Moderate algae and
Rocks Si s1ii sp. diatoms.
Gravel kT ae) 172
Sand Si il itr sp.
Detritus (pupae) 2
Polypedilum sp. 4
I4icrospectra sp 3
Eukiefferiella sp 2
Rheotanytarus sp 2
Chironoin idae
larvae 1
In ctloptera
cpph1la sp.
(pupae) 4
Hydropsyche sp 2
Potainyla sp. 2
Ephemeroptera
Stenoneqna ap. 1
P1 ecoptera
Acroneuria sp. 4
rphfnenvjra sp. 4
Isoperla sp 1
1 genus sp 1
a
Each sample Is from one Surber square foot sampler.
-------
SECTION 10
SPECIAL STUDIES
Four special studies associated with the Contrary Creek Project are dis-
cussed In this section. The first Is a 1977-78 water quality study done to
Identify specific sources of AMD In the project area and to examine the ef-
fects of storm r inoff on the chemistry of Contrary Creek. The second is a
1974 prereclamation biologic study of the Contrary Creek Arm of Lake Anna.
The other studies are of test plots planted at the Arminius Site in 1974—75
and a 1978 metals uptake study of vegetation at the Sulphur and Boyd Smith
SI tes.
WATER QUALITY STUDY BY UNIVERSITY OF VIRGINIA
During 1977 and 1978 the Department of Environmental Sciences of the
University of Virginia conducted a special water quality study of Contrary
Creek entitled “Major Sources of Acid and Heavy Metals Which Contribute to
the Acid Mine Waters of Contrary Creek, Louisa County, Virginia.” This study
was funded from the EPA demonstration grant with the SWCB providing assistance
in field investigations. The complete text of this report can be found In
Appendix D.
The objectives of the study were:
1. To identify the specific sources of AMD along Contrary Creek and
the relative importance of each source.
2. To determine how pH and metal concentrations vary during a rainstorm
and what factors cause these variations.
3. To determine if a heavy rainstorm causes substantial increases in
metal loads.
4. To determine how heavy metals are partitioned between dissolved and
particulate phases and If there are substantial changes during a
rainstorm.
To carry out this study It was proposed that detailed sampling of Con-
trary Creek and its tributaries in the vicinity of the mine sites be conducted
during low flow and changing flow, i.e., a rainstorm event. During a dry
period efflorescent sulfates were to be collected from the surface of the
mine wastes and analyzed for mineralogical and chemical composition. The
occurrence and distribution of these soluble salts were to be correlated with
the major points of metal input during a rainstorm. Water samples were to be
190
-------
collected and flow measurements were to be made at ll regular monitoring
stations along Contrary Creek except MS-5, at two tributary stations of the
Sulphur Site, and at six tributary stations of the Boyd Smith Site. Two
longitudinal transects were to be made along each side of the Sulphur Site
to pinpoint major metal discharges. During a rainstorm water samples and
flow measurements were to be conducted at the four regular 1 nonitoring sta-
tions at the Sulphur, and the three tributary stations at the Boyd Smith.
Two additional tributary stations were to be sampled and measured at the
Boyd Smith provided manpower was available. Automatic samplers were to be
used at two of the regular stations with the other two to be sampled manually.
With the approval of the EPA Project Officer, a $14,148 grant was awarded
for conducting the study from the Contrary Creek EPA demonstration grant.
The original grant period was to be from June 1977 to May 1978, but it was
impossible to complete this study during this period because there was no
measurable flow in many of the tributaries during tI’ e drought of 1977 and
conditions were not opportune for a rainstorm study. In light of these
circumstances, the project was extended for another year and an additional
$2640 was Included in the grant to cover costs associated with the exc r sion.
The only part of the study completed In 1977 was a survey of the efflo-
rescent sulfate minerals forming during dry weather on the mine wastes along
the stream banks. During 1978 several attempts were made to conduct a full-
scale rainstorm event study as proposed, but due to the unpredictable nature
of the storms and the logistics of getting personnel from several distant
places on site at the optimum time, it was not possible to achieve this.
However, six partial rainstorm studies were conducted during 1978 In spite
of the difficulties Involved. During this period a specific conductance and
pH transect was conducted at the Sulphur Site along with Investigations
of acid seep pools In Contrary Creek at the Sulphur Site and a study of the
diurnal variation In water chemistry of the stream.
A brief suninary of the results of this study are:
1. Sources ofAilD are of three types: (a) mine effluents, (b) acid seeps
from the base of tailings piles and (c) soluble hydrated sulfate
minerals occurring at the surface.
2. Only two effluents were Identified as issuing from mine shafts and
both contribute only small proportions of the total AMD loads.
3. AcId seeps from the base of tailings piles contribute the major
portion of AND during dry neriods between storm events.
4. AND Is stored as soluble sulfate minerals in the top layer of mine
tailings during dry periods. During storm events the major portion
of pollutants Is derived from the dissolution and rapid flushing out
of these sulfates. The longer the dry period, the greater the In-
crease In metal concentrations when the rainstorm occurs.
5. ConductivIty and pH transects showed where major increases In dis-
191
-------
solved solids occur and indicated where additional reclamation may be needed.
The final report on this study was submitted to EPA and the SWCB in late 1979.
BIOLOGIC STUDY OF CONTRARY CREEK ARM OF LAKE ANNA
During the spring of 1974 the DES conducted a survey of the Contrary Creek
arm of Lake Anna to characterize the blota and heavy metals content of the
bottom sediments. Algae and macrobenthos and sediments were collected from
seven stations along with physical and chemical testing of water. Four of
the stations were In the affected part of the Contrary Creek arm and three
stations were sampled in nearby unaffected parts of the lake. The study which
Is the only one to date of the Contrary Creek arm revealed that benthic popu-
lations were generally low In diversity and density in the affected portIon
and showed a definite reduction in productivity. The populations were proba-
bly affected as much by substrate co npos1t1on as by AMD. Algal population data
clearly indicated toxic conditions and a pH and dissolved oxygen gradient was
noted from the mouth of Contrary Creek for approximately 3 kilometers out into
Lake Anna. Abnormally high levels cf heavy metals were found in the bottom
sediments with zinc and copper concentrations exceeding levels previously
associated with fish kills. Although fish had invaded the Contrary Creek arm,
the populations were found to be less dense and diverse than the main body
of the lake. Analyses of fish tissue revealed concentrations of heavy metals
In appreciable amounts, and the study warned that the fish were taking up
metals in amounts that should be monitored. This report in its entirety ap-
pears In Appendix D.
REVEGETATION STUDIES AT ARMINIUS SITE
Three sets of test plots were planted a . the Arminius Site In 1974 and
1975 prior to reclamation to study the growth and survival of different plant
species using various rates of soil additives and with no soil additives.
This study was by A. Chandler Mortimer, Consultant for Callahan Mining Corpo-
ration. See Appendix D for a report on the study.
METALS UPTAKE BY VEGETATION - NOVEhBER 1978
In the fall of 1978 the EPA contracted Hlttman Associates, Inc. to conduct
a study of metals uptake in the vegetation growing on the Sulphur and Boyd
Smith Sites. This contract was not funded from the demonstration grant. Com-
posite samples of the various plant species were collected in early November
1978 from areas of both established growth from the first two years of work
and new growth from the most recent fall seeding. Samples consisted only of
the above-ground portions of the plants and care was taken to prevent any
metal contamination from the soil. A control sample was collected from an
undisturbed area of Indigenous vegetation. Table 71 depicts plant species
present and per cent of cover at each sampling site as described by the
testing firm. Laboratory procedures are discussed in Appendix B.
192
-------
TABLE 71. SPECIES MIX AND PER CENT COVER-
METALS UPTAKE STUDY-NOVEMBER 1978
Area Species Mix % Total Cover
Sulphur West
Control Area Escaped grasses 100
Tailing Area Clover (3%), Rye (47%) 90
(Established Growth) Fescue (50%)
Tailing Area Rye (66%), Fescue (33%) 10
(New Growth) Clover (1%)
Sulphur East
Large Area Rye (50%), Fescue (50%) 10
(New Growth)
Large Area Lovegrass (20%), Fescue (80%) 90
(Established G, owth)
Upstream Flat Lovegrass (50%), Rye (20%) 50
(Established Growth) Fescue (30%)
Tipple Area Lovegrass (15%), Fescue (85%) 95
(Established Growth)
North End Rye (70%), Fescue (30%) 5-15
(New Growth)
Boyd Smith
Small Area
of sparse growth Fescue (85%), Lovegrass (15%) 5
Established Growth Fescue (85%), Lovegrass (15%) 90
Modified after Hltt-nan Associates, Inc., (1979).
The results of the metals uptake study are presented In Table 72. The
samples from established growth are generally Indicative of the more success-
ful areas while those designateca as new growth represent the more troublesome
areas that iave required several seedings.
As can be seen from the data, there appear to be no distinct trends,
although some metals tend to be higher from the more severe areas. Lead
seems to reflect this pattern more so than the other metals. In the Tailing
193
-------
TABLE 72. METALS UPTAKE o VEGETATEON (ug/g)
As Cd Cr Cu F. Hq Ni P Pb S. Zn
0.03
1400
0.1.
1.3
0.1-
6.7
26
9.0
—
220
500
1300
155
340
120
1.0
4.6
6.6
So
60
300
0.1-
0.6
4.8
Sulphur West
Contr 1 Area
0.
0.1-
60
Talling Are.
(Established Growth)
0 2-
0.1—
80
Tailing Area
(New Growth)
0.2-
0.1-
60
Sulphur Cast
Area
(New Growth)
0.2-
330
0.1-
240
2.1
345
0.8
40
Large Area
(Established Growth)
0.2-
0.1-
320
1.2
170
0.1-
40
Upstre Flat
(Established Growth)
0.2-
160
0.1-
600
4.3
140
0.1-
1200
I1ri ,le Area
(Established Growth)
3.2-
160
0.1-
300
3 2
100
0.1-
70
North End
(New Growth)
0.2.
180
0.1-
410
6.3
410
0 7
3100
Bo .l’d Smith
Small Area of
sparse growth
0.2-
800
1 5
4.3
20.9
1700
0.1-
760
8 3
180
3.5
0.1-
400
°Establlshed Growth
0.2-
700
2.5
0.7
18.8
70
0.1-
410
2 1
240
0 1
1.2
360
500
700
400
450
2- :
0.4
0.2
2.5
0.4
0.3
1.8
0.09
1.9
0.4
0.2
17.6
3.6
21
7.8
36
0.1-
0.1-
0.1-
0.6
0.4
0.3
0.2
1.2
a
These s le are a ereges of duplicates.
b
Source H:ttman Associates, Inc. (1979).
A (-) sign indicates that the concentration was below the indicated level of detection.
-------
Are’t of Sulphur West copper was found to be about three times higher in
established growth than in new growth, but in the Large Area of Sulphur East
copper was over four times higher from new growth than from established
growth. The two relatlve 1 y high zi, c values of 1200 ug/g and 3100 ug/g were
respectively from established growth on the Upstream Flat, a moderately suc-
cessful area, and from new growth on the North End, one of the more severe
areas. Iron values covered a wide range with the maximum from a small barren
spot at the Boyd Smith Site and the minimum from well established growth at
the same site. Note that samples from five of the reclaimed areas showed
higher iron content than the control. A comparison of Table 71 with Table 34,
p.97 shows no apparent relationship between metals in the vegetation and
soil, but. It must be realized that data are too meager for a really valid
test. The study reconmiended further testing for comparison of metals in the
soil with those in the plants as well as a study to trace metals uptake
through the food chain of maninals, ‘ut no further studies are planned at this
time.
195
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SECTION 11
SUIQIARY OF PROJECT COSTS
This section sumarlzes the Federal and state costs expended on the
Contrary Creek Project thru the end of FY 1980*. It will be recalled from
SectIon 5 that the original grant agreement between EPA and the SWCB provided
for 60 per cent funding by EPA with the SWCB providing 40 per cent matching
funds by in-kind services. Under the terms of the agreement EPA was to qrant
up to $225,158 provided the SWCB matched this amount with the remaining 40
per cent of the total project cost. The original grant agreement was for a
period of three years beginning in July 1975 and terminating in 1978. As
discusscd elsewhere In this report, It was necessary to extend the project
due to great difficulty In establ1shi. g vegetation and abating the AMC
problem. A suninary of Federal costs or EPA grant funds is shown in Table 73.
Detailed cost breakdowns of reclamation and maintenance are presented in
Sections 6 an 7 respectively. The $1006 for aerial photography was paid to
the VDH&T for black and white, color, and Infrared vertical coverage plus
black and white and color nblique shots. The $890 for survey work was for
close-interval contour mapping of the reclamation sites performed by the VDH&T
prior to construction. The $80 for drafting was for preparation of plates
and drawings used In the construction specifications which was done by a
private finn contracted by the SWCB.
Table 74 sumarizes SWCB matching costs expended from 1975 thru the end
of F Y80. Fringe benefits were computed by multlplyir. j personnel costs by 23
per cent. Laboratory analyses costs include all water, sludge, and soil tests,
and laboratory equipment costs were for four automatic flow recorders and re-
pairs. Miscellaneous supplies include containers for sludge and soil samples,
a winch purchased for the vehicle used in monitoring runs, no-trespassing
signs, batteries, etc. The SWCB paid $27,500 for the feasibilitj study per-
formed by Gannett Fleming Corddry and Carpenter prior to the reclc atiOn
work, but this was not part of the SWCB matching funds.
Total EPA and SWCB costs thru the end of F? 80 were:
EPA $132,038
SWCB 163,296
Total $295,334
*FY refers t the fiscal years used by the Comonwealth of Virginia, I.e.
beginnlnç July 1 and ending June 30.
196
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TABLE 73
SUMMARY OF FEDERAL FUNDS EXPENDED THRU FY 1980
1976 Reclamation Work
Construction and seeding $55,710
Stone 9,154
Straw bales 845
Subtotal $65,709
Maintenance
Spring 1977 $20,809
Fall 1977 6,909
Spring 1978 1,222
Fall 1978 7,714
Spring 197 3,b 9
Fall 1979 4,718
Spring 1980 2,687
Subtota l $47,888
Special water quality study by
University of Virginia $16,465
Aerial photography - 1978 $1,006
Prereclamation survey work $ 890
Draft of construction plans $ 80
Grand Total $132,028
This Is around $81,000 less than the $376,661 originally estimated for a three-
year period (see Table 5, Page 27). Major reasons for the lower cc.s s were
the free delivery of sludge to the project ste by the District of Columbia
and the much lower cost for 1976 reclamation work than anticipated. Pre-
construction estimate for the construction work exclusive of cost of riprap
stone was around $138,000. The low bid was approximately $88,000 and the work
was actually done for around $56,000. Cost of riprap stone was estimated at
$35,000 and actually cost less than $12,000 in the original reclamation work.
With the additional $48,000 that was spent for maintenance after 1976 the
total cost of reclamation including the survey work and draf ng thru FY 1980
was $114,567.
Based upon this total figure for construction, seeding, and maintenance
and the total of 19.5 acres measured as seeded in 1976, the average cost of
reclamation at the end of FY 1980 was $5875 per acre or $14,518 per hectare.
This includes all of the costs for riprap, straw bales for erosion control,
and irrigation. ApproximatelY 0.41 hectare of the Sulphur Site was never
197
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TABLE 74. SUMMARY OF SWCB FUNDS EXPENDED
FY 1976 - 1980
FY 1976 1977 1978 1979 1980 Total
Personnel $22,757 $17,870 $14,899 $24,482 $18,101 $98,109
Fringe Benefits 5,234 4,110 3,427 5,630 4,164 22,565
Travel 2,302 1,680 1,687 1,539 i,021 8,229
Laboratory Analyses 8,813 6,251 4,552 5,955 2,452 28,023
Laboratory Equipment 5,007 73 25 5,105
Photo Supplies 142 57 51 95 16 361
Miscellaneous Supplies 154 6 3 517 3 683
Easement Recording 27 27
Bid Advertisement 194 194
Total $44,630 $29,974 $24,692 $38,243 $25,757 $163,296
treated with sludqe and has not had any maintenance since 1976. No breakdown
of overall costs for the two sites has been attempted due to the extensive
maintenance including various application rates of soil additives and small
parcels of acreage reseeded each year. It should be realized that the major
portion of the maintenance has been performed at the Sulphur Site. For de-
tails of reclamation costs, see the tables in Sections 6 and 7.
Due to the need for continued maintenance a request was made to EPA to
extend the project for another two years until 1982. The request for exten-
sion was approved by EPA in October 1980. Under the terms of the extension
the grant was converted to a cooperative agreement and the budget was amended
to a 54:46 Federal to State ratio rather than a 60:40 ratio as in the original
grant. The total grant amount was reduced from $225,158 to $210,070.
198
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REFERENCES
1. Crockett, C. W. Climatological Suninarles for Selected Stations In Vir-
ginia. Water Resources Research Center, Blacksburg, Virginia , 1972.
2. Dagenhart, 1. V. The Acid Mine Drainage of Contrary Creek: Factors
Causing Variation In Stream Chemistry. M. S. Thesis, University of
Virginia, Charlottesville, VIrginia, 1980.
3. Environmental Protection Agency. Elkins Mine Drainage Pollution Control
Demonstration Project. Industrial Environmental Research Laboratory,
Cincinnati, Ohio, 1977.
4. Hill, R. D., K. P. Hinkle, R. S. Kllngensmith. Reclamation of Orphan
Mined Lands with Municipal Sludges — Case Studies. In: Utilization of
Municipal Sewage Effluent and Sludge on Forest and Disturbed Lard, W. E.
Sopper and S. N. Kerr, eds. The Pennsylvania State University Press,
University Park, Pennsylvania, 1979.
5. Hittman Associates, Inc. Draft Report Analysis of Selected Samples for
Metals Uptake. H_C0194/002-78-765D. Columbia, Maryland, 1979.
6. Katz, A. S. The Mineralogy of the Sulphur Mine, Mineral, Virginia. M. S.
Thesis, University of Virginia, Charlottesville, Virginia, 1961.
7. Miorin, A. F., R. S. Klingensmith ai.u J. R. Saliunas. Contrary Creek
Feasibility Study. Gannett Fleming Corddry and Carpenter, Harrisburg,
Pennsylvania, 1974.
8. Nordstrom, D. K. Major Sources of Acid and Heavy Metals Which Contribute
to the Acid Mine Waters of Contrary Creek, Louisa County, Virginia.
University of Virginia, Charlottesville, Virginia, 1979.
9. ClimatologiCal Data. National Oceanic and Atmospheric Administration.
National Climatic Center, Asheville, North Carolina, )975-80.
10. Slninons, G. M. A Pre-impoundmeflt Study of the North Anna River, Virginia.
Ball. 55. Water Resources Research Center, Blacksburg, VirginIa, 1972.
11. Sininons, G. M. and J. R. Reed. Mussels as Indicators of Biological Recov-
ery Zone. Journal of Water Pollution Control Federation, 45:2480-2492,
1973.
12. Soil Conser’atlOfl Service. Soils of Louisa County, Virginia. Report No.
16. Virginia Polytechnic Institute and State University, Blacksburg,
Virginia, 1972.
199
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13. United States Atomic Energy Comisslon. Final Environmental Statement -
North Anna Power Station, Virginia Electric and Power Company. Direc-
torate of Licensing. Washington, D.C., 1973.
14. U.S. Geological Survey. Water Resources Data for Virginia Water Year
1978. U.S.Geological Survey Water-Data Report VA-78-1. Virginia District
of the Water Resources Division of U.S. Geological Survey. Richmond,
Virginia, 1979.
15. Virginia Division of Mineral Resources. Geologic Map of Virginia.
Charlottesville, Virginia, 1963.
16. VirgInia Division of Water Resources. York River Basin Comprehensive
Water Resources Plan, Vol. III, Planning Bull. 227. RIchmond, Virginia.
1970.
17. Virginia Geological Survey. A Geologic Map of the Pyrite-Gold Belt in
Louisa and Spotsylvania Counties, Vwginia. Charlottesville, Virginia,
1921.
18. VIrginia State Water Control Board. Statutes, Regulations, Policies,
Publication No RB-1-78. Richmond, Virginia, 1978.
19. Wood, E. 1. MIne Spoil Reclamation In the Contrary Creek Watershed in
Louisa County, Virg1n a. M.S. Thesis, University of Montana, Missoula,
Montana, 1973.
200
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GLOSSARY
Acidity - A measure of the extent to which a solution Is acid. Usually
measured by titrating with a base to a specific end point.
Acid Mine Drainage - Any acidic water draining or flowing on or from mines
and affected by mining.
Alkalinity - A measure of the capacity to neutralize acids.
Benthic - Pertaining to org n1sms dwelling on the bottom of a body of water.
BOO - Biochemical oxygen demand which is a measure of the quantity of dissolved
oxygen in milligrams per liter necessary for the decomposition of organic mat-
ter by micro-organisms.
Concentration - A weight:volume ratio used In water quality analyses comnonly
expressed In milligrams per liter (mg/i).
Diabase - A finely crystalline igneous rock.
Diatom - Any of a number of related microscopic algae.
Dike - A tabular body of igneous rock that cuts across the structures of
surrounding rock.
— The angle that a geologic formation makes with the horizontal.
Dissolved Oxygen - The amount of dissolved oxygen by weight present in water
coninonly expressed in milligrams per liter.
Efflorescent - Pertaining to the whitish crust formed on rocks by chemical
ilterations under arid conditions.
Facultative — Said of an organism capable of growth under a number of specific
conditions.
Fauna - The entire animal population of a given area or environment.
Fecal Coliform - Bacteria normally found In the feces of warm-blooded animals
coninonly used as an indicator of fecal contamination of water supplies.
Gossan - An Iron-bearing weathered product overlying a sulfide deposit.
201
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Hardp — A general term for a relatively hard impervious layer of soil
occurring at a shallow depth formed by accumul . t1on of mineral matter leached
from the surface.
Heavy Metal - Any of the metals including ccpper, iron, lead, manganese and
zinc with a specific gravity greater than 4, generally having several oxida-
tion states, and readily forming complete Ions.
ydrograph - A graph showing stage, flow, or velocity of water with respect
to time.
Igneous Rock - A rock formed by solidification of molten material.
Instantaneous Flow - The discharge of a stream at a particular instant of
time expressed in cubic feet per second (cfs) or liters per second (l/s).
Load - The quantity of any given chemical constituent that a transporting
stream carries during a given time period usually expressed In kilograms per
day (Kg/d).
Macrobenthos — Bottom dwelling organisms visible to the unaided eye.
Metamorphic Rock - A rock formed by alteration of pre-ex1s 1ng rocks due to
changes In temperature and pressure.
Nutrent - An element essential to plant growth including nitrogen, phosphorus,
arid potassium.
Pegmatite — A coarse-grained igneous rock usually formed in fissures and cracks
in other Igneous rocks.
Periphyton - Sessile biotal components of a fresh-water ecosystem.
- The negative logarithm of the hydrogen-ion activity which denotes the
d gree of acidity or of basicity of a solution.
Potash — The potassium content of a soil or fertilizer in terms of K 2 0.
Precambrian - The earliest era of geologic time.
Pyrite - A comon iron sulfide mineral principally used in the manufacture of
sulfuric acid.
Reclamation - The procedures by which a disturbed area can be reworked to make
it productive, useful, or aesthetically pleasing.
