United States
Environmental Protection
Agency
Great Lakes National Program Office
77 West Jackson Boulevard
Chicago, Illinois 60604
EPA-905-R-04-001
February 2004
&EPA Phase II Investigation of
Sediment Contamination
in White Lake
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PHASE II INVESTIGATION
OF SEDIMENT CONTAMINATION
IN WHITE LAKE
BY
Dr. Richard Rediske
Dr. Michael Chu
Dr. Don Uzarski
Jeff Auch
R. B. Annis Water Resources Institute
Grand Valley State University
740 W. Shoreline Dr.
Muskegon, MI 49441
Dr. Graham Peaslee
Chemistry Department
Hope College
35 E. 12th St.
Holland MI 49423
Dr. John Gabrosek
Department of Statistics
Grand Valley State University
1 Campus Drive
Allendale, MI 49401
GREAT LAKES NATIONAL PROGRAM OFFICE # GL975368-01-0
U. S. Environmental Protection Agency
PROJECT OFFICER:
Dr. Marc Tuchman
U. S. Environmental Protection Agency
Great Lakes National Program Office
77 West Jackson Blvd.
Chicago IL 60604-3590
February 2004
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ACKNOWLEDGEMENTS
This work was supported by grant #GL975368-01-0 from the Environmental Protection
Agency Great Lakes National Program Office (GLNPO) to the Annis Water Resources
Institute (AWRI) at Grand Valley State University.
Project Team
EPA Project Officer
Dr. Marc Tuchman USEPA GLNPO
Principal Scientists
Dr. Richard Rediske AWRI/GVSU Sediment Chemistry
Dr. Michael Chu AWRI/GVSU GIS
Dr. Don Uzarski AWRI/GVSU Aquatic Ecology
Jeff Audi AWRI/GVSU Benthic Macroinvertebrates
Dr. John Gabrosek GVSU Statistical Methods
Dr. Graham Peaslee Hope College Radiochemistry
Project technical assistance was provided by the following individuals at GVSU and U of M:
Trace Analytical
Trimatrix Laboratories
Eric Andrews
Betty Doyle
Gail Smythe
Al Steinman
Ship support was provided by the crew of the R/V Mudpuppy (USEPA) and Captain Joe.
Bonem
Disclaimer
The U.S. Environmental Protection Agency through its Great Lakes National Program Office
funded the project described here under Grant GL-975207 to Grand Valley State University.
It has not been subjected to Agency review and therefore does not necessarily reflect the
views of the Agency, and no official endorsement should be inferred.
Reference herein to any specific commercial products, process or service by trade name,
trademark, manufacturer or otherwise, does not necessarily constitute or imply its
endorsement, recommendation, or favoring by the United States Government. The views and
opinions of the authors expressed herein do not necessarily state or reflect those of the
United States Government, and shall not be used for advertising or product endorsement
purposes.
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TABLE OF CONTENTS
List Of Tables iii
List Of Figures vi
Executive Summary 1
1.0 Introduction 2
1.1 Summary of Anthropogenic Activities In White Lake 5
1.2 Project Objectives And Task Elements 7
1.3 Experimental Design 9
1.4 References 11
2.0 Sampling Locations 13
3.0 Methods 17
3.1 Sampling Methods 17
3.2 Chemical Analysis Methods For Sediment Analysis 18
3.3 Chemical Analysis Methods For Water Analysis 29
3.4 Sediment Toxicity 29
3.5 Benthic Macroinvertebrate Analysis 33
3.6 Radiometric Dating 33
3.7 Statistical Analysis 34
3.8 Contaminant Mapping 34
3.9 References 35
4.0 Results And Discussion 36
4.1 Sediment Chemistry Results 36
4.2 Stratigraphy and Radiodating Results 53
4.3 Toxicity Testing Results 63
4.4 Benthic Macroinvertebrate Results 73
4.5 Chromium Uptake by Aquatic Organisms 87
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4.6 The Environmental Fate and Significance of Chromium and PCBs in
White Lake 90
4.7 Sediment Quality Triad Assessment of Contaminated sediments in
White Lake 100
4.8 Summary and Conclusions 101
4.9 References 102
5.0 Recommendations 106
Appendices 107
Appendix A. Quality Assurance Review of the Project Data 108
Appendix B. Results Physical Analyses On White Lake Sediments, October 2000 115
Appendix C. Organic Analyses On White Lake Sediments, October 2000 120
Appendix D. Results Of Metals Analyses For White Lake Sediments, October
2000 128
Appendix E. Summary Of Chemical Measurements For The Toxicity Test With
Sediments From White Lake, October 2000 133
Appendix F. Summary Of Benthic Macroinvertebrate Results For White Lake,
October 2000 150
11
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LIST OF TABLES
Table 2.1 White Lake Core Sampling Stations 15
Table 2.2 White Lake Stratigraphy Sampling Stations 16
Table 2.3 White Lake PONAR Core Sampling Stations 16
Table 3.1 Sample Containers, Preservatives, And Holding Times 18
Table 3.2.1 Analytical Methods And Detection Limits 19
Table 3.2.2 Organic Parameters And Detection Limits 25
Table 3.2.3 Data Quality Objectives For Surrogate Standards 26
Table 3.2.4 Sediment Detection Limits for PCBs 27
Table 3.3.1 Analytical Methods And Detection Limits For Culture Water 29
Table 3.4.1 Test Conditions For Conducting A Ten Day Sediment Toxicity Test
WUhHyalellaazteca 31
Table 3.4.2 Recommended Test Conditions For Conducting A Ten Day Sediment
Toxicity Test With Chironomus tentans 32
Table 4.1.1 Results Of Sediment Grain Size Fractions, TOC, And Percent Solids
For White Lake Core Samples, October 2000 37
Table 4.1.2 Results Of Sediment Grain Size Fractions, TOC, And Percent Solids
For White Lake PONAR Samples, October 2000 38
Table 4.1.3 Results Of Sediment Metal Analyses For White Lake Core Samples
(mg/kg Dry Weight), October 2000 40
Table 4.1.4 Results Of Sediment Metal Analyses For White Lake PONAR
Samples (mg/kg Dry Weight), October 2000 41
Table 4.1.5 Results of Sediment PCB and Semivolatile Analyses for White Lake
Core Samples (mg/kg Dry Weight), October 2000 42
Table 4.1.6 Results of Sediment PCB and Semivolatile Analyses for White Lake
PONAR Samples (mg/kg Dry Weight), October 2000 43
Table 4.1.7 Spearman Rank Order Correlations for Chemical and Physical
Parameters For White Lake Sediments 52
Table 4.1.8 Concentration of Organic Chromium in White Lake Sediments 53
Table 4.2.1 Stratigraphy and Radiodating Results For Core WL-2S Collected
From White Lake, October 2001 54
Table 4.2.2 Stratigraphy and Radiodating Results For Core WL-7S Collected
From White Lake, October 2001 57
Table 4.2.3 Stratigraphy and Radiodating Results For Core WL-9S Collected
From White Lake, October 2001 59
in
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Table 4.2.4 Results of TCP and PIXE Analyses for Chromium in Core WL-9S
Collected From White Lake, October 2001 62
Table 4.2.5 Average and Corrected Data for Stratigraphy Cores (October 2001)
Compared to the Results of the Top Core Section From the
Investigative Survey (October 2000) for White Lake Sediments 62
Table 4.3.1.1 Summary Of Hyalella azteca Survival Data Obtained During The 10
Day Toxicity Test With White Lake Sediments 64
Table 4.3.1.2 Summary Of Dunnett's Test Analysis Of Hyalella azteca Survival
Data Obtained During The 10 Day Toxicity Test With White Lake
Sediments From Shallow Stations 65
Table 4.3.1.3 Summary Of Dunnett's Test Analysis OfHyalella azteca Survival
Data Obtained During The 10 Day Toxicity Test With White Lake
Sediments From Deep Stations 65
Table 4.3.2.1 Summary Of Chironomus tentans Survival Data Obtained During The
10 Day Toxicity Test With White Lake Sediments 67
Table 4.3.2.2 Summary Of Dunnett's Test Analysis Of Chironomus tentans Survival
Data Obtained During The 10 Day Toxicity Test With White Lake
Sediments From Shallow Stations 68
Table 4.3.2.3 Summary Of Dunnett's Test Analysis OfChironomus tentans Survival
Data Obtained During The 10 Day Toxicity Test With White Lake
Sediments From Deep Stations 68
Table 4.3.2.4 Summary Of Chironomus tentans Dry Weight Data Obtained During
The 10 Day Toxicity Test With White Lake Sediments 69
Table 4.3.2.5 Summary of Dunnett's Test Analysis of Chironomus tentans Growth
Data Obtained During The 10 Day Toxicity Test With White Lake
Sediments From Shallow Stations 70
Table 4.3.2.6 Summary of Dunnett's Test Analysis of Chironomus tentans Growth
Data Obtained During The 10 Day Toxicity Test With White Lake
Sediments From Deep Stations 70
Table 4.3.3.1 Summary of Results of Total Chromium, Organic Chromium, and
Amphipod Survival for White Lake Sediments 71
Table 4.4.1.1 Benthic Macroinvertebrate Distribution In White Lake (#/m2), October
2000. Mean Number Of Organisms And Standard Deviation Reported
For Each Station 74
Table 4.4.1.2 Mean Abundance (#/m2) And Relative Densities (%) of Major
Taxonomic Groups in White Lake, October 2000 77
Table 4.4.2.1 Summary of Diversity And Trophic Status Metrics for the Benthic
Macroinvertebrates in White Lake, October 2000 80
IV
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Table 4.4.2.2 Spearman Rank Order Correlations for Ecological, Chemical, and
Physical Parameters for White Lake 82
Table 4.4.3.1 Summary Statistics for the Analysis of Individual Benthic
Macroinvertebrate Samples from White Lake, October 2000 84
Table 4.5.1 Chromium Concentration in Macrophytes and Zebra Mussels in
Tannery Bay 87
Table 4.5.2 Chromium Concentration in Chironomids from Tannery Bay 88
Table 4.6.1 White Lake Chromium Data 90
Table 4.6.2 White Lake PCB Data 96
Table 4.7.1 Sediment Quality Assessment Matrix for White Lake Data, October
2000. Assessment Matrix from Chapman (1992) 100
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LIST OF FIGURES
Figure 1.1 White Lake 2
Figure 1.2 Areas Of Sediment Contamination Identified In White Lake 5
Figure 2.1 White Lake Core and PONAR Sampling Stations 14
Figure 4.1.1 Distribution of Arsenic in Core Samples Collected in Western White
Lake, October 2000 44
Figure 4.1.2 Distribution of Chromium in Core Samples Collected in Western
White Lake, October 2000 44
Figure 4.1.3 Distribution of Lead in Core Samples Collected in Western White
Lake, October 2000 45
Figure 4.1.4 Comparison of Arsenic Concentrations in PONAR Samples and Top
Core Sections Collected in White Lake, October 2000 45
Figure 4.1.5 Comparison of Chromium Concentrations in PONAR Samples and
Top Core Sections Collected in White Lake, October 2000 46
Figure 4.1.6 Comparison of Lead Concentrations in PONAR Samples and Top
Core Sections Collected in White Lake, October 2000 46
Figure 4.1.7 Distribution of Aroclor 1248 in Core Samples Collected in Western
White Lake, October 2000 48
Figure 4.1.8 Distribution of Chromium in PONAR Samples for White Lake,
October 2000 49
Figure 4.1.9 Bathymetric plot of White Lake 50
Figure 4.1.10 PCA Analysis of White Lake Physical and Chemical Data 51
Figure 4.2.1 Depth and Concentration Profiles for Chromium, Lead-210, and
Cesium-137 at Station WL-2S, White Lake, October 2001 55
Figure 4.2.2 Depth and Concentration Profiles for Chromium, Lead-210, and
Cesium-137 at Station WL-7S, White Lake, October 2001 58
Figure 4.2.3 Depth and Concentration Profiles for Chromium, Lead-210, and
Cesium-137 at Station WL-9S, White Lake, October 2001 60
Figure 4.3.3.1 Relationship Between Total Chromium and Amphipod Survival for
Tannery Bay Sediments 71
Figure 4.3.3.2 Relationship Between Organic Chromium and Amphipod Survival for
Tannery Bay Sediments 72
Figure 4.4.1.1 General Distribution Of Benthic Macroinvertebrates In White Lake,
October 2000 78
Figure 4.4.2.1 Summary Of Trophic Indices (Pollution Tolerance) For The Benthic
Macroinvertebrates In White Lake, October 2000 81
VI
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Figure 4.4.3.1 Canonical Correspondence Analysis of Benthic Macroinvertebrate
Taxa for White Lake, October 2000 83
Figure 4.4.4.1 Plot of CCA Dimension 1 (Macroinvertebrate Taxa) and Chromium
for White Lake Sediments, October 2000 86
Figure 4.5.1 Chromium Accumulation in Macrophytes and Zebra Mussels in
Tannery Bay 88
Figure 4.5.2 Chromium Accumulation in Chironomids from Tannery Bay 89
Figure 4.6.1 Chromium Sampling Points in White Lake 91
Figure 4.6.2 Chromium Sampling Points in the Vicinity of Tannery Bay 92
Figure 4.6.3 Chromium Concentration Contours for White Lake Surficial
Sediments 93
Figure 4.6.4 Generalized Circulation Pattern for White Lake 94
Figure 4.6.5 PCB Sampling Points in White Lake 97
Figure 4.6.6 PCB Concentration Contours in the Surficial Sediments in the Vicinity
of the Former Occidental/Hooker Chemical Discharge 98
Figure 4.6.7 PCB Concentration Contours in the Surficial Sediments in White Lake 99
vn
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Executive Summary
A Phase II investigation of the nature and extent of sediment contamination in White Lake
was performed. Sediment chemistry, solid-phase toxicity, and benthic macroinvertebrates
were examined at 21 locations. Since chromium was previously identified as the major
contaminant in the sediments, experiments were conducted to determine the accumulation of
the metal in zebra mussels, macrophytes, and chironomids. In addition, three core samples
were evaluated using radiodating and stratigraphy to assess sediment stability and
contaminant deposition. High levels of chromium were found to cover a majority of the lake
bottom and to extend 8 km from Tannery Bay. All locations sampled west of Tannery Bay
exceeded the Probable Effect Concentration (PEC). Most of the chromium was found in the
top 51 cm of the core samples. High concentrations of PCBs were found near the outfall of
the former Occidental/Hooker Chemical facility. These levels also exceeded PEC guidelines.
Sediment toxicity was observed in the east bay area and at the Occidental/Hooker Chemical
outfall. Toxicity near the Occidental/Hooker Chemical outfall was probably due to the
presence of PCBs. No obvious toxicant was present in the sediments from the east bay.
While no relationship was previously observed for total chromium and amphipod toxicity, a
significant correlation was found for the organically bound fraction and the metal. Elevated
levels of organic chromium were found in archived sediments from Tannery Bay. Benthic
macroinvertebrate communities throughout White Lake were found to be indicative of
organically enriched conditions. The locations in the east bay were significantly different
than reference sites, as indicated by a shift to chironomids that were predators and sprawlers.
Chironomid populations in the remainder of the lake were burrowers and detritivores. Higher
densities of nematodes and reduced tubificids populations were associated with the stations
with elevated chromium levels (> 400 mg/kg). The metal also was correlated with an
increase in the trophic status of chironomid populations. Chromium accumulation was
observed in chironomid populations throughout White Lake. In addition, macrophytes and
zebra mussels in Tannery Bay were observed to accumulate the metal in their tissue.
All of the stratigraphy cores showed uniform levels of chromium deposition in the top 10 -
15 cm. This pattern suggested that a constant source of chromium was present in White
Lake. A standard exponential decay pattern was absent in the lower sections of the cores,
indicating that historical changes in sedimentation were caused by episodic events. These
data coupled with chromium contour maps and the generalized circulation pattern of the lake
were used to elucidate the fate and transport of the metal. The proximity to the drowned
rivermouth currents at the Narrows and the wind induced resuspension in the bay provided
conditions that facilitated the advection and dispersion of a sediment plume 8 km from its
source. Higher concentrations of chromium were found in the three deep deposition basins
(300-500 mg/kg). In contrast, the PCBs discharged by the Occidental/Hooker Chemical
outfall remained within 100 m of the outfall pipe. The depth of the discharge (15 m) plus the
depositional nature of the discharge zone acted to confine the contaminants to a small area.
The removal of contaminated sediments in Tannery Bay and the Occidental/Hooker outfall
were completed by October 2003. Both remedial actions are essential for the recovery of
White Lake. Remediation at Tannery Bay removed the ongoing source of chromium
contamination while dredging the Occidental/Hooker outfall reduced the amount of
bioaccumulative compounds in the lake.
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1.0 Introduction
White Lake, Michigan is a 10.2 km2 (4,150 acres) drowned river mouth lake that is directly
connected to Lake Michigan by a navigation channel. The lake has a mean depth of 7.3 m
and an estimated volume of 7.6xl07 m3 (Freedman et al. 1979). Deep deposition zones are
located at Dowies Point (17 m) and Long Point (21 m). The lake is part of the White River
watershed, which has a drainage basin of 139,279 hectares (2,634 square miles). The White
River originates in Newaygo County and flows through a large marsh/estuary complex
before entering White Lake. A predominately western flow is maintained through the lake
resulting in a residence time of 56 days. Strong currents are often noted in the region called
the Narrows, where two peninsulas cause a restriction in the watercourse and produce
riverine flow conditions through the passage. White Lake functions as a significant fishery
and recreational area in this region of the Great Lakes and provides an important transition
zone between the open waters of Lake Michigan and the estuary/riverine environments
associated with the White River.
1 MILE
FIGURE 1.1 WHITE LAKE.
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White Lake has a long history of environmental issues related to water quality and the
discharge of toxic materials. The lake was impacted in the mid 1800s when saw mills were
constructed on the shoreline during the lumbering era. During this period, a large portion of
the littoral zone was filled with sawdust, wood chips, timber wastes, and bark. Large
deposits of lumbering waste can still be found today in the nearshore zone of White Lake.
The lumbering era was followed in the 1900s by an era of industrial expansion related to the
construction of specialty chemical production facilities and a leather tanning operation.
Tannery waste from Whitehall Leather was discharged directly into White Lake from 1890-
1973. Effluents from Hooker Chemical's (now Occidental Chemical) chloralkali and
pesticide production were discharged from the 1950-1986 (Evans 1992 and GLC 2000).
Chlorinated organic chemicals from DuPont and Muskegon Chemical (now Koch Chemical)
have also entered White Lake through groundwater and surface water discharges. As a result,
degraded conditions were observed in much of the lake, as well as high sediment
concentrations of heavy metals and pesticide related chemicals. Evans (1992) presented a
review of studies that described extensive areas of oxygen depletion, high quantities of
chromium in the sediments, thermal pollution, the discharge of industrial wastes with a high
oxygen demand from the tannery (sulfide and organic matter), tainted fish, frequent algal
blooms, and high nutrient concentrations. Generally, oligochaetes were the dominant benthic
taxa and macroinvertebrate species richness and diversity were low across the lake (Evans
1976). These factors indicated that eutrophic conditions were prevalent in 1972, especially,
the southeastern portion of the lake. The International Joint Commission designated White
Lake as an Area of Concern (AOC) because of severe environmental impairments related to
these discharges. The AOC boundary includes the lake and several small sub watersheds. In
1973, a state of the art wastewater treatment facility was constructed and the direct discharge
of waste effluents and partially treated municipal sewage to White Lake was eliminated. The
new facility was constructed near Silver Creek and utilized aeration, lagoon impoundment,
spray irrigation and land treatment to remove nutrients, heavy metals, and organic chemicals.
While the system was very effective in reducing the point source load of nutrients to White
Lake, nonpoint contributions from upstream sources increased after construction and a net
reduction in loading was not observed during 1974 and 1975 (Freedman et al. 1979).
Recent and historical studies have indicated extensive contamination of sediments in White
Lake. Elevated levels of chromium, lead, arsenic, and mercury were detected in the
northeastern section of the lake in 1982 during a U.S. Environmental Protection Agency
(U.S.EPA) funded study conducted by the West Michigan Shoreline Regional Development
Commission (WMSRDC 1982). This study also found evidence of heavy metal
contamination in several locations along the northwest shore. In a more recent study
conducted in the summer of 1994 by U.S.EPA/Michigan Department of Environmental
Quality (MDEQ), elevated concentrations of these metals were detected in an area of the
northeast shore of White Lake (Bolattino and Fox 1995). This area (Tannery Bay) was the
historical discharge point for tannery effluent from Whitehall Leather. The chromium levels
found in the sediments of this area (4,500 mg/kg) were some of the highest concentrations
reported from any site in the Great Lakes. In a recent investigation, Rediske et al. (1998)
determined the distribution of chromium in western White Lake and evaluated the toxicity
and stability of sediments in Tannery Bay. Key findings of the investigation were as follows:
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> Sediments in Tannery Bay were acutely toxic to amphipods and midges.
> Chromium concentrations in Tannery Bay ranged from 1000 mg/kg to 4,500 mg/kg.
No correlation was found between solid phase toxicity and total chromium
concentrations.
> The highest degree of toxicity was found in the bay located to the east of Tannery
Bay. Chromium levels were low (100 mg/kg - 200 mg/kg) at this location.
> Benthic macroinvertebrates in Tannery Bay and the east bay were lower in diversity
and contained more pollution tolerant organisms than an uncontaminated control
location.
> Profiles of 210Pb showed that mixing was occurring in the top 20 cm of sediment in
Tannery Bay.
> Chromium levels approaching 900 mg/kg were found 2.4 km (1.5 miles) down
gradient of the discharge point.
> High levels of PCBs (100 mg/kg) were detected in the sediments near the discharge
of the former Occidental Chemical facility (Dowies Point).
The extent of chromium and PCB contamination in western White Lake was not investigated
in the previous study. While we know that high levels of chromium are present in the near
surface zone in many areas of eastern White Lake, the toxicity of these sediments has not
been evaluated. In addition, contaminant sediment profiles, toxicity evaluations, and an
assessment of the macroinvertebrate community have not been performed in section of White
Lake from Dowies Point to the Lake Michigan channel. The presence of contaminated
sediments and ecological impairments in the eastern half of the lake coupled with westerly
flow of water through the lake underscore the importance of conducting a more
comprehensive assessment of the system.
This investigation expanded the historical data and addressed critical data gaps related to the
distribution of chlorinated hydrocarbons and heavy metals in the western half of White Lake
and the toxicity of sediments outside of Tannery Bay. The investigative sampling focused on
regions of sediment contamination in areas near the shoreline and in deeper deposition zones.
A series of 10 sediment cores and 20 PONAR samples were analyzed for heavy metals,
semivolatiles, PCBs, and physical characteristics. PONAR samples were analyzed for
benthic macroinvertebrates and sediment toxicity. Chromium levels in the benthic
macroinvertebrates were also examined. In addition, three cores from deposition zones were
dated using 210Pb and 137Cs. These cores were analyzed for chromium and radionuclides to
determine the depositional patterns and contaminant flux in the lake. The study protocol
followed the sediment quality triad approach (Canfield 1998) and focused on sediment
chemistry, sediment toxicity, and the status of the in situ benthic macroinvertebrate
community. The information from this investigation will be important in the determination
of areas that may require further delineation and the prioritization of remedial action and
habitat restoration activities. Additionally, these data will further our understanding of the
ecological significance of sediments that are mobile and subject to resuspension in drowned
river mouth systems.
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1.1 Summary Of Anthropogenic Activities In White Lake
Areas and sources of contained sediments were recently inventoried as part of the Remedial
Action Plan (RAP) update for White Lake (Rediske 2002). Locations and sources are shown
in Figure 1.2. Wastes discharged by Whitehall Leather from 1890-1973 have impacted
eastern White Lake. Wastewater and sludge from tanning operations based on a tree bark
process were discharged into the east bay and Tannery Bay from 1890 to 1945. The process
was changed to a chromium-based system in 1945 and wastewater containing heavy metals,
hide fragments, and animal hair was discharged directly into the bay. Arsenic and mercury
were added to the process as preservatives. In addition to heavy metals, the wastewater
contained high levels of organic nitrogen, biological oxygen demand (BOD), and sulfide.
Occidental
Chemical
Discharge
DuPont
Chemical
Groundwater
Plume
Tannery
Bay
Koch
Chemical
0.5 0 0.5 1 Miles
FIGURE 1.2 AREAS OF SEDIMENT CONTAMINATION IDENTIFIED IN WHITE LAKE
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Solid wastes, dredged materials from the lagoons, and process sludge were disposed in
landfill areas adjacent to the shore. Local residents frequently reported problems with the
erosion of the solid waste materials. Recent and historical studies have indicated extensive
contamination of sediments in this region of White Lake. High levels of chromium (4,000 -
60,000 mg/kg), mercury (1 -15 mg/kg), and arsenic (10 - 200 mg/kg) were reported
(Bolattino and Fox 1995, Rediske et al. 1998). The sediments were found to be subject to a
high degree of mixing in the bay and they also were toxic in laboratory bioassays. Internal
resuspension plus the presence of high surface zone chromium concentrations 2.4 km from
the discharge point suggested that the sediments were subject to transport by lake currents.
Based on this information, the U.S. Army Corps of Engineers and the Michigan Department
of Environmental Quality conducted a feasibility study and developed a remediation plan for
Tannery Bay that involved the removal of 85,000 cubic yards of contaminated sediment. The
dredging began in September 2002 and was completed in 2003. A contaminated
groundwater plume exists on site and is currently being treated. The treatment system will
have to remain in place to prevent future sediment contamination. A large amount of
contaminated soils is also present on site and needs to stabilized or removed to prevent future
sediment contamination by erosion and runoff.
The sediments in the bay area east of Tannery Bay were found to be contaminated with
chromium slightly above the Probable Effect Concentration (PEC) in 1997 (Rediske et al.
1998). This location is on the shoreline of the Whitehall Leather facility and is also in the
discharge zone of the former City of Whitehall wastewater treatment plant. Sediments were
found to be highly toxic in laboratory bioassays and the diversity and total number of benthic
macroinvertebrates were reduced. The toxicant in the sediments could not be identified. In
consideration of the high toxicity and the degree of impact to the benthic community, further
investigation and toxicity evaluations need to be performed in the east bay.
The Occidental Chemical facility discharge zone near Dowies Point received chemical
production wastes from chloralkali and pesticide intermediate production operations from
1954 to 1977. Levels of chromium and lead that exceeded PEC values were found in the
sediments at this location in previous investigations (West Michigan Shoreline Regional
Development Commission 1982, Evans 1976). Rediske et al. (1998) determined that the
deep water zone off Dowies Point functioned as a deposition area for contaminated
sediments that were transported from Tannery Bay. This determination was based on the
presence of high chromium concentrations and mats of animal hair in the surficial zone. A
core sample collected from the area revealed the presence of high levels of PCBs (> 100
mg/kg) and chlorinated pesticide byproducts at sediment depths of 1-3 ft. Further
investigations conducted by Earth Tech (2000) found a 30 x 100 m area that was
contaminated with PCBs above the PEC value. The area was localized in the former effluent
discharge zone and followed the prevailing lake currents to the west. The Earth Tech
investigation also revealed an elliptical 30 m zone that was devoid of benthic
macroinvertebrates. Because of the high level of PCBs present in the sediments and the
potential for bioaccumulation in the local fish
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populations, Occidental Chemical and the EPA have agreed to remove the contaminated
sediments by dredging. The removal operations were completed in the fall of 2003. A
groundwater treatment system is in place that prevents a plume of contaminants from
reaching White Lake. This system will remain in operation to protect the sediments after
remediation.
The E.I. DuPont Chemical groundwater discharge zone is located between Long Point and
the sand dunes on the Lake Michigan shore. The groundwater discharge is related to
infiltration of lime wastes that contain low levels of heavy metals, high pH levels, and
thiocyanate (EPA 2002). PCBs and chromium were detected at levels exceeding the PEC
guidelines during an investigation in 1981 (West Michigan Shoreline Regional Development
Commission 1982). These chemicals may have originated from Tannery Bay and/or Dowies
Point since they are not related to the groundwater plume.
The Muskegon/Koch Chemical facility is located near Mill Pond Creek. The Creek drains
into an impounded area, Mill Pond, and then discharges into White Lake on the southern
shore. The Muskegon/Koch Chemical facility operated from 1975-1986 and produced a
variety of specialty chemicals. The facility is a Superfund Site (EPA 2002) because the area
groundwater and soil are contaminated with chlorinated solvents and chlorinated ethers
(several compounds are classified as carcinogenic). As part of a consent agreement, a
groundwater treatment system was installed 1995 that intercepts contaminants and prevents
them from reaching Mill Pond Creek. The Creek passes through a residential area and there
is no information available on the presence of contaminated sediments. In consideration that
some of the groundwater contaminants are carcinogenic, a more detailed assessment of the
area is ranked with a high priority. Chlorinated ethers were not observed in the discharge
zone of Mill Pond Creek in White Lake (Rediske et al. 1998). Mill Pond Creek and the pond
were not investigated in this project.
Evans (1992) summarized historical water quality and biological data for White Lake. Prior
to the 1973 wastewater diversion, nuisance algal blooms, fish tainting problems, excessive
macrophyte growth, winter fish kills, and oxygen depletion in the hypolimnion were
common. Average sediment concentrations of total phosphorus and total nitrogen were
3,258 mg/kg and 7,180 mg/kg respectively. Benthic macroinvertebrate communities were
dominated by pollution tolerant oligochaetes and chironomids. While ambient water quality
improved significantly by the mid 1980s, the composition of the benthic community
remained similar due to persistent sediment contamination. The only area where pollution
intolerant organisms such as Hexagenia sp. were found was in the eastern section of White
Lake near the river mouth (Evans 1992, Rediske et al. 1998).
1.2 Project Objectives And Task Elements
The objective of this investigation is to conduct a Category II assessment of sediment
contamination in White Lake. Specific objectives and task elements are summarized below:
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• Determine the nature and extent of sediment contamination in western White Lake.
- A Phase II investigation was conducted to examine the nature and extent of sediment
contamination in western White Lake. Core samples were collected to provide a
historical perspective of sediment contamination. The investigation was directed at
known sources of contamination in the lake and provided expanded coverage in the
area of the old Occidental Chemical facility outfall and the DuPont lime pile
groundwater plume. Arsenic, barium, cadmium, chromium, copper, lead, nickel,
zinc, selenium, mercury, TOC, and grain size were analyzed in all core samples.
- Surface sediments were collected from western White Lake with a PONAR to provide
chemical data for the sediments used in the toxicity evaluations and for the analysis
of the benthic macroinvertebrate communities. The PONAR samples were analyzed
for the same parameters as the sediment cores in addition to PCBs and semivolatile
organics.
- Critical measurements were the concentration of arsenic, barium, cadmium,
chromium, copper, lead, nickel, zinc, selenium, mercury, PCBs, and semivolatile
organics in sediment samples. Non-critical measurements were total organic carbon,
and grain size.
• Evaluate the toxicity of sediments from sites in White Lake.
- Sediment toxicity evaluations were performed with Hyalella azteca and Chironomus
tentans.
- Toxicity measurements in White Lake sediments were evaluated and compared to
control locations. These measurements determined the presence and degree of
toxicity associated with sediments from White Lake.
- Critical measurements were the determination of lethality during the toxicity tests and
the monitoring of water quality indicators during exposure (ammonia, dissolved
oxygen, temperature, conductivity, pH, and alkalinity).
• Determine the abundance and diversity of benthic invertebrates in White Lake.
- Sediment samples were collected with a PONAR in White Lake
- The abundance and diversity of the benthic invertebrate communities were evaluated
and compared to control locations.
- Critical measurements included the abundance and species composition of benthic
macroinvertebrates.
• Determine the bioavailability of chromium in the sediments of eastern White Lake
- Sediment samples were collected with a PONAR in White Lake
- Benthic macroinvertebrates were removed from the sediment and analyzed for total
chromium.
- The sediment was analyzed for total and organic chromium.
- Critical measurements were the determination of total and organic chromium.
-------
• Determine the uptake of chromium by aquatic macrophytes and zebra mussels (Dreissena
polymorpha) in Tannery Bay.
- Benthic samples containing zebra mussels and macrophytes were collected from
Tannery bay and a control location near the mouth of the White River.
- Zebra mussels and macrophytes were removed from the sediment and washed
thoroughly with lake water.
-Critical measurements included the analysis of chromium in sediment and plant, and
zebra mussel tissue.
• Determine the depositional history and stability of selected sediments in White Lake.
- Sediment samples were collected with a piston core in White Lake.
- The profiles of radioisotopes and chromium were determined in the sediment cores.
- Critical measurements include the concentrations of total chromium and the
radioisotopes (210Pb, 214Bi, and 137Cs).
1.3 Experimental Design
This investigation was designed to examine specific sites of possible contamination as well
as provide an overall assessment of the nature and extent of sediment contamination in White
Lake. This bifurcated approach allowed the investigation to focus on specific sites based on
historical information in addition to examining the broad-scale distribution of contamination.
To determine the nature and extent of sediment contamination in western White Lake, 11
core samples were collected from locations that have been impacted by anthropogenic
activity. Four cores were taken from deep depositional zones near Dowies Point, Long
Point, Sylvan Beach, and Indian Bay. Seven additional cores were collected from shallow
areas along the south shore (2), down gradient from Occidental Chemical (3), and the
DuPont ground water plume (2). These core samples were analyzed for heavy metals
(arsenic, barium, cadmium, chromium, copper, lead, selenium, and mercury), semivolatile
organics, PCBs, and physical characteristics (grain size distribution, TOC, and percent
solids). PONAR samples were collected at the same locations. An additional group of 10
PONARs were collected in areas of eastern White Lake. Two PONARs were collected from
the cove area between Whitehall Leather and the White Lake Marina. This location had the
highest level of amphipod toxicity in the NOAA/GVSU investigation (Rediske et al., 1998).
Eight additional PONAR samples were collected from control sites (4) and locations outside
of the Tannery Bay remediation area (4). The latter locations corresponded to Stations E-5,
E-6, E-7, and E-9 in the Rediske et al. (1998) report. High levels of chromium were found in
the near surface zone sediments at these locations. While we know that chromium
contaminated sediments were exported from Tannery Bay, information on their toxicity was
unknown. PONAR samples were analyzed for the same parameters as the cores plus
sediment toxicity and organic chromium (Walsh and O'Holloran, 1996). Organic chromium
complexes have been identified in sediments contaminated with tannery wastes and may
exhibit a higher toxicity than inorganic chromium. Two sets of benthic macroinvertebrate
-------
samples were also collected at the PONAR sites. One set was analyzed for
macroinvertebrate community composition and the second was analyzed for total chromium
to assess the potential for bioaccumulation. A final series of four PONAR samples was used
to evaluate the uptake of chromium by zebra mussels and aquatic macrophytes in Tannery
Bay. Plant material and zebra mussels were removed from the PONAR and washed on site
with lake water to remove attached sediment. Three locations in Tannery Bay and one
location at the control site were examined. Sediment and tissue samples from the aquatic
macrophytes and zebra mussels were lyophilized and analyzed for total chromium. A
complete listing of locations and sample types is provided in Section 2.0
The final location of the core and PONAR samples was determined in cooperation with the
MDEQ and USEPA. Core samples at the above locations were collected by VibraCore
techniques using the R/V Mudpuppy. This part of the project provided both historical and
current information related to the nature and extent of sediment contamination in White
Lake. The benthic macroinvertebrate and toxicity evaluations were used to support this
information and for the evaluation of ecological effects and the prioritization areas for
remediation. Analytical methods were performed according to the protocols described in
SW-846 3rd edition (EPA 1999a). Chemistry data were then supplemented by laboratory
toxicity studies that utilized standardized exposure regimes to evaluate the effects of
contaminated sediment on test organisms. Standard EPA methods (1999b) using Chironomus
tentans and Hyalella azteca were used to determine the acute toxicity of sediments from the
PONAR samples.
In addition to the above scope of work, an investigation of sediment deposition and stability
was conducted using radiodating and detailed stratigraphy. Radiodating profiles were used
to define annual deposition rates and directly reflect sediment stability (Appleby et al. 1983,
Schelske et al. 1994). In consideration of the effluent diversions that occurred in the early
1970s, heavy metal flux into White Lake has changed dramatically over the last 25 years. If
the sediments are stable and not subject to resuspension, lower levels of heavy metals should
be encountered in the surface strata. To help assess the stability and deposition of sediments
in White Lake, two box cores from deep deposition zones and one piston core from a near
shore location were collected and dated using 210Pb and 137Cs. Each core was analyzed for a
target list of heavy metals at 2 cm intervals in order to develop a detailed stratigraphic
profile. Radionuclide and heavy metal profiles in the near shore areas were used to
determine if the sediments are stable or mixed by wave action. Data from the deeper cores
were used to assess the mobility of sediments in the lake. If the near shore sediments were
subject to mixing, contaminated materials from historic discharges may be moved to the
surface and result in a long term impairment of ecological conditions. These data along with
the biological and toxicological studies discussed above will provide a technically sound
basis for the development of remediation alternatives and restoration plans for White Lake.
This project will also provide information on the fate and transport of contaminated
sediments in drowned river mouth systems.
10
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1.4 References
210
Appleby, P. G. and F. Oldfield. 1983. The assessment of Pb data from sites with varying
sediment accumulation rates. Hydrobiologia 103: 29-35.
Bolattino, C. and R. Fox. 1995. White Lake Area of Concern: 1994 sediment assessment.
EPA Technical Report. Great Lakes National Program Office, Chicago.
Canfield, T. J., E.L Brunson, and FJ Dwyer, 1998. Assessing sediments from upper
Mississippi River navigational pools using a benthic invertebrate community
evaluation and the sediment quality triad approach. Arch. Environ. Contain. Toxico.
35 (2):202-212.
Earth Tech 2000. Corrective Measures Study for White Lake Sediment near Dowies Point
for the Former Occidental Chemical Corporation Site Montague, Michigan.
Submitted to the U.S. Environmental Protection Agency. Region V, Chicago,
Illinois.
EPA 1995. White Lake Area of Concern: Division Street Outfall, 1994 sediment assessment.
EPA Technical Report. Great Lakes National Program Office, Chicago. 48 pp.
EPA 1999a. Test Methods for Evaluating Solid Waste Physical/Chemical Methods. U.S.
Environmental Protection Agency. SW-846, 3rd Edition.
EPA 1999b. Methods for Measuring the Toxicity and Bioaccumulation of Sediment-
Associated Contami
EPA/600/R-99/064.
Associated Contaminants with Freshwater Invertebrates. 2nd Edition. EPA Publication
EPA 2002. National Priority Fact Sheets for Michigan. U.S. Environmental Protection
Agency. Region V Superfund Division. Chicago, Illinois. 45 pp.
Evans, E. 1976. Final report of the Michigan Bureau of Water Management's investigation of
the sediments and benthic communities of Mona, Muskegon, and White Lakes,
Muskegon County, Michigan, 1972.
Evans, E.D. 1992. Mona, White, and White Lakes in White County, Michigan The 1950s to
the 1980s. Michigan Department of Natural Resources. MI/DNR/SWQ-92/261.
91pp.
GLC. 2000. Assessment of the Lake Michigan monitoring inventory: A report on the Lake
Michigan tributary monitoring project. Great Lakes Commission, Ann Arbor, MI
Rediske, R., G. Fahnensteil, T. Nalepa, P. Meier, and C. Schelske 1998. Preliminary
Investigation of the Extent and Effects of Sediment Contamination in White Lake,
Michigan. EPA-905-R-98-004.
11
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Rediske, R., 2002. White Lake Area of Concern Contaminated Sediment Update. Remedial
Action Plan Update for the White Lake Area of Concern. 34 pp.
Schelske, C. L., A., Peplow, M. Brenner, and C. N. Spencer. 1994. Low-background
gamma counting: Applications for 210Pb dating of sediments. J. Paleolim. 10:115-
128.
Walsh, A.R. and O'Halloran, J. 1996. Chromium speciation in tannery effluent - II.
Speciation in the effluent and in a receiving estuary. Water Res. 30(10):2401-2412.
West Michigan Shoreline Regional Development Commission. 1982. The White County
Surface Water Toxics Study. Toxicity Survey General Summary. 153 pp.
12
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2.0 Sampling Locations
Sampling locations for the assessment of contaminated sediments in White Lake were
selected based on proximity to potential point and nonpoint sources of contamination. The
locations of these sites were determined by review of historical records. Sediment samples
were collected in areas of fine sediment deposition. Samples from areas containing rubble
and sand were excluded. A total of 10 locations were selected for the collection of core
samples and 24 locations were selected for PONAR samples. The sampling locations are
listed below and displayed on Figure 2.1. GPS coordinates, depths, and visual descriptions
are included in Tables 2.1, 2.2, and 2.3 respectively, for sediment core, stratigraphy core, and
PONAR samples.
Core and PONAR Identification
WL-1 andWL-2
WL-3, WL-4, WL-10, WL-1 3
WL-5, WL-7,
WL-6, WL-8, WL-9, WL-1 3, WL-21
WL-11, WL-12, WL-14, WL-15
WL-22, WL-23, WL-24
WL-1 6 and WL-1 7
WL-18, WL-19, WL-20
Description
DuPont Groundwater Plume
Western White Lake Deposition Basin
Long Point Deposition Basin
Occidental Chemical Outfall Area
Central White Lake Deposition Basin
Tannery Bay
East Bay
Control Locations
13
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WL-23
Figure 2.1 White Lake Core and PONAR Sampling Stations. (PONARs collected at
all stations. Cores collected at stations WL-1 - WL-10 and WL-21.)
14
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TABLE 2.1 WHITE LAKE CORE SAMPLING STATIONS.
