AFO-C90-05
Biota Investigation of
Freshwater Streams Possibly Affected by
Southern Maryland Wood Treating Superfund Site
U.S. Fish and Wildlife Service
April 1990

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Biota Investigation of
Freshwater Streams Possibly Affected by
Southern Maryland Wood Treating Superfund Site
Publication No. AFO-C90-05
U.S. Fish and Wildlife Service
Environmental Contaminants Division
Annapolis Field Office
Annapolis, MD 21401
Prepared by:
Elizabeth Block,
Environmental Contaminants Biologist
Under supervision of:
Richard 0. Bennett, Ph.D., Assistant Supervisor
John P. Wolflin, Supervisor
Annapolis Field Office
Prepared for:
U.S. Environmental Protection Agency
Region III
Philadelphia, PA
April 1990

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Title: Biota investigation of freshwater streams possibly affected by Southern
Maryland Wood Treating Superfund Site
Abstract: Southern Maryland Wood Treating superfund site (SMWT), in
Hollywood, St. Mary's County, Maryland, has been inactive since 1978 but formerly
pressure-treated wood with creosote and pentachlorophenol (PCP). Wastes were
disposed of in unlined lagoons on-site. Contaminated groundwater discharges into
an on-site pond, which drains into Old Tom's Run. Polynuclear aromatic
hydrocarbons, PCP, iron, and mercury have been detected in the creek water at
levels orders of magnitude above U.S. Environmental Protection Agency (EPA)
water quality criteria, and creek sediments are also contaminated. The EPA
requested that U.S. Fish and Wildlife Service (FWS) conduct a biota investigation,
including a wetlands delineation, fish and amphibian survey, and benthic
invertebrate survey, to document impacts of SMWT on aquatic biota and provide
baseline data for future assessments.
Data was collected between October 1989 and March 1990. At eight sites, water
quality parameters and physical conditions were recorded, and and fish populations
were observed by electroshocking. Benthic invertebrates were collected, identified,
and results were analyzed using EPA Rapid Bioassessment Protocols. Wetlands
were delineated within the SMWT property boundary.
Aquatic biota were impacted in Old Tom's Run relative to reference sites. No fish
were observed in the upper reaches of the run adjacent to SMWT. Benthic
invertebrate populations were slightly to moderately impacted, mainly due to the
absence of pollution intolerant groups. Iron bacteria were abundant, covering up to
95% of the substrate. Downstream, fish populations seemed healthy, but
invertebrate population health decreased. The streams for which Old Tom's Run is
a tributary did not show obvious impacts.
Key words: superfund, wood treating, creosote, pentachlorophenol, polynuclear
aromatic hydrocarbons, benthic invertebrates, wetland delineation, mudminnow
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TABLE OF CONTENTS
LIST OF TABLES 	iii
LIST OF FIGURES 		iv
LIST OF APPENDICES		v
INTRODUCTION		1
Cleanup and investigation activities		1
Watershed description 		1
MATERIALS AND METHODS 			5
Physical characteristics		6
Invertebrate sampling		6
Fish and amphibian survey		7
Wetland delineation 		7
RESULTS		8
Water quality parameters 		8
Effects to benthic invertebrates		10
Effects to fish and amphibians		13
Observations of stream conditions		13
Wetland delineation 		13
DISCUSSION		18
Contaminants of concern 		18
Terrestrial routes of exposure 		19
Aquatic routes of exposure		20
Effects to stream ecosystems		20
LITERATURE CITED 			22
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LIST OF TABLES
Table 1. Water quality parameters measured at headwater streams in the
vicinity of Southern Maryland Wood Treating Superfund site,
Hollywood, MD	 9
Table 2. Assessment of pollution impacts on benthic invertebrate
populations at six headwater stream sites near Hollywood, MD
using EPA rapid bioassessment protocols	11
Table 3. Fish, amphibians, and invertebrates observed during electro-
shocking of headwater streams in the vicinity of Southern
Maryland Wood Treating Superfund site, Hollywood, MD	14
Table 4. Wetland plant species identified at Southern Maryland Wood
Treating Superfund site, Hollywood, St. Mary's County, MD	17
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LIST OF FIGURES
Figure 1. Site location 	2
Figure 2. Primary features at the Southern Maryland Wood Treating site ... 3
Figure 3. Eight sites were sampled to determine effects of Southern
Maryland Wood Treating superfund site, Hollywood, MD on
aquatic biota	4
Figure 4. Approximate locations of wetlands on the Southern Maryland
Wood Treating superfund site, Hollywood, MD 		16
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LIST OF APPENDICES
Appendix 1. Activities and dates for eight sites sampled to detect effects
of fish and wildlife from Southern Maryland Wood Treating
(SMWT) superfund site, Hollywood, MD	 23
Appendix 2. Physical characteristics/water quality data sheets for each of
eight sites used to assess effects of Southern Maryland Wood
Treating superfund site, Hollywood, MD on aquatic biota .. 25
Appendix 3. Calculation of Hilsenhoff Family Biotic Index (FBI) for benthic
invertebrates collected at six sites to determine the effects of
contaminants from Southern Maryland Wood Treating
superfund site, Hollywood, MD	 34
Appendix 4. Bird species observed on or nearby Southern Maryland Wood
Treating superfund site, Hollywood, MD	 41
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INTRODUCTION
The Southern Maryland Wood Treating superfund site (SMWT) is located near
Hollywood, Maryland, in St. Mary's County, directly off Route 235 (Figure 1). The
site occupies approximately 24.7 acres of which about 4 acres was formerly used
for wood treating. Wood was preserved by pressure treatment with creosote and
pentachlorophenol (PCP) between 1965 and 1978, and the site has been inactive
since then. Contamination generated by this process included sludges, process
wastes, spills, and drippage from treated wood stored on-site. Wastes were
disposed of in six unlined lagoons on-site, which contaminated a nearby on-site
freshwater pond and groundwater (Figure 2).
Cleanup and investigation activities
Cleanup of the lagoons was conducted in 1982 by former owners, L.A. Clarke &
Sons, Inc. Liquid from the lagoons was sprayed onto an on-site wooded area.
Sediment was excavated from the lagoons and part of the pond, mixed with wood
chips and stabilized sewage sludge, and spread over one corner of the property
(land treatment area, Figure 2). This area was then covered with topsoil and
seeded with grass. Land treatment met with little success, and high levels of
contaminants occur in the soils of this area.
The SMWT site was placed on the U.S. Environmental Protection Agency (EPA)
National Priority List in October 1984. Based on analytical results of site
characterization, emergency cleanup measures were conducted by EPA between
March 1985 and January 1986. Contaminated soils from the lagoon area and
sediment from the northwest side of the pond was excavated, stored on-site and
temporarily capped under an impermeable membrane (Figure 2) for future
treatment. The process area was also capped with clay, graded, and seeded.
U.S. Fish and Wildlife Service (FWS) biologists conducted a site visit in June 1986
and observed evidence of contaminants off-site (iron-colored water) in Old Tom's
Run, Brooks Run, and Mcintosh Run (Figure 3). A preliminary natural resource
survey was conducted by FWS in September 1988. In February 1989, EPA
requested that FWS conduct a biota investigation, including a wetlands delineation,
fish and amphibian survey, and benthic invertebrate survey. The study was
conducted to provide preliminary documentation of on and off-site impacts to fish
and wildlife resources and their habitats, and to document baseline conditions to
determine success of future mitigation. The results of the investigation are reported
here.
Watershed description
Groundwater discharge into surface water is the most probable route of
contaminant exposure to fish and wildlife. Seeps of dark colored, oily looking
groundwater have been observed for several years running in channels into the on-
site pond. The on-site pond flows through culverts under a berm and forms the
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FIGURE 2 PRIMARY FEATURES AT THE SMWT SITE
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Laurel Park

y a
Oakville Berne ntary School
"V.
li
\
Figure 3. Eight sites were sampled to determine effects of
Southern Maryland Wood Treating superfund site,
Hollywood, MD on aquatic biota.
V
J_L
MILES
*
ru
Southern Maryland
Wood Treating arte

