c/EPA
United States
Environmental Protection
Agency
ie->on?,,ental Research
Labor 'ory
Duluth MN 55804
EPA 600 J-79-1/4
December 1979
Research and Development
Environmental
Effects of Western
Coal Surface Mining
Part I—The Limnology
and Biota of Mine
Spoils Ponds in
Northwest Colorado
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development. U.S. Environmental
Protection Agency, have been grouped into nine series These nine broad cate-
gories were established to facilitate further development and application of en-
vironmental technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface in related fields.
The nine series are:
1. Environmental Health Effects Research
2 Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5 Socioeconomic Environmental Studies
6. Scientific and Technical Assessment Reports (STAR)
7. Interagency Energy-Environment Research and Development
8 "Special" Reports
9 Miscellaneous Reports
This report has been assigned to the ECOLOGICAL RESEARCH series. This series
describes research on the effects of pollution on humans, plant and animal spe-
cies, and materials. Problems are assessed for their long- and short-term influ-
ences. Investigations include formation, transport, and pathway studies to deter-
mine the fate of pollutants and their effects This work provides the technical basis
for setting standards to minimize undesirable changes in living organisms in the
aquatic, terrestrial, and atmospheric environments.
This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161.
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EPA-600/3-79-124
December 1979
ENVIRONMENTAL EFFECTS OF WESTERN COAL SURFACE MINING
Part I - The Limnology and Biota of Mine Spoils Ponds in Northwest Colorado
by
Steven P. Canton and James V. Ward
Department of Zoology and Entomology
Colorado State University
Fort Collins, Colorado 80523
Grant No. R803950
Project Officer
Donald I. Mount
Environmental Research Laboratory
Duluth, Minnesota 55804
ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
DULUTH, MINNESOTA 55804 .
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DISCLAIMER
This report has been reviewed by the Environmental Research Laboratory-
Uuluth, 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 commercial products constitute endorsement or recommendation
for use.
ii
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FOREWORD
This report is one of a series of reports describing the impact of
surface mining coal. Several mine spoil ponds were compared to a control
pond. Differences were apparent but in contrast to spoil ponds in the
eastern U.S., these ponds had a relatively rich flora and fauna and appear
to offer recreational utility.
Donald I. Mount, Ph.D.
Environmental Research Laboratory-Duluth
111
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ABSTRACT
Physico-chemical conditions, zooplankton, and benthos were investi-
gated from June 1977 to May 1978 in coal strip-mine ponds in northwestern
Colorado. Two spoils ponds received all of their drainage from the coal
mine, but differed in age; one pond received partial drainage from the mine
spoils; a control pond was located in an adjacent drainage basin. There
were no discernible effects of mine drainage on a variety of physico-
chemical parameters, such as temperature, dissolved oxygen, and hardness.
In stark contrast to spoils ponds in the eastern and midwestern states,
acid mine drainage was not observed. The pH was near or greater than
neutrality and acidity was not detected in the ponds studied. Total
dissolved solids, nitrate and sulfate values were higher in the spoils
ponds than in the control pond. Net zooplankton abundance was lowest in
the youngest spoils pond, but the standing crop of benthos exhibited a
progressive decrease from the youngest spoils pond to the control pond.
Zooplankton and benthos species diversity were lower in the spoils ponds.
Certain groups of zooplankters (Cladocera) and benthos (caddisflies,
amphipods, water mites, and fingernail clams) were rare or absent in the
youngest spoils pond. Colonization phenomena (age and distance from a
source of colonizers) are postulated as responsible, in part, for the
fauna! differences between ponds, although higher levels of nitrate, sulfate,
and TDS in the spoils ponds may provide adverse conditions for certain
species. If these data are typical of the western energy region, they
suggest the potential for development of recreational lakes as a part of
reclamation practices.
iv
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CONTENTS
Page
Foreword iii
Abstract iv
Figures v1
Tables vii
Acknowledgments viii
I. Introduction 1
II. Conclusions 2
III. Recommendations 4
IV. Description of the Study Area 5
V. Methods 8
A. Physico-Chemical Parameters 8
B. Net Zooplankton 8
C. Benthic Macroinvertebrates 9
VI. Results and Discussion 10
A. Physico-Chemical Parameters 10
B. Net Zooplankton 17
C. Benthic Macroinvertebrates 24
D. Summary 35
References 36
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FIGURES
Number Page
1 Pond locations in relationship to Edna Mine spoils
(crosshatched) and present mining activity. Pond P4,
the control pond, is in an adjacent watershed 6
2 Seasonal trends in water temperature 13
3 Seasonal trends in total dissolved solids 15
4 Annual mean densities of net zooplankton 19
5 Percentage composition of major net zooplankton groups
using density values 20
6 Seasonal trends in net zooplankton densities 22
7 Annual mean density and biomass values of macrobenthos 27
8 Percentage composition of major invertebrate groups using
density values (8a) and biomass values (8b) 29
9 Seasonal trends in the densities of macrobenthos 32
vi
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TABLES
Number Page
1 Physico-chemical parameters from ponds associated with
coal mining in northwestern Colorado (June 1977-May 1978) ... 11
2 Selected chemical parameters of northwestern Colorado
coal mine study ponds, compared with coal mine
ponds in Missouri and Ohio 12
3 Sediment particle size and percentage organic matter
for ponds associated with coal mining in northwestern
Colorado 16
4 Species list and mean density (organisms/1) of net
zooplankton from ponds associated with coal mining in
northwestern Colorado (June 1977-May 1978) 18
5 Net zooplankton species diversity, equitability, and
number of taxa for ponds associated with coal mining in
northwestern Colorado 23
6 Coefficient of community and percentage similarity using
zooplankton for ponds associated with coal mining in
northwestern Colorado 23
7 Species list and density (organisms/m2) of benthic
macroinvertebrates from ponds associated with coal
mining in northwestern Colorado (June 1977-May 1978) 25
8 Biomass (g/m2 wet weight) of major invertebrate groups
from ponds associated with coal mining in northwestern
Colorado (June 1977-May 1978) 28
9 Number of taxa in major invertebrate groups from ponds
associated with coal mining in northwestern Colorado
(June 1977-May 1978) 33
10 Macroinvertebrate species diversity, equitability, and
number of taxa for ponds associated with coal mining in
northwestern Colorado 34
11 Coefficient of Community and Percentage Similarity
using macroinvertebrates from ponds associated with coal
mining in northwestern Colorado 34
vii
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ACKNOWLEDGMENTS
We wish to thank Dr. R. K. Skogerboe, Department of Chemistry, Colorado
State University, for valuable suggestions regarding the manuscript and for
providing unpublished chemical data from the ponds. Dr. E. E. Herricks,
Department of Civil Engineering, University of Illinois, also reviewed the
manuscript and provided valuable comments.
This research was funded in part by research grant No. R803950, U.S.