Schist - A metamorphic rock characterized by parallel layers of flaky mInerals.
Sheet Erosion - The removal of a fairly uniform layer of soil material from
the land surface by rainfall and runoff.
202
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pecif1c Conductance - A measure of the ability of water to conduct an
electric current giving an indication of the total dissolved solids content
and conmionly expressed in micromhos per centimeter at 25 degrees centigrade.
Strike - The direction that a geologic formation takes as It intersects the
horizontal.
Substrate - The physical characteristics of the bottom of a stream channel.
Tailing — Wastes left from mining and milling processes.
Transect - An imaginary plane across a stream, normal to the flow direction.
Trellis Drainage - A drainage pattern characterized by parallel main streams
with tributaries entering at or near right angles.
Turbidity - The state of opaqueness or reduced clarity of a fluid due to
suspended matter.
Turnover - A period of uniform vertical temperature in lakes due to vertical
convective circulation usually occurring in the spring and fall.
203
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APPENDIX A
GENERALIZED DEED OF EASEMENT
THIS DE) OF EASEMENT, made by and between the property owner, party of
the first part, and the Commonwea1th of Virginia, State Water Ccntrol Board,
party of the second part.
WITNESSETH:
WHEREAS, the party of the first part is the fee simple owner of the
hereinafter described real estate, adjacent to and located on the waters of
Contrary Creek In Mineral Magisterial District, Louisa County, Virginia;
WHEREAS, it has been represented to the party of the first part that
the mining of minerals and the disposal of mineral waste on the said real
estate in the vicinity of Contrary Creek by previous owners has resulted in
severe water pollution problems, and has had an adverse affect on the natural
and scenic quality of the subject real estate;
WHEREAS, the Comonwealth of Virginia, State Water Control Board, has
determined that it would be in the public interest to reclaim mined areas and
to remove the said mineral waste from the said real property, and to restore
and preserve the natural and scenic qualities of the said real estate so as to
abate the continued pollution of Contrary Creek and Its related tributaries,
and to restore the said Contrary Cre to its natural state;
WHEREAS, the Conronwealth of Virginia, State Water Control Board and the
United States Environmental Protection Agency are in agreement concerning a
project to demonstrate an approach to the elimination and/or control of acid
and other mine related water pollution resulting from the abandoned mining
operations such as those affecting the said real estate. The Comonwealth of
Virginia, State Water Control Board, has determined that the said parcel of
land possesses the necessary characteristics for inclusion In the said project;
WHEREAS, the party of the first part agrees to grant a right of way and
easement over the said real estate to the party of the second part for the
purpose of accomplishing the project, goais and objectives herein described.
NOW, THEREFORE, in consideration of the sum of One Dollar ($1.00), in
hand paid, and other good and valuable considerations, the receipt of which
is hereby acknowledged, and in further consideration of the mutual covenants
and conditions hereinafter set forth, the party of the first part hereby
grants and conveys unto the party of the second part for a period of five
years f.om date a right of way and easement In the hereinafter described
parcel of land, to reclaim mined areas and to remove mineral waste deposited
on said land and to restore to their natural state those land areas and those
portions of Contrary Creek and its tributaries affected by mining operations,
to wit:
204
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(Description of Parcel)
For the purpose of adequately determining the effectiveness of the here-
in descri )ed project, the party of the first part does hereby further grant
and conv unto the party of the second part a right of way and easement to
construt, operate and maintain for a period of five years from date a water
monitoring station adjacent to and on the waters of Contrary Creek on the
above described parcel of land.
The conditions and terms of the foregoing rights of way and easements
are as follows:
a. In the performance of the herein described project, the party of
the second part will confine its activities to that land area and those
portions of Contrary Creek and its tributaries, affected by mining operations
as of January 1, 1975.
b. In the exercise of its rights herein, the party of the second
part, its successors and assigns, will utilize, preserve, protect and maintain
the natural topography and terrain of the landscape of the said real estate.
c. For a period of five years from date, the party of the first part,
its successors and assigns, upon reasonable notice, shall permit representa-
tives of the party of the second part, and the United States Environmental
Protection Agency to enter upon the said real estate at reasonable nours for
the purpose of making periodic Inspections of the reclaimed portions of the
said property.
d. For a period of five years from date no activity will be conduct-
ed on said property that would In any way adversely affect the project, goals
or objectives described herein.
e. Granting of this deed of easement shall not In any way limit the
uses to which the property, other than the reclaimed area, may be placed by
the party of the first part.
The party of the first part, its successors and assigns further grants
unto the party of the second part the following rights and privileges:
(1) For a period of five years from date, the party of the second
part, Its successors and assigns or representatives may enter
upon the said real estate at reasonable hours for the purpose
of taking water samples from the above mentioned monitoring
station.
(2) The party of the first part, its successors and assigns, further
covenants and agrees that it will not make application to any
governmental body for approval of a subdivision or resubdivislon
plan, a building or use permit, license, or zoning amendment
which would In any way violate the restrictions hereinabove
placed upon the said real estate for a period of five years
from date.
This easement is contingent upon the following:
(1) The granting of funds for the project by the United States
Environmental Protection Agency.
(2) The Initiation of the project by the party of the second part.
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APPENDIX B
ANALYTICAL PROCEDURES
WATER - DCLS
Acidity - manual NaOH titration to p11 8.3.
Alkalinity - titration by Fisher automatic titrator.
Suspended Solids — as per Standard Methods usng Reeve Angel glass fiber
filters.
Sulfate — turbidimetriC.
BOD 5 - as per Standard Methods using YSI oxygen meter.
Copper, Iron, Manganese, Zinc - argon coupled pl3sina for simultaneous deter—
niination by emission spectrOScOpY (alternate approved test procedure for
Virginia).
Lead - anodic stripping voltametry (Virginia approved alternate test proce-
dure).
Mercury - cold vapor atomic absorption.
Fecal Coliform — as per Standard Methods - membrane filter or multiple tube
as requested aid appropriate.
Turbidity - hach nephelometer.
SOIL
Titration Curve Method for Lime Requirement - DCLS
Samples were crushed and sieved through a 2 m screen. All material
greater than 2m was discarded as rock. 10-gm samples of soil w re placed
Into a series of 250-cc. Erlenmeyer flasks, and different unts of 0.04
N Ca(OH) 2 were added, using 5 cc. as the equivalent of 1 ton of pulverized
limestone per acre. Samples were then diluted to 100 cc. with distilled
water. Suspensions were allowed to stand In the stoppered flasks for 4
days with .%orough shaking twice a day. pH was determined with a glass
electrode, and a titration curve was made by plotting pH values on the
ordinate and tons of lime per acre on the abscissa. Lime requirements were
determined by the amount Ca(OH) 2 required to reach pH of 6.5.
206
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Water Extraction of Soluble Salts for Metals - DCLS
One hundred gm of dry soil or its equivalent of field moist soil Is
placed in 200 ml of distilled water in a 500-mi conical flask. The flask Is
stoppered and the suspension is shaken for a period of 2 hours or over nlqht.
The solution is filtered and the analysis made on the filtrate. The concen-
tration In the 1:2 extract, multiplied by 2 is the concentration In the soil.
p11 and Nutrient Availability - SCS
pH - Detenuined on a 1:1 soIl to water solution on a volume basis by
glass electrode.
Nutrient Availability - According to double dilute acid test method as pre-
scribed In “Laboratory Procedures, “Soil Testing Laboratory, VPIPISU Exten-
sion, MA-143, 1979.
SLUDGE - DCLS
Alkalinity, Fluoride, Chloride — diluted 1:10 with water, filtered and run by
standaid methods.
Alkalinity - Titration
Chloride — Titration
Fluoride — Specific Ion electrode
Arinonia - distillation from MgO plus titration.
Metals (except ‘lead and mercury) — acid digestion plus atomic absorption.
Lead and Mercury - see method for water above.
Total Nitrogen - Robertson method. Digested with H 2 S0 4 , FeSO 4 , CuSO 4 , and
Na 2 SO 4 plus distillation and titration.
METALS UPTAKE IN VEGETATION - HITIMAN ASSOCIATES, INC.
Grass samples were washed with distilled, deionized water an ven dried
at 80°C for 15-18 hours. After cooling, the samples were ground the best
possible mixture, divided into two portions and weighed. One portion was
subjected to dry ashing (for all elements except arsenic, phosphorus, mercury
aid selenium) and the other portion was subjected to wet ashing for analyse’s
of these elements. An dddltional portion was analyzed for boron after treat-
ment with saturated calcium hydroxide followed by ashing.
Most metal analyses were performed by atomic absorption on a Perkin-
Elmer Model 603. Iron, zinc and manganese were present In the solutions in
the ppm range and flame photometry was used to atomize the sample. The rest
of the elements were present in the ppb range and a graphite furnace (Perkin-
Elmer HGA 2100) was used to atomize the sample. Mercury was analyzed by the
cold vapor technique. Boron was determined colormetrically.
207
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APPENDIX C
METRIC CONVERSION
To Convert To Multiply By
Centimeters Inches 3.937 x 10 _i
Cubic meters Cubic yards 1.308
Hectares Acres 2.471
kIlograms Pounds 2.205
Kilograms/hectare Pounds/acre 8.921 x
KIlometers Miles (statute) 6.214 x iO 1
Liters Gallons 2.642 x 10 _i
Liters/second Cu ft/second 3.531 x io.2
Meters Feet 3.281
Tonnes (metric) Tons (short) 1.102
Tonnes/hectare Tons/acre 4.494 x 10 _i
208
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Appendix D
MAJOR SOURCES OF ACID AND HEAVY METALS
WHICH CONTRIBUTE TO THE ACID MINE WATERS
OP CO RARY CREEK, LOUISA COUNTY, VIRGINIA
FINAL Rfl’ORT
June 1, 1977 to May 30, 1979
Sponsored by a grant from the
VIRGINIA STATE WATER COWL ROL BOAR!)
MINE DRAINAGE ABAT (ENT PROJECT
in cooperation witl. the
VIRONM TAL PROTECTION AGENCY
D. Kirk Nordstrom, Principal Investigator
Thomas V. Dagenhart, Research Assistant
Department of Enviroanental Sciences
University of Virginia
209
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TABLE OF CONTENTS
Page
S ary 211
Introduction 212
Study Site 213
Sf florescent Sulfate Minerals Associated with Acid
Mine Drainage 216
Site Identification Codes 227
Diurnal Variation in Contrary Creek during Dry Weather 228
Specific Conductance and pM Transect of Contrary Creek . . . 235
The Acid Seep Pools of the Su fur Mine 243
Variation in Water C1%emistry during Rainstor ns 246
Discussion 271
Acknowledgements 273
Presentations and Related Publications 274
References 275
Tables
1. Secondary Sulfate Minerals Occurring as
Efflorescences 217
2. Secondary Sulfate Minerals Found at the Al1.ih 219
Cooper Mine
3. Secondary Sulfate Minerals Found at the Cofer Mine . . 220
4. Rainstorm of July 2, 1978 and Diurnal Study of
June 30 — July 1, 1978 229
5. pH and Specific Conductance Transect of Contrary
Creek and Tributaries at the Sulfur Site . . . . . . 236
6. ChsmicalDataforAcidSeepPools 244
7. Rainstorm of June 8, 1978 (CC—4) • 247
8. Rainstorm of June 19, 1978 (CC—4) 248
9. Rainstorms of June 20 and 21, 1978 (CC—4) 250
2 lOa
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Page
10. Rainstorm of September 12, 1978 (CC-3) • 252
11. Rainstorm of September 12, 1978 (CC—4) 254
12. Ch aica1 Data for Contrary Creek and Tributaries,
December 8, 1978 257
13. Metal Loads for Contrary Creek e.nd Tributaries,
December 8, 1978 258
Figures
1. Location of Sulfate Minerals at the Sulfur Mine . . 226
2. Midstream pH and Specific Conductance Transect . . . 239
3. Specific Conductance vs. Time (June 19, 1978). . . . 256
4. pH Conductance vs. Time (June 19, 1978) 256
5. Discharge Conductance vs. Time (June 19, 1978) . . 256
6. Zn, Fe and Al Conductance vs. Time (June 18, 1978) 257
7. Cu and Mn Conductance vs. Time (June 18, 1978) . . 257
8. Zn, Fe and Al Loads vs. Time (June 18, 1978) . . • 258
9. Cu d Mn Loads vs. Time (June 18, 1978) 258
210b
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SU).* ARY
A two—year study of a watershed affected by acid mine drainage was
undertaken to identify the specific sources of acid and heavy metal concen-
trations entering the main stream and to m1ne the variations in water
chemistry during a rainstorm. The study site was Contrary Creek locaL .4 in
Louisa County, Virginia, neat the town of Mineral. The results of this study
are s ariz.d below:
1. Sources of acid and heavy metals are of three types: a) mine effluents,
b) acid seeps from the base of tailings piles and c) soluble hydrated
sulfate minerals occurring in the top soil or on ore surfaces.
2. Only two effluents are identified as issuing from mine entrances
(shafts) and both contribute only small proportions of the total
acid and metal loads.
3. Acid seeps fran the base of tailings piles contribute the major
portion of acid and heavy metals during dry periods bet een storm
events.
4. Acid and heavy metals are stored as soluble suLfate minerals in the
top layer of mine tailings during dry periods. During storm events
th. major portion of pollutants is derived from the dissolution
and rapid flushing out of ches. sulfates. The longer the dry
period, the greater the Increase in metal concentrations when the
next rainstorm hits.
S. The.. sulfate minerals coon.ly occur as e.fflorascent coatings on
or. surfaces and mine tailings and the most abundant are me.Lanterite
(FeSO,•7U 5 0), rozenite (FeSO,.4B 2 0), and copiapite (Fe?a (SO ,) 8 (WO 2 2OH 2 O)
followed by the halGtrichite—pickingerite series and gypsun.
211
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6. pHlcoaductivity traniects have shovn where major incrsaus in
dtasolvsd solids occur end have located sources of acid seepage
wher, additional reclanation nay be useded.
212
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INTRODUCTION
! bUization of toxic metals snd acid by weathering of sulfide tailings
baa caused considerable degradation of vicar quality in the Contrary Creek
watershed located near the t n of Mineral in Louisa County, Virginia. These
tailings vets produced by active mining of massive sulfide ores occurring as
lenses in quartz—ssrtcite sad chlorite schists. Mining began around 1834 when
gossan was removed for iron ore. Later, gold, silver, copper, lead and zinc
minerals wsre mined periodically. Th. pyrice was mined for sulfur until 1922
when active mining ceased. Three mines are located along Contrary Creek: the
Armimius, the Boyd Smith and the Sulfur Mines, and large deposits of mine
tailings are found along the creek banks adjacent to each mine.
In 1974, Miorin, Kllngensmith and Saliunas completed a feasibility study
on Contrary Creek in which it was proposed that erosion and Leaching of acid
mine waters could be greatly reduced by reclamation of the tailings piles.
Reclamation began under a cooperative agreement betweun the Environmental
Protection Agency and the Virginia State Water Control Board for two of t ’ a
thre. tailings sites: the Boyd Smith and the Sulfur sitSe. The third site,
the Arminius Mine, i.e owned and maintained by New Jersey Zinc and Callahan
Mining Companies. Reclamation of Arminius also took place under the direction
of Chandler Mort iner, an environmental consultant for Callahan and New Jersey
Zinc.
The present study was sponsored by the E.P.A. and the S.W.C.B. under the
Contrary Creek Mine Drainage Abatement Project. This study was originally
directed toward answering the following questions:
1) What and where are the specific sources of major metal contamination
in Contrary Creek?
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2) Row do the pH s d metal conemetcatio i.s vary during a rainstorm?
What factors cause thes. variations?
3) Row are the heavy astsls partitioned between the dissolved end part i u—
lit. phase.? Are there substantial change. in the partitioning during
a rainstorm?
2 4
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STU’.)Y SIT !
The Coatary Creek vatershed a located at about 382’30’N and 77’54’W
near the town of Mineral in Louisa County, Virginia. It drains about a
7 square ails area and enptiss into Lake Anna, one of the st popular
recreational lakes in the state. Three nine sites are located along Contrary
Creak: he Sulfur site, the Boyd Snith sits, and the Arathius site (going
fran downstream up). Detailed descriptions can be found in the feasibility
study by Miorin, Klingenamith and Saliun.as (1974). Acid nine vaters seep
fran each site into Contrary Creek fran extensive nine tailings located at
the edge of the creek. The largest quantity of sulfide tailings are found
at the Sulfur site below vt ich the vater quality is the poorest.
215
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EPYLORZSC!NT SULFATE MINZRALS ASSOCIATED WITH ACID MiNE DRAINAGE
An .xtensivs survey of efflorescent sulfate mineralogy was completed in
the Contrary Creak watex.hsd. About 20 distinct mineral species have been
idsntl f ltd and these are listed, along with their chemical :onpositione (from
F1.ischsr, 1975), solubilitiee and appearances in Table 1. Addi:ional sulfate
minerals war, identified iron the nearby Allah Cooper Mine, north of the
Sulfur Mine and the Cofer Mine, east of the Contrary Creek watershed. These
min.rals era given in Tables 2 and 3, and they are provided as a comparison
to those in table 1. The minerals from table 1 are indicative of an acidic
aqueous environment whets. those from Table 3 are indicative of a more
neutral aqueous environment. The minerals from Table 2 indicate a high lead
in the source material and, in fact, tuttrell (1966) mentions that the ore
from Allah Cooper is dom(r ni tly spha.lerite and galena with a high silver
content.
X—ray diffractometry by the powder method has been used to identify these
minerals. Many of the minor mineral species are intimately mixed with the
more abundant minerals; thus identification has been both tedious and time
consuming. Careful attention has been given to the physical appearance, mode
of occurrence and associated minerals in order to facilitate field identification
of mineral hand specimens in the future. A brief desc..iption of each mineral
is given below.
M.lant.rite occurs as light greenish—blue, vitreous, botryoidal to
granular crusts on maseivs sulfide boulders and on stream sediments associated
with acid seeps at the base of the mine dumps. It dehydrates to rorenite
during dry weather and is usually associated with it. Thi. dehydration is
rsvarsibl. if the humidity rises sufficiently, thus melanterite is on. of the
most coom minerals at the Sulf,ar Mine during damp periods. It should be
216
-------
TA8LE 1. SECONDARY SULFATE MINERALS OCCURRING AS EFFLCR(SC(NC(S
IN FORMULA SO1.UBILITY DESCRIPTION
C on Minerals :
ø lanterite FeSO4 7H20 Soluble Vitreous, greenish-blue to
white, translucent grains
Rozenite FeSO 4 •4H 2 0 Slowly soluble White to tan earthy crusts
Koplapite FeFe 4 (S0 4 ) 6 (OH)2 •20H 2 0 Very soluble Bright yellow to brownish. parly to
waxy luster, clayey texture
Nagneslocopiapite MgFe 4 (S0 4 ) 6 (OH) 2 ‘201120 Very soluble Bright yellow to brownish, pearly to
waxy luster, clayey texture
Ali inocopiapite A1 6 7Fe 4 (S04)6(OH)2 ‘201120 Very soluble Bright yellow to brownish, pearly to
waxy luster, clayey texture
rerr copiapite Fe. 67 F( 4 (S0 4 ) 6 (OH)2 ‘201120 Very soluble Bright yellow to brownish, pearly to
waxy luster, clayey texture
I lalotr ichite . I?(SO4)4 ‘221420 Soluble Silky white radially fibrous spheres
Pickeringite MgAl 2 (S0 4 ) 4 .221120 Soluble Silky white radially fibrous spheres
Gypsta CaSO4 ‘24423 Slightly soluble White to grey, earthy to vitreous,
transparent to opaque, In grains
bladed crystals, and asbestifor,
fibers
t ’cc mxn Mh,ereh :
#Ferrohexahydrite FeSO 4 .61120 Soluble White sugary botryoidal crusts
#Siderotil FeSO 4 .51120 Soluble Light blue, white or yellowish,
granular or botryoldal masses
Szo.olnokite Fe 50 4 .1120 Soluble White earthy crusts
-------
TAtE 1 (Continued)
FORMUtA SOLIJSILITY 0€SCRIP I IOM
Jarosite KFe 3 (S04)2(Oii)e Insoluble Orange-yellow resinous rains
Chalcanthite CuSO 4 .51120 Very soluble Vitreous turquoise blue translucent
grains
Alunogen Al 2 (S0 4 ) 3 •18l120 Very soluble White subvltreous grains
Scarce Minerals :
RP oclase ucFe(So4)2 .41120 Slowly soluble Pearly white subtranslucent platelets,
clayey texture
Fibroferrite Fe(Oil)(50 4 ) .51120 Soluble Silky white matted or radiating fibers
Coquinthite Fe 2 (S0 4 ) 3 •9ii O Very soluble Earthy to vitreous, white to pale
lavender grains
Paracoquiwhite Fe2(S04) 3 .91120 Very soluble Vitreous pale lavender grains
Antlerite Cu3SOq(0H)4 Insoluble @ Vitreous emerald green to dark green
crusts and grains
brochantite Cu 4 50 4 (Ofl) 6 Insoluble @ Drusy yellow-green to dart green earthy
crusts
• — found previously by Mitchell (lSlfl and/or Katz (1g61) es well as during present study.
* - not found during this study, noted by Katz (196 1).
• - readily soluble in acid.
-------
TABLE 2. Secondary Sulfate Minerals found at the Allah Cooper Nine
N e Vor.ula Solubility Ieacription
Brochantite Cui SOi(OH)i Insoluble, e.erald kreen, translucent to opaque, vitreous to earthy
Linarice PbCuSO 1 ,(Qll) 2 Insoluble, dark azure bloc, traneluc nt to opa’iue, vitreous to earthy
Angleelte PbSO, Insoluble, colorless to white, transparent to opaque, adanantine to
to earthy
Leadhillite 7 Pb , ,SO (cO,) 2 (OH) 3 Insoluble, @ colorless to white, transparent to opaque. ada antine to
earthy
— readily soluble in acid
-------
TABl. 3. Secondary ulinerals foend at the Cofer Mine — Prospect
None Por.ula
Antlerite Cu,SO. ,(Oil).
Drochantite Cui ,SOu , (Oil).
Chalcanthite CuSO , 5H 2 O
Gypsum C aSO , ,2H2 0
Linarite PbCuSO 1 .(OII)z
Malachite Cu CO, (OH) 2
Serplerite Ca(Cu,Zn) ., (SO..) 2 (Ou) 3li O
— readily soluble in acid
Solubility
Ineoluble, e
Insoluble,
Very Soluble
Slightly Soluble,
insoluble,
Insoluble,
Insoluble, 0
Description
dark green, earthy to vitreoue, opaque
to translucent
green to greeniab-blue, earthy to
vitreous, opaque to translucent
turquoise blu, earthy to vitreous.
opaque to translucent
white to gray, earthy to vitreous,
trdulsparent to opaque
dark azure blue, earthy to vitreous.
transparent to opaque
emerald green, botryoldal to powdery.
waxy to edrihy, opaque
blue-green, earthy, opaque
-------
noted that 1 ancertce and the following four minerals contain the divalent
ferrous ton. Tb. reduced state of iron suggests that these minerals are slow
to oxidize further to ferric Lroo even though they are exposed to the a osphere.
