PRELIMINARY INVESTIGATION OF THE EXTENT OF
SEDIMENT CONTAMINATION IN MUSKEGON LAKE
BY
Dr. Richard Rediske
Dr. Cynthia Thomps on
R. B. Annis Water Resources Institute
Grand Valley State University
740 W. Shoreline Drive
Muskegon, MI 49441
Dr. Claire Schelske
Department of Fish and Aquatic Sciences
University of Florida
Gainesville, FL 32606
Dr. John Gabrosek
Department of Statistics
Grand Valley State University
1 Campus Drive
Allendale, MI 49401
Dr. TomNalepa
Great Lakes Environmental Research Laboratory
National Oceanic and Atmospheric Administration
2205 Commonwealth Boulevard
Ann Arbor, MI 48105
Dr. Graham Peas lee
Chemistry Department
Hope College
35 E. 12th Street
Holland, MI 49423
GREAT LAKES NATIONAL PROGRAM OFFICE # GL-97520701-01
U. S. Environmental Protection Agency
National Oceanic And Atmospheric Administration
PROJECT OFFICER:
Dr. Marc Tuchman
U. S. Environmental Protection Agency
Great Lakes National Program Office
77 West Jackson Boulevard
Chicago IL 60604-3 5 90
July 2002
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ACKNOWLEDGEMENTS
This work was supported by grant #985906-01 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
Principle Scientists
Dr. Richard Rediske GVSU Sediment Chemistry
Dr. John Gabrosek GVSU Statistical Methods
Dr. Cynthia Thompson GVSU Toxicology
Dr. Claire Schelske UofF Radiochemistry
Dr. Graham Peaslee Hope College Radiochemistry
Dr. Thomas Nalepa NOAA Benthic Macroinvertebrates
Project technical assistance was provided by the following individuals at GVSU and U of M:
Glenn Carter
Mike Sweik
Eric Andrews
Betty Doyle
Roxana Taylor
Ship support was provided by the crews of the following Research Vessels:
R/VMudpuppy (USEPA) J. Bohnam
The Gas Chromatograph/Mass Spectrometer used by GVSU for this project was partially
funded by a National Science Foundation Grant (DUE-9650183).
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TABLE OF CONTENTS
List Of Tables iii
List Of Figures v
Executive Summary 1
1.0 Introduction 2
1.1 Summary of Anthropogenic Activities In Muskegon Lake 3
1.2 Proj ect Obj ectives And Task Elements 6
1.3 Experimental Design 7
1.4 References 8
2.0 Sampling Locations 9
3.0 Methods 14
3.1 Sampling Methods 14
3.2 Chemical Analysis Methods For Sediment Analysis 15
3.3 Chemical Analysis Methods For Water Analysis 24
3.4 Sediment Toxicity 24
3.5 Benthic Macroinvertebrates 28
3.6 Radiometric Dating 28
3.7 References 29
4.0 Results And Discussions 30
4.1 Sediment Chemistry Results 30
4.2 Stratigraphy and Radiodating Results 64
4.3 Toxicity Testing Results 73
4.4 Benthic Macroinvertebrate Results 79
4.5 Sediment Quality Triad Assessment 94
4.6 Summary And Conclusions 100
4.7 References 101
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5.0 Recommendations 103
Appendices
Appendix A.
Appendix B.
Appendix C.
Appendix D.
Appendix E.
Appendix F.
..104
Quality Assurance Review of the Project Data 105
Results Physical Analyses On Muskegon Lake Sediments, October
1999
112
Organic Analyses On Muskegon Lake Sediments, October 1999 117
Results Of Metals Analyses For Muskegon Lake Sediments, October
1999 126
Summary Of Chemical Measurements For The Toxicity Test With
Sediments From Muskegon Lake, October 1999 132
Summary Of Benthic Macroinvertebrate Results For Muskegon Lake,
October 1999 143
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LIST OF TABLES
Table 2.1 Muskegon Lake Core Sampling Stations 11
Table 2.2 Muskegon Lake PONAR Sampling Stations 13
Table 2.3 Muskegon Lake Stratigraphy Core Sampling Stations 13
Table 3.1 Sample Containers, Preservatives, And Holding Times 15
Table 3.2.1 Analytical Methods And Detection Limits 16
Table 3.2.2 Organic Parameters And Detection Limits 22
Table 3.2.3 Data Quality Objectives For Surrogate Standards Control Limits For
Percent Recovery 23
Table 3.3.1 Analytical Methods And Detection Limits For Culture Water 24
Table 3.4.1 Test Conditions For Conducting A Ten Day Sediment Toxicity Test
With Hyalella azteca 26
Table 3.4.2 Recommended Test Conditions For Conducting A Ten-Day Sediment
Toxicity Test With Chironomus tentans 27
Table 4.1.1 Results Of Sediment Grain Size Fractions, TOC, And Percent Solids
For Muskegon Lake Core Samples, October 1999 32
Table 4.1.2 Results Of Sediment Grain Size Fractions, TOC, And Percent Solids
For Muskegon Lake PONAR Samples, October 1999 34
Table 4.1.3 Results Of Sediment Metals Analyses For Muskegon Lake Core
Samples (mg/kg Dry Weight), October 1999 35
Table 4.1.4 Results Of Sediment Metals Analyses For Muskegon Lake PONAR
Samples (mg/kg Dry Weight), October 1999 37
Table 4.1.5 Results Of Sediment PAH Analyses For Muskegon Lake Core and
PONAR Samples (mg/kg Dry Weight), October 1999 38
Table 4.1.6 Summary Of Ponar Sampling Locations In Muskegon Lake That
Exceed Consensus Based PEC Guidelines (MacDonald et al. 2000) 56
Table 4.2.1 Results of Stratigraphy and Radiodating Results For Core M-l S
Collected From Muskegon Lake, March 2000 65
Table 4.2.2 Results of Stratigraphy and Radiodating Results For Core M-2S
Collected From Muskegon Lake, March 2000 67
Table 4.2.3 Results of Stratigraphy and Radiodating Results For Core M-5S
Collected From Muskegon Lake, October 2000 70
Table 4.3.1.1 Summary Of Hyalella azteca Survival Data Obtained During The 10
Day Toxicity Test With Muskegon Lake Sediments 74
in
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Table 4.3.1.2 Summary Of Dunnett' s Test Analysi s Of Hyalella azteca Survival Data
Obtained During The 10 Day Toxicity Test With Muskegon Lake
Sediments 74
Table 4.3.2.1 Summary Of Chironomus tentans Survival Data Obtained During The
10 Day Toxicity Test With Muskegon Lake Sediments 75
Table 4.3.2.2 Summary Of Dunnett's Test Analysis Of Survival Data Chironomus
tentans Obtained During The 10 Day Toxicity Test With Muskegon
Lake Sediments 75
Table 4.3.2.3 Summary Of Chironomus tentans Dry Weight Data Obtained During
The 10 Day Toxicity Test With Muskegon Lake Sediments 76
Table 4.3.2.4 Summary of Dunnett's Test Analysis of Weight Data For Chironomus
tentans Obtained During The 10 Day Toxicity Test With Muskegon
Lake Sediments 78
Table 4.4.1.1 Benthic Macroinvertebrate Distribution In Muskegon Lake (#/m2),
October 1999. Mean Number Of Organisms And Standard Deviation
Reported For Each Station 80
Table 4.4.1.2 Mean Abundance (#/M2) And Relative Densities (%) Of Major
Taxonomic Groups In Muskegon Lake, October 1999 83
Table 4.4.2.1 Summary of Diversity And Trophic Status Metrics For The Benthic
Macroinvertebrates In Muskegon Lake, October 1999 85
Table 4.4.3.1 Summary Statistics For The Analysis Of Individual Benthic
Macroinvertebrate Samples From Muskegon Lake, October 1999 89
Table 4.4.3.2 Results Of ANOVA And SNK Evaluations Of Benthic
Macroinvertebrate Data For Muskegon Lake, October 1999 92
Table 4.5.1 Sediment Quality Assessment Matrix For Muskegon Lake Data,
October 1999. Assessment Matrix From Chapman (1992) 99
IV
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LIST OF FIGURES
Figure 1.1 Muskegon Lake 3
Figure 1.2 Areas Of Sediment Contamination Identified In Muskegon Lake 5
Figure 2.1 Muskegon Lake Sampling Stations 10
Figure 4.1.1 Total Chromium In Core Samples Collected From Western Muskegon
Lake, October 1999 40
Figure 4.1.2 Total Cadmium In Core Samples Collected From Western Muskegon
Lake, October 1999 41
Figure 4.1.3 Total Copper In Core Samples Collected From Western Muskegon
Lake, October 1999 42
Figure 4.1.4 Total Lead In Core Samples Collected From Western Muskegon Lake,
October 1999 43
Figure 4.1.5 Total PAH Compounds In Core Samples Collected From Western
Muskegon Lake, October 1999 44
Figure 4.1.6 Total Chromium In Core Samples Collected From Eastern Muskegon
Lake, October 1999 45
Figure 4.1.7 Total Cadmium In Core Samples Collected From Eastern Muskegon
Lake, October 1999 46
Figure 4.1.8 Total Copper In Core Samples Collected From Eastern Muskegon
Lake, October 1999 47
Figure 4.1.9 Total Lead In Core Samples Collected From Eastern Muskegon Lake,
October 1999 48
Figure 4.1.10 Total PAH Compounds In Core Samples Collected From Eastern
Muskegon Lake, October 1999 49
Figure 4.1.11 Total Cadmium In Core Samples Collected From Muskegon Lake,
October 1999 51
Figure 4.1.12 Total Chromium In Core Samples Collected From Muskegon Lake,
October 1999 52
Figure 4.1.13 Total Lead In Core Samples Collected From Muskegon Lake, October
1999 53
Figure 4.1.14 Total Copper In Core Samples Collected From Muskegon Lake,
October 1999 54
Figure 4.1.15 Total PAH Compounds In Core Samples Collected From Muskegon
Lake, October 1999 55
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Figure 4.1.16 Chromium, Copper, And Cadmium In Ponar Samples Collected From
Eastern Muskegon Lake, October 1999. Bold Values Exceed Probable
Effect Concentrations (PECs) 57
Figure 4.1.17 Lead, Mercury, and Total PAH Compounds In Ponar Samples
Collected From Eastern Muskegon Lake, October 1999. Bold Values
Exceed Probable Effect Concentrations (PECs) 58
Figure 4.1.18 Chromium, Copper, And Cadmium In Ponar Samples Collected From
Western Muskegon Lake, October 1999. Bold Values Exceed
Probable Effect Concentrations (PECs) 59
Figure 4.1.19 Lead, Mercury, and Total PAH Compounds In Ponar Samples
Collected From Western Muskegon Lake, October 999. Bold Values
Exceed Probable Effect Concentrations (PECs) 60
Figure 4.1.20 Total Arsenic, Cadmium, and Chromium in Ponar Samples Collected
from Muskegon Lake, October 1999. Patterns Denote Regions of
Muskegon Lake. Bold Lines Identify PEC Levels 61
Figure 4.1.21 Copper, Lead, and Mercury in Ponar Samples Collected from
Muskegon Lake, October 1999. Patterns Denote Regions of
Muskegon Lake. Bold Lines Identify PEC Levels 62
Figure 4.1.22 Total PAH Compounds in Ponar Samples Collected From Muskegon
Lake, October 1999. Bold Lines Identify PEC Levels 63
Figure 4.2.1 Depth and Concentration Profiles for Chromium and Lead At
Station M-l S, Muskegon Lake, March 2000. Sediment Dates
Calculated By Radiodating With Pb-210 66
Figure 4.2.2 Depth and Concentration Profiles for Chromium and Lead At
Station M-2S, Muskegon Lake, March 2000. Sediment Dates
Calculated By Radiodating With Pb-210 68
Figure 4.2.3 Depth and Concentration Profiles for Chromium and Lead at
Station M-3S, Muskegon Lake, October 2000. Sediment Dates
Calculated By Radiodating With Pb-210 71
Figure 4.4.1.1 General Distribution Of Benthic Macroinvertebrates In Muskegon
Lake, October 1999 84
Figure 4.4.2.1 Summary Of Trophic Indices For The Benthic Macroinvertebrates In
Muskegon Lake, October 1999 86
Figure 4.4.2.2 Summary Of Chironomid Detritivores And Predators For The Benthic
Macroinvertebrates In Muskegon Lake, October 1999 87
Figure 4.4.2.3 Summary Of Diversity And The J Index Values For The Benthic
Macroinvertebrates In Muskegon Lake, October 1999 87
VI
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Figure 4.4.3.1 Box Plot Of the Oligochaete Index Data For Muskegon Lake Benthic
Macroinvertebrate Stations (Box = 25%-75% Data Distribution),
October 1999 90
Figure 4.4.3.2 Box Plot Of The Total Number of Organisms For Muskegon Lake
Benthic Macroinvertebrate Stations (Box = 25%-75% Data
Distribution), October 1999 90
Figure 4.4.3.3 Box Plot Of the Oligochaete/Chironomid Ratio For Muskegon Lake
Benthic Macroinvertebrate Stations (Box = 25%-75% Data
Distribution), October 1999 91
Figure 4.4.3.4 Box Plot Of the Total Oligochaete Numbers For Muskegon Lake
Benthic Macroinvertebrate Stations (Box = 25%-75% Data
Distribution), October 1999 91
Figure 4.5.1. Sediment Quality Triad Diagrams For The Ruddiman Creek Area Of
Muskegon Lake 95
Figure 4.5.2. Sediment Quality Triad Diagrams For The Division Street Outfall Area
Of Muskegon Lake 96
Figure 4.5.3. Sediment Quality Triad Diagrams For The Former Foundry Complex
Area Of Muskegon Lake 97
Figure 4.5.4 Results Of A Cluster Analysis Performed On Principal Component
Scores For Sediment Quality Triad Measures For Muskegon Lake
Sediment 98
vn
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Executive Summary
A preliminary investigation of the nature and extent of sediment contamination in Muskegon
Lake was performed using Sediment Quality Triad methodology. Sediment chemistry, solid-
phase toxicity, and benthic macroinvertebrates were examined at 15 locations. In addition,
three core samples were evaluated using radiodating and stratigraphy to assess sediment
stability and contaminant deposition. High levels of cadmium, copper, chromium, lead, and
mercury were found in the Division Street Outfall area. These levels exceeded the Probable
Effect Concentrations (PECs) for current sediment quality guidelines. Most of the heavy
metals were found in the top 80 cm of the core samples. Deeper layers of contamination were
found only near the former Teledyne foundry and down stream from Ruddiman Creek. High
concentrations of PAH compounds were found at a lakeshore industrial area formerly
occupied by a manufactured gas facility, an iron foundry, commercial shipping docks, a rail
yard, and a coal storage facility. These levels also exceeded PEC guidelines. Sediment
toxicity was observed at two stations in the Division Street Outfall area and at the lakeshore
industrial site. These locations had the highest concentrations of metals and PAH compounds
respectively. Benthic macroinvertebrate communities throughout Muskegon Lake were found
to be indicative of organically enriched conditions. The locations in the Division Street
Outfall area were significantly different than reference sites with respect to fewer numbers and
a smaller population of detritivores.