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headwater of Old Tom's Run. The creosote odor noticeable around the pond can
also be detected in the upper reaches of Old Tom's Run. Several structures
remain in the main channel from former filter fences used during EPA emergency
cleanup measures. Old Tom's Run forms a distinct, moderate to steeply banked
channel, about 10 feet between banks for about a third of a mile. Then, the water
flow slows and the channel becomes braided and swampy just upstream of the
confluence with the east tributary. Surface water of the east tributary begins about
180 feet east of the southeast corner of the fenced portion of the property (Figure
4). The east tributary forms a distinct channel with moderate to vertical undercut
banks up to three feet high. The channel averages about five feet between banks,
with occasional small ponds. Both of these streams run through stands of mature
deciduous forest, and are fed by groundwater and small intermittent tributaries.
Downstream of the confluence, Old Tom's Run continues, braided and swampy, for
about a mile before flowing into a small man-made pond which exits through a
culvert under Morgan Road (Figure 3). The run continues for almost another mile
and joins with Brooks Run, about a half mile downstream of where Brooks Run
crosses Highway 245. Beavers have taken over this stretch of Brooks Run, and
much of the bottomland is vegetated in scrub shrub wetland species punctuated by
snags from the former forested vegetation. Shallow standing water is extensive
after rainfall or snowmelt. Downstream of the dammed area, the channel was lush
with submerged and emergent vegetation. About another mile downstream,
Brooks Run converges with Mcintosh Run, which drains the watershed to the west
of the Old Tom's Run watershed. The Mcintosh watershed has been developed
with several housing tracts, causing the formation of several ponds. Mcintosh Run
continues for several miles before emptying into Breton Bay, a tidal embayment of
the Potomac River. The federally endangered freshwater dwarf wedge mussel
(Alasmidonta heterodonl is found in the lower, nontidal reaches of Mcintosh Run.
MATERIALS AND METHODS
Eight sites were sampled on the streams described above. Site 1 was off-site on
Old Tom's Run, about halfway between the south fenceline and the confluence with
the east tributary (Figure 3). Site 2 was on the east tributary, about halfway
between the southern edge of the property and the confluence with Old Tom's
Run. Sites 3 and 4 were both on Old Tom's Run, upstream and downstream of
Morgan Road Pond, respectively. We hypothesized that the pond might serve as a
settling basin for contaminated sediment, and that Sites 1,3, and 4 might show a
gradation of effects. Site 5 was on Brooks Run, upstream of the confluence with
Old Tom's Run, and served as a reference for site 6. Site 6 was on Mcintosh Run,
downstream of the confluence with Brooks Run (and therefore, Old Tom's Run).
Site 7 was at the headwaters of Burnt Mill Creek, about five miles northeast of
SMWT on highway 235, and served as a reference for site 2. Site 8 was at the
headwaters of Laurel Creek, near Laurel Grove Park, about seven miles northeast
of SMWT on highway 235, and served as a reference for sites 1, 3, and 4.
Headwaters of Mcintosh Run were originally intended for the locations of reference
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sites. Due to widespread housing development in the Mcintosh watershed, nearby
headwaters were examined until stream conditions similar to sites 1 and 2 were
located.
Reference sites were selected based on the following criteria. Highway 235 ran
along a ridge dividing watersheds which joined either the Patuxent or Potomac
Rivers. All sites were south of highway 235. Reference sites matched the
experimental sites as closely as possible in terms of vegetative overstory, stream
size and flow, sediment grain size, lack of nearby development, and proximity to
SMWT. Site 5 was located on Brooks Run in a short stretch between a beaver
dam and the confluence with Old Tom's Run. As the dam was likely to influence
upstream fish populations, there were no options for the location of site 5, and
conditions could not be matched with site 6.
Physical characteristics
Sampling dates for sites and activities are shown in Appendix 1. At each site, the
following measurements were taken and samples collected. A Surveyor n II
Hydrolab was used to measure temperature, pH, dissolved oxygen, and
conductivity. The hydrolab was calibrated prior to sampling in accordance with
manual instructions (Hydrolab Corporation 1985). A physical characteristics/water
quality data sheet, based on EPA Rapid Bioassessment Protocols (Plafkin et al.
1989), was completed for each site.
Invertebrate sampling
Aquatic invertebrate samples were collected with a Surber sampler (Wildco
Instruments, Saginaw, Ml). The Surber sampler was deployed three times at each
site. Substrate at all sites was sandy, and invertebrates were concentrated in leaf
drifts. The Surber was set twice in leaf drift areas and once in a sandy area.
Organisms were picked from the net, leaves, and debris in the field, and the three
samples were combined in a single jar and preserved with 70% ethyl alcohol.
Invertebrates were sorted and identified to the lowest level possible; most were
indentified to genus (Finni 1990). The degree of impact of the site on benthic
invertebrates was assessed using EPA Rapid Bioassessment Protocols (Plafkin, et
al. 1989) which describes several methods to determine the degree of impacts to
biota from contaminants. We used Rapid Bioassessment Protocol II for benthic
invertebrates, which allows assessment of intermediate degrees of impact between
sites through the calculation of eight metrics.
Six of eight metrics were used in the analysis. The two metrics not used were both
measures of different functional feeding groups. The stream substrates were all
sandy or silty, and functional feeding groups were expected to be predominantly
shredders. Since metrics addressing functional feeding groups were not used in
the analysis, species lists by site were given a cursory examination to determine
whether all functional feeding groups were represented at each site. The six
metrics used in analysis: taxa richness, family biotic index, ratio of Ephemeroptera,
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Plecoptera, and Trichoptera (EFT) to Chironimidae abundance, percent contribution
of dominant family EPT index, and community similarity indices are described in the
results section. Once the metrics were calculated, they were either evaluated as a
percent of the reference site or evaluated against scoring criteria (Plafkin 1989) to
produce bioassessment scores. The bioassessment scores for each metric were
summed for a site and then evaluated as a percent of the reference site total
bioassessment score to indicate a relative degree of impairment.
One of the metrics involved calculation of family biotic indices for pollution
tolerance. Indices were calculated for families of invertebrates. Family biotic index
values were obtained for insects (Hiisenhoff 1988), molluscs (Bode 1988), and
crustaceans (Hiisenhoff 1977). Family biotic index values were on a scale from 0
(clean) to 10 (highly pollution tolerant) except for crustacean values, which were
scaled from 0 to 5. Crustacean values were doubled to correspond with other
values. Since using a family biotic index, rather than a genus or species index,
introduces some bias, modified bioassessment scores (Hiisenhoff 1988) were used,
rather than those used by Plafkin et al. (1989) to compare calculated results
between sites.
Fish and amphibian survey
A fish and amphibian survey was conducted at each site using a backpack
electroshocker (Smith-Root, Inc., Model 12 Electrofisher, Vancouver, WA). Pulse
frequency was 60-80 Hz, and voltage was 800-900 volts. Shocking proceeded in
an upstream direction for approximately 400 seconds of shocking time. Each fish
or amphibian was identified to species and measured for length. The numbers of
each species were tabulated and compared between sites.
A followup survey was conducted which concentrated on the upper reaches of Old
Tom's Run. The purpose of the survey was to electroshock from the on-site pond,
downstream, until fish were located.
Wetland delineation
Wetlands were delineated within the property boundaries. At the on-site pond,
wetland areas were identified by vegetation and hydrological characteristics. Soil
characteristics were not examined because of high levels of soil contaminants and
because much of the area around the wetlands had been backfilled or otherwise
disturbed. Along Old Tom's Creek and the east tributary, wetlands were identified
by hydrological (standing water) and soil characteristics. Vegetation was not used
because tree species did not vary in the small seep areas, and understory
vegetation had not emerged or leafed out. Due to steeply sloping banks, edges of
the pond and creeks were distinct, and wetland delineation was straightforward. At
the pond, approximate cross-sectional lengths were measured at regular intervals
along the long axis of the pond. For the creeks, the length of the creekbed was
totalled and multiplied by a mean bank-to-bank width (10 feet for Old Tom's Run
and 5 feet for the east tributary). Many seeps ran parallel to the creek and length
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(as determined by soil characteristics) was multiplied by the distance between the
creek edge and a slight rise in topography just beyond the seep surface water.
Irregularly shaped wetlands and the pond area were plotted, and areas calculated
using Sigma-Scan (Jandell Scientific, Code Madera, CA; Acker and Mitchell 1988).
An unnamed tributary within the property boundaries, which entered Old Tom's Run
from the west, was not delineated as it was not impacted by SMWT and no cleanup
activities are planned for this area (Lesley Brunker, EPA project manager, personal
communication).
RESULTS
Water quality parameters
Physical characteristics/water quality data sheets (Appendix 2) contain a variety of
conditions useful in assessing comparability between sites and signs of pollution
and other man-made disturbances. No site had gross signs of pollution, anoxia, or
disturbances.
Temperature, pH, dissolved oxygen, and conductivity measured at each site are
shown in Table 1. Water temperature was not expected to be affected by SMWT,
as no thermal discharges were occurring. Sites 3 and 4 were sampled about two
weeks later than other sites (Appendix 1) and lower temperatures can be explained
by colder weather.
The EPA water quality criteria for pH is 6.5 - 9.0 for the protection of freshwater
aquatic wildlife (U.S.EPA 1986). All sites were more acidic than the criterium. Low
pH was probably caused by soils in the area. The limiting factor for crops grown in
St. Mary's County is most often low soil pH, and runoff from ground disturbances
will generally lower water pH (Al Stewart, District Conservationist, St. Mary's Soil
Conservation District, Soil Conservation Service, personal communication). The
lowest pH found in Mcintosh Run (site 8) may be due to soil disturbance from
upstream urban development. No effect on pH that could be attributed to SMWT
was observed.
Dissolved oxygen (DO) at all sites was above EPA water quality criteria for
protection of the more sensitive early life stages in fresh, warmwater streams (5.0
mg/L, U.S.EPA 1986). Dissolved oxygen levels at site 1 were lower than further
downstream (sites 3 and 4), which could indicate a higher chemical oxygen
demand (COD). However, site 1 DO was higher than both reference sites (sites 7
and 8).
Conductivity was low at all sites, probably due to the headwater nature of the
streams sampled. The water had not yet accumulated levels of dissolved ions
generally found in larger streams with higher conductivity measurements. No effect
on conductivity was observed that could be attributed to SMWT.
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Table 1. Water quality parameters measured at headwater streams in the vicinity of
Southern Maryland Wood Treating Superfund site, Hollywood, MD.
Site
Temp (°C)
PH
Dissolved
Oxygen
(mg/L)
Conductivity
(^mhos)
Site 1
13.9
5.85
7.16
78
Site 2
14.2
5.35
7.27
58
Site 3
7.6
5.68
9.78
72
Site 4
8.9
5.16
8.01
97
Site 5
10.8
6.02
7.25
94
Site 6
11.7
6.41
8.68
107
Site 7
11.0
5.89
6.95
118
Site 8
13.5
4.51
5.53
72
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Effects to benthic invertebrates
Sites 1-4, 7, and 8 were compared using EPA rapid bioassessment protocols to
determine whether contaminants from SMWT were affecting benthic invertebrate
populations. Sites 5 and 6 were excluded from analysis because conditions at
these sites were distinctly different from all other sites, and from each other.
Stream flow and volume at these sites was much higher than all other sites. They
differed from each other in overstory vegetation and flow, volume, and depth of
water. Also, submerged and emergent vegetation grew at site 5 but not at site 6.
Site 7 was used as the only reference site for benthic invertebrate analysis.
Originally, site 7 was intended as a reference for site 2, and site 8 was intended as
a reference for site 1. The number of invertebrates collected at site 8 indicated that
conditions were not optimal for supporting a reference population, which may have
been related to low pH (Table 1) or intermittent stream flow. Site 8 was included in
the analysis to illustrate the range of conditions possible in these small headwater
streams.
Populations of invertebrates at all sites were typical of small, low gradient
headwater streams. Species richness, density, and biomass were all low. Density
ranged from 32-258 organisms/m2, whereas more productive streams sometimes
exceed densities of 10,000 organisms/m2. The sandy or silty substrate of these
streams provided unstable habitat, and most organisms were clumped in leaf drifts
and submerged wood. Several invertebrates were characteristic of drainages with
intermittent flow, another limiting factor on productivity.
All functional feeding groups were represented at each site. As was expected from
streams with a closed canopy overstory, shredders predominated. The reference
site sample included the highest proportion of predators, indicating a productive
habitat. Results from the six metrics used in bioassessment are described below.
Taxa Richness is a measure of the number of genera in each sample and is
expected to increase with increasing water quality, habitat diversity, or habitat
suitability. The reference site had the highest taxa richness. The second highest
taxa richness was found at site 1, downstream of the on-site pond (Table 2).
Family Biotic Index (FBI) addresses the pollution tolerance of each taxonomic
group. The FBI is calculated as z(# individuals within a species x tolerance value
of a species)/total # organisms in a sample. The FBI was calculated only for those
genera with an index value. Thus, nematodes and annelids were not included in
the calculations. For most sites, these organisms made up a very small percentage
of the total number of organisms (<1.8%), but worms at sites 2 and 3 comprised
16.7 and 14.3% of the total sample, respectively. Tolerance values and calculated
indices for each site are shown in Appendix 3. Sites 3 and 4 had the highest
bioassessment scores (Table 2), and site 1 also scored high, indicating an absence
of pollution intolerant species and/or an abundance of pollution tolerant species.
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Table 2. Assessment of pollution impacts on benthic invertebrate populations at six
headwater stream sites near Hollywood, St. Mary's County, MD using
EPA rapid bioassessment protocols.
METRIC VALUES	-SITES-
Metric	1 2 3 4 8 7(R)
Taxa Richness
14
7
11
9
5
16
Family Biotic Index
5.82
4.50
7.25
7.38
5.67
2.73
EPT/Chiron. Abundance
0
0
1.33
0.33
0
18.2
% Contrib. Dom. Taxon
25.5
42
36
50
42
72
EPT Index
0
0
2
2
0
4
Community Loss Index
1.2
2.4
1.6
1.9
3.4
0
PERCENT COMPARISON
Taxa Richness
87.5
43.8
68.8
56.3
31.3
100
Family Biotic Index
46.9
60.7
37.7
37.0
48.2
100
EPT /Chiron. Abundance
0
0
7.3
1.8
0
100
% Contib. Dom. Taxon"
25.5
42
21
50
42
72
EPT Index
0
0
50
50
0
100
Community Loss Index"
1.2
2.4
1.6
1.9
3.4
0
BIOASSESSMENT SCORE
Taxa Richness
6
2
4
2
0
6
Family Biotic Index
2
4
1
0
3
6
EPT/Chiron. Abundance
0
0
0
0
0
6
% Contrib. Dom. Taxon
4
0
2
0
0
0
EPT Index
0
0
0
0
0
6
Community Loss Index
4
2
2
2
2
6
TOTAL
16
8
8
4
5
30
% of Reference
53.3
26.7
26.7
13.3
16.7
100
Degree of Impairment
Slight/
Mod.
Mod.
Severe
Severe
Non.
Moderate