The reduced state of iron also suggests that these minerals are sufficiently
short lived to preclud, extensive oxidation. These observations agree veil
with the fact that the ferrous sulfate. tend to occur in unsheltered locations
wh.re they are stable only during dry periods, from the tine of their crystalli-
zation until the next rain. Melanterice frequently has trace metals substituting
for iron in its structure, e.g. up to 7.2: Zinc. 15.02 Copper and L.9 Manganese
(Pal.ache ,t al, 1951, p. 501) and can be an inportant source of heavy metals
during a rainstorm.
Ferrohexahydrite occur, as white, sugary, hotryoidal crust, on waste
rock at the base of nine taill..g pile.. One would expect to find ferroh.za—
hydrite co only as an intermediate phase in the dehydration of nsl.anterite
to rozentts; however, this mineral has only been found infrequently and vitbout
melanterite and rozenite. The six—water form is apparently stable only under
a very restricted range of environmental conditions or when it incorporates
trace metal impurities into its structure.
Siderotil is found in light blue to yellowish to white, granular and
botryoid.a]. masses on rocks and wood associated with acid seeps at the base
of the mine dumps. Siderotil is also a logical intermediate mineral phase
in the formation of rosenite from nelantertts. Nevertheless, it is not
found with nelanterite and the only occurrence with rozenite shows no signs
of dehydrating to th . four-water salt. Jambor and Traill (1963) determined
that siderotil could crystallize directly from solution and that it is only
stable if at least 52 of the iron is replaced by copper. They found siderotil
with as ench as 1.1.22 copper. Theref ore the presence of sideroUl suggest.
significant trace metal substitution at the Sulfur tine.
221
-------
gosenite is probably the st coonly encountered etn.ral on the d ps
of the Sulfur Mine. It occurs as white to tan, earthy coatings on massive
suit idea and on creek sediments at the baa . of the dumps. Rozenite is
especially notable when it forms a sn ’ white powder on the dark brown
iiaonitic veathexix4 rinds of nasal”. sulfide boulders. It La frequently
mixed with m.laiterite on the sediments t th. base of the “ne dumps.
Unlike the other ferrous sulfates, szomolnok.its tends to be found
with the ferric sulfates, copispite and rhonboclase, and with gypsum. It
appears as a white earthy crust intimately mixed with these minerals. It
seens to be found in sheltered places with the ferric species where t can
exist long enough to form by dehydration, or it is found on rocks exposed
to full sunlight where dehydration can be accelerated by heating of the rock.
Rhomboclue is found as pearly white subtrutslucsnt platelets with a
elaysy texture enrusting copiapite. Szomolnokite has also been found with
rhomboclase. Rhomboclase and the next four minerals are ferric sulfates and
usuel.ly occur in sheltered locations where the mineral efflorescences have
remained exposed to the atmosphere long snough for ferrous iron salts to
oxidize to the ferric state i.e. beneath protruding mine timbers, beneAth
rucks and under overhanging banks.
Pibroferrite occurs as silky white aggregates of matted fibers and as
radioting fibers on copiapite. The matted fibrous texture is diagnostic in
hand specimens. It i.e found only scarcely and in sheltered locations.
Coquimbite and psrscoquimbtte are found as tine crusts on copiapite.
Tb.. snail pale lavender to white grains have a vitreous luster. Because of
their small quantities and scarce ccurrsnce it is difficult to isolate from
copiapite.
222
-------
Copiapits La on. of the mor. coemon minerals at the Sulfur Mine and it
is frsquemtly mistaken for native sulfur. Uncombined sulfur may occur at
the mine but it would be found in inaccessible subsurface reducing environ—
monte and not exposed to the atmosphere in evaporative zones like coptapite.
Copiapit. ii impcrtant toe only as a major secondary mineral in the deposit
but also as a substrate for many of the scarce minerals with which it is
associated, i.e. rhomboclass, fibroferrite, paracoquimbite and szoool.nokite.
Copiapite i.e bright sulfur yellow to brownish yellc.w with a pearly to waxy
lustec. It i.e composed of microscopic trarsparent plates which occur in
botryoidal to shapeless masses. Some earlier researchers at the deposit
sug8esced a chemical relationship between coptaptt. and old wood. Rowever,
it appears that copiapite and wood occur together frequently becaua.i the wood
provide. the necessary mechanical shelter. Copiapite nay contain up Co 2.0:
Zn, 4.62 Cu (Palache et al., 1951, p. 625) and perhve other toxic metals due
to isomorphoua substitution of various metal cationa for iron. Thus, since
it rudily dissolves witen a blowing rain flushes its sheltered sites, trace
metals can be released. Chemical analysis on many samples f copiapite from
toe Sulfur line is curventlj in progress to determine the degree of trace
metal substitution. Copper has een detected in all copiapite samples tested.
Jarosite is found as orange—yellow resinous grains associated with
copiapits and psun. It occurs only sparingly at the mine and it is
intimately mixed with other minerals. Thus it is difficult to isolatu and
analyze. This difficulty it most unfortunate since ja:osite belongs to a
large isomorphous series of minerals end -jould be expected to contain various
metals substituting for potassi and iron. flovever, jarosite is the most
insoluble sulfate mineral found and would not contribute a signifieat.t amount
of heavy metals to Contrary Creek durth a rainstorm. Jarosite ii sometimss
confused with th. yellow ocher variety of goethite. Rowever. where jarosite
223
-------
does occur with go.thite at the Sulfur Mine, the goethite is a distinctive
brown.
Ealotrichite and pickeringite are found as silky white, radially fibrous
sphere. frequently associated with alunogen and occasionally with chalcanthite.
The minerals are co anly found as an efflorescent crust on fine grained
sedimen:. In ths creek bed, also as well developed crystals under overhanging
rock.. These two minerals are treated together since they belong t,j a group
of minerals chemically and structurally very similar. Minerals of this group
contain as much as 3.02 Zn and 6.82 th (Palache ecal., 1951. p. 522—529).
Pickeringite may not be a valid species from this locality. The bulk chemical
analyse. underway at present should reveal tie degree of isomorphism and
chemical substitution.
Chalcanthite is found as turquoise blue vitreoun grains on quartz pebbles
In the creek and on mine timbers. It is associated with pickeringite, alunogen,
copiapice and siderotii ..
Antlarite occurs as vitreous, emerald—green to format—green grains on
fine grained mine spoils adjacent to the creek. It has only been found at
one location on the mine dumps, but here it is plentiful and mined with
gypsum. This mineral is quite insoluble. The same mineral crusts have remained
essentially unchanged through many months of exposure to rain.
Brochantite has not been found at the Sulfur M .ne during this study.
Rovever . Katz (1961) found brochantite as drusy yellow—green to dark—green
earthy crusts, but only in minute quantity. In surveying the secondary
minerals at the nearby Cot er mime, the author has found abundant brochantit.e.
Alunogen is seen as white subvitreous grains generally associated with
halotrichite—pickeringite and sometimes with chalcanthite. Usually it is
found forming on fine grimed sediments in the creek bed. Alunogen, as well
as halotrichite and pick.ringite contain aluminum and are aa indication
224
-------
of the dissolution of soils, sedinents or bedrock by subsurface acid
water.
Gypsum is very co on at the Sulfur 1ine, occurring in many different
forms. With antlerite it is a grey—white earthy mass. With copiapite and
jarosite it develop. vitreous, transparent, radiating, bladed crystals.
Gypsum also is found as white granular to asbestiform masses wtth szooo]nok.tte.
Gypsum is frequently seen as a ring on quartz p.bbles partially i=ersed in
Contrary Creek. The calcium sulfate precipitate. at the air water interface
on pebbles. Gypsum is probably the most coon efflorescent sulfate in
acid nine water environments.
Figure 1 shows the locations of sulfate minerals at the Sulfur site
on the map drawn by Katz (1961). Some of the features napped by Katz have
been altered somewhat by the recent recLamation efforts.
225
-------
Key To Representative Mineral Locations :
H — melanterite, rozenite 2
C copiapite / 3.
H — halotrichite—pickeringite, alunogen /
R — rhomboclaae, fibroferrite, paracoquimbite / 5
J — jarosite 41 6.
A — antlerite
C - gypsum
Ch — chalcanthite
F — ferrohexahydrite, aiderotil
S — szomolnokite
EXPLANATION
Northern—Most Shaft (Vertical)
Exploration Pit
Vertical Shafts
Tailings
Storage Bins
Probable Mill Site
Lake
1
op .
8.
9.
10.
11.
12.
13.
14.
15.
16.
17.
Main Dump
Main Buildings
Tipple
Main Shaft (Vertical)
Ore Shoot
Probable Cable Hoist
Old Gossan Pits
Old Gossan Pits
Southern-Moe t Shaft
Loading Shoot
FIGURE 1. LOCATION OF SULFATE MINERALS AT THE SULFUR MINE SITE
-------
SITE !DE2FrIFICATION CODES
Contrary Creek SWCB No. Site Description
CC—i MS—i A few .ters upstrsan fran
Arminiu.s Mine (gauge site)
CC—2 MS—2 Several aecers downatrean fran
Arminius Mine (gauge site)
CC—3 P 1 5—3 Just below Boyd Smith Mine at
bridge crossing (gauge site)
CC—4 P1 5—4 Downstream a few meters from 522
bridge (gauge site)
Tributaries
Tr—L Tr—l Tributary on west side of Contrary
draining south bank of tailings
pile
Tr—2 Tr—2 Shaft drainage Located between
between green pond. and Contrary
Creek on east side of creek
Tr—d Tributary above shaft drainage
from Boyd Smith Mine
Tr—6 Tr—6 Shaft drainage at Boyd Snith
Mine
Ir—7 Tr—7 2—3 meters below confluence of
tr— .4 and Tr-6
Tr—8 Tr—8 Main drainage from Boyd Smith
Mine a few meters fran confluence
with Contrar/ Creek
Tr—9 Tr—9 Diversion ditch upstream from Tr—8
Tr—lO Tr—lO Diversion ditch downstream from
Tr—8
227
-------
DIURNAL VARIATION IN CONTRARY CREEL DURING DRY W.A R
On Jim. 30 and July 1, 1978, $ study vs. undertakefl to deteruine if the
abrupt changes observed during s rainstorm are superimpos.d upon any regular
daily variation in the baseline chsmiatry and discharge of Contrary Creek.
Th. data (us Table 4) dsmonstrate that a very slight variation occurs with
a twenty—four hour periodicity.
A. Variations in Discharge
Th. daily discharge peak.s around nc on and falls to a minimum about midnight
at nitoring station •4. The difference between naximim and minimum f love
for a given day is on the order of ten percent which is within the error
range for a single discharge measurement. However, this difference is signifi-
cant because continuous monitoring reveals a relative difference in gauge
height which indicates a real change of flow. On the gauge height recorder
the diurnal discharge fluctuation ha, been observed for almost every dry day
during the suer of 1978. The daily peaks and troughs are themselves super-
imposed upon a gradual long term flow decrease. As groundwater seeping into
the creek slowly decreases, the average daily discharge as well as the maximums
and n1m g gradually fall during the dry spell after a storm. Of course,
the averag. daily discharge never quite reaches a steady value before another
rainstorm cones along and raises the water table. Prel 4n*ry investigation
of gauge height recordings for the late autumn and winter show a general
absence of the peak and trough effect. However, the gradual, dry weather
decrease of average daily flow in response to the falling water table still
occurs during cold periods. Thu seasonal absence of the diurnal peak and
trough effect suggests that a warm weather mechanism is responsible for the
cyclical flow variation. Evaporation directly from the creek and/or
228
-------
flate and Tts”e
TABLE 4 — The Rain jtor of July
June 30 to July 1,
2, 1978 and Diunial Varlaclun Study
1978, StatIon 94, Contrary Creel
PIe I A) Conccntrat 10319
Cu Zn
Metal Load* ( /.)
SpecIfic
Conductance
p11 (3rDhos/cm)
lie Igist
(It) (cIa)
Fe Al Ha Cu Zn Fe A) Ha
June 30, 1978
3:05 pa
4:05
3.00
2.98
—
—
.870
.865
1.97
1.86
1.36 6.67
1.32 6.70
1.33 6.86
—
—
—
— 2.65 75.9 372
— 2.60 69.5 353
— 2.62 70.1 361
—
—
—
—
—
—
148
1 )7
138
5:05
2.91
—
.865
6.84
— 2.47 69.0 360
—
—
130
5:35
2.96
—
—
.865
.865
1.86
1.86
1.42 6.97
—
— 2.70 74.8 367
—
—
142
6:05
N)
N)
‘.0
1:05
2.93
—
.860
1.74
1.51 7.07
1.42 7.05
—
—
— 2.67 74.4 348
— 2.64 70.0 347
—
—
- ‘
—
332
130
8:05
2.98
—
.860
1.74
1.74
3.55 7.24
—
— 2.70 76.4 337
—
—
133
9:05
2.97
—
.86G
7.09
—
— 2.58 76.4 349
—
—
127
10:05
2.97
2.97
—
—
.860
.860
1.76
1.74
1.46 1.16
—
— 2.61 71.9 353
—
—
129
11:05
12:05
2.97
—
.860
1.74
1.50
6.97
—
—
2.61
73.9
343
—
12 3
July 1, 1978
3.74
1.50
6 80
—
—
2.61
73.9
335
—
129
1:05 aa
2.96
—
.860
1.48
6.82
2.33
72.9
336
126
2:05
2.97
—
.860
1.74
1.49
6.82
—
—
2.53
73.4
316
—
125
3:05
2.97
2.99
—
—
.860
.860
1.74
1.45
6 84
—
—
2.35
71.5
337
—
126
4:05
5:05
3.00
—
.860
1.74
1.47 6.72
1.39 6 77
—
—
— 2,50 72.4 331
- 2.53 68.5 334
123
126
6:05
3.00
—
.860
1.38 6.15
—
— 2.43 72.7 336
129
7:05
3.00
—
.8( 5
1.86
6.63
—
— 2.63) 71.7 350
—
—
137
8:05
3.01
—
.865
1,86
2.46 73.7 356
—
—
130
10:05
3.01
—
•$f 5
870
1.86
1.9!
1.36
1.31
.43
6.35
—
—
2 32
2.53
11.6
73.1
339
11:05
12:05
1:03 p.
2:05
3.0)
3.00
3.00
2.98
—
—
—
—
.8733
.86%
.81.5
1.97
1.86
1.86
1.36
1.28
1.36
6.25
6 45
E..JI
—
—
—
—
—
—
2.51)
2.33
‘ ‘
73.9
67 4
‘•
369
340
‘33
— 342
- 339
I ll
-------
TAbIJ 4 - (continu ed)
Spcc tile
Conductance
(iusho ’/cm)
Dt charge
(c ia)
Cauge
Height
(it)
Pb ta1 Concentrations
(m /t.)
P ta1 thad ’ (mu/a)
0
Onto end Time
pH
Cu Zn
Fe
Al I4 Cu Zn
Fe
At
*i
3:05
2.95
—
.860
1.74
1.45 6.55
—
— 2.71 71.5 323
—
—
134
4:05
2.96
—
.860
1.14
1.45 6.77
— 2.70 71.5 334
13)
5:05
2.96
—
.855
1.63
1.41 6.99
-
— 2.65 67.9 323
—
—
122
6:06
2.94
—
.850
1.51
1.50 7.01
—
— 2.b7 64.1 300
—
—
114
7:00
2.96
—
.850
1.51
1.46 7.20
—
— 2.61 62.4 308
—
—
112
8:00
2.96
—
.845
1.41
1.54 7.26
—
— 2.84 61.5 290
—
—
113
9:00
2.94
—
.845
1.41
1.61 7.14
—
— 2.82 64.3 285
—
—
113
10:00
2.95
—
.845
1.41
1.61 7.14
—
— 2.70 64.3 285
—
—
108
11:00
2.96
—
.845
1.41
1.61 7.18
—
— 2.72 64.3 287
—
—
109
12:00
2.97
—
.845
1.41
1.58 7.09
—
— 2.82 63.1 283
—
—
11 )
July 2, 1978
1:00 am
2.99
—
.845
1.41
1.59 7.16
—
— 2.78 63.5 286
—
—
Ill
2:00
3.00
—
.845
1.41
1.57 7.07
—
— 2.80 62.7 282
—
—
112
3:00
2.99
—
.845
1.41
1.62 7.09
—
— 2.73 64.7 283
—
—
109
4:00
2.98
—
.8S0
1.51
1.60 6.95
—
— 2.69 68.4 297
—
—
115
5:00
2.94
—
.860
1.74
1.94 7.50
—
— 2.76 95.6 310
—
—
136
6:00
2.89
—
.900
2.10
2.33 7.98
-
- 2.70 178 610
—
—
206
7:00
2.84
—
.915
3.10
3.44 11.4
—
— 2.88 JO? 1(100
—
—
25)
8:00
2.97
—
.940
3.80
2.03 10.6
—
— 2.71 218 1140
—
—
292
9:00
2.99
—
.955
4.22
1.90 8.80
—
— 2.40 227 1050
—
—
287
10:00
3.09
—
.955
4.22
1.29 1.48
—
— 2.38 154 894
—
—
284
11:00
3.17
—
.960
4.35
1.21 6.53
—
— 2.55
149 804
—
—
314
12:00
3.20
—
.960
4.35
1.10 5.88
—
— 2.32
136 724
—
—
286
1:00 pn
3.23
—
.960
4.35
0.94 5.50
—
— 2.39
116 678
—
—
294
2:00
3.24
—
955
4.22
0.93 5.66
—
— 2.61
111 616
—
—
288
3:00
3.24
—
.950
4.09
0.91 6.00
—
— 2.40
105 695
—
—
298
0
-------
TA8I.E 4 — (continued)
4:00
3.24
—
.950
-
4.09
0.81 7.30
—
—
2.38
93.8
846
—
—
276
5:00
3.23
—
.945
3.95
0.95 10.2
—
—
2.54
106
1140
—
—
284
6:00
3.23
—
.940
3.80
0.96 10.4
—
—
2.46
103
1)20
—
265
7:00
3.21
—
.935
3.66
1.03 9.47
—
—
2.29
107
982
—
—
237
8:00
3.20
—
.935
3.66
0.96 8.30
—
—
2.09
99.5
860
—
—
217
9:00 3.20 — .930 3.51 1.10 7.18 — — 2.27 109 714 —
10:00 3.20 — .930 3.5) 0.97 6.53 — — 2.15 96.4 649 —
11:30 3.22 — ,925 3.38 0.99 5.88 — — 2.10 94.8 563 —
Rain began at 4:30 am, July 2, 1978. a moderate rainstorm with 0.64 Inchea of rain recorded In itiulsa.
The last rain fell on June 22. a moderate tlisii eraIiower with 0.84 inches of rain recorded in I.o,,isa.
The creek discharge was approaching base flow by July 2.
Specific
Conduct arice
Date arid Time PH (iunhos/cm)
r’)
.1
-a -
Caugc
Ilcighi. Discharge
(It) (cI a)
Pletal Concentrations
(m g i ?)
* tal loads (sn/s)
Cu Zn Fe Al Pin
— 226
— 214
- 20)
-------
transpiration losses from the water table dos, to the creek may accoimc
for the variations in flow.
B. Variations in Water Ch istry
Copper and zinc concentrations fluctuate approximately ten percent in
association with the daily discharge oscillations. The metal concentrations
peak about vvelve hours out of phase with discharge, that is metal concentra-
tions reach their muim when discharge reaches a minint . This effect is
harder to observe for manganese because the scatter in the analytical data
obscures the actual variation. Iron and specific conductance were not tested
in these samples because the oxidation and hydrolysis of iron had proceeded
too far. The pH was measured but its validity is marginal because of inter-
ferences from iron hydrolysis. The pH value, do show a slight rise and fall
in phase with the discharge variation, but these are less than the uncertainty
of the msuursment.
The copper, zinc and manganese loads do not show the diurnai. peaks and
troughs but are constant throughout a daily cycle because the fluctuations
in metal concentrations offset the variations in dis:harge, i.e., the concentra-
tions peak when discharge reaches a minint and vice versa. The constancy
of the metal Loads demonstrates that soluble metals flow from the creek at
a steady rate during any given dry period. Therefore, the regular daily con-
centration oscillations must be due to the cyclical variations in the flow
which is available to dilute the mine drainage. Metal loads do gradually
decrease over extended periods of dry weather. This load decline would be
expected due to the slow decrease of base flow and mine seepage which respond
to th. falling water table.
Evaporation and transpiration are both ?lausible mechanisms for varying
the flow of Contrary Creek. From the upper end of the Arminius to monitoring
station #4, a distance of almost 4 , the entire creek bed is exposed to
232
-------
direct s 1ight because the poor quality of the creek water inhibits the
growth of overhanging v.getstion. This direct exposure accelerates the daily
beating of Contrary Creek cud allows greater wind velocities over th. water.
Both ths heating and he vied ancourage evaporation. the shallowness of
the creek, lea. than a foot in scat places, permits faster hasting and pro-
duces a higher surface to vole ratio, both of which enhance evaporation.
It is well known that plant trcnepiratio’ prevents significant a unta of
water from reaching the water table. However, it is not clear whether daily
transpirational removal of water from the watar table near the creek can
produce noticeable diurnal fluctuations of groundwater flow into th. creek.
If so, transpiration induced variations in groundwater flow are thought to
be greater above the Lrminiue Mine in the upper end of the Contrary Creek
basin. Here th. tree. and uAderbrush grow right to the water’s edge. Both
of these eachanises. evaporation and transpiration, function with a twenty—
four hour period.icity .n their intensity and could therefore produce a cyclic
removal of water but not heavy natal. from the creek. This phenomenon would
result in the daily concentration naxinums.
The constant arrival tine of discharge peak.. and troughs at ncnitorin 0
station *4 permits an evaluation of the plausibility of the aforementioned
mechanisms. Transpiration peaks around midday and evaporation rates are
highest about mid—afternoon. The discharge reaches a minimum about midnight.
This schedule implies that the water parcel which passes monitoring station
#4 at midnight has been subaerial for at least ten to twelve hours. During
dry weather thi, is not an unreasonable travel ties for water coming fran the
upper reaches of the Contrary Creek basin.
Preliminary inspection of gauge height recordings at monitoring station Q3
indicates that the peaks and trough. arrive there about three hours earlier
233
-------
th.em at station 04. The variation in flow is small at station 03 else. Ths
differences in arrival times suggests that the peaks nov. downstream as a
minute wave with $ tvanty—f our hour p.riod.
Further study would be necessary to describe thoroughly the origin of the
psak md trough effect. e.g., better knowledge of: c;sek velocities at more
points, tha discharges of the many minor tributaries joining Contrary Creek,
end the variation in peak amplitudse in relation to ambient conditions. Of
course, additional research along these Lines La bsyor.a the scope of this
project. Fortunately, these diurnal variations are small and integrated with
he conspicuous changes d rtng a rainstorm they are insignificant. Furthermore,
the machanisma which produce the diurnal changes nay r’t be operating during
the cloudy ht id v..ather accompanying a rainstorm. A cooplets cycle of diurnal
chemical variation wa, monitored only once, but th. daily chemical oscillations
are prsssd to occur throughout the s .r and early fail whenever the
gauge height recorder shows diurnal flow variations. The baseline chemical
data prior to storm of 6—19—78 record a sma.J . fransnt of the daily cycle
on another occasion. During a protracted dry spell, tbs acid seeps dry up
and mata. Loads decrease. This trend is only evident un a tine scale of
several weeks and is no more important than the weak diurnal fluctuations
when describing the rapidly changing creek chemistry in a rainstorm.