Sediment Quality Triad diagrams were prepared and significant correlations were obtained
between chemistry and toxicity and chemistry and diversity (p < .01). Toxicity and diversity
also were positively correlated (p < .05). Based on the results of this investigation, the
Division Street Outfall and the location down gradient from the lakeshore industrial site are
priority areas for further investigation and potential remediation due to adverse ecological
effects, toxicity, and high contaminant levels.
Stratigraphy and radiodating analyses conducted on sediment cores provided important
information related to depositional history. Ruddiman Creek appears to have a significant
influence on the deposition of heavy metals in the southwestern part of Muskegon Lake. A
peak in metals deposition was found that corresponded to the 100+ year flood that occurred
in 1986. The historical deposition was considerably higher than current rates. The deep zone
off the Car Ferry Dock was not found to be an area that accumulates sediments. High
inventories of 210Pb were found near the bottom of this 80 cm core, indicating active mixing
and movement of sediments. The presence of elevated metals in the deeper strata plus the
high 210Pb inventories suggest that contaminated sediments are moved from the eastern part of
Muskegon Lake to this location where they are mixed and made available for resuspension by
the currents traveling along the old river channel. The core from the Division Street Outfall
showed relatively stable sediments in the top 20 cm followed by a stable zone of heavy
accumulation after 1960. Based on these results it is apparent that the removal of
contaminated sediments from Ruddiman Creek and the lagoon would reduce the loading of
heavy metals to western Muskegon Lake. The areas of high sediment contamination in the
eastern part of the lake also appear to be mixed and subject to transport.
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1.0 Introduction
Muskegon Lake, Michigan is a large drowned river mouth lake (4,150 acres) that is directly
connected to Lake Michigan by a navigation channel. It is part of the Muskegon River
watershed which has a drainage basin of 2,634 square miles. Muskegon 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 Muskegon River. Historically, significant anthropogenic
activity has impacted the water and sediment of the lake. Prior to 1973, industrial and
municipal wastes were directly discharged into the waters of Muskegon Lake. These
discharges included effluents from petrochemical, organic chemical, metal finishing, and
manufactured gas facilities. The International Joint Commission designated Muskegon Lake
as an Area of Concern (AOC) because of severe environmental impairments related to these
discharges. A map of Muskegon Lake is provided in Figure 1.1. In 1973, a state of the art
wastewater treatment facility was constructed and the direct discharge of waste effluents was
eliminated. While the water quality has improved considerably over the years, contaminated
sediments remain in the lake. In addition, diffuse sources of contamination continue to enter
the lake from tributaries, local runoff, and impacted groundwater plumes. Previous
investigations of Muskegon Lake have identified areas of sediment contamination and
depauperate benthic communities. High levels of lead (1400 mg/kg), chromium (1000
mg/kg), polycyclic aromatic hydrocarbon (PAH) compounds (10 mg/kg), and mercury (3.6
mg/kg) were found in sediment samples collected along the southern shoreline in 1982 (West
Michigan Shoreline Regional Development Commission 1982). The same investigation also
found high levels of PNAs (500 mg/kg) near an abandoned landfill located on the banks of the
Muskegon River.
A recent investigation (EPA 1995) in the Division Street Outfall area found high levels of lead
(700 mg/kg) and mercury (2 mg/kg) in several surface zone sediments (0-16 in). Higher
levels were detected in the deeper strata. This outfall collected stormwater from a number of
industrial facilities and was subject to historic discharges of untreated wastes. Since industrial
discharges in this area were eliminated in 1973, the presence of high levels of metals in the
zone of recent deposition suggests that the sediments at this location may be mobile and
subject to resuspension. In consideration that many of the areas of contamination may be
subject to the same physical phenomena, information related to sediment stability and mobility
will be central to the development of remediation and restoration plans for the lake.
Since the last major assessment of the lake was conducted in the early 1980s, it is important to
examine the current nature and extent of sediment contamination and the status of the health
of the benthic community. This project utilized a series of sediment sampling stations that
reflect deposition areas near historic industrial locations, wastewater treatment outfalls, and
contamination sites. In addition, a group of sampling locations near the Division Street outfall
were examined. 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 for the determination of areas that may require further delineation and the
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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.
4
: F* n o! i ?**'£
FIGURE 1.1 MUSKEGONLAKE
1.1 Summary Of Anthropogenic Activities In Muskegon Lake
The history of the Muskegon Lake and its watershed was described by Alexander (2000).
Approximately 11,000 years ago, the glacial activity that formed the Great Lakes also created
the Muskegon River watershed. Muskegon Lake was then formed as a drowned rivermouth
by drastic fluctuations in Lake Michigan water levels and the closing of the channel by wind
induced erosion of coastal sand dunes. During the 1700s, Native American tribes depended
on the watershed's natural resources for food and transportation. They named the river the
"Maskigon", which means river with marshes. In its natural state, the watershed was a
continuous system of dense riparian forests, sprawling wetlands and marshes, inland lakes, and
extensive riffle areas. The system was drastically changed in the 1800s when lumber barons
harvested the region's timber resources and left behind a legacy of barren riparian zones and
severe erosion. Saw mills were then constructed on the shoreline and much of the littoral
zone was filled with sawdust, wood chips, timber wastes, and bark. Large deposits of
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lumbering waste can still be found today in the nearshore zone of Muskegon Lake. The
lumbering era was followed in the 1900s by an era of industrial expansion related to foundries,
metal finishing facilities, petrochemical production, and shipping. Local dunes were
extensively mined for foundry sand and the shoreline of Muskegon Lake had to be further
modified to support heavy industry. Large quantities of waste foundry sand and slag were
used as fill material in the remaining littoral zone.
The West Michigan Shoreline Regional Development Commission (1978) inventoried known
and potential contamination sources for Muskegon Lake. The location of these sites is given
in Figure 1.2. Ruddiman Creek served as a collection point for stormwater and waste
discharges from several foundries, metal finishing facilities, and plating companies in addition
to receiving contaminated groundwater from petrochemical storage tanks and transmission
lines. The creek discharges over a shallow sandy zone of Muskegon Lake that rapidly drops
off in a deep basin (45 ft). In addition, a large pulp and paper mill discharged effluent into
this basin. Division Street Outfall also served as a collection point for industrial stormwater
and waste discharges in addition to receiving metal laden effluents from Shaw Walker,
Anaconda Copper, and Michigan Foundry Supply. High levels of heavy metals (copper, lead,
cadmium, and mercury) were found in the sediments at these locations in previous
investigations (West Michigan Shoreline Regional Development Commission 1982 and EPA
1995).
Moving further east along the shoreline, the downtown waterfront was impacted by a coal
gasification facility (MichCon) that produced illumination gas from the early 1870s to 1950.
High levels of coal tar related wastes were found on site in addition to a contaminated
groundwater plume that was moving towards Muskegon Lake. The site was partially
remediated in the 1990s and the amount of contaminated groundwater entering the lake was
never determined. In addition to the MichCon site, this section of Muskegon Lake also was
the location of two major shipping ports, an iron foundry (part of the former Lakey Foundry
Complex), a coal storage operation, rail yards, and a wastewater treatment outfall. The area
was also impacted by dredging and disposal related to the maintenance of commercial
shipping ports. Because of the many potential sources of anthropogenic contamination, this
location will be referred to as the lakeshore industrial area in this report. Sediment
contamination in this area was not investigated in previous studies.
The area east of the downtown waterfront and bordered by Ryerson Creek was the location of
the Lakey and Teledyne Foundries. Foundry sand, slag, and metal scrap were commonly used
as fill materials in this area. High concentrations of heavy metals were found at this location
in 1982 in addition to moderate concentrations of PAH compounds.
The South Branch and North Branch of the Muskegon River enter the lake along the eastern
end. A large metal scrap yard was located on Muskegon Lake between the South Branch and
Ryerson Creek. The wastewater discharge for the City of Muskegon also was located on the
South Branch near the river mouth. Further upstream, a municipal waste landfill (1 mile) and
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1. Ruddiman Creek/Grand Trunk
2. Division Street
3. Downtown Waterfront
4. Ryerson Creek
5. Four Mile/South Branch
6. North Branch
Ruddiman
Creek
FIGURE 1.2. AREAS OF SEDIMENT CONTAMINATION IDENTIFIED IN MUSKEGON LAKE.
the NPDES discharge for Teledyne Continental Motors (2 miles) are located on the river
banks. The 1982 investigation found very high levels of PAH compounds (>500 mg/kg) and
heavy metals near the Teledyne outfall. Contamination sources are also present near the
mouth of the North Branch. A fuel unloading terminal, petroleum tank farms, and a large coal
fired power plant are located in this area. No contamination was found near the mouth of the
North Branch of the Muskegon River in 1982.
Evans (1992) summarized historical water quality and biological data for Muskegon 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 1,258
mg/kg and 8,180 mg/kg respectively. Benthic macroinvertebrate communities were
dominated by pollution tolerant oligochaetes and chironomids. While ambient water quality
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improved significantly by the mid 1980s, the composition of the benthic community remained
similar due to persistent sediment contamination. It is important to note that five months prior
to collection of samples for this project (April 1999), a sewer break resulted in the release of
over 60 million gallons of raw sewage into the lake. The sewage was diverted to Ryerson and
Ruddiman Creeks and was of sufficient magnitude to influence the benthic community in much
of the study area.