Environmental Protection Agency, Environmental Research Laboratory, Duluth,
Minnesota; and by a National Science Foundation Energy Traineeship awarded
to S. P. Canton. The Natural Resource Ecology Laboratory also provided
support and coordination of this research.
vi ii
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SECTION I
INTRODUCTION
The deleterious effects of drainage from coal strip-mines on aquatic
biota have been well documented in the eastern and midwestern United States
(e.g., Appalachian Regional Commission 1969, Roback and Richardson 1969,
Warner 1973). Strip-mine lakes receiving drainage from the high sulfur
coal mines of those regions contain acidic waters which require extended
recovery periods before supporting anything approaching a normal aquatic
biota (Parsons 1964, 1977; Campbell and Lind 1969; Smith and Frey 1971;
King et aJL 1974; Riley 1977).
Remarkably little work has been done to assess the effects on aquatic
systems of drainage from the low sulfur coal mines of the western United
States (Reed 1975). Surface mining activity has been conducted for over 30
years at the Edna Mine in northwestern Colorado. Although low in sulfur
compared to eastern coal, the 2.4% sulfur content and 30.8% iron oxide in
the ash of Edna Mine coal are the highest values for coals studied in
Colorado (Deurbrouck 1970). Yet a two-year study failed to indicate any
distinctly deleterious effects of the Edna Mine on the adjacent stream (Canton
and Ward 1978). The apparent lack of adverse effects was attributed to the
presence of a buffer strip between the mine spoils and the stream and to
climatic, hydrologic, and geochemical conditions (Ward £t al_. 1978).
Strip mining at the Edna Mine leaves the overburden in large spoil
piles which are presently being regraded. Drainage from the spoils form
ponds at the base of the coal seam against the highwall of the pit. In
June 1977 research was undertaken on these spoils ponds which receive
drainage directly from the mine. The purpose of the research reported
herein was to investigate the limnological conditions, zooplankton and
benthic communities of spoils ponds of different ages which were differ-
entially influenced by mine drainage. Despite some differences in other
variables such as morphometry, the ponds were similar enough to provide
comparative data previously unavailable for spoils ponds of the western
energy region.
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SECTION II
CONCLUSIONS
The following conclusions are based upon a one-year study of two
spoils ponds which received all of their drainage from a coal mine, but
differed in age; one pond which received partial drainage from mine spoils,
and a control pond in an adjacent drainage basin.
1. There were no apparent effects of mine drainage on temperature,
dissolved oxygen, hardness, pH, acidity, alkalinity, calcium, iron,
orthophosphate, or the organic content of the substrate.
2. Acid mine drainage was not observed in any of the ponds, in stark
contrast to eastern mine spoils ponds where pH may remain below 4.0 50
years after cessation of mining activities.
3. Total dissolved solids and nitrate levels were higher in the spoils
ponds than the control pond. The youngest spoils pond exhibited the
highest values.
4. Sulfate levels were much higher in ponds receiving mine drainage, but
this was due to gypsum (CaSO^ • H20) rather than the oxidized sulfides
associated with acid mine drainage.
5. Net zooplankton densities were lowest in the youngest spoils pond and
greatest in the control pond. Cladocerans appeared to be the group
most adversely affected by conditions in spoils ponds. There was a
progressive increase in the number of zooplankton taxa from the
youngest spoils pond to the control pond. Shannon-Weaver diversity
index values were lower in the two spoils ponds; highest values
occurred in the control pond.
6. There was a progressive decrease in macroinvertebrate density and
biomass from the youngest spoils pond to the control pond. Chironomids
and tubificid worms were responsible for the high standing crop in
the youngest spoils pond. The predominant groups in the control pond
were amphipods, mayflies, leeches, and odonates. The following major
taxa were not collected from the youngest spoils pond: Amphipoda,
Hydracarina, Trichoptera, and Sphaeriidae. The fewest species occurred
in the youngest spoils pond; the other three ponds had a larger number
of species and were similar to each other in the total number of taxa.
Shannon-Weaver index values showed similar trends.
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7. Coefficient of Community and Percentage Similarity indices suggest
that colonization phenomena (age and proximity to a source of colonizers)
may be responsible, in part, for the zooplankton and macroinvertebrate
communities of the ponds. The higher levels of nitrate, sulfate, and
IDS in the spoils ponds may, however, provide adverse environmental
conditions for some species.
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SECTION III
RECOMMENDATIONS
1. Additional studies of physico-chemical conditions and biota are needed
to determine whether or not the results contained herein are typical
of spoils ponds in the western energy region.
2. These data suggest that spoils ponds in the western energy region have
potential as recreational lakes.
3. These ponds may provide environmental conditions suitable for a
variety of aquatic organisms. The feasibility of transplanting
macrophytes, plankton, benthos, and fishes from local lentic habitats
as a mechanism of speeding natural colonization processes, should be
investigated.
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SECTION IV
DESCRIPTION OF THE STUDY AREA
Edna Mine coal is mined from the Wadge seam in the Williams Fork Unit
of the Mesa Verde group. The Williams Fork formation overburden consists
primarily of shale, sandy shale, and thin beds of sand (McWhorter et al_.
1975).
Four pond study sites were established to correspond to a gradient of
mining effects (Figure 1). Two of the ponds received all of their drainage
from the mine, but differed in age; one pond received only partial drainage
from mine spoils, and the control pond received no drainage from mining
activity.
Pond PI: 2164 m elevation. This pond, approximately 10 years old,
formed where water accumulates against a highwall. The area of the pond is
approximately 0.02 ha; the maximum depth is 1.0 m. The bottom of the pond
was covered with the alga Chava globularis throughout the summer and fall.
Ice covered the pond from November through early March.
Pond P2: 2170 m elevation. This pond, approximately 30 years old, is
located at the base of a highwall where drainage from the area of oldest
mining activity accumulates. This is the largest pond with an area of
approximately 0.39 ha and a maximum depth of 3.8 m. Aquatic macrophytes
were generally sparse, although Carex, Junaus, and Typha grew along the
edge. Potamogeton became abundant in late summer-early autumn, but was
limited to the shallow areas. Ice cover occurred from November through
late March.
Pond P3: 2164 m elevation. This is an old stock pond formed by
damming an intermittent drainage. Although not located directly in the
mine, it receives some drainage from the mine spoils. This pond is similar
in size to PI with an area of 0.02 ha and a maximum depth of about 1.0 m.
Throughout the summer, over 90% of the pond surface was covered with a
floating mat of filamentous alga (Spirogyra). Due to the input of ground-
water and the insulating effect of the algal mat, the water under the mat
was at times 5-10°C cooler than the surface water. Ice covered the pond
from November through early March.
Pond P4: 2133 m elevation. The control pond is located 5 km northeast
of PI. This pond is also an old stock pond formed by damming a small
drainage, but it is not affected by mining activity. The pond has an area
of 0.05 ha and a maximum depth of 1.5 m. Dense growths of Myriaphyllum
-------
P-4
(control)
kilometers
Figure 1. Pond locations in relationship to Edna Mine spoils (crosshatched)
and present mining activity, Pond P4, the control pond is in an
adjacent watershed.