234
-------
SPECIFIC CO DUCT?JiCE AND pH TRA ’ISEC? OF CONTRARY CREU
A transect of specific conductance and .S data has been collected at
50 intervals along an 1100 m section of Contrary Creek I loving through the
Sulfur Mine site. Th. sanpies vera gathered on September 26. 1978 when the
creek was at fairly 1ev flow. At each 30 m interval pH, specific conductance
and temperature were determined at midstream and a point close to each bani .
These three point transects ware continued upstream until the creek became
so narrow at 850 n that only one point was necessary to ch.aracterize the
strean. Very little Sulfur Mine caste was heaped above this point and there
yes very little cross s.ctioual variation. Samples were also collected at
midstream on three tributaries entering Contrary Creek.
The ;H and specific conductance data reveal several interesting trends
in the creek chemistry. The specific ccnductance offers a crude yet useful
measure of the dissolved solids in a given volume of water. “a specific
conductance of Contrary Creek nearly triples while passing throu the Sulfur
Mine site (see Table 3). Along this 1 stretch three tributaries and
numerous seeps swell the creek’s discharge. An al st tripled dissolved
solids concentration and a substantially augmented discharge produce a more
than tripled dissolved solids load. All of t e increased dissolved load can
b. attributed to the Sulfur Mine seepage because the tributaries have very
clean ester. The pH falls one and a half units along the transect. This
means a thirty—two fold increase in hydronium ion, or acid, concentration.
Graphical analysis of the longitudinal transect of creek chemistry can
fscilitats finding areas of high and low acid drainage. Th. slope of the
specific conductance versus distance in Figure 2 represents th. rate of change
in dissolved solids concentration along the creek. When the slope is horizontal
as frt.s 1000 to 850 m, there is zero chang. in dissolved solids concentration.
235
-------
TABLK 5—p t l and ptc1fic Conductance TraneectofConrrary Creek and
Tributortea at the Sulitir Mine Site, Seplemt)er 26, 1918
Southenat Nnrthwast
sido aide NidHtrea .
975 995
Southeast
side Station Description
Just downat eem tr the bridge
1000 and a tend in the creek. well
aixed.
Under dt nstrea. edge of bridge,
1083 21 meters beloi, (reels creek
entel Ii. , Eros NW.
Pyritlierous aedlsent us, both
buu ,k ,, breep rock taLe sin SC
Iein.k — —
Small waste rock pile on S 1
bunk.
ALIJ e us entering 1ri S F.
bunk, large waste rock pile
in SE bjiiik,
Idige w sfe rock pih end a
1sw mine t labers us, l. hunk.
350 meters 3.22
400 meters 3.68
3.64 643 636
large waste rock pile on S bank,
912 some pyrltiferous waSte on iN
bank.
Vcry large tailings orj i1eun
811 NW bjnk numerous jtiii bCe )S
CI I I cr1 usg
Veiy 1 1 7je tahlingb pile on
670 liauik bMfls pyritiferissa waSte
sin ‘iij bank.
I I) meiLls dcwnbtre.uD irsi ’ m Il
SI ’) d.sin .i, ,d w. ,tcr fall • sit y l.ii kC
.11 I I s .i . . ;sI Ii . ii ,, NU i..,,k
Loent ton
Northwest
side Midstream
Monitoring
Station 4
Speci lic Conductance
1)1 1 (ps lioa/c.)
3.36
3.34
3.36
it. 522
8ridge
(0 meters)
3.41
3.37
3.25
832 1032
00 meters 3.28 3.30 3.29
SO meters
(upstream of 3.25 3.27 3.27
bridge)
2 mt .ts above old
980 976 968 abut.e,d , massive
exposed on S bant
bridge
bullide
981 973 978
150
meters
3.32 3.32 3.31
960 979
200
meterS
337
337 3.22 907
923 1485
250 macera .1.47 3.47
300 meters 3.44
3.30
858 855 1031
3.51 3.31 917
829
3.62 3.31 1476 730
3.72
65(J meters 3.77 3.96
L76 615 46(
-------
Station Description
Brat de! Stream channel, acid
p0019 Ofl SE bank.
Braided stream channel. —-
pyritlierous sediments on
both banks .
Braided strea. channel,
LioaJ bottosland covered with
waSte rock on SE bank .
Braided stream channel, broad
bottomiand cove!e with wajLa
rock on St bank.
Broad hot toaland covered with
waste rock on SE bank.
Some waste rock on SE bank
and floodplain.
Fairly wide floodplain, only
a little waste fro. the sulfur
rntne upstream of this point .
(‘reek becou,es arrower, 5 meters
downstream fro. a fresh creek
ener &fro. WV .
liroad hare floodplain on SE
— bank.
bare floodplain on 5E
— bank.
PJ TpTaIn sTill broad, but
— no on er bare.
!ntesing Ira. Nh, very clean
water (analysed).
p 11
Souast
Midstream Bide
3.98 3.Sl
4.09 4.04
4.19 4.03
4.37 4.37
4.73 4.40
4.76 4.76
4.80 4.74
— 4.49
TABI. 5 (continued)
Specitic Conductance
(li mh3s/cm)
Northwest Sot.theast
side Midstream Bide
499 468 681
467 458 462
436 452 499
381 393 498
352 353 368
351 354 354
309 314 319
320 — 392
Northveat
Location aide
500 meters 3.95
550 .era , 5 4.01
600 meters 4.17
650 meters 4.39
700 meters 4.76
750 meterS 4.78
800 meters 4.79
850 meters 5.02
900 meters —
950 meters —
1000 meters —
Vresh
tributary —
it 21 meters
4.7,)
4.80
4,82
365
369
364
6.86
36
-------
TABLE 5 — (cant Inued)
Specific Conductance
p 1 1 (i’mhoalcm)
Northwest Southeast Northwest Southenat
I.oc .itlon side Midstream aide side Nidstre.tm side Stntion Description
Entering from 14W, Just before
TR—1, confluenee with Contrary
tributary
5.97 161 — (.rcek.
at 463
meters
___________________________________________________________________ - 55 meters upstream of confluence
Tk—1 6.56 113 — with Contrary Creek, flowing
past taiLings pile .
110 meterS upstream of confluence
TR—1 6.62 96 — with Contrary Creek, above all
______________________________________________________________________L! _taI1Ing _ _____________
luiterilig from NW.
Fresh
tributary 6.70 29
at 855
met era
The last rain was a light shower on September 22 wIth 0.22 indies recorded In Louisa.
Otherwise, the last half of September was fairly diy , therefore the creek was approaching base flow.
-------
VICUKK 2.
Midstream
pH
and
September
26 1978
Specific Conductance Transect
I
ci
(4
0
on d.
stream flow
>
LI
O lifl
- Jia)
LI4-
pH
U
U
4,
0.
U)
Di
once
ers
ove Rt 522 b’
Id ge
4
-------
The very steep slope from 450 to hO a indicates a very rapid increase in
dissolved solid.. and marks the location of heaviest acid seepage. The specific
conductance versus distance curve rises gently between 800 and 450 a. The
dese slope reflects the beginning of moderate mine drainage. The slope of
the pH versus distance graph falls very slowly between 1000 and 700 a indicating
a very alight addition of acid. Perhaps part of this gradual pH drop especially
above 850 n is due to the oxidation and hydrolysis of iron already in the
creek from the Boyd Smith and Arninius Mines. The pH values fall much more
rapidly between 700 and 50 a. In this range the slope remains fairly constant,
suggesting a constant influx of acid between these points. This trend con-
flicts with the evidence from specific conductance which indicates much
heavier seepage below 430 a and lighter seepage above. However, it must be
remembered that pH units are a negative logarithmic scale of hydronium ion
(H 3 0+) concentration. Therefore a constant negative slope for pH values
represents a positive logarithmic increase in acid seepage. On a typical
logarithmic curve the last half, which is the distance below 430 a, has the
steepest slope, which is aLalogous to the highest acid discharge. Between
1000 and 450 a the hydroniun ion concentration (assumed — activity) rises
from 0.15 l0 to 1.10 l0 moles/liter. Between 45 and 50 a the
hydroniun ion concentration goes from 1.10 10 to 5.37 X lO moles/liter.
Thus about 80% of the acid concentration originates between 450 and 50 a,
the region between the large tailings pile and old bridge abutments. U
discharge measurements were available and acid loads were computed, more than
802 of the acid load could be shown to originate between 450 and 50 a.
The cross sectional variation in pH and specific conductance also shows
the location of acid seeps (Table 6). As an example, at 650 a the specific
conductance falls from 498 Uahos/cm near the southeast bank to 303 at midstream
to 381 near the northwest bank. These values indicate acid seepage from the
southeast whicb is not unexpected since waste rock is piled on the southeast
240
-------
32.
bank. The pH gradient is not as obvious. A more extrens gradient is found
at 330 m where the specific conductance varies from 1476 jmhos/cm on the
northwest side of the creek to 730 at midstream to 811 near the outheait
bank. Heavy acid seepage from the northvest bank where the largest tailings
at. located and modest acid seepage from the southeast where there are
smaller acct ulations of mine vast. prc duce this cross sectional gradient.
The pH values vary sympathetically being lowest where seepage is highest.
These conductivity and pH gradients are convenient tracers for indicating
where greater recl.ematioc effort would be efficacious.
Whenever a fresh tributary enters Contrary Creek, the resulting dilution
usually causes a kink in the enooth trends of the pH and specific conductance
curves as seen in Figure 2. Generally, the tributary water hugs the bank
from which it entered and gradually mixes over the next 50 m. The first
sample interval below a tributary usually reflect this dilution in the sample
tak next to he bank and to a lesser extant at midstream. This cross sectional
gradient mimics those gradients due to seepage on the opposite bank. Monitoring
station *6 is about 100 m downstream of a fresh tributary. There was some
concern that the creek might not be well mixed at this station. However, the
data in Table 5 and data collected numerous other tines have shown the creek
to be homogeneous at station *4. The right angle bend, the shallow depth and
the turbulence in the creek thoroughly mix the water above this station.
Therefore, one sample taken at midstream will be characteristic of the entire
creek and can be used for accurately calculating metal loads.
The tributary entering Contrary Creek at 660 n, ovn as Tr—l, flows
a.tomg the southern edge of the main tailings pile for 120 m and suffers
measurable degradation in this short distance. Tr—1 is still much cleaner
than Contrary Creek. A small nan—made waterfall just below the confluence
241
-------
of Tr—1 cauaca a rapid ix1.ng of the creek and tributary. Accordingly samples
tak.n at 450 n do not have a wedge of I reah watsr along the northwest bank.
In fact, the sample taken on the northvsat side shows evidence of acid
seepage.
242
-------
THE ACID SEEP POOLS OF THE SULFUR MINE
LU three nines along Contrary Creek trickle acid sod metal laden water
into the creek. At the Boyd Smith and Arninius Mines, these seeps generally
enter from above the creek water level. The Sulfur Mine also has a few seeps
sntering the creak above tha water level. The paucity of these seeps in
relation to the hugs input of dissolved solids and acid revealed by the pH
and specific conductance transect suggests a nich larger hidden flow of natal
and acid. This flow of mine seepage is obscured because it enters Contrary
Creek below the water level. Th. only manifestations of this suboqueous
seepage are the dark brown pools which cluster along the creak banks and in
shallow depressions of the creak bed. The pools axe nest n erous at the
base of the huge nine tailings pile which borders 130 n of the creak beginning
330 n above the Rt. 522 bridge. However, pools can be found at many scattered
locations from the bridge to the area 750 n upstream.
The seep pools are a good indication of the chemistry of the groundwater
flowing through the tailings piles at the Sulfur site. Ten seep pools have
been analyzed and the results ar’ shown in Table 6. The pH values are all
close to 2.0 and they have very high dissolved solids as reflected in the
specific conductance which ranges f:,m 20,000 — 30,000 nicronhos and is more
than 20 tines the values found in Contrary Creek. When water of this compoaicion
is found flowing from a mine portal, a cementation plant would be set up to
recover the copper. These seeps have about the highest concentration of copper
ever reported for acid mine water. Unfortunately, the discharge i.e not nearly
enough to warrant a cementation operation.
The seep pools develop their maxim size during dry weather. However,
if the dry period is long enough, lik, the drought in th. s er of 1977, them
243
-------
Table 6. Che.Ical Oats t)r Acid Seeps
Collected In Si er, 1978
spec.
Date Cu Zn Fe Mn Cd Pb Ca Mg Na K pH cond.
220 SE
335 NW
7-01-78
7-01-78
4.75
411
14.6
563
365
9130
6.4
60
0.05
2.40
<0.5
<0.5
88
300
126
1520
5.0
3.2
3.3
0.3
2.11
2.11
3,150
1 ,300
338 NW
343 NIl
9-22—78
9-22-78
144
59.4
534
825
7750
12500
g
168
0.95
0.65
<0.5
<0.5
480
! 80
2280
3900
6.7
10.0
0.7
0.3
2.28
2.37
19,900
27,300
359 NW
370 NW
9-22—78
7-01-78
741
187
619
387
15200
9730
66
2.65
0.70
<0.5
<0.6
510
260
1570
1450
3.5
6.7
0.1
0.8
2.37
2.22
76,100
20.600
430 NW
430 NW
6-12-78
6-23-78
516
623
100
389
16 00
13800
32
1.50
1.72
<0.5
<0.5
560
290
1600
1210
3.7
2.3
0.1
‘0.1
2.0
2.0
23,400
23,500
430 NW
430NW
7-01-78
9—22-78
756
692
528
497
15600
14300
66
3.25
2.40
<0.5
<0.5
250
510
1410
1830
3.5
2.4
0.2
<0.1
2.0
2.25
25,300
23,400
Seep
concentration In mg/i
-------
tbs seep pool., ars found to dwindl, in size. The maximum development during
modest dry spells suggests that the pool, are flushed away during the high
discharge in vet weather. This egress well with field observations. During
day weather th. seep pools cs ot engage in turbulent miring with the creek
because the creek velocities are too low and the pooia 3re too dense. Of
course there is a smell exchange of ions by 3rovn an motion, but this is mini—
scule co ared to the exchange resulting from turbulent mixing. This situation
co ares well to the density imposed Layering in estuaries where a lens of
fresh river water rides out across of abody of denser salt water. When the
river flo’,ds, it flUShdS much of the underlying body of salt water from the
estuary. The response in Contrary Creek is analogous. As the creek’s discharge
rises, its velocity increases and the shear forces exerted on the creek bed
grown. These augmented shear forces result in greater turbulence and the
entrainment of the dense seep pools. Once the creek subsides the pools begin
to grow again. The density of the 430 m pool is very consistent. On three
occasions during dry weather the values ranged from 1.064 to 1.067 s/cc. The
one tine the density dropped below 1.06 g/cc is June 23, 1978, two days after
a series of three thundershowers. )n this day the discharge was still above
normal. This low density probably reflects the dilution of the pool by mixing.
One final n.,te should serve to illustrate how the acid seep pools resist
mixing. When the creek bed is disturbed upstream of a seep pool, tue ferric
hydroxide precipitate which carpets the bottom sends an orange cloud drifting
downstream. As this cloud passes above the seep pool, gravitational settling
of the suspended particles drops them upon the seep-creek water interface.
Rath.r than cross thin interface, thi bright orange particles highlighted against
the dark brown pooi glide on downstream. The ferric hydroxide follc.vs the
current which refuses to mix with the acid pool.
245
-------
VARIAZION IN WATER CWfLSTRY DU’RENG RAINStOR tS
Several att pts vers made to collect simultaneous discharge and water
chemistry data at eight tributary site. and four sites in Contrary Creek at
regular intervals during a rainstorm. Unfortunately, this sampling effort
was never achieved because of the highly unpredictable nature of the ve. .ther
during the period of research. Nevertheless, severalsets of sanples were
collected with automatic samplers at two of the dovnstr .am sites in Contrary
Creek during six different rainstorms. These data along with the results of
investigations on efflorescent metal sulfate ninerala and transects on stream
water quality in Contrary Creek are presented. Fur hsr interpretation of the
data is being prepared in the t.S. thesis of Tom Dagenhart.
For six thunderstorms between June 8 end September 12, 1978, the creek
water was collected at regular intervals for a few hours before and on through
the rainstorm. Th. data are provided in Tables 4, 7—U and Figures 3—9
samp es were collected with en ISCO automatic sampler, packed with ice to slow
the oxidation of iron. The first scorn, June 8, was rampled at one and a
quarter hour intervals for a day. The second stern, June 19, was sampled
at one hour intervals for one day. Then the sampler was reset to collect at
three hour interval.. for four days. During this period two additional storm..
were monitored on June 20 and 21. The fifth scorn, July 2, was sampled at
an. hour intervals for most of a day. Water samples for the first five storms
were only collected at monitoring station 44. The sixth storm, September 12,
was umpled every half hour for twelve hours at both monitoring stations 93
end 94. Then sampling was continued for another daj and a half at longer
interval.. For thi . last storm pre—rainstorm baseline samples were not collected
end the ‘irat sample was not taken until one hour into the storm. The baseline
end early rainstorm samples were missed becaused of the extreme difficulty of
forecasting the weather.
246
-------
TABLE 7 - The Kalnator. of lime 8, 1978, Stat fun 94. Contrary (:reek
Spec Ilic
Conductance
(lmlsoa/cm)
7:45 3.82 457
9:1W) 1.82 661
10:15 .1 80 4 6
12:45 1.62 ¶ 1) ’)
Rain began at 12: 15, a I tgIit t lsiiiidi ’r
fb the previous day thei e had hee n a
.975 4.81 .76 4.37 28.5 6.0
.970 4.65 .76 4.51 29.0 5.3
•97fl 4.65 .76 4.53 29.3 4.8
.96(1 4.15 .74 4.34 28.1 6 6
I w,•i wIth 0.31 inc liee of rain recorded In
1 i Iit t lsisri .Ier shower wIth 0. I I I in hie ol
595 1880 817 -
594 3820 698 -
¶99 3860 632 —
535 1490 567 —
e.auge
lie Iglit
(ft)
I t i (‘.onceu.trationa
(.g/ 1)
Metal Lead. (.g/a)
Date and Time
pH
I)Isclnirge
-
Cu
Zn
Fe
Al
MeCu Zn
Ye Al
Mn
June 8, 1978
10:30 am
3.60
525
.970
11:00
3.62
525
.970
.83
5.15
24.5
6.5
-
109 678
3230 856
—
11:30
3.62
525
.965
.81
5.05
26.0
6.5
—
101 665
3420 856
-
12:00
3.62
530
.965
.82
4.86
26.3
6.3
—
105 619
3350 803
—
12:30
3.60
540
.965
4.50
4.81
.82
.81
4.79
4.54
26.5
24.7
6.0
.8
—
—
lOS 610
110 618
3380 765
3360 790
—
1:00 p.
3.42
670
.980
4.96
2:15
3.40
680
.995
5.15
35.0
7.5
-
177 723
4920 1050
—
3:30
3.58
530
1.000
5.45
1.42
6.63
37.5
8.2
—
219 1020
5790 1270
—
4:45
3.70
483
1.000
.94
4.94
25.5
5.6
—
149 783
4040 888
-
6:00
3.74
469
1.000
5.6
5.6
.78
.78
4.34
4.21
72.2
21.3
4.8
4.4
—
—
124 688
124 668
3520 761
3380 698
—
—
7:15
3.77
466
1.000
5.6
8:30
1.75
471
1.000
.16
4.08
21.5
4.4
—
121 647
3410 698
—
9:45
3.72
502
L000
5,6
5.6
.71
4.68
23.5
4.8
—
III 742
3730 761
-
11:00
3.73
483
995
.83
6 12
25.5
5.1
—
Ii? 1070
4060 8119
—
June 9, 1978
.80
5.48
25.5
4.8
-
123 846
3940 741
—
12:15
3.74
476
.995
5.45
.81
4.74
26.8
5.6
—
125 132
4140 864
-
1:30 am
3.77
461
.990
2:45
3.81
442
.985
5.29
.76
4.40
26.1
4.8
—
114 659
3940 719
-
4:00
3.81
645
.985
.75
4.11
26.1)
5.1
—
$09 591
3780 741
—
5:15
3.81
448
.980
4.96
.74
4.1!
21.1
5.1
—
108 197
i940 741
—
6:30
3.83
4 0
.9 /3
4.81
.74
.76
4.20
4.30
27.8
28.0
5.3
5.6
—
—
04 590
104 586
3900 744
3810 763
—
—
- 104
- 100
- I O U
-- 91
I,I) I I sa.
ru I ,, ri i ,rJe ,I in i4ltIltla.
lii. i rctI had n t yet r ’t*srui.’d to b.i v I luw.
-------
TA8LM 8 — The Kftinstor of June 19, 1978, SLncIon 4, Contrury Creek
Specific
Conductance
( Iaudios/ri
C.auge
IIc1 lut
(It)
I)lec liargu
(cfH )
tie tat Ci iicent ru t I one
( mg/ I )
Zn Fe
Metal Loada (.ig/s )
Cs. Zn Fe Al
June 19, 1978
,
Mn
1:00 p.
3:00
3.28
3.25
835
864
.865
.860
1.86
1.14
1.26
1.31
6.1
6.4
47.3
50.2
10.5
2.57 66.4
321
7490
551
1)3
5:00
3.76
874
.853
1.63
1.39
6.1
51.7
2.64 64.6
315
2470
361
110
6:15
3.10
1025
.910
4.65
2.03
6.8
56.5
9.5
19.0
2.63 64.2
267
282
896
2391)
439
121
6:31)
—
—
1.1)70
84
—
—
-
-
— —
—
-
2300
-
129
-
7;15
2.95
156)
1.060
8.0
7.56
7 50
—
—
1.055
7.8
—
8:15
3.28
783
1.100
9.6
2.28
8:10
—
—
1.110
10.9
9:15
3.42
567
1.135
11.2
—
1.36
24.0
12.2
5.8
110
36.0
18.7
35.0
13.0
9.5
2.74
2.15
1.76
1110
620
431
5440
3320
1840
24900
9790
5930
7931)
3019
621
585
558
11:15
3.66
417
1.145
11.6
.81
3.6
12:15
3.80
366
1.145
11.6
.b2
4.0
6.0
1.15
266 1184)
4160
June 20.
1978
4.8
1.41
206 1)10
427(1
1:15 a
3.88
437
1.125
10.7
.78
2:15
3.89
422
1.100
9.6
.70
7.3
13.0
13.0
4.8
2.5
1.81)
I 9)
2)6 3060
1114) 1980
3940
351))
1450
( Ml)
545
5)9
2680 571
1970 443
1380 463
9.15
3 8 )
400
.993
5.45
10:15
3.8 ,
406
.991)
3.29
11:15
3.82
416
.9 ) 11)
4 9i ,
12:15
3.79
4:15
3.89
365
1 (160
8 I)
.53
4.6
369
5:15
3.88
358
1.043
7.4
.50
3.6
1.40
120
1040
3060
816
3)7
6:13
3.87
364
1.010
6.8
.52
16.1
6.0
1.15
lO S
692
337))
126(1
281
7:13
3.88
373
1.015
6.2
.55
2.9
11.6
1$ /
6.0
4.8
1.29
I 16
1.61
1.30
I ‘i ’)
I 36
IO U
96 6
95 I
¶32.6
¶32.1
89 11
597
509
476
478
47’)
44’J
3390
3281)
3150
II’fll
15 ()
1/40
1160
84)
788
761
lll(.()
s ’)!