a - Range of values is evaluated, not percent comparability.
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EPT/Chironomid Abundance is a measure of community balance. These four
groups should be well represented in healthy streams. Ephemeroptera, Plecoptera,
and Trichoptera are known to be pollution-sensitive, while Chironomids are known
to be pollution tolerant. Populations skewed by a disproportionate number of
Chironomids may indicate environmental stress. The numbers of individuals in
each group were totalled, and the ratio calculated (Table 2). Samples from sites 1
and 2 contained no EPT species, and sites 3 and 4 contained very few EPT
species relative to the reference site.
Percent Contribution of Dominant Taxon is another measure of community balance.
A community dominated by one or a few species would indicate environmental
stress. The number of individuals of the most common genus was compared to
total number of individuals in the sample to calculate this metric. The population of
site 7, the reference site, had the highest percentage of a single genus. Sites 1
and 3 on Old Tom's Run had the lowest percentages of a single genus. These
results are opposite of what would be expected. Examining the dominant species
at each site gives more information. Site 1 was dominated by a genus from the
Chironomid family with a FBI of 8, indicating high pollution tolerance. Similarly, site
3 was dominated by a genus from the Asellidae family, with an FBI of 10. Site 4
was dominated by Asellidae to a greater degree than site 3, indicating lower water
quality. The dominant genus at site 7 belonged to the family Ephemeroptera which
has a FBI of 2, indicating a pollution intolerant species. While the cause for such a
high population of Ephemeroptera at site 7 is unknown, the effect of this
unexpected result is to lower the total bioassessment score of the reference site
(Table 2), thus making the other sites look better than they would be if the
population at site 7 had been more evenly distributed between taxonomic groups.
However, this effect on the analysis is somewhat compensated for in other metrics
involving EPT measurements.
EPT Index is the total number of distinct taxa (in this case, genus) within the orders
Ephemeroptera, Plecoptera, and Trichoptera, and should increase with increasing
water quality. As previously mentioned, samples from sites 1 and 2 contained no
EPT species, and sites 3 and 4 did not contain enough species, relative to the
reference site, to raise the bioassessment scores above zero.
Community Loss Index assesses the number of species missing from an
experimental site, relative to the reference site. The metric is calculated as (#
reference site species - # species common to both samples) / # experimental site
species. The reference site had four genera in common with each other site.
Because site 1 had a high diversity of species, it had the highest bioassessment
score next to the reference site (Table 2). Scores at all other sites were similar.
Total bioassessment scores were compared to the reference site total
bioassessment score and indicated that site 1 had the lowest degree of impairment,
followed, in order of increasing impairment, by site 3, site 2, site 8, and site 4.
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Effects to fish and amphibians
Species and numbers of individuals shocked at each site are listed in Table 3. The
species that seemed to be characteristic of the low gradient headwater streams
was the eastern mudminnow MJmbra pvamaeal. This was the only fish species
found at sites 2 and 8, and occurred at 8 in very high densities. Mudminnows were
also found at site 5 in low gradient areas. This species was absent from sites 1
and 7. Absence from site 7 may have been because the stretch that was sampled
was channelized and flowed at higher velocity than the other areas where
mudminnows were found. Fish were absent from site 1 both times the area was
surveyed. Green frogs (Rana clamitans^ were observed at site 1 in reasonable
numbers (Table 3).
Further downstream on Old Tom's Run, sites 3 and 4 contained a reasonable
number and variety of fish, and the presence of predators (American eel, Anauilla
rostrata and chain pickerel, Esox niaer) indicated a healthy ecosystem. Similarly,
the variety and number of fish at site 6 indicated that possible contamination was
not causing gross effects to fish populations.
Additionally, four eastern box turtle shells (Terrapene Carolina^ were found
throughout the SMWT property. They probably also occurred at sites outside of
SMWT property but were not observed because less time was spent at these sites.
Observations of stream conditions
The most noticeable thing about the upper reaches of Old Tom's Run above and
below site 1 was a thick covering of orange-brown periphyton. A sample was
collected and examined under a microscope and was identified as iron bacteria
(Lepothrix ochraceaV About 95% of the substrate was covered with the bacteria,
which was absent or very limited at sites 2, 5, 6, 7, and 8. Bacteria occurred
further downstream in Old Tom's Run, at sites 3 and 4, but it had the appearance
of having drifted downstream.
Wetland delineation
A total of 2.39 acres of wetlands was determined to occur on SMWT property
(Figure 4). The pond was surrounded by palustrine emergent wetland growing on
steep, eroded banks. Vegetation consisted of a variety of annual grasses and
herbs, as well as the wetland species listed in Table 4. Total area of this wetland
was calculated to be 0.40 acres, of which 0.14 acres was open water and 0.26
acres was palustrine emergent wetland. The south end of the pond terminated
abruptly at a man-made berm where water exited through culverts and seeps,
forming Old Tom's Run. Of the total wetlands not associated with the pond, 0.313
acres occurred as steep-banked stream channel (0.175 acres of Old Tom's Run
and 0.138 acres of the east tributary), 0.909 acres occurred as braided swampy
stream channel of Old Tom's Run in the south portion of the property, and 0.771
acres occurred as seeps alongside the channels. An area upstream of surface
13