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occurred during summer. The emergents, Carex and Junaus, and the floating
plant Lernna were present along the edges. Ice covered the pond from
November through late March.
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SECTION V
METHODS
The four ponds were sampled monthly from June 1977 through May 1978
except December and February. Ice conditions prevented the sampling of
pond P4 in January.
A. PHYSICO-CHEMICAL PARAMETERS
Water temperature was measured with a thermister at 10 cm depth
intervals. Dissolved oxygen levels were measured in the field using the
azide modification of the Winkler titration method. The pH was determined
in the field using comparator discs. One-liter water samples were trans-
ported to the laboratory in an ice chest. Bound C02 (methyl orange alka-
linity) was measured by titration with HC1 using methyl orange as an
indicator (Pennak 1977) and was recorded as nig/liter CaC03. Orthophosphate
and nitrate levels were determined bimonthly using the colorimetric method
of Lind (1974).
Total dissolved solids were determined bimonthly by filtration of
0.5 1 water samples through cellulose discs (0.45 ym apertures) and subse-
quent evaporation of the filtrate in a sand bath at 60CC (Ward 1974). The
residue was fired at 600°C in a muffle furnace to obtain loss on ignition
values. In addition, water samples collected before and after spring
runoff were subjected to more detailed analyses by the Colorado State
University Chemistry Department.
Substrate samples were collected with an Ekman grab in June 1977 from
the 0.5 m depth contour. Organic content was determined using wet digestion
with dichromic acid; the hydrometer method was used for particle size
analysis. The Colorado State University Soil Testing Laboratory performed
the analyses.
B. NET ZOOPLANKTON
Net zooplankton samples were taken by filtering 20 1 of pond water
from a depth of 10-20 cm through the bucket of a Juday plankton trap.
Samples were preserved with 80% EtOH. In the laboratory 1 ml aliquots were
transferred to a Sedgwick-Rafter counting cell with a Hensen-Stempel pi pet
and the zooplankters were enumerated at 100 X. Identifications to the
generic (and in some cases specific) level were based on the keys of Brooks
(1957), Edmondson (1959), and Pennak (1978).
8
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The Shannon-Weaver index was used to calculate zooplankton species
diversity using the computational formula in Weber (1973). Equitability, a
component of species diversity, was calculated using the tables of Lloyd
and Ghelardi (1964). Faunal similarity was calculated using two methods
outlined by Whittaker (1975). Coefficient of Community is based solely on
the presence or absence of species. Percentage Similarity also considers
the quantitative representation of each taxon.
C. BENTHIC MACROINVERTEBRATES
Benthic macroinvertebrates were collected by taking three Ekman grab
samples from each pond. The samples were combined, stored on ice, and
returned to the laboratory. The samples were washed through a 250 v.m mesh
sieve and preserved in 5% formalin. The organisms were sorted from the
debris and placed in 80% ethyl alcohol for later identification and enumera-
tion. Identifications to the generic (and in some cases specific) level
were based on the keys of Edmondson (1959), Anderson (1962), Musser (1962),
Hilsenhoff (1970), Mason (1973), Wiggins (1977), Zalom (1977), and Wu
(1978).
Species diversity, equitability, and similarity coefficients were
calculated in the same manner as for zooplankton.
Statistical analysis of variance was calculated for certain physico-
chemical, zooplankton, and benthic invertebrate data.
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SECTION VI
RESULTS AND DISCUSSION
A. PHYSICO-CHEMICAL PARAMETERS
Mean values and ranges for the physico-chemical parameters which were
sampled monthly or bimonthly are shown in Table 1. Additional chemical
parameters are presented in Table 2 in relationship to strip-mine lakes of
the midwest.
The temperatures of the ponds were generally similar. Most differences
were attributable to differences in the time readings were taken. The
ponds were well exposed to wind action and thermal stratification was
normally not apparent. Some stratification was observed at P3 in the
summer when the algal mat formed a nearly opaque layer just below the
surface. All ponds exhibited similar seasonal patterns (Figure 2).
Dissolved oxygen values were also similar between ponds; variations in
mean values were primarily a function of the degree of supersaturation
encountered. At P3 samples were taken under the algal mat when present.
The highest mean value for bound C02 was recorded from P3 (108 mg/1
CaC03), a pond not directly associated with mining activity. The control
pond, P4, also had a relatively high value of 77 mg/1 CaC03. The ponds
receiving drainage directly from the mine, PI and P2, had the lowest values
for bound C02 (57 and 37 mg/1 CaC03, respectively).
According to Pennak (1971), the waters of P2 would be classified as
"medium," PI and P4 as "hard," and P3 as "very hard." It is not possible
to account for the large seasonal variations observed, which appear unrelated
to the influence of mine drainage. The control pond (P4) exhibited autumn
values nearly seven times greater than those encountered during spring.
Acid mine drainage was not evident in any of the ponds. Median pH
values ranged from 7.4 to 7.6; the lowest value was 6.8 (Table 1). The
youngest spoils pond (PI), which receives all drainage directly from the
mine, exhibited pH values from 7.1 to 8.1. This is in stark contrast to
eastern mine spoils ponds where pH may remain below 4.0 fifty years after
the cessation of mining (Campbell and Lind 1969). In the ponds in Colorado
there was no relationship between pH levels and either age or extent of
mining influence.