1.2 Project Objectives And Task Elements
The objective of this investigation is to conduct a Category II assessment of sediment
contamination in Muskegon Lake. Specific objectives and task elements are summarized
below:
• Determine the nature and extent of sediment contamination in Muskegon Lake.
- A preliminary investigation was conducted to examine the nature and extent of
sediment contamination in Muskegon 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 Division Street Outfall. Arsenic, barium, cadmium, chromium, copper,
lead, nickel, zinc, selenium, mercury, TOC, semivolatile organics, resin acids, and
grain size were analyzed in all core samples.
- Surface sediments were collected from Muskegon Lake with a Ponar dredge 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.
- Critical measurements were the concentration of arsenic, barium, cadmium, chromium,
copper, lead, nickel, zinc, selenium, mercury, semivolatile organics, and resin acids in
sediment samples. Non-critical measurements were total organic carbon and grain size.
• Determine the depositional history and stability of selected sediments in Muskegon Lake.
- Sediment samples were collected with a box core and a piston core in Muskegon
Lake. Concentration vs. depth profiles of radioisotopes and heavy metals were
determined in the sediment cores.
- Critical measurements were the concentrations of lead, chromium, and the
radioisotopes (210Pb, 214Bi, and 137Cs).
• Evaluate the toxicity of sediments from sites in the lower Muskegon Lake area.
- Sediment toxicity evaluations were performed with Hyalella azteca and Chironomus
tentans.
- Toxicity measurements in Muskegon Lake sediments were evaluated and compared to
the two control locations. These measurements determined the presence and degree
of toxicity associated with sediments from Muskegon 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 Muskegon Lake
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- Sediment samples were collected with a Ponar in Muskegon Lake.
- The abundance and diversity of the benthic invertebrate communities were evaluated
and compared to the two control locations.
- Critical measurements were the abundance and species composition of benthic
macroinvertebrates.
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
Muskegon 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 address contamination at specific sites, 12 core samples were collected
from locations likely to have been impacted by significant anthropogenic activity. The
locations were selected to target current and historical point sources and downstream sites
from known industrial and municipal discharges. These sites were determined by the analysis
of historical data and industrial site locations. Analysis of lake depositional areas was then
used to select locations that would reflect the general distribution of contaminants.
Sediment samples were collected using the U.S. EPA Research Vessel Mudpuppy. The
sediment cores were collected with a VibraCore device with core lengths ranging from 1m-
2.4 m. The core samples were then sectioned for chemical analysis. In general, two 38 cm
segments were removed for the top and middle sections. The remainder of the core length
was designated as the bottom section. Section lengths were altered if changes in the strata
were noted. Ponar samples also were collected at these locations to provide an assessment of
the near surface zone sediments. For each core, the analytical parameters included a general
series of inorganic and organic constituents as well as specific chemicals related to a particular
source or area. The general chemical series for each core included the following heavy
metals; arsenic, cadmium, chromium, copper, lead, mercury, nickel, and zinc. Analytical
methods were performed according to the protocols described in SW-846 3rd edition (EPA
1999). 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 (1999) 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 and
Schelske et al., 1994). In consideration of the effluent diversions that occurred in the early
1970s, heavy metal flux into Muskegon 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 Muskegon 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
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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 Muskegon Lake.
1.4 References
Alexander, J. 2000. The Muskegon River Unnatural Wonder. Special Series of The
Muskegon Chronicle. September 12-15 1999. Muskegon, MI. 20pp.
210
Appleby, P.G. and F. Oldfield. 1983. The assessment of Pb data from sites with varying
sediment accumulation rates. Hydrobiologia 103: 29-35.
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. Contam. Toxico. 35 (2):202-
212.
EPA 1994. Test Methods for Evaluating Solid Waste Physical/Chemical Methods. U.S.
Environmental Protection Agency. SW-846, 3rd Edition.
EPA 1995. Muskegon Lake Area of Concern: Division Street Outfall, 1994 sediment
assessment. EPA Technical Report. Great Lakes National Program Office, Chicago.
48pp.
EPA 1999. Methods for Measuring the Toxicity and Bioaccumulation of Sediment-
Associated Contam
EPA/600/R-99/064
Associated Contaminants with Freshwater Invertebrates. 2nd Edition. EPA Publication
Evans, E.D. 1992. Mona, White, and Muskegon Lakes in Muskegon County, Michigan The
1950s to the 1980s. Michigan Department of Natural Resources. MI/DNR/SWQ-
92/261. 91pp.
Schelske, C.L., A. Peplow, M. Brenner, and C.. Spencer. 1994. Low-background gamma
counting: Applications for 210Pb dating of sediments. J. Paleolim. 10:115-128.
West Michigan Shoreline Regional Development Commission. 1977. Point Source Inventory:
Sourcebook for Water Quality Planning. 156 pp.
West Michigan Shoreline Regional Development Commission. 1982. The Muskegon County
Surface Water Toxics Study. Toxicity Survey General Summary. 153 pp.
-------
2.0 Sampling Locations
Sampling locations for the assessment of contaminated sediments in Muskegon Lake were
selected based on proximity to potential point and non-point 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 12 locations were selected for the collection of core samples
and 15 locations were selected for Ponar samples. Cores were not collected in the Division
Street Outfall area (M-5, M-6, and M-7) because of the previous sampling event performed by
the EPA (1995). In addition, three stratigraphy cores were collected. Two were collected
from the same general location as M-l (M-1S) and M-5 (M-5S). The third stratigraphy core
was collected at the deepest location in the lake off the Car Ferry Dock (M-2S). The
sampling locations are listed below and displayed on Figure 2.1. GPS coordinates, depths,
and visual descriptions are included in Tables 2.1 and 2.2 respectively, for core and Ponar
samples.
Core Identification
M-l and M-l S
M-2S
M-3 and M-4
M-5, M-5S, M-6, M-7
M-8
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
Potential Source
Ruddiman Creek/Paper Mill
Deep Deposition Area off Car Ferry Dock
Ruddiman Creek
Division Street Outfall (Ponars)
Westran/Shaw Walker
Mart Dock Marina
Teledyne/Lakey Foundry
Teledyne/Lakey Foundry/Ryerson Creek
Ryerson Creek
Mouth of Muskegon River South Branch
Mouth of Muskegon River North Branch
Control
Lakeshore Industrial Area (MichCon/Lakey Foundry)
-------
\
a.5 a o.s 1
Figure 2.1 Muskegon Lake Core and PONAR Sampling Stations.
10
-------
TABLE 2.1 MUSKEGON LAKE CORE SAMPLING STATIONS.
Muskegon Lake Core Sampling Stations.
Station
M-l
M-3
M-4
M-8
M-9
M-10
M-ll
Sample ID
Muskegon 1 Top
Muskegon 1 Middle
Muskegon 1 Bottom
Muskegon 3 Top
Muskegon 3 Middle
Muskegon 3 3-4
Muskegon 34-5
Muskegon 4 Top
Muskegon 4 Bottom
Muskegon 8 Top
Muskegon 8 2
Muskegon 8 3
Muskegon 8 4
Muskegon 9 Top
Muskegon 9 Bottom
Muskegon 10 Top
Muskegon 10 Middle
Muskegon 10 Bottom
Muskegon 1 1 Top
Muskegon 112
Muskegon 113
Muskegon 11 Bottom
Date
10/26/99
10/26/99
10/28/99
10/28/99
10/27/99
10/27/99
10/27/99
Depth to Core
m
12.0
12.0
12.0
12.0
12.2
12.2
12.2
12.2
12.2
12.8
12.8
12.8
8.2
8.2
8.2
8.2
8.2
7.5
7.5
7.5
7.4
7.4
7.4
7.4
8.8
Depth of
Core
cm
91
0-30
30-61
61-91
152
0-30
30-91
91-122
122-152
84
0-30
30-84
198
0-38
38-76
76-137
137-198
81
0-41
41-81
122
0-38
38-76
76-122
183
0-38
38-76
76-114
114-183
Latitude
N
43° 13.39'
43° 13.42'
43° 13.36'
43° 14.08'
43° 14.38'
43° 14.63'
43° 14.72'
Longitude
W
86° 1869'
86° 17.22'
86° 17.34'
86° 16.26'
86° 15.78'
86° 15.56'
86° 15.39'
Description
Black silt oil sheen
Black silt
Hard sandy black clay
Black silt oil sheen
Black silt
Black silt
Black sand with wood chips
Black silt with wood chips
Loose sand with silt
Black-brown silt with oil sheen
and hydrocarbon odor
Black silt with oil sheen
Brown silt
Brown silt and grey sandy clay
with shells
Grey Sand
Black sand with wood chips
and shells, hydrocarbon odor
Black-brown silt with oil sheen
and hydrocarbon odor
Black sandy silt w/ wood chips
and oil drops
Grey-brown sand
Black-brown silt with oil drops
and hydrocarbon odor
Brown silt
Brown silt
Brown silt
11
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TABLE 2.1 (CONTINUED) MUSKEGON LAKE CORE SAMPLING STATIONS
(*FIELD DUPLICATE SAMPLE)
Muskegon Lake Core Sampling Stations.
Station
M-llDup*
M-12
M-13
M-14
M-15
M-16A
Sample ID
Muskegon 1 ID Top
Muskgeon 1 ID 2
Muskgeon 1 ID 3
Muskegon 1 ID Bottom
Muskegon 12 Top
Muskegon 12 Middle
Muskegon 12 Bottom
Muskegon 13 Top
Muskegon 13 2
Muskegon 13 3
Muskegon 13 Bottom
Muskegon 14 Top
Muskegon 14 2
Muskegon 14 3
Muskegon 14 Bottom
Muskegon 15 Top
Muskegon 15 Middle
Muskegon 15 Bottom
Muskegon 16A Top
Muskegon 16A Bottom
Date
10/27/99
10/27/99
10/28/99
10/27/99
10/27/99
10/29/99
Depth to Core
m
8.9
8.9
8.9
8.9
8.9
4.2
4.2
4.2
4.2
9.6
9.6
9.6
9.6
9.6
8.6
8.6
8.6
8.6
8.6
9.6
9.6
9.6
9.6
5.9
5.9
5.9
Depth of
Core
cm
147
0-38
38-76
76-114
114-147
165
0-84
84-122
122-165
198
0-38
38-76
76-137
137-198
170
0-38
38-76
76-114
114-170
160
0-38
38-84
84-160
76
0-38
38-76
Latitude
N
43° 14.56'
43° 14.90'
43° 15.04'
43° 14.60'
43° 14.46'
Longitude
W
86° 14.96'
86° 15.18'
86° 15.11'
86° 16.46'
86° 15.48'
Description
Black-brown silt with oil drops
Brown silt
Brown silt
Brown silt
Brown silt
Grey sand with hydrocarbon
odor
Sandy, dark silt with
hydrocarbon odor
Damp clay silt
Black silt
Black silt
Grey Peate
Sandy clay with wood chips
Black silt
Black sandy silt
Black sandy clay silt
Black clay silt
Black silt
Black silt
Sand
Black coal tar, very strong
solvent odor
Sand, tar/coal flecks, solvent
odor
12
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TABLE 2.2 MUSKEGONLAKE PONAR SAMPLING STATIONS (*FIELD
DUPLICATE SAMPLE)
Muskegon Lake Ponar Sampling Stations.