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Table 3. Fish, amphibians, and invertebrates observed during electroshocking of
headwater streams in the vicinity of Southern Maryland Wood Treating
superfund site, Hollywood, MD.
Taxonomic	Number of
Site Group Species	Individuals
Site 1 - Old Tom's Run, downstream of SMWT
AMPHIBIANS
Green frog (Rana clamitans^	5
Site 2 - unnamed tributary to Old Tom's Run
FISH
Eastern mudminnow (Umbra pvamaeal	6
AMPHIBIANS
Green frog	2
Site 3 - Old Tom's Run, upstream of Morgan Road Pond
FISH
American eel (Anguilla rostrata)	2
Chain pickerel fEsox niaert	2
Blacknose dace (Rhinichthvs atratulusl	5
Pirate perch (Aphredoderus savanus^	2
AMPHIBIANS
Green frog	1
Site 4 - Old Tom's Run, downstream of Morgan Road Pond
FISH
American eel	5
Chain pickerel	1
Blacknose dace	5
Creek chubsucker (Erimvzon oblonausl	1
Bluegill (Lepomis macrochirusl	1
INVERTEBRATES
Crayfish (Cambarus sp.)	2
Site 5 - Brooks Run, reference for Site 6
FISH
American eel	1
Eastern mudminnow	3
Chain pickerel	5
Creek chubsucker	1
Yellow bullhead (Ictalurus natalisl	1
Bluegill	7
14

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Table 3. Continued. Fish, amphibians, and invertebrates observed during
electroshocking of headwater streams in the vicinity of Southern Maryland
Wood Treating Superfund site, Hollywood, MD.
Taxonomic	Number of
Site Group Species	Individuals
Site 5 - Continued, Brooks Run, reference for Site 6
INVERTEBRATES
Crayfish	3
Site 6 - Mcintosh Run, downstream from confluence of Old Tom's Run
FISH
Chain pickerel	4
Blacknose dace	1
Pirate perch	1
Pumpkinseed	1
Bluegill	9
Redear sunfish (Lephomis microlophusl	3
Tesselated darter (Etheostoma olmstedil	1
Site 7 - Burnt Mill Creek, reference for Site 2
FISH
Brown bullhead (Ictalurus nebulosus)	1
Pumpkinseed	2
AMPHIBIANS
Green frog	3
Pickerel frog fRana palustris)	1
INVERTEBRATES
Crayfish	1
Site 8 - Laurel Creek, reference for Site 1
FISH
Eastern mudminnow	49
AMPHIBIANS
Green frog	3
15

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16

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Table 4. Wetland plant species identified at Southern Maryland Wood
Treating Superfund site, Hollywood, MD.
Palustrine Emergent Wetland
Woolgrass (Scirpus cyperinus)*	facw
Umbrella sedge (Cvperus spp.)	obl-upl
Green briar (Smilax rotundafolia)*	fac
Japanese honeysuckle (Lonicera japonical	fac
Soft rush (Juncus effusus)*	facw
Cattail fTypha latifolia)	obi
Seed box (Ludwiaia alternifolia^	facw
Red maple (Acer rubrum)	fac
Sneezeweed (Helenium autumnal*	facw
Wax-myrtle (Mvrtica cerifera)	fac
Calico-starred aster (Aster lateriflorus)*	facw
Palustrine Forested Wetland
Loblolly pine fPinus taeda)	fac
Holly (Hex opacal	facu
Sycamore (Plantanus occidentalism*	facw
Sweet gum (Liquidambar stvrac'rflual*	fac
Sweet bay (Magnolia virginiana)*	facw
Hercules club (Aralia spinosa)	fac
Red maple (Acer rubrum)	fac
American hornbeam (Carpinus caroliniana)	fac
Arrowwood (Viburnum sp.)	fac
Green briar (Smilax rotundifolia)	fac
Soft rush (Juncus effususl	facw
Netted chain fern AA/oodwardia aerolata^	facw+
Cinnamon fern (Qdmunda cinnamomeai	facw
* dominant species
obi • obligate species
fac • facultative species
facw - facultative wet species
facu • facultative upland species
upl - upland species
17

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water in the east tributary had abundant evidence of hydrology, but soils did not
indicate saturated conditions, and the area was determined not to be wet.
Two areas not delineated because they were outside the property boundary may
need to be considered for effective cleanup. The channelized portion of Old Tom's
Run continues just outside the property boundary for about a third of the stretch
between the confluence with the east tributary and the on-site pond. Also the
confluence of Old Tom's Run and the east tributary is just outside of the property
boundary. The braided nature of this area indicates that water flow slows, and
contaminated sediments may have accumulated here.
DISCUSSION
Contaminants of concern
The contaminants of concern to date have been polynuclear aromatic
hydrocarbons (PAH), PCP, and other organics. The abundance of iron bacteria in
the upper reaches of Old Tom's Run prompted a review of metal levels in soil,
sediment, and water. Iron levels were elevated in surface soils at the site and in
water and sediment of Old Tom's Run. Iron in background surface soil samples
occurred at levels of 3950-4730 milligrams per kilogram (mg/kg), and in deeper
soils up to 9210 mg/kg (Shapot 1988). Iron was elevated in soils throughout the
site at levels up to 19,500 mg/kg. Iron in pond sediments was as high as 89,300
mg/kg, and in Old Tom's Run sediment as high as 44,000 mg/kg. Iron levels in
water exceeded EPA freshwater chronic water quality criteria of 1.0 milligrams per
liter (mg/L) at all sites along Old Tom's Run tested by Shapot (1988). Also,
mercury in Old Tom's Run was detected at levels of 0.0003 mg/L, which exceeded
the EPA freshwater chronic criteria for mercury (0.000012 mg/L).
Pentachlorophenol was detected well above water quality criteria for the protection
of aquatic resources in the on-site pond and in the upper reaches of Old Tom's
Run. This criteria is based on pH, as lower pH causes greater toxicity. The four-
day mean which should not be exceeded more than once every three years is
calculated as e[1.005(pH)-5.290]. When pH was set equal to 5.5 (mean of sites 1-
4) the criteria was calculated as 1.27 micrograms per liter (/xg/L). In surface water
from the pond, PCP was measured at 120 /xg/L. Water samples from the upper
reaches of Old Tom's Run had PCP levels at 10-82 ng/L Concentrations at
different sediment depths indicated coutinual input (Shapot 1988), and chronic
exposure of biota may be a problem. Further downstream, PCP was not detected.
Toxicity problems are less likely to occur downstream. Typically, PCP is not
bioaccumulated in biota or adsorbed to sediment, and microbial and
photodegradation is fairly rapid (Eisler 1989).
Polynuclear aromatic hydrocarbons are a major contaminant on the site. The PAHs
are a diverse group of chemicals with differing effects. The two and three-ring
molecules are fairly mobile and are photodegraded rapidly in water. They are
18