Nitrate levels were higher in ponds receiving mine drainage than in
the control pond. In the semi-arid climate of this region, surface mining
10
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TABLE 1. PHYSICO-CHEMICAL PARAMETERS FROM PONDS ASSOCIATED WITH COAL MINING
IN NORTHWESTERN COLORADO (JUNE 1977-MAY 1978)
Ponds
Parameter
Temperature (°C) 10 cm
Range
Dissolved 02 (mg/1)
Range
Bound C02 (mg/1 CaC03J
Range
pH (median)
Range
Nitrate (mg/1)
Range
Orthophosphate (mg/1)
Range
Total dissolved solids (mg/1)
Range
Loss on ignition (mg/1)
Range
PI
11.0
0.0-20.0
15.6
8.2-29.4
56.6
27.5-94.0
7.4
7.1-8.1
16.34
6.38-26.3
0.15
0.0-0.34
3811
2504-5626
1079
662-1725
P2
12.6
0.0-23.0
11.1
7.6-16.2
36.6
11.5-52.0
7.4
6.8-7.7
0.55
0.0-2.63
0.07
0.0-0.11
1770
1429-2561
412
204-604
P3
11.2
0.0-17.5
12.7
8.5-17.5
108.2
50.0-145.5
7.4
7.0-7.5
0.89
0.03-4.0
0.17
0.13-0.21
2632
2422-2963
749 •
645-1001
P4
14.7
2.0-24.0
15.0
6.4-29.6
77.0
18.5-124.0
7.6
7.0-8.1
0.14
0.0-0.48
0.30
0.0-0.89
547
254-758
193
116-758
Percentage of TDS 28 23 28 35
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TABLE 2. SELECTED CHEMICAL PARAMETERS OF NORTHWESTERN COLORADO COAL MINE STUDY PONDS
COMPARED WITH COAL MINE PONDS IN MISSOURI AND OHIO
Parameter
Acidity (mg/1 CaC03)
Alkalinity (mg/1 CaC03)
Sulfate (mg/1)
Calcium (mg/1)
Total Iron (mg/1)
Manganese (mg/1)
Magnesium (mg/1)
Sodium (mg/1)
Potassium
Z1nc (mg/1)
P1a/
0
66-189
2500-3180
350-360
0.03
<0.001
400-550
98-160
14.4-19
<0.01
PZ8/
0
98-143
940-1260
57-364
0.13
0.001-0.21
82-140
19-36
3-6.6
<0.01
P3*/
0
283-316
1360-1500
330-340
0.09
0.002-0.009
226-340
20-21
4.6-5.4
<0.01
Ponds
P4i»/
0
167-282
168-290
200-300
0.14
0.001-0.011
56-118
19-23
2.5-4
<0.01
A!*/
227-4920
0
1620-5030
82-253
74-272
27-95
65-175
8.9-23.3
0.2-1.6
24.8-86
A3^ 01^
27-55 14
0 2
108-324 560
29-79
0.44-1.88 <1.0
0.79-3.18
6.3-17
1.3-4.6
3.35-9.2
0.58-1.56
oia/
0
80
580
127
0.81
0.02
38.9
—
—
—
^Colorado State University Chemistry Department, 29 April 1977 and 29 July 1977. P4 1s a control pond.
^34-year-old mine pond 1n Missouri (Campbell and L1nd 1969).
^50-year-old mine pond 1n Missouri (Campbell and Lind 1969).
-'Ohio pond at 40 years (Rlley 1977).
5/Oh1o pond at 55 years (Rlley 1977).
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xr is GO in co E*
1977-78
Figure 2. Seasonal trends in water temperature.
13
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increases leaching of soluble salts (Ward £tal_. 1978). It appears that
nitrate levels remain high for a number of years. The youngest mine spoils
pond (PI) exhibited consistently high values for nitrate (mean = 16.34
rog/1). Nitrate levels in the mine spoils, as measured by saturated paste
analysis, were similar throughout the mined area (McWhorter et_ al_. 1975)
and cannot explain the high levels at PI. Orthophosphate values, however,
did not exhibit any discernible relationship with age or degree of mining
effects. The highest levels were found in the control pond.
Mean values of total dissolved solids (TDS) were 3-7 times greater in
the spoils ponds than the control pond (Table 1). The highest value
(3811 mg/1) occurred in the youngest spoils pond. TDS thus appears to be
influenced by watershed disturbance from mining in a manner similar to
nitrate. Statistical analysis of variance was run on the TDS values for
the year's data to determine the strength of the relationship seen in
Table 1 and Figure 3. The results indicate a significant difference between
the ponds (P < 0.01). TDS exhibited little seasonality except in the
youngest spoils pond (PI) which showed much lower values during late summer
and autumn (Figure 3). Loss on ignition averaged 23-35% of the total
dissolved solids.
To provide comparative data, selected chemical parameters from the
Colorado ponds are related to mine ponds in regions of acid mine drainage
(Table 2). The Missouri ponds studied by Campbell and Lind (1969) were 34
years old (Al) and 50 years old (A3). Riley (1977) studied a pond in Ohio
(01), which was formed in 1918, when it was 40 years old and when it
was 55 years old. There is a striking difference between the Colorado
ponds and those in areas of acid mine drainage (AMD). Acidity was never
detected in the Colorado ponds, but was still measurable (27-55 mg/1 CaC03)
50 years after mining in A3. Alkalinity was high in all the Colorado
ponds, but was not detected in Al or A3. Only in the Ohio pond, 55 years
after mining, did alkalinity values approach those of the youngest pond in
Colorado (80 mg/1 CaC03 in Ohio; 66-189 mg/1 CaC03 at PI). Sulfate levels
were very high in the Colorado ponds associated with the mining activity
(PI, P2, and P3) ranging from 940-3180 mg/1, which was comparable to levels
observed in pond Al (1620-5030 mg/1). However, the high levels of sulfates
in the Colorado ponds are due to the gypsum (CaSO^ • H20) found in the
overburden rather than the oxidized sulfides associated with the high
pyritic content of the overburden in areas of AMD (McWhorter et al. 1975).
The gypsum and the shale content of the overburden accounted Tor the
generally high levels of calcium in the Colorado ponds (57-364 mg/1) compared
to pond A3 (29-79 mg/1). Unlike areas of AMD where total iron levels can
be quite high (74-272 mg/1 at Al), the Colorado ponds had extremely low
levels of iron (0.03-0.14 mg/1) comparable to mine ponds 50-55 years old.
Other differences in the ionic composition between the ponds in Colorado
and those in areas of AMD generally reflected differences in regional
geology.
Table 3 summarizes the particle size distribution and organic content
of the sediment in the four ponds. The particle size distribution at PI
was fairly evenly divided among the sand, silt, and clay fractions. The
substrate at P2 was predominately sand (49%). The two ponds not directly
14
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o»
E
GO
— in to
1977-78
Figure 3. Seasonal trends in total dissolved solids,
15
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TABLE 3. SEDIMENT PARTICLE SIZE AND PERCENTAGE
ORGANIC MATTER FOR PONDS ASSOCIATED WITH
COAL MINING IN NORTHWESTERN COLORADO
Ponds
% sand (0.0625-2.0 mm)
% silt (0.0039-0.0625 mm)
% clay (<0.0039 mm)
% organic matter
PI
34
38
28
6.7
P2
49
25
26
11.4
P3
22
57
21
8.4
P4
36
41
23
9.2
16
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associated with the mining, P3 and P4, had predominantly silt sediments
(57% and 41%, respectively). The relative contribution of organic matter
was similar at all ponds, ranging from 6.7% at PI to 11.4% at P2.
B. NET ZOOPLANKTON
During the study 21 zooplankton taxa were identified (Table 4).
Annual mean density ranged from 39 organisms/1 at PI to 283 organisms/1 at
P4. Despite great differences in mean density values (Figure 4), no
statistically significant difference (P > 0.05) between the ponds was
indicated. The great temporal variations in density of individual species
obscured between-pond differences when analyses were run on the raw numbers
of zooplanters for the entire year's data.
Protozoa were present in all ponds, but abundant only at P2 (Table 4).