Station
M-l-P
M-3-P
M-4-P
M-5-P
M-6-P
M-7-P
M-8-P
M-8-P Dup*
M-9-P
M-10-P
M-ll-P
M-12-P
M-13-P
M-14-P
M-15P
M-16AP
Sample ID
M-l-P
M-3-P
M-4-P
M-5-P
M-6-P
M-7-P
M-8-P
M-8-P
M-9-P
M-10-P
M-ll-P
M-12-P
M-13-P
M-14-P
M-15P
M-16AP
Date
10/29/99
10/29/99
10/29/99
10/29/99
10/29/99
10/29/99
10/29/99
10/29/99
10/28/99
10/28/99
10/28/99
10/28/99
10/29/99
10/29/99
10/29/99
10/29/99
Depth to
Sediment
m
12.0
12.2
12.8
6.4
4.1
7.9
8.2
8.2
7.5
7.4
8.8
4.2
9.6
8.6
9.6
5.4
Latitude
N
43° 13.37'
43° 13.42'
43° 13.36'
43° 13.95'
43° 13.99'
43° 14.01'
43° 14.01'
43° 14.01'
43° 14.39'
43° 14.64'
43° 14.72'
43° 14.57'
43° 14.89'
43° 15.04'
43° 14.61'
43° 14.47'
Longitude
W
86° 18.69'
86° 17.21'
86° 17.34'
86° 15.92'
86° 15.92'
86° 15.92'
86° 16.27'
86° 16.27'
86° 15.71'
86° 15.56'
86° 15.38'
86° 14.95'
86° 15.18'
86° 15.12'
86° 16.46'
86° 15.52'
Description
Black silt, oil sheen
Sandy silt
Sandy silt
Black silt with oil sheen, hydrocarbon odor
Black silt with oil sheen, hydrocarbon odor
Black silt
Sandy silt
Sandy silt
Black silt with organic matter and zebra
mussels
Sand with hydrocarbon odor
Sandy silt
Sandy silt
Black silt, hydrocarbon odor
Black silt
Black silt
Sand/ gravel, hydrocarbon odor and tar/coal
flecks
TABLE 2.3 MUSKEGON LAKE STRATIGRAPHY SAMPLING STATIONS
Station
M-1S
M-2S
M-5S
Date
03/29/2000
03/29/2000
10/292000
Depth to
Sediment
m
12.1
22.5
6.4
Latitude
N
43° 13.37'
43° 13.48'
43° 13.95'
Longitude
W
86° 18.69'
86° 17.83'
86° 15.92'
13
-------
3.0 Methods
3.1 Sampling Methods
Sediment and benthos samples were collected using the U.S. EPA Research Vessel
Mudpuppy. Vibra Core 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 was 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.
14
-------
TABLE 3.1 SAMPLE CONTAINERS, PRESERVATIVES, AND HOLDING TIMES
Hold Times
Matrix Parameter
Sediment
Sediment
Sediment
Water
Culture
Metals
TOC
Container Preservation Extraction Analysis
250 mL Wide cooi ^o 40^; — 6 months,
Mouth Plastic Mercury-28
Days
250 mL Wide Freeze -10°C
Mouth Plastic
Sediment Grain Size 1 Quart Zip-Lock cooi to 40^;
Plastic Bag
Toxicity 4 liter Wide Mouth Cool to 4°C
Glass
Semi-Volatile
Organics and
Resin Acids
Alkalinity
1000 mL Amber
Glass
250 mL Wide
Mouth Plastic
Cool to 4°C 14
Cool to 4°C
6 months
Sediment Semi-Volatile 500 mL Amber Cool to 4°C 14 days 40 days
Organics Glass
6 months
45 days
40 daYs
24 hrs.
Water
Ammonia
Hardness
Conductivity
pH
250 mL Wide
Mouth Plastic
Cool to 4°C
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. Instrumental
conditions and a summary of quality assurance procedures are provided in the following
sections.
15
-------
TABLE 3.2.1 ANALYTICAL METHODS AND DETECTION LIMITS
SEDIMENT MATRIX
Parameter
Arsenic, Lead,
Selenium, Cadmium
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, 74711, 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 was added to each sample. Vessels then were 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 using 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 centrifuge
16
-------
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,
samples were mixed, and the centrifuge tubes were returned in 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 along 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
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
3
4
5
Temp,0
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 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.
17
-------
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
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,0
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 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 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
3
4
5
6
Temp,0
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 pyrolysis step. The calibration curve was
constructed from four standards and a blank. Validity of calibration was verified with a check
18
-------
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
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
3
4
5
6
Temp,0
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 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 by 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
Cr
Cu
Fe
Wavelength, nm
308.2
233.5
315.9
267.7
324.8
259.9
19
-------
Element Analyzed
Mg
Mn
Ni
Zn
Wavelength, nm
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
interferences 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 with 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. The samples
were allowed to air dry again prior to analysis. 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.
20
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3.2.10 Semivolatiles Analysis
Sediment samples were extracted for semivolatiles analysis 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 1 mL volume.
The sample extracts were analyzed by GC/MS on a Finnigan GCQ 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
lul
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 meeting method acceptance
criteria. The MS and MSD samples were analyzed at a 5% frequency.
21
-------
TABLE 3.2.2 ORGANIC PARAMETERS AND DETECTION LIMITS
Sediment
(mg/kg)
Semi-Volatile Organic Compounds (8270)
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
Fluor ene 0.33
4,6-Dinitro-2-methylphenol 1.7
4-Bromophenyl-phenyl ether 0.33
22
-------
TABLE 3.2.2 ORGANIC PARAMETERS AND DETECTION LIMITS (CONTINUED)
Sediment
(mg/kg)
Semi-Volatile Organic Compounds (8270)
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%
23
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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-NHs F.
Hardness Standard Methods 2340 C. 10 mg/1
3.4 Sediment Toxicity
The evaluation of the toxicity of the Muskegon 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
A moderately hard well water for H. azteca and C. tentans cultures and maintenance was
employed.
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,
24
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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.
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 Tetrafin®. 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 Tetrafin® 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 the test.
25
-------
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 organi sms
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).
26
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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 organi sms
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.
Test Method 100.2. EPA Publication 600/R-94/024 (July 1994).
27
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3.4.4 Stati sti cal Analy si s
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.
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 and rocks decays. In the atmosphere, 222Rn decays to 210Pb which is
deposited at the earth's surface with atmospheric washout as unsupported or excess 210Pb.
Supported 210Pb in lake sediments is produced by the decay of 226Ra that is deposited as one
fraction of erosional inputs. In the sediments, gaseous 222Rn produced from 226Ra is trapped
28
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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.
Sediment ages were calculated using a CRS model (Appleby and Oldfield 1983). This model
calculates ages based on the assumption that the flux of excess 210Pb 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:
t = (1/k) [In (Ao/A)]
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
toBinford(1990).
3.7 References
Appleby, P. G. and F. Oldfield. 1983. The assessment of Pb data from sites with varying
sediment accumulation rates. Hydrobiologia 103: 29-35.
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.
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.
29
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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 Sediment Quality Triad Analysis
Section 4.6 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. Finally, Section 4.5 provides a discussion of all the data using the Sediment
Quality Triad to assess the significance of the sediment contamination in Muskegon Lake.
The project summary and conclusions are provided in section 4.6.
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 for the laboratory control sample, indicating that the problem was matrix related. The
data was 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 in total organic carbon (TOC 1% - 4%) in the top 40 cm. Grain size
distributions changed to include a greater sand fraction (125-500 um range) in the next 40 cm
section. Most cores contained > 50% sand in depths beyond 80 cm. This pattern is consistent
with historical industrial development of the shoreline. Much of the lake shoreline was filled
with foundry sand during the 1930s-1950s. Erosion of the fill material 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. Cores from stations M-4, M-9, M-12, and M-16 did not fit
this pattern. M-4 was collected near an aggregate storage area and in the deposition zone of
Ruddiman Creek. Erosion inputs from both of these sources would increase the sand fraction
30
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present in the core. Station M-9 was collected near a peninsula that once contained an
abandoned metal finishing facility. The site has limited vegetation and is also subject to wave
induced erosion. Station M-12 was different than the other cores in that a fine grained silt
layer was found below 80 cm of sandy sediment. This site was located near an abandoned
foundry, an aggregate storage area, and the mouth of Ryerson Creek. The core from M-16
was the only location that contained a significant gravel fraction that may have been the result
of historical dredging or filling in the area. The sediments at this station also contained flecks
of coal tar/coal and had a strong odor of aromatic hydrocarbons. 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). PONARS collected from M-4,
M-9, M-12, and M-16 were all found to contain a higher fraction of sandy sediments. 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.
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 PAH analyses for the same sample
groupings are given in Table 4.1.5. Figures 4.1.1, 4.1.2, and 4.1.3, 4.1.4, and 4.1.5 illustrate
the spatial distribution of chromium, cadmium, copper, lead, and PAH compounds,
respectively, in core samples collected from western Muskegon Lake. This section of the lake
is located down stream from the historical industrial activity found along the southeast shore
and in the deposition zone of Ruddiman Creek. Low levels of metals were found at M-4. As
discussed earlier, this station contained sandy sediment that would not accumulate heavy
metals. The highest levels of chromium, cadmium, copper, and lead were found in the top 30
cm layer of the core from M-l. Levels decrease dramatically as depth increased, indicating
the source of contaminants is relatively recent. In contrast, the concentrations of the same
metals were higher in the middle 30-60 cm section than the top layer of the M-l core. Very
little change was noted in the bottom core section, as all metals remained elevated. This
pattern suggests that the near shore environment is subject to mixing and resuspension from
wind and wave induced currents. Station M-l was located in the middle of the lake and
outside the influence of near shore currents. Since deposition from Ruddiman Creek would
influence both locations and no industrial activity was present along the local shoreline,
sediment mixing at M-3 in combination with the advection of contaminants along the old river
channel would account for the pattern of deposition observed at the locations.
Figures 4.1.6, 4.1.7, and 4.1.8, 4.1.9, and 4.1.10 present the spatial distribution of chromium,
cadmium, copper, lead, and PAH compounds, respectively, in core samples collected from
eastern Muskegon Lake. The southern shoreline of this part of the lake was heavily
industrialized and also extensively backfilled with foundry sand. Only station M-9 did not
contain elevated levels of heavy metals. The core from this location had a large sand fraction
and would have a limited capacity to retain metals. Three depositional patterns were noted in
31
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TABLE 4.1.1 RESULTS OF SEDIMENT GRAIN SIZE FRACTIONS, TOC, AND PERCENT SOLIDS FOR MUSKEGON LAKE CORE
SAMPLES, OCTOBER 1999.
Sample
ID
M-1 -top
M-1 mid
M-1 bot
M-3 top
M-3-mid
M-3 3-4'
M-3 4-5'
M-4 top
M-4 bot
M-8 top
M-8-2
M-8-3
M-8-bot
M-9 top
M-9 bot
M-1 0 top
M-10 mid
M-1 0 bot
M-1 1 top
M-11 2
M-11 3
M-1 1 bot
M-1 1D top
M-11D2
M-11D3
M-1 1 D bot
<2000 um 1 000-2000 um
Weight
0.0
0.3
1.9
1.0
0.1
0.1
0.1
4.6
2.7
0.0
0.7
0.0
0.8
2.4
3.7
0.5
6.6
0.2
0.1
0.1
0.3
0.5
0.0
0.0
0.0
0.1
Weight
0.3
0.8
1.7
0.1
0.1
0.1
0.1
0.6
0.5
0.1
0.2
0.0
0.6
0.2
2.1
0.2
4.1
0.4
0.1
0.0
0.1
0.1
0.1
0.0
0.0
0.1
850-1000 um
Weight
0.1
0.4
0.7
0.0
0.0
0.1
0.1
0.2
0.1
0.0
0.1
0.0
0.3
0.5
0.8
0.1
1.8
0.2
0.1
0.0
0.0
0.1
0.0
0.0
0.0
0.0
500-850 um
Weight
0.8
3.7
5.1
0.2
0.3
0.4
1.1
0.7
0.9
0.3
0.9
9.1
3.2
10
6.0
0.4
7.2
2.6
0.2
0.3
0.2
0.4
0.1
0.6
0.2
0.2
125-500 um
Weight
6.4
35
70
5.2
3.9
9.9
61
45
67
14
17
0.4
36
65
65
10
46
79
3.2
6.1
5.9
8.5
4.6
5.7
3.9
6.8
63-125 um <63 um
Weight
6.6
3.5
1.1
9.0
5.4
6.8
3.5
7.5
3.9
0.2
4.6
7.8
16
1.9
3.5
12
3.2
2.4
8.0
12
11
7.5
9.2
8.6
8.9
9.1
Weight
86
56
19
85
90
83
34
41
25
86
76
83
43
20
19
76
32
15
88
81
82
83
86
85
87
84
Solids
Weight
16
30
77
16
17
19
45
49
55
20
28
31
58
89
77
28
54
83
24
29
34
34
24
29
34
37
TOC
Weight
4.2
2.1
<0.5
5.1
3.9
2.6
1.1
1.2
<0.5
4.7
3.4
5.2
<0.5
<0.5
<0.5
1.5
<0.5
<0.5
4.3
3.2
1.3
<0.5
4
3.1
1.8
<0.5
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TABLE 4.1.1 (CONTINUED) RESULTS OF SEDIMENT GRAIN SIZE FRACTIONS, TOC, AND PERCENT SOLIDS FOR MUSKEGON
LAKE CORE SAMPLES, OCTOBER 1999.