248
2)’)
235
2)2
!7 I
! I ’)
.58
.60
.62
.64
2.9
3.1
3.2
3.2
19.2
20.1
21 7
/ 1. I
l..8
4.8
7 1
1 I
-------
TABLI 8 - (cnnttr.t,et i)
Mct l Concentr,itiona
SpcclfIc Couge
Conductance Ilcight lilechorge ___________ Metal Load. (mg/a)
Date and Time pit (1Jmhos/c ) (It) (cr8) Cii Zn Fe Al _ Hn Cu Zn Fe Al Mn
1:15 pa 3.75 445 .970 4.65 .67 3.3 25 0 7.1 1.59 88.2 435 3290 915 209
2:15 3.71 456 .960 4.15 .70 3.3 2%.0 9.5 &.7S 06.2 407 3080 liii) 216
3:15 3.( . 7 477 .955 422 .7’ 3.6 25.5 9.5 1.75 83.7 430 3050 1140 209
4:15 3.63 488 .950 4.09 .70 3.6 25 0 8.3 1.15 81.1 417 2900 961 203
5:15 3.61 487 .945 3.95 .74 3.6 27 1 7.1 1.14 82.8 425 3030 794 195
‘. 0 Rain began at 5:45 pa :i heavy thundershower with 3.Cl Inches of aLn recorded in Louis.i.
The last rain fell on .Jjne 13. a light inInstor with 0.27 Indies of rain recorded In Louisa.
The creek discharge was approaching base flow by Jdne 19.
-------
TABLE 9 — The )&ei1nstor s at Juiic 20 and 21, 1978, StatIon Coetrary Creek
1:15
8:10
9:00
12:00
Ji••it 22, 1978
1:00 tb
1.2 )0
— 1.3 S
123 1.34 9
161 L2I(1
14.8
25 1
22.7
16. 8
— 70)
— 495
S 1 icc If Ic
Couiductaucc
(imihos/cmi)
Gauge
lie iglit
(it)
Discharge
(eta)
Pletal Conrcntrat tons
( ‘ i c R)
14ts1 LoodR (mg/ri4
TI.e
pH
—
-
Cu
Zn
Fe
At
I*
Cu Zn
Fe
Al
Na
June 20, i9ig
4:15 p.
5:15
6:00
6:35
1:15
3.63
3.61
3.47
—
3.22
488
407
603
—
900
.950
.945
.940
L.IOO
1.190
4.09
3.95
3.80
9.6
9.6
.70
.74
.19
—
4.07
3.60
3.80
4.05
-
17.8
25.0
27.1
10.3
—
40.0
2.3
7.1
—
—
19.0
1.15
1.14
1.80
-
1.76
81.1 417
82.2 425
65.0 436
- —
1110 4840
2900
3030
1110
10870
961
794
—
—
203
195
194
478
U I
8:25
3.65
427
1.090
9.2
—
—
—
—
—
— —
—
—
—
9:00
3.5)
461
1.080
0.8
.70
3.50
6.0
1.38
174 872
1500
344
12:00
3.57
412
1.0)0
6.8
.58
2.80
8.3
—
1.20
112 539
1600
—
231
inne 21,
1978
1:00
3.53
416
.999
5.29
.66
3.20
9.9
-
I . 3(1
98.9 479
1480
—
195
6:0 1 )
3.51
549
.919
4.65
.84
5.10 13.0
—
1.54
ilL 698
1710
—
203
9:0 (1
3.49
581
.9(0
4.33
.81
4.45 14.1
-
1 6)
99.8 548
1140
—
198
12:00
3.48
596
.955
4.22
.91
4.52 20.2
•-
t 6’i
fl9 540
2410
—
202
J:00 p.
3.48
606
.945
3.95
.85
4.48 15.6
.
1 13
93. 5 (1)
1750
196
6:00
3.38
625
.935
3.66
.86
6.52 16.6.
-
I 1P
81.1 469
1510
-
184
6:40
—
—
1.275
15.7
—
—
—
— —
1.68
3.19
.54 2.58 1.8 1.0’; 147 1i60 2160
.53 4.61 3.1 — I 18 222 1848 1300
3.77
367 1.115 10.2
.49 2.61 5.1 — 1MM 142 760 1410
-------
TARLE9 (cun Inued)
Caugc
1k ighi Diacharge
(It) (c ia)
12:00 3.58 563 35 3.66 .94 4.58 31.4 — 1.74 91.4 475 3250 — 180
Rain began at 6:15 p. on June 70, a .nderate rhunderehower with 0.34 bruce of rain recnrded In Loulari.
Rain began at 6:00 pa’ en June 21, a moderate thundershower with 0.39 inchea of rain recnrded In Louisa.
Tire laat iain fell on June 19, a heavy tltnuin iersiiower wIth 3.0! Inches of rain ricorde ,I in louisa.
The scoras of the 20th an’l 2iti. werr .onitored accidentally while checking tire rccovery response of Contrary Cre ’k
after tire Bti’ra of 19th.
Spc ’cI( Ic
r.onduuc C once
Date and Tire oil (i .ho /ce.)
r .,
(7
P tal Cnnccntrat 10 ( 19
(m ’ ,/t)
Metal Loade (.r,/nn)
Cu
Zn
Ye
AL
Mn
en.
Zn
We AL
Mn
6:00
3.72
406
1.070
8.4
.55
2.76
5.9
—
1.24
131
657
1400
—
295
9:00
3.1 !
435
1.035
1.0
64
3.01
9.6
—
1.35
127
597
1900
—
268
12:00
3.77
462
1.020
6.4
.68
3.28
11.9
—
1.36
123
594
2160
—
246
3 00 p.
3.69
484
1.000
5.6
.71
3.39
13.6
—
1.40
113
538
2160
—
222
6.00
3 60
549
.91)
4.81
.80
3.70
13.1
—
1.50
Inil
504
1780
—
204
9.00
).5’
53!
.965
4.50
.81
3.88
21.9
—
1.54
106
491.
2790
—
196
12.00
3.59
Sit
.9 )5
4.22
.80
3.93
20.5
—
1.60
103
470
2450
—
191
June 23, 1918
3:00 aa
3.59
570
.950
4.09
.9!
4.10
74.6
—
1.69
105
498
2850
—
196
6..)0
3.59
381
.930
4.09
.9L
4.61
26.1
—
1.12
:os
534
3020
—
199
9:00
3.59
364
.96)
3.95
.91
4.1,8
29.6
—
1.72
109
501
3310
—
192
-------
Tnblo 10. iii. 8.m1neto . of Scple.bcr 12, $978, Stnt Ion 93, Contrary Cr .k
r P!!&Iii) .. -- — - — — _______ ___ —
Date and TI .. $11
Speilfic Citj 1 .
Condurt nice lIeISht OIacl,i, e
JL L__ ... .S’L°)
-— Cu in Ve _ Phi Cdfl Ca
Sept. 92, 1978
7:00 p.
10:00
10:30
10:50
11:10
0. SR I)
0 575
0. 700
0. 1 )5
0.1 )5
$2.7
11.6
59.5
17 ,3
66 8
Sept. 93, 1979
3.79 416 0.770 91.4
1.50 4.90 2.55 2.36 0.035 26.9 $5.1 2.16 2.47
1 1 :25
(.7 ’
F .)
12:03 a*
4.40
304
0.930
232.2
0.51
3.31
.91)
1.50
0.015
cot
20.L
$1.9
3.95
2 25
12:25
.60
287
1.060
413.4
0.37
3.80
.67
9.35
0.015
19.6
11.1.
2 92
.JI
92:30
4.76
248
1.070
4)’ 2
0.26
3.26
.64
1.11
0.010
.c ,4
16.9
10.0
7.03
7 I ’ .
12:55
4.53
462
1.090
475.1
1.64
26.8
2 10
1.09
0.090
<0.1
46.7
23.6
2 50
.1.?’)
1:25
4.27
638
1.115
750.4
0.89
20.2
1.38
2.55
0.065 o.i
27.2
11.2
2.53
2.32
1:55
4.79
311
1.150
591.5
0.40
0.11
1.52
1.79
0.0)0 < I
22.8
10.5
2.52
1 99
2:25
5.64
IH
4.085
464.4
0.07
2.40
0.46
1.16
0.010 <0.1
12.3
6.4
2.53
1.6)
2:55
6.01
138
1.020
3)4.1
0.04
1.44
0 32
1.03
0.010 i
10.5
5.8
2.41
1.(,$
3:25
6.14
131
0.955
251.1
0.04
1.31
0.16
I ii
0.010 ‘ ö I
10.0
5.8
2.45
1.6)
3:55
4:25
455
5:25
5:55
6.15
6.10
6.02
6.03
6.03
139
146
148
148
154
0.925
0.905
0.880
0.855
0.540
229 4
209.5
186.9
165.1
452.9
0.04
0.05
0 05
0.04
0.04
1.25
1.29
1.36
1.31
1.41
.42
6?
.26
.53
. 1
1.18
1.16
1.15
1.1$
1.06
0.010 <0.1
0.010 - I
0.010 - i
OVID ‘ (1 I
0 010 1
10.2
10.6
10.6
$0.7
10.0
6.0
6.4
6.3
6.5
6.6
7 45
1 49
2 55
1 5’)
7.62
I 60
1 1..:
1 51
1 ‘0)
I 64)
6:25
6:55
7.25
1:55
0:25
5.93
5.89
5.79
5.60
5.56
156
161
161
$71
$04
0 820
0 895
0 190
U 175
4) 764)
$35.9
11) 2
109.9
$09.5
91 2
8’.. ’ )
02.7
11.3
11.9
6’) 4
006
0 $14
4 ’ oc
I ) 05
0.06
0.06
0.01
0.07
0 4)7
Cl (48
1.40
1.4’s
l c2
1.59
1.65
1.62
1.61
I .9
1./8
1.0)
.21
.12
.22
.13
.30
.2!
.11
.16
./1
.2)
1.07
1.11
1.17
1.11
I 19
I 18
$9
I IN
I . ‘ I I
(0
0)0 .-43
0.0I0 .(n
9.019 . 3
0.01$) ‘0 I
-.
11.1
$ S
Il 1
$2.4
11.0
6.R
1 , 4)
1.1
1.6
8.!
7 61
2 64.
7
2 10
2 70
1 5 ’
I ‘0
$ co
I 65
I $44
0 01(1 ‘0 I
41010 <1) I
04410 - ,i
ii
0.0)4) — i
II .?
I! 4
11.1
$4.2
$6.1
7.8
8.’
8.4
0.8
8.8
2.72
2.69
7.15
7.12
21.3
2. H
I 65
I 61
61.
I , ‘
8:55
9:25
9:3%
025
0:55
5.61
5.51
5.49
5.4’,
5.6)
lB S
lBS
189
$ 14
$91
0 iS O
0.1 / .5
41.735
4) 725
II. 120
-------
ruble 10 lli . R.jIs ,utor ol September 12. l918 . StatIOø •) Cintrery Creek (cunt Inued)
r
U,
(4
Concdntrat 109$ (.e/I
Date nd Tt.u
p 11
Conductarne
(iu.boeic)
height
(It)
Diti harge
(lid)
Cu
Zn
Pc
Mn
Cd
Pb
C.
lIg
We
K
11:25
5.39
203
203
0.715
0.110
66.8
64.3
0.09
0.09
3.05
4.39
.08
.09
1.20
1.20
0.010
0.0115
<0.1
<0.1
44.8
14.1
9.1
9.2
2.76
2.15
1.62
1.59
44:55
205
0.705
62.0
0.09
2.13
.09
1.18
0.010
<0.1
Ie.9
9.4
2.16
1.60
12:25 p.
207
0.100
59.5
0.09
1.99
.10
1.19
0.010
<0.1
14.8
9.4
2.75
1.62
12:55
214
0.695
51.7
0.10
2.01
.13
1.29
0.010
<0.1
IS.?
9.8
2.79
1.63
1:55
2:55
5.21
223
226
0.690
0.685
54.9
52.7
0.10
0.09
2.01
2.10
.09
.09
1.26
1.36
0.010
0010
(0.1
<0.1
16.3
16.8
10.1
30.4
2.86
2.9)
1.62
1.13
3:55
5.21
235
0.675
41.9
0.10
2.13
.a.lS
t...1
0.1110
<0.1
11.6
10.9
2.95
1.65
4:55
5.22
240
0.670
45 6
0.10
2.17
0.16
I 46
0,010
<0.1
17.6
10.9
3.00
1.66
5:55
5.20
244
0.665
43.3
0.11
2.12
0.15
1.52
0.010
<0.1
17.9
11.2
3.01
1.65
6:55
5.18
1:55
5.18
248
249
0.665
0.660
43.3
41.1
0.11
0.11
2.39
2.38
1.15
1.15
1.55
1.54
0.010
0010
<0.1
44.1
18.3
18.5
11.4
11.4
3.06
3.01
1.69
1.61
0:55
5.18
256
0.655
39.4
0.11
2.40
1.16
1.56
0.010
(0.1
lB 0
11.4
3.1)6
1.64
9:55
5.36
256
0.650
37.4
0.11
2.43
1.11
1.56
0.010
<0.1
17 8
11.3
3.41
1.70
10:55
Sept. 34,
1918
37.4
0.31
2.51
0.13
1.57
0.010
<0.3
19.4
12.2
3.18
1.66
1 SS
5.12
260
C
1.65
4:55
3.11
269
218
0.640
35.4
33.1
0.11
0.12
2.60
2.19
0.16
0.2?
1.64
1.11
0.010
0.010
<0.1
<0.4
20.2
20.6
12.1
13.0
3.31
1.67
7:55
5.01
285
0.630
29 . 1
0.12
2.95
0.43
1.85
0.010
‘0.1
21.1
13.5
3.35
10:55
5.04
293
0.625
27.5
0.12
2.83
0.50
188
1) 040
‘0.1
21.3
13.7
3.39
1.55 p.
5 03
302
0.620
25.5
0.12
3.10
0.46
1.94
0.010
‘0.1
22.2
14.2
3.43
4:55
1:55
4.92
4.90
318
3 I
0.615
0.615
2) 8
21.8
0.19
0.16
3.70
3.45
0.36
0.43
2.06
2.12
0.010
0 010
cO.)
<0.1
22.5
23.2
14.7
15.2
3.46
3.52
1.11
10:55
-------
Table II. the Painetor. a? Septe .6.r 1.2, 1978, Stat to., 14
Contrary Creek
Cauge
Height
(It)
Date and Ti.. pH
Sept. 12, 1918 —
Sped tic
Conduclante
( t : .boeLcm) -
Concent rat tons (mgi I )
Dtuchnrgc Cu ? Fe Mn Cd Pb Ca 11 N K
hOOp.
-
-
0.800
21.5
10:00
-
-
0.800
21.5
10:40
—
—
1.100
271.8
—
—
—
—
11:05
—
—
1.020
181.2
—
—
-
—
11:15
2.90
2250
1.040
201.9
16.9
69
211
4.04
U i
0.210 - 0.1. 56.0 51.5
2.45
2.29
11:50
2.98
1550
1.120
294.5
1.30
44
109 2.92
0.110
0.1
38.5
32.4
2.80
2.10
12:00
—
—
1.125
103.0
—
—
— —
—
—
—
—
—
—
Sept. 13,
1978
•
12:15
2.91
1290
1.125
303.0
4.60
20.9
11.0 2j4
0.06S
< 0.1
38.0
23.8
2.86
2.29
12:20
—
—
1.125
303.0
—
—
— —
—
< 0.1
—
—
—
—
12:45
3.15
890
!.190
390.8
2.2)
11.8
21.7 1 99
0.040
< 0.1
27.4
17.5
2.82
2.4t
1:00
—
—
1.245
478.6
—
—
— -
-
—
-
—
—
-
1:15
3.43
613
1.250
487.0
1.31
1.0
17.8 2.04
0 030
( 0.1
23.3
1.5.0
2.86
2.19
1:40
—
—
1.255
495.5
—
—
—
-
—
—
—
—
—
1:45
3.57
SIt
1.265
512.5
1.1.4
5.4
13.2 1.83
0.030
< 0.1
21.1
13.6
2.82
2.31
2:00
—
—
1.305
580.5
—
—
— —
-
-
-
—
—
—
2:15
3.69
439
1.305
580.5
0.74
4.9
10 S I 5)
0.025
< 0.1
1.8.6
12.1.
2.87
2.87
2:30
—
—
1.305
580.5
—
—
-
—
—
—
—
—
2:45
3.77
489
1.275
529.5
0.94
15.5
9.2 2.10
0.010
0.1
23.4
is.:i
2.66
2.2%
3:15
3.86
557
1.230
453 I
1.25
20.7
9.2 2.36
0.010
< 0.1
32.4
I? 9
7.68
2 4
3:45
3.99
457
1.200
604.9
0.96
13.8
9.4 I 80
0 050
0.1
25.9
13.8
7 1
2.23
4:15
3.98
355
1.170
362.3
0.61
1.4
9.7 1.35
0.030
c 0.1
11.6
10.0
7.65
1.91
4:45
3.91
I II
1.145
328.5
0.44
4.5
10.1 1.28
0 010
< 0.!
136
8.4
2 63
1.69
5:15
3.91
298
1.130
308.5
0.39
3.3
10.5 III
<0 ulO
< 0.1
12.0
7.9
2.64
1.1(1
5:45
3.91
294
1.115
288.8
0.39
2.81
11.1 1.18
0 010
< 0.1
II 4
7.8
7.63
1.68
6:15
3.90
299
1.100
271.8
0.38
2.67
11.8 I 24
<(I 1110
< 0 I
11.3
8.’
2 64
1.66
-------
T jIaIe 1). The Ralnetora of Septe.ber 12, 1918, Stat Ion 84, Contrary Creck (cent inn eil)
Specific Cau 8 e r ,tration. ....L .*FI)
flat. and Ti.. pH Conduct.nce lie Ight fliuctiarge (.u Zn Fe tin Cd Pb Ca Kg Na k
( p..il) (!!.L_. ( l/e ) _______________ ________
6:43 3.90 110 1.1 185 254.9 0.40 2.66 12.V , 1.28 0.010 ‘0.1 11.3 S.? 7.68 2.53
7:1 3.90 310 1.0 15 243.5 0.40 2.68 12.8 1.30 (0.010 (0.1 11.5 6.4 2.65 1.63
1:45 3.89 3 11 1.045 232.2 0.42 2.10 11.4 1.29 0.0I0 ‘0.1 11.7 6.6 2.11 1.64
6:15 3.09 324 1.050 215.2 0.42 2.65 16.4 1.30 ‘0.020 0.1 11.5 8.? 2.73 1.68
8:45 3.81 331 1.040 203.9 0.44 2.80 ‘5.1 I 29 (0.010 ‘0.1 12.1 9.3 2.11 1.61
9:13 3.61 350 1.030 192.6 0.47 2.86 16.0 1.31 ‘0.010 ‘0.1 12.4 9.5 2.71 2.17
9:45 3.83 346 1.020 181.2 0.46 2.88 16.1 1.31 <0.010 <0.1 12.7 9.8 2.80 1.11
10:15 3.83 351 1.010 169.9 0.47 2.91 17.0 I 31 ‘0.010 ‘0.1 12.3 10.0 7.80 1.65
10:45 3.83 357 1.000 158.6 0.51 2.91 11.5 1.30 <0.010 ‘0.1 12.6 10.1 7.86 1.63
11:15 3.63 163 0.990 149.8 0.52 3.01 18.3 1.10 (0.010 <0.1 12.9 10.4 2.95 1.65
11:45 3.02 311 0 985 145.3 0.53 3.09 18 9 1.33 0.010 ‘0.1 13.2 10.5 2.81 1.78
12:15 p. 3.19 391 0.980 140.5 0.58 3.23 20.5 1.34 0.010 ‘0 1 13.3 10.8 2.89 1.11
12:45 3.76 413 0.915 136.2 0.62 3.39 22.0 1.38 0.010 <0.1 13.7 11.4 2.88 I 14
1:45 3.70 438 0.975 136.2 0.65 3.62 21.1 1.41 ‘0.010 <0 1 14.4 11.9 2.93 1.79
•s 2:45 3.70 441 0.970 131.7 0.65 3.12 21.3 1.45 0.010 ‘0.3 14.7 12.0 2.96 1.73
U i
U,
3:45 3.70 450 0.960 123.2 0.66 3.70 22.1 1.48 ‘0.010 ‘0.1 15.1 12.5 2.96 1.74
4:45 3.69 466 0.955 119.5 0.70 3.69 24.9 1.51 0.010 (0.1 15.6 13.0 2.91 1.69
5:45 3.68 411 0.950 115.8 0.72 3.19 26 0 1.51 ‘0.010 <0.1 16.0 13.5 3.04 1.75
6:45 3.68 480 0.945 111.9 0.7) 3.85 26.4 1.62 0.010 <0.1 16.2 13.7 3.04 1.76
1:45 3.67 493 0.940 101.6 0.75 3.98 26.8 1.66 0.010 (0.1 16.6 14.1 3.06 1 if.
8:45 3.61 502 0 935 103.6 0.76 3.97 2T1 1 0 010 <0.1 17.0 14.5 3.13 1.75
9:45 3.66 510 0.930 99.4 0.16 3.99 28.5 Ill 0010 (0.1 17.0 14.6 3.11 I 75
10:45 3.66 522 0.925 95.1 0.79 4.861 29 3 1.11 0.010 c0.L J?.4 14.9 3.21 I 18
11:45 3.57 528 0.920 91.7 0.19 3.91 28.5 1.80 0.010 (0.1 11.8 IS.) 2.24 I 87
Sept. 14, 1978
2:45 a. 3.36 553 0.9 S 87.8 0.81 4.1? 31.) P 89 0 010 0 1 18 4 16.1 3.11 i.qn
:4 5 3.31 570 0.905 80.1 0 83 6.31 33 0 1.93 0.010 0 I 19.0 16.5 3 34 1.94
8:45 3.57 586 0 900 16.5 0.85 6.44 35.9 1.99 0.010 0.1 19.3 I7. 3.38 1.03
11:45 3.57 592 0.900 76.5 0.85 4.79 35 7 2.02 0.010 0.1 19.1 17 4 3.44 I 83
2:45 p. 3.53 663 0.890 69.4 0.89 4.87 31.9 2.4]? 0.010 0.1 20.1 18 2 3.44 1.82
5:45 3.50 655 0.885 66.0 0 9) 5.12 38.5 2 IS 0.010 0.1 20 0 18.9 3.47 P. 85
6:45 3.49 674 0.880 62.6 0.97 5.13 41 (3 2 7 1 ) (P 0 10 0.1 20.9 19.4 3 55 1.86
11:45 3.50 6 113 0.815 59.2 1.00 5.29 41.1 2.114 0.010 0.1 II.) 20.0 3.55 1.86
-------
16
0
E
FICtIRES 3, 4, £fld 5
Specific Conductcr ce
vs
Ti me
3
2.