Protozoans accounted for 33% of the zooplankton density at PI (Figure 5),
with Difflugia being the only representative. Difflugia and CeraUum
accounted for 88% of the total density at P2. Protozoans were less important
at the other ponds accounting for 17% of the density at P3 and only 8% at
P4, with Difflugia the main representative. Difflugia was also an abundant
zooplankter in a strip-mine lake in Kansas (Burner and Leist 1953).
Rotifers were collected in all ponds, but were abundant only at P4.
Rotifer density was low at PI, but they accounted for 20% of the zooplankton
density (Figure 5), with Branehionus and Epiphanes being most abundant. At
pond P2, rotifers accounted for only 9% of the density; Asplanohna was the
most abundant taxon. Although rotifers increased in absolute abundance at
P3 (especially Branchionus* Epiphanes, Notholca, and Lepadella), they
accounted for only 17% of the total density. The density of rotifers was
much greater at P4, accounting for 29% of the total zooplankton density.
Keratella quadrata and Filinia longiseta were abundant in P4.
Cladocerans were important only at P3 and P4, the ponds not directly
associated with mining activity. A single specimen of Bosmina longirostris
was the only Cladoceran collected from PI during the year of study. At
P2, Cladocerans made up only 2% of the zooplankton density; Daphnia pulex
was the main representative. The greater Cladoceran abundance at P3 was
due to Chydorus sphaeriaus, which accounted for 28% of the zooplankton
density. Although Cladocerans were most abundant at P4, they accounted for
only 17% of the zooplankton density at this pond. Ceriodaphnia retiaulata
was the most abundant species.
Limnetic copepods were represented by a single species, Cyolops
biauspidatus thomasi. This species was important in all the ponds, except
P2, accounting for 46% of the density at PI, 38% at P3, and 46% at P4. In
all cases, the nauplius stage accounted for most of the copepod abundance.
Cyolops was also found to be abundant in a strip-mine lake in Kansas
(Burner and Leist 1953).
17
-------
TABLE 4. SPECIES LIST AND MEAN DENSITY (ORGANISMS/L) OF NET
ZOOPLANKTON FROM PONDS ASSOCIATED WITH COAL MINING
IN NORTHWESTERN COLORADO (JUNE 1977-MAY 1978)
Ponds
Protozoa
Diff lug-La sp.
Ceratium sp.
Rota tori a
Monostyla sp.
Lecane s p .
Keratella quadrata (0. F. Muller)
Bfanohionus sp.
Asplanehna sp.
Ep-Lphanes sp.
Testudinella sp.
Ascomorpha sp.
Filinia longiseta (Ehrenburg)
Notholoa sp.
Lepadella sp.
Ph-Llodina sp.
Polyarthpa sp.
Cladocera
Bosmina longirostris (0. F. Muller)
Daphnia pulex (DeGeer)
Ceriodaphnia reticulata (Jurine)
Alona guttata Sars
Chydorus sphaeriaus (0. F. Muller)
Copepoda
Cyclops biauspidatus thomasi Forbes
nauplii
Total
PI
13
13
--
8
1
1
--
3
a/
2
--
a/
--
a/
--
--
--
a/
a/
--
--
--
--
18
6
13
39
P2
96
51
45
10
1
1
1
1
3
2
--
--
--
1
i/
--
2
a/
2
--
—
§./
1
--
1
109
P3
15
14
1
15
1
a/
4
1
4
1
a/
2
2
--
—
25
--
a/
a/
25
34
8
26
89
P4
22
17
5
83
2
5
30
4
7
5
—
a/
27
a/
--
1
1
47
--
4
38
2
3
131
26
105
283
Present but less than 1 organism/1.
18
-------
300
O)
'^ 200
CO
tr
_
o
o
N
100
P I
P2
P3
P4
Figure 4. Annual mean densities of net zooplankton
19
-------
9O
80
70
g
•^ s* s\
co 60
o
Q.
•^
8 50
LJ
£ 40
S 30
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20
10
n
—
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—
-
!
xs>
$^
1
^
mmmmmm
[~1 Protozoa
|^g Rotatorla
| JGIadocera
^ Copepoda
iL 1
% %
<^\\:
^N
1
\^\
I
\\\
^
^
1
^
i
PI
P2
P3
P4
Figure 5. Percentage composition of major net zooplankton groups using
density values.
20
-------
Net zooplankton density exhibited various degrees of seasonality in
the ponds (Figure 6). Pond PI showed little seasonality with small peaks
in density in late summer due to increased abundance of Cyclops bicuspidatus
thomasi and Branahionus, and in January resulting from an increase in
Difflugia. Greater seasonal trends were observed at P2, with a late summer
peak of Ceratium and an early spring peak in the density of Chydorus
sphaericus and Cyclops bicuspidatus thomasit pond P3 exhibited little
temporal variation. Pond P4 had the greatest zooplankton density in late
summer, with a small peak in November. The high density in late summer-
early fall was due to great abundance of Cyclops bicuspidatus thomasi from
July through September, and August peaks in the density of Keratella
quadrata and Ceriodaphnia reticulata. The peak in November was due to the
occurrence of great numbers of Filinia longiseta.
The seasonal pattern in protozoan density, with late winter peaks at
PI and P2, was similar to the pattern for protozoans observed by Pennak
(1949) in Gaynor Lake, Colorado. The August peak in the density of Keratella
quadvata was also similar to late summer pulses observed by Pennak (1949).
Filinia longiseta is considered dicyclic, with summer and autumn peaks
(Pennak 1949), although it may exhibit only one of these peaks as in the
fall peak at P4. The late summer peak density of Ceriodaphnia reticulata
contrasted with early summer peaks for this species reported from a Kansas
pond (Armitage and Smith 1968). Cyclops bicuspidatus thomasi had peak
densities in late summer-early fall at PI, P3, and P4. This pattern was
similar to seasonal trends for this genus observed by Pennak (1949) in
Colorado and Young (1974b) in England, as well as Armitage and Smith (1968)
for other cyclopoid copepods in a Kansas pond.
The ponds also differed in the number of taxa collected (Table 5).
The fewest number of taxa (10) was found at the youngest spoils pond (PI).
The control pond, P4, had the greatest number of taxa with 18. The trend
was statistically significant (P < 0.01). Species diversity index values
were lower in the ponds in the mine spoils (PI, P2) than the other two
ponds (Table 5). The highest value was calculated for P4. Equitability
did not exhibit a clear pattern.
The Coefficient of Community was used to test the similarity of the
ponds with respect to the presence or absence of zooplankton taxa (Table 6)
Using this index, ponds P2 and P3 exhibited the highest similarity (0.83);
however, the index values were high for all combinations, which reflected
the similar taxa found at the ponds. Percentage Similarity considers
relative abundance as well as taxa present. Using this index (Table 6),
ponds PI and P3 exhibited the greatest similarity (0.66). This could be
explained in the context of island biogeography (MacArthur and Wilson
1967). Pond PI, the youngest pond, would receive the greatest number of
colonizers from the nearest source, which is P3. The similarity was greatest
for the quantitative representation of the protozoans and rotifers in these
ponds. Both of these groups (especially protozoans) have been shown to be
dispersed passively with the action of the wind, flying insects, and birds
(Maguire 1963, Stewart £t aj_. 1970, Milliger et al. 1971, Solon and Stewart
1972).