Station
WL-1
WL-1 Duplicate
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-21
Sample ID
White Lake 1 Top
White Lake 1 Middle
White Lake 1 Bottom
White Lake ID Top
White Lake ID Middle
White Lake ID Bottom
White Lake 2 Top
White Lake 2 Middle
White Lake 2 Bottom
White Lake 3 Top
White Lake 3 Middle
White Lake 3 Bottom
White Lake 4 Top
White Lake 4 Bottom
White Lake 5 Top
White Lake 5 Middle
White Lake 5 Bottom
White Lake 6 Top
White Lake 6 Middle
White Lake 6 Bottom
White Lake 7 Top
White Lake 7 Middle
White Lake 7 Bottom
White Lake 8 Top
White Lake 8 Middle
White Lake 8 Bottom
White Lake 9 Top
White Lake 9 Middle
White Lake 9 Bottom
White Lake 10 Top
White Lake 10 Middle
White Lake 1 0 Bottom
White Lake 21 Top
White Lake 21 Middle
White Lake 21 Bottom
Date
10/24/2000
10/24/2000
10/24/2000
10/24/2000
10/23/2000
10/23/2000
10/24/2000
10/23/2000
10/23/2000
10/23/2000
10/23/2000
10/24/2000
Depth to Core
m
15.0
14.9
20.3
16.5
14.4
11.9
21.5
10.8
12.32
9.73
14.35
15.11
Depth of Core
cm
183
0-51
51-102
102-152
191
0-51
51-102
102-152
229
0-51
51-102
102-152
188
0-51
51-102
102-152
120
0-51
51-102
201
0-51
51-102
102-152
191
0-51
51-102
102-152
147
0-51
51-102
102-152
185
0-51
51-102
102-152
170
0-51
51-102
102-152
196
0-51
51-102
102-152
155
0-51
51-102
102-152
Latitude
N
43° 22.58'
43° 22.58'
43° 22.46'
43° 22.41'
43° 22. 27
43° 22. 73'
43° 22. 95'
43° 22. 60'
43° 23. 01'
43° 23. 27
43° 22. 18'
43° 23. 16'
Longitude
W
86° 24.56'
86° 24.56'
86° 24. 16'
86° 24.81'
86° 24. 16'
86° 23. 50'
86° 22. 88'
86° 23. 28'
86° 22. 53'
86° 22.44'
86° 24.61'
86° 22. 57
Description
Black silt
Black silt
Brown clay
Black silt
Black silt
Brown Black silt
Black silt
Black silt
Black sand to Beach sand
Black silt
Black silt
Brown silt
Sand Black Silt with Hydrocarbon odor
Sandy Black silt
Fine Black silt
Black silt
Brown silt
Black silt with clay
Black silt
Grey clay
Black silt
Black silt
Brown silt plastic
Fine Black silt no odor
Black silt Brown clay
Black silt Brown clay
Fine Black silt
Fine Black silt
Brown peat plastic
Fine Black silt
Fine Black silt
Fine Black silt
Red, Yellow, Black chemical odor
Black silt no odor
Black silt no odor
15
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TABLE 2.2 WHITE LAKE STRATIGRAPHY SAMPLING STATIONS
Station
WL-2S
WL-7S
WL-9S
Date
10/25/00
10/25/00
10/25/00
Depth to
Sediment
M
20.32
21.46
15.11
Latitude
N
43° 22.45'
43° 22.61'
43° 23. 27'
Longitude
W
86° 24. 15'
86° 23. 27'
86° 22.43'
TABLE 2.3 WHITE LAKE PONAR CORE SAMPLING STATIONS
Station
WL-l-P
WL-2-P
WL-3-P
WL-4-P
WL-5-P
WL-6-P
WL-7-P
WL-8-P
WL-9-P
WL-10-P
WL-ll-P
WL-12-P
WL-13-P
WL-14-P
WL-15-P
WL-16-P
WL-17-P
WL-18-P
WL-19-P
WL-20-P
WL-21-P
WL-22-P
WL-23-P
WL-24-P
Date
10/25/00
10/25/00
10/25/00
10/25/00
10/26/00
10/26/00
10/26/00
10/26/00
10/27/00
10/27/00
10/27/00
10/27/00
10/27/00
10/27/00
10/27/00
10/24/00
10/24/00
10/24/00
10/24/00
10/24/00
10/27/00
10/27/00
10/27/00
10/27/00
Depth to Sediment
m
15.04
20.32
16.54
14.35
11.89
21.46
10.85
12.32
9.73
14.35
14.30
16.15
10.90
8.76
8.48
3.43
4.14
3.18
3.78
2.74
15.11
3.66
2.44
3.20
Latitude
N
43° 22.58'
43° 22.45'
43° 22. 41'
43° 22.27'
43° 22.73'
43° 22.95'
43° 22.61'
43° 23.01'
43° 23 .27'
43° 22. 18'
43° 23. 54'
43° 23. 62'
43° 23. 08'
43° 23. 69'
43° 23. 87'
43° 24. 16'
43° 24.20'
43° 24.39'
43° 24.32'
43° 24. 51'
43° 23. 15'
43° 23. 99'
43° 24.02'
43° 24.02'
Longitude
W
86° 24. 5 5'
86° 24. 15'
86° 24.77'
86° 24. 16'
86° 23. 50'
86° 22.86'
86° 23 .27'
86° 22. 53'
86° 22.43'
86° 24.61'
86° 22.25'
86° 21. 97'
86° 22.33'
86° 21. 63'
86° 21. 83'
86° 21. 15'
86° 21. 25'
86° 21. 26'
86° 21. 14'
86° 21. 22'
86° 22.57'
86° 21. 28'
86° 21. 26'
86° 21. 30'
Description
Fine Black silt
Fine Black silt
Fine Black silt
Sand Black Silt with Hydrocarbon odor
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
Fine Black silt
16
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3.0 Methods
3.1 Sampling Methods
Sediment and benthos samples were collected using the U.S. EPA Research Vessel
Mudpuppy. VibraCore methods were used to collect sediment cores for chemical analysis.
A 4-inch aluminum core tube with a butyrate liner was used for collection. A new core tube
and liner were used at each location. The core samples were measured and sectioned into
three equal segments corresponding to top, middle, and bottom. Each section was then
homogenized in a polyethylene pan and split into sub-samples. The visual appearance of
each segment was recorded along with the water depth and core depth.
PONAR samples were collected for toxicity testing, sediment chemistry, and benthic
macroinvertebrates. For sediment chemistry and toxicity testing, a standard PONAR sample
was deposited into a polyethylene pan and split into sub-samples. The PONAR was washed
with water in between stations. A petite PONAR was used for the collection of benthic
macroinvertebrates. Three replicate grabs were taken at each of the sites and treated as
discrete samples. All material in the grab was washed through a Nitex screen with 500 |j,m
openings and the residue preserved in buffered formalin containing rose bengal stain.
GPS system coordinates were used to record the position of the sampling locations. Since
the core and PONAR samples were collected on different days, some variation in the location
may have occurred.
3.1.2 Sample Containers, Preservatives, And Volume Requirements
Requirements for sample volumes, containers, and holding times are listed in Table 3.1.
All sample containers for sediment chemistry and toxicity testing were purchased,
precleaned, and certified as Level II by I-CHEM Inc.
17
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TABLE 3.1 SAMPLE CONTAINERS, PRESERVATIVES, AND HOLDING TIMES
Hold Times
Matrix Parameter
Sediment
Sediment
Sediment
Sediment
Sediment
Water
Culture
Water
Metals
TOC
Semi-Volatile
Organic s
Grain Size
Toxicity
Semi-Volatile
Organics and
Resin Acids
Alkalinity
Ammonia
Hardness
Conductivity
pH
Container Preservation Extraction Analysis
250 mL Wide Cool to 4°C — ^ months,
Mouth Plastic Mercury-28
Days
250 mL Wide Freeze -10°C
Mouth Plastic
500 mL Amber
Glass
Cool to 4°C 14 daYs
1 Quart Zip-Lock Cool to 4°C
Plastic Bag
4 liter Wide Mouth Cool to 4°C
Glass
1000 mL Amber Cool to 4°C 14 days
Glass
250 mL Wide
Mouth Plastic
250 mL Wide
Mouth Plastic
Cool to 4°C
Cool to 4°C
6 months
40 days
6 months
45 days
40 days
24 hrs.
24 hrs.
3.2 Chemical Analysis Methods For Sediment Analysis
A summary of analytical methods and detection limits is provided in Table 3.2.1. Instrument
conditions and a summary of quality assurance procedures are provided in the following
sections.
18
-------
TABLE 3.2.1 ANALYTICAL METHODS AND DETECTION LIMITS
Parameter
Arsenic, Lead,
Selenium, Cadmium
SEDIMENT MATRIX
Method Description
Arsenic-Graphite Furnace
Analytical
Method
70601
3 0511 Digest! on
Barium, Chromium, Inductively Coupled Plasma 60101,
Copper, Nickel, Zinc Atomic Emission Spectroscopy 30521 Digestion
Mercury
Grain Size
Mercury Analysis of Soils, 7471 \ Prep
Sludges and Wastes by Manual Method in 7471l
Cold Vapor Technique
Wet Sieve
Total Organic Carbon Combustion/IR
WRI Method
PHY-010
90601
USEPA
Semivolatiles
Solvent Extraction and GC/MS 82701,
analysis 35501 Extraction
Detection
Limit
0.10 mg/kg
2.0 mg/kg
0.10 mg/kg
1%
0.1%
Table 3.2.2
1 - SW846 3rd. Ed. EPA 1994.
3.2.1 Sample Preparation For Metals Analysis
For aluminum, arsenic, barium, calcium, cadmium, chromium, copper, iron, magnesium,
manganese, nickel, lead, selenium, and zinc analysis, sediment samples were digested
according to a modified version of EPA SW-846 method 3052 "Microwave Assisted Acid
Digestion of Sediments, Sludges, Soils and Oils". Samples were air-dried prior to digestion.
A Questron (Mercerville, NJ) Q-4000 microwave system was used. The system provided a
controlled temperature and pressure in each digestion vessel. Approximately 0.25 g of
sediment was weighed into a Teflon liner. 4 mL Type 1 deionized water, 3 mL of
concentrated nitric acid, 6 mL of concentrated hydrochloric acid, and 4 mL of hydrofluoric
acid were added to each sample. Vessels were then capped and placed into the microwave
cavity. The program was set to raise the temperature inside the vessels to 200°C for 20.0
minutes. After completion of the run, vessels were cooled and vented. Then 15 mL of
saturated boric acid was added to each sample in place of hydrogen peroxide. The vessels
were recapped and placed into the microwave cavity. The program was set to raise the
temperature inside the vessels to 180°C for 15.0 minutes. After completion of the second
run, the vessels were cooled and vented. The contents were transferred into 50 mL
19
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centrifuge tubes and brought up to 50 mL with Type I deionized water. Samples were
centrifuged for 5 minutes at 3000 rpm before analysis. For every batch of 20 samples at least
one set of the following quality control samples was prepared:
Method Blank (4 mL of Type 1 deionized water, 3 mL of nitric acid and 6 mL of
hydrochloric acid);
Laboratory Control Spike (Blank Spike);
Matrix Spike;
Matrix Spike Duplicate.
For determining total mercury the samples were prepared by EPA SW-846 method 7471 A,
"Mercury in Solid and Semisolid Waste". Approximately 0.2 g of wet sediment was
weighed into a 50 mL centrifuge tube. 2.5 mL of Type I deionized water and 2.5 mL of aqua
regia were then added to the tube. Samples were heated in a water bath at 95°C for 2
minutes. After cooling, the volume of the samples was brought up to 30 mL with Type I
deionized water. Then 7.5 mL of 5% potassium permanganate solution was added to each
sample, the samples were mixed, and the centrifuge tubes were returned to the water bath for
a period of 30 minutes. Three mL of 12% hydroxylamine chloride solution was added to
each sample after cooling. Finally, the samples were mixed and centrifuged for 5 minutes at
3,000 rpm. Calibration standards were digested concurrent with the samples. Quality
control samples were prepared as stated previously for every batch of 10 samples or less.
3.2.2 Arsenic Analysis By Furnace
Arsenic was analyzed in accordance with the EPA SW-846 method 7060A utilizing the
Graphite Furnace technique. The instrument employed was a Perkin Elmer 4110ZL atomic
absorption spectrophotometer. An arsenic EDL Lamp was used as a light source at a
wavelength of 193.7 nm. The instrument utilized a Zeeman background correction that
reduces the non-specific absorption caused by some matrix components. The temperature
program is summarized below:
Step
1
2
O
4
5
Temp,
°C
110
130
1300
2100
2500
Time, sec.
Ramp
1
15
10
0
1
Hold
35
37
20
5
3
Gas Flow,
mL/min
250
250
250
0
250
Read
X
A Pd/Mg modifier was used to stabilize As during the pyrolysis step. The calibration curve
was constructed from four standards and a blank. Validity of calibration was verified with a
check standard prepared from a secondary source. This action was taken immediately after
calibration, after every 20 samples, and at the end of each run. At least 1 post-digestion
spike was performed for every analytical batch of 20 samples.
20
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3.2.3 Cadmium Analysis By Furnace
Cadmium was analyzed in accordance with the EPA SW-846 method 7060A utilizing the
Graphite Furnace technique. The instrument employed was a Perkin Elmer 4110ZL atomic
absorption spectrophotometer. A hollow cathode lamp was used as a light source at a
wavelength of 228.8 nm. The instrument utilized a Zeeman background correction that
reduces the non-specific absorption caused by some matrix components. The temperature
program is summarized below:
Step
1
2
3
4
5
Temp,
°C
110
130
500
1550
2500
Time, sec.
Ramp
1
15
10
0
1
Hold
40
45
20
5
3
Gas Flow,
mL/min
250
250
250
0
250
Read
X
A Pd/Mg modifier was used to stabilize Cd during the pyrolysis step. The calibration curve
was constructed from four standards and a blank. Validity of calibration was verified with a
check standard prepared from a secondary source. This action was taken immediately after
calibration, after every 20 samples, and at the end of each run. At least 1 post-digestion
spike was performed for every analytical batch of 20 samples.
3.2.4 Lead Analysis By Furnace
Lead was analyzed in accordance with the EPA SW-846 method 7060A utilizing the
Graphite Furnace technique. The instrument employed was a Perkin Elmer 4110ZL atomic
absorption spectrophotometer. A lead EDL Lamp was used as a light source at a wavelength
of 283.3 nm. The instrument utilized a Zeeman background correction that reduces the non-
specific absorption caused by some matrix components. The temperature program is
summarized below:
Step
1
2
O
4
5
6
Temp,
°C
120
140
200
850
1900
2500
Time, sec.
Ramp
1
5
10
10
0
1
Hold
20
40
10
20
5
3
Gas Flow,
mL/min
250
250
250
250
0
250
Read
X
A Pd/Mg modifier was used to stabilize Pb during the pyrolysis step. The calibration curve
was constructed from four standards and a blank. Validity of calibration was verified with a
21
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check standard prepared from a secondary source. This action was taken immediately after
calibration, after every 20 samples, and at the end of each run. At least 1 post-digestion
spike was performed for every analytical batch of 20 samples.
3.2.5 Selenium Analysis By Furnace
Selenium was analyzed in accordance with the EPA SW-846 method 7060A utilizing the
Graphite Furnace technique. The instrument employed was a Perkin Elmer 4110ZL atomic
absorption spectrophotometer. An arsenic EDL Lamp was used as a light source at a
wavelength of 196.0 nm. The instrument utilized a Zeeman background correction that
reduces the non-specific absorption caused by some matrix components. The temperature
program is summarized below:
Step
1
2
O
4
5
6
Temp,
°C
120
140
200
1300
2100
2450
Time, sec.
Ramp
1
5
10
10
0
1
Hold
22
42
11
20
5
3
Gas Flow,
mL/min
250
250
250
250
0
250
Read
X
A Pd/Mg modifier was used to stabilize Se during the pyrolysis step. The calibration curve
was constructed from four standards and a blank. Validity of calibration was verified with a
check standard prepared from a secondary source. This action was taken immediately after
calibration, after every 20 samples, and at the end of each run. At least 1 post-digestion
spike was performed for every analytical batch of 20 samples.
3.2.6 Metal Analysis By ICP
Aluminum, barium, calcium, chromium, copper, iron, magnesium, manganese, nickel, and
zinc were analyzed in accordance with EPA SW-846 method 6010A using Inductively
Coupled Plasma Atomic Emission Spectroscopy. Samples were analyzed on a Perkin Elmer
P-1000 ICP Spectrometer with Ebert monochromator and cross-flow nebulizer. The
following settings were used:
Element Analyzed
Al
Ba
Ca
Element Analyzed
Cr
Cu
Fe
Wavelength, nm
308.2
233.5
315.9
Wavelength, nm
267.7
324.8
259.9
22
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Mg
Mn
Ni
Zn
279.1
257.6
231.6
213.9
RF Power:
1300 W
Matrix interferences were suppressed with internal standardization utilizing Myers-Tracy
signal compensation. Interelement interference check standards were analyzed in the
beginning and at the end of every analytical run and indicated absence of this type of
interference at the given wavelength. The calibration curve was constructed from four
standards and a blank, and was verified with a check standard prepared from a secondary
source.
3.2.7 Mercury
After the digestion procedure outlined in 3.2.1, sediment samples were analyzed for total
mercury by cold vapor technique according to SW-846 Method 7471. A Perkin Elmer
5100ZL atomic absorption spectrophotometer with FIAS-200 flow injection accessory was
used. Mercury was reduced to an elemental state using stannous chloride solution, and
atomic absorption was measured in a quartz cell at an ambient temperature and a wavelength
of 253.7 nm. A mercury electrodeless discharge lamp was used as a light source. The
calibration curve consisted of four standards and a blank, and was verified with a check
standard prepared from a secondary source.
3.2.8 Total Organic Carbon
Total Organic Carbon analysis of sediments was conducted on a Shimadzu TOC-5000 Total
Organic Carbon Analyzer equipped with Solid Sample Accessory SSM-5000A. Samples
were air dried and then reacted with phosphoric acid to remove inorganic carbonates. Prior
to analysis, the samples were air dried a final time. Calibration curves for total carbon were
constructed from three standards and a blank. Glucose was used as a standard compound for
Total Carbon Analysis (44% carbon by weight).
3.2.9 Grain Size Analysis
Grain size was performed by wet sieving the sediments. The following mesh sizes were
used: 2 mm (granule), 1 mm (very coarse sand), 0.85 mm (coarse sand), 0.25 mm (medium
sand), 0.125 mm (fine sand), 0.063 (very fine sand), and 0.031 (coarse silt). After sieving,
the fractions were dried at 105°C and analyzed by gravimetric methods to determine weight
percentages.
i.2.10 Semivolatiles Analysis
23
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Sediment samples were extracted for analysis of semivolatiles using SW-846 Method 3050.
The sediment samples were dried with anhydrous sodium sulfate to form a free flowing
powder. The samples were then serially sonicated with 1:1 methylene chloride/acetone and
concentrated to a volume of 1 mL.
The sample extracts were analyzed by GC/MS on a Hewlett Packard 5895 MSD Mass
Spectrometer according to Method 8270. Instrumental conditions are itemized below:
MS operating conditions:
- Electron energy:
- Mass range:
Scan time:
Source temperature:
Transfer line temperature:
70 volts (nominal).
40-450 amu.
820 amu/second, 2 scans/sec.
190° C
250°C
GC operating conditions:
Column temperature program:
Injector temperature program:
Sample volume:
45°C for 6 min., then to 250°C at
10°C/min, then to 300°C at 20°C/min
hold 300°C for 15 min.
250°C
A list of analytes and detection limits is given in Table 3.2.2. Surrogate standards were
utilized to monitor extraction efficiency. Acceptance criteria for surrogate standards are
given in Table 3.2.3. The GC/MS was calibrated using a 5-point curve. Instrument tuning
was performed by injecting 5 ng of decafluorotriphenylphosphine and then adjusting spectra
to meet method acceptance criteria. The MS and MSD samples were analyzed at a 5%
frequency.
TABLE 3.2.2 ORGANIC PARAMETERS AND DETECTION LIMITS
Semi-Volatile Organic Compounds (8270) Sediment (mg/kg)
24
-------
Phenol 0.33
Bis(2-chloroethyl)ether 0.33
2-Chlorophenol 0.33
1,3-Dichlorobenzene 0.33
1,4-Dichlorobenzene 0.33
1,2-Dichlorobenzene 0.33
2-Methylphenol 0.33
4-Methylphenol 0.33
Hexachloroethane 0.33
Isophorone 0.33
2,4-Dimethylphenol 0.33
Bis(2-chloroethoxy)methane 0.33
2,4-Dichlorophenol 0.33
1,2,4-Trichlorobenzene 0.33
Naphthalene 0.33
Hexachlorobutadiene 0.33
4-Chloro-3-methylphenol 0.33
2-Methylnaphthalene 0.33
Hexachlorocyclopentadiene 0.33
2,4,6-Trichlorophenol 0.33
2,4,5-Trichlorophenol 0.33
2-Chloronaphthalene 0.33
Dimethylphthalate 0.33
Acenaphthylene 0.33
Acenaphthene 0.33
Diethylphthalate 0.33
4-Chlorophenyl-phenyl ether 0.33
Fluorene 0.33
4,6-Dinitro-2-methylphenol 1.7
4-Bromophenyl-phenyl ether 0.33
25
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TABLE 3.2.2 ORGANIC PARAMETERS AND DETECTION LIMITS (CONTINUED)
Semi-Volatile Organic Compounds (8270) Sediment (mg/kg)
Hexachlorobenzene 0.33
Pentachlorophenol 1.7
Phenanthrene 0.33
Anthracene 0.33
Di-n-butylphthalate 0.33
Fluoranthene 0.33
Pyrene 0.33
Butylbenzylphthalate 0.33
Benzo(a)anthracene 0.33
Chrysene 0.33
Bis(2-ethylhexyl)phthalate 0.33
Di-n-octylphthalate 0.33
Benzo(b)fluoranthene 0.33
Benzo(k)fluoranthene 0.33
Benzo(a)pyrene 0.33
Indeno(l,2,3-cd)pyrene 0.33
Dibenzo(a,h)anthracene 0.33
Benzo(g,h,i)perylene 0.33
3-Methylphenol 0.33
TABLE 3.2.3 DATA QUALITY OBJECTIVES FOR SURROGATE STANDARDS CONTROL LIMITS
FOR PERCENT RECOVERY
Parameter Control Limit
Nitrobenzene-d5 30%-97%
2-Fluorobiphenyl 42%-99%
o-Terphenyl 60%-101%
Phenol-d6 43%-84%
2-Fluorophenol 33%-76%
2,4,6-Tribromophenol 58%-96%
3.2.11 PCS Analysis
26
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The sediment samples were extracted for PCBs using SW-846 Method 3050. Sediment
samples were air dried for 24 hours, and then equal weights of the dried soil and anhydrous
sodium sulfate were mixed together. The samples were then extracted using 50 mL of
methanol and 100 mL of hexane. The samples were sonicated for 3 minutes, and then the
hexane layer was removed and filtered through anhydrous sodium sulfate. The process was
repeated two more times, adding 50 mL of hexane each time. The hexane extract was
concentrated to 1 mL in the Turbovap, and then run through a chromatography column
packed with 2% deactivated florisil and anhydrous sodium sulfate. Copper turnings cleaned
with 1 M hydrochloric acid were added to remove sulfur. The eluent was concentrated to 1
mL using the Turbovap, and concentrated sulfuric acid was added as a final clean-up step.
Solvent transfer to iso-octane was achieved under a flow of nitrogen gas and condensed to a
final volume of 1 mL.
Sample extracts were analyzed using gas chromatography with a Nies electron capture
detector and RTX-5 capillary column. Helium and nitrogen were used as the carrier gas and
makeup gas, respectively. Instrumental operating conditions were as follows:
> Column temperature program: 80°C for 2 min., 10°C/min to 160°C,
> 1.5°C/min to 190°C, 2°C/min to 256°C and hold at 256°C for 6 min.
> Injector temperature: 260°C
> Detector temperature: 330°C
> Sample volume: 1 jil
Table 3.2.4 presents a list of PCB congeners and their detection limits. Two surrogate
standards, tetrachloro-m-xylene and decachlorobiphenyl were used to monitor extraction
efficiency. Acceptance limits for the surrogates were + 50% for precision and accuracy.
Table 3.2.4 Sediment Detection Limits for PCBs
PCB Formulation Detection Limit (mg/kg)
Aroclor 1221 0.33
Aroclor 1232 0.33
Aroclor 1242 0.33
Aroclor 1248 0.33
Aroclor 1254 0.33
Aroclor 1260 0.33
27
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3.2.12 Organic Chromium Analysis
The organic chromium fraction in sediment was extracted using 0.1 M Na2P2Oy at a 10:1
(v/m) ratio by shaking for 18 hours (Walsh and O'Halloran 1996). Twenty grams of wet
sediment were extracted. The extract was centrifuged, filtered with a 0.45 um membrane and
analyzed for total chromium as described previously. Sample results were converted to a dry
weight basis for reporting.
3.2.13 Proton Induced X-Ray Emission Spectroscopy (PIXE)
Dried 2-cm-sections of sediment cores were homogenized by mechanical shaking. A sample
of approximately 0.1 to 0.2 g of sediment was pressed into a self-supporting thin target by
10,000 psi of hydraulic pressure in a standard pellet press. The exact mass and thickness of
the pellet was not critical as long as the resultant target remains thin with respect to the range
of accelerated protons used in the irradiation. A current of approximately 10 nA of 2.3 MeV
protons was used as an ion analysis probe for X-ray emission. The sediment samples were
loaded on a target wheel in a vacuum chamber, which was subsequently evacuated to <10~5
torr. Each sample was exposed to the beam for approximately 300 seconds, or a total
accumulated charge of approximately 3 |j,Coulomb. The incident beam current was measured
with a Faraday cup immediately before and after irradiation and an average current was used
to calculate the exact charge collected on each target. The resultant X-rays emitted from the
irradiation were detected with a 4 cm2 Si(Li) detector located at 135° from the incident beam.
There was a thin vacuum window and a piece of Be foil in front of the active detector, as
well as an adjustable wheel of Kaptan® foils that was interspersed between the target and X-
ray detector to attenuate the excess low-energy X-rays. A 2 mil (.002") of Kaptan® foil was
used to suppress low energy X-rays on sediment sample irradiation. The X-ray energies
were calibrated with a set of known metal standards (Si, Ti, In, Au) and for each run (up to a
maximum of 36 samples per target wheel) a NIST standard mud pellet was used to
standardize the X-ray yield calculations. We use both Buffalo River Sediment (NIST SRM
2704) and Trace Elements in Soil (NIST SRM 2586) as calibration standards for sediment
samples. The X-ray spectra were acquired by standard NIM and CAMAC electronics and
recorded onto a PC in binary format. The spectra were analyzed off-line by GUPIX II® a
commercial PIXE analysis programl. The limits of detection vary from element to element,
but typically range between the ppb - ppm level for most metals. A general review of the
technique and examples of earth science applications are provided by Johanssen and
Campbell (1988).
28
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3.3 Chemical Analysis Methods For Water Analysis
The parameters, methods, and detection limits for the measurements performed on the
culture water used in the sediment toxicity tests are listed in Table 3.3.1. All methods were
performed according to procedures outlined in Standard Methods 14th Edition (1996).
TABLE 3.3.1 ANALYTICAL METHODS AND DETECTION LIMITS FOR CULTURE WATER
Parameter Method Detection Limit
Specific Conductance Standard Methods 2510 B. NA
Alkalinity Standard Methods 2320 10 mg/1
Temperature Standard Methods 2550 NA
Dissolved Oxygen Standard Methods 4500-O G. 0.5 mg/1
Ammonia Electrode Standard Methods 0.05 mg/1
4500-NH3 F.
Hardness Standard Methods 2340 C. 10 mg/1
3.4 Sediment Toxicity
The evaluation of the toxicity of the White Lake sediments was conducted using the ten-day
survival test for the amphipod Hyalella azteca and the dipteran Chironomus tentans. The
procedures followed are contained in EPA/600/R-94/024, Methods for Measuring the
Toxicity and Bioaccumulation of Sediment-associated Contaminants with Fresh Water
Invertebrates. All sediments were stored at 4°C prior to analysis.
3.4.1 Laboratory Water Supply
Moderately hard well water was employed for the culture and maintenance of H. azteca and
C. tentans.
3.4.2 Test Organisms
The original stock of H. azteca was obtained from the Great Lakes Environmental Research
Laboratory in Ann Arbor, Michigan. The H. azteca culture was maintained in four 20 L
glass aquaria using maple leaves as a substrate and as a food source. The food source was
supplemented with a suspension of Tetramin® fish food. The original stock of C. tentans
was obtained from the University of Michigan Department of Environmental Health in Ann
Arbor, Michigan. The culture of C. tentans was maintained in 36 L glass aquaria using
shredded paper toweling as a substrate and was fed a suspension of Tetrafin® goldfish food.
29
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3.4.3 Experimental Design
For the November testing, eight replicates per sediment were set up for both H. azteca and C.
tentans exposures, with the sediment from site M-15P designated as the control. In all tests,
moderately hard well water was utilized as the overlying water. The experimental conditions
outlined in Tables 3.4.1 and 3.4.2 were used for the toxicity evaluations.
One day prior to the start of the test (day -1), the sediment from each site was mixed
thoroughly and a 100 mL aliquot was transferred to each of the eight test chambers.
Additionally, visual observations of the sediments were made. Moderately hard well water
also was added at this time. On day 0, the overlying water was renewed once before the test
organisms were introduced into each of the glass beakers. Measurement of water quality
parameters also was initiated on this day. Ten, 7-14 day old H. azteca and 10 third instar C.
tentans larvae were randomly added to their respective test chambers. At this time the
organisms were fed 1.5 mL of Tetrafm®. The glass beakers were placed in a rack and
transferred to a temperature controlled room (23 + 1°C). The light cycle was 16 hours on and
8 hours off. Temperature and dissolved oxygen measurements were taken from one
randomly selected beaker for each sediment sample every 12 hours, after which the overlying
water was renewed in all the beakers. Feeding with the Tetrafm® suspension occurred after
the morning renewal. This procedure was repeated daily through day 10, at which point the
test was terminated. On day 0, the overlying water from the beakers was composited from
each sediment sample and 250 mL were retained for alkalinity, pH, conductance, hardness
and ammonia analysis. On the last day the same procedure was carried out. On day 10, the
sediments were sieved, and the surviving test organisms were removed and counted. The
biological endpoint for these sediment tests was mortality. The validity of the test was based
on EPA (1994) criteria of greater than 80% survival in the control treatment for H. azteca
and greater than 70% survival in the control treatment for the C. tentans. In addition, EPA
(1994) recommended that the hardness, alkalinity, pH, and ammonia in the overlying water
within a treatment should not vary by more than 50% over the duration of the test.
3.4.4 Statistical Analysis
Survival data for the toxicity testing were analyzed first for normality with Chi Square and
then for homogeneity using Bartlett's Test. All data passed the normality and homogeneity
tests without transformation. The data were then examined using Dunnett's Procedure to
determine whether there was a significant difference in survival between the designated
control sediment and those sediments containing pollutants. The TOXSTAT® 3.5 Computer
Program was used for the statistical evaluations.
30
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TABLE 3.4.1 TEST CONDITIONS FOR CONDUCTING A TEN DAY SEDIMENT TOXICITY
TEST WITH HYALELLA AZTECA.
1. Test Type: Whole-sediment toxicity test with renewal of overlying water
2. Temperature (°C): 23 + 1°C
3. Light quality: Wide-spectrum fluorescent lights
4. Illuminance: About 500 to 1000 lux
5. Photoperiod: 16 h light, 8 h darkness
6. Test chamber size: 300 mL high-form lipless beaker
7. Sediment volume: 100 mL
8. Overlying water volume: 175 mL
9. Renewal of overlying
water: 2 volume additions per day (i.e., one volume addition
every 12 hours)
10. Age of test organisms: 7 to 14 days old at the start of the test
11. Number of organisms
per chamber: 10
12. Number of replicate
chambers per treatment: 8
13. Feeding: Tetramin® fish food, fed 1.5 mL daily to each test
chamber
14. Aeration: None, unless dissolved oxygen in overlying water drops
below 40% of saturation
15. Overlying water: Reconstituted water
16. Overlying water quality: Hardness, alkalinity, conductivity, pH, and ammonia
measured at the beginning and end of a test.
Temperature and dissolved oxygen measured daily.
17. Test duration: 10 days
18. End point: Survival, with greater than 80% in the control
Test Method 100.1. EPA Publication 600/R-94/024 (July 1994).
-------
TABLE 3.4.2 RECOMMENDED TEST CONDITIONS FOR CONDUCTING A TEN DAY
SEDIMENT TOXICITY TEST WITH CHIRONOMUS TENTANS.
1. Test Type: Whole-sediment toxicity test with renewal of overlying
water
2. Temperature (°C): 23 + 1°C
3. Light quality: Wide-spectrum fluorescent lights
4. Illuminance: About 500 to 1000 lux
5. Photoperiod: 16 h light, 8 h darkness
6. Test chamber size: 300 mL high-form lipless beaker
7. Sediment volume: 100 mL
8. Overlying water volume: 175 mL
9. Renewal of overlying
water: 2 volume additions per day (i.e., one volume addition
every 12 hours)
10. Age of test organisms: Third instar larvae (All organisms must be third instar
or younger with at least 50% of the organisms at third
instar)
11. Number of organisms
per chamber: 10
12. Number of replicate
chambers per treatment: 8
13. Feeding: Tetrafm® goldfish food, fed 1.5 mL daily to each test
chamber (1.5 mL contains 4.0 mg of dry solids)
14. Aeration: None, unless dissolved oxygen in overlying water drops
below 40% of saturation
15. Overlying water: Reconstituted water
16. Overlying water quality: Hardness, alkalinity, conductivity, pH, and ammonia
measured at the beginning and end of a test.
Temperature and dissolved oxygen measured daily.
17. Test duration: 10 days
18. End point: Survival, with greater than 70% in the control. Weight
> 0.6 mg per midge in the control
Test Method 100.2. EPA Publication 600/R-94/024 (July 1994).
32
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3.5 Benthic Macroinvertebrate Analysis
Samples were washed with tap water to remove formalin and extraneous debris through a
USGS #30 mesh screen. The retained portion was poured into a white enamel pan from
which the organisms were picked into two groups. These were oligochaetes and "other". The
worms were preserved with 4% formalin and later identified to the lowest practical level.
The worms were mounted separately and examined under 100X and 400X. The "other"
group was preserved in 70% ethanol. Midges were removed from this group and a head
mount of each midge was made and examined under 100X and 400X. The number and taxa
were reported. The remainder of the organisms were identified and enumerated utilizing a
60X dissecting microscope.
3.6 Radiometric Dating
Radiometric measurements were made using low-background gamma counting systems with
well-type intrinsic germanium detectors (Schelske et al. 1994). Dry sediment from each
section was packed to a nominal height of 30 mm in a tared polypropylene tube (84 mm high
x 14.5 mm outside diameter, 12 mm inside diameter). Sample height was recorded and tubes
were weighed to obtain sample mass. Samples in the tubes were then sealed with a layer of
epoxy resin and polyamine hardener, capped, and stored before counting to ensure
equilibrium between 226Ra and 214Bi. Activities for each radionuclide were calculated using
empirically derived factors of variation in counting efficiency with sample mass and height
(Schelske et al. 1994). Total 210Pb activity was obtained from the 46.5 keV photon peak, and
226Ra activity was obtained from the 609.2 keV peak of 214Bi. 226Ra activity was assumed to
represent supported 210Pb activity. Excess 210Pb activity was determined from the difference
between total and supported 210Pb activity and then corrected for decay from the coring date.
The 661.7 keV photon peak is used to measure 137Cs activity.
Sediments were aged using activity measurements of the above radioisotopes in the sediment
samples. The method was based on determining the activity of total 210Pb (22.3 yr half-life),
a decay product of 226Ra (half-life 1622 yr) in the 238U decay series. Total 210Pb represents
the sum of excess 210Pb and supported 210Pb activity in sediments. The ultimate source of
excess 210Pb is the outgassing of chemically inert 222Rn (3.83 d half-life) from continents as
226Ra incorporated in soils as rocks decay. In the atmosphere, 222Rn decays to 210Pb which is
deposited at the earth's surface with atmospheric washout as unsupported or excess 210Pb.
o i n T7f\
Supported Pb in lake sediments is produced by the decay of Ra that is deposited as one
fraction of erosional inputs. In the sediments, gaseous 222Rn produced from 226Ra is trapped
and decays to 210Pb. By definition, supported 210Pb is in secular equilibrium (production rate
matches decay rate) with sedimentary 226Ra and is equal to total 210Pb activity at depths
where excess 210Pb activity is not measurable due to decay. Because the decay of excess
210Pb activity in sediments provides the basis for estimating sediment ages, it is necessary to
make estimates of total and supported 210Pb activities so excess 210Pb activity can be
determined by difference. Excess 210Pb activity was calculated either by subtracting 226Ra
activity from total 210Pb activity at each depth or by subtracting an estimate of supported
210Pb activity based on measurements of total 210Pb activity at depths where excess 210Pb
activity was negligible.
33
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Sediment ages were calculated using a CRS model (Appleby and Oldfield 1983). This model
210
calculates ages based on the assumption that the flux of excess Pb to the lake was constant
and therefore that variation in 210Pb activity from a pattern of exponential decrease with
depth depends on variation in rate of sedimentation. The age of sediments at depth x is given
by:
where t is time in yr, k is 0.03114 (the 210Pb decay constant), AO is the total residual excess
210Pb activity in the sediment core, and A is the integrated excess 210Pb activity below depth
x. Calculations for each depth provide a continuous profile of ages as a function of depth.
Mass sedimentation rate (MSR) at depth x was determined by:
MSR = m/t
where m is dry mass of sediment (g /cm2) for the sampling interval. Errors in age and mass
sedimentation rate were propagated using first-order approximations and calculated
according to Binford (1990).
3.7 Statistical Analysis
Multivariate analyses were conducted using SAS version 8.0 (Gary, North Carolina).
Principal Components Analysis (PCA) was conducted on the physical/chemical parameters.
Correspondence Analysis (CA) was conducted on the benthic macroinvertebrate data using
the individual taxa.
Spearman Rank Correlation was used to determine significant relationships between
individual physical and chemical parameters and the trophic status indices. Pearson
correlation analysis was conducted using SYSTAT version 5.0 (Evanston, Illinois).
3.8 Contaminant Mapping
ArcView GIS and Surfer were utilized for analyzing and mapping contaminant
concentrations in White Lake. ArcView was primarily used for geographic projection and
spatial distribution mapping while Surfer was used for creating contour maps of chromium
and PCB concentrations, in which Kriging was selected as a gridding method.
The original GPS observation points were expressed in decimal degrees under the
Geographic-Lat/Long system. To determine the coordinates of the station locations, ArcView
GIS 3.3 and the MI DNR Projection Extension were used to project the station points to the
Michigan GeoRef NAD 1983 system. Kriging was used for the interpolation of chromium
concentrations at the grid points. Specific information concerning the range of X and Y
34
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coordinates, grid size, as well as the variogram model, drift type, and nugget effect are shown
below:
X Coordinates 465255 - 471530 meters
Y Coordinates 312504 - 317754 meters
Grid Size 876 rows x 1047 columns
Variogram Model Type: Linear
Parameters: Scale: 671000; Length: 3310
Drift Type No Drift
Nugget Effect Error Variance: 0; Micro Variance: 0
Anisotropy Ratio = 1; Angle = 0
3.9 References
>y, P. G. ;
sediment accumulation rates. Hydrobiologia 103: 29-35.
210
Appleby, P. G. and F. Oldfield. 1983. The assessment of Pb data from sites with varying
210
Binford, M. W. 1990. Calculation and uncertainty analysis of Pb dates for PIRLA project
lake sediment cores. J. Paleolim. 3:253-267.
EPA. 1994. Methods for Measuring the Toxicity and Bioaccumulation of Sediment-
Associated Contaminants with Freshwater Invertebrates. EPA Publication 600/R-
94/024.
Johanssen, S.A.E. and J. L Campbell. 1988. PIXE, A Novel Technique for Elemental
Analysis, John Wiley & Sons, Chichester, NY. 458 pp.
Schelske, C. L., A. Peplow, M. Brenner, and C. N. Spencer. 1994. Low-background
210
gamma counting: Applications for Pb dating of sediments. J. Paleolim. 10:11128.
Walsh, A.R. and O'Halloran, J. 1996. Chromium speciation in tannery effluent - II.
Speciation in the effluent and in a receiving estuary. Water Res. 30(10):2401-2412.
35
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4.0 Results And Discussion
The results and discussion section is organized according to 6 sections that present and
summarize the information related to the following topics:
Section 4.1 Sediment Chemistry Results
Section 4.2 Stratigraphy and Radiodating Results
Section 4.3 Toxicity Testing Results
Section 4.4 Benthic Macroinvertebrate Results
Section 4.5 Chromium Uptake In Aquatic Organisms
Section 4.6 Environmental Fate and Transport Analysis
Section 4.7 Sediment Quality Triad Assesment
Section 4.8 Summary and Conclusions
The sediment chemistry results are presented for the core and PONAR samples (Section 4.1)
and include metals, semivolatiles, and physical parameters. A discussion is also included
related to the comparison of the data with published sediment quality guidelines. The
stratigraphy and radiodating results are presented in Section 4.2 and include the results of
radioisotopes and the target list of metals (chromium and lead). Toxicity and Benthic
Macroinvertebrate results are presented in Sections 4.3 and 4.4, respectively. Statistical
analyses of the data and comparisons to related chemical and biological data are also
discussed. Chromium accumulation in selected aquatic organisms and the results are
summarized in Section 4.5. Section 4.6 provides a discussion of the environmental fate and
transport of contaminants in White Lake using the results of this investigation plus studies by
Rediske et al. (1998) and Earth Tech (2001). Finally, Section 4.7 presents the investigative
data in the contex of the Sediment Quality Triad. The project summary and conclusions are
provided in section 4.8.
The project data were reviewed for compliance with the Data Quality Objectives outlined in
the Quality Assurance Project Plan. Low matrix spike recoveries were obtained on one
sample for semivolatiles and one sample for metals. Acceptable recoveries were obtained in
the laboratory control sample, indicating that the problem was matrix related. The data were
not qualified due to the fact that the project was a preliminary investigation. The results of
the Quality Assurance reviews are summarized in Appendix A.