Sample
ID
M-12top
M-12mid
M-12bot
M-13top
M-132
M-133
M-13bot
M-14top
M-142
M-143
M-14bot
M-15top
M-15mid
M-15Bot
M-16top
M-16 mid
M-16Atop
M-16Abot
<2000 urn
Weight
3.4
0.6
0.3
0.2
0.0
0.1
2.8
0.4
0.9
0.3
0.0
0.0
0.0
0.4
9.0
2.6
2.9
7.8
1000-2000 urn
Weight
1.3
0.5
0.3
0.0
0.0
0.1
1.1
0.1
0.1
0.1
0.4
0.1
0.0
0.2
1.8
0.3
0.5
4.0
850-1000 urn
Weight
0.7
0.3
0.2
0.0
0.0
0.0
0.2
0.1
0.0
0.1
0.1
0.0
0.0
0.0
0.4
0.3
0.3
1.7
500-850 urn
Weight
8.4
2.1
0.7
0.1
0.1
0.1
1.0
0.2
0.3
0.3
0.4
0.1
0.3
1.3
2.2
3.0
1.2
11
1 25-500 urn
Weight
65
49
15
3.8
4.7
4.9
20
8.5
23
23
6.0
2.1
9.8
85
61
73
34
64
63-125 urn
Weight
4.7
15
9.7
9.3
12
9.2
8.4
13
16
16
9.2
3.7
7.5
1.3
6.8
0.8
8.6
1.4
<63 urn
Weight
17
33
74
87
83
86
67
78
60
60
84
94
82
11
18
20
53
10
Solids
Weight
91
68
50
34
37
39
44
28
46
45
38
18
28
88
78
81
39
88
TOC
Weight
<0.5
<0.5
<0.5
2.7
1.9
2.6
4.0
2.4
1.5
1.1
<0.5
2.2
1.6
<0.5
0.8
<0.5
1.9
<0.5
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TABLE 4.1.2 RESULTS OF SEDIMENT GRAIN SIZE FRACTIONS, TOC, AND PERCENT SOLIDS FOR MUSKEGON LAKE PONAR
SAMPLES, OCTOBER 1999.
Sample
ID
M-1P
M-3P
M-4P
M-5P
M-6P
M-7P
M-8P
M-8PD
M-9P
M-10P
M-11P
M-12P
M-13P
M-14P
M-15P
M-16AP
<2000 um
Weight
0.9
0.5
5.6
0.2
0.3
0.9
0.0
0.0
1.3
0.5
0.0
17
0.9
0.9
2.9
8.8
1 000-2000 um
Weight
0.0
0.2
0.5
0.1
0.2
0.1
0.0
0.1
1.1
0.0
0.1
2.7
0.2
0.2
0.1
1.8
850-1000 um
Weight
-0.1
0.0
0.1
0.0
0.0
0.0
0.0
0.0
0.6
-0.0
0.0
1.2
0.1
0.1
0.0
0.3
500-850 um
Weight
0.2
0.2
1.6
0.3
0.2
0.2
0.3
0.2
5.9
0.1
0.0
8.9
0.3
0.2
0.1
1.8
125-500 um
Weight
6.2
6.9
73
7.2
11
7.9
6.4
4.5
74
3.2
2.9
53
7.1
6.5
9.7
67
63-125 um
Weight
2.1
9.0
4.2
11
13
15
10
7.7
2.2
7.5
8.4
1.7
13
12
4.5
9.6
<63 um
Weight
91
83
15
81
75
76
83
87
15
89
89
15
79
81
83
11
Solids
Weight
15
18
72
22
23
20
16
17
66
22
23
85
25
25
19
65
TOC
Weight
4.5
5.5
<0.5
4.1
5.3
8.0
5.2
4.5
<0.5
1.1
4.3
<0.5
4.2
2.3
2.5
1.4
-------
TABLE 4.1.3 RESULTS OF SEDIMENT METALS ANALYSES FOR MUSKEGON LAKE CORE SAMPLES (MG/KG DRY WEIGHT),
OCTOBER 1999.
Sample ID
M ITop
M 1 Middle
M 1 Bottom
MSTop
M 3 Middle
M33-4
M34-5
M4Top
M 4 Bottom
MSTop
M82
M83
M84
M9Top
M 9 Bottom
M 10 Top
M 10 Middle
M 10 Bottom
M 1 1 Top
M 112
M 11 3
M 1 1 Bottom
M 1 ID Top
M 11D2
M 11D3
M 1 ID Bottom
Total
Arsenic
mg/kg
15
7.8
10
12
10
14
2.7
5.4
7.9
7.3
9.1
8.7
7.3
1.2
4.4
10
12
5.5
7.6
10
7.6
6.7
6.1
8.9
7.3
9.0
Total
Barium
mg/kg
150
94
18
130
140
150
36
45
32
140
130
85
38
10
28
100
65
16
110
130
150
92
100
130
140
130
Total
Cadmium
mg/kg
12
3.4
0.11
3.7
11
10
0.21
0.88
1.4
11
20
0.76
0.13
0.66
0.35
5.5
2.8
0.12
2.7
5.3
12
1.6
2.8
5.4
9.5
10
Total
Chromium
mg/kg
440
160
8.4
130
420
230
11
38
48
290
78
25
7.5
8.2
8.0
110
27
2.8
63
160
150
27
66
170
240
86
Total
Copper
mg/kg
85
31
2.2
65
90
87
6.0
21
16
100
150
17
3.5
7.0
4.5
68
19
1.5
50
81
100
25
50
81
94
82
Total
Nickel
mg/kg
27
15
3.1
24
29
24
6.4
8.8
6.4
33
29
17
5.0
2.5
4.1
24
7.3
1.2
20
38
34
17
20
39
36
25
Total
Lead
mg/kg
150
62
5.1
120
170
170
6.8
42
35
180
160
19
2.6
7.5
10
110
45
1.9
68
120
160
51
71
130
140
150
Total
Zinc
mg/kg
360
140
23
270
380
300
27
82
71
420
290
77
20
21
26
240
87
9.8
170
300
270
99
170
320
300
220
Total
Mercury
mg/kg
0.65
0.29
<0.10
0.39
0.69
1.2
<0.10
0.12
0.11
0.82
1.8
0.23
<0.10
<0.10
<0.10
0.41
0.19
<0.10
0.26
0.37
0.58
0.26
0.28
0.40
0.54
0.59
Total
Selenium
mg/kg
0.24
<0.10
<0.10
0.50
0.55
0.58
<0.10
0.29
<0.10
0.45
0.49
0.30
<0.10
<0.10
<0.10
<0.10
<0.10
<0.10
0.41
0.45
0.44
0.31
0.42
0.46
0.43
0.38
-------
TABLE 4.4.3 (CONTINUED) RESULTS OF SEDIMENT METALS ANALYSES FOR MUSKEGON LAKE CORE SAMPLES (MG/KG
DRY WEIGHT), OCTOBER 1999.
Sample ID
M 12 Top
M 12 Middle
M 12 Bottom
M 13 Top
M 132
M 133
M 13 Bottom
M 14 Top
M 142
M 143
M 14 Bottom
M 15 Top
M 15 Middle
M 15 Bottom
M 16A Top
M 16A Bottom
Total
Arsenic
mg/kg
0.90
5.1
11
6.8
5.9
7.5
5.1
7.4
5.8
5.5
6.7
8.3
5.8
5.0
8.4
1.8
Total
Barium
mg/kg
9.5
45
140
99
110
94
59
88
66
58
87
140
120
12
90
13
Total
Cadmium
mg/kg
0.17
1.5
8.5
5.0
7.6
4.0
0.24
1.0
2.4
1.1
0.42
10
1.4
<0.10
7.4
0.15
Total
Chromium
mg/kg
4.8
28
210
140
160
42
18
34
69
18
24
190
33
3.8
47
4.0
Total
Copper
mg/kg
9.4
34
130
40
49
31
9.9
32
26
17
16
72
24
<0.10
58
1.5
Total
Nickel
mg/kg
2.3
8.7
31
21
20
16
12
16
15
11
19
26
20
1.8
16
2.1
Total
Lead
mg/kg
12
73
320
77
70
110
10
42
70
100
16
160
48
1.5
140
4.6
Total
Zinc
mg/kg
18
120
450
200
200
120
44
110
140
62
71
300
110
14
180
12
Total
Mercury
mg/kg
<0.10
0.32
0.84
0.30
0.41
0.37
<0.10
0.14
0.19
0.15
<0.10
0.60
0.26
<0.10
0.72
<0.10
Total
Selenium
mg/kg
<0.10
<0.10
0.52
0.40
0.41
0.36
<0.10
0.39
0.31
0.28
0.33
0.82
0.47
<0.10
0.46
<0.10
-------
TABLE 4.1.4 RESULTS OF SEDIMENT METALS ANALYSES FOR MUSKEGON LAKE PONAR SAMPLES (MG/KG DRY WEIGHT),
OCTOBER 1999.
Sample ID
M IP
MSP
M4P
MSP
M6P
M7P
M8P
M8PD
M9P
M 10P
M IIP
M 12P
M 13P
M 14P
M 15P
M 16AP
Total
Arsenic
mg/kg
10
6.1
5.2
11
9.5
11
8.2
5.1
5.6
6.2
6.8
5.2
10
5.2
5.8
3.7
Total
Barium
mg/kg
130
130
14
180
180
120
120
140
20
110
110
10
97
88
120
33
Total
Cadmium
mg/kg
3.9
2.0
0.13
12
7.9
4.2
4.2
4.6
0.38
2.9
2.3
0.1
3.1
1.1
2.5
1.3
Total
Chromium
mg/kg
250
71
4.8
210
160
120
95
120
9.6
77
61
2.8
80
30
68
20
Total
Copper
mg/kg
63
52
4.0
260
260
100
78
89
6.8
58
49
3.4
39
33
46
16
Total
Nickel
mg/kg
24
19
2.0
38
38
29
24
27
3.4
22
20
2.6
19
14
19
6.8
Total
Lead
mg/kg
120
83
5.8
270
280
140
120
130
12
89
67
6.2
63
31
64
31
Total
Zinc
mg/kg
260
190
13
600
640
290
240
270
30
200
160
14
160
100
160
67
Total
Mercury
mg/kg
0.38
0.20
<0.10
1.7
1.7
0.56
0.50
0.55
<0.10
0.34
0.26
<0.10
0.25
0.14
0.26
0.14
Total
Selenium
mg/kg
0.72
0.44
<0.10
0.49
0.53
0.48
0.54
0.83
<0.10
0.58
0.59
<0.10
0.38
0.38
0.42
<0.10
-------
TABLE 4.1.5 RESULTS OF SEDIMENT PAH ANALYSES FOR MUSKEGON LAKE CORE AND
PONAR SAMPLES (MG/KG DRY WEIGHT), OCTOBER 1999.
Sample ID Naphthalene
M 1 Top < 0.33
M 1 Mid < 0.33
MlBot
M3Top
M3Mid
M33-4
M34-5
M4Top
M4Bot
M8Top
M82
M83
M84
M9Top
M9Bot
M 10 Top
M 10 Mid
M 10 Bot
M 1 1 Top
M112
M113
Mil Bot
M 1 ID Top
M11D2
M11D3
Ml ID Bot
M 12 Top
M 12 Mid
M 12 Bot
M 13 Top
M132
M133
M 13 Bot
M 14 Top
M142
M143
M 14 Bot
M 15 Top
M 15 Mid
M 15 Bot
M 16ATop
M16ABot
M1P
M3P
M4P
MSP
M6P
M71P
MSP
M8PD
M9P
M10P
M11P
M12P
MOP
M14P
M15P
M16AP
<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
<0.33
<0.33
<0.33
<0.33
<0.33
320
1.5
<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
0.87
2-Metiiyl-
naphthalene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
450
3.3
<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
Acenaph-
thylene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
39
0.60
<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
3.8
Acenaph-
thene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
390
5.7
<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
8.8
Dibenzofuran Fluorene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
40
0.53
<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
0.74
<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
<0.33
<0.33
<0.33
<0.33
<0.33
220
3.1
<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
6.7
Phenanthrene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
640
8.6
<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
30
Anthracene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
200
2.9
<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
11
Carbazole
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
4.7
<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
Fluor-
anthene
<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
0.34
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
0.66
<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
250
3.8
<0.33
<0.33
<0.33
0.82
1.3
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
16
38
-------
TABLE 4.1.5 (CONTINUED) RESULTS OF SEDIMENT PAH ANALYSES FOR MUSKEGON
LAKE CORE AND PONAR SAMPLES (MG/KG DRY WEIGHT), OCTOBER 1999.