1
pH
Time
vs
‘I)
U
-9
L
U
(I ,
Dischcr e
vs
Ti me
7 10 1 4 7
pm ine 19,1978 cm Ji .. re 20 pm
Time (flours)
256
-------
PICUP.ES 6 and 7
Zinc 1 Aluminum, and Iron
Concentrations
vs
Time
Fe
am
Time (ho’j
C,
Li
C
U
1
4
E
10 1 4
6
4
U
C
C
U
0
-I
Copper and Mcnganese
C once nt rct ‘ 0 ns
vs
T i rn e
4
pm June19 1978
1 4
10
June 20 pm
4
257
-------
2
20
FIG ES 8 arc S
Zinc, Aluminum, and Iron
Loads
vs
Time
12
F
e
Fe
4
4
1
4
1 4
Copper
C,
and Mcngcnese
Loads
vs
Ti m e
Mn
pm June 1
1
8
4
cm June 20 Pm
Time (hours)
1 4
258
-------
all water samples vets analyzed for pB, specific conductance and tenpera—
ture in the field except those in table 9 which were measured i n the lab on
th. following day. Zenediately upon returning to the lab, dissolved iron,
copper, zinc, manganese and aluminum were determined by atomic absorption
spectroscopy. For the first five storms the water samples were neither
filtered nor acidified since it would take as Long to treat the samples as
it would to recurn to Charlottesville and run an iron analysis. There was
also a critical shortage of sample bottles in which to store treated samples
at that time. Samples from the sixth storm were filtered (0.45 u filters) and
acidified in the field. In addition to the metals mentioned above, the major
cationi and anions are being analyzed in the samples collected from the sixth
storm.
For the third, fourth and fifth storms water samples remained in the
automatic sampler for several days due to the length of the sample period.
When the samples were pickad up, it was found that oxidation of iron from the
ferrous to ferric state had induced flocculation of ferric hydroxide. Con-
sequently the dissolved iron and pH values may be useless. For these three
storms the pH, specific conductance and iron values were either not measured
or they should be considered as rough estimates where reported. However, the
copper, zinc, manganese and aluminum values are reliable for the following
reason. Flocculated samples have been analyzed for these metals both before
and after acidification and results indicate that at the pH values characteris
ic of Contrary Creek, all of these metels remain in solution even though iron
hydroxide precipitates. Thsrsf ore, values for copper, zinc, aluminum and
mangenese listed in Tables 7 through 11 represent both total and dissolved
concentrations. The iron concentrations listed in these tables only represent
dissolved iron at the t.me of analysis and not at the time of sample collection.
The •tabiltty of dissolved iron in samples stored in the automatic sampler
259
-------
determined by removing a portion of the first sample and iediately filter 1 ng
and acidifying it. tron levels in the treated sample were compared to the
iron lev..l.a in he untreated sample stored in the automatic sampler overnight.
£ decrease of less than 5% was found in the untreated sample. If a sample
was lsft more than 36 hours without treatzen , the ice in the sampler melted
and significant iron oxidation occurred as manifested by an orange gel coating
the walls of the sample bottles. In .u ary only the first, second and sixth
yielded good dissolved iron data. Total iron was not determined except on a
few random samples. Total iron is about 5C% greater than dissolved iron during
high discharge. In the previous progress report we reported that total iron
ass equal or nearly equal to dissolved iron during low flow. Prior to a
storm, the creek water is clear and the creek bottom gradually accunulates
a thick (1—2 cm) orange carvet of amorphous ferric hydroxide. During a storm
the turbulence associated with increaseS discharge churns up the unconsolidated
ferric hydroxide thus creating a suspended iron load and coloring the creek
a muddy orange. The orange carpet is noticeably thinner after a storm.
Several general trends are apparent in the chemical data for Contrary
Creek during rainstorms. For t .e fIrst one to two hours of a ra .nstorm the
concentrations of iron, copper, zinc, and eluninum and the specific conductance
rise abruptly with the initial increase in discharge. Simultaneously the pa
falls. These data demonstrate a surge of surface runoff fr the old Sulfur
Mine site which is only a few hundred meters upstream of monitoring station
4, Readily soluble, efflorescent sulfate nin ’rals supply a mobile form of
heavy metals to surface runoff. Less obvious sulfate minerals impregnating
the soil may actually be more important than these visible efflorescences.
Dark brown pools of acid seepage laden with metals are scattered along the
creek banks and these pools may also contribute to th. metal loading when the
turbulence of the rising waters miies with these poe1 .. The drop in p
260
-------
eonce jtant with the increase in m*ta .l concentration ra .u1ti from (1) the
hydrolysis of iron in the ferric sulfate m.nsrals, especially cepLepite, and
(2) the flushing of acid from the top few centimeters of soil.
There are severs.) reasons why the acid seep pools probably make £
nsgligible contr bucioc to ths spike in the dissolved constituents during
the first part of a rainstorm. First, the fast response tine seems to
indicate a readily mobilized form such as soluble salts in surface runoff.
The seep pools are dense, stable layers which tend not to be mixed into the
math stream until the dtsch.arge has risen considerably and become turbulent
veil above the water level at low flow. Second, the seep poois probably
represent, at maxinwi, about 1 of the tot.il volune o’ the water in the area of
the Sulfur site. If we ae’una their averi ge conductance is 25,000 micromnoe
and figure on a l;l00 dilution on mixing then their conductance contribution
would only be an sdditional 250 micronhos. Since Contrary Creek varies around
300—500 micromhos at low flow then the seep pool contribution could only
anount to an additional 50—802 whereas the actual increase is anywhere from
two to aidht t3.mes the contribution at by flow. It also might be argued that
add .tional seepage water might be discharged into the stream during a rainstorm
by elevation of the groundwater table or increased soil wat r flc’v. However,
this phenomenon vo ild be a ‘elayed response effec t which would show up
in the first hour or two of the rainstorm (especially since the tailings piles
contain a lot of impermeable clays). Finally, as explained below, the relation-
ship between the chemograph record (the spik3ng effect in metal concentrations),
th. weather patterns and the duration of dry periods can be re readily
explained in terms of the diasoluti in of efflorescant salts than the mixing
in of seepag. waters.
Several factors control the magnitud. of the peak metal beds and con-
centrations. First, the length of the dry spell pr.csedin. th. storm is
261
-------
i pertant. Longer periods allow greater oxidation ,f the primary sulfide
iinerals and greatsr dsvelopnent of sulfate efflorescences. These sfflor.scsnces
form by vtspillary upflow and evaporetion of netal sulfate bearing interstitial
water La the nine d p soil. Second, clin ttc factors such as cenoerature,
re.ative ht .idity and wind speed are Important. Righ temperatures • low
relative hunidity and high wind speeds favor evaporation which in turn
encourages heavy development of sulfats efflorescences. Kigh relat.Lve
h iditi. and high tenperatures increase the oxidation rate. Third, the
amount of rainfall and its duration inf’uence the peak magnitudes. Suffic .ent
rain emit fall to saturate the surface of the soil before there can be signif i—
cant overland runoff. If the rain falls clouly over time, the natal peaks
will be diffuse and weak. When the runoff is slow, nuch of the rainwater
will infiltrate carrying the aetal into the ground instead of directly to
the creek.
The first storm on June 8 exemplifies the worst conditions for seeing
aetal concentration and load peaks, i.e. , a weak storm on the day after
another sco n. Consequently, the peak copper and zinc loads were harely
tvice the baseline loads. The fifth scorn on July 2 demonstrate’ moderate
metal loading because itwasanoderate intensity scorn after a five day dry
speU The peak copper and zinc loads fo’ thi. storm were roughl quadruple
the ba.aelin. loads. The second scorn on June 19 represents high metal loading
because of a very heavy thundershower f llovthg six days of dry weather. As
a result,peak copper and zinc loads gave more than a twenty fold increase
over baseline. The sixth storm on September 1.2 occurred under extreme con-
ditiona. The very heavy thunderstorm of short duration was receded by almost
two weeks of hoc, dry weather. The resulting peak in the copper and zinc
loads was roughly fifty tizes the baseline loads. The third and fourth storms
were sempled at such broad intervals, i.e., three hours, that discussion of
the data would not provide any urther information.
262
-------
Otce the staL concentrations and loads peak, they drop very rapidly
(see Figure 3—9). This drop occurs for several reasons. The supply of
soluble metal sulfates becomes exhausted and unpoilu..ed runoff from upstream
sources dilutes the Sulfur Mine runoff. In some storms the rain may step
before the efflor.scent minerals completely dissolve. hus ha1tin the trans-
port of metals to the creek. etal loads do not fall as raptdly as the metal
concentrations because th. creek discharge continues to rise while concen—
tx tions fail. In fact, the creek disch.arge generally reaches a broad peak
several hour, after the metal concentratioig. Dilution causes metal concen-
trations to fall below normal dry weather 1e:els. The metal loads remain
substantially above fair weather loads because the discha:ge is high. If
thi, were a simple system with a single mine polluting Coutrary Creek, the
natal concentrations and specific conductance would be expected to rise
slowly to their pr.—storm level. as dilution effects subside. Si.nulraneously
pB valu.s, discharge and metal loads would be expected to fall gradually to
normal levels. Instead specific conductance and some of the metal conceotacions.
especially zinc, rise to a sec ni smaller peak.
This second concentration peak arrives at monitoring station 14 anywhere
from four to eleven hours after the first concentration peak. The travel tine
depen.as on the storm’s intensity. Higher stream velocities which accompany
the higher discharge from a sudden, heavy thunderstorm, lik, the Septsmb.r 12
storm, result Lu a quick •L tvat. Also surface runoff dev.i s more quickly
in a heavy rain so soluble sulfate sinarala are transported to the creek
faster. Conversely weak storm., Like the July 2 rain, result in a slow arrival.
The correlation of travel time with storm intensity suggests that the second
concentration peak originates from a sourca et. a constant distance upstream
from the Su3 fur Mine. During the last storm, vst r samples ware collected
263
-------
upstream of the Sulfur Nine at monitoring station 03. These samples indicate
that th. second concentration peak seen at monitoring station 04 originates
from the Arminius Mime based on the following line of reasoning. N,nitoring
station 03 is located on t’. downstream edge of he Boyd Smith Mins and 1.4
kilometers below the Arminius Mine. During a stern ‘ orh nines would be
expected to produce a metal loading peak, but the Boyd Sm.ith peak would
arrive first because of the mine’s proximity to the station. Indeed two
peak copper loads were measured at station The ftrst peak arrive an hour
after the storm began and the second peat arrived two hours Later. T e Boyd
Smith peak, the fii st to arrive, carried only one—fifth the copper load of
the £rmtniu.s peak. Of the two loading peaks detected at station 43, only the
Arminius peak carried enough copper to produce the second loading peak mesi ..rod
at station 04. Therefore, it appears that surface runoff fam the Arm.tnius
Mine is responsible for the second loading peak at bot’ statinns and 04.
In contrast, the large first peak at station 44 comes from the Sulfur Mine and
the first peak at station #3 comes from the Boyd Smith Mine. b hsther the weak
Boyd Smith peak can b. discerned between the w e Su1f. i and nius
at station 44 is questionable. Further analysis of samples from the Last
storm for zinc, lead, cadm.ium, iron, aluminum and manganese will be completed
before any final conclusions are dra . However, cert i.n field observations
also indicate thaL the Armi. ius t ne produces the second metal loading peak.
First, sulfide ore and sulfate efforescs ’ces are much more abundant at the
Arminiua Mine than the Boyd Smith Mine. Second, the Arminius Mime tailings
cover roughly twic, the area of the Boyd Smith (the tailings.
The chemical composition of the s cond loading p.ak at station #4 in the
first, second, fifth and six_h ser’es as a fingerprint for s urces of the metal.
For example, the zinc to copper ratio in the second peak is roughly double
264
-------
the ratio in the first peak. This high ratio iaplies a zinc rich source for
the second peak, iuch as the Arm.tniua Mine which is tno ’ for its zinc rich
sulfide ore. Manganese and specific conductance clinb to much weaker pea5.
ring most stoma, iron, alumin and pH valucs do not rsa:h a seccnd peak
at nitoring station 44. £ s.comd iron p.4k m y form from the A.rninius
dishearge but in the tine the water takes to flow to monitoring station 4.
the iron nay oxidize and flocculate out. Conae uently the second iran peat
could be obliterated. Above the Sulfur ML s dissolved al ini. nov precl7i—
tate as the hydroxide because of the high pH values associated with storn
runoff and thus eliminate the second aluninun peak if it exists.
Once the second peak has passed, the creek behaves as expected. Dtschar e.
natal loads and pH values gradually fall to dry weather levels. At the same
time, net. .l concentrattons and specific conductance rise to norma. va ta With
the fall in discharge th. orange turbidity disappears and the creek water regains
its transparency. The creek chenLstry requirei approximately a week to ret ..ru
to quail—steady conditions. Recovery tine appears to vary depending upon the
intensity and duration of the rain.
An ex.i’aple of the relative contrIbutions of n..al concentrations Iron
the various tributaries and nine sites can be se, on aSle 12. Severa lte=s
are worth noting from these data. Tha most acid tributary is Tr—2 with the
lowest pH (2.75) and the highest conductance (278Q). l1’is trioutary drains
from a shaft of the Sulfur Mine which ta probably connected to a large
excavated or caved in area just south of the shaft by underground workings.
The excavated area is filled with water and probably represents the Level of
tha ground water table. This level is several feet higher than the level of
Ccntrary Creek, thereby exerting preesur. on subsurface waters to flow towards
the creek. Although Tr—2 La very acid it does not have as high metal concen-
trations as some of the other trtbutaries and it has the lowest flow. ‘.PUrlng
the s er and fa]l it comeonly dries up.
265
-------
C.rtais variations in sets]. counsatrac inns irs particularly notsworthy.
aing dovoacrean transport fron CC—I to CC—4 the Largest Increases in hydrogen,
copper and iron concsntrsttans occur between CC—3 and CC—4 (past the Sulfur
Un. tailing. p11..). In contrast the largest incretse in zinc and calciun
concentrations occurs between CC—i and CC—2 end the Largest increase in
sanganese occurs between CC—2 and CC—3. These data inpiicat . the Aruinius
sits a. s source of anonoleusly high zinc L.aching and the Boyd Snith site as
a source of anonolously high nanganese leaching. though the abundance of
sine and ngansss—rich omen]., in the respective ors deposits are not ovn
at this tine it certainly is a point worth pursuing. Boulders fron the
£rslnius tailings have been found to contain abundant crystals of gabnite.
zinc—rich apin.l,and this oks.rvation nay be indicative of a zinc—rich portion
of the ore body.
Increase, in nagnesiun, sodiun and potassi are either proportionally
about the sane between sonitoring itatiens in Contrary Creek or are negligible.
fleas elenents axe indicative of leaching of the country rock, a quartz-sericite-
chlorite schist, which is the sane throughout all the others]. deposits and
would not be expected to reflect any anonoLous values in the waxer chenistry.
)Iatal loads have been calculated fron the data in Table 12 to denoostrate
cbs relative n as a transport of dissolved ostals fron different sources (Table
13). II CC—4 is considered cbs point of nas a output Iron the watershed and
CC—3, Tr—l and Tr—2 ar. considered identifiable overland flow inputs then the
difference represents non—identifiable inputs which are prinarily subsurface
seepage (t clud both inter—flow and base flow). On this basis we find that
overland flow sccounts for only U of th. copper input at the Sul.fur site and
89Z cones Iron subsurface seeps. This mount is a very large conponent of
subsurface flow cc arsd to zinc Vbich is 4)1 overland flow and 391 subsurfaCe
266
-------
Table 12.
Source Cu Zn Fe Mn
T N-i
TR—2
.32
4.11
Che.ical Data for Contrary Creek
and Tributaries on December 8, 1978
spec.
Cd Pb C. Mg Na K pH cond.
2.38
6.84
0.36
8.71
29.0
63.2
TR-4
TR-6
0.010
0.040
<0.5
<0.5
<0.05
0.22
7.4
208
<0.05
0.77
4.7
108
0.06
6.10
2.99
4.04
0.06
1.31
F1 w
0.010
0.010
1.46
1.26
4 • 80
2.75
<0.5
(0.5
0.20
2.24
235
2788
TN—i
TR-8
TR-9
TN- 10
3.5
5.9
0.82
16.7
0.147
0.00025
2.7
3.6
7.15 0.41
28.8 14.9
4.06
3.75
0.015
0.075
0.78
1.20
6 • 38
3.55
cO.5
<0.5
5.73
0.45
62
335
5.3
49
39.8
17.5
0.0138
0.0036
4.3
42
34.0 10.0
0.57 17.8
4.08
4.71
1.09
5.02
0.300
0.070
4.73
3.03
<0.5
<0.5
173
1216
59
237
0.0203
>0.0203
80
142
4.08
11.0
5.03
6.45
CC- 3
CC—4
3.l(
3.9!
0.16
1.10
CC—i
<0.05
(0.05 0.27
0.04 0.010
<05
3.5
2.3
3.37
1.30
6.8
59
1.90
CC—2
0.09
3.54 0.52
0.42 0.010
<0.5
12.8
7.7
3.61
1.59
S!9
184
1.67
1702
1962
2.96
4.85
0.00062
0.0034
1.71
1.96
0.69
38.5
0.010
0.015
<0.5
<0.5
19.6
18.8
13.2
17.2
3.84
3.88
1.58
1 .74
4.4
3.5
299
59,
2.45
3.80
Concentratloni are mg/i and discharges in cfs.
(equivalent to microethos/co).
Specific conductance Is In micro Siemeus/Ca
-------
TABLE 13. Metal Loads (kg/day) for Contrary Creek and Tributaries on
December 8, 1978.
Source Cu Zn Fe Mn
Tr—1 0.11 0.86 10.5 0.13
Tr—2 0.003 0.004 0.039 0.005
Tr—4 < 0.002 < 0.002 0.002 0.002
Tr—6 0.002 0.006 0.054 0.011
Tr—7 0.010 0.040 0.355 0.021
Tr—8 > 0.11 0.83 1.5 0.74
Tr—9 0.0086 0.060 0.052 0.016
Tr—iO 0.003 0.145 0.004 0.15
CC—i < 0.23 < 0.23 1.3 0.19
CC—2 0.37 14.4 2.2 2
CC—3 0.95 17.7 4.1 10.3
CC—4 10.2 45.1 358 18.2
268
-------
seepage. A similar disparity is seen for $ mass balanc, at the Boyd Smith
sit. where 132 of th. copper is overland flow from Boyd Smith, 392 is flow
from the Axnin.ius and 482 ii subsurface f low compared to 132 subsurface sinc
flow. Iron behaves like copper with 962 of the input coming from subsurface
seeps at the Sulfur site. Manganese is most similar to magnesium, sodium and
potuslon with 572 coming from overland f low and 432 from subsurface seeps.
Bevever, at the Boyd Smith site 742 of he Loput to CC-3 is from subsurface
seeps vtiich means that most of the manganes a is coning from subsurfacs f].aw
at the Boyd Smith site. Two possible reasons may explain the high manganese
at Boyd Smith: (1) there may be a greater abundance of . ‘ ganes. in the
tailim;i at this site or (2) a more reducing enviroin.nt exists in the Boyd
Smith tailings which is required f or th. dissolution of manganese from typical.
aanganaae—beariog minerals. The latter is the most lik&1y of the two alterna-
tives.
Pinally, interpretations of this type (hued on Table 13) are snbject to
criticism f or several reasons and can only be considered r0u9h estimates of
a mass balance at on. point in time. Per example, at another time of the
year the mass flow might be considerably different dus to changes in the
t eraturs, the amount of soil aeration, and the height of the groundwater
table, etc. Also, chmeicai. reactions take place, especially on M4y4ng, which
confus, these calculations • For example, iron is oxidizing and precipitating
in a particulate form in th. stream sediments. irace .lonents are either
coprscipitating or adsorbing onto sediments during transport. We have one
set of date which shows a striking example of adsorption and/or copr.cipitation.
On August 28, 1978 samples were collected at CC—l, 2, 3 and 4 and tributaries
Tx4, 9 and 10 and analysed for dissolved lead. Tr-8, the mouth of the main
flow from Boyd Smith has the highest dissolvsd lead found anywhere, 0.25 mg/i
(pH • 2.8$). At CC—3 th. dissolved lead was 0.003 mg/i (p3 • 4,75), a
269
-------
eonaUsrabl. decrease for only a f., asters dovnitreaa fron the n1Y 1 g point.
Probably aou of the lead vs. r oved by sorption onto partic. es (or copre—
cipftatsd vith fsrric hydroxide) although we o uot have say values for the
discharge to calculate the decrwe f:ot ( 4ng. The decrease in conductance
between Tr—8 and CC—3 suggest. a dilution uf 4.4 tines which indicates that
952 of the dissolved lead vs. adsorbed onto ,trea . . •edi ’ ’ts!
270
-------
DIS SSIOM
ft. relative contribution of each of the three nines to tbs natal.
loading during storm runoff can be qualitatively evaluated with he data
from the six storms. Obviously, the Sulfur Mine contributes th. bulk of
the metal and acidity to Contrary Creek during a rainstorm. Surface runeff
from h. ether nina . could net possibly arrive in tins to add to the first
and largest peak of natal conc.ntrations and loads. For cost metals it is
dLf icult to diflerentiate the Arminius surf ace runoff load fran possible
Sulfur Mine interfiow and basef low loads. Zinc Lean exception since it has
en obvious second concentration and Load peak. For the first and fifth stoma
tha secoad peak tint load approached the magnitude of the Sulfur Mine peak
tine lead. Movv.r, son. of the zinc loading in th. creek, when the Amminius
concentration sad load peak arrived, was probably derived from the Sulfur
Mine. The second peak zinc load during the second storm was issa than half
the Sulfur Kin. peak Load and in the sixth storm the setood peak we. only
equal to two—thirds of the Sulfur Mine peak. Again a significant fraction of
the s.cond peak may have drained from the Sulfur Mine. Further analyses and
interpretation are needed to distinguish surface runoff from bue f 1ev and
interflov although the Arminius sits certainly appears to be of secondary
twportancs in zinc loading compared to the Sulfur site. Differences in rain-
fall intensity at the nine site. may account for sane variation in the relative
gnitude of peak heights. The Boyd Smith Mine has shown a small concentration
end load pe*k at monitoring station #3 in th. sixth storm. As n.nUoasd saner,
seaple. were not collected for the first hour of this storm and the Boyd Smith
peak ssened to be arriving wham th* first sample vu taken. If th. peak
arrived earlier, then its magnitude was under.. t mated. Rovever th. actual
peak is not thought to have beet aich Larger because the proximity of the
271
-------
s ling station to the aLas indicates that roughly one hour vould b. required
for the b.gtI Itng of runoff and its flowing to the station. When thi.s anall
Boyd Smith load reached monitoring station D4, it vas difficult to detect
bcauae it mixed with the last part of the huge Sulfur Mine load. In
Piguras —9 for the second storm a snail bulge on the shoulder of the Sutfur
(In. load and concentration peaks may be the Boyd Smith load. This bulge could
also represent runoff frOm the upper end of the Sulfur ttne, the first arrival
of Sulfur Mine Interf low or a second pulse of runoff from the cain Sulfur Mine
d ps dus to a second wave of rainfall. The double peak in the discharge for
this storm suggests the third alternative. Whether this bulge, or third peak,
occ s during all storms is questionable. Thsse results demonstrate the
relative inaianificance of the Boyd Smith Mine as a pollution source. In
conclusion, the contribution by each mine to the runoff pollution is roughly
proportional to the contribution by each mine during Low flow conditions.
Purther calculations and interpretation of he data should be available In
£ M.S. thesis (Ton Dagenhart).