4.1 Sediment Chemistry Results
The results of sediment grain size fractions, percent solids and TOC for the core and PONAR
samples are presented in Tables 4.1.1 and 4.1.2, respectively. The sediments from most of
the core samples can be characterized as having fine grain size (> 70% of particles < 63 um)
and moderate to high in total organic carbon (TOC 1% - 10%) in the top 51 cm. Grain size
distributions changed to include a greater sand fraction (125-500 um range) in the middle
(51-102 cm) and bottom (102-152 cm) sections. This pattern is consistent with historical
modification and development of the shoreline. Much of the lake shoreline was modified by
36
-------
TABLE 4.1.1 RESULTS OF SEDIMENT GRAIN SIZE FRACTIONS, TOC, AND PERCENT SOLIDS FOR WHITE LAKE CORE
SAMPLES, OCTOBER 2000. (Top = 0-52 CM, MID = 52-102 CM, EOT = 102-152 CM)
>2000Mm 2000-1000 Mm
Sample ID Weight %
WL-1 TOP
WL-1 MID
WL-1 EOT
WL-2 TOP
WL-2 MID
WL-2 EOT
WL-3 TOP
WL-3 MID
WL-3 TOP
WL-4 TOP
WL-4 MID
WL-5 TOP
WL-5 MID
WL-5 EOT
WL-6 TOP
WL-6 MID
WL-6 EOT
WL-7 TOP
WL7MID
WL-7 EOT
WL-8 TOP
WL-8 MID
WL-8 EOT
WL-9 TOP
WL-9-MID
WL-9 EOT
WL-10TOP
WL-10MID
WL-10BOT
WL-21 TOP
WL-21 MID
WL-21 EOT
0
0
0
1
0
0
0
0
0
0
0
0
0
0
0
1
0
0
0
0
0
0
0
0
0
0
6
0
0
0
0
0
Weight%
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
1
0
0
0
0
0
0
0
0
1000-850 Mm
Weight %
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
850-500 Mm
Weight %
0
0
0
0
0
2
0
1
0
0
3
0
0
0
0
2
1
0
0
0
0
0
0
0
0
0
0
0
0
0
1
1
500-125 Mm
Weight %
2
13
7
4
13
90
4
23
7
10
80
7
9
6
2
43
8
8
11
8
8
8
6
9
9
7
23
11
6
10
10
6
125-63 Mm
Weight %
6
9
9
4
9
2
8
11
9
14
3
12
12
10
5
8
13
12
17
18
16
11
12
14
10
11
6
10
7
5
15
6
<63Mm
TOC
Solids
Weight % % %
92
78
84
92
77
5
87
65
84
76
13
81
79
84
93
46
78
80
72
75
76
80
83
76
81
81
71
79
87
84
74
86
3.9
11
9.5
6.5
10
<1.0
2.2
4.8
8.1
2.9
<1.0
5.8
8.9
7.2
3.0
10
3.0
3.6
10
10
6.6
1.2
1.3
7.5
7.1
8.1
5.0
9.7
8.9
2.7
7.1
3.4
12
14
15
11
15
67
13
18
15
13
53
12
15
15
17
38
16
12
16
15
12
15
16
13
15
16
14
15
14
20
16
13
37
-------
TABLE 4.1.2 RESULTS OF SEDIMENT GRAIN SIZE FRACTIONS, TOC, AND PERCENT SOLIDS FOR WHITE LAKE PONAR SAMPLES,
OCTOBER 2000.
Sample ID
WL-1 P
WL-2P
WL-3P
WL-4P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-1 OP
WL-11 P
WL-1 2 P
WL-1 3 P
WL-1 4 P
WL-1 5 P
WL-1 6 P
WL-1 7 P
WL-1 8 P
WL-1 9 P
WL-20P
WL-21 P
WL-22P
WL-23P
WL-24P
>2000 Mm
Weight %
0
0
0
0
0
0
0
0
0
0
0
1
0
1
1
0
0
0
0
0
0
6
3
3
2000-1000 Mm
Weight%
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
2
3
1
1000-850 Mm
Weight %
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
0
850-500 Mm
Weight %
0
0
0
5
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
1
2
1
500-125 Mm
Weight %
4
6
4
82
6
5
7
8
7
5
7
6
30
13
6
3
5
8
6
11
19
12
10
12
125-63 Mm
Weight %
5
5
5
2
10
7
10
10
9
5
9
9
14
10
10
7
10
8
11
17
9
13
9
7
<63 Mm
Weight %
91
88
90
11
83
88
83
82
83
89
84
84
55
76
83
90
84
84
83
70
71
65
73
76
TOC
8.0
3.5
3.0
<1.0
5.0
4.4
6.6
5.5
6.4
2.2
6.0
7.1
5.0
18
7.4
10
10
11
11
8.5
5.6
4.6
5.9
8.2
Solic
7
10
10
61
11
10
10
11
11
10
11
11
15
13
12
14
15
16
15
16
13
11
12
15
38
-------
logging in the 1800s and urban/industrial development in the 1900s. The subsequent erosion and
runoff probably resulted in a sand layer being deposited throughout the near shore area. The
presence of the finer grained material is consistent with the recent history of a more stable
shoreline and eutrophic conditions present in the lake. Station WL-4 was different with respect
to grain size distribution as it contained a higher sand fraction (80%) in the 52-102 cm core
section. WL-4 was collected off a sloping contour with a public boat launch located to the south.
Since the particle size and TOC characteristics of sediments will influence their ability to retain
metals and organic chemicals, these data will be important in explaining the distribution of
anthropogenic contaminants.
Very little difference was noted between the grain size and TOC content of the PONAR samples
(Table 4.1.2) and the top core sections (Table 4.1.1) for all samples except WL-4. The PONAR
collected at this location was very high in sand fraction sediments (80%) suggesting that
sediment composition is variable at this location. The variability may be due to the landscape
variables discussed above or depositional patterns. Since these samples were used for chemical
analysis in addition to the assessment of sediment toxicity and benthic invertebrate diversity, the
influence of particle size and TOC content will also be an important factor in the evaluation of
the project data. Chemical and ecological results from W-4 will be influenced to a large extent
by the physical characteristics of the substrate.
The results of sediment metals analyses are presented for the core and PONAR samples in
Tables 4.1.3 and 4.1.4 respectively. The results of semivolatile and PCB analyses for the same
sample groupings are given in Tables 4.1.5 and 4.1.6. Figures 4.1.1, 4.1.2, and 4.1.3 illustrate
the distribution of arsenic, chromium, and lead respectively, in core samples collected from
western White Lake. In general, arsenic concentrations in the three core sections showed little
variation (±3 mg/kg) with depth (Figure 4.1.1). The same pattern was noted in the prior
investigation (Rediske et al. 1998) for samples collected in eastern White Lake. These data
suggest a relatively constant deposition rate of arsenic in the lake occurred over time. Uniform
deposition rates over an extended period of time are usually related to regional geology and do
not indicate anthropogenic pollution. Chromium and lead (Figures 4.1.2 and 4.1.3 respectively)
did not follow this pattern as the highest levels of these elements were found in the top 51 cm of
sediment. The sediment chemistry profiles of chromium and lead are indicative of recent
anthropogenic pollution and cannot be attributed to background levels. A comparison of the
results for arsenic, chromium and lead is provided in Figures 4.1.4, 4.1.5, and 4.1.6 respectively.
The PONAR collects sediments to an approximate depth of 18 cm and can be used to estimate
very recent deposition. The results for arsenic are again indicative of a relatively constant
deposition rate, as there was little difference between PONAR and core sections (Figure 4.1.4).
Chromium results follow a similar pattern indicating stable deposition rates in the more recent
strata (Figure 4.1.5). In consideration that the deeper strata were considerably lower in
chromium, these results suggest a relatively constant source is currently present in the lake. This
is significant because the tannery ceased its discharge of chromium laden wastewater to White
Lake in 1975. Chromium deposition in the western half of the lake reflects a constant loading of
chromium after the wastewater diversion. These data support the hypothesis that the erosion and
transport of sediments from Tannery Bay play an important role in the mobilization and
deposition of contaminants in the western portion of White Lake (Rediske et al. 1998). Lead
39
-------
TABLE 4.1.3 RESULTS OF SEDIMENT METAL ANALYSES FOR WHITE LAKE CORE SAMPLES (MG/KG DRY WEIGHT), OCTOBER 2000.
(TOP = 0-52 CM, MID = 52-102 CM, EOT = 102-152 CM)
Sample
WL-1 Top
WL-1 Mid
WL-1 Bot.
WL-2 Top
WL-2 Bot
WL-3 Top
WL-3 Mid
WL-3 Bot
WL-4 Top
WL-4 Mid
WL-5 Top
WL-5 Mid
WL-5 Bot
WL-6 Top
WL-6 Mid
WL-6 Bot
WL-7 Top
WL-7 Mid
WL-7 Bot
WL-8 Top
WL-8 Mid
WL-8 Bot
WL-9 Top
WL-9 Mid
WL-9 Bot
WL-1 0 Top
WL-1 0 Mid
WL-10Bot
WL-21 Top
WL-2 1 Mid
Arsenic
(mg/kg)
9.1
6.1
6.6
9.0
7.5
7.9
6.2
5.7
9.0
1.8
8.9
6.3
6.1
6.7
12
12
8.2
6.5
5.5
7.7
7.7
7.3
9.6
7.5
7.0
6.5
5.8
6.5
9.5
7.8
Barium
(mg/kg)
130
130
160
160
150
120
110
130
130
18
140
130
150
180
88
110
130
110
110
140
120
1470
140
120
120
92
110
110
162
120
Cadmium
(mg/kg)
1.3
0.87
0.74
1.6
0.97
1.5
0.61
0.48
1.9
0.15
1.4
0.53
<0.1
1.3
0.26
0.19
1.6
0.65
0.35
1.4
0.42
0.49
1.5
0.6
0.51
1.1
0.47
0.36
1.2
0.78
Chromium
(mg/kg)
270
34
37
470
34
290
33
28
440
8.1
300
34
24
410
19
17
600
40
33
380
34
40
500
38
35
210
33
30
430
99
Copper
(mg/kg)
29
18
21
33
18
33
17
16
34
2.3
31
18
17
23
12
13
34
19
17
32
18
18
34
18
17
23
16
16
23
12
Mercury
(mg/kg)
0.42
<0.1
<0.1
0.42
0.14
0.39
0.16
<0.1
0.49
<0.1
0.52
0.10
<0.1
0.38
<0.1
<0.1
0.62
0.13
<0.1
0.58
<0.1
<0.1
0.63
0.12
<0.1
0.34
0.11
<0.1
0.51
0.11
Nickel
(mg/kg)
23
16
18
18
12
24
14
13
27
U
24
15
12
27
13
14
28
16
15
26
15
16
26
16
14
18
14
14
28
19
Lead
(mg/kg)
140
15
9.8
190
24
190
28
8.2
180
2.1
110
16
5.9
340
13
7.7
180
22
7.9
180
9.6
8.9
120
18
8.0
97
18
6.9
290
170
Selenium
(mg/kg)
2.8
2.8
2.6
2.6
2.7
2.7
2.1
2.6
2.5
0.47
3.6
2.9
3.1
2.1
0.86
1.5
2.6
1.9
<0.1
<0.1
<0.1
1.7
5.1
2.6
2.6
<0.1
2.0
2.7
1.5
1.8
Zinc
(mg/kg)
140
75
86
140
87
150
80
65
160
16
160
82
69
110
46
45
160
90
70
160
76
78
170
81
69
120
75
64
160
85
40
-------
TABLE 4.1.4 RESULTS OF SEDIMENT METAL ANALYSES FOR WHITE LAKE PONAR SAMPLES (MG/KG DRY WEIGHT), OCTOBER 2000.
Sample
WL-1 P
WL-2P
WL-3P
WL-4P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-1 OP
WL-11 P
WL-1 2 P
WL-1 3 P
WL-1 4 P
WL-1 5 P
WL-1 6 P
WL-1 7 P
WL-1 8 P
WL-1 9 P
WL-20 P
WL-21P
Arsenic
(mg/kg)
6.3
7.5
5.5
1.4
6.2
8.4
7.6
8.8
7.9
7.0
6.3
5.9
6.3
6.3
6.0
5.8
5.4
5.3
5.7
6.2
6.5
Barium
(mg/kg)
140
150
120
12
130
130
120
130
170
120
*
*
*
*
*
*
*
*
*
*
*
Cadmium
(mg/kg)
0.85
0.85
0.73
< 0.1
1.1
1.0
0.99
0.93
0.87
0.91
0.96
1.03
0.96
1.10
0.75
0.84
0.64
0.51
0.42
0.61
1.00
Chromium
(mg/kg)
270
300
190
18
400
360
390
380
420
270
310
510
250
480
250
190
50
29
39
28
450
Copper
(mg/kg)
30
34
29
2.2
31
28
37
27
34
31
32
30
32
31
28
27
30
32
31
28
31
Mercury
(mg/kg)
0.20
0.20
0.16
< 0.1
0.27
0.25
0.29
0.25
0.30
0.34
0.32
0.28
0.27
0.25
0.26
0.27
0.05
0.05
0.05
0.05
0.24
Nickel
mg/kg)
17
18
16
1.6
19
18
25
20
23
19
18
17
17
17
17
18
19
20
21
19
18
Lead
(mg/kg)
70
76
54
8.3
89
73
86
75
74
75
78
70
67
72
71
75
34
22
26
21
65
Selenium
(mg/kg)
<0.1
<0.1
<0.1
< 0.1
2.9
3.0
3.6
3.7
3.0
<0.1
*
*
*
*
*
*
*
*
*
*
*
Zinc
(mg/kg)
120
120
100
33
120
120
130
120
130
120
116
118
108
95
101
105
115
125
131
124
132
PONAR analyzed for target list metals. Barium and selenium not analyzed.
41
-------
TABLE 4.1.5 RESULTS OF SEDIMENT PCB AND SEMIVOLATILE ANALYSES FOR WHITE LAKE CORE SAMPLES (MG/KG DRY
WEIGHT), OCTOBER 2000. (SAMPLES AND PARAMETERS THAT WERE NOT DETECTED WERE OMITED.) (Top = 0-52 CM,
MID = 52-102 CM, EOT = 102-152 CM)
Sample ID
WL-1 Top
WL-1 Top
WL-1 Mid
WL-1 Mid
WL-1 Bot
WL-1 Bot
WL-2 Top
WL-2 Mid
WL-3 Top
WL-3Mid
WL-3 Bot
WL-4 Top
WL-4Mid
WL-5 Top
WL-5Mid
WL-5 Bot
WL-6 Top
WL-6Mid
WL-6 Bot
WL-7 Top
WL-7Mid
WL-7 Bot
WL-8 Top
WL-8Mid
WL-8 Bot
WL-9 Top
WL-9 Mid
WL-9 Bot
WL-1 0 Top
WL-10Mid
WL-10 Bot
WL-21 Top
WL-21 Mid
Aroclor
1248
mg/kg
0.22
0.49
<0.33
0.07
<0.33
.061
0.07
<0.33
0.05
<0.33
0.06
0.17
<0.33
0.17
<0.33
0.06
0.39
<0.33
<0.33
0.24
<0.33
<0.33
0.27
0.054
<0.33
0.07
0.06
<0.33
0.06
0.06
<0.33
22
0.84
1,3-
DICHLORO
BENZENE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
<0.93
< 1.0
< 1.3
<0.33
< 1.3
< 1.2
< 1.1
< 1.1
<0.46
<0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
1.9
0.29
1,4- BIS
DICHLORO (2-ETHYLHEXYL)-
BENZENE PHTHALATE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
<0.93
< 1.0
< 1.3
<0.33
< 1.3
< 1.2
< 1.1
< 1.1
<0.46
<0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
0.65
<0.33
mg/kg
0.38
< 1.5
< 1.1
0.42
.26
0.32
0.56
0.35
0.99
<0.93
0.39
< 1.3
<0.33
< 1.3
< 1.2
< 1.1
0.22
0.19
0.14
0.28
0.25
< 1.1
0.25
< 1.1
< 1.1
< 1.4
< 1.1
0.23
0.25
< 1.1
< 1.2
0.94
0.54
DI-N-
BUTYL
PHTHALATE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
<0.93
< 1.0
1
<0.33
< 1.3
< 1.2
< 1.1
< 1.1
<0.46
<0.45
1.1
0.99
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
0.44
0.46
0.98
1.1
0.84
< 1.2
<0.98
FLUORANTHENE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
< 0.93
< 1.0
0.10
< 0.33
0.097
< 1.2
< 1.1
< 1.1
< 0.46
< 0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
< 1.2
< 0.98
HEXACHLORO
BENZENE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
< 0.93
< 1.0
< 1.3
< 0.33
< 1.3
< 1.2
< 1.1
< 1.1
< 0.46
< 0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
0.54
0.051
HEXACHLORO
BUTADIENE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
<0.93
< 1.0
< 1.3
<0.33
< 1.3
< 1.2
< 1.1
< 1.1
<0.46
<0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
<0.33
<0.98
HEXACHLOROCYCLO
PENTADIENE PYRENE
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
< 0.93
< 1.0
< 1.3
< 0.33
< 1.3
< 1.2
< 1.1
< 1.1
< 0.46
< 0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
< 0.33
< 0.98
mg/kg
< 1.5
< 1.7
< 1.1
< 1.2
< 1.2
< 1.2
< 1.7
< 1.2
< 1.4
<0.93
< 1.0
< 1.3
<0.33
< 1.3
< 1.2
< 1.1
< 1.1
<0.46
<0.45
< 1.5
< 1.1
< 1.1
< 1.3
< 1.1
< 1.1
< 1.4
< 1.1
< 1.1
< 1.1
< 1.1
< 1.2
< 1.2
<0.98
42
-------
TABLE 4.1.6 RESULTS OF SEDIMENT PCB AND SEMIVOLATILE ANALYSES FOR WHITE LAKE PONAR SAMPLES (MG/KG DRY
WEIGHT), OCTOBER 2000. (SAMPLES AND PARAMETERS THAT WERE NOT DETECTED WERE OMITED.)
Sample ID
WL-1P
WL-2P
WL-3P
WL-4P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-10P
WL-11P
WL-12P
WL-13 P
WL-14P
WL-15 P
WL-16P
WL-17P
WL-18P
WL-19P
WL-20 P
WL-21 P
Aroclor
1248
mg/kg
<0.33
0.086
<0.33
<0.33
<0.33
0.071
0.084
0.076
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
21
1,3-
DICHLORO
BENZENE
mg/kg
< 1.8
<1.7
< 1.5
<0.33
< 1.7
<1.5
<1.7
<1.7
< 1.5
< 1.7
*
*
*
*
*
< 1.2
*
*
*
*
< 1.3
Die™ (2-ETH^HEXYL)- B™ FLUORANTHENE ™XpA™RO ™^™° ™™
BENZENE PHTHALATE PHTHALATE BENZENE BUTADIENE PENTADII
mg/kg
< 1.8
<1.7
<1.5
<0.33
<1.7
< 1.5
< 1.7
< 1.7
<1.5
<1.7
*
*
*
*
*
<1.2
*
*
*
*
< 1.3
mg/kg mg/kg mg/kg mg/kg mg/kg
0.92 ^ 1.8 < 1.8 < 1.8 ^ 1.8
<1.7 <1.7 <1.7 <1.7 <1.7
0.31 <1.5 <1.5 <1.5 <1.5
<0.33 <0.33 <0.33 < 0.33 < 0.33
0.62 < 1.7 < 1.7 < 1.7 < 1.7
0.25 <1.5 <1.5 <1.5 <1.5
0.32 0.3 < 1.7 < 1.7 < 1.7
0.35 0.25 < 1.7 < 1.7 < 1.7
1.3 <1.5 <0.33 <1.5 <1.5
<1.7 <1.7 <1.7 <1.7 <1.7
* * * * *
* * * * *
* * * * *
* * * * *
* * * * *
1.1 <1.2 0.18 <1.2 <1.2
* * * * *
* * * * *
* * * * *
* * * * *
0.4 < 1.3 < 1.3 < 1.3 < 1.3
mg/kg
< 1.8
< 1.7
< 1.5
<0.33
< 1.7
< 1.5
< 1.7
< 1.7
< 1.5
< 1.7
*
*
*
*
*
< 1.2
*
*
*
*
< 1.3
mg/kg
0.12
43
-------
12.0-r
__
r——^i — ~
WL-4 —r—~~~^^ ' K J
WL-5 .... - I T_' ^ ,
WL"6 WL-7 ] ~|—=rl
inii Q I
WL-8
WL9 WL-10
0-51 cm
51-102 cm
102-152 cm
FIGURE
nl--3 WL-10
4.1.1 DISTRIBUTION OF ARSENIC IN CORE SAMPLES COLLECTED IN
WESTERN WHITE LAKE, OCTOBER 2000.
600
WL-8
WI Q
WL9
WL-10
FIGURE 4.1.2 DISTRIBUTION OF CHROMIUM IN CORE SAMPLES COLLECTED IN
WESTERN WHITE LAKE, OCTOBER 2000.
44
-------
350
^
WL-8
WL S
WL-10
FIGURE 4.1.3 DISTRIBUTION OF LEAD IN CORE SAMPLES COLLECTED IN WESTERN
WHITE LAKE, OCTOBER 2000.
10.0
9.0
0.0
WL-1 WL, r—^i-LJ-J-J^ J~H ~l
WL-3 1 -=*T J ~^ )
WL-4 —^ ^^t_ I x' ~"^
WL-5 .... - i —S^L^ I
-------
600
• 0-18 cm
D 0-51 cm
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
0-18 cm
0-51 cm
WL-9
WL-10
FIGURE 4.1.5 COMPARISON OF CHROMIUM CONCENTRATIONS IN PONAR
SAMPLES (0-18 CM) AND TOP CORE SECTIONS (0-51 CM) COLLECTED IN
WHITE LAKE, OCTOBER 2000.
350
WL-1
WL-7
WL-8
WL-9
WL-10
FIGURE 4.1.6 COMPARISON OF LEAD CONCENTRATIONS IN PONAR
SAMPLES (0-18 CM) AND TOP CORE SECTIONS (0-51 CM) COLLECTED IN
WHITE LAKE, OCTOBER 2000.
46
-------
follows a different depositional pattern as the PONAR samples have lower contaminant
concentrations than the 0-51 cm core sections (Figure 4.1.6). Lead was removed from fuel
formulations during the 70s and lower deposition rates in the more recent sediments reflect
this change.
With the exception of the sample collected at WL-21, high levels of PCBs and organic
chemicals were not present in sediment cores (Table 4.1.5). Station WL-21 was collected
near the outfall of the former Hooker/Occidental Chemical facility and contained similar
PCB levels as previously reported (Rediske et al. 1998). Figure 4.1.7 shows the distribution
of Aroclor 1248 in the three core sections. PCBs appear to be localized in the vicinity of the
outfall and show minimal migration to areas in the western basin. Low levels of phthalate
esters (bis ethylhexyl phthalate and di-n-butyl phthalate) were sporadically found in a
number of core sections (Table 4.1.5). Phthalate esters are often found in plastic materials
and are common laboratory contaminants. Their sporadic distribution in the samples does
not point to a particular contaminant source or time period. PONAR samples (Table 4.1.6)
reflect a similar deposition pattern for Aroclor 1248. The highest concentration was found at
WL-21 and no significant migration of PCBs was noted in the western stations. Organic
contaminants were not detected in the PONAR sample from WL-16. This station exhibited
the highest degree of toxicity in the previous investigation (Rediske et al. 1998) and in this
project (Section 4.3). These results strongly indicate that the heavy metals and/or the scan list
of organic chemicals are not responsible for the toxicity observed at this WL-16.
Chromium concentrations were analyzed in a series of PONAR samples collected in the
eastern section of White Lake to provide an indication of the distribution of this contaminant
throughout the entire system. The results of the PONAR samples are summarized in Figure
4.1.8. While a decreasing trend in chromium concentration is noted moving downgradient
from Tannery Bay to Long Point, it is significant to note that the lowest chromium value
measured in the organic sediments was 190 mg/1. The low chromium concentration observed
at station WL-4 can be attributed to the physical characteristics (80% sand). Since the
PONAR collects samples from the biologically active zone of 0-18 cm, the results can be
compared to sediment quality guidelines to evaluate ecological effects. For this purpose, the
Probable Effect Concentration (PEC) (MacDonald et al. 2000) for chromium (111 mg/kg)
can be used as a reference point. Stations with concentrations above the chromium PEC are
identified on Figure 4.1.8. PECs are consensus based guidelines that indicate a >75%
probability that adverse ecological effects may be observed when the concentrations are
exceeded. The results suggest that a majority of the organic sediments in White Lake west
of the Tannery are contaminated with chromium at levels exceeding the PEC. The
bathymetric plot for White Lake (Figure 4.1.9) supports this conclusion as it shows a shallow
zone with an approximate depth of 4 m that is present along the perimeter west of the
Narrows (white and light green contours). This shelf area consists of sandy sediments
related to the native soils and has physical characteristics that limit the accumulation of
chromium. Depositional organic sediments are found in the deeper areas of the lake west of
Tannery Bay and in the shallow zone extending from the rivermouth to the Narrows. All of
the samples collected in this depositional zone were contaminated with chromium at levels
significantly above the PEC and are representative of a majority of the lake bottom.
47
-------
WL-1
WL-2 WL_3
WL-8
0-51 cm
51-102 cm
102-152 cm
WL-9
Core
Depth
WL-10
Station
WL-21
FIGURE 4.1.7 DISTRIBUTION OF AROCLOR 1248 IN CORE SAMPLES COLLECTED IN
WESTERN WHITE LAKE, OCTOBER 2000.
In contrast to chromium, the pattern of PCB contamination shows that it is localized in the
area near the Occidental/Hooker Chemical outfall near WL-21 (Figure 4.1.7). The discharge
of PCBs occurred in a deep area near the Occidental/Hooker Chemical outfall (15 m) that
was not subject to wave action and currents. The stability of the sediments plus the
hydrophobic nature of PCBs limited the ability of this contaminant to be transported to areas
downgradient from the outfall zone. In contrast, the discharge of chromium occurred in an
area of shallow sediments (< 3 m) that were subject to shoreline erosion and currents related
to the flow of the drowned rivermouth and wave action. Even though chromium is very
insoluble in natural water due to the formation of Cr(OH)3, the combination of resuspension
by wave action and advection by lake currents resulted in contamination throughout the basin
west of Tannery Bay. Factors influencing the spatial distribution of contaminants in White
Lake will be discussed in Section 4.6.
48
-------
1400
1200
1000
Tannery Bay
800
_
I 600
O
East of Dowies Point
East of Long Point
400
200
FIGURE 4.1.8 DISTRIBUTION OF CHROMIUM IN PONAR SAMPLES FOR WHITE LAKE, OCTOBER 2000. LINE
DENOTES PROBABLE EFFECT CONCENTRATION (PEC) (MACDONALD ET AL. 2000).
49
-------
318000—
3 ^ODD-
SI 6000-
315000-
314000-
313000—
n
26
24
22
20
18
16
14
12
10
8
6
4
2
0
466000
467000
468000
469000
470000
471000
472000
FIGURE 4.1.9 BATHYMETRIC PLOT OF WHITE LAKE.
50
-------
Principal Component Analysis (PCA) was conducted on the physical and chemical
parameters collected during this investigation (Figure 4.1.10). In the first two principal
components
PCA Using Chemical / Physical Data
White Lake
DryWt.
2 -
I OH
w
CN
ro
CN 5
C O -2
.2 0 co
0 -"O
of o
O.S2
-2 -
-4 -
-6 -
-8 -
-10 -
-12
500-125 urn
Depth
PCB1248 Mercury
-12 -10
-8
-6
-4
-2
\
0
2
TOC
Chromium
Lead
Cadmium
Arsenic
< 63 urn
Copper
Zinc
Nickle
125-63 urn
Dimension 1 (52%)
Arsenic, Cadmium, Copper, Nickle, and Zinc
vs. Dry Wt. and 125 - 500 urn sediment
FIGURE 4.1.10 PCA ANALYSIS OF WHITE LAKE PHYSICAL AND CHEMICAL DATA.
(explaining 73.2% of the variation), the deep sites and the west bay were pulled away from
the locations upgradient from the tannery (WL-17, WL-18, WL-19, and WL-20). The
upgradient sites (WL-17, WL-18, WL-19, and WL-20) were pulled in the direction of
51
-------
physical parameters (TOC and grain size) while the remainder of the stations clustered
around the contaminants chromium, mercury, and lead. Station WL-4 did not follow this
pattern as it was pulled in the direction of the grain size (sand fraction) and % solids. This
station had the greatest sand fraction, the highest dry weight (% solids), and was the only
deep station that contained low contaminant concentrations. Spearman Rank Order
Correlations were developed for chromium and the physical/chemical parameters measured
in the investigation (Table 4.1.7) to further examine the relationship between the variables.
Chromium showed a strong positive correlation with lead, arsenic, and mercury. In addition,
chromium showed a negative correlation with % solids. Previous investigations (Bolattino
and Fox. 1995, Rediske et al. 1998) established that arsenic, lead, and mercury were
associated with the tannery discharge and found in high concentrations in Tannery Bay. The
clustering of the deep stations in the PCA around these contaminants plus the Spearman
Correlations indicate that the tannery is the predominant source of metal enrichment in
western White Lake.
TABLE 4.1.7 SPEARMAN RANK ORDER CORRELATIONS FOR CHROMIUM, CHEMICAL, AND
PHYSICAL PARAMETERS FOR WHITE LAKE SEDIMENTS. (VALUES IN BOLD DENOTE
STATISTICALLY SIGNIFICANT CORRELATIONS)
Chromium with: r
Arsenic 0.644
Cadmium 0.906
Copper 0.347
Mercury 0.63
Nickel 0.063
Lead 0.616
Zinc 0.189
Depth 0.459
<63um -0.03
Total organic carbon -0.03
% Solids -0.52
Organic chromium was analyzed in the PONAR samples by extraction with sodium
pyrophosphate (Walsh and O'Halloran 1996). This fraction contains chromium bound to
alkaline extractable ligands such as humic and fulvic acids. Organically bound chromium
was found in sediments contaminated with tannery wastes in New Zealand (Walsh and
O'Halloran 1996). The results of organic chromium determinations are given in Table 4.1.8.
No detectable organic chromium was found in the stations east of Tannery Bay (WL-17,
WL-18, WL-19, and WL-20) and at WL-4. The high sand content and low organic carbon
would prevent this fraction of chromium from accumulating at this location. Stations west of
Tannery Bay had levels of organic chromium ranging from 23-55 mg/kg. A set of archived
samples that had been collected from Tannery Bay (Rediske et al. 1998) were also analyzed
(Table 4.1.8). Organic chromium in these samples ranged from 40-380 mg/kg. The location
with the lowest organic chromium fraction (1-6) was similar to WL-4 in that it contained a
52
-------
high sand fraction. Samples that were previously noted to contain hide fragments, 1-5 and I-
3, exhibited the highest levels of organic chromium (380 and 160 mg/kg, respectively). The
relationship between organic chromium and sediment toxicity will be discussed in Section
4.3.3.
TABLE 4.1.8 CONCENTRATION OF ORGANIC CHROMIUM IN WHITE LAKE SEDIMENTS.
Organic Total Organic Total
Station Chromium Chromium Station Chromium Chromium
(mg/kg) (mg/kg) (mg/kg) (mg/kg)
WL1 P
WL2P
WL3P
WL4P
WL5P
WL6P
WL7P
WL8P
WL9P
WL10P
WL11 P
WL12P
WL13P
WL14P
55
37
45
0
41
41
39
30
38
31
30
54
23
53
270
300
190
18
400
360
390
380
420
270
310
510
250
480
WL15P
WL16P
WL17P
WL18P
WL19P
WL20P
WL21 P
I-3*
I-4*
I-5*
I-6*
I-7*
I-8*
27
24
0
0
0
0
39
155
120
380
40
110
160
250
190
50
29
39
28
450
934
1890
4100
2650
2560
515
Collected in 1996 (Rediske et al. 1998)
While discharges from the tannery and Occidental/Hooker Chemical left large areas of
contaminated sediment in White Lake, samples collected near the DuPont groundwater
plume (WL-1 and WL-2) did not contain elevated levels of organic compounds. Chromium
and other metals were at concentrations consistent with the tannery discharge. No obvious
signature related to the DuPont groundwater plume was noted in the core or PONAR
samples.
4.2 Stratigraphy and Radiodating Results
Three cores were collected for radiodating and the analysis of detailed stratigraphy for
chromium. Stations were selected based on bathymetry and the chromium concentrations
measured in the initial cores. One core was collected from a deep depositional area and the
remaining two were collected at locations that showed high accumulations of chromium in
the 0-51 cm section of the initial cores. The first core (WL-2S) was collected at station WL-
2 and was located in the deep basin (20.3 m) west of Long Point (Figures 2.1 and 4.1.8) and
53
-------
near the channel to Lake Michigan. This station represented the deep depositional zone of
the lake. The second core (WL-7S) was collected at WL-7 in a shallower zone (10.8 m) east
of Long Point. This station had the highest level of chromium in the 0-51 cm zone of the
initial set of cores (600 mg/kg). The final core (WL-9S) was collected at station WL-9
located west of Dowies Point at a depth of (9.7 m). This site is nearer to Tannery Bay than
the previous cores and contained the second highest level of chromium (500 mg/kg). The
results of each core are presented in the following sections.
4.2.1 CoreWL-2S
Stratigraphy and radiodating results for WL-2S are presented in Table 4.2.1. Station WL-2S
is located at the deep point in White Lake near Long Point and within the flow path of the
old river channel (Figure 2.1). Profiles of depth and concentration for chromium, 210Pb, and
137Cs are shown on Figure 4.2.1. Elevated concentrations of chromium continue beyond the
estimated date of 1894, which indicates that the CRS model did not yield credible results for
the deeper strata. Depositional patterns for 210Pb describe three regions in the core. The top
25 cm exhibits an exponential decay pattern for the radionuclide, which indicates stable
deposition (Robbins and Herche 1993). Estimated dates within the top 19 cm of the core
appear to be realistic as a peak in 137Cs activity is noted at 15cm. This peak corresponds to
TABLE 4.2.1 STRATIGRAPHY AND RADIODATING RESULTS FOR CORE WL-2S COLLECTED
FROM WHITE LAKE, OCTOBER 2001.
Depth (cm)
3
7
11
15
19
23
27
31
35
39
43
47
51
55
59
61
Total
Chromium
mg/kg
340
341
317
347
415
481
625
688
793
1137
1915
2046
1846
1400
911
679
Ra-226
Activity
(dpm/g)
1.797
2.529
2.384
2.359
2.980
2.612
2.612
2.090
2.342
2.187
2.205
2.737
3.260
3.093
3.514
2.446
Cs-137
Activity
(dpm/g)
0.992
1.438
1.992
8.801
5.181
2.070
2.055
2.384
2.904
2.466
0.932
0.209
0.437
0.759
0.305
-0.542
Excess Pb-
210
Activity
(dpm/g)
17.667
8.904
7.538
4.637
2.198
5.012
2.318
0.970
3.385
2.598
0.000
0.000
0.000
0.000
0.000
0.000
Date at
Given
Depth
1996
1986
1977
1966
1958
1954
1947
1935
1930
1910
1890
54
-------
Chromium Concentration (mg/kg)
500 1000 1500 2000 2500
Unsupported Pb-210 (dpm)
Q.OOO 5.000 10.000 15.000 20.000 25.000 30.000
0 -
-5.000
Cs-137 activity (dpm))
0.000 5.000 10.000
15.000
10 -
20 -
£30-|
'S.
40
50 -
60 J
FIGURE 4.2.1 DEPTH AND CONCENTRATION PROFILES FOR CHROMIUM , LEAD-210, AND CESIUM-IS? AT STATION
WL-2S, WHITE LAKE, OCTOBER 2001.
55
-------
the maximum deposition of the radionuclide that occurred during 1962 from atomic testing.
The CRS model estimated the data of this interval to be 1966, indicating good agreement
with the 137Cs peak. Chromium deposition appears to be constant in the top 15 cm of the
core, which indicates a relatively constant supply of the element. Since the tannery discharge
ceased in the mid 70s, the continued deposition of chromium can be attributed to the
transport of contaminated sediment from Tannery Bay by lake currents. From 19 cm to 39
cm, 210Pb deposition is uniform. Chromium deposition increases from 415 mg/kg to 1915
mg/kg at the end of this interval. Excess 210Pb activity is absent in the region below 43 cm.
Chromium levels peak at 47 cm (2071 mg/kg) and then decrease to 795 mg/kg at the bottom
of the core (81 cm). The results of the strata below 19 cm suggest that210Pb deposition was
attenuated by dilution from excessive sedimentation. Since 226Ra inventories were relatively
consistent throughout the core, it is unlikely that sediments generated by the erosion of
surficial soils were responsible for the dilution of the 210Pb signal. A similar pattern of high
chromium levels in strata with no 210Pb inventories was noted for sediment cores taken in
Tannery Bay (Rediske et al. 1989). Dilution by the discharge of industrial waste materials
was thought to have attenuated the 210Pb signal in Tannery Bay. In the deep basin where
WL-2S is located, it is likely that the additional sedimentation was generated by primary
productivity and/or the input of organic matter. This location is 8 km from Tannery Bay and
no known source of industrial waste is present in the area. Since the historical tannery
discharge also contained high levels of nitrogen and phosphorus from the processing of
animal hides, the productivity of White Lake may have been greater during the years prior to
1960. Observations and data from Evans (1992) support this conclusion as the water quality
in White Lake was significantly degraded during the 50s and early 60s. Excessive algal
blooms, high turbidity, and degraded benthic populations were reported for this time period.
A trend of increasing water quality was noted in the late 60s. The fact that a peak in
chromium deposition is coupled with the absence of 210Pb suggests that the tannery was
discharging high levels of metal laden waste materials into White Lake prior to the early
1960s and that organic sedimentation was elevated by primary productivity.
4.2.2 CoreWL-7S
Stratigraphy and radiodating results for WL-7S are presented in Table 4.2.2. Profiles of
depth and concentration for chromium and lead are shown in Figure 4.2.2. This core was
taken at a depth of 21.5 m in the deep basin near Dowies Point (Figure 2.1). The top 11 cm
showed an exponential decay pattern for 210Pb while the remainder of the core had variable
radioisotope inventories. These data suggest a recent pattern of stable deposition followed
by a period of mixing and excess sedimentation from advection within the lake. Since White
Lake is a drowned rivermouth, storm events and currents are capable of transporting
significant amounts of sediment on an episodic basis. The layer of uniform 210Pb inventories
56
-------
TABLE 4.2.2 STRATIGRAPHY AND RADIODATING RESULTS FOR CORE WL-7S COLLECTED
FROM WHITE LAKE, OCTOBER 2001.
Total
Depth (cm) Chromium
mg/kg
7
11
15
19
23
27
31
35
39
43
47
51
55
59
61
Ra-226
Activity
(dpm/g)
Cs-137
Activity
(dpm/g)
Excess Pb-
210
Activity
(dpm/g)
Date at
Given
Depth
204
242
273
330
470
462
397
702
928
893
1052
1230
1848
1779
1418
1072
4.047
3.773
3.056
2.947
2.535
3.356
3.531
3.083
3.562
3.018
3.398
3.734
3.404
3.126
3.357
2.639
1.922
2.184
2.244
2.348
2.195
2.828
2.183
3.247
4.015
3.695
4.611
3.515
3.434
3.877
4.282
3.467
30.878
27.848
22.008
16.646
18.633
20.804
12.293
16.398
11.531
13.742
11.814
14.954
13.294
11.450
13.387
9.901
1999
1996
1992
1990
1983
1977
1971
1966
1964
1957
1951
1947
1939
1928
1918
1900
may be due to a combination of mixing and excess deposition by episodic events. The
absence of a 137Cs horizon (Figure 4.2.2) also supports the hypothesis of sediment mixing
and transport, as the radionuclide profile shows a slightly increasing deposition pattern
instead of the classic peak shape found in core WL-2S (Figure 4.2.1). In consideration of the
atypical radioisotope at this location, the dates assigned by the constant supply model cannot
be considered to be accurate. Chromium deposition patterns (Figure 4.2.2) also show the
dates to be inaccurate as the highest levels of chromium were estimated to be deposited prior
to the conversion of the tanning process in 1945. Chromium levels were relatively consistent
in the top 11 cm and then increased to a maximum of 1848 mg/kg at 51 cm. This region of
the core also contained 210Pb inventories that were more representative of exponential decay,
indicating stable sediments and a constant supply of chromium. Increasing chromium
deposition is evident in the deeper region where the 210Pb is variable. The presence of excess
210Pb throughout this region of the core indicates a continuous influx of sediment and
frequent movement out of the location. Based on the increasing and decreasing pattern, it
appears that episodic events such as storms act to remove and deposit varying amounts of
sediment at this location.
57
-------
Chromium Concentration (mg/kg)
0 500 1000 1500 2000
10 -
20 -
-------
4.2.3 CoreWL-9S
Stratigraphy and radiodating results for WL-9S are presented in Table 4.2.3. Profiles of
depth and concentration for chromium and lead are shown in Figure 4.2.3 along with the
calculated dates from the 210Pb deposition model. The radiodating results indicate that
stable sediments are not accumulating at this location. The accumulation of stable sediments
would result in a 210Pb profile that exhibits an exponential decay of the radioisotope (Robbins
and Herche 1993) similar to core WL-2S. No exponential decay pattern is visible in core
WL-2S (Table 4.2.3). Instead, a mixed layer with uniform 210Pb inventories was observed
for the first 15 cm followed by a pattern of sections with increasing and decreasing 210Pb
concentrations ranging from -11-19 dpm. The presence of excess 210Pb throughout the core
indicates a continuous influx of sediment and frequent movement out of the location. Based
on the increasing and decreasing pattern, it appears that episodic events such as storms act to
remove varying amounts of sediment from the location. The depositional pattern of
chromium also exhibits sporadic changes in concentration indicating the influence of
episodic events. The relatively uniform concentrations of chromium noted in the top 11 cm
correspond to a mixed sediment layer shown in the 210Pb profile. Chromium concentrations
peak at 31 cm and then decline to the base of the core. Station WL-9S is closer to Tannery
Bay than the two previous cores and is also located in shallower water (15.2 m).
TABLE 4.2.3 STRATIGRAPHY AND RADIODATING RESULTS FOR CORE WL-9S COLLECTED
FROM WHITE LAKE, OCTOBER 2001.