21
-------
1000 r
« 800 -
— 10 to
1977-78
Figure 6. Seasonal trends in net zooplankton densities,
22
-------
TABLE 5. NET ZOOPLANKTON SPECIES DIVERSITY,
EQUITABILITY, AND NUMBER OF TAXA FOR PONDS
ASSOCIATED WITH COAL MINING IN
NORTHWESTERN COLORADO
Ponds
PI
P2 P3 P4
.Shannon-Weaver Index 1.95 1.78 2.49 2.68
Equitability 0.54 0.33 0.52 0.49
Number of taxa 10 14 15 18
TABLE 6. COEFFICIENT OF COMMUNITY AND
PERCENTAGE SIMILARITY USING ZOOPLANKTON FOR
PONDS ASSOCIATED WITH COAL MINING IN
NORTHWESTERN COLORADO
Coefficient of Community
5
s-
-------
C. BENTHIC MACRO INVERTEBRATES
During the study, 52 taxa of benthic macroiinvertebrates were identified
from the four ponds, although only 14 were considered numerically abundant
(Table 7).
Standing crop (density and biomass) of the benthic invertebrates
exhibited a marked pattern (Figure 7), with the greatest standing crop at
PI, the youngest spoils pond, and the lowest standing crop at the control
pond, P4. The large standing crop at PI was due to the large numbers of
tubificid worms and chironomids (Table 7). The density (5222 organisms/m2)
and biomass (28.7 g/m ) at P2 was dominated by sphaeriid clams, with
chironomids being less abundant (Tables 7 and 8). The lower standing crop
at P3 was due to decreased abundance and biomass of tubificid worms and
chironomids. The control ponds had the lowest standing crop (3160 organ-
isms/m and 24.7 g/m ) due to low numbers of worms and midges. The standing
crop at P4 was dominated by the density of amphipods and mayflies, and the
biomass of amphipods, mayflies, leeches, and odonates. Statistical analysis
of variance run on density and biomass values for the year's data failed to
show a significant difference between the ponds (P > 0.05) due to the great
temporal variations in the abundance of individual taxa.
Oligochaeta were present in all ponds, but abundant only in PI and P3.
At pond PI, oligochaetes comprised 44% of the invertebrate density (Figure
8a) and 65% of the invertebrate biomass (Figure 8b), with Lirmodrilus
hoffmeisteri the predominant species. Tubificid worms were less abundant
at P2, accounting for only 11% of the density and 14% of the biomass. At
P3, oligochaetes comprised 45% of the invertebrate density and 52% of the
biomass, with Lirmodrilus hoffmeistevi predominating. Oligochaetes were
less abundant at P4, accounting for only 7% of the density and 8% of the
biomass. In all ponds, Lirmodrilus hoffmeisteri was more abundant than
Tubifex tubifex, a relationship also observed by Young (1974a) in a small
English pond.
Hirudinea were collected from all ponds, although only rarely in PI.
Leeches were more abundant in the other ponds, accounting for approximately
5% of the density and 10% of the biomass, with Helobdella stagnalis the
predominant species in all cases.
Molluscs varied in abundance in the ponds. At PI, molluscs accounted
for only 4% of the density, but 14% of the biomass (shells removed) due to
the abundance of Physa. Molluscs accounted for 43% of the density and 40%
of the invertebrates biomass at P2, due primarily to large numbers of
Pisidiim variabile. Molluscs were relatively unimportant at P3, comprising
only 1% of the density and 5% of the biomass. At P4, the molluscs were
slightly more abundant, accounting for 12% of the density and 9% of the
biomass. Pisidiwn variabile and Gyraulus were the predominant taxa.
Amphipods were represented by a single species, Hyalella azteaa. This
species was never collected at PI, the youngest spoils pond. At P2, amphi-
pods accounted for 5% of the density and 3% of the bioinass, while at P3
24
-------
TABLE 7. SPECIES LIST AND DENSITY (ORGANISMS/M2) OF BENTHIC
MACROINVERTEBRATES FROM PONDS ASSOCIATED WITH COAL
MINING IN NORTHWESTERN COLORADO (JUNE 1977-MAY 1978)
Ponds
Oligochaeta
Limnodrilus hoffmeisteri Claparede
Tubifex tubifex (0. F. Miiller)
Eiseniella tetraedr>a (Savigny)
Hirudinea
He lobde 1 la stagna Us (Linn.)
Maorobdella sp.
Erpobdella punotata (Leidy)
Glossiphonia oomplanata (Linn.)
Mollusca
Physa sp.
Lymnaea sp.
Gyraulus sp.
Pisidittm variabile Prime
Amphipoda
Hyalella azteoa (Saussere)
Hydracarina
Hydrachna sp.
Plecoptera
Malenka sp.
Ephemeroptera
Callibaetis sp.
Baetis sp.
Caenis sp.
Henri ptera
Hesperooorixa laevigata (Uhler)
Notonecta lobata Hungerford
N. unifasoiata Guerin
Odonata
Neoneura sp.
Ampkiagrion sp.
Enallagma sp.
Anax sp.
Sympetrum corruption (Hagen)
PI
3425
3223
202
1
1
1
M _
--
296
260
32
4
--
--
--
--
20
9
M _
11
10
6
4
65
23
17
24
__
—
P2
591
532
59
360
359
1
--
2261
78
23
50
2110
286
--
--
44
10
34
6
6
--
92
20
4
66
1
1
P3
2176
1817
356
3
252
251
1
49
14
6
29
342
1
1
50
49
1
17
13
3
1
14
4
3
6
1
P4
209
204
5
w
164
134
6
\j
19
5
375
3
153
218
660
5
—
1192
3
2
1188
16
5
11
35
11
16
2
6
25
-------
TABLE 7. Continued
Ponds
Trichoptera
Agraylea sp.
Ochrotriohia sp.
Limnephilus sp.
Phryganea ainerea Wai ker
Oeoetis sp.
Neatopsyohe sp.
Indet. larva
Megaloptera
Sialis sp.
Coleoptera
Hydroporus tenebrosus LeConte
Agdbus disintegratus (Crotch)
Hydatiaus sp.
Tvop-iste'xmus sp.
Haliplus spp.
Diptera
Tdbanus sp.
Paralimna sp.
Euparyphus sp.
Tipula sp.
Eexatoma sp.
Bezz-ia sp.
Pvobezzia sp.
Palpomyia. sp.
Chironomus sp.
Procladius sp.
Tany tarsus sp.
Orthocladius sp.
Phaenopseotra sp.
Ablabeemyia sp.