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rarely carcinogenic, and acute toxicity levels are almost always much higher than
levels in water (Eisler 1987). Four to seven-ring molecules have low mobility,
volatility, and solubility, and some are carcinogenic. These compounds tend to
associate with sediment where they degrade slowly (Eisler 1987). The larger PAHs
can be bioaccumulated by invertebrates. While excretion in fish is rapid,
metabolism to a more water soluble form for excretion can activate PAHs to more
carcinogenic forms. Creating criteria for such a diverse group of chemicals is
difficult. Current drinking water criteria for total PAHs (sum of fluoranthene,
benzo(a)pyrene, benzo(g,h,i)perylene, benzo(b)fluoranthene, benzo(k)fluoranthene,
and indeno(1,2,3-cd)pyrene) is 0.2 ^g/L (Eisler 1987). As no wildlife protection
criteria exist, the drinking water criteria will be used for comparison with SMWT
levels. Shapot (1988) indicated that levels of individual components shown in
appendices were not reliable, but ranges of total PAH levels were well above
drinking water criteria. The concentration of total PAHs in water of the on-site pond
was 238 /ig/L and, in the upper reaches of Old Tom's Run, was 54 /xg/L. While
PCP toxicity in Old Tom's Run is likely to be acute in a limited area, toxicity of the
larger PAH molecules is likely to be chronic and persistent until contaminated
sediment is buried or otherwise made unavailable to biota.
Toxic impurities of both PCP and PAHs are dioxins and furans. The most
thoroughly studied dioxin, 2,3,7,8-tetrachloro dibenzodioxin (2,3,7,8-TCDD), has
been characterized as exceedingly stable, readily incorporated into aquatic and
terrestrial ecosystems, extraordinarily persistent, and virtually impossible to destroy
(Eisler 1986). Dioxin and furan levels were reported in 2,3,7,8-TCDD toxicity
equivalent factors (Shapot 1988) which did not allow comparison with water quality
criteria levels. The levels of dioxins and furans found in on-site soils were well
above background levels.
Terrestrial routes of exposure
Terrestrial animals are most likely to be exposed to contaminants from soil, surface
water, or through the food chain. A chain-link fence surrounds the portion of the
site targeted for cleanup and should serve to exclude larger animals from on-site
contaminants. However, during site visits in late 1989, fencing had been vandalized
in two places, and numerous tracks indicated that not only did white-tailed deer
/Odocoileus columbianus^ have access to the site, but were using it on a regular
basis. Future site plans should address fence maintenance. The fence will not
exclude smaller animals. During a site visit, a clear game trail ran under the fence
and may have been used by rabbits (Svlvilaaus floridanusl opossums (Didelphis
marsupialis!. or similar-sized animals. Birds observed on or near SMWT are listed
in Appendix 4.
High levels of soil contaminants were found in the land treatment area (Figure 2).
Animals on-site may be exposed to soil contaminants, particularly those species
which live close to the ground, such as mice, shrews, and snakes. Fossorial
animals would be particularly vulnerable to this exposure route, and mole tunnels
were observed off-site near site 1.
19

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Terrestrial animals may also be exposed to contaminants from surface water and
the pond may attract water-oriented terrestrial animals. During one site visit, a
great blue heron (Ardea herodias^ was found dead in the pond. The bird had a
broken wing, and it is unclear whether contaminants in the pond contributed to its
death. [Advanced signs of PCP intoxication include spasms and tremors (Eisler
1989) but whether the levels found in the pond would induce these reactions in this
species to a degree which would cause broken bones is unknown]. Surface water
was also observed at the south end of the land treatment area. These large
puddles were likely a result of surface runoff from recent rainfall. Runoff from the
land treatment area may pick up contaminants from the soil.
Exposure may also occur through the food chain. Turkey vultures (Cathartes
aural, broad-winged hawks fButeo platypterusl. red-tailed hawks fButeo
famaicensisl and other unidentified hawks have been observed regularly on and
around SMWT. This route of exposure is less likely, as PAHs and PCP do not tend
to biomagnify through the food chain. Insectivorous species may be more likely to
be exposed through the food chain, as insects are less efficient than vertebrates at
metabolizing PAHs (Eisler 1987).
Aquatic routes of exposure
Aquatic animals may be exposed to waterborne contaminants through dermal
exposure, respiration (gills), or through the food chain. Rainwater runoff may
introduce contaminants into surface water, but the most constant source of
contaminants has been groundwater seepage. Exposure is likely to be chronic.
Contaminants from groundwater seepage have probably been entering Old Tom's
Run for years and are likely to continue until cleanup measures have been fully
implemented. Lipophilicity of PCP increases with lower pH (Eisler 1989). The low
pH of the streams surveyed may indicate an increased likelihood of
bioaccumulation.
Effects to stream ecosystems
The presence of frogs and the diversity and relatively high density of benthic
invertebrates indicate that negative effects of contaminants are somewhat limited.
Results from benthic invertebrate population analysis placed the upper reaches of
Old Tom's Run in the slightly to moderately impacted category. The impact was to
the pollution intolerant groups, the Ephemeroptera, Plecoptera, and Trichoptera.
The absence of mudminnows in the upstream portion of Old Tom's Run may have
been due to contaminants. However, fish were located just downstream of a small
waterfall (about one foot high) which may have limited the upstream movement of
mudminnows. If this obstacle is removed during cleanup activities, mudminnows
would be expected to eventually return to the upper portion of Old Tom's Run.
The EPT organisms were also absent from the east tributary. The east tributary
was about half the size of Old Tom's Run, and invertebrate populations may have
been more affected by intermittent stream flow. Groundwater on the eastern
20

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portion of the property was not found to be contaminated (Shapot 1988), and the
east tributary is fairly well buffered from on-site runoff. Contaminant levels in
sediment were relatively low, although ultraviolet screening for PAHs showed a few
hot spots.
The analysis of benthic invertebrate populations yielded results opposite those
expected. Conditions deteriorated further downstream, and site 4 was categorized
as severely impacted. These results are supported by previous toxicity testing.
Ambient water just upstream of the Morgan Road pond caused 20% mortality to
Ceriodaphnia while tests with water from five other sites upstream showed no
mortality. Several explanations could account for the results of biomonitoring data.
Decrease in downstream invertebrate population heafth may not have been related
to SMWT, but associated with intermittent flow, as the channel is braided in this
area. Contaminated sediment may have accumulated historically near the Morgan
Road pond, but analysis of sediment gave confusing results. Gas chromatographic
analysis of sediment did not detect contaminants in samples just above and below
the Morgan Road pond, but ultraviolet screening indicated relatively high levels of
PAHs at the pond outlet and further downstream. Alternately, benthic community
results at site 1 may have indicated healthier populations because it was located in
a stretch where stream conditions temporarily improved. Both chemical analysis
and toxicity testing support this theory. Sediment elutriate tests caused decreased
reproduction in Ceriodaphnia at all bioassay sites except the site closest to site 1.
Contaminant levels in sediment just downstream of site 1 were lower than both the
levels detected upstream, closer to the on-site pond, and downstream near the
confluence.
The apparent decrease in downstream invertebrate population health may have
been an artifact of site placement. The fish populations at sites 3 and 4 seemed to
be healthy. One may infer that the stream is impacted by SMWT based on
comparison between invertebrate populations of site 1 and the reference site;
however, specific trends in biota from three sites on Old Tom's Run are likely to be
influenced by variations in substrate and flow conditions.
Indications of contamination to Brooks Run and Mcintosh Run observed by
previous FWS biologists during June of 1986 were no longer apparent. Fish
populations upstream and downstream of the confluence with Old Tom's Run did
not indicate impacts from SMWT.
U.S. Fish and Wildlife aquatic trustee resources that might be affected by SMWT
contaminants are anadromous fish in Breton Bay and endangered dwarf wedge
mussels in lower Mcintosh Run. Contaminated water and sediment would be quite
diluted this far downstream of the site, and resources would most likely not be
affected. Migratory birds may be affected by terrestrial and aquatic exposure
routes, but further study would be required to determine whether an impact is
taking place.
21

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LITERATURE CITED
Acker, C.J., and D. Mitchell. 1988. Sigma-Scan: The scientific measurement
program. Version 3.90. Jandel Scientific, Corte Madera, CA.
Bode, R.W. 1988. Quality assurance work plan for biological stream monitoring in
New York State. New York State Department of Environmental
Conservation.
Eisler, R. 1986. JDioxin hazards to fish, wildlife, and invertebrates: a synoptic
review. U.S. Fish Wild). Serv. Biol. Rep. 85(1.8).
	. 1987. Polycyclic aromatic hydrocarbon hazards to fish, wildlife, and
invertebrates: a synoptic review. U.S. Fish Wildl. Serv. Biol. Rep.
85(1.11).
	. 1989. Pentachlorophenol hazards to fish, wildlife, and invertebrates:
a synoptic review. U.S. Fish Wildl. Serv. Biol. Rep. 85(1.17).
Finni, G.R. 1989. Southern Maryland Woodtreating Superfund site benthic
macroinvertebrate processing. Letter dated Feb. 7,1990. Dayton
OH.
Hilsenhoff, W.L. 1977. Use of arthropods to evaluate water quality of streams.
Technical Bulletin No. 100. Department of Natural Resources,
Madison, Wl.
	. 1988. Rapid field assessment of organic pollution with a family-level
biotic index. J. N. Am. Benthol. Soc. 7:65-68.
Hydrolab Corporation. 1985. Surveyor1" II operating manual (and performance
manual). Revision A. Austin, TX.
Plafkin, J.L, M.T. Barbour, K.D. Porter, S.K. Gross, and R.M. Hughes. 1989.
Rapid bioassessment protocols for use in streams and rivers: Benthic
macroinvertebrates and fish. U.S. Environmental Protection Agency,
Washington, D.C.
Shapot, R.M. 1988. Remedial investigation/feasibility study report for the Southern
Maryland Wood Treating Site, Hollywood, Maryland. Document No.
193-FSI-RT-GBKN. CDM Federal Programs Corporation, Fairfax, VA.
U.S. Environmental Protection Agency. 1986. Quality criteria for water, 1986. U.S.
No. EPA 440/5-86-001. Environmental Protection Agency Office of
Water Regulations and Standards, Washington D.C.
22