Depth (cm)
3
7
11
15
19
23
27
31
35
39
43
47
51
55
59
Total
Chromium
mg/kg
454
464
488
606
643
695
917
1201
849
778
750
732
678
722
630
Ra-226
Activity
(dpm/g)
1.797
2.529
2.384
2.359
2.980
2.339
2.612
2.612
2.090
1.839
2.040
2.205
2.272
3.326
3.093
Cs-137
Activity
(dpm/g)
0.992
1.438
1.992
8.801
5.181
3.576
2.070
2.055
2.384
2.261
2.239
1.932
1.759
0.851
0.759
Excess Pb-
210
Activity
(dpm/g)
24.098
23.798
23.858
20.499
17.389
16.061
14.196
14.602
15.705
10.988
15.262
12.225
17.246
18.967
19.093
Date at
Given
Depth
1999
1996
1991
1989
1984
1978
1972
1967
1963
1958
1955
1947
1932
1912
1890
59
-------
Chromium Concentration (mg/kg)
0 500 1000 1500
Unsupported Pb-210 (dpm)
10 20 30 40
Cs-137activity(dpm)
234
10 -
20 -
30-
40 -
50 -
60 -
10 -
20 -
o
30 -
40 -
50 -
60 -I
10 -
20 -
30 -
40 -
50 -
60 -I
FIGURE 4.2.3 DEPTH AND CONCENTRATION PROFILES FOR CHROMIUM , LEAD-210, AND CESIUM-IS?
AT STATION WL-9S, WHITE LAKE, OCTOBER 2001.
60
-------
4.2.4 Stratigraphy and Radiodating Summary
In examining the results of the three stratigraphy cores together, some important patterns in
contaminant deposition are evident. All of the cores show uniform levels of chromium
deposition in the top 10 - 15 cm. This pattern indicates that a relatively constant source of
chromium is currently present in White Lake. These data coupled with the previous
investigation (Rediske et al. 1998) suggest that the heavily contaminated sediments near the
historic tannery discharge are being transported out of the bay by currents and then deposited
throughout the lake. In addition, the lack of a standard exponential decay pattern in the
lower sections of the core illustrates that sediments in the open waters of the lake are also
mobile and influenced by currents and episodic events. Even when there is evidence of a
distinct 137Cs horizon as in WL-2S, the deeper sections of the core still contain atypical 210Pb
profiles that suggest mixed sediment layers.
The stratigraphy cores were analyzed by PIXE while the investigative samples were
evaluated by ICP. The PIXE method is a form of elemental analysis based on the
characteristics of X-rays and the nature of X-ray detection (Johansson et al. 1995). The
method uses beams of energetic ions, produced by an accelerator to generate a beam of
protons in the 2-5 MeV range, used to create inner electron shell vacancies. As these inner
shell vacancies become filled by outer shell electrons, the characteristic X-rays emitted by
this cascade effect can be detected by wavelength dispersion. PIXE techniques provide a
rapid screening of the samples for metals without sample preparation. The PIXE results
represent a total analysis of metals due to the interaction of the proton beam with all metallic
forms (Rajander et al. 1999). In contrast, the microwave digestion used for the investigative
samples provides data on acid extractable metals. Comparative studies of the two techniques
found that acid extractable digestions underestimate chromium concentrations by up to 40%
because of the stability of chromite (Ma et al. 1997, Chen and Ma 2001). Total metal
digestions involving HF are necessary to dissolve the refractory chromite. In order to
compare the results of the stratigraphy cores with the investigative samples, the core from
WL-9S was analyzed by PIXE and ICP methods. The results of the comparison study are
shown in Table 4.2.4. With respect to White Lake sediments, there appears to be a 21%
difference between the two methods (based on grand mean). Since the soils in the White
River watershed consist of glacial tills that originated in the Canadian Shield, background
levels of chromite can be expected in the core samples. The results also indicate that some of
the chromium originating in the tannery waste may be refractory to acid digestion. The
results of the top core section from the investigative samples (0-51 cm) are compared to the
same depth interval of the stratigraphy cores in Table 4.2.5. When a 21% factor is applied to
the PIXE results to account for the difference between total and extractable metals, the
results between the methods show good agreement. There appears to be some high bias
associated with the stratigraphy results that is probably related to sample collection methods.
The investigative samples were collected by VibraCore methods that tend to compress
flocculent sediments. It is possible that some of the deeper strata were included in the
VibraCore samples. It is also interesting to note that the middle core section of the
investigative samples (51-102 cm) had chromium levels that ranged from 34-38 mg/kg
(Table 4.1.3). These results suggest that anthropogenic chromium contamination does not
extend down into this region of the core.
61
-------
TABLE 4.2.4 RESULTS OF ICP AND PIXE ANALYSES FOR CHROMIUM IN CORE WL-9S
COLLECTED FROM WHITE LAKE, OCTOBER 2001.
Depth Chromium (ICP) Chromium (PIXE) %
(cm) mg/kg mg/kg Difference
3 359 454 21
7 427 464 8
11 421 488 14
15 484 606 20
19 496 643 23
23 552 695 21
27 709 917 23
31 870 1200 28
35 678 849 20
39 627 778 19
43 611 750 19
47 540 732 26
51 564 678 17
55 564 712 20
59 359 454 21
Grand
Mean 551 695 21
TABLE 4.2.5 AVERAGE AND CORRECTED DATA FOR STRATIGRAPHY CORES (OCTOBER
2001) COMPARED TO THE RESULTS OF THE TOP CORE SECTION FROM THE INVESTIGATIVE
SURVEY (OCTOBER 2000) FOR WHITE LAKE SEDIMENTS.
Stratigraphy Core Average Stratigraphy Core Corrected Investigative Core Top
Station Chromium (PIXE) Average Chromium (PIXE) Section Chromium (ICP)
mg/kg mg/kg* mg/kg**
3 695 549 470
7 869 686 600
11 712 574 500
* Corrected for 21% difference between PIXIE and ICP results
** Top Core Section Results (0-51 cm)
62
-------
4.3 Toxicity Testing Results
The toxicity evaluations of the White Lake sediments were performed during November
2000. Grab sediment samples collected from 21 different sites were evaluated using the EPA
(1994) solid phase testing protocol with Hyalella azteca and Chironomus tentans.
Conductivity, hardness, alkalinity, ammonia, and pH were determined for the culture water at
the beginning and on the tenth day of each test (Appendix E: Tables E-l, E-3). With the
exception of ammonia in most of the sediments and conductivity and hardness in M10-P,
these parameters remained relatively constant. Variations of less than 50% from initial to
final measurements for both test species were observed. Based on the initial pH values (all <
8.00) and the fact that the overlying water was exchanged prior to adding the organisms,
toxicity related to unionized ammonia was not anticipated to be a factor in these experiments.
Temperature and dissolved oxygen measurements were recorded daily throughout the
duration of the tests (Appendix E: Tables E-2, E-4). Very little variation was noted with
respect to temperature. The dissolved oxygen remained above 40% saturation in all of the
test beakers.
4.3.1 Hyalella azteca
Survival data for solid phase toxicity tests with Hyalella azteca are presented in Table
4.3.1.1. The survival in the control (WL-20P and WL-4P) treatments exceeded the required
80%. In order to group the samples based on depth, WL-20P was used as the control for the
shallow locations east of the Narrows and WL-4P was used as the control for the deep
stations. Separate statistical analyses also were performed on the two groups of data. Un-
transformed survival data were evaluated to determine whether they were consistent with a
normal distribution. The Chi-Squared distribution was used to compare the expected count
of data values at the 10th, 20th, ..., and 90th percentiles with the observed count. The sample
data from both groups were found to be consistent with those drawn from a normal
population (p > 0.01). Dunnett's Test (Table 4.3.1.2) showed a statistically significant (p <
0.05) difference for the survival data compared to control site WL-20P in 1 out of 4 shallow
stations. Sediments from site WL-16P had significantly reduced survival compared to WL-
20P (66% vs 90% respectively). Dunnett's Test (Table 4.3.1.3) showed a statistically
significant (p < 0.05) difference for the survival data compared to control site WL-4P in 1
out of 9 deep stations. Sediments from site WL-21P had significantly reduced survival
compared to WL-4P (65% vs 88% respectively). All of the other deep and shallow locations
had greater than 80% survival.
63
-------
TABLE 4.3.1.1 SUMMARY OF HYALELLA AZTECA SURVIVAL DATA OBTAINED DURING
THE 10 DAY TOXICITY TEST WITH WHITE LAKE SEDIMENTS.
(WL-4 AND WL-20 ARE CONTROLS.)
Sample
ID
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
WL-1 2
WL-1 3
WL-1 4
WL-1 5
WL-1 6
WL-1 7
WL-1 8
WL-1 9
WL-20
WL-21
Number of
Organisms
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Replicate
A
10
10
10
10
10
9
10
9
10
8
10
8
10
10
10
9
10
8
10
7
10
10
10
8
10
9
10
10
10
8
10
6
10
9
10
9
10
9
10
9
10
7
B
10
8
10
10
10
9
10
7
10
9
10
9
10
7
10
9
10
8
10
9
10
10
10
9
10
9
10
9
10
9
10
7
10
8
10
10
10
10
10
10
10
6
c
10
9
10
10
10
10
10
9
10
10
10
8
10
9
10
10
10
9
10
8
10
9
10
9
10
8
10
8
10
8
10
6
10
9
10
8
10
8
10
10
10
9
D
10
10
10
10
10
9
10
9
10
10
10
10
10
6
10
8
10
8
10
8
10
8
10
9
10
6
10
7
10
6
10
5
10
10
10
9
10
10
10
9
10
6
E
10
9
10
9
10
8
10
8
10
10
10
10
10
9
10
7
10
10
10
9
10
7
10
8
10
7
10
10
10
8
10
6
10
8
10
7
10
7
10
8
10
8
F
10
8
10
10
10
10
10
10
10
9
10
10
10
9
10
10
10
8
10
8
10
10
10
10
10
9
10
6
10
6
10
8
10
10
10
10
10
9
10
9
10
5
G
10
9
10
7
10
9
10
10
10
8
10
7
10
8
10
8
10
9
10
7
10
8
10
9
10
8
10
10
10
9
10
7
10
9
10
9
10
8
10
8
10
6
H
10
9
10
10
10
8
10
9
10
8
10
8
10
10
10
8
10
9
10
9
10
9
10
8
10
10
10
7
10
10
10
8
10
8
10
8
10
8
10
9
10
5
Survival
Mean
9.000
9.500
9.000
8.875
9.000
8.750
8.500
8.625
8.625
8.125
8.875
8.750
8.250
8.375
8.000
6.625
8.875
8.750
8.625
9.000
6.500
Std Dev
0.7559
1 .0690
0.7559
0.9910
0.9258
1.1650
1.4142
1 .0607
0.7440
0.8345
1.1260
0.7071
1.2817
1 .5980
1.4142
1 .0607
0.8345
1.0351
1 .0607
0.7559
1.4142
Variance
0.571
1.143
0.571
0.982
0.857
1.357
2.000
1.125
0.554
0.696
1.268
0.500
1.643
2.554
2.000
1.125
0.696
1.071
1.125
0.571
2.000
64
-------
TABLE 4.3.1.2 SUMMARY OF DUNNETT'S TEST ANALYSIS OFHYALELLA AZTECA SURVIVAL
DATA OBTAINED DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE SEDIMENTS
FROM SHALLOW STATIONS (< 4.5 M).
ID
WL-20P
WL-19P
WL-18P
WL-17P
WL-16P
MEAN
9.0000
8.6250
8.7500
8.8750
6.6250
TSTAT
0.0000
0.7828
0.5219
0.2609
4.9580
SIG
0.05
*
Dunnett's critical value = 2.2500. 1 Tailed, alpha = 0.05.
TABLE 4.3.1.3 SUMMARY OF DUNNETT'S TEST ANALYSIS OFHYALELLA AZTECA SURVIVAL
DATA OBTAINED DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE SEDIMENTS
FROM DEEP STATIONS (> 4.5 M).
ID
WL-4P
WL-2P
WL-3P
WL-1P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-21P
MEAN
8.8750
9.5000
9.0000
9.0000
9.0000
8.7500
8.5000
8.6250
8.6250
6.5000
TSTAT
0.0000
-1.1832
-0.2366
-0.2366
-0.2366
0.2366
0.7099
0.4733
0.4733
4.4962
SIG
0.05
*
Dunnett's critical value = 2.4800. 1 Tailed, alpha = 0.05.
65
-------
4.3.2 Chironomus tentans
Survival data for solid phase toxicity tests with Chironomus tentans are presented in Table
4.3.2.1. The survival in the control treatments (WL-4P and WL-20P) exceeded the required
70%. Un-transformed survival data were evaluated as described above with the Chi-Squared
distribution. The sample data were found to be consistent with those drawn from a normal
population (p > 0.01). Dunnett's Test (Table 4.3.2.2) showed a statistically significant (p <
0.05) difference for the survival data compared to control site WL-20P in 1 out of 4 shallow
stations. Sediments from site WL-16P had significantly reduced survival compared to WL-
20P (66% vs 90% respectively). Dunnett's Test (Table 4.3.2.3) showed a statistically
significant (p < 0.05) difference for the survival data compared to control site WL-4P in 1
out of 9 deep stations. Sediments from site WL-21P had significantly reduced survival
compared to WL-4P (65% vs 88% respectively). All of the other deep and shallow locations
had greater than 80% survival.
Chironomus tentans growth data are presented in Table 4.3.2.4. Un-transformed growth data
were found to be consistent with a Chi-Squared distribution at p > 0.01. Dunnett's Test
(Table 4.3.2.5) showed a statistically significant (p < 0.05) difference for the growth data
compared to control site WL-20P in 1 out of 4 shallow stations. Sediments from site WL-
16P had significantly reduced growth compared to WL-20P (0.5375 mg/individual vs 1.1522
mg/individual respectively). Dunnett's Test (Table 4.3.2.6) showed a statistically significant
(p < 0.05) difference for the growth data compared to control site WL-4P in 1 out of 9 deep
stations. Sediments from site WL-21P had significantly reduced growth compared to WL-4P
(0.6263 mg/individual vs 0.9834 mg/individual respectively). All of the other deep and
shallow locations had average individual weights of >0.6 mg.
4.3.3 Sediment Toxicity Data Discussion
Statistically significant (p < 0.05) acute toxicity effects were observed in the sediments from
sites WL-16 and WL-21 for the amphipod, H. azteca. In addition, statistically significant (p
< 0.05) mortality and growth rates were noted for the midge, C. tentans in sediment from the
same sites. Sediment from station located in the east bay, WL-16, contained no detectable
organic compounds and metals that were above PEC guidelines (MacDonald et al. 2000).
The toxic agent(s) present at this location were not identified in the current protocol. Given
the high level of toxicity measured in this study and the previous investigation, a more
detailed assessment of east bay area is warranted. A Toxicity Identification Evaluation (TIE)
protocol needs to be performed to examine the classification of the toxicant. The east bay is
located adjacent to the old storage reservoir for the tree bark tanning agent used from 1890-
1940. Since tannins are known to be toxic to herbivores including insects (Cowan 1999,
Bernays et al. 1989, and Kubanek et al. 2001), it is possible that this class of compounds is
responsible for the amphipod and midge mortality. The dark, opaque color of pyrophosphate
extract from
66
-------
TABLE 4.3.2.1 SUMMARY OF CHIRONOMUS TENTANS SURVIVAL DATA OBTAINED
DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE SEDIMENTS.
(WL-4 AND W-20 ARE CONTROLS.)
Sample
ID
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
WL-1 2
WL-1 3
WL-1 4
WL-1 5
WL-1 6
WL-1 7
WL-1 8
WL-1 9
WL-20
WL-21
Number of
Organisms
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Initial
Final
Replicate
A
10
7
10
8
10
8
10
8
10
9
10
6
10
8
10
8
10
8
10
7
10
7
10
7
10
6
10
9
10
10
10
7
10
10
10
8
10
7
10
8
10
6
B
10
6
10
7
10
9
10
9
10
8
10
5
10
9
10
7
10
6
10
9
10
8
10
8
10
8
10
12
10
8
10
6
10
8
10
6
10
8
10
8
10
5
C
10
8
10
8
10
8
10
8
10
7
10
8
10
7
10
6
10
7
10
8
10
10
10
7
10
5
10
8
10
8
10
5
10
8
10
8
10
7
10
8
10
6
D
10
8
10
9
10
7
10
8
10
8
10
9
10
8
10
5
10
6
10
7
10
7
10
5
10
8
10
10
10
8
10
3
10
8
10
6
10
6
10
7
10
5
E
10
8
10
8
10
8
10
9
10
9
10
7
10
6
10
9
10
8
10
10
10
11
10
10
10
5
10
10
10
4
10
5
10
7
10
7
10
9
10
9
10
6
F
10
9
10
8
10
9
10
8
10
8
10
6
10
7
10
10
10
6
10
7
10
8
10
5
10
7
10
9
10
4
10
5
10
6
10
6
10
9
10
7
10
5
G
10
9
10
9
10
8
10
7
10
8
10
8
10
9
10
9
10
9
10
9
10
11
10
8
10
10
10
9
10
8
10
8
10
8
10
8
10
7
10
6
10
7
H
10
8
10
8
10
8
10
8
10
7
10
9
10
9
10
8
10
6
10
8
10
7
10
7
10
7
10
9
10
6
10
4
10
7
10
7
10
8
10
8
10
5
Survival
Mean
7.875
8.125
8.125
8.125
8.000
7.250
7.875
7.750
7.000
8.125
8.625
7.125
7.000
9.500
7.000
5.375
7.750
7.000
7.625
7.625
5.625
Std Dev
0.9910
0.6409
0.6409
0.6409
0.7559
1.4880
1.1260
1.6690
1.1952
1.1260
1.7678
1.6421
1.6903
1.1952
2.1381
1.5980
1.1650
0.9258
1.0607
0.9161
0.7440
Variance
0.982
0.411
0.411
0.411
0.571
2.214
1.268
2.786
1.429
1.268
3.125
2.696
2.857
1.429
4.571
2.554
1.357
0.857
1.125
0.839
0.554
67
-------
TABLE 4.3.2.2 SUMMARY OF DUNNETT'S TEST ANALYSIS OF CHIRONOMUS TENTANS
SURVIVAL DATA OBTAINED DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE
SEDIMENTS FROM SHALLOW STATIONS (<4.5 M).
ID
WL-20P
WL-19P
WL-18P
WL-17P
WL-16P
MEAN
7.6250
7.6250
7.0000
7.7500
5.3750
TSTAT
0.0000
0.0000
1.0773
-0.2155
3.8781
SIG
0.05
*
Dunnett's critical value = 2.2500. 1 Tailed, alpha = 0.05.
TABLE 4.3.2.3 SUMMARY OF DUNNETT'S TEST ANALYSIS OF CHIRONOMUS TENTANS
SURVIVAL DATA OBTAINED DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE
SEDIMENTS FROM DEEP STATIONS (> 4.5 M).
ID
WL-4P
WL-1P
WL-2P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-10P
WL-21P
MEAN
8.1250
7.8750
8.1250
8.0000
7.2500
7.8750
7.7500
7.0000
8.1250
5.6250
TSTAT
0.0000
0.4585
0.0000
0.2292
1.6047
0.4585
0.6877
2.0632
0.0000
5.6250
SIG
0.05
*
Dunnett's critical value = 2.4800. 1 Tailed, alpha = 0.05.
68
-------
TABLE 4.3.2.4 SUMMARY OF CHIRONOMUS TENTANS DRY WEIGHT DATA OBTAINED
DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE SEDIMENTS.
(WL-4 AND WL-20 ARE CONTROLS.)
Sample
WL-1 A
WL-1 B
WL-1 C
WL-1 D
WL-1 E
WL-1 F
WL-1 G
WL-1 H
WL-2A
WL-2B
WL-2C
WL-2D
WL-2E
WL-2F
WL-2G
WL-2 H
WL-3A
WL-3B
WL-3C
WL-3D
WL-3E
WL-3F
WL-3G
WL-3 H
WL-4 A
WL-4B
WL-4C
WL-4D
WL-4E
WL-4F
WL-4G
WL-4H
WL-5 A
WL-5B
WL-5C
WL-5D
WL-5E
WL-5F
WL-5G
WL-5H
WL-6A
WL-6B
WL-6C
WL-6D
WL-6E
WL-6F
WL-6G
WL-6 H
WL-7 A
WL-7B
WL-7C
WL-7 D
WL-7E
WL-7 F
WL-7G
WL-7 H
Individual
Weight (mg)
0.9714
1.2167
0.9500
0.9875
1.0500
0.8667
0.9111
1.0625
0.9500
1.0429
1.2000
0.8444
0.9500
1.0125
0.8222
1.1250
1.3750
1.0667
1.0500
1.3571
1.4000
2.1000
1.8250
1.4375
0.8250
0.8667
1.1125
0.7750
1.1111
1.0750
1.0143
1.0875
1.1333
1.1250
1.0857
1.0750
0.8111
0.8125
0.7625
0.9429
1.1833
0.9200
1.1000
1.1556
1.0571
0.8667
1.1000
0.9444
1.3000
0.9222
1.2000
0.9125
1.2833
1.1571
0.9778
0.9667
Average
Individual
Weight (mg)
1 0020
0 9685
Sample
WL-8 A
WL-8 B
WL-8C
WL-8D
WL-8E
WL-8 F
WL-8G
WL-8H
WL-9 A
WL-9B
WL-9C
WL-9D
WL-9E
WL-9F
WL-9G
WL-9H
WL-1 0 A
WL-10 B
WL-10C
WL-10 D
WL-10 E
WL-1 OF
WL-10G
WL-10 H
WL-11 A
WL-11 B
WL-11 C
WL-11 D
WL-11 E
WL-11 F
WL-1 1 G
WL-11 H
WL-1 2 A
WL-1 2 B
WL-1 2 C
WL-1 2 D
WL-1 2 E
WL-1 2 F
WL-1 2 G
WL-1 2 H
WL-1 3 A
WL-1 3 B
WL-1 3 C
WL-1 3 D
WL-1 3 E
WL-1 3 F
WL-1 3 G
WL-1 3 H
WL-1 4 A
WL-1 4 B
WL-1 4 C
WL-1 4 D
WL-1 4 E
WL-1 4 F
WL-1 4 G
WL-1 4 H
Individual
Weight (mg)
1.0875
1.4571
1.9000
1.5800
0.9556
1.0100
1.0333
1.0500
1.0250
1.0167
0.9429
1.2667
0.9375
1.0000
0.8667
1.0000
0.9143
0.7333
0.9000
1.0714
0.9900
1.0857
0.8556
0.8625
0.9714
0.9750
0.8600
0.9143
0.9364
1.1500
0.9636
1.0714
0.9286
0.8250
0.8714
0.9600
0.5800
1.0600
1.0375
0.8571
1.9000
1.3750
1.3200
1.3875
0.5400
1.1857
0.9600
0.9143
1.1111
0.8083
0.9750
0.9600
1.0000
0.9667
1.1333
1.1444
Average
Individual
Weight (mg)
1.2592
1.0069
0.9266
0.9803
0.8900
1.1978
1.0124
Sample
WL-1 5 A
WL-1 5 B
WL-1 5 C
WL-1 5 D
WL-1 5 E
WL-1 5 F
WL-1 5 G
WL-1 5 H
WL-1 6 A
WL-1 6 B
WL-1 6 C
WL-1 6 D
WL-1 6 E
WL-1 6 F
WL-1 6 G
WL-1 6 H
WL-1 7 A
WL-1 7 B
WL-1 7 C
WL-1 7 D
WL-1 7 E
WL-1 7 F
WL-1 7 G
WL-1 7 H
WL-1 8 A
WL-1 8 B
WL-1 8 C
WL-1 8 D
WL-1 8 E
WL-1 8 F
WL-1 8 G
WL-1 8 H
WL-1 9 A
WL-1 9 B
WL-1 9 C
WL-1 9 D
WL-1 9 E
WL-1 9 F
WL-1 9 G
WL-1 9 H
WL-20 A
WL-20 B
WL-20 C
WL-20 D
WL-20 E
WL-20 F
WL-20 G
WL-20 H
WL-21 A
WL-21 B
WL-21 C
WL-21 D
WL-21 E
WL-21 F
WL-21 G
WL-21 H
Individual
Weight (mg)
1.0700
1.1125
1.0625
1.1875
1.5250
1.9000
1.9875
0.9000
0.7857
0.6111
0.4625
0.3667
0.7250
0.2600
0.7500
0.3250
0.7636
1.0125
1.0500
0.9500
1.1429
1.1000
1.0375
1.0000
0.8625
1.0500
0.9000
1.1500
1.0714
1.0500
0.9500
0.9429
1.0857
1.1333
0.8857
0.9333
0.9556
0.8111
1.0714
1.0714
1.1429
0.9875
1.1000
0.9571
1.9667
0.7714
1.1667
1.1250
0.7000
0.5000
0.6000
0.6600
0.6333
0.6800
0.6571
0.5800
Average
Individual
Weight (mg)
1.3431
0.5357
1.0071
0.9971
0.9935
1.1522
0.6263
69
-------
TABLE 4.3.2.5 SUMMARY OF DUNNETT'S TEST ANALYSIS OF CHIRONOMUS TENTANS
GROWTH DATA OBTAINED DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE
SEDIMENTS FROM SHALLOW STATIONS (<4.5 M).
ID
WL-20P
WL-19P
WL-18P
WL-17P
WL-16P
MEAN
1.1522
0.9935
0.9971
1.0071
0.5357
TSTAT
0.0000
1.6051
1.4816
1.4816
6.1733
SIG
0.05
*
Dunnett's critical value = 2.2500. 1 Tailed, alpha = 0.05.
TABLE 4.3.2.6 SUMMARY OF DUNNETT'S TEST ANALYSIS OF CHIRONOMUS TENTANS
GROWTH DATA OBTAINED DURING THE 10 DAY TOXICITY TEST WITH WHITE LAKE
SEDIMENTS FROM DEEP STATIONS (> 4.5 M).
ID
WL-4P
WL-2P
WL-3P
WL-1P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-21P
MEAN
0.9834
0.9934
1.4514
1.0020
0.9685
1.0409
1.0900
1.2592
1.0069
0.6263
TSTAT
0.0000
-0.2551
-4.7197
0.2551
-0.6378
-1.1480
-2.9339
-0.1276
0.5102
3.5717
SIG
0.05
*
Dunnett's critical value = 2.4800. 1 Tailed, alpha = 0.05.
WL-16 provides indirect evidence of the presence of high levels of tannins due to their
solubility in alkaline conditions. The toxicity observed at WL-21 was most likely due to the
presence of PCBs (22 mg/kg) and/or chlorinated hydrocarbons. This area was dredged in
2003 and further toxicity evaluations are not necessary.
No correlation was found between amphipod toxicity and chromium concentrations in
Tannery Bay sediments in the previous investigation (Rediske et al. 1998). Table 4.3.3.1
70
-------
contains the 1996 data for total chromium and amphipod toxicity plus the recently measured
values of organic chromium. The correlation results for amphipod toxicity and total
chromium and organic chromium are displayed in Figures 4.3.3.1 and 4.3.3.2, respectively.
The results clearly show that a significant correlation exists between organic chromium and
TABLE 4.3.3.1 SUMMARY OF RESULTS OF TOTAL CHROMIUM, ORGANIC CHROMIUM, AND
AMPHIPOD SURVIVAL FOR WHITE LAKE SEDIMENTS (REDISKE ET AL. 1998). (ORGANIC
CHROMIUM ANALYSIS PERFORMED ON ARCHIVED SEDIMENT FROM 1996.)
Total
Station
E-l
1-1
1-2
1-3
1-4
1-5
1-6
1-7
1-8
Cr
(mg/kg)
35
212
259
934
1890
4100
2650
2560
515
Survival
H.
azteca
84
9
1
20
53
9
60
41
23
Organic
Cr
(mg/kg)
160
120
380
40
110
155
33
58
27
I 30
0 500 1000 1500 2000 2500 3000 3500 4000 4500
Total Chromium (mg/kg)
FIGURE 4.3.3.1 RELATIONSHIP BETWEEN TOTAL CHROMIUM AND AMPHIPOD SURVIVAL
FOR TANNERY BAY SEDIMENTS (REDISKE ET AL. 1998).
71
-------
70 -,
60
50
FT = 0.6902
ro
o
40
ro
>
'> 30
W
20
10
50 100 150 200 250
Organic Chromium (mg/kg)
300
350
400
FIGURE 4.3.3.2 RELATIONSHIP BETWEEN ORGANIC CHROMIUM AND AMPHIPOD
SURVIVAL FOR TANNERY BAY SEDIMENTS (REDISKE ET AL. 1998). (ORGANIC CHROMIUM
ANALYSIS PERFORMED ON ARCHIVED SEDIMENT FROM 1996.)
amphipod toxicity (r2=0.6902). No correlation was observed for total chromium and
amphipod toxicity. Chromium (III) is anticipated to be the only form of the metal present in
the sediments of White Lake due to their reducing nature (ENVCA 1994). While trivalent
chromium compounds have low membrane permeabilities (Eisler 1986), organically bound
metals exhibit increased absorption (Barnhart 1997). Once in the cell, chromium (III) has
been shown to bind with DNA and induce conformational changes in bio molecules (Snow
1994). In consideration of these chemical properties and the correlation with amphipod
mortality, it is possible that the organic chromium fraction in the sediments of Tannery Bay
is responsible for the observed toxicity. More research would be required to link cause and
effect with the organic chromium fraction. The presence of the decomposing animal hides in
Tannery Bay may contribute a form of organic chromium that is more toxic than the material
found in the remainder of the lake.
72
-------
4.4 Benthic Macroinvertebrate Results
Triplicate PONAR grab samples were used to characterize the benthic macroinvertebrate
populations at each of the investigative stations. The locations, depths, and physical
characteristics of the sediments are given in Table 2.2. Benthic macroinvertebrate
populations were assessed by three methods. These data were first analyzed for differences
in taxa and total number of organisms and the results summarized in Section 4.4.1. A further
analysis of these data using trophic indices and diversity metrics was then conducted and
presented in Section 4.4.2. Finally, the community composition on an organismal level was
statistically analyzed in Section 4.4.3 to determine if differences in community composition
were associated with contaminant concentration and distribution.
4.4.1 Benthic Macroinvertebrate Results Of Individual Samples
The population composition and abundance data are summarized in Table 4.4.1.1 by mean
and standard deviation for each station. The results for each replicate are presented in
Appendix F, Table F-l. The general distribution of organisms is shown in Figure 4.4.1.1.
Tubificids dominated the benthic macroinvertebrate assemblages at most stations.
Nematodes were the dominant taxon at WL-12, WL-9, and WL-14. Chironomids also were
abundant at most stations. Benthic populations show an increase in both total numbers and
species compared to the historic data reported by Evans (1992) for the 1980s. A summary
of total organisms and taxometric groups is presented in Table 4.4.1.2. Total density was
generally high and ranged between 2,297/m2 and 34,405/m2 with 15 of 21 sites having >4000
organisms/m2. Tubificidae were the most abundant group at all but three of the sites
sampled, comprising between 1,880/m2 and 30,171/m2. Fifteen of the locations had tubificid
populations that accounted for 75% of the total organisms. Four species, Aulodrilus
limnobius, Aulodriluspigueti, Limnodrilus hoffmeisteri, and Ilyodrilus templetoni were found
at most sites (Table 4.4.1). One of the more pollution tolerant species, L. hqffmeisteri, was
found at all sites and was the dominant tubificid taxon. Howmiller and Scott (1977) and
Milbrink (1983) classified benthic macroinvertebrate assemblages dominated by these
species as enriched with organic (nutrient) materials. Sites with the highest chromium levels
(WL-9, WL-12, and WL-14) had lower tubificid densities (45%, 23%, and 37%
respectively). WL-20, the control station, was also characterized by a lower percentage of
these organisms (31%) and a slightly larger abundance of amphipods (35%). The shallow
depth and presence of macrophytes at this station provided an environment more conducive
to the growth of amphipods.
Nematoda were the second most abundant group in White Lake with densities that ranged
from 0/m2 to 7,7807 m2 (Table 4.4.1.2). Stations WL-9, WL-12, and WL-14 had nematode
densities of 47%, 72%, and 55% of the total population, respectively, and the organisms were
found in greater abundance than tubificids. This taxon was not found in significant
quantities in the shallow stations (WL-16 - WL20) and several of the deeper locations (WL-
2, WL-3, WL-4, and WL-7). Nematodes are generally considered part of the microbenthos,
73
-------
TABLE 4.4.1.1 BENTHIC MACROINVERTEBRATE DISTRIBUTION IN WHITE LAKE
(#/M2), OCTOBER 2000. MEAN NUMBER OF ORGANISMS AND STANDARD DEVIATION
REPORTED FOR EACH STATION.
Taxa
Amphipoda
Gammarus
Hyallela
Isopoda
Mollusca
Gastropoda
Amnicola
Physa
Valvata tricarinata
Viviparous
Bivalvia
Dreissena polymorpha
Pisidium
Sphaerium
Annelida
Tubificidae
Aulodrilus limnobius
Aulodrilus pigueti
llyodrilus templetoni
Limnodrilus hoffmeisteri
Limnodrilus claparianus
Quistrodrillus
Naididae
Haemonais waldvogeli
Hirundinea - Glossiphoniidae
Helobdella
Nematoda
Tricladida
Planaridae
Diptera
Chaoboridae
Chaoborus punctipennis
Ceratapogonidae
Chironomidae
Ablabesmyia
Chironomus
Clinotanypus
Coelotanypus
Cryptochironomus
Dicrotendipes
Heterotrissocladius
Paraphaenocladius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironomus
Tanypus
Ephemeroptera
Caenis
Ephemera
Hexagenia
Isonychia
Trichoptera
Polycentroapodidae
Pseudosfenop/7y/ax
Megaloptera
Stalls
Hydracarina
Odonata - Zygoptera
WL-1
Mm*
0
0
0
0
0
0
14
0
0
0
0
0
57
0
0
0
0
0
703
2612
0
0
0
0
0
0
502
0
0
0
0
1292
0
43
0
57
0
0
0
43
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
0
0
0
0
0
21
0
0
0
0
0
61
0
0
0
0
0
55
1668
0
0
0
0
0
0
354
0
0
0
0
745
0
75
0
35
0
0
0
75
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-2
Mm*
0
14
14
0
0
0
43
0
0
0
0
0
100
0
0
0
93
0
926
2340
0
0
0
0
0
0
14
0
0
0
0
2497
0
129
0
646
0
0
0
100
0
0
0
0
0
14
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
21
21
0
0
0
41
0
0
0
0
0
71
0
0
0
25
0
128
1647
0
0
0
0
0
0
25
0
0
0
0
1422
0
114
0
366
0
0
0
101
0
0
0
0
0
25
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-3
Mm*
0
14
0
0
0
0
72
0
0
0
0
14
129
0
0
0
43
32
54
1521
0
0
0
0
0
0
14
0
0
0
0
1565
0
0
0
72
0
0
0
0
0
0
14
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
21
0
0
0
0
81
0
0
0
0
21
75
0
0
0
49
41
124
1182
0
0
0
0
0
0
21
0
0
0
0
843
0
0
0
60
0
0
0
0
0
0
21
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL^l
Mm*
0
43
0
0
0
0
29
0
0
0
0
129
115
0
0
0
132
220
265
569
178
0
0
14
0
0
0
0
0
0
0
761
0
0
0
29
0
0
0
14
0
0
0
0
0
57
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
38
0
0
0
0
25
0
0
0
0
107
64
0
0
0
55
100
183
895
120
0
0
21
0
0
0
0
0
0
0
537
0
0
0
25
0
0
0
21
0
0
0
0
0
36
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-5
Mm*
0
0
0
0
0
0
57
0
0
0
0
29
43
0
0
0
646
0
517
6028
0
0
0
0
0
0
646
0
0
0
0
445
0
129
0
330
0
0
0
0
0
0
0
0
0
86
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
0
0
0
0
0
99
0
0
0
0
50
23
0
0
0
52
0
36
3908
0
0
0
0
0
0
434
0
0
0
0
243
0
75
0
192
0
0
0
0
0
0
0
0
0
70
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-6
Mm*
0
14
0
0
0
0
57
0
0
0
0
0
14
0
0
0
733
183
504
2612
0
0
0
0
0
0
646
0
14
0
0
1077
0
230
0
1435
0
0
14
43
0
0
14
0
0
29
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
25
0
0
0
0
36
0
0
0
0
0
21
0
0
0
157
85
235
1880
0
0
0
0
0
0
351
0
21
0
0
597
0
163
0
883
0
0
21
75
0
0
21
0
0
43
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-7
#/mz
0
29
0
0
0
0
43
0
0
0
0
144
29
0
0
0
21
4
4
1234
0
0
0
0
0
0
0
0
0
0
0
330
0
0
0
43
0
0
14
0
0
0
0
0
0
14
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
25
0
0
0
0
41
0
0
0
0
128
25
0
0
0
79
50
50
1109
0
0
0
0
0
0
0
0
0
0
0
229
0
0
0
41
0
0
25
0
0
0
0
0
0
25
0
0
0
0
0
0
0
0
0
0
0
0
0
0
74
-------
TABLE 4.4.1.1 (CONTINUED) BENTHIC MACROINVERTEBRATE DISTRIBUTION IN WHITE
LAKE (#/M2), OCTOBER 2000. MEAN NUMBER OF ORGANISMS AND STANDARD DEVIATION
REPORTED FOR EACH STATION.
WL-8
Taxa
Amphipoda
Gammarus
Hyallela
Isopoda
Mollusca
Gastropoda
Amnicola
Physa
Valvata tricarinata
Viviparous
Bivalvia
Dreissena polymorpha
Pisidium
Sphaerium
Annelida
Tubificidae
Aulodrilus limnobius
Aulodrilus pigueti
llyodrilus templetoni
Limnodrilus hoffmeisteri
Limnodrilus claparianus
Quistrodrillus
Naididae
Haemonais waldvogeli
Hirundinea - Glossiphoniidae
Helobdella
Nematoda
Tricladida
Planaridae
Diptera
Chaoboridae
Chaoborus punctipennis
Ceratapogonidae
Chironomidae
Ablabesmyia
Chironomus
Clinotanypus
Coelotanypus
CryptDchironomus
Dicrotendipes
Heterotrissocladius
Paraphaenocladius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironomus
Tanypus
Ephemeroptera
Caenis
Ephemera
Hexagenia
Isonychia
Trichoptera
Polycentroapodidae
Pseudostenophylax
Megaloptera
Sialis
Hydracarina
Odonata - Zygoptera
mm'
0
0
0
0
0
0
115
0
0
0
0
0
57
0
0
0
660
110
220
3746
0
0
0
0
0
0
1177
0
0
0
0
201
14
72
0
215
0
0
14
0
14
0
0
0
14
115
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
0
0
0
0
0
120
0
0
0
0
0
85
0
0
0
55
21
43
2541
0
0
0
0
0
0
705
0
0
0
0
129
21
64
0
130
0
0
21
0
25
0
0
0
21
107
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-9
mm'
0
29
0
0
0
0
43
0
0
0
0
86
100
0
0
0
785
0
349
1270
423
0
0
0
0
0
3804
0
0
0
0
158
0
0
0
230
0
0
0
0
0
0
14
0
0
144
0
0
0
0
0
0
0
0
0
14
0
0
0
0
STDEV
0
25
0
0
0
0
41
0
0
0
0
101
101
0
0
0
87
0
35
1363
88
0
0
0
0
0
2569
0
0
0
0
126
0
0
0
153
0
0
0
0
0
0
21
0
0
89
0
0
0
0
0
0
0
0
0
21
0
0
0
0
WL-10
mm'
0
29
0
0
0
0
29
0
0
0
0
43
86
0
0
0
0
112
419
1409
328
0
0
14
0
0
172
0
0
0
0
1077
0
0
0
115
0
0
0
0
0
0
0
0
0
29
14
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
43
0
0
0
0
43
0
0
0
0
41
70
0
0
0
0
49
119
748
148
0
0
21
0
0
163
0
0
0
0
598
0
0
0
120
0
0
0
0
0
0
0
0
0
25
21
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-11
mm'
0
14
0
0
0
0
14
0
0
0
0
0
0
0
0
0
298
119
1491
6967
0
683
0
14
0
0
1277
0
0
0
0
416
0
301
0
904
0
0
0
29
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
25
0
0
0
0
21
0
0
0
0
0
0
0
0
0
60
25
536
1432
0
81
0
21
0
0
697
0
0
0
0
242
0
172
0
490
0
0
0
25
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-12
mm'
0
0
0
0
0
0
57
14
0
0
0
43
0
0
0
0
215
0
431
1421
0
0
0
0
0
0
7780
0
0
0
0
129
14
43
0
172
0
0
0
0
0
0
0
0
0
115
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
0
0
0
0
0
61
25
0
0
0
64
0
0
0
0
25
0
150
675
0
0
0
0
0
0
4390
0
0
0
0
76
21
41
0
143
0
0
0
0
0
0
0
0
0
105
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-13
mm'
0
43
0
0
0
0
129
0
0
0
0
29
0
0
0
0
1837
0
0
2110
0
0
0
0
0
0
574
0
0
0
0
201
0
72
0
144
0
0
0
0
0
0
0
0
0
115
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
23
0
0
0
0
69
0
0
0
0
43
0
0
0
0
742
0
0
1247
0
0
0
0
0
0
440
0
0
0
0
139
0
52
0
104
0
0
0
0
0
0
0
0
0
89
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-14
mm'
0
57
0
14
0
0
43
0
0
0
0
72
0
0
0
0
0
0
675
2770
0
0
0
0
0
0
5698
0
14
0
0
0
14
72
0
273
0
0
57
0
0
14
0
0
0
158
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
85
0
21
0
0
38
0
0
0
0
74
0
0
0
0
0
0
321
932
0
0
0
0
0
0
3620
0
21
0
0
0
21
60
0
162
0
0
49
0
0
25
0
0
0
97
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-15
mm'
0
14
0
0
0
0
172
0
0
0
0
57
0
0
0
0
514
73
73
1852
0
0
0
0
0
0
617
0
0
0
0
0
43
115
0
359
0
43
72
0
0
0
0
0
0
172
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
21
0
0
0
0
110
0
0
0
0
35
0
0
0
0
156
21
25
760
0
0
0
0
0
0
592
0
0
0
0
0
41
77
0
381
0
38
52
0
0
0
0
0
0
130
0
0
0
0
0
0
0
0
0
0
0
0
0
0
75
-------
TABLE 4.4.1.1 (CONTINUED) BENTHIC MACROINVERTEBRATE DISTRIBUTION IN WHITE
LAKE (#/M2), OCTOBER 2000. MEAN NUMBER OF ORGANISMS AND STANDARD DEVIATION
REPORTED FOR EACH STATION.