PI
— _
--
--
--
--
--
--
— ~
1
149
59
9
--
82
3872
9
--
--
—
--
--
--
120
13
1682
808
1210
30
—
P2
26
--
--
17
3
3
1
1
6
17
1
3
1
11
1531
56
1
--
—
--
--
--
75
29
771
527
21
52
10
P3
12
1
3
7
--
--
--
•• ~
— ~
66
10
—
56
1846
1
--
13
6
1
20
12
102
528
21
423
684
22
12
P4
2
--
--
2
--
--
--
"" ~
~ —
185
24
5
3
13
140
317
22
2
3
— —
--
21
44
54
--
8
16
43
104
~ ~
Total
7840
5222 4826
3160
26
-------
8000
6000
CM
E
1 4000
O)
z
2000
Density
3iomass
PI
P2
P3
-i50
40
30
CM
-------
TABLE 8. BIOMASS (G/M2) WET WEIGHT OF MAJOR
INVERTEBRATE GROUPS FROM PONDS ASSOCIATED
WITH COAL MINING IN NORTHWESTERN COLORADO
(JUNE 1977-MAY 1978)
Ponds
Oligochaeta
Hirudinea
Mollusca
Amphipoda
Hydracarina
Plecoptera
Ephemeroptera
Hemiptera
Odonata
Trichoptera
Megaloptera
Coleoptera
Diptera
Total
PI
27.4
+a/
6.1
--
--
--
0.4
0.8
0.5
--
0.1
1.8
5.0
42.1
P2
4.0
3.7
11.6
1.0
--
--
0.2
0.1
1.8
3.2
0.3
0.4
2.5
28.7
P3
14.6
2.6
1.4
2.0
+
+
0.4
0.6
0.2
0.2
—
0.3
5.8
28.2
P4
1.9
3.2
2.2
3.4
+
—
6.0
0.8
3.8
0.3
—
1.8
1.2
24.7
- + = present but less than 0.05 g/m2.
28
-------
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30
20
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they comprised 7% of the invertebrate density and biomass. Amphipods were
most abundant in the control pond, P4, accounting for 21% of the density
and 14% of the biomass.
Hydracarina were collected infrequently at P3 and P4, the ponds not
directly associated with mining activity. Water mites were never collected
at PI or P2.
Plecoptera are generally not found in ponds. A single specimen of
Malenka. was collected at P3.
Ephemeropterans were collected at all ponds, but were abundant only at
P4 where they accounted for 38% of the density and 24% of the invertebrate
biomass due to large numbers of Caenis.
Henriptera accounted for less than 1% of the invertebrate density at
all ponds. This was partly due to the sampling method which is not designed
to collect strong swimmers. Hesperooorixa laevigata was the most abundant
species in all ponds.
Odonata were collected in all ponds with damsel flies being the most
abundant suborder. Odonates were unimportant at PI and P3, accounting for
approximately 1% of the invertebrate density and biomass. While the
odonates accounted for only 2% of the density at P2 and 1% at P4, they
accounted for 6% of the biomass at P2 and 15% at P4, due to the abundance
of the damsel flies, Neoneura and Enallagma.
Trichoptera occurred infrequently except at P2, where they accounted
for 11% of the invertebrate biomass, due to the presence of the large
caddisfly larvae Phryganea einerea and Limnephilus. Caddisflies were never
collected at PI, the youngest pond in the mine, and only rarely at P3 and
P4.
The megalopteran sialis was collected infrequently only at PI and P2,
the ponds in the mine spoils, where they accounted for less than 1% of the
density and biomass.
Aquatic beetles (Coleoptera) were present in all ponds, but abundant
only at PI and P4. Coleopterans comprised 2% of the invertebrate density
and 4% of the invertebrate biomass at PI, due to the abundance of Haliplus
spp. and Hydroporus tenebrosus. Beetles were less important at P2 and P3,
accounting for only 1% of the invertebrate density and biomass. Coleoptera
were most important at P4, accounting for 6% of the density and 7% of the
biomass due to the greater abundance of Haliplus spp. Species of Haliplus
are often found in strip-mine ponds (Brigham and Sanderson 1974), which are
used as refugia in areas with little standing water.
Dipterans were abundant at all ponds. They comprised 49% of the
density, and 12% of the biomass at PI, due to the abundance of the midge
larvae Procladius, Tanytarsus, and Orthoeladius. Chironomids were also
shown to be major members of the benthos in strip-mine lakes in Indiana
(Smith and Frey 1971). At P2, the dipterans comprised 29% of the density
30
-------
and 9% of the biomass due to high numbers of the chironomids Proeladius and
Tanytarsus, as well as Tabanus and Palpomyia, Ceratopogonids (e.g.,
Palpomyia) were also abundant in a strip-mine lake in Kansas (Burner and
Leist 1953). At P3, dipterans accounted for 38% of the density and 20% of
the biomass, due to the abundance of Chironomus, Tanytarsus, Orfhoaladius,
and Palpomyia. The control pond (P4) had the lowest density of dipterans,
which comprised only 10% of the density and 5% of the biomass, primarily
due to decreased abundance of chironomids.
Benthic macroinvertebrate density exhibited marked seasonal trends at
the ponds (Figure 9), ranging from 15,326 organisms/m2 at PI in January to
474 organisms/m2 at P4 in October. The seasonal pattern at PI exhibited
little fluctuation in summer and early fall, with major peaks in January
and May. The peak in density in January was due to a large increase in
Ovthoaladius and oligochaetes. The increased density in May was due to
increased numbers of L-Lmnodrllus hoffmeisteri and Tanytarsus. A spring
maximum for Limnodrilus hoffmeisteri was also observed by Young (1974a) in
a small pond in England.
The seasonal pattern at P2 exhibited marked peaks in density in summer
and late fall. The peak in June was due to high numbers of Pisidium
variabile and the chironomids Pvoolad-ius and Tanytarsus. The increase in
density in fall was due to Pisidium variabile* Proeladius3 Tanytavsus,
Hyalella azteoa, and Limnodrilus hoffmeisteri.
The pattern at P3 was similar to that observed at P2. Peak density in
June was due to large numbers of Chironomus, Tanytarsus, Orthoaladius,
Limnodrilus hoffmeisteri3 and Tubifex tubifex. The increase in fall was
due to tubificid worms in October and Hyalella azteca in November. Increased
density of Tanytarsus and Orthooladius in January offset decreases in the
density of tubificid worms and amphipods.
The seasonal trends at P4 were less distinct. There was a peak in
density in June due to the great abundance of the mayfly Caenis. The
emergence of this mayfly resulted in lower density in July. Little change
in density occurred through late fall. The higher density in March was due
primarily to increased abundance of Hyalella azteca and to a lesser extent
Limnodrilus hofftneisteri. A more detailed analysis of seasonal trends in
fauna! abundance would require detailed examinations of life cycles of
individual taxa which is beyond the scope of this study.