272
-------
AC OWLGflf TS
V. its $r .t.Sul to th. Callahan Mining Corporation aad Richard Raid. for
allovln* no to u sa thur of fine ahsd at thu £rslaius Nina for skaltar during
fiald processing of sanpisa. Also on would iLk. to thank then for paroitting
access to the Cot at Mine. Vs at. Indebted to the Cbarlcttsavilhs offics of
the Stats V tir Control Board for providing gauge height recording. of Contrary
Crank and a rating curv , to calculate the discharge. Both the Charlottssvil.l.
office sod cbs Bridg.iatsr office hays grn.roualy £ssist ed in thu collection
of wstsr sa l.a and discharg, data. Richard S. Mitchell of the University
of Virginia first identified sane of the Cater Mine nin.rala. Ru cooperation
and contribution to the study of soluble sulfate ninarala at all th. nines is
appreciasod. Pat Ryan, Andy Davi., Steve Goodwin sad John Walton, graduate
•tudsuta at cbs Dniv.rstty, have kindly usistad in the field work and in the
nic.s.l analysis.
273
-------
PRES TATIONS AND R J 1 T!D PUBLICATIONS
Nordetron, D. K. and Dsgsnhart, V. V. (1978) Hydrated iron suliats ninerals
associated vith pyrite oxidation: field relation. and thermodynamic
properties, paper pres.ntsd at the 91st Annual Ms.ting of the Geological
Society of America, Toronto, Canada, October, 1978.
M G.ocbmeistry of Acid Mine Drainage from Massiv Sulfide Deposits,” • “t
presented by D. K. Nordstr ’n at the Department of Geological Sciences,
Virginia Polytechnic Institute and State Uulv.rsity, Black.aburg,
November, 1978.
Nordstrom, D. K., Jsnne, !. A. and Ball, 7. V. (1978) “Radar equilibria of
iron La acid mine vaters,” • 1 ar presented at the 176th Annual Meeting
of the American Chemical Society, Miami Beach, Plorida, September. 1978,
to be published in Chemical Modeling in Aqueous Systems. Speciation,
Sorption. Solubility and .inetics .
Nordatran, D. K. (1979) Aqueous pyrite oxidation and the formation of secondary
iron sulfate end iron oxide/hydroxide minerals, Acid Sulfate Weathering
Symposii , Soil Science Society of America, Annual Meeting, Pt. Collins,
Colorado.
274
-------
R . 1CZS
T1.iacher, H. (1973) 1925 Glossary of Hinaral Sp.cie. , Mineraiogicil Racerd,
Inc., 143 p.
Jaabor, .1. L. and ft. .7. Trail (1963) On rozanits and .idsrotil, Can. Mineral.
L. 731—763.
Luttrsll, C. V. (1966) Baa.— and precioua- ana1 and related ore d.postts of
Virginia, Mineral Rasour. Rapt. 7, 167 p.
Hiorin, A. V., KLiagsna th, ft. S. and Sa1i maa, 3. R. (1974) Contrary Creek
Mine Drainage Abatsnant Project: Peasibiliry Study, Gannett Y1 ing
Corddry sad Carpenters Engineers Rsport, 73 p.
PaI.ache, C., krncn, H. and Proadel, C. (1951) Dana’s Systen of Mineralojy ,
Vet. II, Wiley and Sons, M.T., 1124 p.
275
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Appendix E
BIOLOGICAL SURVEY OF THE
CONTRARY CREEK ARM OF
LAKE ANNA, VIRGINIA
BS74-003
By
Richard W. Ayers
Division 0 f Ecological Studies
Bureau of Surveillance and Field Studies
January, 1975
276
-------
TABLE OF CONTENTS
Page
LIST OF TABLES 278
LIST OF FIGURES 279
ABSTRACT 280
CONCLUSIONS 281
INTRODI’CTION 282
METHODS AND MATERIALS 283
RESULTS AND DISCUSSION 287
Physical-Chemical Parameters 287
Algae 2Y 0
SwTlary 294
Heavy Metals 295
Sumary 3’)1
MacrobenthoS 3’)2
Sumary 305
Fish 307
Sumary 309
REFERENCES 310
277
-------
LIST OF TABLES
Table No. Page
1 PhysIcal—Chemical Propcrtles at Survey
Stations 288
2 Taxonomic List of Plankton Organisms per
Station 291
3 Heavy Metals Analysis of Bottom Sediment 296
4 Taxonomic List of Organisms 303
5 Fish Netted In Contrary Creek 308
278
-------
LIST OF FIGURES
Figure Page
A Map of Survey Area 286
1 Plankton Populations of the Contrary Creek Arm
and Control Stations of Lake Anna, Virginia 293
2 ZInc In Bottom Sediments of Contrary Creek arm and
Control Stations in Lake Anna, Virginia 298
3 Copper in Bottom Sediments of Contrary Creek arm and
Control Stations in Lake Anna, Virginia 299
4 Chromium in Bottom Sediments of Contrary Creek arm
and Control Stations in Lake Anna, Virginia 300
279
-------
ABSTRACT
The biological conditions In the Contrary Creek arm of Lake
Anna, Virginia were determined by sampling physical - chemical
properties, algae, f$sh,macrobenthos, and bottom sediments. Acid
mine drainage from the upstream, free flowing porticn of Coitrary
Creek Is causing an alteration of normal lake physical - chemical
properties and algal and fish populations. The bottom sediments are
contaminated with heavy metals from acid mine drainage. Macrobentho
populations are limited as much by substrate composition as by acid
mine drainage.
280
-------
CONCLUSIONS
1. Algal populations and light penetration data show a definite
reduction in productivity In the acid waters of the Contrary
Creek arm.
2. A pH and 0.0 çradlent was noted from the upper end of the Contrary
Creek arm to the control stations.
3. Heavy metals in the sediments are much higher In Contrary Creek
than in areas previously unaffected by acid mine drainage and
mey be high enough to adversely affect macrobenthic populations.
4. Natural substrate composition in the study area Is a factor
favoring pollution tolerant bottom organisms, thus rendering
pollution determination by evaluation of macrobenthic coniuunitles
Impossible.
5. The fish population of Contrary Creek has Improved since creation
of the impoundment.
6. This fish population Is not as dense nor as diverse as that found
In the main body of the lake.
7. The fish In Contrary Creek are taking up heavy metals in amounts
that should require monitoring.
281
-------
INTRODUCTION
During May and June, 1974, a survey was conducted on the
Contrary Creek and Douglas Creek arms of Lake Anna In Louisa and
Spotsylvanla Counties. The pu’poce of the survey was to characterize
the blota and the heavy metals content of the bottom sediments in
Contrary Creek ann of the lake. The Douglas Creek stations were
used as controls. Contrary Creek is affected by acid mine drainage
from three abandoned pyrite mine sites above the lake portion of
the stream.
The acid mine situation results from the oxidation of iron
disulfides exposed to air by the mining activity. These materials,
usually found In slag piles, when exposed to water and air are
oxidized to ferrous sulfate and sulfuric acid, as In the reaction:
2FeS2 + 702 + 2H20 ) 2F S04 + 2H2S04
The ferrous sulfate is then further oxidized to ferric sulfate by
chemical or bacterial activity:
2FeSO4 + 0 + 2112504 )Fe2(S04)3 + 1120 + 112S04(2)
The ferric sulfate is hydrolyzed by the water in the receiving stream
to the final reaction products, sulfuric acid and ferric hydroxide.
Fe2(S04)3 + 6 1120 2Fe(0H) + 3112 S04 (2)
The reaction products are then carried into Contrary Creek by small
surface or ground water tributaries ihich drain the mine area. The
acid water condition found upstream persists into the Contrary Creek
arm of Lake Anna.
282
-------
METHODS AND MATERIALS
Sediments were sampled in the former creek bottoms (maximum
depth) at each station using a six-Inch Ponar dredge. Material
from the top 1/2 Inch 0 f the dredge sample was collected In plastic
bags and refrigerated until analysis. The metals analyses were
performed by the State Division of Consolidated Laboratory Services
using an acid digestion-atomic absorption spectrophotometriC method.
Mercury digestion was done with sulfuric and nitric acids. All
other metals were run using hydrochloric and nitric acids in the
digestion step. The results are reported on a dry weight basis.
Water conditions were measured in the field with the collection
of algae samples. Measurements of light penetration were made using
an eight inch Secchi disc. The maximum visible depth, as the disc
was lowered from the surface, was averaged with the first visible
depth, as the disc was raised from the bottom, to determine light
penetration. Dissolved oxygen and temperature were measured with
a YSI Model 57 dIssolved oxygen meter and probe. The pH was
determined colorimetrically using the Hach wide range indicator kit.
Five algae samples were collected at each station. Two of the
samples were surface “grab” samples. Three were collected with a
Wisconsin plankton net by making vertical tows from the thermocline,
when one was present, to the surface. One of the surface and two of
the vertical tow samples from each station were preserved in 10%
Lugols solution. The other samples were examined unpreserved.
Examination of the samples was made using a compound microscope
and the Palmer-Maloney Nanoplankton cell. Quantitative figures
283
-------
were obtained by determining the volume of water sampled by each
net tow and applying this volume to the total number per milliliter
figures from the Palmer cell counts.
Two grabs with a six Inch Ponar dredge were taken at each
station for macrobenthos identification. All benthic collections
were located at approximately the same depth (four feet) to allow
more direct comparison. The samples were washed in a bucket with
a standard No. 30 sieve bottom. The material retained by the sieve
was preserved in 70% isopropyl alcohol and returned to the office
for sorting and identification. Taxonomic identification was made
to the lowest level experience, available Information, and time
would permit.
The fish data collection and part of the Interpretation for
the fish section was taken from work underway by the Department of
Biology, Virginia Coninonwealth University under a grant from Virginia
Electric Power Company. The fish were taken with experimental gill
nets set over night at stations in Contrary Creek and at the reactor
site. #tals analysis of fish tissue was made on an atomic absorption
spectrophotometer by the flame method.
The survey area and station locations are shown on the map.
StatIons 1 and 2 were in the Contrary Creek arm above the confluence
of Freshwater Creek. This section Is the area most affected by
acid mine drainage. The water is clear and live aquatic vegetation
Is sparse. Station 3 was on Freshwater Creek arm in an area which
was not affected by acid mine drainage before the Impoundment.
Stations 4 and 5 were located In Contrary Creek where recovery from
284
-------
the upstream conditions might be expected. StatIon 4 was 300 yds.
below the Rt. 652 bridge and Station 5 was 500 yds. alove the mouth
of the Contrary Creek arm. StatIon 6 and 7, used for unaffected
comparison, were located across the lake from Station 5 In Douglas
Creek. StatIon 7 was two thirds of a mile upstream of station 6 In
a shallow tributary.
285
-------
o
-.
•
I
Jl ..
- 7
•‘
- - i r
I -— , •,
/ .
i; r ’ P
IS 74-003 Contruy Creek
Loulsi Co. Yoric R. Basin
I
-------
RESULTS AND DISCUSSION
Physical — Chemical Parameters
The productivity of waters is closely related to the carbonate
buffering system. The addition of mineral acids, coninonly found In
acid mine drainage, preempts the carbonate buffering capacity; and
the original biological productivity Is reduced In proportion to
the degree that such capacity is exhausted. Water with pH values
below 4.5 is considered to be devoid of measurable carbonate buffering;
and therefore, very low in biological productivity. Most researchers
agree that aquatic organisms survive best In a p11 range of 6.5 - 8.5
although some specially adapted forms will thrive in pH values above
or below this range. In general. the density and diversity of an
aquatic corinunity will decrease when the pH falls below the optinvm
range.
The tests made of surface water pH IndIcate a definite change
In water quality conditions as one approaches the main body of Lake
Anna from the head of the Contrary Creek ann. The pH values from
stations 1 to 4 were in the 4.0 - 6.0 range. This is below the
optimum level for most aquatic inhabitants. The data for Station 5
compares favorably with ph values from stations 6 and 7. This
indicates that the upper end of Contrary Creek ann Is affected by
low pH, while the main body of the lake is not (See Table 1).
In a study of six acid mine lakes, Smith and Frey (1970)
found the level of dissolved oxygen and the percentages saturation
increased with Increasing pH. They found that waters with chronic
low pH condItions are subject to high oxygen demand from dissolved
substances and thus contain lower dissolved oxygen (DO) than waters
287
-------
1 .A&t I
PHY5ICAL—CI4 MICAL PROP(RTIES AT SURVU SlATIOPIS
SECCIII OtS
STATIOJI DEPTH 0.0. mQ/1 •_ •OC R AOT G
Surface 6.2 23 4.0
3 ’ 6.2 23 4.0 3’
2
Surface
10’
6.9
23
21
4.4
10’
3
Surface
7.0
23
5.3
10’
18
4
Surface
7.3
22
5.8
8’
22
14’
19
16’
I?
19’
16
24
16
l1 ’7
S
Surface
8.0
23
7.6
8’
7.9
21
11’
20
15’
6.4
17
6’l
23’
4,6
IS
33’
1.9
13
44’
1.3
13
6
Surface
8.1
22
7.8
5’
8.1
22
10’
8.0
22
IS’
6.2
18
81 ’
20’
5.3
16
25’
4.1
14
36’
1.0
12
7
Surface
8.0
24
7.7
S ’2
6’
288
-------
without the solutes. The dissolved oxygen levels found at each
of our stations Indicate that no severe oxygen depletion is occurring
In the acid water at stations 1-4. The DO at these stations Is,
however, lower than at the other stations indicating a possible
correlation between low pH and lowered DO. The fact that surface
temperature readings were nearly uniform for all stations also
lend support to the association of pH and DO data.
A stratification of temperature and DO was noted for the deeper
waters at Stations 5 and 6. No significant differences were found
between the two stations in this respect and the conditions are
assumed to be those normally expected In lake waters.
The penetration of light, as measured by the secchi disc
readings, Is much greater in the clear acid waters of Stations 1-4
than at St4tlons 5-7. The differences are expected as the latter
stations exhibit normal pH and increased turbidity, partly due to
higher concentrations of plankton. Light penetration Is essential
for plant growth; however, secchi readings In the Contrary Creek arm
at Stations 1—4 IndIcate great clarity. This visibility is, un-
fortunately, not an indication of good growth potential but rather a
lack of algal growth and natural turbidity, which would cloud the
water somewhat.
289
-------
Algae
A taxonomic list of plankton collected and their abundance
at each station are presented In Table 2.
The majority of these algae normally exist under alkaline conditions.
In areas of extreme acid conditions all organisms may be absent.
Below p14 3.9 dIversity Is reduced to a few green algae and flagellates,
both of which appeared dominant where organisms were present in
Contrary Creek. Five samples were taken at each station and, while Table
2 does not show it, a small number or the absence of plankton were
noted on the majority of Contrary Creek samples. This indicates a
paucity of living algal species and a definite pH caused reducflon
In the flora of Cont ary Creek. Small chlamydomonads and an un-
identified oval ç’reen algae, which is probably a rarely occurring
form tolerant of low p I, were the dominant species observed. Desmids,
which are tolerant of low pH, were also present. These organisms
were found in the very low pH waters of C ntray Creek as well as in
Douglas Creek.
Asterlonella , a peno te diatom capable of forming blooms, was
0 the dominant plankton In the survey. The abundant occurrence of
this organism has been reported by other workers studying phytoplankton
succession in this new lake (Simons, 1972). It is comon to have a
spring diatom pulse In lakes and Asterlonella was undergoing such a
pulse during our sampling. The population size differences in
Asterionella from station to station make pH selectivity in this
diatom very apparent. The Douglas Creek samples contained as much
as four times as many Asterfonella as the Contrary Creek samples.
The StatIon 3 data shows a higher Asterionella population present
In Freshwater Creek as well.
290
-------
TABLE 2
TAXONOMIC LIST OF PLANKTON ORGANISMS PER STATION
Presented as numbers per milliliter
Station Station Station Station Station Station Station
___ 2 3 4 5 6 7
CMorophyceae
Coelastruni 1,020 +
Pedlastrum + 1,020 1,020 1,020
Scenedesmus 1,020 1,020
Chiamydomonas 1,020 1,020 +
Tetraedron 1,020
Cosmarium
Staurastrum 1,020 2,040 1,020 1,020
Mouqeotia +
Unidentified 1,020 16,320
Chrysophyceae
D nobryon +
Centric Diatoms
Melosira 9,640
Unidentified 1,020
Pennate Diatoms
Asterionella 3,060 8,160 5,100 19,380 12,240
Gomphonema +
Tabellarla + +
Eugi enophyta
Trachelomonas 1,020 +
Dl nophyceae
Perid lnium 1,020
Rhi zopoda
Difflugia 1,020 3,060 +
Rotifera
Brachi onus +
Euch1an s +
F’ l l ln Ia +
Cl adocera
Daphn la + +
Copepoda + + +
Total 1,020 5,100 9,180 6,120 8,160 51,480 14,280
Organisms per
liter of net
volume 7,698 4,730 7,884 3,156 6,839 52,875 43,363
(+) Observed
291
-------
In terr%s of total plankton populations per milliliter of
sample 3 aefinlte progression can be found as one moves out of the
Influence of the acid mine drainage. The populations are represented
graphically In Figure 1. One can see a gradual rise in over-all
population from Station 1 to 5 as one moves toward the main b dy
of the lake. The Station 3 figure Is higher than any Contrary Creek
sample even though it is In the Freshwater Creek arm, an area
influenced by Contrary Creek water. The heavy metals content of
this water may be lower than In the Contrary Creek arm and the
inflow of fresh unaffected water from Freshwater Creek nay be
helping to maintain this higher plankton population. The control
areas had from 2 (Station 7) to 6 (Station 6) tImes the population
of the best Contrary Creek station. The difference in control
figures is partly due to the difference in depth of the water at
the two stations. When converted to numbers per liter of tow net
volu’ne the control stations are more closely . gned (Table 2).
The control stations, 6 and 7, show a much greater diversity
of plankton than the Contrary Creek stations (Figure 1). There were
15 taxa found at Station 6 and 13 at S ation 7. When these figures
are compared to one for Station 1, four for Station 2, sIx for
Station 4 and three for Station 5 the diversity differences stand
out quite well. Such an increase in diversity at the controls Is
another Indication that the conditions In the Contrary Creek arm
are not suitable for abundant or normal plankton populations.
All plankton observed were typical lake Inhabitants and no
toxic forms were noted.
292
-------
0
Total Plankion
54. ( 1/ / 11 No. Goner. is
48 16
7.
42 / 14
I /
136’ / 12
‘I
I
3O.
E ,1 I
/ ‘$1
a
C
/
a.
$ 18
1 ‘6
12 / / .4
/ /
/ / .2
6 dlii
/ /
— ..4_
1 2 4 5 3 6 7
Contrary Creek Ar. / Control
FIgure 1. Plankton populations of the contrary Crsekarm
and control stations of Lake Anna,VirgInla.
293
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Sunriary . Algae population data clearly Indicates toxic
conditions In the Impounded sections of Contrary Creek. The
plankton population of the Contrary Creek arm of the lake is
depressed due to low pH conditions, which are compounded by
high levels o heavy metals, low carbonate levels and low
alkalinity. Pennate diatoms, green algae and flagellates
are present In low numbers as compared to the population in
Douglas Creek. Diversity In t e Contrary Creek population
is also reduced as compared to the controls.
294
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Heavy Metals
A sui inary of heavy metals concentrations at the seven sampling
sites is presented ir. Table 3.
Bottom sediments are known to concentrate heavy metals to
levels many times higher than those found in the overlying water
column (Benoit et. al., 1967). Metals concentrated by sediments
can redissolve Into the water and produce harmful effects on aquatic
organisms. Figures 2, 3, and 4 Indicate a high level of metals
contamination In the Contrary Creek arm of Lake Anna. Stations 1,
2, 4 and 5 have consistently high concentrations of iron, lead,
copper, chromium, manganese, mercury and zinc. The manganese
levels did not follow the general pattern set by the six other
metals tested. Iron was by far the most abundant metal followed
by zinc, manganese, copper, lead, chromium and mercury.
The data Indicates a trend towards heavy metals at Station 4
and 5. This might be explained by considering that metals will
precipitate out of solution In higher pH water. At the same time
the high levels at StatIon 1 and 2 may be due to settling of suspended
particles carrying metals from upstream.
Due to Its location on a previously unaffe ted stream, Station 3
sediment had low levels of heavy metals. Station 6 and 7 values were
lower than the Contrary Creek stations in all but the manganese
concentrations. The levels found here reflect the high metals content
of the soils in the Lake Anna basin.
The levels of metals In the sediment of the Contrary Creek arm
are much greater than those found In Farmvllle Lake, which receives
295
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TABLE 3
Heavy Metals Analysis of Bottom Sediment
mg/ kg
Station Cu Cr Fe Pb Zn Mn
1 799 31.9 108,000 145 1307 0.62 72.6
2 788 33.3 72,000 35 1161 0.33 131
3 80 19.4 19,000 28 320 0.05 220
‘C
4 410 35.9 610,000 296 592 0.25 137
5 904 46.0 66.000 321 1151 0.25 411
6 180 29.1 37,000 46.7 395 0.13 9 9
7 27.3 11.3 18,000 16.2 92 0.07 439
-------
no acid mine drainage, following a copper sulfate caused fish kill,
#74-092. The total copper values ran from 635 to 171 mg/kg in
Farmville Lake while the Contrary Creek samples were In the 904
to 410 mg/kg range (Figure 3). Levels of chromium, zinc and lead
were also comparable or higher in Contrary Creek.
The investigation of another copper sulfate fish kill.
p69-022, on a water supply lake in Charlottesville revealed that
sediment copper levels of 2u mg/kg were nct harmful to bottom
organisms while levels of 370 mg/kg drastically reduced the
population (Figure 3).
Values of zinc, copper, chromium and lead from Contrary Creek
were all at or above levels found in the bottom sediments of the
Shenandoah River below Front Royal. This area has been the scene
of many suspected heavy metals (zinc and copper) caused fish kills.
due primarily to movement of metals stored In the sediment back
Into the water column. This toxicity was accomplished by the re-
dissolving of metals during favorable water conditions and re-
suspension of contaminated sediment particles at other times. The
spring and fall turnover activity coninon to lakes could make toxic
levels of sediment stored heavy metals available to aquatic organisms
in Contrary Creek or Lake Anna.
Bottom sediments taken following a heavy metals caused fish kill
on the South Anna River In Louisa Co. (#68-060) showed chromium
levels in the 27.7 to 109.2 mg/kg range (FIgure 4). Zinc levels ran
from 9.3 to 730.8 mg/kg (Figure 2) and lead ranged from 5.6 to 18.6 mg/kg.
297
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1400
Level associated with
fish rortal tieS
1 2 4 3 6
contrary Creek Attn / Control
Figure 2. ZInc in bottom sediments of Contrary Creek arm
wid control stations in Lake Anna.Virgiflha.
1
1260.
1120.
980
MO
70O
1
56O
I -
420_
280.
140
298
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Level associated with
fish morta1 t es
Level associated witn
benthic mortalities
LM
6 7
/ Control
FIgure 3. Copper In bottom sediments of Contrary Creek arm
and coritrot stations In Lake Anna,VIrginIa.
Contrary Creek Ann
299
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Contrary Creek Arm / Control
FIgure 4. ChromIum In bottom sediments of Contrary Creek arm
and control stations in Lake Anna,Virginla.