Taxa
Amphipoda
Gammarus
Hyallela
Isopoda
Mollusca
Gastropoda
Amnicola
Physa
Valvata tricarinata
Viviparous
Bivalvia
Dreissena polymorpha
Pisidium
Sphaerium
Annelida
Tubificidae
Aulodrilus limnobius
Aulodrilus pigueti
llyodhlus templetoni
Limnodrilus hoffmeisteri
Limnodrilus claparianus
Quistrodrillus
Naididae
Haemonais waldvogeli
Hirundinea - Glossiphoniidae
Helobdella
Nematoda
Tricladida
Planaridae
Diptera
Chaoboridae
Chaoborus punctipennis
Ceratapogonidae
Chironomidae
Ablabesmyia
Chironomus
Clinotanypus
Coelotanypus
Cryptochironomus
Dicrotendipes
Heterotrissocladius
Paraphaenocladius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironom us
Tanypus
Ephemeroptera
Caenis
Ephemera
Hexagenia
Isonychia
Trichoptera
Polycentroapodidae
Pseudostenophylax
Megaloptera
Sialis
Hydracarina
Odonata - Zygoptera
WL-16
#/m2
0
29
0
0
0
0
43
0
0
0
0
244
0
0
0
0
0
0
890
2225
0
0
0
0
0
0
14
0
29
0
0
0
14
86
0
115
0
0
0
0
0
0
0
0
0
57
0
0
0
0
0
0
0
0
0
0
0
14
0
0
STDEV
0
25
0
0
0
0
38
0
0
0
0
226
0
0
0
0
0
0
25
110
0
0
0
0
0
0
21
0
43
0
0
0
25
81
0
64
0
0
0
0
0
0
0
0
0
60
0
0
0
0
0
0
0
0
0
0
0
25
0
0
WL-17
#/m2
0
57
0
0
0
0
72
29
0
0
0
72
43
0
0
0
0
2411
0
1716
0
322
0
0
0
0
0
0
0
0
0
0
0
0
0
29
0
0
144
0
0
0
0
0
0
43
0
29
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
36
0
0
0
0
42
43
0
0
0
81
41
0
0
0
0
83
0
174
0
64
0
0
0
0
0
0
0
0
0
0
0
0
0
23
0
0
123
0
0
0
0
0
0
41
0
43
0
0
0
0
0
0
0
0
0
0
0
0
WL-18
#/m2
0
43
0
0
0
0
14
0
0
14
0
86
0
0
0
0
0
115
115
1306
0
0
0
0
0
0
14
0
0
0
0
0
14
187
0
43
0
0
0
0
0
0
0
0
0
57
0
0
0
0
0
29
0
0
0
0
0
0
0
0
STDEV
0
23
0
0
0
0
25
0
0
25
0
82
0
0
0
0
0
0
0
0
0
0
0
0
0
0
21
0
0
0
0
0
21
137
0
64
0
0
0
0
0
0
0
0
0
85
0
0
0
0
0
23
0
0
0
0
0
0
0
0
WL-19
#/m2
0
43
0
0
0
0
57
0
0
0
0
0
0
0
0
0
0
165
165
1837
0
0
0
0
0
0
14
0
0
0
0
0
0
172
29
43
57
0
129
0
0
0
0
0
0
57
0
0
0
0
0
29
0
0
0
0
0
0
0
0
STDEV
0
41
0
0
0
0
49
0
0
0
0
0
0
0
0
0
0
0
0
56
0
0
0
0
0
0
21
0
0
0
0
0
0
230
23
38
49
0
76
0
0
0
0
0
0
60
0
0
0
0
0
43
0
0
0
0
0
0
0
0
WL-20
#/m2
0
2483
230
100
0
0
144
14
14
0
0
201
0
0
0
0
0
0
215
1521
0
0
0
0
0
14
0
0
431
0
0
0
115
560
0
86
0
0
57
0
0
0
0
14
0
301
0
0
0
14
14
129
14
0
14
0
0
0
14
57
STDEV
0
2312
290
101
0
0
142
25
21
0
0
247
0
0
0
0
0
0
149
136
0
0
0
0
0
25
0
0
590
0
0
0
98
422
0
76
0
0
56
0
0
0
0
21
0
164
0
0
0
21
25
129
25
0
25
0
0
0
25
99
WL-21
#/m2
0
100
0
0
0
0
86
0
0
0
0
43
144
0
0
0
3986
996
5381
18444
0
0
0
0
0
14
2268
0
0
0
0
976
0
258
0
976
0
0
14
0
0
0
0
14
0
316
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
88
0
0
0
0
74
0
0
0
0
38
99
0
0
0
1154
281
1223
9279
0
0
0
0
0
21
1337
0
0
0
0
594
0
281
0
691
0
0
25
0
0
0
0
21
0
192
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL-21 DUD
#/m2
0
244
0
0
0
0
43
0
0
0
0
14
100
14
0
0
772
114
772
5177
0
0
0
0
0
0
330
0
0
0
0
488
0
187
0
646
0
0
14
0
0
0
14
0
0
244
0
0
0
0
0
0
0
0
0
0
0
0
0
0
STDEV
0
132
0
0
0
0
41
0
0
0
0
25
88
25
0
0
292
45
406
2644
0
0
0
0
0
0
309
0
0
0
0
483
0
161
0
362
0
0
21
0
0
0
21
0
0
136
0
0
0
0
0
0
0
0
0
0
0
0
0
0
76
-------
TABLE 4.4.1.2 MEAN ABUNDANCE (#/M2) AND RELATIVE DENSITIES (%) OF MAJOR
TAXONOMIC GROUPS IN WHITE LAKE, OCTOBER 2000.
Station
N
Tuberficidae (%) Nematoda (%) Chironomidae (%) Amphipoda (%) Other
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
WL-12
WL-13
WL-14
WL-15
WL-21
WL-16
WL-17
WL-18
WL-19
WL-20
4521
4880
2713
2612
9287
7378
2297
7119
8067
3660
12947
10736
5569
10277
4981
34405
4177
4196
2383
3172
7162
3804
3804
2383
2182
7966
4866
1981
5311
3603
3129
10392
2497
4464
3804
3316
30171
3531
3679
1880
2541
2253
84
78
88
84
86
66
86
75
45
85
80
23
80
37
67
88
85
88
79
80
31
502
14
14
0
646
646
0
1177
3804
172
1277
7780
574
5698
617
2268
14
0
14
14
0
11
0
1
0
7
9
0
17
47
5
10
72
10
55
12
7
0
0
1
1
0
144
890
86
100
545
1765
72
445
388
158
1234
330
330
574
761
1579
258
244
287
488
1019
3
18
3
4
6
24
3
6
5
4
10
3
6
6
15
5
6
6
12
15
14
0
14
14
43
0
14
29
0
29
29
14
0
43
57
14
100
29
57
43
43
2483
0
0
1
2
0
0
1
0
0
1
0
0
1
1
0
0
1
1
2
1
35
72
158
215
287
129
86
215
187
244
172
29
129
158
144
273
287
344
215
158
86
1407
however it is evident that larger forms were retained by the screen during elutriation. Very
little information is available on the pollution tolerance of these organisms.
Densities of Chironomidae ranged between 72/m2 and 1,765/m2 and this taxa group was the
third most abundant group at 8 of 21 of the stations sampled (Table 4.4.1.2). A total of 15
taxa were identified (Table 4.4.1.1). Chironomus spp. was found at all sites and Procladius
spp. was present at 18 of the 21 stations. Abundance of Chironomus spp. ranged from 29/m2
to 1,435/m2 and was generally the most common chironomid encountered. Procladius spp.
abundance was low and did not exceed 301/m2. With the exception of Dicrotendipes spp. and
Cryptochironomus spp., the remaining species were found infrequently and were generally
low in abundance. Organisms from these two genera are predatory in nature and do not
exclusively feed on organic detritus like Chironomus spp. (Berg 1995). Sites with the highest
levels of heavy metals (M-5, M-6, and M-7) had chironomid populations dominated by this
organism, which may suggest an impact from contaminated sediments. Chironomus was the
most abundant midge genus in the enriched stations with the highest oligochaete densities.
77
-------
35000
30000
Western White Lake
v %
DN
• Tubificidae
D Nematoda
D Chironomidae
• Amphipoda
D Other
Station
FIGURE 4.4.1.1 GENERAL DISTRIBUTION OF BENTHIC MACROINVERTEBRATES IN WHITE LAKE, OCTOBER 2000.
78
-------
Station WL-20 was very different than the other stations with respect to macroinvertebrate
composition as amphipods were the dominant genera (35%) along with four mayfly taxa plus
odonata and trichoptera species. The latter three groups were not present in the other
shallow stations. WL-20 was located in closest proximity to the mouth of the White River
and away from the marinas. The absence of both physical and chemical anthropogenic
disturbance at this station influenced the quality of the macroinvertebrate population at this
location.
4.4.2 Analysis of Macroinvertebrate Results Using Trophic Indices and Diversity Metrics
The benthic macroinvertebrate data were analyzed by a variety of trophic status indices and
diversity metrics. The following indices and metrics were utilized:
• Shannon Weaver Diversity (Krebs 1989)
• Margalefs Richness (Krebs 1989)
• Evenness (Krebs 1989)
• Pielou's J (Krebs 1989)
• Oligochaete Index (Howmiller and Scott 1977, Hilsenhoff 1987)
• Chironomid Index (Hilsenhoff 1987)
• Oligochaete + Chironomid Index (*)
• Trophic Index (Hilsenhoff 1987)
* Modified from Howmiller and Scott (1977)
Tolerance values used to calculate the Trophic Index and the individual indices for
Chironomids and Oligochaetes were taken from Winnell and White (1985), Lauritsen et al.
(1985), Hilsenhoff (1987), Schloesser et al. (1995), and Barbour et al. (1999). The results of
the population metrics are summarized in Table 4.4.2.1. Summaries of Trophic Indices for
the benthic populations are shown in Figure 4.4.2.1. Shallow stations WL-20 and WL-17
had the most favorable trophic index scores for overall community structure (Hilsenhoff) and
chironomids. All of the other shallow stations and the deep stations exhibited high scores for
the Hilsenhoff index, indicating enriched conditions. Chironomid index values for the
shallow stations WL-18, WL-19, and WL-20 were all <7.5. Deep stations had higher
chironomid index values that were again representative of organic enrichment. It is
interesting to note that the stations WL-4 and WL-20 had similar Shannon-Weaver scores,
indicating a more balanced community structure (-2.1). Shannon-Weaver scores for the
other stations ranged from 0.8-1.5, indicating a more limited diversity. The increased
diversity at WL-4 appears to be related to the lower TOC and increased sand fraction.
79
-------
TABLE 4.4.2.1 SUMMARY OF DIVERSITY AND TROPHIC STATUS METRICS FOR THE BENTHIC
MACROINVERTEBRATES IN WHITE LAKE, OCTOBER 2000.
Station
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
WL-12
WL-13
WL-14
WL-15
WL-21
WL-16
WL-17
WL-18
WL-19
WL-20
N
4521
4880
2713
2612
9287
7378
2297
7119
8067
3660
12947
10736
5569
10277
4981
34405
4177
4196
2383
3172
7162
Hilsenhoff
Index
9.573
9.282
9.153
8.162
9.258
8.723
9.231
8.859
8.388
9.201
9.431
9.051
7.616
9.377
8.406
8.869
9.303
7.049
8.758
8.757
6.413
Oligochaete
Index
9.715
9.563
9.567
8.426
9.358
8.682
9.707
9.022
8.444
9.446
9.545
9.238
7.659
9.722
8.699
8.912
9.686
7.051
9.388
9.381
9.750
Chironomid
Index
7.860
8.819
9.333
8.943
8.653
9.034
8.960
8.506
9.319
9.073
8.670
8.922
8.609
8.610
8.483
8.844
8.267
8.012
7.140
7.059
7.262
Shannon-
Weaver
0.808
1.402
0.976
2.100
0.923
1.588
0.925
1.182
1.833
1.542
1.229
1.442
1.170
1.248
1.689
1.264
1.255
1.343
1.393
1.387
2.086
Margalef s
Richness
0.734
1.191
1.187
1.602
0.892
1.497
1.358
1.397
1.349
1.397
1.076
1.149
0.833
1.437
1.467
1.258
1.215
1.293
1.445
1.387
2.495
Evenness
0.321
0.370
0.265
0.628
0.280
0.350
0.229
0.251
0.521
0.390
0.311
0.423
0.403
0.268
0.416
0.253
0.319
0.319
0.336
0.334
0.350
J
0.415
0.585
0.424
0.819
0.420
0.602
0.386
0.461
0.738
0.621
0.512
0.626
0.563
0.487
0.658
0.479
0.523
0.541
0.561
0.558
0.665
Taxa
Richness
7
11
10
13
9
14
11
13
12
12
11
10
8
13
13
14
11
12
12
12
23
80
-------
10.000^
9.000-
x
a)
•a
8.000-
7.000-
6.000-
Station
FIGURE 4.4.2.1 SUMMARY OF TROPHIC INDICES (POLLUTION TOLERANCE) FOR THE BENTHIC
MACROINVERTEBRATES IN WHITE LAKE, OCTOBER 2000
81
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Spearman Rank Order Correlations were developed for the indices and physical/chemical
parameters (Table 4.4.2.2) to determine variables that help define community structure.
Chromium showed significant correlations with nematodes and the Chironomid index.
Elevated levels of chromium were associated with increased abundance of nematodes and a
decrease in the quality of the chironomid population. The chironomid index value was
positively correlated with depth and negatively correlated with TOC. This pattern shows that
increased pollution tolerance is associated with greater depth and more organic carbon in the
sediments. A negative correlation was found between the Chironomid/Oligocheate ratio and
TOC, indicating that chironomids are associated with lower organic enrichment in the
sediments than oligochaetes. There is a strong relationship between Hilsenhoff index values
and fine grain sediments, indicating that pollution tolerance is associated with soft,
depositional sediments. Taxa richness and fine grain sediments were negatively correlated,
indicating that the number of taxa decrease as sediments become more finely grained. The
significant correlations with TOC, grain size, and depth all point to eutrophication related
factors having the greatest influence on the benthic community. Increased nematodes were
strongly linked with chromium enrichment. The positive correlation with the chironomid
index may also be influenced by depth since the chromium was also linked to this variable
(Table 4.1.7).
TABLE 4.4.2.2 SPEARMAN RANK ORDER CORRELATIONS FOR ECOLOGICAL, CHEMICAL,
AND PHYSICAL PARAMETERS FOR WHITE LAKE. (SIGNIFICANT CORRELATION IN BOLD.)
Parameter Cr Depth TOC <63um
Total Organisms 0.241 0.029 0.047 -0.201
Total Tubificidae 0.455 0.226 -0.073 -0.039
Total Chironomidae 0.299 0.089 0.202 -0.253
Nematoda 0.800 0.380 -0.070 0.030
Hilsenhoff Index 0.445 0.305 -0.133 0.518
Oligochaete Index 0.015 -0.127 0.145 0.313
Chironomid Index 0.509 0.714 -0.551 0.109
Shannon-Weaver -0.27 -0.049 0.096 -0.201
Margalefs Richness -0.32 -0.336 0.259 -0.352
Evenness -0.25 0.075 -0.165 -0.069
J -0.29 -0.044 0.018 -0.229
Taxa Richness -0.10 -0.190 0.255 -0.513
Chironomid/Oligochaet _Q Q5 _Q^ _
e Ratio
82
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4.4.3 Analysis of Macroinvertebrate Results Using Community Structure
The benthic macroinvertebrate taxa were further analyzed for associations with chromium by
canonical correspondence analysis (Figure 4.4.3.1). A description of the taxa abbreviations
are provided in Table 4.4.3.1. Dimensions 1 and 2 accounted for 55% of the variability in
the data set (31% and 24%, respectively). Four data clusters are evident. The clean site,
Station WL-20, was characterized by amphipods, mayflies, and isopods. This assemblage
was not
C\J
c
o
'to
c
CD
0
-2
-2
\
0
\
2
\
4
Dimension 1 (31%)
FIGURE 4.4.3.1 CANONICAL CORRESPONDENCE ANALYSIS OF BENTHIC MACRO-
INVERTEBRATE TAXA FOR WHITE LAKE, OCTOBER 2000. (LABELS INDICATE SPECIFIC
TAXA AND STATIONS. SHALLOW STATIONS LISTED IN RED AND DEEP STATIONS IN GREEN.)
83
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TABLE 4.4.3.1 SUMMARY STATISTICS FOR THE ANALYSIS OF INDIVIDUAL BENTHIC
MACROINVERTEBRATE SAMPLES FROM WHITE LAKE, OCTOBER 2000.
Taxa
Gammarus
Hyallela
Isopoda
Amnicola
Physa
Valvata tricarinata
Viviparous
Dreissena polymorpha
Pisidium
Aulodrilus limnobius
A ulodrilus pigue ti
Ilyodrilus templetoni
Limnodrilus hoffmeisteri
Limnodrilus claparianus
Quistrodrillus
Haemonais waldvogeli
Helobdella
Nematoda
Planaridae
Ceratapogonidae
Chironomidae
Ablabesmyia
Abbreviation
gam
hya
iso
amn
phy
tri
viv
drei
pis
limn
Pig
temp
hof
clap
qui
wald
hel
nem
pla
cer
Chir
Abla
Taxa
Chironomus
Clinotanypus
Coelotanypus
Cryptochironomus
Dicrotendipes
Heterotrissocladius
Paraphaenocladius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironomus
Tanypus
Caenis
Ephemera
Hexagenia
Isonychia
Polycentroapodidae
Pseudostenophylax
Sialis
Zygoptera
Abbreviation
chiron
clin
coel
cryp
die
heter
para
par
pha
poly
pro
pseu
tany
cae
ephem
hex
iso
polyc
pseudos
sia
found in the other sites. WL-16, the site in the east bay with high solid phase toxicity, was
grouped around the two tubificid taxa Quistrodrillus spp. and Aulodrilus pigiieti, the
gastropod Physa spp., and the midges Tanytarsus spp., Ablabesmyia spp., Cryptochironomus
spp., and Clinotanypus spp. The tubificid taxa represent additional pollution tolerant
organisms at this location. Tanytarsus spp. is classified as a "sprawler" because it resides on
the surface and does not burrow in the sediment. Ablabesmyia spp., Cryptochironomus spp.,
and Clinotanypus spp. are predators and do not ingest sediment and/or detritus. The
additional pollution tolerant tubificids and the shift to predatory and surface dwelling midges
are indicative of adverse conditions in the sediment.
Stations WL-9, WL-12, and WL-14 cluster together around Nematoda, Pseudostenophylax
spp., and Paraphaenocladius spp. The latter two organisms were found in very low numbers
84
-------
(1 organism in the triplicate PONARS) and cannot be considered as important members of
the benthic assemblage. Chromium concentrations and the order Nematoda showed a strong
correlation (Table 4.4.2.2). Stations WL-9, WL-12, and WL-14 had the highest
concentrations of chromium (420 mg/kg, 510 mg/kg, and 480 mg/kg, respectively).
Nematodes have been reported to be tolerant of heavy metal pollution (Gyedu-Ababio et al.
1999, Fiscus and Neher 2002). Some are able to produce phytochelatins that are able to
detoxify heavy metals (Cobbett 2000, Vatamaniuk et al. 2001). In addition to changes in the
nematode population, this group of locations also had the lowest percentage of tubificids
(Table 4.4.1.2). Samples at stations WL-9, WL-12, and WL-14 contained tubificid
percentages of 45%, 23%, and 37%, respectively. The tubificid percentage range for the
other deep stations was 66-85%. Based on these results, the benthic macroinvertebrate
populations at these stations appear to be influenced by chromium.
The remainder of stations and organisms form a cluster in the middle of the CCA plot.
Benthic macroinvertebrate assemblages of the remaining shallow stations (WL-17, WL-18,
and WL-19) with low chromium levels are grouped with deep locations that contain high
concentrations of the metal. These sites are characterized by similar TOC, % solid, and grain
size values. This suggests that organic enrichment from eutrophication exerts the
predominant influence on the benthic community for this cluster.
4.4.4. Benthic Macroinvertebrate Data Summary
The benthic macroinvertebrate community of White Lake is characterized by organisms that
are tolerant of organic (nutrient) enrichment. The presence of organic deposition from the
White River, the eutrophic conditions in the lake, and the historical anthropogenic
enrichment from the lumbering operations, the Tannery, and the wastewater treatment plant
all act to increase the densities of pollution tolerant organisms. To this extent, detritivores
such as tubificids and chironomids from the genus Chironomus should dominate the benthic
populations (Winnell and White 1985). While these conditions would indicate habitat
degradation in a more pristine system, organic enrichment forms the basis for structuring the
benthic community in White Lake. The only sites that did not fit this characterization were
the locations with high chromium levels (WL-9, WL-12, and WL-14) and the east bay site,
WL-16. The most notable difference with respect to the first group of stations was a change
in benthic taxa from tubificids to nematodes. WL-16 was characterized by a change in
chironomid species from detritivores to predators. A shift to more opportunistic organisms
has previously been attributed to contaminant impact (Dauer 1991).
With respect to the influence of chromium on the benthic ecology in White Lake, a
significant relationship exists between the metal and the macroinvertebrate community
(Figure 4.4.4.1). When dimension 1 of the CCA (invertebrate taxa) is plotted against
chromium, a strong relationship is noted (r = -0.588, p < 0.017). An increase in chromium
concentration shifts the population from an assemblage dominated by tubificids to one
dominated by nematodes. Changes in the benthic community in response to chromium have
been previously reported (Leslie et al. 1999). The significance of this shift is unknown and
would require further taxonomic resolution to identify and classify the nematode species with
85
-------
respect to pollution tolerance. In addition, a more detailed assessment of benthic biomass
would be required to determine if this shift is significant with respect to ecological resources
in White Lake. Finally, a more detailed evaluation of the nutrient and organic composition
would need to be performed to determine if this shift was related to food quality or a
response to sediment contamination.
Invertebrate Community Composition and Chromium Consentrations
(r = -0.588; p = 0.017)
1.0
0.5 -
„_ 0.0 -
c
o
'w
c
CD
E -0.5 -
Q
o
o
-1.0 -
-1.5
Control
Locations
WL-18
WL-19
WL-20
100 200 300 400
Chromium (mg kg"1)
500
600
FIGURE 4.4.4.1 PLOT OF CCA DIMENSION 1 (MACROINVERTEBRATE TAXA) AND
CHROMIUM FOR WHITE LAKE SEDIMENTS, OCTOBER 2000.
86
-------
4.5 Chromium Uptake by Aquatic Organisms
The accumulation of chromium in several aquatic organisms was examined to determine the
biological fate of the metal in White Lake. The contaminated sediments in Tannery Bay
contained the highest levels of chromium (1,000-4,000 mg/kg) and supported dense
macrophyte and zebra mussel populations (Rediske et al. 1998). For this project, triplicate
collections of macrophytes (Ceratophyllum spp.) and zebra mussels (Dreissena polymorpha)
were made at three sites in Tannery Bay and at WL-20. The results are shown in Table 4.5.1
and displayed in Figure 4.5.1. Only macrophyte shoots and the attached zebra mussels were
analyzed to minimize the inclusion contact with the highly contaminated sediment. The
Ceratophyllum spp. tissue found in Tannery Bay contained significantly higher chromium
levels than the control location (13-35 mg/kg vs. 5 mg/kg respectively). Zebra mussel tissue
followed a similar trend, however the difference between the chromium concentrations in
samples from Tannery Bay (16-33 mg/kg) and from the control area (2 mg/kg) were greater.
Chromium accumulation in macrophytes (Vajpayee et al. 1995) and zebra mussels (Redders
and Bij de Vaate 1993, LaValle et al. 1999) has been previously reported. The results from
this investigation demonstrate the bioavailability of chromium in the sediments of Tannery
Bay. In consideration of the dense macrophyte growth in the bay and the level of chromium
accumulation, translocation and senescence would not contribute significant concentrations
of the metal to the sediment. While the macrophytes would contribute organic matter and
nutrients to the sediments, mixing and resuspension provide the mechanism for maintaining
the high chromium levels in the surficial layers. The accumulation of chromium in zebra
mussels also supports the mixing and resuspension hypothesis as these organisms are filter
feeders and ingest suspended particulates.
TABLE 4.5.1 CHROMIUM CONCENTRATION IN MACROPHYTES AND ZEBRA MUSSELS IN
TANNERY BAY. (STATION 20 is THE CONTROL SITE.)
Chromium in Chromium in
Station Zebra Mussels Plant Tissue
(mg/kg) (mg/kg)
22A 52 14
22B 12 11
22C 14 16
23A 16 36
23B 12 48
23C 23 23
24A 45 54
24B 16 36
24C 23 20
20A 0.84 6.9
20B * 3.5
* Insufficient organisms present for
replicates
87
-------
D Zebra Mussels
D Plant Tissue
24 24 20
Station
FIGURE 4.5.1 CHROMIUM ACCUMULATION IN MACROPHYTES AND ZEBRA MUSSELS IN
TANNERY BAY
The accumulation of chromium was evaluated at all of the PONAR locations. Chromium
concentrations in the sediment and in chironomid tissue from each station are presented in
Table 4.5.2 and displayed graphically in Figure 4.5.2. The results show a significant
TABLE 4.5.2 CHROMIUM CONCENTRATION IN CHIRONOMIDS FROM TANNERY BAY.
Station
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
Chromium in Chromium in
Sediment (mg/kg) Chironomids (mg/kg)
270
300
190
18
400
360
390
380
420
270
310
59
44
41
10
84
75
92
91
99
62
69
Station
WL-12
WL-13
WL-14
WL-15
WL-16
WL-17
WL-18
WL-19
WL-20
WL-21
Chromium in
Chromium in
Sediment (mg/kg) Chironomids (mg/kg)
510
250
480
250
190
50
29
39
28
450
140
85
88
67
48
14
12
14
13
130
FIGURE 4.5.2 CHROMIUM ACCUMULATION IN CHIRONOMIDS FROM TANNERY BAY.
88
-------
O
c
O
.c
o
160 -,
140 -
120 -
100 -
80 -
60 -
40 -
20 -
R2 = 0.8833
100
200 300 400
Chromium in Sediment (mg/kg)
500
600
relationship between chromium uptake and the concentration in the sediment. The Spearman
Correlation coefficient was 0.92 (p < 0.001), indicating a strong relationship between
sediment and chironomid concentrations. Locations with sediment concentrations < 50
mg/kg had chromium concentrations in the chironomid populations of 10-14 mg/kg. In
contrast, locations with chromium concentrations > 100 mg/kg had accumulated metal levels
of 48-140 mg/kg. These data coupled with the increased chironomid index value (Table
4.4.2.2) suggest that chromium is associated with an adverse impact to this group of
organisms. A more detailed evaluation of physiological response to chromium would be
necessary to establish a direct link between accumulation and the increased pollution
tolerance.
The results of the tissue analyses showed that chromium in the sediment from White Lake
was accumulated by macrophytes, chironomids, and zebra mussels. Based on the dense
growth of macrophytes and the high numbers of zebra mussels in Tannery Bay, there was no
obvious ecological effect apparent in these organisms. More research would be necessary to
establish the linkage between chromium accumulation in chironomids and ecological
impairment.
89
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4.6 The Environmental Fate and Significance of Chromium and PCBs in White Lake
The results of this investigation coupled with previous studies (Rediske et al. 1998, Earth
Tech 2001) provide an extensive sampling grid for chromium and PCBs in White Lake. The
chromium sampling points are shown in Figure 4.6.1 for White Lake and in Figure 4.6.2 for
the Tannery Bay area. Coordinates and chromium concentrations are listed in Table 4.6.1.
TABLE 4.6.1 WHITE LAKE CHROMIUM DATA. (PONAR SAMPLES FROM CURRENT
INVESTIGATION AND REDISKE ET AL. 1998)
Station
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
WL-1 2
WL-1 3
WL-1 4
WL-1 5
WL-1 6
WL-1 7
WL-1 8
WL-1 9
WL-20
Latitude
N
43° 22.58'
43° 22.45'
43° 22.41'
43° 22.27'
43° 22.73'
43° 22.95'
43° 22.61'
43° 23.01'
43° 23.27'
43° 22. 18'
43° 23.54'
43° 23.62'
43° 23.08'
43° 23.69'
43° 23.87'
43° 24. 16'
43° 24.20'
43° 24.39'
43° 24.32'
43° 24.51'
Longitude
W
86° 24.55'
86° 24. 15'
86° 24.77'
86° 24. 16'
86° 23.50'
86° 22. 86'
86° 23.27'
86° 22.53'
86° 22.43'
86° 24.61'
86° 22.25'
86° 21. 97'
86° 22.33'
86° 21. 63'
86° 21. 83'
86° 21. 15'
86° 21. 25'
86° 21. 26'
86° 21. 14'
86° 21. 22'
Chromium
mg/kg
270
300
190
18
400
360
390
380
420
270
310
510
250
480
250
190
50
29
39
28
Station
WL-21
WL-22
WL-23
WL-24
1-1
I-2
I-3
I-4
I-5M
I-6
I-7M
I-8
E-1-P
E-2-P
E-3-P
E-4-P
E-5-P
E-6-P
E-7-P
E-9-P
Latitude
N
43° 23. 15'
43° 23.99'
43° 24.02'
43° 24.02'
43° 24.15'
43° 24.11'
43° 24.06'
43° 24.05'
43° 24.04'
43° 23.98'
43° 23.97'
43° 23.97'
43° 24.59'
43° 21.10'
43° 23.89'
43° 23.93'
43° 23.70'
43° 23.70'
43° 23.59'
43° 23.13'
Longitude
W
86° 22.57'
86° 21. 28'
86° 21. 26'
86° 21. 30'
86° 21.15'
86° 21.27'
86° 21.32'
86° 21.31'
86° 21.26'
86° 21.25'
86° 21.22'
86° 21.36'
86° 21.59'
86° 21.38'
86° 21.50'
86° 21.69'
86° 21.61'
86° 21.95'
86° 21.71'
86° 21.59'
Chromium
mg/kg
450
520
1200
1300
212
259
934
1890
4100
2650
2560
515
23
64
43
344
492
771
541
369
Chromium concentration contours plotted from the data using kriging are shown in Figure
4.6.3. Concentrations are plotted for the > 4 m depth contours as shallower sediments in the
lake are sandy and related to shoreline erosion. Organic depositional sediments are typically
found at depths > 4 m. The concentration map shows that the spatial extent of chromium
contamination covers the area of the lake from Tannery Bay to the navigation channel.
Advective transport and deposition are also evident from the reservoir of highly
contaminated sediment in Tannery Bay. Moving westward from Tannery Bay, an area of
low chromium concentration is present in the Narrows, where drowned rivermouth related
currents would be highest. The maximum chromium concentration outside of Tannery Bay
(771 mg/kg) occurs
90
-------
t
N
FIGURE 4.6.1 CHROMIUM SAMPLING POINTS IN WHITE LAKE (CURRENT INVESTIGATION AND REDISKE ET AL.
1998). (RED LINE DENOTES THE 4 M DEPTH CONTOUR.)
91
-------
FIGURE 4.6.2 CHROMIUM SAMPLING POINTS IN THE VICINITY OF TANNERY BAY . (CURRENT
INVESTIGATION AND REDISKE ET AL. 1998. RED LINE DENOTES THE 4 M DEPTH CONTOUR.)
92
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318000
317000
316000
315000
314000
313000
500 1000 1500 2000
466000
467000
468000
469000
X(m)
470000
471000
472000
FIGURE 4.6.3 CHROMIUM CONCENTRATION CONTOURS FOR WHITE LAKE SURFICIAL SEDIMENTS.
(CONCENTRATIONS PLOTTED FOR DEPTHS > 4 M. TANNERY BAY AREA SHOWN IN GREATER DETAIL)
93
-------
in the first deposit!onal basin (16 m) at the midpoint between Dowies Point and the Narrows
(Figures 4.1.8 and 4.6.3). The next areas of high chromium concentration occur in the
deposit!onal basins to the east (420 mg/kg) and west (400 mg/kg) of Dowies Point (6 m and
20 m, respectively). In the depositional basin west of Long Point (22 m), chromium levels
decrease to 300 mg/kg and continue to decline in concentration to the channel (190 mg/kg).
The plume of contaminated sediment emanating from Tannery Bay extends « 8 km from the
source. Depositional contours also follow the generalized circulation pattern for White Lake.
Lung (1975) described a westerly flow of water from the drowned rivermouth and a wind
induced countercurrent along the southern shore (Figure 4.6.4). The predominant westerly
wind results in a current moving eastward until it reaches the Narrows where it is nullified by
the drowned rivermouth flow. The shallow depths and sandy nature of the sediments on the
southern shore of the lake are indicative of the erosional character of this current and its
effect on the shoreline. The extensive shallow zone along the southern shore is the result of
the erosional effects on the shoreline and the rapid depositional process resultant from the
interaction of the counter currents. The northern shoreline is protected from the prevailing
FIGURE 4.6.4 GENERALIZED CIRCULATION PATTERN FOR WHITE LAKE (LUNG 1975).
wind by the high banks and shows little evidence of erosion. The morphometry of the
northern shore and the two points result in the formation of two gyres that enhance sediment
94
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and detrital deposition. Based on these flow characteristics, chromium deposition should be
lower along the southern shore and higher to the north. The chromium concentration map
fits the generalized flow pattern as the higher metal concentrations follow the northern
shoreline of White Lake. The position of Tannery Bay in the eastern corner of the lake and
morphometry associated with the Narrows would make this area a deposition and transport
zone depending on the nature of the storm event. Small storm events and wind surges would
cause sediment resuspension in the bay and result in a minor degree of transport out into the
drowned rivermouth current. Larger storm events would result in considerable resuspension
and transport as the increased wave action facilitates sediment advection out of the bay and
into the main section of the lake. The 20 cm mixed layer previously reported in the Tannery
Bay sediments (Rediske et al. 1998) and the influence of episodic events on chromium
stratigraphy described in Section 4.2 are evidence of these phenomena.
The environmental fate and transport of the PCB discharge in White Lake from the former
Occidental/Hooker Chemical facility is very different from the chromium release from the
tannery. The data from the extensive sampling of the Occidental/Hooker Chemical discharge
zone (Earth Tech 2001) plus the results of current and previous investigations of White Lake
are given in Table 4.6.2. A map of the sampling locations is provided in Figure 4.6.5. Maps
of PCB concentration contours for the discharge zone and for White Lake are shown in
Figures 4.6.6 and 4.6.7, respectively. The effluent pipe was located at a depth ~ 10 m and
the maximum PCB concentration occurred at ~ 11 m (390 mg/kg). Sediment contamination
is confined to a 100 m2 zone around the outfall. The discharge from this facility began in the
mid 50s and the origin of the PCBs is not known. Occidental/Hooker Chemical
manufactured chlorinated pesticide intermediates and the PCBs were either produced as
byproducts or were released from the electrical systems on site. The discharge of chemical
wastes was terminated in the mid 70s, however treated groundwater from an activated carbon
system is currently released from the old outfall. Concentration contours follow the
southwestern flow of the drowned rivermouth and the depth change from 10 m to 14 m. The
affinity of PCBs for sediment coupled with the location of the outfall in the deep deposit!onal
basin resulted in conditions that limited the advective transport of the chemical outside the
area around Dowies Point. This environment is in stark contrast to the shallow area of the
tannery discharge and its proximity currents associated with the Narrows. The presence of
PCBs in the surficial sediments is problematic because of the depositional nature of the
discharge zone. If this location was a true depositional zone, the PCBs would have been
covered by clean sediment over the last 20+ years. The groundwater treatment discharge
(«1.6 mgd) may cause turbulence in the local area and result in the resuspension and limited
transport of PCBs. The complex flow pattern for this area (Figure 4.6.5) may also result in
limited redistribution of sediments.
The highly contaminated sediment in Tannery bay and near the former Occidental/Hooker
Chemical outfall will be removed by dredging in 2003. Removing the sediments from
Tannery Bay will eliminate the source that has contaminated the depositional sediments in
95
-------
TABLE 4.6.2 WHITE LAKE PCB DATA. (PONAR SAMPLES FROM EARTH TECH 2001 AND
THE CURRENT AND PREVIOUS INVESTIGATION)
Aroclor1248
Sample
SD-99-01
SD-99-02
SD-99-03
SD-99-05
SD-99-06
SD-99-07
SD-99-08
SD-99-09
SD-99-10
SD-99-11
SD-99-12
SD-99-13
SD-99-14
SD-99-15
SD-00-01
SD-00-02
SD-00-03
SD-00-04
SD-00-06
SD-00-07
SD-00-08
SD-00-09
SD-00-10
SD-00-11
SD-00-12
SD-00-13
SD-00-17
SD-00-18
SD-00-19
SD-00-20
SD-00-21
SD-00-22
SD-00-23
SD-00-34
SD-00-35
SD-00-38
SD-00-40
SD-00-41
SD-00-46
SD-00-47
SD-00-48
SD-00-49
SD-00-50
SD-00-51
(mg/kg)
<0.3
<0.3
6.3
0.55
<0.3
<0.3
413
390
110
0.58
<0.3
0.47
9
0.4
0.88
7.6
1.4
38
2.1
1.1
44
27
0.76
0.35
0.99
0.47
<0.3
0.55
1.1
1.3
4.3
<0.3
<0.3
34
<0.3
76
50
3.3
<0.3
0.35
1.5
0.56
0.82
110
A
1456881
1456885
1456882
1456903
1456813
1456928
1456911
1456915
1456934
1456959
1456978
1456931
145647.
1456997
1456870
1456900
1456960
1456866
1456920
1456946
1456859
1456896
1456926
1456801
1456765
1456699
1456969
1456990
1456924
1456868
1456828
1456891
1456819
1457055
1456846
1456697
1456894
1456927
1457097
1457050
1457022
1456887
1456822
1456887
.77
.82
.99
.31
.09
.34
.14
.93
.64
.40
.93
.41
75
.48
.26
.67
.59
.68
.27
.05
.61
.51
.84
.24
.84
.94
.63
.59
.39
.38
.58
.26
.55
.22
.44
.60
.22
.94
.29
.21
.73
.74
.38
.81
Y
694618.
694617.
694581.
694609.
694632.
694653.
694532.
694552.
694574.
694600.
694622.
694516.
694562.
694604.
694582.
694552.
694507.
694540.
694492.
694475.
694495.
694467.
694445.
694501.
694363.
694215.
694297.
694393.
694410.
694436.
694468.
. Aroclor1248
,72
08
86
,45
34
,54
,07
40
49
,19
,57
,70
,27
88
,65
86
,16
,53
04
,87
,57
,79
,57
,97
,00
,55
,55
,18
49
,77
,79
694314.74
694335.
694554.
694564.
694274.
694487.
694543.
694530.
694584.
694536.
694386.
694388.
694593.
,65
38
03
,53
,45
62
,11
42
46
30
,65
,90
bample
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
WL-10
WL-11
WL-1 2
WL-1 3
WL-1 4
WL-1 5
WL-1 6
WL-1 7
WL-1 8
WL-1 9
WL-20
WL-21
1-1
I-2
I-3
I-4
I-5M
I-6
I-7M
I-8
E-1-P
E-2-P
E-3-P
E-4-P
E-5-P
E-6-P
E-7-P
E-9-P
(mg/kg)
<0.05
0.09
<0.05
<0.05
<0.05
0.07
0.08
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
22
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
5.5
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
43°
N
22.58'
22.45'
22.41'
22.27'
22.73'
22.95'
22.61'
23.01'
23.27'
22.18'
23.54'
23.62'
23.08'
23.69'
23.87'
24.16'
24.20'
24.39'
24.32'
24.51'
23.15'
24.15'
24.11'
24.06'
24.05'
24.04'
23.98'
23.97'
23.97'
24.59'
24.10'
23.90'
23.93'
2370'
23.70'
23.59'
23.13'
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
86°
W
24.55'
24.15'
24.77'
24.16'
23.50'
22.86'
23.27'
22.53'
22.43'
24.61'
22.25'
21.97'
22.33'
21.63'
21.83'
21.15'
21.25'
21.26'
21.14'
21.22'
22.57'
21.15'
21.27'
21.32'
21.31'
21.25'
21.25'
21.22'
21.36'
21.59'
21.38'
21.50'
21.69'
21.61'
21.95'
21.71'
22.59'
96
-------
SD-gg-oi -.--,^-1^
SD-99-07SD-99-05 SD-99-15
^n.nnm- SD-99-1 1 SD-OD-
SD-00-01SD_gg_
SD-HD-35
SD-00-48 SD_oD_4B
N
FIGURE 4.6.5 PCB SAMPLING POINTS IN WHITE LAKE (EARTH TECH 2001, CURRENT INVESTIGATION AND
REDISKE ET AL. 1998. OCCIDENTAL/HOOKER CHEMICAL AREA SHOWN IN GREATER DETAIL)
97
-------
315100 —
315080 —
315060 —
315040 —
315020 —
315000 —
314980 —
14 14.5 15 155
469420
400
300
200
180
160
140
120
100
80
60
40
20
10
8
6
4
2
1
0
PCBs
(mg/kg)
FIGURE 4.6.6 PCB CONCENTRATION CONTOURS IN THE SURFICIAL SEDIMENTS IN THE VICINITY OF THE
FORMER OCCIDENTAL/HOOKER CHEMICAL DISCHARGE.
98
-------
318000-
317000-
316000-
315000-
314000-
313000-
466000
467000
468000
469000
470000
471000
X(m)
FIGURE 4.6.7 PCB CONCENTRATION CONTOURS IN THE SURFICIAL SEDIMENTS IN WHITE
LAKE. (OCCIDENTAL/HOOKER CHEMICAL AREA SHOWN IN GREATER DETAIL.)