Sample ID
Ml Top
Ml Mid
Ml Bot
M3Top
M3Mid
M3 3-4
M34-5
M 4 Top
M4Bot
MS Top
M82
M83
M84
M9Top
M9Bot
M 10 Top
M 10 Mid
M 10 Bot
M 1 1 Top
Mil 2
Mil 3
M 1 1 Bot
Ml ID Top
M11D2
M11D3
Ml ID Bot
M 12 Top
M 12 Mid
M 12 Bot
M 13 Top
M132
M133
M 13 Bot
M 14 Top
M142
M143
M 14 Bot
M 15 Top
M 15 Mid
M 15 Bot
M16ATop
M16ABot
M1P
M3P
M4P
MSP
M6P
M71P
MSP
M8PD
M9P
M10P
M11P
M12P
M13P
M14P
M15P
M16AP
Pyrene
<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
1.9
0.47
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
0.76
<0.33
1.4
<0.33
<0.33
1.4
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
290
4.6
<0.33
<0.33
<0.33
0.83
1.1
<0.33
<0.33
<0.33
0.34
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
20
Benzo(a)
anthracene
<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
<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
110
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
9.6
Chrysene
<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
1.8
0.36
<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
100
1.6
<0.33
<0.33
<0.33
<0.33
0.81
<0.33
<0.33
<0.33
0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
9.1
Benzo(b)
fluoranthene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
88
1.4
<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
5.2
Benzo(k)
fluoranthe
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
53
<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
7.0
Benzo(a)
pyrene
<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
2 2
0.45
<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
97
1.4
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
0.36
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
9.6
Indeno(l,2,3-cd)
pyrene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
13
0.43
<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
2 2
Dibenzo(a,h)
anthracene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
4.4
<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
0.72
Benzo(g,h,i)
perylene
<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
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
<0.33
10
0.42
<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
1.8
Total
PAH
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
8
0
0
0
0
0
0
1
0
1
0
0
1
0
0
0
0
0
0
0
0
0
0
0
3319
42
0
0
0
2
3
0
0
0
1
0
0
0
0
0
0
143
39
-------
M-l
Depth (cm) Cr
0-30 440 mg/kg
30-61 160 mg/kg
61-91 8.4 mg/kg
Depth (cm) Cr
0-30 38 mg/kg
30-84 48 mg/kg
0.25
0.50
0,75
Miles
FIGURE 4.1.1 CHROMIUM IN CORE SAMPLES COLLECTED FROM WESTERN
MUSKEGON LAKE, OCTOBER 1999.
40
-------
M-3
Depth (cm)
Cd
0-30 3.7mg/kg
30-91 11
mg/kg
91-122 10 mg/kg
M-l
Depth (cm) Cd
0-30 12 mg/k
30-61 3.4 mg/k
61-91 0.11 mg/k
M-4
Depth (cm) Cd
0-30 0.88 mg/kg
30-84 1.4ma/k2
M
u.z..
|U. JU
U.. / J 1
Miles
FIGURE 4.1.2 CADMIUM IN CORE SAMPLES COLLECTED FROM WESTERN MUSKEGON
LAKE, OCTOBER 1999.
41
-------
M-4
Depth (cm) Cu
0-30 21 mg/kg
16 mg/kg
0.25
0.50
0,75
Miles
FIGURE 4.1.3 COPPER IN CORE SAMPLES COLLECTED FROM WESTERN MUSKEGON
LAKE, OCTOBER 1999.
42
-------
M-4
Depth (cm) Pb
0-30 42 mg/kg
30-84 35 mg/kg
0.25
0.50
0..75
Miles
FIGURE 4.1.4 LEAD IN CORE SAMPLES COLLECTED FROM WESTERN MUSKEGON
LAKE, OCTOBER 1999.
43
-------
M-3
Depth (cm) PAH
0-30 <1.0mg/kg
30-91 <1.0mg/kg
91-122 <1.0mg/kg
M-l
Depth (cm) PAH
0-30 <1.0mg/k
30-61 <1.0mg/k
61-91 <1.0mg/k
M-4
Depth (cm) PAH
0-30 <1.0mg/kg
30-84 <1.0ni2/k2
0.25
0.50
0,75
Miles
FIGURE 4.1.5 TOTAL PAH COMPOUNDS IN CORE SAMPLES COLLECTED FROM
WESTERN MUSKEGON LAKE, OCTOBER 1999.
44
-------
M-14
Depth (cm) Cr
0-38 34mg/kg
38-76 69mg/kg
76-114 18mg/kg
M-13
Depth (cm) Cr
0-38 140 mg/kg
38-76 160 mg/kg
76-137 42 mg/kg
M-ll
Depth (cm) Cr
0-38 63 mg/kg
38-76 160 mg/kg
76-114 150 mg/kg
M-15
Depth (cm) Cr
0-38 190 mg/kg
38-84 33 mg/kg
84-160 3.8 mg/kg
M-10
Depth (cm) Cr
0-38 110 mg/kg
38-76 27 mg/kg
76-122 2.8 mg/kg
M-12
Depth (cm) Cr
0-84 4.8 mg/kg
84-122 28 mg/kg
122-165 210 mg/kg
M-8
Depth (cm) Cr
0-38 290 mg/kg
38-76 78 mg/kg
76-137 25 mg/kg
M-16
Depth (cm) Cr
0-38 47 mg/kg
38-76 4.0 mg/k
M-9
Depth (cm) Cr
0-41 8.2 mg/kg
41-81 8.0 mg/kg
0.25
0.50
0,75
Miles
FIGURE 4.1.6 CHROMIUM IN CORE SAMPLES COLLECTED FROM EASTERN MUSKEGON
LAKE, OCTOBER 1999.
45
-------
M-14
Depth (cm) Cd
0-38 l.Omg/kg
38-76 2.4 mg/kg
76-114 1.1 mg/kg
M-13
Depth (cm) Cd
0-38 5.0 mg/kg
38-76 7.6 mg/kg
76-137 4.0 mg/kg
M-ll
Depth (cm) Cd
0-38 2.7 mg/kg
38-76 5.3 mg/kg
76-114 12 mg/kg
M-15
Depth (cm) Cd
0-38 l.Omg/kg
38-84 1.4 mg/kg
84-160 <0.10 mg/kg
M-10
Depth (cm) Cd
0-38 5.5 mg/kg
38-76 2.8 mg/kg
76-122 0.12 mg/kg
M-12
Depth (cm) Cd
0-84 0.17mg/k
84-122 1.5 mg/kg
122-165 8.5 mg/kg
M-8
Depth (cm) Cd
0-38 11 mg/kg
38-76 20 mg/kg
76-137 0.76 mg/kg
M-16
Depth (cm) Cd
0-38 7.4 mg/kg
38-76 0.15 mg/kg
M-9
Depth (cm) Cd
0-41 0.66 mg/k
41-81 0.35 mg/kg
0.25
0.50
0,75
FIGURE 4.1.7 CADMIUM IN CORE SAMPLES COLLECTED FROM EASTERN MUSKEGON
LAKE, OCTOBER 1999.
46
-------
M-14
Depth (cm) Cu
0-38 32 mg/kg
38-76 26 mg/kg
76-114 17 mg/kg
M-13
Depth (cm) Cu
0-38 40 mg/kg
38-76 49 mg/kg
76-137 31 mg/kg
M-ll
Depth (cm) Cu
0-38 50 mg/kg
38-76 81 mg/kg
76-114 100 mg/kg
M-15
Depth (cm) Cu
0-38 72 mg/kg
38-84 24 mg/kg
84-160 <1.0 mg/kg
M-10
Depth (cm) Cu
0-38 68 mg/kg
38-76 19 mg/kg
76-122 1.5 mg/kg
M-12
Depth (cm) Cu
0-84 9.4 mg/kg
84-122 34 mg/kg
122-165 130 mg/kg
M-8
Depth (cm) Cu
0-38 100 mg/kg
38-76 150 mg/kg
76-137 17 mg/kg
M-16
Depth (cm) Cu
0-38 58 mg/kg
38-76 1.5 mg/kg
M-9
Depth (cm) Cu
0-41 7.0 mg/kg
41-81 4.5 mg/kg
0.25
0.50
0,75
Miles
FIGURE 4.1.8 COPPER IN CORE SAMPLES COLLECTED FROM EASTERN MUSKEGON
LAKE, OCTOBER 1999.
47
-------
M-14
Depth (cm) Pb
0-38 42mg/kg
38-76 70 mg/kg
76-114 100 mg/kg
M-13
Depth (cm) Pb
0-38 77 mg/kg
38-76 70 mg/kg
76-137 110 mg/kg
M-ll
Depth (cm) Pb
0-38 68 mg/kg
38-76 120 mg/kg
76-114 160 mg/kg
M-15
Depth (cm) Pb
0-38 160 mg/kg
38-84 48 mg/kg
84-160 1.5 mg/kg
M-10
Depth (cm) Pb
0-38 110 mg/kg
38-76 45 mg/kg
76-122 1.9 mg/kg
M-12
Depth (cm) Pb
0-84 12 mg/kg
84-122 73 mg/kg
122-165 320 mg/kg
M-8
Depth (cm) Pb
0-38 180 mg/kg
38-76 160 mg/kg
76-137 19 mg/kg
M-16
Depth (cm) Pb
0-38 140 mg/kg
38-76 4.6 ma/ka
M-9
Depth (cm) Pb
0-41 7.5 mg/kg
41-81 10 mg/kg
0.25
0.50
0,75
Miles
FIGURE 4.1.9 LEAD IN CORE SAMPLES COLLECTED FROM EASTERN MUSKEGON
LAKE, OCTOBER 1999.
48
-------
M-14
Depth (cm) PAH
0-38 <1.0mg/kg
38-76 <1.0mg/kg
76-114 <1.0mg/kg
M-13
Depth (cm) PAH
0-38 <1.0mg/kg
38-76 <1.0mg/kg
76-137 <1.0mg/kg
M-ll
Depth (cm) PAH
0-38 <1.0mg/kg
38-76 <1.0mg/kg
76-114 <1.0mg/kg
M
Depth (cm)
0-38 •
38-84 <
84-160 <
-15
PAH
:1.0mg/kg
l.Omg/kg
l.Omg/kg
M-10
Depth (cm) PAH
0-38 7.6 mg/kg
38-76 1.6 mg/kg
76-122 <1.0 mg/kg
M-12
Depth (cm) PAH
0-84 <1.0 mg/kg
84-122 <1.0 mg/kg
122-165 1.4 mg/kg
M
Depth (cm)
0-38 <
38-76 <
76-137 <
PAH
l.Omg/kg
l.Omg/kg
l.Omg/kg
M-16
Depth (cm) PAH
0-38 3320 mg/kg
38-76 41.6ma/k2
M-9
Depth (cm) PAH
0-41 <1.0mg/k
41-81 <1.0mg/k
0.25
0.50
0,75
Miles
FIGURE 4.1.10 TOTAL PAH COMPOUNDS IN CORE SAMPLES COLLECTED FROM
EASTERN MUSKEGON LAKE, OCTOBER 1999.
49
-------
the remaining cores. Cores collected between the inlet of Ryerson Creek and the south branch
of the Muskegon River had higher levels of metals in the deeper strata. This area was subject
to the recent influx of sand from the Muskegon River (Rediske 2000) and from erosion along
Ryerson Creek. Sources at these locations include the abandoned Teledyne Foundry, a
historic landfill, and a metal scrap yard. A second type of deposition pattern was observed in
the cores collected at M-8, M-10, and M-15. At these locations, the highest concentrations of
chromium and lead were observed in the top 40 cm. Higher levels of cadmium and copper
were noted in the 40-80 cm section. Since most of the industrial activity occurred prior to the
1970s, sediment resuspension and advection are major influences in the eastern section of the
lake.