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Appendix 1. Activities and dates for eight sites sampled to detect effects of fish and
wildlife from Southern Maryland Wood Treating (SMWT) superfund
site, MD.
23

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Appendix 1.
Date	Site	Activity
October 25
Site 7
Hydrolab measurements
Electroshocking
Surber sampling

Site 8
Hydrolab measurements
Electroshocking
Surber sampling
October 26
Site 5
Hydrolab measurements
Electroshocking
Surber sampling

Site 6
Hydrolab measurements
Electroshocking
Surber sampling
October 27
Site 2
Hydrolab measurements
Electroshocking
Surber sampling

Site 1
Hydrolab measurements
Electroshocking
Surber sampling
November 17
Site 3
Hydrolab measurements
Surber sampling

Site 4
Hydrolab measurements
Surber sampling
November 20
SMWT
Wetland delineation
November 21
Site 3
Site 4
Site 6
Electroshocking
November 29
Site 7
Surber sampling

Sites 1-8
Physical conditions
data sheet
February 9
Between sites
Electroshocking
1990
1 and 3

March 12
SMWT
Wetland delineation
24

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Appendix 2. Physical characteristics/water quality data sheets for each of eight
sites used to assess effects of Southern Maryland Wood Treating
superfund site, Hollywood, MD on aquatic biota.
25

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PoSSt bl^ llrr^ac&d
*• FHYSICAL CHARACTERISTICS/WATER QUALITY DATA SHEET	,v^(v
J	j	 Moderate Heavy
Local watershed NFS pollution: evidence^ Potential Obvious
Estimated stream width i' -1 i^i
depth: Riffle rJ/V Run \c5	Pool
High water mark (above stream bank) '^"6o»bu- Velocity IU »\/^	
Dam present: yes	 no ;C_ Channelized: yes
Overstory percent canopy cover: 0-25% 25-50% 50-75%
Dominant species ik-cn. ToUu ~?cy\*r 		
Percent veg. w/in 2 m of water surface: ^6-5%j5-10% 10-20% 20-30% >303
DCBOinant species [V-iU . i/y\Uv*.t>jn Ate, i: h\*c2> mii tint* c{- 	
Percent instream cover: 0-5% c3rlS% 10-20% 20-30% >30%
Type of cover (logs, undercut banks) b»VA*u 	
SEDIMENT	:r
/ ~) |(w I
J
Sediment odors: Normal Sewage Petroleum Chemical1 Anaerobic None
Other
Sediment oils: ^&bsen£)Slight Moderate Profuse
Sediment deposits: Sludge Sawdust Paper fiber Sand Relict shells
Other iuiva-	
Are undersides of not deeply embedded stones black? yes	no V
Inorganic	SUBSTRATE COMPONENTS Organic
%	composition % composition
Bedrock	Detritus (sticks,	ICQ*?
Boulder (>256 mm)	leaves, coarse	°
Ccbble (64-256 mm)	organic matter)
Gravel (2-64 mm)	Muck (fine, black)
Sand (0.06-2 mm)	90'/- Marl (shell fragments)
Silt (0.004-0.06 mm)	Other	 ;	Hp**	I
Clay (<0.004 mm)			j
water CXJAUIY	profile.
Temp	 Dissolved 02	 pH	 Conductivity
Other	 Instrument (s)
Stream type: Coldwater	^
Hater odors: Normal Sewage Petroleum QjemicaiP Other	'
Turbidity i^glear^ Slightly turbid Turbid Opaque Oolor	
Fhotograpty number
Heather and other observations:
(Yki 40°? fi* i5cefc tfcJ	wind frtvW
4 W h*m i»	<**>
iV^Ui Cvrc	up it I ln C.J'Jive. )h£-Hr UkA	¦'"'k

-------
possibly Im^ackcf S\t
CJiARACIERISTICS/WATER QUALITY DMA SHEET
Site	«-t y.j'rl\s.st\ IvilJCJt"-v	5.A-C
Date i\),-\/ 1<-1 I1<(-1 Staff i>i»-
mm
Predominant land use: c.Pgresfi Field/Pasture Residential
Commercial Industrial Other	
local watershed erosion: <^one) hfcpderate Heavy
Local watershed NPS pollution: fNo evidence? Potential Obvious
Estimated stream width 0-6 »w.	£3	
depth: Riffle	Run r6c^- Pool
High water mark (above stream bank) n** v»i(o^ Velocity		
Dam present: yes	 no jL Channelized: yes if mat^nb -j^CTK
Overstory percent canopy cover: 0-25% 25-50% 50-75% ^5-100%)
Dominant species ? v/ew rtivt-.-s-ft- T«h A r>^!c*-	 	
Percent veg. w/in 2 m of water surface:'' 5-5% 5-10% <10-26%) 20-30% >30%
Dominant species A/u/Af	%	 v""— 	
Percent instream cover:5-10% 10-20% pQ-30%) >30%
iype of cover (logs, undercut banks) lAuUrc^f ^n/rz foh of ta c/ -
SEDIMENT
Sediment odors: (Normal) Sewage Petroleum Chemical Anaerobic None
Other. 	
Sediment oils: <&bsent-3 slight Moderate Profuse
Sediment deposits: Sludge Sawdust Paper fiber Sand Relict shells
Other	jOpv*-	;	
Are undersides of not deeply embedded stones black? yes	 po
Inorganic	SUBSTRATE OOMPOND7TS	Organic
% composition	% composition
Bedrock	Detritus (sticks,
Boulder (>256 mm)	leaves, coarse
Cobble (64-256 mm) c	organic matter)
Gravel (2-64 mm) 1'->'(c	Muck (fine, black)
Sand (0.06-2 mm)	Marl (shell fragments)
Silt (0.004-0.06 mm) &h	Other	
Clay (<0.004 mm)
WATER CUAI3TIY
Tenp	 Dissolved 02	 pH	 Conductivity
Other		 Instrument (s}_
Stream type: Colguater
Water odors: wgriiaVi Sewage Petroleum Chemical Other
Turbidity: Q3^arJ Slightly turbid Turbid Opaque Color
Photograph, number 5 (j>
Weather and <
fjpje
Weather and other observations:	, _ , _
27

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Po*sMj Wpqckd 5(W
51\eJb HffSICAL	quality data sheet
site DCf~) 7pM£ $UfO	&/- /&dd ad W)onr*rv\ fcM rcc&sioz
Date Upc: /f? Staff gcgyg.	J	J
HABITAT
Predominant land use: fftorest^ Field/Pasture Residential
Ccsnmercial Industrial Other 	
Local watershed erosion: CNone) Moderate Heavy	^ ^	\vv<
Local watershed NPS pollution: 30%
Dominant species iv^Krs7		
Percent instream cover: 0-5% $-10%J> 10-20% 20-30% >30%
Type of cover (logs, undercut banks) 	
aniuiacji
Sediment odors	Sewage Petroleum Chemical Anaerobic None
Sediment oils: jflpsegt^ Slight Moderate Profuse
Sediment deposits: Sludge Sawdust Paper fiber Sand Relict shells
Other i\Jcw-a—	
Are undersides of not deeply embedded stones black? yes	 no	
Inorganic	SUBSTRATE COMPONENTS	Organic
% composition	% composition
Bedrock	Detritus (sticks,	i0$c{o
Boulder (>256 mm)	leaves, coarse ,L>
Gobble (64-256 mm)	organic matter)
Gravel (2-64 mm)	Muck (fine, black)
Sand (0.06-2 mm)	f>c'lo Marl (shell fragments)
Silt (0.004-0.06 mm)	Other	
Clay (<0.004 mm)
WATER CCALJTY
Tenp	 Dissolved 02	 pH	 Conductivity	
Other		 Instrument^
Stream type:
Water odors: ftfonnajj Sewage Petroleum Chemical Other
Turbidity: Clear Slightly turbid Turbid Opaque Color
Photograph number
to
Weather and other observations:
28