472000
400
300
200
180
160
140
120
100
80
60
40
20
10
8
6
4
2
1
PCBs
(mg/kg)
99
-------
90% of White Lake. The complex flow pattern of the lake will continue to redistribute the
remaining contaminated sediments throughout the western basins. Even though the source
has been eliminated, it will take many years to observe a significant trend of reduced
chromium deposition in the surficial zone. Dredging should have a more immediate impact
on the ecosystem in Tannery Bay as the toxic sediments will be removed from the
environment. The removal of PCB contaminated sediment from the Occidental/Hooker
Chemical outfall will also have an immediate benefit to the local ecosystem through the
elimination of toxic sediment. On a broader scale, the removal of PCBs will eliminate a
major area of persistent bioaccumulative toxicants from White Lake.
4.7 Sediment Quality Triad Assessment of Contaminated sediments in White Lake
In order to determine the significance of the remaining areas of sediment contamination, an
assessment matrix (Chapman 1992) can be used to examine the relationship between
chemistry, toxicity, and benthic macroinvertebrate data. An assessment matrix for the White
Lake data is presented in Table 4.6.3. Stations exceeding the PEC (MacDonald et al. 2000)
TABLE 4.7.1 SEDIMENT QUALITY ASSESSMENT MATRIX FOR WHITE LAKE DATA,
OCTOBER 2000. ASSESSMENT MATRIX FROM CHAPMAN (1992).
Station
No stations fit the
criteria
WL-17, WL-18, WL-
19, WL-20
WL-1, WL-2, WL-3,
WL-4, WL-5, WL-6,
WL-7, WL-8, WL-10,
WL-11, WL-13. WL-15
No stations fit the
criteria
No stations fit the
criteria
WL-21
WL-16
WL-9, WL-12,
WL-14
Sediment
Chemistry
+
-
+
-
-
+
-
+
Toxicity
Test
+
-
-
+
-
+
+
-
Benthic
Community
+
-
-
-
+
-
+
+
Possible Conclusions
Impact highly likely; contaminant induced
degradation of sediment dwelling organisms
evident
Impact highly unlikely; contaminant degradation
of sediment dwelling organisms not likely
Impact unlikely; contaminants unavailable to
sediment dwelling organisms
Impacts possible; Unmeasured contaminants or
conditions exist that have the potential to cause
toxicity
Impacts unlikely; no degradation of sediment
dwelling organisms in the field apparent relative
to sediment contamination; physical factors may
be influencing benthic community
Impact likely; toxic chemicals probably stressing
system
Impact likely; unmeasured toxic chemicals
contributing to the toxicity
Impact likely; sediment dwelling organisms
degraded by toxic chemical, but toxicity tests not
sensitive to chemicals present
I- = Indicator classified as affected; as
= Indicator not classified as affected:
determined based on comparison to the PEC or control site
as determined based on comparison to the PEC or control site
100
-------
were classified as having a potential impact from sediment chemistry. Toxicity and benthic
community impacts were based on observing a statistically significant difference in mortality
and diversity/trophic status metrics, respectively. Using this assessment methodology, the
Occidental/Hooker Chemical Outfall (WL-21), the east bay (WL-16), and the high chromium
sites (WL-9, WL-12, and WL-14) were likely to be impacted by contaminated sediments.
None of the stations were positive for all three components of the triad. Station WL-21 had
levels of chromium and PCBs that exceeded the PEC and solid phase toxicity. The benthic
community at this location was not significantly different from the other deep stations in
White Lake. Given the organically enriched conditions present in the sediment, it is difficult
to detect a toxic response in the benthos above effects caused by eutrophication. Sediments
from WL-16 exhibited solid phase toxicity and impacted benthic invertebrates. None of the
chemicals however were at sufficient concentrations to produce the toxic effect. Stations
WL-9, WL-12, and WL-14 had chromium levels above the PEC, no solid phase toxicity, and
a marginally impacted benthic community. Nematodes were the most abundant organism at
these locations while tubificids dominated the other stations. Based on the Assessment
Matrix, ecological impairments exist at all of these sites due to contaminated sediments.
Stations WL-17, WL-18, WL-19, and WL-20 did not exhibit solid phase toxicity, benthic
impairment, or contaminant concentrations above the PEC. While the remaining stations
exceeded the chromium PEC, solid phase toxicity was absent and the benthic community
was similar to WL-17, WL-18, and WL-19. Because of these findings, impacts from
contaminated sediments were not anticipated at these locations.
In consideration of the remediation of the sediments in Tannery Bay and near the
Occidental/Hooker Chemical Outfall, the source of impairments due to chromium and PCBs
in White Lake should be eliminated. While dredging should remove all of the sediment
containing harmful levels of PCBs, the extent of chromium contamination throughout
western White Lake and the cost of remediation make removal an unfeasible alternative.
Natural attenuation by the redistribution and burial of contaminated sediments appears to be
the most cost effective option.
4.8 Summary And Conclusions
A Phase II investigation of the nature and extent of sediment contamination in White Lake
was performed. Sediment chemistry, solid-phase toxicity, and benthic macroinvertebrates
were examined at 21 locations. Since chromium was previously identified as the major
contaminant in the sediments, experiments were conducted to determine the accumulation of
the metal in zebra mussels, macrophytes, and chironomids. In addition, three core samples
were evaluated using radiodating and stratigraphy to assess sediment stability and
contaminant deposition. High levels of chromium were found to cover a majority of the lake
bottom and extend 8 km from the Tannery Bay. All locations sampled west of Tannery Bay
exceeded the Probable Effect Concentration (PEC). Most of the chromium was found in the
top 51 cm of the core samples. High concentrations of PCBs were found near the outfall of
the former Occidental/Hooker Chemical facility. These levels also exceeded PEC guidelines.
Sediment toxicity was observed in the east bay area and at the Occidental/Hooker Chemical
outfall. Toxicity near the Occidental/Hooker Chemical outfall was probably due to the
presence of PCBs. No obvious toxicant was present in the sediments from the east bay.
101
-------
While no relationship was previously observed for total chromium and amphipod toxicity, a
significant correlation was found for the organically bound fraction. Elevated levels of
organic chromium were found in archived sediments from Tannery Bay. Benthic
macroinvertebrate communities throughout White Lake were found to be indicative of
organically enriched conditions. Invertebrate community structure of locations in the east
bay were significantly different than reference sites, as indicated by a shift to chironomids
that were predators and sprawlers. Chironomid populations in the remainder of the lake were
burrowers and detritivores. Higher densities of nematodes and reduced tubificid populations
were associated with the stations with elevated chromium levels (> 400 mg/kg). The metal
also was correlated with an increase in the trophic status of chironomid populations.
Chromium accumulation was observed in chironomid populations throughout White Lake.
In addition, macrophytes and zebra mussels in Tannery Bay were observed to accumulate the
metal in their tissue.
All of the stratigraphy cores showed uniform levels of chromium deposition in the top 10 -
15 cm. This pattern suggested that a constant source of chromium was present in White
Lake. A standard exponential decay pattern was absent in the lower sections of the cores,
indicating that historical changes in sedimentation were caused by episodic events. These
data coupled with chromium contour maps and the generalized circulation pattern of the lake
were used to elucidate the fate and transport of the metal. The proximity to the drowned
rivermouth currents at the Narrows and the wind induced resuspension in the bay provided
conditions that facilitated the advection and dispersion a sediment plume 8 km from its
source. Higher concentrations of chromium were found in the three deep deposition basins
(300-500 mg/kg). In contrast, the PCBs discharged by the Occidental/Hooker Chemical
outfall remained within 100 m of the outfall pipe. The depth of the discharge (15 m) plus the
depositional nature of the discharge zone acted to confine the contaminants to a small area.
The removal of contaminated sediments in Tannery Bay and the Occidental/Hooker outfall
was completed in October 2003. Both remedial actions were essential for the recovery of
White Lake. Remediation at Tannery Bay removed the ongoing source of chromium
contamination while dredging the Occidental/Hooker outfall reduced the amount of
bioaccumulative compounds in the lake.
4.9 References
Barbour, M.T., J. Gerritsen, B.D. Snyder, J.B. Stribling. 1999. Rapid Bioassessment
Protocols for Use in Streams and Wadeable Rivers: Periphyton, Benthic
Macroinvertebrates and Fish, Second Edition. EPA 841-B-99-002. U.S.
Environmental Protection Agency; Office of Water; Washington, D.C.
Barnhart, J. 1997. Chromium chemistry and implications for environmental fate and
toxicity. Journal of Soil Contamination. 6: 561-568.
102
-------
Berg, M. H. 1995. Larval food and feeding behavior. Pages 139-168 in P. Armitage, P. S.
Cranston and L. C. V. Finder, eds. The Chironomidae: The biology and ecology of
non-biting midges. Chapman and Hall, London, England.
Bernays EA, Cooper Driver G and Bilgener M. 1989. Herbivores and plant tannins.
Advances in Ecological Research 19:263-301.
Chapman, P.M. 1992. Sediment quality triad approach. In: Sediment Classification Methods
Compendium. EPA 823-R-92-006. USEPA. Washington, D.C.
Chen, M. and L.Q. Ma. 2001. Comparison of three aqua regia digestion methods for
analyzing 16 elements in soils. Soil Sci. Soc. Am. J. 65:491-499.
Cobbett, C.S. 2000. Phytochelatins and Their Roles in Heavy Metal Detoxification. Plant
Physiology, 123: 825-832.
Cowan M.J.. 1999. Plant Products as Antimicrobial Agents. Clinical Microbiology Reviews
12(4):564-582.
Dauer DM. 1991. Biological criteria, environmental health, and estuarine macrobenthic
community structure: Mar. Pollut. Bull. 26:249-257.
Del Vails TA and P.M Chapman. 1998. Site-specific sediment quality values for the Gulf of
Cadiz (Spain) and San Francisco Bay (USA), using the sediment quality triad and
multivariate analysis: Cienc. Mar. 24:313-336.
Eisler, R. 1986. Chromium hazards to fish, wildlife, and invertebrates: a synoptic review.
U.S. Fish Wildl. Serv. Biol. Rep. 85(1.6) 60 pp.
ENVCA 1994. Priority Substances List Assessment Report, Chromium and its Compounds.
Chemicals Evaluation Division, Environment Canada Quebec, Canada KIA OH3. 59
pp.
EPA 1990 Macroinvertebrate Field and Laboratory Methods for Evaluating the Biological
Integrity of Surface Waters. EPA/600/4-90/03.
Evans, E.D. 1992. Mona, White, and White Lakes in White County, Michigan The 1950s to
the 1980s. Michigan Department of Natural Resources. MI/DNR/SWQ-92/261.
91pp.
Fiscus, D.A. and D.A. Neher. 2002. Distinguishing nematode genera based on
relative sensitivity to physical and chemical disturbances. Ecological
Applications 12(2): 565-575.
103
-------
Gyedu-Ababio TK, J.P. Furstenberg, D Baird, and A Vanreusel. 1999. Nematodes as
indicators of pollution: A case study from the Swartkops River system, South Africa.
Hydrobiologia 397: 155-169.
Hilsenhoff, W.L. 1987. An Improved Biotic Index of Organic Stream Pollution. Great
Lakes Entom. 20:31-39.
Howmiller, R.P. and M.A. Scott. 1977. An environmental index based on the relative
abundance of oligochaete species. J. Water Pollut. Cont. Fed. 49: 809-815.
Johansson S.A., J.L. Campbell, K.G. and Malmquist: Particle Induced X-Ray Emission
Spectrometry (PIXE). John Wiley & Sons, Chichester, New York, 1995
Krebs, C. J. (1989). Ecological methodology. New York: Harper & Row. 325 pgs
Kubanekl J., M. E. Hays, P. J. Brown, N. Lindquist, and W. Fenicall 2001. Lignoid
chemical defenses in the freshwater macrophyte Saururus Cernuus. Chemoecology
11:1-8.
Lauritsen, D.D., S.C. Mozley, and D.S. White. 1985. Distribution of oligochaetes in Lake
Michigan and comments on their use as indices of pollution. J. Great Lakes Res.
11:67-76.
LaValle, P.D., A. Brooks, Andrew, and L V. Chris. 1999. Zebra Mussel Wastes and
Concentrations of Heavy Metals on Shipwrecks in Western Lake Erie J. Great Lakes
Res. 25(2):330-338.
Leslie, H.A., T.I. Pavluk, A.B. de Vaate, M.H.S. Kraak, 1999. Triad assessment of the
impact of chromium contamination on benthic macro-invertebrates in the Chusovaya
River (Urals, Russia). Arch. Environ. Contam. Toxicol. 37(2): 182-189.
Lung, W. S. 1975. Modeling of Phosphorus Sediment-Water Interactions in White Lake,
Michigan. Doctoral Thesis. University of Michigan. Department of Civil
Engineering.
Ma, L.Q., F. Tan and W.G. Harris. 1997. Concentrations and distributions of 11 elements in
Florida soils. J. Environ. Qual. 26:769-775.
MacDonald D.D., C.G. Ingersoll, and T.A. Berger. 2000. Development and Evaluation of
Consensus-Based Sediment Quality Guidelines for Freshwater Ecosystems. Arch.
Environ. Contam. Toxicol. 39(1):20-31.
Merritt, R.W. and K.W. Cummins. 1996. An Introduction to the Aquatic Insects of North
America. 3rd edition. Kendall/Hunt Publishing Co., Dubuque, IA. 789 pp.
104
-------
Milbrink, G. 1983. An improved environmental index based on the relative abundance of
oligochaete species. Hydrobiologia 102: 89-97.
Rajander, J., and L. Harju. 1999. Monitoring of chromium, copper and arsenic in
contaminated soils using thick-target PIXE. Nuclear Instruments and Methods in
Physics Research Section B: Beam Interactions with Materials and Atoms 150: 510-
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Reeders, H. H., and A. Bij de Vaate, 1992. Bioprocessing of Polluted Suspended Matter
from the Water Column by the Zebra Mussel(Dreissenapolymorpha Pallas),"
Hydrobiologia, 239:53-63.
Rediske R, G. Fahnenstiel, P. Meier, T. Nalepa, and C. Schelske, 1998. Preliminary
Investigation of the Extent and Effects of Sediment Contamination in White Lake,
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Robbins, J. A., and L. R. Herche. 1993. Models and uncertainty in 210Pb dating of
sediments. Int. Ver. Theor. Angew. Limnol. Verh 25:217-222.
Schelske, C. L. and D. Hodell. 1995. Using carbon isotopes of bulk sedimentary organic
matter to reconstruct the history of nutrient loading and eutrophication in Lake Erie.
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Schloesser, Don W., Trefor B. Reynoldson, Bruce A. Manny. 1995, Oligochaete fauna of
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Res. 21(3):294-306.
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Vatamaniuk, O.K., Bucher, E.A., Ward, J.T., and Rea, P. A. 2001. A new pathway for heavy
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Vajpayee, P.R., U. N., Sinha, S., Tripathi, R. D., and Chandra, P. 1995 Bioremediation of
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553.
Walsh, A.R. and O'Halloran, J. 1996. Chromium speciation in tannery effluent - II.
Speciation in the effluent and in a receiving estuary. Water Res. 30(10):2401-2412.
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105
-------
5.0 Recommendations
The remediation of contaminated sediments in Tannery Bay and in the vicinity of the
Occidental/Hooker Chemical outfall provide a unique opportunity monitor the restoration of
these areas and effects on the ecology of White Lake. The following recommendations are
based on the results of this investigation and the completion of the above sediment
remediation:
1. East Bay. Solid phase toxicity and an impaired benthic community were identified in
the current and previous investigations. Conventional analyses for metals and
organic compounds were unable to identify a toxicant. In consideration that the east
bay contains one of the few undeveloped littoral zones, it is important to identify the
source of the toxicity and the benthic impairment. A Toxicity Identification
Evaluation (TIE) study should be conducted to evaluate the nature of the toxicant.
Tannin levels in the sediments should also be evaluated. Once the toxic agent(s) have
been identified, remediation and restoration options can be developed.
2. The removal of contaminated sediments from Tannery Bay and in the vicinity of the
Occidental/Hooker Chemical outfall remediated the two major source areas
responsible for the Area of Concern designation for White Lake. In order to prepare
for future delisting activities, it is important to initiate a lake wide monitoring
program to evaluate the effectiveness of the remediation. Annual monitoring of
sediment chemistry, toxicity, benthic macroinvertebrates, and the macrophyte
community should be conducted in the remediated areas to determine whether the
influx of contaminants has ceased and a stable benthic community is established. In
addition, sediment chemistry and benthic macroinvertebrates should be examined on
a lake wide scale to evaluate the effects of reduced chromium loading on the
ecosystem. The stations used in this investigation will provide a solid data set that
describes the condition of the lake prior to remediation. Since the sampling locations
reflect a broad range of chromium concentrations and depths, the data from this
investigation will provide a baseline to evaluate changes in specific areas of elevated
contamination and on a lake wide scale.
3. No sediment contamination related to the DuPont groundwater plume was detected in
the investigation. Based on these results, questions related to contaminated sediments
should not prevent the disposition of the DuPont property west of Long Point.
4. The only remaining site with potential sediment contamination is the Mill Pond area
downstream from Koch Chemical. This site should be investigated since hazardous
chemicals were discharged in the creek and the area is residential.
106
-------
Appendices
107
-------
Appendix A. Quality Assurance Review of the Project Data.
108
-------
QA/QC Analysis Checklist for
SEDIMENT CHEMISTRY ANALYSIS
GRANT/TAG NUMBER: GL-GL975368-01-0
PROJECT NAME: Phase II Investigation of Sediment Contamination in White Lake
REVIEWER: Richard Rediske
DATE: 6-26-03
1. What sediment chemistry data has been collected (CHECK ALL THAT APPLY)?
Total Metals __X_ PCBs pH TOC _X
Dioxins/Furans PAHs X Pesticides X DO AVS
SEM Metals Particle Size X Other Semivolatile Organics X
2. Were the target detection limits met for each parameter?
YES
NO X (UNACCEPTABLE) (Target Detection Limits
were not met for semivolatile organics due to low % solids))
3. Were the Method Blanks less than the established MDL for each parameter?
YES X
NO (UNACCEPTABLE)
4. Did the results of Field Duplicate Analysis vary by less than the % RPD specified in the
QAPP?
YES X
NO (UNACCEPTABLE)
5. Did the results of the Field Replicates Analysis vary by less than the % RPD specified in
the QAPP?
YES X Field replicates were not required in the QAPP
NO (UNACCEPTABLE)
6. Did the surrogate spike recoveries meet the limits set forth in the QAPP?
YES X
NO (UNACCEPTABLE)
109
-------
7. Did the MS/MSD recoveries meet the limits set forth in the QAPP?
YES X
NO
8. Did the RPD (%) of the MS/MSD sample set meet the limits set forth in the QAPP?
YES X
NO
9. Did the initial calibration verification standards meet the requirements set forth in the
QAPP?
YES X
NO (UNACCEPTABLE)
10.. Were any level of contaminants detected above the MDL for the trip blanks and storage
blanks?
YES (UNACCEPTABLE)
NO X Trip and Storage blanks were not required in the QAPP
11. Did all required analysis take place within the required holding time protocols set forth
in the QAPP?
YES X
NO (UNACCEPTABLE)
12. Did the laboratory duplicates vary by less than the % RPD specified in the QAPP?
YES X
NO (UNACCEPTABLE)
13. Are measured dry weight contaminant concentrations reported? (Note: Conversion
from wet weight to dry weight concentration may occur ONLY if data on moisture or TOC
are provided. Nominal concentrations are unacceptable.)
YES X
NO (UNACCEPTABLE)
110
-------
14. Please provide details for all of the "UNACCEPTABLE" marked above. Include
details on the specific analytes affected by any QA/QC discrepancies, and recommendations
regarding usability of data.
Sediment samples had very low % solids that resulted in raising the detection limits for
semivolatiles. The results are listed in the data tables. A larger sample volume should be
used at these locations if additional assessments are made. Target detection limits were
achieved on all other samples.
Ill
-------
QA/QC Analysis Checklist for
ACUTE AND CHRONIC WHOLE SEDIMENT TOXICITY TESTS
(10-dayC. tentans and 10-day or 28-day H. azteca)
GRANT/TAG NUMBER: GL975368-01-0
PROJECT NAME: Phase II Investigation of Sediment Contamination in White Lake
REVIEWER: Richard Rediske
DATE: 2-26-02
1. Did toxicity tests employ appropriate procedures? [ASTM: El367, E1611, El706, USEPA (2000)]
YES X
NO (UNACCEPTABLE)
2. Does sample storage time exceed the allowable storage time specified in the QAPP?
Allowable Storage Days Specified in QAPP 45
Number of Storage Days Prior to Testing 14 DYAS AND 30 DAYS
YES (UNACCEPTABLE)
NO X
3. Was the age for H. azteca organisms between 7- to 14-days at the start of the test with an age
range less than 2-days?
YES X
NO (UNACCEPTABLE)
4A. Were all of the C. tentans organisms second- to third-stage larvae with at least 50% at the third
instar?
YES X
NO (UNACCEPTABLE)
4B. How was the developmental stage of the C. tentans larvae measured?
Head Capsule Width (See Table 10.2 of EPA/600/R-99/064, March 2000)
Length X (Should fall between 4 mm to 6 mm)
Weight (Should fall between 0.08 to 0.23 mg/individual)
5. Do flow rates through the different test chambers differ by more than 10% at any particular time
during the test?
YES (UNACCEPTABLE)
NO X (QAPP REQUIRED 2X DAILY RENEWAL OF OVERLYING
WATER INSTEAD OF FLOW THROUGH)
112
-------
6. Did Dissolved Oxygen remain above 2.5 mg/L?
YES X
NO (Provide Explanation at end of Checklist)
7. Does daily mean Temperature remain at 23 ± 1°C?
YES X
NO (UNACCEPTABLE)
8. Does the instantaneous Temperature remain in the range of 23 ± 3EC?
YES X
NO (UNACCEPTABLE)
9. Do the Ranges of for Hardness, Alkalinity, pH, and Ammonia fluctuate more than 50%
from the mean?
Maximum % Difference:
DO 30% Alk 22%
pH 6% NH3 50%
YES (UNACCEPTABLE)
NO
10. Was the Ammonia concentration ever greater than 20 mg/L?
YES (See EPA/600/R-99/064, March 2000 to determine if ammonia
contributed to toxicity of H. azteca.)
NO X
11. Was the Ammonia concentration greater than 82 mg/L?
YES (See EPA/600/R-99/064, March 2000 to determine if ammonia
contributed to toxicity of C. tentans)
NO X
12. Was the Mean Control Survival in the H. azteca Control Sediments greater than or equal to 80%?
YES X
NO (UNACCEPTABLE)
13. Was the Mean Control Survival in the C. tentans Control Sediments greater than or eqaul to
70%?
YES X
NO (UNACCEPTABLE)
113
-------
14. Was the mean weight per surviving C. tentans control organism greater than 0.48 mg (ash-free
dry weight)?
YES X QAPP used dry weight of 0.8 mg/ individual. This was achieved.
NO (UNACCEPTABLE)
15. Was the overlying water renewed at a rate of 2 volumes per day?
YES X
NO (UNACCEPTABLE)
16. Please provide details for all of the "UNACCEPTABLE" responses marked above. Include
details on the specific results that potentially may be affected by any QA/QC discrepancies, and
recommendations regarding usability of data.
All discrepancies were related to following methods approved in the project QAPP.
114
-------
Appendix B. Results Physical Analyses On White Lake Sediments,
October 2000
115
-------
TABLE B-l. RESULTS OF GRAIN SIZE, TOC, AND % SOLIDS ANALYSES ON WHITE LAKE
SEDIMENT CORE SAMPLES. OCTOBER 2000.
>2000Mm 2000-1000 Mm
Sample ID Weight %
WL-1 TOP
WL-1 MID
WL-1 EOT
WL-1 TOP DUP
WL-1 MID DUP
WL-1 EOT DUP
WL-2 TOP
WL-2 MID
WL-2 EOT
WL-3 TOP
WL-3 MID
WL-3 TOP
WL-4 TOP
WL-4MID
WL-5 TOP
WL-5 MID
WL-5 EOT
WL-6 TOP
WL-6 MID
WL-6 EOT
WL-7 TOP
WL7MID
WL-7 EOT
WL-8 TOP
WL-8 MID
WL-8 EOT
WL-9 TOP
WL-9-MID
WL-9 EOT
WL-1 0 TOP
WL-10MID
WL-1 0 EOT
WL-21 TOP
WL-21 MID
WL-21 EOT
0
0
0
0
0
0
1
0
0
0
0
0
0
0
0
0
0
0
1
0
0
0
0
0
0
0
0
0
0
6
0
0
0
0
0
Weight%
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
1
0
0
0
0
0
0
0
0
1000-850 Mm
Weight %
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
850-500 Mm
Weight %
0
0
0
0
0
0
0
0
2
0
1
0
0
3
0
0
0
0
2
1
0
0
0
0
0
0
0
0
0
0
0
0
0
1
1
500-125 Mm
Weight %
2
13
7
2
6
12
4
13
90
4
23
7
10
80
7
9
6
2
43
8
8
11
8
8
8
6
9
9
7
23
11
6
10
10
6
125-63 Mm
Weight %
6
9
9
6
9
12
4
9
2
8
11
9
14
3
12
12
10
5
8
13
12
17
18
16
11
12
14
10
11
6
10
7
5
15
6
<63 Mm
TOC
Solic
Weight % % %
92
78
84
92
86
75
92
77
5
87
65
84
76
13
81
79
84
93
46
78
80
72
75
76
80
83
76
81
81
71
79
87
84
74
86
3.9
11
9.5
3.1
1.5
9
6.5
10
<1.0
2.2
4.8
8.1
2.9
<1.0
5.8
8.9
7.2
3.0
10
3.0
3.6
10
10
6.6
1.2
1.3
7.5
7.1
8.1
<1.0
9.7
8.9
2.7
7.1
3.4
12
14
15
11
15
14
11
15
67
13
18
15
13
53
12
15
15
17
38
16
12
16
15
12
15
16
13
15
16
14
15
14
20
16
13
116
-------
TABLE B-2. RESULTS OF GRAIN SIZE, TOC, AND % SOLIDS ANALYSES ON WHITE LAKE
SEDIMENT SAMPLES. OCTOBER 2000.
>2000«m 2000-1000 am
Sample ID
WL-1 P
WL-2P
WL-3P
WL-4P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-1 OP
WL-1 1 P
WL-1 2 P
WL-1 3 P
WL-1 4 P
WL-1 5 P
WL-1 6 P
WL-1 7 P
WL-1 8 P
WL-1 9 P
WL-20 P
WL-21 P
WL-22 P
WL-23 P
WL-24 P
Weight %
0
0
0
0
0
0
0
0
0
0
0
1
0
1
1
0
0
0
0
0
0
6
3
3
Weight%
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
2
3
1
1000-850 am
Weight %
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
0
850-500 wm
Weight %
0
0
0
5
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
1
2
1
500-125 wm
Weight %
4
6
4
82
6
5
7
8
7
5
7
6
30
13
6
3
5
8
6
11
19
12
10
12
125-63 am
Weight %
5
5
5
2
10
7
10
10
9
5
9
9
14
10
10
7
10
8
11
17
9
13
9
7
<63 am
Weight %
91
88
90
11
83
88
83
82
83
89
84
84
55
76
83
90
84
84
83
70
71
65
73
76
TOC
<10
3.5
3.0
<1.0
5.0
4.4
6.6
5.5
6.4
2.2
6.0
7.1
5.0
18
7.4
10
10
11
11
8.5
5.6
4.6
5.9
8.2
Soli(
7
10
10
61
11
10
10
11
11
10
11
11
15
13
12
14
15
16
15
16
13
11
12
15
117
-------
TABLE B-3. TOC MATRIX SPIKE AND MATRIX SPIKE DUPLICATE RESULTS FOR WHITE
LAKE SEDIMENT SAMPLES. OCTOBER 2000.
Matrix Spike Data
Sample OC
Sample ID
WL-5 Top
WL-6 Bot
WL-9 Top
WL-21 Top
WL-5P
WL-14P
WL-18P
mg
6.1
2.6
8.0
2.7
5.0
7.2
9.0
MSOC
mg
20.2
56.9
28.7
22.3
26.5
31.8
36.1
Matrix Spike
Cone, mg
12.4
52.9
21.0
18.6
23.5
25.1
26.7
% Recovery
114
103
98
106
91
98
101
Matrix Spike Duplicate Data
Sample OC
Sample ID
WL-5 Top
WL-6 Bot
WL-9 Top
WL-21 Top
WL-5P
WL-14P
WL-18P
mg
6.1
2.6
8.0
2.7
5.0
7.2
9.0
MSDOC
mg
30.9
33.1
41.5
19.9
31.4
29.8
30.1
Matrix Spike
Cone, mg °i
23.4
29.1
34.1
18.6
25.8
22.7
21.6
% Recovery RPD*
106 8
105 2
98 0
92 13
102 11
99 8
98 0
* RPD was calculated using the % recoveries for the ms and msd.
Different amounts (mg) of sample and spike were used for the ms and msc
118
-------
TABLE B-4. QUALITY CONTROL RESULTS FOR GRAIN SIZE ANALYSES ON WHITE LAKE
SEDIMENT SAMPLES. OCTOBER 2000.
>2000Mm 2000-1000 Mm 1000-850 Mm 850-500 Mm 500-125 Mm 125-63 Mm <63Mm
Sample ID Weight % Weight% Weight % Weight % Weight % Weight % Weight %
WL-2Bot 00 0 2 90 2 5
WL-2BotDup 00 0 3 90 2 5
WL-4Mid 00 0 3 81 2 12
WL-4 Mid Dup 00 0 3 81 3 12
Wl-6 Mid 1 0 0 2 43 8 46
WL-6MidDup 01 0 2 42 7 47
WL-10P 00 0 0 5 5 89
WL-lOPDup 00 0 0 6 5 90
WL-15 PI 0 0 0 6 11 83
WL-15PDup 00 0 0 6 10 83
WL-18P 00 0 0 8 8 84
WL-18PDup 10 0 1 6 11 82
WL-21P 00 0 1 19 9 71
WL-21PDup 00 0 1 17 9 73
119
-------
Appendix C. Organic Analyses On White Lake Sediments, October 2000.
120
-------
TABLE C-l. RESULTS OF SEMIVOLATILE ORGANIC ANALYSES ON WHITE LAKE SEDIMENTS,
OCTOBER 2000. (MG/KG DRY WT)
WL-1
WL-1 Dup
WL-2
WL-3
WL-4
PCB-1016
PCB-1221
PCB-1232
PCB-1242
PCB-1248
PCB-1254
PCB-1260
1,2,4-TRICHLOROBENZENE
1,2-DICHLOROBENZENE
1,3-DICHLOROBENZENE
1,4-DICHLOROBENZENE
2,4,5-TRICHLOROPHENOL
2,4,6-TRICHLOROPHENOL
2,4-DICHLOROPHENOL
2,4-DIMETHYLPHENOL
2,4-DINITROPHENOL
2,4-DINITROTOLUENE
2,6-DINITROTOLUENE
2-CHLORONAPHTHALENE
2-CHLOROPHENOL
2-METHYLNAPHTHALENE
2-METHYLPHENOL
2-NITROANILINE
2-NITROPHENOL
3,3'-DICHLOROBENZIDINE
3-NITROANILINE
4,6-DINITRO- 2-METHYLPHENOL
4-BROMOPHENYL PHENYLETHER
4-CHLORO-3-METHYLPHENOL
4-CHLOROANILINE
4-CHLOROPHENYLPHENYL- ETHER
4-METHYLPHENOL
4-NITROANILINE
4-NITROPHENOL
ACENAPHTHENE
ACENAPHTHYLENE
ANTHRACENE
BENZO (A) ANTHRACENE
BENZO (A) PYRENE
BENZO (B) FLUORANTHENE
BENZO (G,H,I,) PERYLENE
BENZO (K) FLUORANTHENE
BIS (2-CHLOROETHOXY)- METHANE
BIS (2-CHLOROETHYL) ETHER
BIS (2-CHLOROISOPROPYL)- ETHER
BIS (2-ETHYLHEXYL)- PHTHALATE
BUTYL BENZYL PHTHALATE
CARBAZOLE
CHRYSENE
DI-N-BUTYLPHTHALATE
DI-N-OCTYLPHTHALATE
DIBENZO (A,H) ANTHRACENE
DIBENZOFURAN
DIETHYLPHTHALATE
DIMETHYLPHTHALATE
FLUORANTHENE
FLUORENE
HEXACHLOROBENZENE
HEXACHLOROBUTADIENE
HEXACHLOROCYCLOPENTADIENE
HEXACHLOROETHANE
INDENO (1,2,3-CD) PYRENE
ISOPHORONE
N-NITROSO-DI-PHENYLAMINE
N-NITROSODI-N-PROPYLAMINE
NAPHTHALENE
NITROBENZENE
PENTACHLOROPHENOL
PHENANTHRENE
PHENOL
PYRENE
'op
0.33
0.33
0.33
0.33
0.22
0.33
0.33
1.7
1.7
1.7
1.7
8.6
1.7
1.7
1.7
8.6
1.7
1.7
1.7
1.7
1.7
1.7
8.6
1.7
10
8.6
8.6
1.7
1.7
6.6
1.7
1.7
8.6
8.6
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
0.38
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
8.6
1.7
1.7
1.7
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
Bottom
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.26
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
Top
< 0.33
< 0.33
< 0.33
< 0.33
0.44
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 10
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.42
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
Bottom
< 0.33
< 0.33
< 0.33
< 0.33
0.06
< 0.33
< 0.33
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.32
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
Top
< 0.33
< 0.33
< 0.33
< 0.33
0.06 0.07
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 10
< 8.6
< 8.6
< 1.7
< 1.7
< 6.6
< 1.7
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
0.56
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 4.7
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.35
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
Top
< 0.33
< 0.33
< 0.33
< 0.33
0.06
< 0.33
< 0.33
< 1.4
< 1.4
< 1.4
< 1.4
< 7.2
< 1.4
< 1.4
< 1.4
< 7.2
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 7.2
< 1.4
< 8.4
< 7.2
< 7.2
< 1.4
< 1.4
< 5.5
< 1.4
< 1.4
< 7.2
< 7.2
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
0.99
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 1.4
< 7.2
< 1.4
< 1.4
< 1.4
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.93
< 0.93
< 0.93
< 0.93
< 4.8
< 0.93
< 0.93
< 0.93
< 4.8
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 4.8
< 0.93
< 5.6
< 4.8
< 4.8
< 0.93
< 0.93
< 3.7
< 0.93
< 0.93
< 4.8
< 4.8
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 0.93
< 4.8
< 0.93
< 0.93
< 0.93
Bottom
< 0.33
< 0.33
< 0.33
< 0.33
0.06
< 0.33
< 0.33
< 1.0
< 1.0
< 1.0
< 1.0
< 5.4
< 1.0
< 1.0
< 1.0
< 5.4
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 5.4
< 1.0
< 6.3
< 5.4
< 5.4
< 1.0
< 1.0
< 4.1
< 1.0
< 1.0
< 5.4
< 5.4
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
0.06
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 1.0
< 5.4
< 1.0
< 1.0
< 1.0
Top
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.3
< 1.3
< 1.3
< 1.3
< 6.6
< 1.3
< 1.3
< 1.3
< 6.6
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 6.6
< 1.3
< 7.8
< 6.6
< 6.6
< 1.3
< 1.3
< 5.1
< 1.3
< 1.3
< 6.6
< 6.6
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
0.17
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 6.6
< 1.3
< 1.3
< 1.3
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 0.33
< 0.33
< 0.33
< 1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 0.33
< 2.0
< 1.7
< 1.7
< 0.33
< 0.33
< 1 .3
< 0.33
< 0.33
< 1.7
< 1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 0.33
< 0.33
< 0.33
121
-------
TABLE C-l (CONTINUED). RESULTS OF SEMIVOLATILE ORGANIC ANALYSES ON WHITE LAKE
SEDIMENTS, OCTOBER 2000.
PCB-1016
PCB-1221
PCB-1232
PCB-1242
PCB-1248
PCB-1254
PCB-1260
1,2,4-TRICHLOROBENZENE
1,2-DICHLOROBENZENE
1,3-DICHLOROBENZENE
1,4-DICHLOROBENZENE
2,4,5-TRICHLOROPHENOL
2,4,6-TRICHLOROPHENOL
2,4-DICHLOROPHENOL
2,4-DIMETHYLPHENOL
2,4-DINITROPHENOL
2,4-DINITROTOLUENE
2,6-DINITROTOLUENE
2-CH LORONAPHTHALEN E
2-CHLOROPHENOL
2-METHYLNAPHTHALENE
2-METHYLPHENOL
2-NITROANILINE
2-NITROPHENOL
3,3'-DICHLOROBENZIDINE
3-NITROANILINE
4,6-DINITRO-2-METHYLPHENOL
4-BROMOPHENYL PHENYLETHER
4-CHLORO-3-METHYLPHENOL
4-CHLOROANILINE
4-CHLOROPHENYLPHENYL- ETHER
4-METHYLPHENOL
4-NITROANILINE
4-NITROPHENOL
ACENAPHTHENE
ACENAPHTHYLENE
ANTHRACENE
BENZO (A) ANTHRACENE
BENZO(A)PYRENE
BENZO (B) FLUORANTH EN E
BENZO(G,H,I,)PERYLENE
BENZO (K) FLUORANTH EN E
BIS (2-CHLOROETHOXY> METHANE
BIS (2-CHLOROETHYL) ETHER
BIS (2-CHLOROISOPROPYL)- ETHER
BIS (2-ETHYLHEXYL)- PHTHALATE
BUTYL BENZYL PHTHALATE
CARBAZOLE
CHRYSENE
DI-N-BUTYLPHTHALATE
DI-N-OCTYLPHTHALATE
DIBENZO (A,H) ANTHRACENE
DIBENZOFURAN
DIETHYLPHTHALATE
DIMETHYLPHTHALATE
FLUORANTH ENE
FLUORENE
HEXACHLOROBENZENE
HEXACHLOROBUTADIENE
HEXACHLOROCYCLOPENTADIENE
HEXACHLOROETHANE
INDENO(1,2,3-CD)PYRENE
ISOPHORONE
N-NITROSO-DI-PH ENYLAMIN E
N-NITROSODI-N-PROPYLAMINE
NAPHTHALENE
NITROBENZENE
PENTACHLOROPHENOL
PHENANTHRENE
PHENOL
PYRENE
<
<
<
<
<
«
<
<
<
<
Top
0.33
0.33
0.33
0.33
0.17
0.33
0.33
'
'
6.6
'
6.6
'
'
'
'
6.6
'
6.6
6.6
'
5.1
'
6.6
6.6
'
'
'
'
'
'
'
'
1.3
'
1.3
'
'
'
'
1.3
1.3
1.3
1.3
1.3
1.3
1.3
1.3
1.3
1.3
1.3
6.6
1.3
1.3
1.3
WL-5
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 6.1
'
< 6.1
'
'
'
'
< 6.1
'
< 6.1
< 6.1
'
< 4.7
'
< 6.1
< 6.1
'
'
'
'
'
'
'
'
< 1.2
'
< 1.2
'
'
'
'
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
Bottom
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 5.4
'
< 5.4
'
'
'
'
< 5.4
'
< 5.4
< 5.4
'
< 4.2
'
< 5.4
< 5.4
'
'
'
'
'
'
'
'
< 1.1
'
< 1.1
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.4
< 1.1
< 1.1
< 1.1
Top
< 0.33
< 0.33
< 0.33
< 0.33
0.39
< 0.33
< 0.33
'
'
< 5.7
'
< 5.7
'
'
'
'
< 5.7
'
< 5.7
< 5.7
'
< 4.4
'
< 5.7
< 5.7
'
'
'
'
'
'
'
'
0.22
'
< 1.1
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.7
< 1.1
< 1.1
< 1.1
WL-6
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 2.4
'
< 2.4
'
'
'
'
< 2.4
'
< 2.4
< 2.4
'
< 1.8
'
< 2.4
< 2.4
'
'
'
'
'
'
'
'
0.19
'
< 0.46
'
'
'
'
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 0.46
< 2.4
< 0.46
< 0.46
< 0.46
Bottom
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 2.3
'
< 2.3
'
'
'
'
< 2.3
'
< 2.3
< 2.3
'
< 1.8
'
< 2.3
< 2.3
'
'
'
'
'
'
'
'
0.14
'
< 0.45
'
'
'
'
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 0.45
< 2.3
< 0.45
< 0.45
< 0.45
Top
< 0.33
< 0.33
< 0.33
< 0.33
0.24
< 0.33
< 0.33
'
'
< 7.8
'
< 7.8
'
'
'
'
< 7.8
'
< 7.8
< 7.8
'
< 6.0
'
< 7.8
< 7.8
'
'
'
'
'
'
'
'
0.28
'
< 1.5
'
'
'
'
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
WL-7
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 5.8
'
< 5.8
'
'
'
'
< 5.8
'
< 5.8
< 5.8
'
< 4.4
'
< 5.8
< 5.8
'
'
'
'
'
'
'
'
0.25
'
0.99
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
Botom
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 5.4
'
< 5.4
'
'
'
'
< 5.4
'
< 5.4
< 5.4
'
< 4.2
'
< 5.4
< 5.4
'
'
'
'
'
'
'
'
< 1.1
'
< 1.1
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.4
< 1.1
< 1.1
< 1.1
Top
< 0.33
< 0.33
< 0.33
< 0.33
0.27
< 0.33
< 0.33
'
'
< 6.6
'
< 6.6
'
'
'
'
< 6.6
'
< 6.6
< 6.6
'
< 5.1
'
< 6.6
< 6.6
'
'
'
'
'
'
'
'
0.25
'
< 1.3
'
'
'
'
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 1.3
< 6.6
< 1.3
< 1.3
< 1.3
WL-8
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 5.8
'
< 5.8
'
'
'
'
< 5.8
'
< 5.8
< 5.8
'
< 4.4
'
< 5.8
< 5.8
'
'
'
'
'
'
'
'
< 1.1
'
< 1.1
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
Bottom
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
'
'
< 5.4 <
'
< 5.4 <
'
'
'
'
< 5.4 <
'
< 5.4 <
< 5.4 <
'
< 4.2 <
'
< 5.4 <
< 5.4 <
'
'
'
'
'
'
'
'
< 1.1 <
'
< 1.1 <
'
'
'
'
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 1.1 <
< 5.4 <
< 1.1 <
< 1.1 <
< 1.1 <
Top
0.33
0.33
0.33
0.33
0.33
0.33
0.33
'
'
7.1
'
7.1
'
'
'
'
7.1
'
7.1
7.1
'
5.5
'
7.1
7.1
'
'
'
'
'
'
'
'
1.4
'
1.4
'
'
'
'
1.4
1.4
1.4
1.4
1.4
1.4
1.4
1.4
1.4
1.4
1.4
7.1
1.4
1.4
1.4
WL-9
Middle
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 5.8
'
< 5.8
'
'
'
'
< 5.8
'
< 5.8
< 5.8
'
< 4.4
'
< 5.8
< 5.8
'
'
'
'
'
'
'
'
< 1.1
'
< 1.1
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
Botom
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
'
'
< 5.4
'
< 5.4
'
'
'
'
< 5.4
'
< 5.4
< 5.4
'
< 4.2
'
< 5.4
< 5.4
'
'
'
'
'
'
'
'
0.23
'
< 1.1
'
'
'
'
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.4
< 1.1
< 1.1
< 1.1
122
-------
TABLE C-l (CONTINUED). RESULTS OF SEMIVOLATILE ORGANIC ANALYSES ON WHITE LAKE
SEDIMENTS, OCTOBER 2000.