The third pattern of deposition was related to the distribution of PAH compounds. A
concentrated and localized source of PAH compounds was found at M-16 (Fig 4.1.10).
Total PAH compounds in excess of 3,000 mg/kg were found in the top 30 cm of the sediment
core. Concentrations were reduced to 41.6 mg/kg in the second 30 cm section. The
migration of these compounds was not noted in the down stream cores (M-15 and M-8). The
presence of significant levels of PAH compounds in a near surface zone is suggestive of a
groundwater source entering the lake or a deposit of contaminated materials from historic
dredging/filling operations. A Manufactured Gas facility, coal yards, commercial shipping
docks, and a foundry all operated in this area for over 80 years and may be the logical source
of this material. Lower concentrations of PAH compounds also were detected in the top and
middle 30 cm sections at M-10 and bottom 120-160 cm section at M-12. These locations are
near the historic Lakey/Teledyne foundry complex and may also be the result of groundwater
influx. In consideration of the high levels found at M-16, an additional investigation of
sediment contamination is recommended in this area.
The results of all the core sections for cadmium, chromium, lead, copper, and PAH
compounds are shown in Figures 4.1.11, 4.1.12, 4.1.13, 4.1.14, and 4.1.15, respectively.
Cadmium in excess of 5 mg/kg was found in the top sections of cores collected at M-l, M-8,
M-10, and M-16 (Fig 4.1.11). The highest cadmium concentration was found at M-l, which
was located in the depositional area down stream from Ruddiman Creek. A similar level of 11
mg/kg was also found near the Division Street Outfall at M-8. Although surface
contamination with cadmium was not noted at M-12, this location had the highest
concentration of all stations in the bottom core section (8 mg/kg). Chromium (Fig 4.1.12)
followed a similar distribution with the highest concentrations being detected at M-l and M-8
(440 mg/kg and 290 mg/kg, respectively). Significant enrichment of chromium was noted
only in the bottom core section at M-12 (210 mg/kg).
Copper and lead (Figs 4.1.13 and 4.1.14) followed a different distribution pattern as the
highest concentration of both elements was observed in the bottom core section at M-12 (130
mg/kg and 320 mg/kg, respectively). Station M-8 contained the highest concentration of both
metals (100 mg/kg and 180 mg/kg) followed by M-l (85 mg/kg and 150 mg/kg).
Contamination with PAH (Fig 4.1.15) compounds was limited to only 4 locations with the
highest concentrations found at M-16. While diffuse sources such as stormwater runoff and
50
-------
Cadmium in Top Core Sections
14-/
D)
_§
C
o
I
I
o
O
M- 1 M-3 M-4 M- 8 M-9 M-l 0 M-l 1 M-l 2 M-l 3 M-l 4 M-l 5 M-l 6
Station
Cadmium in Middle Core Sections
14-.
12
c
o
M-l M-3 M-4 M-8 M-9 M-l 0 M-l 1 M-l 2 M-l 3 M-l 4 M-l 5 M-l 6
Station
Cadmium in Bottom Core Sections
M-l M-3 M-8 M-10 M-ll M-12 M-13 M-14 M-l 5
Station
FIGURE 4.1.11 TOTAL CADMIUM IN CORE SAMPLES COLLECTED FROM MUSKEGON
LAKE, OCTOBER 1999. (AVERAGE DEPTHS: TOP SECTION 0-38 CM, MIDDLE SECTION 38-
76 CM, BOTTOM SECTION > 76 CM. DEPTHS GIVEN IN TABLE 4.1.2.)
51
-------
Chromium in Top Core Sections
-1 M-3 M-4 M- 8 M-9 M - 1 0 M - 1 1 M - 1 2 M - 1 3 M-1 4 M - 1 5 M-1 6
Station
Chromium in Middle Core Sections
M-l M-3 M-4 M-
M-9 M-10 M-l 1 M-12 M-13 M-14 M-15 M-16
Station
Chromium in Bottom Core Sections
M-3 M-8 M-10 M-ll M-12 M-13 M-14 M-15
FIGURE 4.1.12 TOTAL CHROMIUM IN CORE SAMPLES COLLECTED FROM MUSKEGON LAKE,
OCTOBER 1999. (AVERAGE DEPTHS: TOP SECTION 0-38 CM, MIDDLE SECTION 38-76 CM,
BOTTOM SECTION > 76 CM. DEPTHS GIVEN IN TABLE 4.1.2.)
52
-------
Lead in Top Core Sections
O
O
-1 M-3 M-4 M- 8 M-9 M-1 0 M-1 1 M-1 2 M-1 3 M-1 4 M-1 5 M-1 6
Station
Lead in Middle Core Sections
240 -
200 -
160 -
120 -
M-l M-3 M-4 M-8 M-9 M-1 0 M-1 1 M-1 2 M-1 3 M-1 4 M-1 5 M-1 6
Station
Lead in Bottom Core Sections
320 -,
280 -
—. 240 -
O)
^
1> 200-
o 160-
•e 120 -
O
O
M-3 M-8 M-10 M-ll M-12 M-13 M-14 M-15
Station
FIGURE 4.1.13 TOTAL LEAD IN CORE SAMPLES COLLECTED FROM MUSKEGON LAKE,
OCTOBER 1999. (AVERAGE DEPTHS: TOP SECTION 0-38 CM, MIDDLE SECTION 38-76 CM,
BOTTOM SECTION > 76 CM. DEPTHS GIVEN IN TABLE 4.1.2.)
53
-------
Copper in Top Core Sections
o
O
li- I M-3 M-4 M- 8 M-9 M-1 0 M-1 1 M-1 2 M-1 3 M-1 4 M-1 5 M-1 6
Station
Copper in Middle Core Sections
o
O
M-l M-3 M-4 M-8 M-9 M-1 0 M-1 1 M-1 2 M-1 3 M-1 4 M-1 5 M-1 6
Station
Copper in Bottom Core Sections
o
O
Station
FIGURE 4.1.14 TOTAL COPPER IN CORE SAMPLES COLLECTED FROM MUSKEGON LAKE,
OCTOBER 1999. (AVERAGE DEPTHS: TOP SECTION 0-38 CM, MIDDLE SECTION 38-76 CM,
BOTTOM SECTION > 76 CM. DEPTHS GIVEN IN TABLE 4.1.2.)
54
-------
Total PAHs in Top Core Sections
Total PAH mg/kg
81
7
6
5
4-
3
2-
1 -
1*1
/
/
/
"
'
*s
'
1
1
M-1 M-3 M-4 M-8 M-9 M- M- M- M- M- M-
10 11 12 13 14 15
Station
3000 -
=? 2500-
CD
^ 2000
I
J 1500-
3 1 000 -
H 500-
:•: :-.•.
•"^
',,,,:
M-16A
Station
Total PAH in Middle Core Sections
Total PAH mg/kg
451
40-
35
30-
25
20-
15-
10-
5-
o
^^< m*>-*r €S» •-•*•* -** s-r-'^r-'-w^-.
•^
^
M-1 M-3 M-8 M-10 M-11 M-12 M-13 M-14 M-15 M-16A
Station
Total PAH in Bottom Core Sections
1.4-,
1.2-
» 1
|> 0.8
< 0.6
I 0.4
0.2
0
x^^
x^^
x^^
x^^
^.faSSSiSSBi^^
^_
Kl
^_
gg^SP^^^g^^,,^
M-1 M-3 M-4 M-8 M-9 M-10 M-11 M-12 M-13 M-14 M-15
Station
FIGURE 4.1.15 TOTAL PAH COMPOUNDS IN CORE SAMPLES COLLECTED FROM
MUSKEGON LAKE, OCTOBER 1999. (AVERAGE DEPTHS: TOP SECTION 0-38 CM, MIDDLE
SECTION 38-76 CM, BOTTOM SECTION > 76 CM. DEPTHS GIVEN IN TABLE 4.1.2.)
55
-------
releases from shipping can account for the presence of PAH compounds in sediment, the
result of this type of activity would reflect a more broad distribution of contamination. When
high levels of contaminants are located adjacent to known sources of anthropogenic activity,
the sediment contamination may be linked to the venting of contaminated groundwater,
erosion of contaminated soils, and/or dredging/filling operations.
The spatial distribution of contaminants in the PONAR samples is given in Figures 4.1.16-
4.1.19. Since the PONAR collects samples from the biologically active zone of 0-20 cm, the
results can be compared to sediment quality guidelines to evaluate ecological effects. For this
purpose, levels exceeding the Probable Effect Concentrations (PECs) (MacDonald et al.
2000) are listed in bold print. PECs are consensus based guidelines that indicate a >75%
probability that adverse ecological effects may be observed when the concentrations are
exceeded. PEC concentrations and the stations where exceedences are observed are itemized
TABLE 4.1.6 SUMMARY OF PONAR SAMPLING LOCATIONS IN MUSKEGON LAKE THAT
EXCEED CONSENSUS BASED PEC GUIDELINES (MACDONALD ET AL. 2000).
„ . Consensus-Based PEC Location in Muskegon that
Contaminant °
mg/kg Exceed the PEC
Arsenic 33.0 None
Cadmium 4.98 M-5 and M-6
Chromium 111 M-1, M-5 M-6, M-7, and M-8
Copper 149 M-5 and M-6
Lead 128 M-5 M-6, and M-7
Mercury 1.06 M-5 and M-6
Nickel 48.6 None
Zinc 459 M-5 and M-6
Total PAH Compounds 22.9 M-16
in Table 4.1.6. In the western part of Muskegon Lake (Figs 4.1.16 and 4.1.17), only
chromium at M-l (250 mg/kg) exceeds the PEC of 111 mg/kg. In contrast, a number of
locations exceeded PEC guidelines in the eastern section of the lake (4.1.18 and 4.1.19).
Stations M-5 and M-6 had concentrations of chromium, mercury, cadmium, lead, copper, and
zinc that exceeded PEC guidelines. Lead and chromium at M-7 also exceeded the PECs. The
only station with total PAH compounds above the PEC guideline was M-16.
Figures 4.1.20-4.1.22 provide a relative comparison of metals and PAH compounds in the
PONAR samples. The Division Street Outfall area (M-5, M-6, M-7, and M-8) contains the
highest concentrations of most elements and exceeds the PEC guidelines with the greatest
frequency. The Ruddiman Creek area ranks second with respect to heavy metal
contamination; however only exceeds the PEC guideline for chromium. Levels of heavy
metals in the foundry area were similar in concentration to the remaining stations and did not
56
-------
M-
Metal
Cr
Cu
Cd
o
Cone.
71 mg/kg
5
2 mg/kg
2.0 mg/kg
M-l
Metal Cone.
Cr 250 mg/kg
Cu 63 mg/kg
Cd 3.9 mg/kg
M-4
Metal Cone.
Cr 4.8 mg/kg
Cu 4.0 mg/kg
Cd 0.13 mg/kg
0.25
0.50
0,75
Miles
FIGURE 4.1.16 CHROMIUM, COPPER, AND CADMIUM IN PONAR SAMPLES COLLECTED
FROM EASTERN MUSKEGON LAKE, OCTOBER 1999. BOLD VALUES EXCEED
PROBABLE EFFECT CONCENTRATIONS (PECS).
57
-------
# /
4 _rp /
/t£|
V. ^s=i:>-''^'^^>
M-l
Metal Cone.
Pb 120mg/kg
Hg 0.38 mg/kg
PAH < 1.0 mg/kg
\
V}
-------
M-14
Metal Cone
Cr 30 mg,
Cu 33 mg,
Cd l.lmg/k
M-13
Metal Cone.
Cr 80 mg/kg
Cu 39 mg/kg
Cd 3.1 mg/kg
M-15
Metal Cone.
Cr 68 mg/kg
Cu 46 mg/kg
Cd 2.5 mg/kg
M-10
Metal Cone.
Cr 77 mg/kg
Cu 58 mg/kg
Cd 2.9 mg/kg
M-12
Metal Cone.
Cr 2.8 mg/kg
Cu 3.4 mg/kg
Cd 0.1 mg/kg
M-8
Metal Cone.
Cr 120 mg/kg
Cu 78 mg/kg
Cd 4.2 mg/kg
M-16
Metal Cone.
Cr 20 mg/kg
16 mg/kg
1.3 mg/kg
M-9
Metal Cone.
Cr 9.6 mg/kg
Cu 6.8 mg/kg
Cd 0.38 mg/kg
M-5
Metal Cone.