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PcTiSl bu I Ivtfbc Krcl 5
Site
Date
^ » (JfflYSICAL CHARACTERISTICS/WATER QUALITY DATA SHEET
o"
Old Tern's Hur>- cidA/^sh^m fww Wc-nt(; of CVlorc;g/rVs Uonri ftro^C/Xr
IU10-20% 20-30% >30%
Dominant species ,-)Krub 5	
Percent instream cover: 30%
Type of cover (logs, undercut banks) Icjn	
SEDIMENT
Sediment odors: I^onail) Sewage Petroleum Chemical Anaerobic None
Other
lbP7o
Sediment oils: ^Absent? Slight Moderate . Profuse
Sediment deposits:^Sludge Sawdust Paper fiber Sand Relict shells
Other |Ocvi2-	
Are undersides of not deeply embedded stones black? yes	 no IS
Inorganic	SUBSTRATE CCMPONZNTS	Organic
% composition	% composition
Bedrock	Detritus (sticks,
Boulder (>256 mm)	leaves, ooarse
Cobble (64-256 mm)	organic matter)
Gravel (2-64 mm) 30	Muck (fine, black)
Sand (0.06-2 mm) lO	Marl (shell fragments)
Silt (0.004-0.06 mm)	Other	
Clay (<0.004 mm)
WATER QUALITY
Temp	 Dissolved 02	 pH	 Conductivity
Other	 Instrument (s)
Stream type: Ooldwater JWSgiwaterP . . .
Water odors: (formal ^Sewage Petroleum Chemical Other nfrfclWv
Turbidity: Clear~3Tiqhtly turbid Turbid Opaque Color	
Photograph number '£D.4-\, 	
Weather and other observations:
Afe r^-tYw-v 1b(j0 cj hcticv\\
\rcn bactena. J
29

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^L^Ort^OL Sik ^oj~	cioKjYiSfrtcurA cr^ OldlCvnS Ruw ooJ^eWncs.
HTCSICAL CHARACTERISTICS/WATER QUALTIY DATA SHEET
Site
Date
MmimimU Pw a hi*. CcnflvttnccL 4 Old'T &lw S7hb>+^
Local watershed erosion:	Moderate Heavy
Local watershed NPS pollution: /^tto evidenced Potential Obvious $cACf Crcl>SiO^ <-fS{rrc<
Estimated stream width 3 -V m
depth: Riffle klhV Run M//h Pool .2JIgiy> .
High water nark (above, stream bank) 	 Velocity 		
Dam present: yes k S 		 Channelized: yes	 no )xC
Overstory percent canopy cover: Q-25|> 25-50% 50-75% 75-100%
Dcsninant species \r30%
Dominant species fed	hc-sk?
Percent instream cover: 0-5% 5-10% clO-zP%> 20-30% >30%
Type of cover (logs, undercut banks) /q-< , Sfrl/	
SEDIMENT
Sediment odors: Normal Sewage Petroleum Chemical Anaerobic None
Sediment oils: (Absents slight Moderate Profuse
Sediment deposits: Sludge Sawdust Paper fiber Sand Relict shells
Other		
Are undersides of not deeply embedded stones black? yes	 no	
Inorganic	SUBSTRATE COMPONENTS	Organic
% composition	% composition

Bedrock	Detritus (sticks,
Boulder (>256 mm)	leaves, coarse
Cobble (64-256 mm)	organic matter)	> (7	
Weather and other observations:
Lcfc elf JAI/ i\zf Ho
30

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Possibt^ Im^Qckdi
» PHYSICAL CHARACTERISTICS/WATER QUALITY DftTA SHEET
Site fcHtf/Utt	f) Did 7^*0/*^-^- Svt-^ (o
Date I ifLs/Jr}	Staff 7fr/V/<	CA,U>h-*i.
nam present: yes	 no V Channelized: yes	no K.
Overstory percent canopy cover: 0-25% 25-50% (*"50-75%^ 75-100%
Dominant species T—	
Percent veg. w/in 2 m of: water surface: 0-5%f5-10f> 10-20% 20-30% >30%
Dominant species '-i.tr		
Percent instream cover: 0-5% CS-10%^ 10-20% 20-3(5% >30%
Type of cover (logs, undercut banks) />-< k'	*LS
SEDIMENT
Sediment odors CNorn?^ Sewage Petroleum Chemical Anaerobic None
Other 	
Sediment oils: CAHqgn-f) slight Moderate Profuse
Sediment deposits: sludge Sawdust Paper fiber CSanc£> Relict shells
Other 	
Are undersides of not deeply embedded stones black? yes	 no	
Inorganic	SUBSTRATE OQMPONENTS	Organic
% composition	% composition
Bedrock	Detritus (sticks,	yco
Boulder (>256 mm)	leaves, coarse
Cobble (64-256 mm) fr	organic matter)
Gravel (2-64 mm)	10	Muck (fine, black)
Sa«i (0.06-2 mm) J±£rk 50	Marl (shell fragments)
Silt (0.004-0.06 mm)(o%ao	Other	
Clay (<0.004 mm)
WftTFR WTOf
Itenp	 Dissolved 02	 pH	 Conductivity	
Other	 Instrument (s)
Stream type: Coldwater C3jannwateg>
VJater odors: <&ormaT) Sewage Petroleum Chemical Other
Turbidity: Qezp slightly turbid Turbid (^Qpaqug) Color J""- ~
Photograph, number /
31

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sdt (or UYwawcd
» PHYSICAL CHARftCIERISTICS/WftTER QUALITY DMA SHEET
Site Ou**dt rVulx. OuJ,i- 5ik7	
Date ///^T 7<"t7	Staff	K/l/C*r( c
habitat
Preckminant land use: C[For^t.J> Field/Pasture Residential
Caumercial Industrial Other	
Local watershed erosion: cTNohe Moderate Heavy
Local watershed NFS pollution: Cno evident Potential Obvious
Estimated stream width >'?m.
depth: Riffle td'A- Run /<\ca+~. Pool /J//b
High water nark (above stream bank)
Dam present: yes	 no j<
	 Velocity
Channelized: yes	no x
Overstory percent canopy cover: 0-25% 25-50% 50-75%05-100%^
Dominant species R ¦ ;v> <~r>U I'Hih t'v 	
Percent veg. w/in 2 m of water surface: 0-5% 5-10% 10-20% 20-30% >30%
Dominant species 'noify ,		
5-10% 10-20% 20-30% >30%
Percent instream cover: (0-5$?
lype of cover (logs, undercut banks)
SEDIMENT
Sediment odors: (No:
A
Or ¦
Sewage Petroleum Qiemical Anaerobic None
Sediment oils: 4&seQfc Slight Moderate Refuse
Sediment deposits: Sludge Sawdust Paper fiber (garsj) Relict shells
Other 	
Are undersides of not deeply embedded stones black? yes	
no
Inorganic
SUBSTRATE COMPONENTS
Bedrock
Boulder (>256 mm)
Oobble (64-256 ran) v
Gravel (2-64 ran) t.0 b
Sand (0.06-2 ran) JcZ,
Silt (0.004-0.06 mm)
day (<0.004 ran)
% oanposition
Organic
Detritus (sticks,
leaves, coarse
organic matter)
Muck (fine, black)
Marl (shell fragments)
Other
% composition
WATER CUAIJTY
Temp	
Dissolved 02
PH
Conductivity
Other
Instrument (s)
Stream type: Ooldwater Warrawater
Water odors: (frtorroab Sewage Petroleum Chemical Other
Turbidity: (Clea^> ^Slightly turbid Turbid Opaque Color
Photography number |0 /11
Weather and other observations:
c,/c*d$ j
32

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Old "TirnrVs
«- HtfSICAL CHARACTERISTICS/WATER QUALITY DMA SHEET
Site Laufti Cirv-Jt, Pc-U-
Date ivicvj 7&. ItM Staff Ht-Qioci*-e P*-ks Kn,(.kr
isssm	ccjn(y
Predominant land use: forest} Field/Pasture Residential
Canmgrcial Industrial Other	
local watershed erosion: ifonej Moderate Heavy
Local watershed NFS pollution: rfto" evidenced Potential Obvious
Estimated stream width 01' 1 ^ ,v
depth: Riffle	Run lO c**. Pool
High water nark (above stream bank) m	Velocity lO
Dam present: yes	no X	 Channelized: yes	no X
Overstory percent canopy covep: 0-25% 25-50% 50-75% <$5.-lodf)
Dominant species	rijcicu;W-> 4u(,-, ne-Jo^ -su 	
Percent veg. w/in 2 m of water surface: 6-5%' 5-10% (£0-20%) 20-30% >30%
Dominant species	bcw .ru.sncffa-	
Percent instream cover: 0-5% 5-10% 10-20% 20-30% >30%
Type of cover (logs, undercut banks) /c-s	
SEDIMENT
Sediment odors: (Normal Sewage Petroleum Chemical Anaerobic None
Other		
Sediment oils: ^Absent) Slight Moderate Profuse
Sediment deposits: "Sludge Sawdust Paper fiber Sand Relict shells
Other iacvj_	
Are undersides of not deeply embedded stones black? yes	 no	
Inorganic	SUBSTRATE COMPONENTS	Organic
% composition	% composition
Bedrock	Detritus (sticks,
Boulder (>256 mm)	leaves, coarse
Cobble (64-256 mm)	organic matter)
Gravel (2-64 mm) /£%	Muck (fine, black)
Sand (0.06-2 mm) 1	Marl (shell fragments)
Silt (0.004-0.06 mm)207c-	Other	
Clay (<0.004 mm)
WATER CUAUIY
Tenp	 Dissolved 02	 pH	 Conductivity	
Other	' Instrument(s)		
Stream type: Ooldwater <3