PCB-1016
PCB-1221
PCB-1232
PCB-1242
PCB-1248
PCB-1254
PCB-1260
1,2,4-TRICH LOROBENZEN E
1,2-DICHLOROBENZENE
1,3-DICHLOROBENZENE
1,4-DICHLOROBENZENE
2,4,5-TRICH LOROPH ENOL
2,4,6-TRICHLOROPHENOL
2,4-DICHLOROPHENOL
2,4-DIMETHYLPHENOL
2,4-DINITROPHENOL
2,4-DINITROTOLUENE
2,6-DINITROTOLUENE
2-CHLORONAPHTHALENE
2-CHLOROPHENOL
2-METHYLNAPHTHALEN E
2-METHYLPHENOL
2-NITROANILINE
2-NITROPHENOL
3,3'-DICHLOROBENZIDINE
3-NITROANILINE
4,6-DINITRO- 2-METHYLPHENOL
4-BROMOPHENYL PHENYLETHER
4-CHLORO-3-METHYLPHENOL
4-CHLOROANILINE
4-CHLOROPHENYLPHENYL- ETHER
4-METHYLPHENOL
4-NITROANILINE
4-NITROPHENOL
ACENAPHTHENE
ACENAPHTHYLENE
ANTHRACENE
BENZO(A) ANTHRACENE
BENZO(A)PYRENE
BENZO (B) FLUORANTHENE
BENZO(G,H,I,)PERYLENE
BENZO (K) FLUORANTHENE
BIS (2-CHLOROETHOXY)- METHANE
BIS (2-CHLOROETHYL) ETHER
BIS (2-CHLOROISOPROPYL)- ETHER
BIS (2-ETHYLHEXYL)- PHTHALATE
BUTYL BENZYL PHTHALATE
CARBAZOLE
CHRYSENE
DI-N-BUTYLPHTHALATE
DI-N-OCTYLPHTHALATE
DIBENZO(A.H) ANTHRACENE
DIBENZOFURAN
DIETHYLPHTHALATE
DIMETHYLPHTHALATE
FLUORANTHENE
FLUORENE
HEXACHLOROBENZENE
HEXACHLOROBUTADIENE
HEXACHLOROCYCLOPENTADIENE
HEXACHLOROETHANE
INDENO(1,2,3-CD)PYRENE
ISOPHORONE
N-NITROSO-DI-PHENYLAMINE
N-NITROSODI-N-PROPYLAMINE
NAPHTHALENE
NITROBENZENE
PENTACHLOROPHENOL
PHENANTHRENE
PHENOL
PYRENE
Top
< 0.33
< 0.33
< 0.34
< 0.33
0.06
< 0.33
< 0.33
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 6.8
< 5.8
< 5.8
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 5.8
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
0.25
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
WL-10
Middle Bottom
< 0.33
< 0.33
< 0.34
< 0.33
0.06
< 0.33
< 0.33
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 6.8
< 5.8
< 5.8
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 5.8
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 1.1
< 5.8
< 1.1
< 1.1
< 1.1
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.84
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
WL-21 .... ,_
... , „ WL-1P
Top Middle
< 0.33
< 0.33
< 0.33
< 0.33
22
< 0.33
< 0.33
< 1.2
< 1.2
1.9
0.65
< 6.1
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 7.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 6.1
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.94
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
0.54
0.081
0.036
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 1.2
< 6.1
< 1.2
< 1.2
< 1.2
< 0.98 <
< 0.98 <
< 0.99 <
< 0.98 <
0.84 <
< 0.98 <
< 0.98 <
< 0.98
< 5.0 <
< 0.98 <
0.29 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 5.0 <
< 0.98 <
< 5.9 <
< 5.0 <
< 5.0 <
< 0.98 <
< 0.98 <
< 3.9 <
< 0.98 <
< 0.98 <
< 5.0 <
< 5.0 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
0.54
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.98 <
< 5.0 <
< 0.98 <
< 0.98 <
< 0.98 <
< 0.46 <
< 0.46 <
< 0.46 <
< 0.46 <
< 2.4 <
< 0.46 <
< 0.46 <
< 0.46 <
0.33
0.33
0.33
0.33
0.33
0.33
0.33
1.8
1.8
1.8
1.8
9.2
1.8
1.8
1.8
9.2
1.8
1.8
1.8
1.8
1.8
1.8
9.2
1.8
11
9.2
9.2
1.8
1.8
1.8
1.8
9.2
9.2
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
0.92
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
1.8
9.2
1.8
1.8
1.8
WL-1P
Dup
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 10
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
WL-2P WL-3P
< 0.33 <
< 0.33 <
0.34 <
< 0.33 <
0/09 <
< 0.33 <
< 0.33 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 7.8 <
< 1.5 <
< 1.5 <
< 1.5 <
< 7.8 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 7.8 <
< 1.5 <
< 9.2 <
< 7.8 <
< 7.8 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 7.8 <
< 7.8 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 1.5 <
< 7.8 <
< 1.5 <
< 1.5 <
< 1.5 <
0.33
0.33
0.34
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
1.7
0.33
0.33
0.33
1.7
0.33
0.33
0.33
0.33
0.33
0.33
1.7
0.33
2.0
1.7
1.7
0.33
0.33
0.33
0.33
1.7
1.7
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.31
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
1.7
0.33
0.33
0.33
WL-4P
< 0.33
< 0.33
< 0.34
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.8
< 1.7
< 1.7
< 1.7
< 8.8
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.8
< 1.7
< 10
< 8.8
< 8.8
< 1.7
< 1.7
< 1.7
< 1.7
< 8.8
< 8.8
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.8
< 1.7
< 1.7
< 1.7
WL-5P
< 0.33
< 0.33
< 0.34
< 0.33
< 0.33
< 0.33
< 0.33
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 9.2
< 7.8
< 7.8
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 7.8
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
0.62
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
WL-6P
< 0.33
< 0.33
< 0.34
< 0.33
0.07
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 10
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
0.32
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
WL-7P
< 0.33
< 0.33
< 0.34
< 0.33
0.08
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 10
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
0.35
< 1.7
< 1.7
< 1.7
0.30
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
WL-8P
< 0.33
< 0.33
< 0.34
< 0.33
0.08
< 0.33
< 0.33
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 9.2
< 7.8
< 7.8
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 7.8
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
1.3
< 1.5
< 1.5
< 1.5
0.25
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 1.5
< 7.8
< 1.5
< 1.5
< 1.5
WL-9P
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 10
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 1.7
123
-------
TABLE C-l (CONTINUED). RESULTS OF SEMIVOLATILE ORGANIC ANALYSES ON WHITE LAKE
SEDIMENTS, OCTOBER 2000.
WL-10P WL-11P WL-12P WL-13P WL-14P WL-15P WL-16P WL-17P WL-18P WL-19P WL-20 WL-21
PCB-1016
PCB-1221
PCB-1232
PCB-1242
PCB-1248
PCB-1254
PCB-1260
1,2,4-TRICHLOROBENZENE
1,2-DICHLOROBENZENE
1,3-DICHLOROBENZENE
1,4-DICHLOROBENZENE
2,4,5-TRICHLOROPHENOL
2,4,6-TRICHLOROPHENOL
2,4-DICHLOROPHENOL
2,4-DIMETHYLPHENOL
2,4-DINITROPHENOL
2,4-DINITROTOLUENE
2,6-DINITROTOLUENE
2-CHLORONAPHTHALENE
2-CHLOROPHENOL
2-METHYLNAPHTHALENE
2-HETHYLPHENOL
2-NITROANILINE
2-NITROPHENOL
3,3-DICHLOROBENZIDINE
3-NITROANILINE
4,6-DINITRO- 2-METHYLPHENOL
4-BROMOPHENYL PHENYLETHER
4-CHLORO-3-HETHYLPHENOL
4-CHLOROANILINE
4-CHLOROPHENYLPHENYL- ETHER
4-HETHYLPHENOL
4-NITROANILINE
4-NITROPHENOL
ACENAPHTHENE
ACENAPHTHYLENE
ANTHRACENE
BENZO (A) ANTHRACENE
BENZO(A)PYRENE
BENZO fB) FLUORANTHENE
BENZO (G,H,I,) PERYLENE
BENZO (K) FLUORANTHENE
BIS (2-CHLOROETHOXY)- METHANE
BIS (2-CHLOROETHYL) ETHER
BIS (2-CHLOROISOPROPYL)- ETHER
BIS(2-ETHYLHEXYL)- PHTHALATE
BUTYL BENZYL PHTHALATE
CARBAZOLE
CHRYSENE
DI-N-BUTYLPHTHALATE
DI-N-OCTYLPHTHALATE
DIBENZO (A,H) ANTHRACENE
DIBENZOFURAN
DIETHYLPHTHALATE
DIMETHYLPHTHALATE
FLUORANTHENE
FLUORENE
HEXACHLOROBENZENE
HEXACHLOROBUTADIENE
HEXACHLOROCYCLOPENTADIENE
HEXACHLOROETHANE
INDENO (1,2,3-CD) PYRENE
ISOPHORONE
N-NITROSO-DI-PHENYLAHINE
N-NITROSODI-N-PROPYLAMINE
NAPHTHALENE
NITROBENZENE
PENTACHLOROPHENOL
PHENANTHRENE
PHENOL
PYRENE
<
<
<
<
<
<
*
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
<
0.33 <
0.33 <
0.33 <
0.33 <
0.33 <
0.33 <
0.33 <
1.8 <
9.2 <
1.8 <
9.2 <
1.8 <
1.8 <
1.8 <
1.8 <
9.2 <
1.8 <
11 <
9.2 <
9.2 <
1.8 <
7.1 <
1.8 <
9.2 <
9.2 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
0.92 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
1.8 <
9.2 <
1.8 <
1.8 <
0.33
0.33
0.33
0.33
0.33
0.33
0.33
1.7
8.6
1.7
8.6
1.7
1.7
1.7
1.7
8.6
1.7
10
8.6
8.6
1.7
6.6
1.7
8.6
8.6
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
8.6
1.7
1.7
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 1.7 <
< 8.7 <
< 1.7 <
< 8.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 8.7 <
< 1.8 <
< 11 <
< 8.6 <
< 8.6 <
< 1.7 <
< 6.7 <
< 1.7 <
< 8.6 <
< 8.6 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 8.6 <
< 1.7 <
< 1.7 <
0.33
0.33
0.33
0.33
0.33
0.33
0.33
1.7
8.8
1.7
8.8
1.7
1.7
1.7
1.7
8.8
1.9
12
8.6
8.6
1.7
6.8
1.7
8.6
8.6
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
8.6
1.7
1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 8.9
< 1.7
< 8.9
< 1.7
< 1.7
< 1.7
< 1.7
< 8.9
< 1.10
< 13
< 8.6
< 8.6
< 1.7
< 6.9
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 8.10
< 1.7
< 8.10
< 1.7
< 1.7
< 1.7
< 1.7
< 8.10
< 1.11
< 14
< 8.6
< 8.6
< 1.7
< 6.10
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 8.11
< 1.7
< 8.11
< 1.7
< 1.7
< 1.7
< 1.7
< 8.11
< 1.12
< 15
< 8.6
< 8.6
< 1.7
< 6.11
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
1.1
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
0.18
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 0.33 <
< 1.7 <
< 8.12 <
< 1.7 <
< 8.12 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 8.12 <
< 1.13 <
< 16 <
< 8.6 <
< 8.6 <
< 1.7 <
< 6.12 <
< 1.7 <
< 8.6 <
< 8.6 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 1.7 <
< 8.6 <
< 1.7 <
< 1.7 <
0.33
0.33
0.33
0.33
0.33
0.33
0.33
1.7
8.13
1.7
8.13
1.7
1.7
1.7
1.7
8.13
1.14
17
8.6
8.6
1.7
6.13
1.7
8.6
8.6
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
8.6
1.7
1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 8.14
< 1.7
< 8.14
< 1.7
< 1.7
< 1.7
< 1.7
< 8.14
< 1.15
< 18
< 8.6
< 8.6
< 1.7
< 6.14
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 0.33
< 1.7
< 8.15
< 1.7
< 8.15
< 1.7
< 1.7
< 1.7
< 1.7
< 8.15
< 1.16
< 19
< 8.6
< 8.6
< 1.7
< 6.15
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
< 0.33
< 0.33
< 0.33
21
< 0.33
< 0.33
< 0.33
< 1.7
< 8.16
< 1.7
< 8.16
< 1.7
< 1.7
< 1.7
< 1.7
< 8.16
< 1.17
< 20
< 8.6
< 8.6
< 1.7
< 6.16
< 1.7
< 8.6
< 8.6
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
0.4
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 1.7
< 8.6
< 1.7
< 1.7
124
-------
TABLE C-2. SURROGATE STANDARD RECOVERIES FOR SEMIVOLATILE ORGANICS ANALYSES
ON WHITE LAKE SEDIMENTS, OCTOBER 2000.
Sample
WL-1 Top
WL-1 Middle
WL-1 Bottom
WL-1 Top Dup
WL-1 Middle Dup
WL-1 Bottom Dup
WL-2 Top
WL-2 Middle
WL-3 Top
WL-3 Middle
WL-3 Bottom
WL-4 Top
WL-4 Middle
WL-5 Top
WL-5 Middle
WL-5 Bottom
WL-6 Top
WL-6 Middle
WL-6 Bottom
WL-7 Top
WL-7 Middle
WL-7 Bottom
WL-8 Top
WL-8 Middle
WL-8 Bottom
WL-9 Top
WL-9 Middle
WL-9 Bottom
WL-1 0 Top
WL-10 Middle
WL-1 0 Bottom
WL-21 Top
WL-21 Middle
WL-1P
WL-2P
WL-3P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-1 OP
WL-16P
WL-21 P
2-Fluoro
biphenyl
77
97
89
84
83
86
83
72
89
82
89
81
90
63
56
56
75
77
83
91
84
80
53
70
65
63
64
82
85
86
81
94
91
81
87
91
87
85
78
86
72
69
84
94
2-Fluoro
phenol
79
89
92
82
82
81
81
70
79
77
83
67
74
52
46
44
71
73
66
71
69
69
41
57
53
52
56
65
65
65
70
78
77
75
70
76
72
79
66
79
61
65
70
86
d5-Nitro
benzene
61
72
77
72
80
73
68
64
73
77
79
67
61
49
36
44
68
34
73
54
63
60
42
58
46
51
45
56
60
70
61
70
72
73
80
69
73
77
75
69
63
64
71
85
d6-Phenol
72
84
80
76
79
79
76
68
78
75
78
63
72
53
46
45
67
73
65
68
70
71
43
56
52
52
51
65
65
66
69
72
78
73
73
76
76
74
70
77
65
62
84
64
o-Terphenyl
66
71
70
68
66
70
67
61
69
66
73
67
65
52
45
47
65
70
71
64
68
67
46
57
55
52
47
65
61
65
62
70
73
73
67
68
71
66
65
70
58
57
63
65
2,4,6-Tribromo
phenol
59
72
67
63
63
63
62
48
63
57
60
46
58
53
45
47
54
58
56
73
70
55
34
56
52
51
41
68
68
61
65
72
61
58
64
63
58
55
52
54
61
48
59
52
125
-------
TABLE C-3. RESULTS OF MATRIX SPIKE/MATRIX SPIKE DUPLICATE ANALYSES FOR
SEMIVOLATILE ORGANICS ANALYSES ON WHITE LAKE SEDIMENTS, OCTOBER 2000.
WL-1 Bottom
Parameter
Acenaphthene
1,4-Dichlorobenzene
2,4-Dinitrotoluene
Naphthalene
N-Nitrosodi-n-Propylamine
Pyrene
1,2,4-Trichlorobenzene
4-Chloro-3-Methyl phenol
2-Chlorophenol
4-Nitrophenol
Pentachlorophenol
Phenol
WI-10Top
Parameter
Acenaphthene
1,4-Dichlorobenzene
2,4-Dinitrotoluene
Naphthalene
N-Nitrosodi-n-Propylamine
Pyrene
1,2,4-Trichlorobenzene
4-Chloro-3-Methylphenol
2-Chlorophenol
4-Nitrophenol
Pentachlorophenol
Phenol
WL-2P
Parameter
Phenol
2-Chlorophenol
1,4-Dichlorobenzene
N-Nitrosodi-n-Propylamine
1,2,4-Trichlorobenzene
Naphthalene
4-Chloro-3-Methylphenol
Acenaphthene
4-Nitrophenol
2,4-Dinitrotoluene
Pentachlorophenol
Pyrene
WL-9P
Parameter
Phenol
2-Chlorophenol
1,4-Dichlorobenzene
N-Nitrosodi-n-Propylamine
1,2,4-Trichlorobenzene
Naphthalene
4-Chloro-3-Methylphenol
Acenaphthene
4-Nitrophenol
2,4-Dinitrotoluene
Pentachlorophenol
Pyrene
Sample Cone
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<1.70
<1.70
<0.33
Sample Cone
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<1.70
<1.70
<0.33
Sample Cone
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<1.70
<0.33
<1.70
<0.33
Sample Cone
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<1.70
<0.33
<1.70
<0.33
Spike Quantity
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
Spike Quantity
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
3.33
Spike Quantity
6.67
6.67
3.33
3.33
3.33
3.33
6.67
3.33
6.67
3.33
6.67
3.33
Spike Quantity
6.67
6.67
3.33
3.33
3.33
3.33
6.67
3.33
6.67
3.33
6.67
3.33
Sample +Spike
3.07
2.87
2.97
3.01
3.55
3.28
2.82
3.22
3.09
2.37
2.71
3.20
Sample +Spike
2.97
2.80
2.96
2.90
3.18
3.14
2.76
3.01
2.91
2.62
2.78
2.92
Sample +Spike
6.51
6.11
2.80
2.72
2.86
2.96
5.90
2.86
3.99
2.84
5.38
2.33
Sample +Spike
5.91
5.49
2.45
2.64
2.59
2.84
5.79
2.79
3.80
2.64
4.47
2.24
Spike %Rec
92
86
89
90
107
98
85
97
93
71
81
96
Spike %Rec
89
84
89
87
95
94
83
90
87
79
83
88
Spike %Rec
98
92
84
82
86
89
88
86
60
85
81
70
Spike %Rec
89
82
74
79
78
85
87
84
57
79
67
67
Control Limits
47-112
43-122
52-128
55-129
48-120
42-129
57-116
61-125
51-126
34-128
20-143
58-126
Control Limits
47-112
43-122
52-128
55-129
48-120
42-129
57-116
61-125
51-126
34-128
20-143
58-126
Control Limits
58-126
51-126
43-122
48-120
57-116
55-129
61-125
47-112
34-128
52-128
20-143
42-129
Control Limits
58-126
51-126
43-122
48-120
57-116
55-129
61-125
47-112
34-128
52-128
20-143
42-129
126
-------
Table C-4. Surrogate Standard Recoveries For PCB Analyses On White Lake Sediments,
October 2000.
Sample
WL-1 Top
WL-1 Middle
WL-1 Bottom
WL-1 Top duplicate
WL-1 Middle duplicate
WL-1 Bottom duplicate
WL-2 Top
WL-2 Middle
WL-3 Top
WL-3 Middle
WL-3 Bottom
WL-4 Top
WL-4 Middle
WL-5 Top
WL-5 Middle
WL-5 Bottom
WL-6 Top
WL-6 Middle
WL-6 Bottom
WL-7 Top
WL-7 Middle
WL-7 Bottom
WL-8 Top
WL-8 Middle
WL-8 Bottom
WL-9 Top
WL-9 Middle
WL-9 Bottom
WL-10Top
WL-10 Middle
WL-10 Bottom
WL-21 Top
WL-21 Middle
WL-1P
WL-2P
WL-3P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-10P
WL-11P
WL-12P
WL-13P
WL-14P
WL-15P
WL-16P
WL-17P
WL-18P
WL-19P
WL-20P
WL-21 P
Tetrachloro-M-xylene
84
83
82
85
91
94
90
82
79
79
75
84
85
81
83
83
81
84
81
86
84
87
82
86
84
86
83
88
90
84
86
*
83
79
78
81
76
81
80
84
84
83
81
80
82
73
71
70
81
80
80
89
73
Decachlorobiphenyl
91
94
88
94
100
99
95
87
85
86
85
90
93
90
89
91
93
91
88
94
89
92
90
92
90
91
90
94
94
90
92
*
96
86
81
88
88
91
91
92
90
91
86
89
99
89
75
87
86
90
93
97
86
Surrogates not available due to dilution
127
-------
Appendix D. Results Of Metals Analyses For White Lake Sediments,
October 2000.
128
-------
TABLE D-l. RESULTS OF METALS ANALYSES IN WHITE LAKE SEDIMENT, OCTOBER 2000. (MG/KG DRY WT)
Sample
WL-1 Top
WL-1 Mid
WL-1 Bot.
WL-2 Top
WL-2 Bot
WL-3 Top
WL-3 Mid
WL-3 Bot
WL-4 Top
WL-4 Mid
WL-5 Top
WL-5 Mid
WL-5 Bot
WL-6 Top
WL-6 Mid
WL-6 Bot
WL-7 Top
WL-7 Mid
WL-7 Bot
WL-8 Top
WL-8 Mid
WL-8 Bot
WL-9 Top
WL-9 Mid
WL-9 Bot
WL-1 0 Top
WL-1 0 Mid
WL-10Bot
WL-21 Top
WL-2 1 Mid
Arsenic
9.1
6.1
6.6
9.0
7.5
7.9
6.2
5.7
9.0
1.8
8.9
6.3
6.1
6.7
12
12
8.2
6.5
5.5
7.7
7.7
7.3
9.6
7.5
7.0
6.5
5.8
6.5
9.5
7.8
Barium
130
130
160
160
150
120
110
130
130
18
140
130
150
180
88
110
130
110
110
140
120
1470
140
120
120
92
110
110
162
120
Cadmium
1.3
0.87
0.74
1.6
0.97
1.5
0.61
0.48
1.9
0.15
1.4
0.53
<0.1
1.3
0.26
0.19
1.6
0.65
0.35
1.4
0.42
0.49
1.5
0.6
0.51
1.1
0.47
0.36
1.2
0.78
Chromium
270
34
37
470
34
290
33
28
440
8.1
300
34
24
410
19
17
600
40
33
380
34
40
500
38
35
210
33
30
430
99
Copper
29
18
21
33
18
33
17
16
34
2.3
31
18
17
23
12
13
34
19
17
32
18
18
34
18
17
23
16
16
23
12
Mercury
0.42
<0.1
<0.1
0.42
0.14
0.39
0.16
<0.1
0.49
<0.1
0.52
0.10
<0.1
0.38
<0.1
<0.1
0.62
0.13
<0.1
0.58
<0.1
<0.1
0.63
0.12
<0.1
0.34
0.11
<0.1
0.51
0.11
Nickel)
23
16
18
18
12
24
14
13
27
U
24
15
12
27
13
14
28
16
15
26
15
16
26
16
14
18
14
14
28
19
Lead
140
15
9.8
190
24
190
28
8.2
180
2.1
110
16
5.9
340
13
7.7
180
22
7.9
180
9.6
8.9
120
18
8.0
97
18
6.9
290
170
Selenium
2.8
2.8
2.6
2.6
2.7
2.7
2.1
2.6
2.5
0.47
3.6
2.9
3.1
2.1
0.86
1.5
2.6
1.9
<0.1
<0.1
<0.1
1.7
5.1
2.6
2.6
<0.1
2.0
2.7
1.5
1.8
Zinc
140
75
86
140
87
150
80
65
160
16
160
82
69
110
46
45
160
90
70
160
76
78
170
81
69
120
75
64
160
85
129
-------
TABLE D-l (CONTINUED). RESULTS OF METALS ANALYSES IN WHITE LAKE SEDIMENT, OCTOBER 2000. (MG/KG DRY WT)
Sample
WL-1 P
WL-2P
WL-3P
WL-4P
WL-5P
WL-6P
WL-7P
WL-8P
WL-9P
WL-1 OP
WL-11 P
WL-1 2 P
WL-1 3 P
WL-1 4 P
WL-1 5 P
WL-1 6 P
WL-1 7 P
WL-1 8 P
WL-1 9 P
WL-20 P
WL-21P
Arsenic
(mg/kg)
6.3
7.5
5.5
1.4
6.2
8.4
7.6
8.8
7.9
7.0
6.3
5.9
6.3
6.3
6.0
5.8
5.4
5.3
5.7
6.2
6.5
Barium
(mg/kg)
140
150
120
12
130
130
120
130
170
120
*
*
*
*
*
*
*
*
*
*
*
Cadmium
(mg/kg)
0.85
0.85
0.73
<0.1
1.1
1.0
0.99
0.93
0.87
0.91
0.96
1.03
0.96
1.10
0.75
0.84
0.64
0.51
0.42
0.61
1.00
Chromium
(mg/kg)
270
300
190
18
400
360
390
380
420
270
310
510
250
480
250
190
50
29
39
28
450
Copper
(mg/kg)
30
34
29
2.2
31
28
37
27
34
31
32
30
32
31
28
27
30
32
31
28
31
Mercury
(mg/kg)
0.20
0.20
0.16
<0.1
0.27
0.25
0.29
0.25
0.30
0.34
0.32
0.28
0.27
0.25
0.26
0.27
0.05
0.05
0.05
0.05
0.24
Nickel
mg/kg)
17
18
16
1.6
19
18
25
20
23
19
18
17
17
17
17
18
19
20
21
19
18
Lead
(mg/kg)
70
76
54
8.3
89
73
86
75
74
75
78
70
67
72
71
75
34
22
26
21
65
Selenium
(mg/kg)
<0.1
<0.1
<0.1
<0.1
2.9
3.0
3.6
3.7
3.0
<0.1
*
*
*
*
*
*
*
*
*
*
*
Zinc
(mg/kg)
120
120
100
33
120
120
130
120
130
120
116
118
108
95
101
105
115
125
131
124
132
PONAR analyzed for target list metals. Barium and selenium not analyzed.
130
-------
TABLE D-2. RESULTS OF QUALITY CONTROL ANALYSES FOR METALS IN WHITE LAKE
SEDIMENT, OCTOBER 2000.
WL-1 Top
Analyte
Arsenic
Barium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Zinc
Sample
Concentration
(mg/ml)
9.08
133
1.339
267
29.0
135
0.419
23.1
2.80
140
MSSpk
Added
(mg/ml)
798
319
319
319
319
319
0.813
319
798
319
MSDSpk
Added
(mg/ml)
768
307
307
307
307
307
0.844
307
768
307
MS Results
(mg/ml)
728.3
462.9
365.4
650.2
368.5
495.5
1.159
359.7
677.8
475.8
MSD Results
(mg/ml)
691.8
451.6
300.3
547.7
353.2
421.8
1.194
338.7
644.3
459.7
MS
%Rec
90
103
114
120
106
113
91
105
85
105
MSD
%Rec
89
104
97
91
106
93
92
103
84
104
RPD
1.1
0.97
16
27*
0
19
1.1
1.9
1.2
0.96
QC
RPD
20
20
20
20
20
20
23
20
20
20
QC
%REC
75-125
75-125
75-125
75-125
75-125
75-125
65-131
75-125
75-125
75-125
*No qualificarion of data is necessary
WL-7 Mid
Analyte
Arsenic
Barium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Zinc
WL-5P
Analyte
Arsenic
Barium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Zinc
Sample
Concentration
(mg/ml)
6.48
113
0.648
40.3
18.9
22.3
0.1338
15.5
1.91
89.8
Sample
Concentration
(mg/ml)
6.24
133.7
1.11
401.8
30.9
88.7
0.268
19.0
2.91
125
MSSpk
Added
(mg/ml)
522
209
209
209
209
209
0.667
209
522
209
MSSpk
Added
(mg/ml)
934
373
373
373
373
373
0.960
373
934
373
MSDSpk
Added
(mg/ml)
637
255
255
255
255
255
0.667
255
637
255
MSDSpk
Added
(mg/ml)
952
381
381
381
381
381
0.942
381
952
381
MS Results
(mg/ml)
431.1
303.8
186.9
218.4
219.1
206.5
0.8019
214.0
406.1
282.8
MS Results
(mg/ml)
863.8
526.9
380.0
769.9
419.6
465.8
1.28
400.0
796.4
523.1
MSD Results
(mg/ml)
523.0
351.6
238.5
270.7
270.7
260.4
0.7809
265.0
491.0
345.2
MSD Results
(mg/ml)
825.2
538.5
363.0
737.0
406.9
441.0
1.24
414.4
763.9
529.8
MS
%Rec
81
92
89
85
96
88
100
95
77
92
MS
%Rec
92
105
101
99
104
101
105
102
85
107
MSD
%Rec
81
94
93
90
99
93
97
98
77
100
MSD
%Rec
86
106
95
88
99
93
103
104
80
106
RPD
0
2.2
4.4
5.7
3.1
5.5
3.0
3.1
0
8.3
RPD
6.7
0.95
6.1
12
4.9
8.2
1.9
1.9
6.1
0.94
QC
RPD
20
20
20
20
20
20
23
20
20
20
QC
RPD
20
20
20
20
20
20
23
20
20
20
QC
%REC
75-125
75-125
75-125
75-125
75-125
75-125
65-131
75-125
75-125
75-125
QC
%REC
75-125
75-125
75-125
75-125
75-125
75-125
65-131
75-125
75-125
75-125
131
-------
TABLE D-3. RESULTS OF STANDARD REFERENCE MATERIAL ANALYSES FOR METALS
(RESULTS IN MG/KG EXCEPT WHERE NOTED).
Sample ID As Hg Cd Cr Cu Pb Ni Zn
ERA-1 190 1.8 120 180 90 72 71 200
% RSD 95% 90% 86% 95% 82% 80% 89% 89%
ERA-2 160 1.8 110 150 76 58 60 170
% RSD 80% 90% 79% 79% 69% 64% 75% 76%
ERA-3 200 1.6 120 180 89 72 70 200
%RSD 100% 80% 86% 95% 81% 80% 88% 89%
132
-------
Appendix E. Summary Of Chemical Measurements For The Toxicity
Test With Sediments From White Lake, October 2000.
133
-------
TABLE E-l. SUMMARY OF INITIAL AND FINAL CHEMICAL MEASUREMENTS FOR
HYALELLAAZTECA IN WHITE LAKE SEDIMENTS
Sample
WL-1
WL-2
WL-3
WL-4
WL-5
WL-6
WL-7
WL-8
WL-9
Parameter
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH^)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
Day
0
8.06
550
160
160
0.3
8.06
560
180
150
0.6
8.05
510
160
140
0.8
8.11
570
170
140
0.4
8.04
610
160
140
0.3
8.08
660
160
140
0.3
8.10
660
160
150
0.6
8.10
660
170
140
0.2
8.13
660
150
140
1.3
10
8.13
530
160
130
<0.1
8.46
488
160
120
<0.1
8.68
499
140
120
<0.1
8.45
494
170
120
<0.1
8.40
520
160
120
<0.1
8.21
514
150
120
<0.1
8.36
530
170
130
<0.1
8.55
510
150
120
<0.1
8.85
530
170
130
<0.1
Difference
(%)
1
4
0
19
#VALUE!
5
13
11
20
#VALUE!
8
2
13
14
#VALUE!
4
13
0
14
29900
4
15
0
14
39900
2
22
6
14
#VALUE!
3
20
6
13
#VALUE!
6
23
12
7
#VALUE!
9
20
13
7
#VALUE!
134
-------
Table E-l (continued). Summary of Initial and Final Chemical Measurements for
Hyalella azteca in White Lake Sediments
Sample
WL-10
WL-11
WL-12
WL-13
WL-14
WL-15
WL-16
WL-17
WL-18
Parameter
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
Day
650
8.02
660
170
140
0.6
8.06
650
160
140
0.3
8.11
650
180
150
0.4
8.11
650
160
140
0.3
8.09
610
160
150
0.2
7.98
480
160
140
1.9
7.97
480
190
140
3.0
7.97
540
180
150
4.5
8.00
430
160
130
2.1
170
10
8.27
499
160
130
0.1
7.97
477
160
120
0.2
8.27
520
160
130
<0.1
8.96
520
150
130
<0.1
8.64
520
160
140
<0.1
8.87
560
210
160
0.2
8.05
520
160
130
<0.1
8.27
525
180
130
0.1
8.66
540
190
140
0.1
Difference
(%)
3
24
6
7
77
1
27
0
14
47
2
20
11
13
#VALUE!
10
20
6
7
#VALUE!
7
99
0
7
#VALUE!
11
17
31
14
89
1
8
16
7
176
4
3
0
13
97
8
26
19
8
93
135
-------
Table E-l (continued). Summary of Initial and Final Chemical Measurements for
Hyalella azteca in White Lake Sediments
Sample
WL-19
WL-20
WL-21
Parameter
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
Day
0
8.05
420
160
130
1.6
7.98
480
170
150
2.3
8.10
490
160
140
0.6
140
10
9.16
530
190
140
<0.1
8.97
552
170
140
<0.1
8.50
541
180
130
0.15
Difference
(%)
14
26
19
8
#VALUE!
12
15
0
7
#VALUE!
5
10
13
7
75
136
-------
Table E-2. Summary Of Daily Temperature And Dissolved Oxygen Measurements For Hyallela azteca In The Solid Phase Toxicity Tests For
White Lake Sediments
Sample:
WL-1
Day
0
Temp
°C
22.2
DO
%
99.80
1
Temp
°C
22.7
DO
%
86.30
2
Temp
°C
22.0
DO
%
73.50
3
Temp
°C
22.5
DO
%
79.40
4
Temp
°C
22.4
DO
%
64.10
5
Temp
°C
22.4
DO
%
72.40
6
Temp
°C
22.8
DO
%
69.30
7
Temp
°C
22.4
DO
%
62.40
8
Temp
°C
22.7
DO
%
61.20
9
Temp
°C
22.1
DO
%
65.30
10
Temp
°C
22.4
DO
%
43.50
Sample:
WL-2
Day
0
Temp
°C
22.4
DO
%
99.70
1
Temp
°C
22.4
DO
%
88.60
2
Temp
°C
22.5
DO
%
72.50
3
Temp
°C
22.5
DO
%
76.90
4
Temp
°C
22.6
DO
%
66.10
5
Temp
°C
22.6
DO
%
75.70
6
Temp
°C
22.7
DO
%
62.70
7
Temp
°C
22.7
DO
%
63.10
8
Temp
°C
22.9
DO
%
53.40
9
Temp
°C
22.9
DO
%
65.50
10
Temp
°C
22.8
DO
%
47.40
Sample:
WL-3
Day
0
Temp
°C
22.2
DO
%
96.70
1
Temp
°C
22.2
DO
%
85.70
2
Temp
°C
111
DO
%
77.00
3
Temp
°C
22.6
DO
%
76.70
4
Temp
°C
22.5
DO
%
60.80
5
Temp
°C
22.6
DO
%
68.80
6
Temp
°C
22.6
DO
%
51.30
7
Temp
°C
22.7
DO
%
64.50
8
Temp
°C
22.9
DO
%
50.10
9
Temp
°C
22.9
DO
%
59.20
10
Temp
°C
22.6
DO
%
47.50
Sample:
WL-4
Day
0
Temp
°C
22.3
DO
%
99.30
1
Temp
°C
22.6
DO
%
83.90
2
Temp
°C
22.4
DO
%
71.80
3
Temp
°C
22.8
DO
%
71.30
4
Temp
°C
22.4
DO
%
63.00
5
Temp
°C
22.0
DO
%
70.40
6
Temp
°C
22.1
DO
%
56.50
7
Temp
°C
22.8
DO
%
68.50
8
Temp
°C
111
DO
%
46.60
9
Temp
°C
22.5
DO
%
48.10
10
Temp
°C
22.4
DO
%
45.50
Sample:
WL-5
Day
0
Temp
°C
22.1
DO
%
96.20
1
Temp
°C
22.3
DO
%
85.00
2
Temp
°C
22.6
DO
%
61.30
3
Temp
°C
22.6
DO
%
74.40
4
Temp
°C
22.6
DO
%
62.10
5
Temp
°C
22.3
DO
%
71.60
6
Temp
°C
22.4
DO
%
64.30
7
Temp
°C
22.6
DO
%
59.90
8
Temp
°C
22.7
DO
%
55.60
9
Temp
°C
22.8
DO
%
64.00
10
Temp
°C
22.6
DO
%
51.60
137
-------
Table E-2 (Cont). Summary of Daily Temperature and Dissolved Oxygen Measurements for Hyallela azteca in the Solid Phase Toxicity Tests for
White Lake Sediments
Sample:
WL-6
Day
0
Temp
°C
22.8
DO
%
98.50
1
Temp
°C
22.1
DO
%
90.30
2
Temp
°C
22.5
DO
%
79.50
3
Temp
°C
22.3
DO
%
80.40
4
Temp
°C
22.5
DO
%
62.50
5
Temp
°C
22.5
DO
%
71.70
6
Temp
°C
22.1
DO
%
76.10
7
Temp
°C
22.3
DO
%
70.30
8
Temp
°C
22.8
DO
%
59.60
9
Temp
°C
22.8
DO
%
63.50
10
Temp
°C
22.5
DO
%
44.20
Sample:
WL-7
Day
0
Temp
°C
22.8
DO
%
82.60
1
Temp
°C
22.9
DO
%
76.60
2
Temp
°C
22.3
DO
%
67.80
3
Temp
°C
22.3
DO
%
70.80
4
Temp
°C
22.9
DO
%
62.90
5
Temp
°C
22.0
DO
%
72.30
6
Temp
°C
22.2
DO
%
61.70
7
Temp
°C
22.5
DO
%
63.30
8
Temp
°C
22.5
DO
%
52.50
9
Temp
°C
22.0
DO
%
60.90
10
Temp
°C
22.2
DO
%
48.30
Sample:
WL-8
Day
0
Temp
°C
22.8
DO
%
93.00
1
Temp
°C
22.1
DO
%
84.70
2
Temp
°C
22.3
DO
%
75.90
3
Temp
°C
22.5
DO
%
76.60
4
Temp
°C
22.2
DO
%
76.20
5
Temp
°C
22.0
DO
%
77.20
6
Temp
°C
22.3
DO
%
64.60
7
Temp
°C
22.5
DO
%
69.40
8
Temp
°C
22.8
DO
%
57.30
9
Temp
°C
22.1
DO
%
61.00
10
Temp
°C
22.3
DO
%
53.90
Sample:
WL-9
Day
0
Temp
°C
22.9
DO
%
93.70
1
Temp
°C
22.2
DO
%
88.10
2
Temp
°C
22.4
DO
%
80.30
3
Temp
°C
22.4
DO
%
77.50
4
Temp
°C
22.3
DO
%
66.60
5
Temp
°C
22.9
DO
%
73.30
6
Temp
°C
22.2
DO
%
57.90
7
Temp
°C
22.6
DO
%
63.50
8
Temp
°C
22.6
DO
%
59.60
9
Temp
°C
22.2
DO
%
65.80
10
Temp
°C
22.3
DO
%
53.20
Sample:
WL-10
Day
0
Temp
°C
22.7
DO
%
94.20
1
Temp
°C
22.0
DO
%
87.90
2
Temp
°C
22.2
DO
%
75.80
3
Temp
°C
22.3
DO
%
79.60
4
Temp
°C
22.1
DO
%
70.20
5
Temp
°C
22.0
DO
%
76.20
6
Temp
°C
22.2
DO
%
51.80
7
Temp
°C
22.3
DO
%
74.70
8
Temp
°C
22.6
DO
%
60.10
9
Temp
°C
22.0
DO
%
67.50
10
Temp
°C
22.2
DO
%
54.20
138
-------
Table E-2 (Cont). Summary of Daily Temperature and Dissolved Oxygen Measurements for Hyallela azteca in the Solid Phase Toxicity Tests
for White Lake Sediments
Sample:
WL-11
Day
0
Temp
°C
22.1
DO
%
98.40
1
Temp
°C
22.1
DO
%
85.50
2
Temp
°C
22.2
DO
%
56.90
3
Temp
°C
22.0
DO
%
76.20
4
Temp
°C
22.8
DO
%
69.30
5
Temp
°C
22.3
DO
%
80.00
6
Temp
°C
22.1
DO
%
82.30
7
Temp
°C
22.0
DO
%
69.70
8
Temp
°C
22.2
DO
%
66.40
9
Temp
°C
22.2
DO
%
80.10
10
Temp
°C
22.0
DO
%
49.70
Sample:
WL-12
Day
0
Temp
°C
22.1
DO
%
96.90
1
Temp
°C
22.4
DO
%
85.60
2
Temp
°C
22.1
DO
%
62.00
3
Temp
°C
22.3
DO
%
77.10
4
Temp
°C
22.0
DO
%
65.70
5
Temp
°C
22.3
DO
%
79.40
6
Temp
°C
22.1
DO
%
84.90
7
Temp
°C
22.3
DO
%
70.60
8
Temp
°C
22.8
DO
%
81.50
9
Temp
°C
111
DO
%
62.50
10
Temp
°C
22.7
DO
%
58.10
Sample:
WL-13
Day
0
Temp
°C
22.1
DO
%
95.70
1
Temp
°C
22.1
DO
%
92.30
2
Temp
°C
23.2
DO
%
70.40
3
Temp
°C
22.8
DO
%
85.40
4
Temp
°C
22.3
DO
%
74.60
5
Temp
°C
23.2
DO
%
84.40
6
Temp
°C
23.0
DO
%
83.50
7
Temp
°C
22.7
DO
%
83.10
8
Temp
°C
22.2
DO
%
73.60
9
Temp
°C
22.9
DO
%
72.70
10
Temp
°C
22.5
DO
%
61.80
Sample:
WL-14
Day
0
Temp
°C
22.8
DO
%
98.30
1
Temp
°C
22.3
DO
%
81.70
2
Temp
°C
22.5
DO
%
74.50
3
Temp
°C
22.5
DO
%
74.40
4
Temp
°C
22.4
DO
%
65.50
5
Temp
°C
22.2
DO
%
70.50
6
Temp
°C
22.3
DO
%
59.60
7
Temp
°C
22.3
DO
%
59.90
8
Temp
°C
22.6
DO
%
63.80
9
Temp
°C
22.4
DO
%
61.40
10
Temp
°C
22.4
DO
%
52.80
Sample:
WL-15
Day
0
Temp
°C
22.5
DO
%
91.20
1
Temp
°C
22.8
DO
%
86.30
2
Temp
°C
22.0
DO
%
75.80
3
Temp
°C
22.9
DO
%
75.90
4
Temp
°C
22.1
DO
%
69.40
5
Temp
°C
22.3
DO
%
75.00
6
Temp
°C
22.3
DO
%
58.90
7
Temp
°C
22.5
DO
%
69.00
8
Temp
°C
22.6
DO
%
63.60
9
Temp
°C
22.3
DO
%
70.60
10
Temp
°C
22.4
DO
%
49.70
139
-------
Table E-2 (Cont). Summary of Daily Temperature and Dissolved Oxygen Measurements for Hyallela azteca in the Solid Phase Toxicity Tests
for White Lake Sediments
Sample:
WL-16
Day
0
Temp
°C
20.8
DO
%
86.10
1
Temp
°C
20.8
DO
%
79.00
2
Temp
°C
22.2
DO
%
66.30
3
Temp
°C
22.9
DO
%
72.60
4
Temp
°C
22.3
DO
%
68.10
5
Temp
°C
22.2
DO
%
76.00
6
Temp
°C
22.0
DO
%
86.00
7
Temp
°C
22.5
DO
%
78.30
8
Temp
°C
22.6
DO
%
79.70
9
Temp
°C
22.0
DO
%
65.30
10
Temp
°C
22.2
DO
%
61.70
Sample:
WL-17
Day
0
Temp
°C
22.1
DO
%
84.70
1
Temp
°C
22.2
DO
%
78.20
2
Temp
°C
22.4
DO
%
62.80
3
Temp
°C
22.2
DO
%
72.60
4
Temp
°C
22.4
DO
%
72.70
5
Temp
°C
22.5
DO
%
80.00
6
Temp
°C
22.9
DO
%
73.90
7
Temp
°C
22.9
DO
%
83.40
8
Temp
°C
22.2
DO
%
68.90
9
Temp
°C
22.2
DO
%
78.10
10
Temp
°C
22.9
DO
%
62.90
Sample:
WL-18
Day
0
Temp
°C
22.2
DO
%
88.30
1
Temp
°C
22.3
DO
%
77.10
2
Temp
°C
22.5
DO
%
70.70
3
Temp
°C
22.4
DO
%
68.50
4
Temp
°C
22.3
DO
%
62.80
5
Temp
°C
22.2
DO
%
73.00
6
Temp
°C
22.3
DO
%
65.40
7
Temp
°C
22.4
DO
%
71.40
8
Temp
°C
22.7
DO
%
69.00
9
Temp
°C
22.1
DO
%
65.50
10
Temp
°C
22.2
DO
%
52.00
Sample:
WL-19
Day
0
Temp
°C
20.9
DO
%
96.60
1
Temp
°C
20.8
DO
%
84.70
2
Temp
°C
22.1
DO
%
64.10
3
Temp
°C
22.8
DO
%
74.00
4
Temp
°C
22.1
DO
%
72.00
5
Temp
°C
22.2
DO
%
76.10
6
Temp
°C
22.9
DO
%
82.20
7
Temp
°C
22.8
DO
%
78.40
8
Temp
°C
22.8
DO
%
68.60
9
Temp
°C
22.0
DO
%
77.50
10
Temp
°C
22.2
DO
%
61.90
Sample:
WL-20
Day
0
Temp
°C
22.9
DO
%
89.00
1
Temp
°C
22.9
DO
%
83.70
2
Temp
°C
22.3
DO
%
70.20
3
Temp
°C
22.3
DO
%
70.70
4
Temp
°C
22.2
DO
%
59.40
5
Temp
°C
22.1
DO
%
72.30
6
Temp
°C
22.0
DO
%
68.90
7
Temp
°C
22.4
DO
%
60.20
8
Temp
°C
22.5
DO
%
57.90
9
Temp
°C
22.2
DO
%
60.90
10
Temp
°C
22.0
DO
%
47.50
140
-------
Table E-2 (Cont). Summary of Daily Temperature and Dissolved Oxygen Measurements for Hyallela azteca in the Solid Phase Toxicity Tests
for White Lake Sediments
Sample:
WL-21
Day
0
Temp
°C
22.7
DO
%
93.50
1
Temp
°C
22.8
DO
%
84.30
2
Temp
°C
22.8
DO
%
65.50
3
Temp
°C
22.9
DO
%
74.10
4
Temp
°C
23.2
DO
%
70.90
5
Temp
°C
23.1
DO
%
83.10
6
Temp
°C
22.8
DO
%
88.90
7
Temp
°C
22.6
DO
%
74.40
8
Temp
°C
22.1
DO
%
78.10
9
Temp
°C
22.5
DO
%
79.60
10
Temp
°C
22.2
DO
%
63.80
141
-------
TABLE E-3. SUMMARY OF INITIAL AND FINAL CHEMICAL MEASUREMENTS FOR
CHIRONOMUS TENTANS IN WHITE LAKE SEDIMENTS
Sam pie
W L-1
W L-2
W L-3
W L-4
W L-5
W L-6
W L-7
W L-8
W L-9
Param eter
pH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (m g/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (m g/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (m g/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
pH
Conductivity (umhos/cm)
Alkalinity (m g/l CaCO3)
Ha rd ness (mg/ICaCO3)
Ammonia (mg/l NH3.N)
pH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Ha rd ness (mg/ICaCO3)
A m m onia (m g/l N H 3)
Day
0
8.05
530
150
150
0.3
7.90
477
150
140
0.6
8.05
519
150
1 40
0.6
7.98
509
150
150
1 .2
8.05
477
150
140
0.2
7.95
514
1 40
150
0.3
8.01
474
140
150
0.3
7.98
517
1 40
150
0.1
8.01
489
150
150
0.7
10
8.07
482
170
130
0.2
8.30
562
180
130
<0.1
8.50
562
180
130
<0.1
8.03
583
170
130
0.4
8.06
530
170
130
0.2
8.03
530
170
130
0.2
8.05
583
170
130
0.2
8.1 8
530
180
1 30
<0.1
8.39
583
180
130
<0.1
Difference
(%)
0
9
1 3
13
50
5
18
20
7
#VALUE!