70
60’
I
I
30’
20
• 10
1 2 4 5 3 6 7
300
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Surmnary . Contrary Creek bottom sediments are contaminated
with heavy metals at abnormally high levels. These levels compare
favorably to those found In areas experiencing heavy metals caused
fish kills. The possibility exists that these heavy metals levels
could be limiting benthic populations. It Is also possible that
spring and fall turnover could create toxic conditions In the
Contrary Creek arm of the lake by resuspending or redissolving
heavy metals found in the sediments.
Uote: The horizontal lines shown on Figures 2, 3, and 4
are Intended to present an mdi cation of warning level only.
Other water characteristics such as pH, dIssolved oxygen,
suspended solids, alkalinity and hardness will effect the
avaf lability of these metals for reactions with aquatic organisms.
These characteristics will vary from stream to stream thus making
the Indicated levels less definite for Contrary Creek but none
the less useful as indicators of possible prob1e ns.
301
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Macrobenthos
A taxonomic list of organisms Is given In Table 4.
Station 1 was located just at the point where Contrary Creek
becomes an arm 0 f Lake Anna. The substrate here was imid and orange
ferric hydroxide precipitate. The area is obviously subject to
frequent silt deposits from the flowing portion of the stream and
along with the low pH conditions, this restricts the benthic
coninunity to those forms hearty enough to survive. At this station
the dominant organism was the midge Chironomus ( Chironomus ) sp. a
very tolerant type bottom dweller. The plecopteran and the elmid
beetle larva may have drifted down from upstream, their capacity to
survive In conditions like those at Station 1 being very limited.
Station 2 was by far the most productive station In terms of
individual organisms present. The substrate at Station 2 was dead
grasses and ferric hydroxide precipitate over gravel and clay. The
presence of the dead grass must constitute a much more suitable
habitat than the other types of substrate found. Although midges
were dominant at this station, other dipterans (Insect larvae) and
a few odonatans (dragonfly and damselfly) were also pres t. These
organisms are not coninon Inhabitants of acid mine streams but they
are typical lake Inhabitants. The larval and adult stages of
Dineutus (whirligig beetle), were both noted at this station.
It would be difficult to say that Station 2 benthic data
Indicates an Increase In water quality over Station 1, especIally
In the light of the DO and pH readings. The major factor here must
be the change In substrate composition.
302
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1 E 4. TA IC LIST CF CF8MIS16 •
StatIon 1 Stitlon 2 StatIon 3 StatIon 4 Stitlon S St.t$ø. 6 StatIon 1
Tr lctioptera
Wor aldIa 2
OtrIchta I
Plecoptera
Larva caee 2
Coleopter.
CleIdap 2
Olneutus 2 6 4
Odonata
LIbeliula Needhl 2
Cefltbe&s ellsa 2
Ischnura I
Pertihonts tenera
LIbellula Iuctuo a 6 4
Mpod a
Siarldae 2
Diptera
F IIy Ollrono.ldee
ChIrøno.tj (Ctilronis ) 132 104 248 6 12
Chfronosjs (Cryptocblronorias ) 4 10 4 8 2
Po lypedtlua 486 4 2 2 18
Paralauter bornlell . 2 4
Stenochlronoireis 4
Tribe Chironominl unldentlf led 40
Procladlus I? 12 18 16 62 80
Tanytarsu 14 440 20 8 6 12
Pu at ChironosInI 10 40 4 2
a Tanytarslnt 16
. . .YQL orthocladlnac 4
LMidentlf led chlronomtdae 54 2 4
Fi.liy Culcldae
Chaoporus 2
F11 7 Heleldie
Bezzla - type larvae 2 2 4
TOTALS IndIvIduals 164 1188 304 40 30 110 116
Taza 7 16 8 7 4 ii S
• *abers are per s ,are foot
Welgtit g.1rt 2 0.0844 0.4358 1.0458 0.0338 0.0452 0.0314 0.0140
-------
Station 3 was located in the Freshwater Creek arm 300 yards
above its confluence with the Contrary Creek arm. This stream
was not subject to acid mine waters until the Impoundment activity
caused the waters of Contrary Creek to mix back up Freshwater
Creek. The substrate at this station was detritus over fine gravel
with a thin mud layer between. No ferric hydr’xlde precipitate
was present. The benthics here did not present what was expected,
i.e, , a recovery from conditions found at the previous stations
Instead, there were fewer taxa and a lower density than at Station 2.
With water quality slightly above the Station 2 levels, an explanation
of this low population condition is substrate composition. The number
of taxa found here was exceeded only at Station 2 and 6 and Station 3
ranked seconc 1 in numbers of individuals. This indicates that the
potential for population growth Is good in this area but some factor,
perhaps substrate, prevented us from finding what was expected.
Station 4 and 5 were on the Contrary Creek arm of the lake
1 1/2 and 1/2 mile respectively, from the confluence with the main
body. The substrate conditions found at this station were similar.
Both had detritus over thin mud over sand. This substrate did not
prove to be attractive to large numbers of organisms. The samples
were dominated by chronomid midge larvae with one or two other taxa
present, all In very low density.
Station 6 was on the Douglas Creek arm about one half mile
above the main body of the lake. The substrate conditions here were
similar to those at StatIon 4 and 5 with detritus over thin mud over
sand. The benthic population at Station 6 was again dominated by
304
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chlronomid larvae and the diversity was second only to Station 2.
Density, however, was the third lowest of all stations. Substrate
composition may again be the Influencing factor In benthic population.
The high diversity of this station shows a potential for further
growth In population size.
Station 7 was located at the upper end of the Sturgeon Creek
arm of the lake. The substrate here was detritus over thick mud.
This substrate Is generally more hospitable to benthic colonizers
than that found at Station 6. The organisms at Station 7 were all
chironomid larvae with only 5 different taxa observed. The density
of the population was the fourth highest 0 f the samples collected
and considering the population composition and the substrate
available this density is below expectations.
Suim ary . The benthic populations sampled were generally
low In diversity and density. All samples were dominated by the
larvae of chironomid midges. While no one type was found at
each station several were widespread throughout the survey area.
These ‘r gan1sms are very tolerant and they are comonly the dominant
species in acid mine drainage streams. In lakes the normal water
quality may be high enough to support less tolerant forms, but
factors such as substrate composition and stratification of lake
water any select the more tolerant organisms. An attempt was made
to eliminate the effects of variance In water quality according to
depth by sampling all stations at approximately the same depth.
The selectivity of substrate for more tolerant forms may have had
an Important Impact on the results from these samples.
305
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The substrate at most stations was composed of a thin layer
of detritus and mud over fine gravel or sand. This Is not suitable
for most aquatic Invertebrates In terms of food sources or living
habitat. The area of Station 2, which is severely affected by
acid mine drainage, was more hospitable to Invertebrates because
of the presence of dead grasses on the substrate. The populations
at Stations 3 and 6, although limited In size by the substrate, were
high in diversity and Indicate the potential for future expansion if
the substrate conditions Improve.
With the possible exception of Stations 1 and 7, the substrate
sampled was not under water before the Impoundment of the lake in
1972. This factor will have a great deal to do with the benthic
population found at each station. The build-up of silt and organic
particles with time will provide more habitat and food for benthic
organisms at this depth and colonization from feeder streams and
other waters should increase both density and diversity.
In terms of the effects of acid mine pollution on ‘he bottom
org nisms of the Contrary Creek ann, the populations sampled did
not indicate a recovery from low pH toxicity as one moved Into
water of more normal pH levels. In other words no pH toxicity was
apparent in the benthic populations, either because It did not exist
or because it was masked by a selectivity for tolerant forms on the
part of the substrate.
306
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Fish
The effects of acid mine drainage on fish populations has
been widely studied. Most observers agree that pH values above
4.0 rarely prove lethal unless the lowered pH has caused the
toxicity of some other water characteristics to increase. pH
affects many water components, C02, alkalinity, end the solubility
of heavy metals especially. The effects of pH In the range 4.0 -
6.6 are usually physiological and can be manifested by abnorma’
behavior patterns, body deformities, reduced egg production and
hat:habillty. Mount (1973) stated that his experimental results
using the fathead minnow collectively support the need to maintain
pH at or above 6.5. Even though sustained fish populations may
exist at lower pH levels, production will most likely be reduced’.
Eleven fish species have been collected from Contrary Creek
In the area of Station 4 over the two years since 1972. See Table
5. SIx of these species were not found until thIs year. A small
population contributed to the early colonizers of Contrary Creek
and the lake proper has added more species recently.
The numbers of Individuals collected in the Contrary Creek
arm were generally lower than those from the main body. A few
species noted for the lake are not yet known In the Contrary Creek
are. These may be types which are more sensitive to acid mine
drainage than those found In Contrary Creek. The black crappie,
golden shiner, and brown bullhead are the major species in the
population of Contrary Creek. The bullhead is considered one of
the species most tolerant of acid mine drainage. The abundance
of crappie and shiners may be due to their early migration from
Freshwater Creek. No data Is available on the fish populations
307
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T LE 5
FISH NETTED IN CONTRARY CREEK
Esox niqer chain pickeral
Cyprinus car2.p european carp
Notemigonus crysoleu:as golden shiner
Erirnyzon oblongus creek chubsucker
Ictalurus nebulosus brown bullhead
Lepomis macrochirous bluegill
Micropterus selmoides largemouth bass
Pomoxis nigromaculatus black crappie
Perca flavescens yellow perch
Dorosorna cepedianum threadf in shad
Semotilus corporalis* failfish
* In Freshwater Creek arm
308
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in the area of Stations 1 and 2 but a decline from the figures
from the Station 4 area would be expected. The pH change from
Station 4 to Station 2, 5.8 to 4.4, Is a major factor in making
this assumption.
The uptake of heavy metals by fish In Contrary Creek is
just beginning to attract the tent1on of researchers. The
few creek chubsuckers analyzed for zinc and lead contamination
thus far have contained levels well above those found by researchers
in Illinois and Michigan who made extensive surveys of metals in
fish in their areas. Although no conclusions can be made from
the Contrary Creek fish data because of smal,l sample numbers, It
does indicate that the fish In the Contrary Creek ann are absorbing
and storing heavy metals. The importance of this contamination
from both human health and fisheries management viewpoints warrents
continued intensive monitoring of fish from Contrary Creek and
adjacent waters.
Summary . The fish population of the Contrary Creek arm of
the lake is smaller in size and diversity than the population of
the reactor site area. The Contrary Creek population is dominated
by black crappie, brown bullhead, and golden shiner, initial data
on heavy metals uptake in Lake Anna fish indicates significant
contamination by zinc and lead and points out the need for more
research in this area.
309
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REFERENCES
Benolt, R.J., J. Cairns and C.W. Reimer. A Limlogical
Reconnaissance of Impoundment Receiving Heavy Metals
with E has1s on Diatoms and Fish”. NReservolr of
Fish Research Synoslum,” American Fish. Soc., April
5—7, 1967.
Mount, 0.1. Chronic Effects of Low PH on Fathead Minnow
Survival, Growth and Reproduction”. Water Research ,
Vol. 7, pp. 987-993. 1973.
Simons, G.M., Jr. ‘A Preimpoundment Study of the North
Anna River, Virginia”, Bulletin 55, VIrginia Water
Resources Research Center. 1972.
Smith, R.W. and D.G. Frey. ‘Acid Mine Pollution Effects
on Lake Biology. Indiana University Wat r Resources
Research Center. 1971.
310
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Appendix F
EXPERIMENTAL STUDIES AT ARMINJUS TAILINGS
BY
A. CHANDLER MORTIMER*
NOVEMBER 1979
In 1974 and 1975 three separate sets of field revegetation experiments
were established on the Arminius tailings, adjacent to and on the east side
of Contrary Creek. The purpose of each set of experiments was to determine
(a) species nd varieties of grasses and legumes which could be successful,
(b) quantities of limestone which would be appropriate for vegetation on the
pyritic tailings, (c) quantities of Inorganic fertilizers which would be
needed, and (d) alternative soil amendments to the tailings which would act
as physical conditioners and which would contribute some nutrients for
vegetation.
These sets of experiments have been left in place, without any subsequent
maintenance, fertilization, or other treatment since the original seedbed prep-
aration. They have served, along with additional subsequent experiments, as
a basic guide for large-scale techniques and materials for revegetation at the
site of Anninius tailings on both the eastern and western sides of Contrary
Creek.
These experiments also are useful In assessing the long-range prospects
and maintenance requirements of the large-scale revegetation at all Contrary
Creek sites since they were planted on sites which are reasonably representa-
tive of mo c tailings areas, and since they were initiated between one and
three years earlier than other sites at Arminius, Boyd Smith and Sulfur tail-
ings.
STUDY I: TAILINGS-ONLY EXPERIMENTS
On September 12, 1974, a randomized-block-factorial experiment was plant-
ed. There are 54 indivIdual rectangular plots, each 7.5 feet by 6.0 feet.
Nine species of grass and legumes are represented, measured against three
levels of application of ground dolomitic limestone. There are two replica-
tions of each combination of vegetation species with given lime rates. A
uniform rate of application of comercial fertilizer was applied just prior
to planting over the entire experimental site: 10-10-10 at 1450 lb./acre.
* Consultant for Callahan Mining Corporation.
311
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Grass and legume species sown by hand were:
1. Golden millet
2. Blackwell switchgrass
3. WeepIng lovegrass
4. Crown vetch ‘Penngift’
5. Orchard grass
6. Serlcea lespedeza
7. Tall fescue ‘Alta’
8. Annual ryegrass
9. Red top
Liming rates were:
1. 5.0 tons/acre
2. 2.5 tons/acre
3. No ground dolomitic limestone
Experimental preparation methods are sumarlzed as follows:
A. Rototill site to a 6-inch depth
B. Apply fertilizer by cyclone seeder
C. Apply limestone at appropriate rates
0. Rototill entire area for the second time
E. Rake area to smooth the seedbed
F. Apply seed by hand, one variety of seed to each individual
plot
G. Rake each plot to cover seed
H. Apply straw mulch to all plots, two tons per acre
I. Apply biodegradable erosion control netting to all plots
Prior to application of limestone, pH of these (as well as most Arminius
tailings) was 3.6. For as long as one-an 1-a-half years after application, the
“high” level of lime maintained pH 4.7, and the “low” rate of lime elevated it
to pH 4.1.
Where lime was applied at both the “high” and “low” rates, the grasses
Tall fescue, Orchard grass, Red top, and Weeping lovegrass all showed good
cover and growth through the first year. During the second year (1976),
marked deterioration, as evidenced by lack of vigor and dying out, occurred,
especially where the “low” rate of lime had been applied. By 1977 and 1978
only very limited stands of these grasses continued to survive. This contin-
ues to be the case. On unhimed trials, only Weeping lovegrass germinated, and
only In very limited numbers. A few plants still remain after five ye”s.
Planted legumes, Crown vetch and Sericea lespedeza, g’rn inated only where
limed at “low” and “high” rates. By the fall of 1979, fIve years after plant-
ing, Crown vetch survives where the “high” rate of lime was applied, but there
Is little evidence of its spreading. Sericea lespedeza, however, has spread
(by reseeding) into several other plots where limed at the “high” rate. Seri-
cea is stunted, but continues to survive and spread at a very gradual rate.
312
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The most successful vegetation In this experiment Is one that was not
sown or planted: Virginia pine. Prior to Initiating reclamation experiments
It was noted that In the spring, hundreds of pine seedlings had germinated
at Arminlus tailings on both sides of Contrary Creek, but by mid-suniner these
seedlings had perished. It can be assumed that this was an annual cycle which
had been repeated for many years. By May, 1976, eIght seedlings In the ex-
perimental plots were noted to have survived one winter. By December, 1976,
21 volunteers were noted to have survived one or more growing seasons. By
1979, the number of Virginia pines has grown to more than 100, and the tallest
of these are almost five feet tall. This quantity of trees points to a poten-
tially very dense forest growth in the future, should the trend continue. As
of this time there is an average of one Virginia pine per 25 square feet in
the experimental area.
It Is clear that the combination of mulch, lime, and some grass growth,
and to a lesser extent, fertilizer, all contributed to the proliferation of
surviving pine trees. It Is believed that shielding young seedlings from
isolation (by mulch, and by thin stands of grass) have been the most important
factors In this process. There are more trees where lime was applied at both
“low” and “high” rates, but some occur In the unlimed tailings. Fertilizer
does not seem to be a significant Ingredient because any benefits conferred
in 1974 can be assumed to have been dissipated.
In the future, it can be assumed that the Invasion of pine seedlings
will decelerate since very little mulch or grass still exists in quantities
needed to provide the shade required on the dark-colored tailings and to
prevent girdling of roots. In fact, there are very few new seedlings in 1979
as compared with 1978. By the same token, however, it can be assumed with
some certainty that established volunteers will continue to grow without
additional fertilizer, just as they have in the past. These, in turn, will
provide greater shade as they grow. They will likely provide a more hos-
pitable environment for future seedlings from surrounding areas. They will
also provide some mulch from dropping needles and may in time produce their
own seeds.
In sumary, the long-term prospects for this experimental site appear to
be that it will become densely covered with Virginia pines, with possibly an
Increase in spread of lespedeza.
STUDY II: SAPROLITE/TAILINGS EXPERIMENTS
On October 2, 1974, a block-factorial experiment was planted, with a total
of 22 individual plots, each measuring 7.5 feet by 6.0 feet. The entire are
was covered by approximately eight Inches of saprolite. 11 plots were limed
(ground dolomitic limestone at the rate of 2.0 tons per acre) and 11 were not
limed. There are two replications of each of the following species and combi-
nations, one of which was limed and one of which was not:
1. Blackwell switchgrass
2. Weeping lovegrass
3. Crown vetch ‘Penngift’
4. Orchard grass
313
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5. Sericea lespedeza
6. Tall fescue ‘Alta’
7. Annual ryegrass
8. Red top
9. Red fescue ‘Penniawn’
10. Mixture of 1-4 above
11. Mixture of 6-10 above
Procedures were the same as listed above for Study I, with the following
noteworthy distinctions: (a) tailings not mixed with saprolite since the
coverage of saprolite was deeper than the tilling; (b) mulch applied at 1.5
tons per acre rate instead of 2.0 tons per acre.
Fertilizer (10-10-10) was applied to all areas at the rate of 1450 lb.
per acre.
By May, 1976, the most promising species in terms of ground cover, were
‘Pennlawn” Red fescue, ‘Alta’Tall fescue, Orchard grass, and Red top. How-
ever, these lost vigor during the second growing season (1976).
Meanwhile, during this second year, both Crown vetch and Sericea lespe-
deza began to show signs of vigor and increased ground coverage. Photographs
from 1976 show that Crown vetch was thriving only where limed, but that Seri-
cea lespedeza was prospering both with and without lime.
As of the autumn 1979, lespedeza has spread not only Into all 22 individ-
ual trials but has also reseeded outside of the boundaries of the experiment.
Crown vetch continues to survive where it was originally planted, but in 1979
it began to be crowded out by lespedeza. There is little survival of Crown
vetch where it was not treated with dolomitic limestone.
The spread of lespedeza ha been especially marked during 1978 and 1979.
This has occurred by means of reseeding, and it is anticipated that by 1980
the entire area will show an extremely dense stand of Sericea lespedeza that
Is about four feet tall.
Where lespedeza has been slower to invade (a function of physical dis-
tance), Virginia pines have also invaded in substantial numbers. It is un-
certain at this time whether the complete, dense cover of lespedeza will crowd
out the pine seedlings in this study area, but it appears likely to because
of its aggressive nature.
In sumary, this study area exhibits very complete coverage and extensive
spreading by Sericea lespedeza, and more complete ground cover in each suc-
ceeding year.
STUDY III: SLUDGE/TAILINGS EXPERIMENTS
On October 11, 1975, sIx species of grasses and legumes were sown in 20
individual plots, each measuring 7.5 feet by 6.0 feet. The entire area was
covered by four Inches of Richmond (VA) digested sewage sludge, which was
314
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rototilled to a depth of eight inches. (ihus the top eight inches of “soil
material” consisted of 50% Richmond sludge and 50% tailings, overlying
Arminlus tailings.)
Ground agricultural limestone was applied to the entire area at the rate
of three tons per acre, and rototliled Into the sludge/tailings regime. No
fertilizer was applied, and no mulch or erosion control netting was used.
Otherwise, procedures In Studies I and II were followed.
In the 30 IndivIdual plots, there were five (randomized-block-factorial)
replications each of the following six species:
1. Tall fescue ‘Kentucky-31’
2. Crown vetch ‘Penngift’
3. Orchard grass
4. Ladino clover
5. Red top
6. Weeping lovegrass
The application of sludge and limestone raised initial pH of tailings
(pH 3.6) to slightly higher than pH 6.0, at which point it has remained
constant to date.
Early results (May, 1976) reflected the fast, aggressive growth of Tall
fescue, Orchard grass, and Ladino clover.
By the end of the first growing season (1976), it was apparent that
digested sewage sludge was the amendment of choice, with results far surpass-
Ing earlier experiments at the same stage of growth. By this time, however,
clover had been so heavily browsed by deer as to be completely eradicated.
All other species had achieved complete, vigorous, and dense ground cover.
By the spring of 1979, however, Crown vetch had become so aggressive as
to invdde 18 of the 30 Individual trials. By October 1979, 25 of the 30 plots
exhibited very dense Crown vetch, to the point that other species were crowd-
ed out.
With Crown vetch so abundant and aggressive, it can be assumed with
certainty that Crown vetch will completely over-run all other species by 1980
in this experiment, because of Its luxuriant growth. There is 100% lush
ground cover on all plots, with either the originally planted grass or with
Crown vetch. A substantial amount of organic material has been generated
over this entire area during the four years since planting.
SU1’ IARY
By the end of the 1979 growing season, Studies I and II, and Study III
have been through five, and four years’, observations respectively. These
five years have supplied an abundance of unusually harsh weather, ranging
from extremely cold winters with abundant snow Insulation, to extremely cold
‘inters without significant snow cover, dry and wet springs and autumns, and
t xtremely hot sumers with little precipitation.
315
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Despite all these vagaries of climate (which seem to average out to
near the normal) results of each study have continued to show improving results
In terms of vegetat 4 ve ground cover and growth.
None of the study areas has received any maintenance at all. Yet, each
of the studies shows a trend toward vegetative development In a son ’ what dif-
ferent direction. With no amendments (i.e. using the tailings as ;eedbed with
only short-term lime, mulch, and fertilizer) native Virginia pine Is becom—
Ing well established. With saprolite, Sericea lespedeza Is very aggressive
and domInant. Where sludge was utilized, Crown vetch is destined to crowd
out all other vegetation in the Imediate future.
From these differing results, what is one to conclude from these results?
At this time it seems evident that Virginia pine, native to the area, is the
most tolerant species under very low-nutrient levels, and once some ground
cover can be established, these will volunteer, survive and grow. This would
eventually, should present trends continue, bring Arminius tailings into a
general homeostasis with its surroundings from the vegetational standpoint.
However, if nutritional levels and acidity are reduced near the surface by
means of coverage by local red-clay subsoil (saprolite), Sericea lespedeza
is likely to predominate at least for the short-run. If nutritional levels
and pH are raised substantially by sewage sludge applications, growing condi-
tions may be improved to the point that Crown vetch will not only survive
but will aggressively prosper.
In each of these cases, the studies show that under representative tail-
ings conditions at Contrary Creek, vegetation can be established and self—
maintaining.
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