Water odors: (Normal^ Sewage Petroleum Chemical Other
Turbidity: CLeaf) Slightly turbid Turbid Opaque Color
Photograph, number "7
• «			a _j_i	
Weather and other observations:

33

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Appendix 3. Calculation of Hilsenhoff Family Biotic Index (FBI) for benthic
invertebrates collected at six sites to determine the effects of
contaminants from Southern Maryland Wood Treating superfund site,
Hollywood, MD.
34

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Appendix 3.
SITE 1
Tolerance
CLASS Order Family	Value N FBI x N
CRUSTACEA
Asellidae	10 5	50
Gammaridae	4 2	8
INSECTA
Ephemeroptera
Heptageniidae	4	0
Leptophlebiidae	2	0
Odonata
Calopterygidae	5	0
Aeshnidae	3	0
Cordulegastridae	3	0
Gomphidae	1	0
Plecoptera
Capniidae	1	0
Megaloptera
Sialidae	4	0
Corydalidae	0 5	0
Trichoptera
Hydropsychidae	4	0
Limnephilidae	4	0
Phryganeidae	4	0
Polycentropodidae	6	0
Diptera
MOLLUSCA
Sericostomatidae	3	0
Chironomidae	8	18	144
Simuliidae	6	0
Psychodidae	10	1	10
Tipulidae	3	14	42
Syrphidae	10	1	10
Tabanidae	6	8	48
Sphaeriidae	8	18
TOTAL	"55	320
FBI	5.82
N - number of organisms
35

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Appendix 3. (continued)
SITE 2
Tolerance
CLASS Order Family	Value N FBI x N
CRUSTACEA
Asellidae	10	0
Gammaridae	4 5	20
INSECTA
Ephemeroptera
Heptageniidae	4	0
Leptophlebiidae	2	0
Odonata
Calopterygidae	5	0
Aeshnidae	3	0
Cordulegastridae	3	0
Gomphidae	1	0
Plecoptera
Capniidae	1	0
Megaloptera
Sialidae	4 2	8
Corydalidae	0	0
Trichoptera
Hydropsychidae	4	0
Limnephilidae	4	0
Phryganeidae	4	0
Polycentropodidae	6	0
Diptera
MOLLUSCA
Sericostomatidae	3	0
Chironomidae	8	0
Simuliidae	6	0
Psychodidae	10	0
Tipulidae	3	13
Syrphidae	10	0
Tabanidae	6	16
Sphaeriidae	8	18
TOTAL	~l0	"45
FBI	4.5
N - number of organisms
36

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Appendix 3. (continued)
SITE 3
Tolerance
CLASS Order Family	Value N FBI x N
CRUSTACEA



Asellidae
10
9
90
Gammaridae
4
5
20
INSECTA



Ephemeroptera



Heptageniidae
4

0
Leptophlebiidae
2

0
Odonata



Calopterygidae
5

0
Aeshnidae
3

0
Cordulegastridae
3

0
Gomphidae
1

0
Plecoptera



Capniidae
1
3
3
Megaloptera



Sialidae
4

0
Corydalidae
0

0
Trichoptera



Hydropsychidae
4

0
Limnephilidae
4

0
Phryganeidae
4
1
4
Polycentropodidae
6

0
Sericostomatidae
3

0
Diptera



Chironomidae
8
3
24
Simuliidae
6

0
Psychodidae
10

0
Tipulidae
3

0
Syrphidae
10

0
Tabanidae
6

0
MOLLUSCA



Sphaeriidae
8
15
120
TOTAL

"36
261
FBI


7.25
N - number of organisms
37

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Appendix 3. (continued)
SITE 4




Tolerance


CLASS Order Family
Value
N
FBI x N
CRUSTACEA



Asellidae
10
36
360
Gammaridae
4
25
100
INSECTA



Ephemeroptera



Heptageniidae
4

0
Leptophlebiidae
2

0
Odonata



Calopterygidae
5

0
Aeshnidae
3

0
Cordulegastridae
3

0
Gomphidae
1

0
Plecoptera



Capniidae
1
1
1
Megaloptera



Sialidae
4

0
Corydalidae
0

0
Trichoptera



Hydropsychidae
4
1
4
Limnephilidae
4

0
Phryganeidae
4

0
Polycentropodidae
6

0
Sericostomatidae
3

0
Diptera



Chironomidae
8
6
48
Simuliidae
6

0
Psychodidae
10

0
Tipulidae
3
1
3
Syrphidae
10

0
Tabanidae
6

0
MOLLUSCA



Sphaeriidae
8
1
8
TOTAL

"7T
524
FBI


7.38
N - number of organisms
38

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Appendix 3. (continued)
SITE 7 (reference)
Tolerance
CLASS Order Family	Value N FBI x N
CRUSTACEA
Asellidae
Gammaridae
INSECTA
Ephemeroptera
Heptageniidae
Leptophlebiidae
Odonata
Calopterygidae
Aeshnidae
Cordulegastridae
Gomphidae
Plecoptera
Capniidae
Megaloptera
Sialidae
Corydalidae
Trichoptera
Hydropsychidae
Limnephilidae
Phryganeidae
Polycentropodidae
Sericostomatidae
Diptera
MOLLUSCA
Chironomidae
Simuliidae
Psychodidae
Tipulidae
Syrphidae
Tabanidae
Sphaeriidae
TOTAL
FBI
10
4
4
2
5
3
3
1
4
0
4
4
4
6
3
8
6
10
3
10
6
8
18
88
1
1
1
1
1
1
120
0
72
0
72
5
0
3
1
0
0
0
4
0
6
3
40
0
0
3
0
6
8
327
2.73
N - number of organisms
39

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Appendix 3. (continued)
SITE 8
Tolerance
CLASS Order Family	Value N FBI x N
CRUSTACEA
Asellidae	10 1	10
Gammaridae	4 5	20
INSECTA
Ephemeroptera
Heptageniidae	4	0
Leptophlebiidae	2	0
Odonata
Calopterygidae	5	0
Aeshnidae	3	0
Cordulegastridae	3 2	6
Gomphidae	1	0
Plecoptera
Capniidae	1	0
Megaloptera
Sialidae	4	0
Corydalidae	0	0
Trichoptera
Hydropsychidae	4	0
Limnephilidae	4	0
Phryganeidae	4	0
Polycentropodidae	6	0
Sericostomatidae	3	0
Diptera
MOLLUSCA
Chironomidae	8	4 32
Simuliidae	6	0
Psychodidae	10	0
Tipulidae	3	0
Syrphidae	10	0
Tabanidae	6	0
Sphaeriidae	8	0
TOTAL	"12	"68
FBI	5.67
N - number of organisms
40

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Appendix 4. Bird species observed on or nearby Southern Maryland Wood
Treating superfund site, Hollywood, MD.
41

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Appendix 4.
Turkey vulture
Red-tailed hawk
Broad-winged hawk
Great blue heron
American woodcock
Mourning dove
Yellow-billed cuckoo
Red-bellied woodpecker
Downy woodpecker
Northern flicker
Eastern wood pewee
Acadian flycatcher
Barn swallow
Blue jay
Fish crow
Carolina chickadee
Tufted titmouse
Carolina wren
Blue-gray gnatcatcher
American robin
Eastern bluebird
Northern mockingbird
Brown thrasher
White-eyed vireo
Red-eyed vireo
European starling
Northern Parula warbler
Ovenbird
Kentucky warbler
Louisiana waterthrush
Common yellowthroat
Hooded warbler
Yellow-breasted chat
Summer tanager
Indigo bunting
Field sparrow
Grasshopper sparrow
Song sparrow
Dark-eyed junco
Eastern meadowlark
Common grackle
American goldfinch
Cathartes aura
Buteo jamaicensis
Buteo platvpterus
Ardea herodias
Scolopax minor
Zenaida macroura
Coccvzus americanus
Melanerpes carolinus
Picoides pubescens
Colaptes auratus
Contopus virens
Empidonax virescens
Hirundo rustica
Cvanocitta cristata
Corvus ossifraaus
Parus carolinensis
Parus bicolor
Thryothorus ludovicianus
Polioptila caerulea
Turdus miaratorius
Sialia sialis
Mimus DQlvQlottos
Toxostoma rufum
Vireo griseus
Vireo olivaceus
Sturnus vulgaris
Parula americana
Seiurus aurocapillus
Oporornis formosus
Seiurus montacilla
Geothlvpis trichas
Wilsonia c'rtrina
Icteria virens
Piranga rubra
Passerina cvanea
Spizella pusilla
Ammodramus savannarum
Melospiza melodia
Junco hvemalis
Sturnella maona
Quiscalus auiscula
Carduelis tristis
42

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