6
8
20
7
#VALU E!
1
15
13
13
63
6484
64
1 3
100
1 5
1
3
21
13
40
0
23
21
1 3
43
3
3
29
20
#VALUE!
5
19
20
1 3
#VALU E!
142
-------
TABLE E-3 (CONTINUED). SUMMARY OF INITIAL AND FINAL CHEMICAL
MEASUREMENTS FOR CHIRONOMUS TENTANS IN WHITE LAKE SEDIMENTS
Sample
WL-10
WL-11
WL-12
WL-13
WL-14
WL-15
WL-16
WL-17
WL-18
Parameter
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
Day
8
8.06
483
140
150
0.5
7.92
490
150
150
0.3
8.00
525
150
150
<0.1
8.06
522
150
140
0.3
8.10
525
150
140
0.2
7.94
525
140
150
1.7
7.88
530
160
140
2.5
7.81
519
170
150
4.7
8.11
512
160
140
2.3
10
8.02
552
180
130
0.3
7.86
530
180
120
0.3
8.15
594
180
130
<0.1
8.46
583
180
130
<0.1
8.04
595
180
130
<0.1
8.14
585
180
140
0.1
8.10
569
180
120
<0.1
8.03
563
190
130
<0.1
8.12
563
180
130
<0.1
Difference
(%)
0
14
29
13
34
1
8
20
20
17
2
13
20
13
#VALUE!
5
12
20
7
#VALUE!
1
98
20
7
#VALUE!
3
11
29
7
92
3
7
13
14
221
3
8
12
13
#VALUE!
0
10
13
7
#VALUE!
143
-------
TABLE E-3 (CONTINUED). SUMMARY OF INITIAL AND FINAL CHEMICAL
MEASUREMENTS FOR CHIRONOMUS TENTANS IN WHITE LAKE SEDIMENTS
Sample
WL-19
WL-20
WL-21
Parameter
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
PH
Conductivity (umhos/cm)
Alkalinity (mg/l CaCO3)
Hardness (mg/l CaCO3)
Ammonia (mg/l NH3)
Day
0
8.02
532
160
150
1.7
7.98
505
170
140
2.6
8.12
546
160
170
0.6
10
8.63
597
180
130
<0.1
8.26
528
180
130
0.1
7.97
630
180
140
0.3
Difference
(%)
8
12
13
13
#VALUE!
4
5
6
7
96
2
15
13
18
55
144
-------
TABLE E-4. SUMMARY OF DAILY TEMPERATURE AND DISSOLVED OXYGEN MEASUREMENTS FOR CHIRONOMUS TENTANS IN THE
SOLID PHASE TOXICITY TESTS FOR WHITE LAKE SEDIMENTS.
Sample:
WL-1
Day
0
Temp
°C
22.3
DO
%
91.90
1
Temp
°C
22.5
DO
%
82.20
2
Temp
°C
22.5
DO
%
42.70
3
Temp
°C
22.3
DO
%
62.10
4
Temp
°C
22.3
DO
%
52.70
5
Temp
°C
22.0
DO
%
59.30
6
Temp
°C
22.7
DO
%
49.10
7
Temp
°C
22.9
DO
%
62.60
8
Temp
°C
19.2
DO
%
55.20
9
Temp
°C
22.1
DO
%
50.90
10
Temp
°C
23.4
DO
%
31.70
Sample:
WL-2
Day
0
Temp
°C
22.4
DO
%
90.90
1
Temp
°C
22.2
DO
%
86.80
2
Temp
°C
22.5
DO
%
60.90
3
Temp
°C
22.7
DO
%
89.30
4
Temp
°C
22.1
DO
%
60.50
5
Temp
°C
22.1
DO
%
61.70
6
Temp
°C
22.6
DO
%
51.30
7
Temp
°C
23.4
DO
%
63.50
8
Temp
°C
18.8
DO
%
65.20
9
Temp
°C
22.2
DO
%
57.40
10
Temp
°C
23.1
DO
%
37.10
Sample:
WL-3
Day
0
Temp
°C
23.3
DO
%
88.90
1
Temp
°C
23.0
DO
%
84.40
2
Temp
°C
23.2
DO
%
65.40
3
Temp
°C
23.0
DO
%
82.20
4
Temp
°C
22.8
DO
%
63.40
5
Temp
°C
22.8
DO
%
73.90
6
Temp
°C
22.6
DO
%
40.70
7
Temp
°C
23.6
DO
%
61.20
8
Temp
°C
19.3
DO
%
51.60
9
Temp
°C
22.5
DO
%
43.60
10
Temp
°C
22.2
DO
%
41.80
Sample:
WL-4
Day
0
Temp
°C
22.5
DO
%
81.40
1
Temp
°C
22.6
DO
%
75.10
2
Temp
°C
22.7
DO
%
44.40
3
Temp
°C
22.7
DO
%
59.30
4
Temp
°C
22.6
DO
%
41.80
5
Temp
°C
22.3
DO
%
47.70
6
Temp
°C
22.7
DO
%
41.20
7
Temp
°C
22.7
DO
%
58.20
8
Temp
°C
22.7
DO
%
40.20
9
Temp
°C
22.5
DO
%
63.50
10
Temp
°C
22.7
DO
%
54.40
Sample:
WL5
Day
0
Temp
°C
22.4
DO
%
83.70
1
Temp
°C
22.6
DO
%
73.70
2
Temp
°C
22.7
DO
%
43.60
3
Temp
°C
22.7
DO
%
59.80
4
Temp
°C
22.7
DO
%
41.30
5
Temp
°C
22.6
DO
%
47.70
6
Temp
°C
22.6
DO
%
41.10
7
Temp
°C
22.5
DO
%
59.90
8
Temp
°C
22.8
DO
%
44.80
9
Temp
°C
22.9
DO
%
52.00
10
Temp
°C
22.8
DO
%
41.90
145
-------
TABLE E-4. (CONT). SUMMARY OF DAILY TEMPERATURE AND DISSOLVED OXYGEN MEASUREMENTS FOR CHIRONOMUS TENTANS
IN THE SOLID PHASE TOXICITY TESTS FOR WHITE LAKE SEDIMENTS.
Sample:
WI^6
Day
0
Temp
°C
22.5
DO
%
73.70
1
Temp
°C
22.9
DO
%
59.60
2
Temp
°C
22.7
DO
%
53.00
3
Temp
°C
22.7
DO
%
55.30
4
Temp
°C
22.6
DO
%
41.00
5
Temp
°C
23.0
DO
%
60.00
6
Temp
°C
22.8
DO
%
44.90
7
Temp
°C
22.5
DO
%
40.30
8
Temp
°C
22.0
DO
%
40.20
9
Temp
°C
22.2
DO
%
47.10
10
Temp
°C
22.9
DO
%
47.80
Sample:
WI^7
Day
0
Temp
°C
22.9
DO
%
79.50
1
Temp
°C
22.2
DO
%
80.10
2
Temp
°C
22 3
DO
%
62.00
3
Temp
°C
22 2
DO
%
77.90
4
Temp
°C
22.5
DO
%
58.60
5
Temp
°C
22.6
DO
%
58.60
6
Temp
°C
22 4
DO
%
40.00
7
Temp
°C
22.3
DO
%
57.10
8
Temp
°C
19.3
DO
%
47.20
9
Temp
°C
22 1
DO
%
40.10
10
Temp
°C
22.6
DO
%
39.70
Sample:
WI^8
Day
0
Temp
°C
22.3
DO
%
75.80
1
Temp
°C
22.5
DO
%
71.60
2
Temp
°C
22.4
DO
%
48.80
3
Temp
°C
22.7
DO
%
70.20
4
Temp
°C
22.3
DO
%
40.00
5
Temp
°C
22.4
DO
%
43.10
6
Temp
°C
22.6
DO
%
52.90
7
Temp
°C
22.8
DO
%
48.60
8
Temp
°C
22.0
DO
%
44.20
9
Temp
°C
22.7
DO
%
61.20
10
Temp
°C
23.1
DO
%
40.80
Sample:
WI^9
Sample:
WL-10
0
Temp
°C
22.8
0
Temp
°C
22.0
DO
%
84.70
DO
%
80.00
1
Temp
°C
22.8
1
Temp
°C
22.1
DO
%
80.00
DO
%
71.80
2
Temp
°C
22.9
2
Temp
°C
22.6
DO
%
59.50
DO
%
53.60
3
Temp
°C
22.8
3
Temp
°C
22.4
DO
%
74.30
DO
%
63.10
4
Temp
°C
22.6
4
Temp
°C
22.4
DO
%
44.50
DO
%
44.30
Da
5
Temp
°C
22.8
Da
5
Temp
°C
22.3
y
DO
%
53.10
y
DO
%
43.50
6
Temp
°C
22.6
6
Temp
°C
22.5
DO
%
50.70
DO
%
52.20
7
Temp
°C
23.0
7
Temp
°C
22.7
DO
%
61.60
DO
%
44.80
8
Temp
°C
22 2
8
Temp
°C
22.3
DO
%
40.20
DO
%
39.60
9
Temp
°C
22.2
9
Temp
°C
22.3
DO
%
52.10
DO
%
43.70
1C
Temp
°C
23.2
1C
Temp
°C
22.8
DO
%
51.00
DO
%
41.40
146
-------
TABLE E-4. (CONT). SUMMARY OF DAILY TEMPERATURE AND DISSOLVED OXYGEN MEASUREMENTS FOR CHIRONOMUS TENTANS
IN THE SOLID PHASE TOXICITY TESTS FOR WHITE LAKE SEDIMENTS.
Sample:
WL-11
Day
0
Temp
°C
22.0
DO
mg/1
81.40
1
Temp
°C
22.2
DO
mg/1
77.20
2
Temp
°C
22.0
DO
mg/1
57.80
3
Temp
°C
22.3
DO
mg/1
68.20
4
Temp
°C
22.4
DO
mg/1
49.00
5
Temp
°C
22.8
DO
mg/1
42.40
6
Temp
°C
22.7
DO
mg/1
59.10
7
Temp
°C
22.6
DO
mg/1
53.10
8
Temp
°C
22.1
DO
mg/1
51.50
9
Temp
°C
22.3
DO
mg/1
65.70
10
Temp
°C
23.1
DO
mg/1
50.10
Sample:
WL-12
Day
0
Temp
°C
22.8
DO
mg/1
86.90
1
Temp
°C
22.7
DO
mg/1
84.40
2
Temp
°C
22.7
DO
mg/1
60.20
3
Temp
°C
22.9
DO
mg/1
62.80
4
Temp
°C
22.5
DO
mg/1
53.90
5
Temp
°C
23.0
DO
mg/1
60.60
6
Temp
°C
22.8
DO
mg/1
70.10
7
Temp
°C
23.1
DO
mg/1
55.90
8
Temp
°C
22.3
DO
mg/1
43.50
9
Temp
°C
21.9
DO
mg/1
59.80
10
Temp
°C
23.4
DO
mg/1
40.50
Sample:
WL-13
Day
0
Temp
°C
22.7
DO
mg/1
85.10
1
Temp
°C
22.8
DO
mg/1
75.10
2
Temp
°C
22.6
DO
mg/1
56.10
3
Temp
°C
22.8
DO
mg/1
49.60
4
Temp
°C
22.5
DO
mg/1
53.10
5
Temp
°C
22.8
DO
mg/1
58.70
6
Temp
°C
22.8
DO
mg/1
55.80
7
Temp
°C
22.9
DO
mg/1
61.40
8
Temp
°C
22.1
DO
mg/1
53.80
9
Temp
°C
22.0
DO
mg/1
60.00
10
Temp
°C
23.3
DO
mg/1
48.00
Sample:
WL-14
Day
0
Temp
°C
22.2
DO
mg/1
78.80
1
Temp
°C
22.4
DO
mg/1
76.40
2
Temp
°C
22.6
DO
mg/1
55.00
3
Temp
°C
22.6
DO
mg/1
60.00
4
Temp
°C
22.5
DO
mg/1
43.70
5
Temp
°C
22.5
DO
mg/1
44.60
6
Temp
°C
22.6
DO
mg/1
47.90
7
Temp
°C
22.7
DO
mg/1
40.80
8
Temp
°C
22.6
DO
mg/1
49.70
9
Temp
°C
22.4
DO
mg/1
62.50
10
Temp
°C
23.0
DO
mg/1
41.30
Sample:
WL-15
Day
0
Temp
°C
22.4
DO
mg/1
81.60
1
Temp
°C
22.7
DO
mg/1
72.90
2
Temp
°C
22.7
DO
mg/1
56.00
3
Temp
°C
22.6
DO
mg/1
64.40
4
Temp
°C
22.3
DO
mg/1
47.90
5
Temp
°C
22.7
DO
mg/1
51.30
6
Temp
°C
22.7
DO
mg/1
44.10
7
Temp
°C
22.8
DO
mg/1
41.50
8
Temp
°C
22.3
DO
mg/1
46.60
9
Temp
°C
21.5
DO
mg/1
49.90
10
Temp
°C
23.2
DO
mg/1
41.80
147
-------
TABLE E-4. (CONT). SUMMARY OF DAILY TEMPERATURE AND DISSOLVED OXYGEN MEASUREMENTS FOR CHIRONOMUS TENTANS
IN THE SOLID PHASE TOXICITY TESTS FOR WHITE LAKE SEDIMENTS.
Sample :
WL-16
Day
0
Temp
°C
22.7
DO
mg/1
89.40
1
Temp
°C
22.5
DO
mg/1
77.10
2
Temp
°C
22.9
DO
mg/1
59.50
3
Temp
°C
22.6
DO
mg/1
72.70
4
Temp
°C
22.6
DO
mg/1
56.50
5
Temp
°C
23.0
DO
mg/1
53.90
6
Temp
°C
22.3
DO
mg/1
42.40
7
Temp
°C
22.9
DO
mg/1
57.40
8
Temp
°C
22 3
DO
mg/1
43.90
9
Temp
°C
22.0
DO
mg/1
51.70
10
Temp
°C
23.3
DO
mg/1
41.10
Sample:
WL-17
Day
0
Temp
°C
22.6
DO
mg/1
72.70
1
Temp
°C
22.3
DO
mg/1
68.80
2
Temp
°C
22 5
DO
mg/1
46.30
3
Temp
°C
22.6
DO
mg/1
59.80
4
Temp
°C
22.6
DO
mg/1
40.90
5
Temp
°C
22.7
DO
mg/1
51.30
6
Temp
°C
22.6
DO
mg/1
47.70
7
Temp
°C
22.6
DO
mg/1
51.70
8
Temp
°C
22.3
DO
mg/1
38.70
9
Temp
°C
21.9
DO
mg/1
55.80
10
Temp
°C
23.1
DO
mg/1
39.80
Sample:
WL-18
Day
0
Temp
°C
22.2
DO
mg/1
86.00
1
Temp
°C
22.3
DO
mg/1
75.50
2
Temp
°C
22 3
DO
mg/1
53.90
3
Temp
°C
22.3
DO
mg/1
57.50
4
Temp
°C
22 3
DO
mg/1
44.40
5
Temp
°C
22.7
DO
mg/1
59.70
6
Temp
°C
22.8
DO
mg/1
56.50
7
Temp
°C
22.8
DO
mg/1
55.60
8
Temp
°C
22.4
DO
mg/1
46.20
9
Temp
°C
22 2
DO
mg/1
51.30
10
Temp
°C
23.2
DO
mg/1
39.20
Sample:
WL-19
Sample :
WL-20
0
Temp
°C
22.2
0
Temp
°C
21.8
DO
mg/1
83.30
DO
mg/1
84.80
1
Temp
°C
22.5
1
Temp
°C
22.4
DO
mg/1
76.50
DO
mg/1
79.10
2
Temp
°C
22 5
2
Temp
°C
22.4
DO
mg/1
56.10
DO
mg/1
66.50
3
Temp
°C
22.6
3
Temp
°C
22.4
DO
mg/1
61.40
DO
mg/1
78.80
4
Temp
°C
22 5
4
Temp
°C
22.3
DO
mg/1
46.50
DO
mg/1
51.20
Da
5
Temp
°C
22.6
Da
5
Temp
°C
22.7
y
DO
mg/1
57.10
y
DO
mg/1
55.70
6
Temp
°C
22 4
6
Temp
°C
22.5
DO
mg/1
43.00
DO
mg/1
42.90
7
Temp
°C
22.6
7
Temp
°C
22.4
DO
mg/1
42.30
DO
mg/1
51.50
8
Temp
°C
21.9
8
Temp
°C
21.5
DO
mg/1
38.10
DO
mg/1
50.30
9
Temp
°C
21.9
9
Temp
°C
21.5
DO
mg/1
51.50
DO
mg/1
53.50
1C
Temp
°C
22.7
1C
Temp
°C
22.3
DO
mg/1
43.70
DO
mg/1
47.90
148
-------
TABLE E-4. (CONT). SUMMARY OF DAILY TEMPERATURE AND DISSOLVED OXYGEN MEASUREMENTS FOR CHIRONOMUS TENTANS
IN THE SOLID PHASE TOXICITY TESTS FOR WHITE LAKE SEDIMENTS.
Sample:
WL-21
Day
0
Temp
°C
22.0
DO
%
87.90
1
Temp
°C
22.1
DO
%
81.80
2
Temp
°C
22 2
DO
%
63.20
3
Temp
°C
22.9
DO
%
72.80
4
Temp
°C
22.2
DO
%
56.20
5
Temp
°C
22.6
DO
%
59.00
6
Temp
°C
22 3
DO
%
52.40
7
Temp
°C
22.2
DO
%
71.30
8
Temp
°C
19.1
DO
%
52.10
9
Temp
°C
22.9
DO
%
59.80
10
Temp
°C
22.7
DO
%
42.10
149
-------
Appendix F. Summary Of Benthic Macroinvertebrate Results For White
Lake, October 2000
150
-------
TABLE F-l. BENTHIC MACROINVERTEBRATE RESULTS FOR WHITE LAKE, OCTOBER 2000
Amphipoda
Gammarus
Hyallela
sopoda
Mollusca
Gastropoda
Amnicola
Physa
Valvata tricar inata
Viviparous
Bivalvia
Dreissena polymorpha
Pisidium
Sphaerium
Annelida
Tubificidae
Aulodrilus limnobius
Aulodrilus pigueti
llyodrilus templetoni
Limnodrilus hoffmeisteri
Limnodrilus claparianus
Quistrodrillus
Immature w/ hair
Immature w/o hair
Naididae
Haemonais waldvogeli
Hirundinea - Glossiphoniidae
Helobdella
Nematoda
Tricladida
Planaridae
Diptera
Chaoboridae
Chaoborus punctipennis
Ceratapogonidae
Chironomidae
flb/abesmyia
Chironomus
C/inotanypus
Coe/otanypus
Cryptochironomus
Dicrotendipes
Heteroirissocladius
Paraphaenocladius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironomus
Tanypus
Ephemeroptera
Caenis
Ephemera
Hexagenia
Isonychia
Tricoptera
Polycentroapodidae
Pseudostenophy/ax
Megaloptera
Safe
Odonata - Zygoptera
WL
1a
0
0
0
0
0
0
0
0
129
0
0
0
129
301
0
0
904
2325
0
0
818
0
1206
0
129
0
43.1
0
0
0
129
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1b
0
0
0
0
0
0
0
0
0
0
0
0
43.1
388
0
0
560
2627
0
0
517
0
1722
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1C
0
0
0
43.1
0
0
0
0
43.1
0
0
0
86.1
517
0
0
646
2885
0
0
172
0
947
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL
2,1
0
0
0
86.1
0
0
0
0
172
0
43.1
0
172
86.1
0
0
861
1421
0
0
43.1
0
2971
0
0
0
646
0
0
0
215
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
2b
43.1
43.1
0
0
0
0
0
0
86.1
0
0
0
258
258
0
0
1550
1981
0
0
0
0
2799
0
129
0
474
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
2c
0
0
0
43.1
0
0
0
0
43.1
0
0
0
0
301
0
0
646
3617
0
0
0
0
1722
0
258
0
818
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL
3a
0
0
0
172
0
0
0
0
86.1
0
86.1
43.1
215
646
0
0
172
1593
0
0
0
0
1679
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
3b
43.1
0
0
43.1
0
0
0
43.1
129
0
0
0
0
431
0
0
172
1120
0
0
43.1
0
1421
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
3c
0
0
0
0
0
0
0
0
172
0
86.1
86.1
0
603
0
0
43.1
1852
0
0
0
0
1593
0
0
0
129
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
0
0
0
WL
4,1
0
0
0
43.1
0
0
0
258
129
0
43.1
172
43.1
258
0
0
172
560
0
0
0
0
775
0
0
0
43.1
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
4b
43.1
0
0
43.1
0
0
0
86.1
129
0
86.1
215
431
904
258
0
1033
1292
43.1
0
0
0
1249
0
0
0
43.1
0
0
0
43.1
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
4c
86.1
0
0
0
0
0
0
43.1
86.1
0
129
43.1
43.1
215
172
0
646
388
0
0
0
0
258
0
0
0
0
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
WL
5a
0
0
0
172
0
0
0
86.1
43.1
0
43.1
0
86.1
990
0
0
1550
6760
0
0
990
0
517
0
86.1
0
215
0
0
0
0
0
0
0
0
0
172
0
0
0
0
0
0
0
0
0
0
5b
0
0
0
0
0
0
0
0
43.1
0
129
0
43.1
646
0
0
603
4521
0
0
689
0
431
0
172
0
431
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
5c
0
0
0
0
0
0
0
0
43.1
0
43.1
0
43.1
947
0
0
1335
6803
0
0
258
0
388
0
129
0
344
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
WL
6,1
43.1
0
0
86.1
0
0
0
0
0
0
129
0
0
603
0
0
689
2282
0
0
732
0
904
0
215
0
1722
0
0
0
129
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
6b
0
0
0
43.1
0
0
0
0
43.1
0
388
172
474
1120
0
0
2239
2454
0
0
646
0
1335
0
388
0
732
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
6c
0
0
0
43.1
0
0
0
0
0
0
172
0
0
646
0
0
1335
3100
0
0
560
43.1
990
0
86.1
0
1852
0
0
43.1
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
0
0
0
WL
7a
43.1
0
0
86.1
0
0
0
258
43.1
0
129
86.1
86.1
517
0
0
0
258
0
0
0
0
560
0
0
0
43.1
0
0
43.1
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
7b
43.1
0
0
0
0
0
0
0
0
0
129
0
0
344
0
0
0
1679
0
0
0
0
258
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7c
0
0
0
43.1
0
0
0
172
43.1
0
172
0
0
603
0
0
86.1
1765
0
0
0
0
172
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL
8,1
0
0
0
86.1
0
0
0
0
0
0
129
0
0
388
0
0
947
2153
0
0
1550
0
258
0
129
0
215
0
0
0
0
43.1
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
8b
0
0
0
0
0
0
0
0
0
0
86.1
43.1
0
301
0
0
1120
5641
0
0
1292
0
258
43.1
86.1
0
129
0
0
43.1
0
0
0
0
0
43.1
258
0
0
0
0
0
0
0
0
0
0
8c
0
0
0
258
0
0
0
0
172
0
43.1
0
86.1
301
0
0
904
3445
0
0
689
0
86.1
0
0
0
301
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
151
-------
TABLE F-l (CONTINUED). BENTHIC MACROINVERTEBRATE RESULTS FOR WHITE LAKE,
OCTOBER 2000
Amphipoda
Gammarus
Hyallela
Isopoda
Mollusca
Gastropoda
Amnico/a
Physa
Va/vata tricarinata
Viviparous
Bivalvia
Dre/ssena polymorpha
Pisidium
Sphaerium
Annelida
Tubificidae
Aulodrilus limnobius
Aulodrilus pigueti
llyodrilus temp/etoni
Limnodri/us hoffmeisteri
Limnodri/us c/aparianus
Quistrodrillus
Immature w/ hair
Immature w/o hair
Naididae
Haemonais waldvogeli
Hirundinea - Glossiphoniidae
Helobdella
Nematoda
Tricladida
Planaridae
Diptera
Chaoboridae
Chaoborus punctipennis
Ceratapogonidae
Chiron omidae
Ablabesmyia
Chironomus
Clinotanypus
Coe/otanypus
Cryptochironomus
Dicrotendipes
Heterotrissoc/adius
Paraphaenoc/adius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironomus
Tanypus
Ephemeroptera
Caenis
Ephemera
Hexagenia
Isonychia
Tricoptera
Polycentroapodidae
Pseudostenophylax
Megaloptera
S/a//s
Odonata - Zygoptera
WL
9a
43.1
0
0
86.1
0
0
0
43.1
86.1
0
215
0
43.1
560
172
0
990
2756
0
0
1938
0
129
0
0
0
86.1
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
9b
0
0
0
43.1
0
0
0
215
215
0
86.1
0
43.1
129
0
0
301
1033
0
0
3186
0
301
0
0
0
258
0
0
0
0
0
0
0
0
0
215
0
0
0
0
0
0
0
0
0
0
9c
43.1
0
0
0
0
0
0
0
0
0
86.1
0
86.1
215
129
0
2110
1292
0
0
6287
0
43.1
0
0
0
344
0
0
0
0
0
0
43.1
0
0
129
0
0
0
0
0
0
0
43.1
0
0
WL
10,1
0
0
0
0
0
0
0
86.1
0
0
0
86.1
172
775
0
0
344
1033
0
0
172
0
990
0
0
0
86.1
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
10b
86.1
0
0
0
0
0
0
0
129
0
0
0
258
603
86.1
0
861
2110
0
0
0
0
1335
0
0
0
258
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
10c
0
0
0
86.1
0
0
0
43.1
129
0
0
86.1
215
474
344
0
388
2067
43.1
0
344
0
904
0
0
0
0
0
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
WL
11a
43.1
0
0
0
0
0
0
0
0
0
0
43.1
344
603
0
172
1593
6545
0
0
1120
0
560
0
215
0
861
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
11b
0
0
0
0
0
0
0
0
0
0
129
43.1
172
560
0
43.1
1033
6890
0
0
1507
0
388
0
388
0
818
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
11c
0
0
0
43.1
0
0
0
0
0
0
86.1
0
560
1033
0
0
3100
9516
43.1
0
1206
0
301
0
301
0
1033
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
WL
12a
0
0
0
129
43.1
0
0
0
0
0
43.1
0
86.1
129
0
0
603
1636
0
0
9387
0
129
0
43.1
0
43.1
0
0
0
0
0
0
0
0
0
215
0
0
0
0
0
0
0
0
0
0
12b
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
301
689
0
0
5641
0
172
0
0
0
344
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
12c
0
0
0
43.1
0
0
0
129
0
0
0
0
0
0
0
0
1033
1938
0
0
8311
0
86.1
43.1
86.1
0
129
0
0
0
0
0
0
0
0
0
129
0
0
0
0
0
0
0
0
0
0
WL
13a
43.1
0
0
129
0
0
0
0
0
0
86.1
0
0
301
0
0
1981
2325
0
0
215
0
129
0
43.1
0
86.1
0
0
0
0
0
0
0
0
0
215
0
0
0
0
0
0
0
0
0
0
13b
43.1
0
0
129
0
0
0
86.1
0
0
43.1
0
0
301
0
0
1636
2110
0
0
431
0
344
0
43.1
0
258
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
13c
43.1
0
0
129
0
0
0
0
0
0
86.1
0
0
603
0
0
1895
1895
0
0
1077
0
129
0
129
0
86.1
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
WL
14a
0
0
0
0
0
0
0
0
0
0
0
0
0
43.1
0
0
732
1722
0
0
8784
0
0
0
0
0
215
0
0
86.1
0
0
43.1
0
0
0
215
0
0
0
0
0
0
0
0
0
0
14b
172
0
0
86.1
0
0
0
172
0
0
0
0
43.1
258
0
0
775
4435
0
0
3660
0
0
43.1
129
0
215
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
14c
0
0
43.1
43.1
0
0
0
43.1
0
0
0
0
0
258
0
0
517
2153
0
0
4650
43.1
0
0
86.1
0
388
0
0
86.1
0
0
0
0
0
0
172
0
0
0
0
0
0
0
0
0
0
WL
15a
0
0
0
86.1
0
0
0
43.1
0
0
86.1
0
43.1
990
0
0
215
1292
0
0
172
0
0
86.1
172
0
258
0
0
43.1
0
0
0
0
0
0
301
0
0
0
0
0
0
0
0
0
0
15b
0
0
0
258
0
0
0
86.1
0
0
86.1
43.1
0
603
0
0
1163
2282
0
0
1421
0
0
0
43.1
0
0
0
43.1
43.1
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
15c
43.1
0
0
172
0
0
0
43.1
0
0
129
0
0
861
0
0
603
1981
0
0
258
0
0
43.1
129
0
818
0
86.1
129
0
0
0
0
0
0
172
0
0
0
0
0
0
0
0
0
0
WL
16,1
43.1
0
0
0
0
0
0
258
0
0
0
0
43.1
172
0
0
2067
1033
0
0
0
0
0
43.1
86.1
0
86.1
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
43.1
0
16b
43.1
0
0
86.1
0
0
0
474
0
0
0
0
0
258
0
0
560
3660
0
0
0
86.1
0
0
172
0
129
0
0
0
0
0
0
0
0
0
129
0
0
0
0
0
0
0
0
0
0
16c
0
0
0
43.1
0
0
0
0
0
0
0
0
0
86.1
0
0
43.1
1981
0
0
43.1
0
0
0
0
0
129
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
152
-------
TABLE F-l (CONTINUED). BENTHIC MACROINVERTEBRATE RESULTS FOR WHITE LAKE,
OCTOBER 2000
Amphipoda
Gammarus
Hyallela
Isopoda
Mollusca
Gastropoda
Amnicola
Physa
Valvata tricarinata
Viviparous
Bivalvia
Dreissena polymorpha
Pisidium
Sphaerium
Annelida
Tubificidae
Aulodrilus limnobius
Aulodrilus pigueti
llyodrilus templetoni
Limnodrilus hoffmeisteri
Limnodrilus claparianus
Quistrodrillus
Immature w/ hair
Immature w/o hair
Naididae
Haemonais waldvogeli
Hirundinea - Glossiphoniidae
Helobdella
Nematoda
Tricladida
Planaridae
Diptera
Chaoboridae
Chaoborus punctipennis
Ceratapogonidae
Chironomidae
Ablabesmyia
Chironomus
Clinotanypus
Coelotanypus
Cryptochironomus
Dicrotendipes
He tero trissocladius
Paraphaenocladius
Paratendipes
Phaenopsectra
Polypedilum
Procladius
Pseudochironomus
Tanypus
Ephemeroptera
Caenis
Ephemera
Hexagenia
Isonychia
Tricoptera
Polycentroapodidae
Pseudostenophylax
Megaloptera
Stalls
Odonata - Zygoptera
WL
17a
86.1
0
0
86.1
0
0
0
43.1
43.1
0
0
0
0
258
0
0
732
4177
0
0
0
0
0
0
0
0
0
0
0
215
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
17b
43.1
0
0
43.1
86.1
0
0
172
86.1
0
0
129
0
43.1
0
0
388
1852
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
17c
43.1
0
0
86.1
0
0
0
0
0
0
0
172
0
388
0
129
6115
86.1
0
0
0
0
0
0
0
0
43.1
0
0
215
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
0
0
WL
18a
43.1
0
0
43.1
0
0
43.1
172
0
0
0
0
0
0
0
0
344
1852
0
0
0
0
0
0
301
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
18b
43.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
215
1077
0
0
43.1
0
0
43.1
43.1
0
129
0
0
0
0
0
0
0
0
0
172
0
0
0
0
43.1
0
0
0
0
0
18c
43.1
0
0
0
0
0
0
86.1
0
0
0
0
0
0
0
0
129
990
0
0
0
0
0
0
215
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
43.1
0
0
0
0
0
WL
19a
43.1
0
0
86.1
0
0
0
0
0
0
0
0
0
86.1
0
0
474
2368
0
0
0
0
0
0
474
0
0
86.1
0
129
0
0
0
0
0
0
43.1
0
0
0
0
0
0
0
0
0
0
19b
86.1
0
0
86.1
0
0
0
0
0
0
0
0
0
129
0
0
215
1593
0
0
0
0
0
0
43.1
43.1
43.1
0
0
86.1
0
0
0
0
0
0
0
0
0
0
0
86.1
0
0
0
0
0
19c
0
0
0
0
0
0
0
0
0
0
0
0
0
86.1
0
0
301
1550
0
0
43.1
0
0
0
0
43.1
86.1
86.1
0
172
0
0
0
0
0
0
129
0
0
0
0
0
0
0
0
0
0
WL
203
5426
603
215
301
43.1
0
0
517
0
0
0
0
258
258
0
0
43.1
1163
0
43.1
0
1206
0
0
215
0
0
0
0
0
0
0
0
0
0
0
301
0
0
0
43.1
0
43.1
43.1
0
0
172
20b
258
0
0
0
0
0
0
0
0
0
0
0
0
215
0
0
301
2024
0
0
0
0
0
215
1033
0
86.1
0
0
129
0
0
0
0
43.1
0
344
0
0
43.1
0
301
0
0
0
0
0
20c
1765
86.1
86.1
129
0
43.1
0
86.1
0
0
0
0
0
0
0
0
301
1378
0
0
0
86.1
0
129
431
0
172
0
0
43.1
0
0
0
0
0
0
258
0
0
0
0
86.1
0
0
0
0
0
WL
21 a
43.1
0
0
129
0
0
0
0
43.1
0
258
43.1
431
1550
0
0
9645
mm
0
0
1378
0
517
0
172
0
301
0
0
43.1
0
0
0
0
0
0
172
0
0
0
0
0
0
0
0
0
0
21 b
215
0
0
129
0
0
0
86.1
215
0
301
172
258
2325
0
0
mm
mm
0
43.1
2971
0
1120
0
603
0
1593
0
0
0
0
0
0
0
0
0
344
0
0
0
0
0
0
0
0
0
0
21 c
43.1
0
0
0
0
0
0
43.1
172
0
301
0
474
2842
0
0
9301
mm
0
0
2454
0
1292
0
0
0
1033
0
0
0
0
0
0
0
43.1
0
431
0
0
0
0
0
0
0
0
0
0
WL
21a1
258
0
0
86.1
0
0
0
43.1
43.1
43.1
172
43.1
215
947
0
0
7622
3273
0
0
646
0
431
0
258
0
474
0
0
0
0
0
0
0
0
0
301
0
0
0
0
0
0
0
0
0
0
21 b1
215
0
0
0
0
0
0
0
43.1
0
172
0
215
1335
0
0
2497
2454
0
0
0
0
0
0
0
0
775
0
0
43.1
0
0
0
0
0
0
215
0
0
0
0
0
0
0
0
0
0
21c1
258
0
0
43.1
0
0
0
0
215
0
172
0
86.1
1249
0
0
4005
2928
0
0
344
0
1033
0
301
0
689
0
0
0
0
0
0
43.1
0
0
215
0
0
0
0
0
0
0
0
0
0
153
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