The fewest number of macroinvertebrate taxa were collected at PI, the
youngest spoils pond, with only 25 taxa represented (Table 10). The other
ponds had approximately the same number of species (36-38). This trend was
not statistically significant (P > 0.05) due to the seasonal occurrence of
the benthic taxa in the ponds. The increased number of species at the
other ponds was due to more species of Hirudinea, Amphipoda, Odonata,
Trichoptera, and Diptera (Table 9); organisms that may not have colonized
PI yet due to low dispersal ability (e.g., Amphipoda) or lack of adequate
time to reach the pond. Species diversity values exhibited similar trends
(Table 10), with the lowest value at PI, the youngest pond in the mine, and
higher, more similar values at the other ponds, although equitability
31
-------
CJ
16,000
14,000
I2t000
10,000
w
'E
o
8,000
CO
o
6,000
4,000
2,000
— o>
°- K o
o> u «
(/) O z
in co 12
1977-78
o
-3
00
& f
< 2
in to
Figure 9. Seasonal trends in the densities of macrobenthos.
32
-------
TABLE 9. NUMBER OF TAXA IN MAJOR
INVERTEBRATE GROUPS FROM PONDS ASSOCIATED
WITH COAL MINING IN NORTHWESTERN COLORADO
(JUNE 1977-MAY 1978)
Ponds
Oligochaeta
Hirudinea
Mollusca
Amphipoda
Hydracari na
Plecoptera
Ephemeroptera
Henri ptera
Odonata
Trichoptera
Megaloptera
Coleoptera
Di ptera
PI
3
1
3
0
0
0
2
2
3
0
1
3
7
P2
2
2
4
1
0
0
2
1
5
5
1
4
9
P3
3
2
3
1
1
1
2
3
4
3
0
2
13
P4
2
4
3
1
1
0
3
2
4
1
0
5
10
33
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TABLE 10. MACROINVERTEBRATE SPECIES DIVERSITY,
EQUITABILITY, AND NUMBER OF TAXA FOR PONDS
ASSOCIATED WITH COAL MINING IN
NORTHWESTERN COLORADO
Ponds
PI P2 P3 P4
Shannon-Weaver Index 2.49 2.95 3.03 3.13
Equitability 0.31 0.30 0.30 0.34
Number of taxa 25 36 38 36
TABLE 11. COEFFICIENT OF COMMUNITY AND
PERCENTAGE SIMILARITY USING MACROINVERTEBRATES
FROM PONDS ASSOCIATED WITH COAL MINING IN
NORTHWESTERN COLORADO
Coefficient of Community
>,
•r—
S-
^y^trm
*O tz
•M-r-
C 00
0)
PI
P2
P3
P4
PI
--
0.42
0.68
0.14
P2
0.75
—
0.36
0.31
P3
0.70
0.68
0.26
P4
0.62
0.75
0.73
34
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values exhibited no difference between ponds. It is felt that the less
diverse benthic community at PI is largely a function of colonization
phenomena, although higher levels of nitrate, sulfate, and IDS may provide
an adverse environment for some species.
Coefficient of Community was calculated to test the similarity of the
ponds with respect to the presence or absence of benthic macroinvertebrate
taxa (Table 11). As with the zooplankton, the values were high for all
combinations. Using the Percentage Similarity index, which also takes
relative abundance into account, ponds PI and P3 were most similar (0.68),
as was true for zooplankters. Pond P3 was the nearest source of colonizers
for the younger pond. Pi and P4, the control pond, were the most dissimilar
(0.14), as expected, since the control pond is in a watershed adjacent to
the mine spoils.
D. SUMMARY
Mine drainage appeared to have no effect on a variety of physico-
chemical parameters measured in spoils ponds in Colorado. Acid mine
drainage was not observed. Total dissolved solids, nitrate and sulfate
levels, however, were higher in the spoils ponds than the control pond.
Zooplankton density was greatest in the control pond and lowest in
the youngest spoils pond. Macroinvertebrate standing crop exhibited an
opposite trend with the highest value in the youngest spoils pond.
Certain zooplankters (e.g., Cladocera) and benthic invertebrates
(e.g., Amphipoda, Trichoptera) were rare or absent in the youngest spoils
pond which also contained the fewest species of zooplankton and benthos.
Biological differences between ponds may be attributed to colonization
phenomena and higher levels of nitrate, sulfate and TDS in the spoils
ponds.
35
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REFERENCES
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38
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-600/3-79-124
2.
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE
Environmental Effects of Western Coal Surface Mining.
Part I - The Limnology and Biota of Mine Spoils Ponds
in Northwest Colorado
5. REPORT DATE
December 1979 issuing date
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
Steven P. Canton and James V. Ward
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Department of Zoology and Entomology
Colorado State University
Fort Collins, Colorado 80523
10. PROGRAM ELEMENT NO.
1NE625
11. CONTRACT/GRANT NO.
R803950
12. SPONSORING AGENCY NAME AND ADDRESS
Environmental Research Laboratory-Duluth, MN
Office of Research and Development
U.S. Environmental Protection Agency
Duluth, Minnesota 55804
13. TYPE OF REPORT AND PERIOD COVERED
Final
14. SPONSORING AGENCY CODE
EPA/600/03
15. SUPPLEMENTARY NOTES
16. ABSTRACT
Physico-chemical conditions, zooplankton, and benthos were investigated in coal strip-
mine ponds in northwestern Colorado. There were no discernible effects of mine drain-
age on a variety of physico-chemical parameters. In stark contrast to spoils ponds in
the eastern and midwestern states, acid mine drainage was not observed. Total
dissolved solids, nitrate and sulfate values were higher in the spoils ponds than in
the control pond. Net zooplankton abundance was lowest in the youngest spoils pond,
but the standing crop of benthos exhibited a progressive decrease from the youngest
spoils pond to the control pond. Zooplankton and benthos species diversity were lower
in the spoils ponds. Certain groups of zooplankters and benthos were rare or absent
in the youngest spoils pond. Colonization phenomena (age and distance from a source
of colonizers) are postulated as responsible, in part, for the faunal differences
between ponds. If these data are typical of the western energy region, they suggest
the potential for development of recreational lakes as a part of reclamation practices.
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.IDENTIFIERS/OPEN ENDED TERMS
c. COSATI Field/Group
Spoil ponds
Invertebrates
Zooplankton
Macrobenthos
Effects of mining
Energy development
Coal mining
Water quality
06/F
68/D
18. DISTRIBUTION STATEMENT
RELEASE TO PUBLIC
19. SECURITY CLASS (ThisReportj
UNCLASSIFIED
21. NO. OF PAGES
47
20. SECURITY CLASS (This page)
UNCLASSIFIED
22. PRICE
EPA Form 2220-1 (R«v. 4-77) PREVIOUS EDITION is OBSOLETE
39
,. U S. GOVERNMENT MUNIINO OFFICE: 1880-657-146/5526
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