Cr 210 mg/kg
Cu 260 mg/kg
Cd 12 mg/kg
M-7
Metal Cone.
Cr 120 mg/kg
Cu 100 mg/kg
Cd 4.2 mg/kg
M-6
Metal
Cr
Cu
Cd
Cone.
160 mg/kg
260 mg/kg
7.9 mg/kg
0,75
Miles
FIGURE 4.1.18 CHROMIUM, COPPER, AND CADMIUM IN PONAR SAMPLES COLLECTED
FROM WESTERN MUSKEGON LAKE, OCTOBER 1999. BOLD VALUES EXCEED
PROBABLE EFFECT CONCENTRATIONS (PECS).
59
-------
M-15
Metal
Pb
Hg
PAH
Cone.
64 mg/kg
0.26 mg/kg
<1.0 mg/kg
ML-14
Metal Cone.
Pb 31 mg/kg
Hg 0.14 mg/kg
PAH <1.0 mg/kg
ML-13
Metal Cone.
Pb 63 mg/kg
Hg 0.25 mg/kg
PAH <1.0 mg/kg
M-ll
Metal Cone.
Pb 67 mg/kg
Hg 0.26 mg/kg
PAH <1.0 mg/kg
M-10
Metal Cone.
Pb 89 mg/kg
Hg 0.34 mg/kg
PAH <1.0 mg/kg
M-12
Metal Cone.
Pb 6.2 mg/kg
Hg <0.10mg/k
PAH <1.0 mg/kg
M-8
Metal Cone.
Pb 120 mg/kg
Hg 0.50 mg/kg
PAH <1.0 mg/kg
M-16
Metal Cone.
Pb 31 mg/kg
Hg 0.14 mg/kg
PAH 143 mg/kg
M-9
Metal Cone.
Pb 12 mg/kg
Hg <0.10 mg/kg
PAH l.Omg/k
M-5
Metal Cone.
Pb 270 mg/kg
Hg 1.7 mg/kg
PAH 2.7 mg/kg
M-7
Metal Cone.
Pb 140 mg/kg
Hg 0.56 mg/kg
PAH <1.0 mg/kg
M-6
Metal
Pb
Hg
PAH
Cone.
280 mg/kg
1.7 mg/kg
4.8 mg/kg
0,75
Miles
FIGURE 4.1.19 LEAD, MERCURY, AND TOTAL PAH COMPOUNDS IN PONAR SAMPLES
COLLECTED FROM WESTERN MUSKEGON LAKE, OCTOBER 1999. BOLD VALUES
EXCEED PROBABLE EFFECT CONCENTRATIONS (PECS).
60
-------
M- M- M- M- M- M- M- M- M- M- M- M- M- M- M-
1P 3P 4P 5P 6P 71P 8P 9P 10P IIP 12P 13P 14P 15P 16P
M- M- M- M- M- M- M- M- M- M- M- M- M- M- M-
1P 3P 4P 5P 6P 71P 8P 9P 10P IIP 12P 13P 14P 15P 16P
Sf
50-,
30-
10-
90-
70-
50-
30-
10-
90-
70-
50-
30-
10-
,,ffil
=
^
Mli
f" &
m
—
PEC
F| __
II B
II II
1 M liP BSP ^V
n
II
H3=JnJ=
M- M- M- M- M- M- M- M- M- M- M- M- M- M- M-
1P 3P 4P 5P 6P 71P 8P 9P 10P IIP 12P 13P 14P 15P 16P
Ruddiman
Division St.
Foundry
FIGURE 4.1.20 TOTAL ARSENIC, CADMIUM, AND CHROMIUM IN PONAR SAMPLES
COLLECTED FROM MUSKEGON LAKE, OCTOBER 1999. PATTERNS DENOTE REGIONS OF
MUSKEGON LAKE. BOLD LINES IDENTIFY PEC LEVELS.
61
-------
240 -
200 -
"a 160 -
£
S 120 -
M- M- M- M- M- M- M- M- M- M- M- M- M- M- M-
1P 3P 4P 5P 6P 71P 8P 9P 10P IIP 12P 13P 14P 15P 16P
M- M- M- M- M- M- M- M- M- M- M- M- M- M- M-
1P 3P 4P 5P 6P 71P 8P 9P 10P IIP 12P 13P 14P 15P 16P
M- M- M- M- M- M- M- M- M- M- M- M- M- M- M-
1P 3P 4P 5P 6P 71P 8P 9P 10P IIP 12P 13P 14P 15P 16P
Station
Ruddiman
Division St.
Foundry
FIGURE 4.1.21. COPPER, LEAD, AND MERCURY IN PONAR SAMPLES COLLECTED FROM
MUSKEGON LAKE, OCTOBER 1999. PATTERNS DENOTE REGIONS OF MUSKEGON LAKE.
BOLD LINES IDENTIFY PEC LEVELS.
62
-------
"5k
150-
140 -f
130-
120-
iio-T
100-
90-
80-
70-
60-
50-'
40-'
30-
20-
M-1P M-3P M-4P M-5P M-6P M-7P M-8P M-8PD M-9P M-10P M-11P M-12P M-13P M-14P M-15P M-
16AP
Station
FIGURE 4.1.22. TOTAL PAH COMPOUNDS IN PONAR SAMPLES COLLECTED FROM
MUSKEGON LAKE, OCTOBER 1999. BOLD LINES IDENTIFY PEC LEVELS.
exceed PEC guidelines. The station down gradient from the former lakeshore industrial area
(M-16) was the only location to exceed the PEC for total PAH compounds. The sediment
concentration of total PAH compounds at this location was 143 mg/kg compared to the PEC
of 22.9 mg/kg. PAH compounds were also found at the Division Street Outfall locations M-5
and M-6 (2.7 mg/kg and 4.8 mg/kg, respectively).
In summary, the core show that heavy metal contamination is present in the 0-80 cm zone at
most stations. The only core samples with significant levels of heavy metals at > 80 cm were
near the former Teledyne foundry and near the confluence of Ruddiman Creek. High levels of
PAH compounds were found in only one location that was located downgradient from the
former lakeshore industrial area. Near surface zone sediments in the Division Street Outfall
were contaminated with a variety of heavy metals at concentrations above the PEC guidelines.
PEC guidelines for total PAH compounds were exceeded at the location downgradient from
the former lakeshore industrial area. The most significant area of sediment heavy metal
contamination was in the vicinity of the Division Street Outfall. The deposition basin down
stream from Ruddiman Creek ranked second with respect to heavy metal enrichment.
63
-------
4.2. Stratigraphy and Radiodating
Three cores were collected for radiodating and the analysis of detailed stratigraphy for
chromium and lead. The first core (M-1S) was collected at station M-l and would reflect
contributions from Ruddiman Creek and the general westerly movement of sediment in
Muskegon Lake. The second core (M-2S) was collected at the deepest location in Muskegon
Lake and would provide an indication of sediment movement from the industrialized shoreline
located to the east. The final core (M-5S) was collected at station M-5 in the Division Street
Outfall area. This location would provide an indication of depositional history and sediment
stability in this heavily contaminated area. The results of each core are presented in the
following sections.
4.2.1 Core M-lS
Stratigraphy and radiodating results for M-1S are presented in Table 4.2.1. Profiles of depth
and concentration for chromium and lead are shown on Figure 4.2.1 along with the calculated
dates from the 210Pb deposition model. Chromium and lead followed different depositional
patterns. Concentrations in the top 10 cm for both elements were relatively uniform. Excess
210Pb inventories were also uniform over the same interval, indicating that some degree of
mixing occurs in this region. Below this level, two peaks in concentration were observed for
chromium. The first peak corresponds to 1988 and contained a concentration of 440 mg/kg.
The second peak corresponded to 1964 and contained 560 mg/kg. In contrast, the
stratigraphy for lead only showed one peak of 200 mg/kg in approximately 1988. Increasing
concentrations were noted for both elements beginning in the 1920s. It is interesting to note
that a catastrophic flood occurred in the Muskegon River watershed during 1986. Rainfall in
excess of the 100 year flood fell and several dam failures occurred. The presence of
depositional peaks for both elements during this time frame suggests the strong influence of
storm events on the system. Ruddiman Creek has a lagoon located near the confluence with
Muskegon Lake. A recent investigation by the U.S. Army Corps of Engineers (ACOE 2000)
found that the lagoon sediments were highly contaminated with heavy metals including
chromium and lead. Thus, the results suggest the storm event of 1986 may have mobilized
contaminated sediments from the Ruddiman Lagoon and deposited them in this region of
Muskegon Lake.
4.2.2 CoreM-2S
Stratigraphy and radiodating results for M-2S are presented in Table 4.2.2. Station M-2S is
located at the deepest point in Muskegon Lake and within the flow path of the old river
channel. Profiles of depth and concentration for chromium and lead are shown on Figure
4.2.2. This location was originally thought to be a depositional area due to its depth (70 ft).
64
-------
TABLE 4.2.1 RESULTS OF STRATIGRAPHY AND RADIODATING RESULTS FOR CORE M-1S
COLLECTED FROM MUSKEGON LAKE, MARCH 2000.
iepth
cm)
2
4
6
8
10
12
14
16
18
20
22
24
26
28
30
32
34
36
38
40
42
44
46
48
50
52
54
56
58
60
62
64
Total
Chromium
mg/kg
141
108
123
123
131
170
220
440
260
220
380
380
480
420
440
400
560
460
98
72
58
48
52
62
64
60
76
46
42
10
8
11
Total
Lead
mg/kg
125
110
113
120
125
168
175
200
150
95
120
120
140
120
120
100
130
110
48
33
39
32
29
32
29
33
29
20
20
9
9
10
Total Pb-
210
22.548
23.607
25.890
23.139
20.603
20.801
19.510
17.851
17.037
16.293
9.951
8.000
7.877
7.353
5.360
4.107
Ra-226
Activity
(dpm/g)
3.935
4.518
6.107
5.297
3.981
4.668
4.256
3.281
3.053
2.994
2.430
2.222
2.596
2.354
2.583
2.643
Cs-137
Activity
(dpm/g)
1.841
1.337
1.601
1.600
1.592
1.483
1.762
3.321
8.406
4.567
2.995
1.926
1.860
2.196
1.584
1.231
Excess
Pb-210
18.613
19.089
19.783
17.842
16.622
16.133
15.254
14.570
13.983
13.299
7.521
5.778
5.281
4.999
2.777
1.465
Date at
Depth
1998
1996
1992
1988
1984
1979
1974
1968
1962
1954
1947
1941
1935
1925
1917
1912
65
-------
100
Chromium mg/kg
200 300 400 500 600
50
Lead mg/kg
100 150
200
250
10
U
|
Q
30
50
60
20
u
.c
'S.
Q
40
60
Date
1998
1996
1992
1988
1984
1979
1974
1968
1962
1954
1947
1941
1935
1925
1917
FIGURE 4.2.1 DEPTH AND CONCENTRATION PROFILES FOR CHROMIUM AND LEAD AT STATION M-1S, MUSKEGON LAKE,
MARCH 2000. SEDIMENT DATES CALCULATED BY RADIODATING WITH Pe-210
66
-------
TABLE 4.2.2 RESULTS OF STRATIGRAPHY AND RADIODATING RESULTS FOR CORE M-2S
COLLECTED FROM MUSKEGON LAKE, MARCH 2000.
DEPTH
cm
0-4
4-8
8-12
12-16
16-20
20-24
24-28
28-32
32-36
36-40
40-44
44-48
48-52
52-56
56-60
60-64
64-68
68-72
72-76
76-80
80-84
84-88
88-92
Total
Chromium
mg/kg
52
58
52
80
98
124
130
135
155
200
250
265
285
335
330
285
380
360
325
275
235
255
315
Total Lead
mg/kg
58
62
62
87
103
128
135
140
140
135
140
135
130
130
115
95
120
115
100
105
115
125
130
Total Pb-
210
Activity
(dpm/g)
22.018
21.944
20.419
21.208
14.030
9.771
9.658
12.705
8.543
8.188
7.455
9.299
9.131
8.170
6.143
8.579
9.625
9.470
5.632
6.509
8.830
6.324
6.636
Ra-226
Activity
(dpm/g)
5.180
5.492
4.891
5.133
3.282
4.222
3.833
3.524
3.066
3.255
3.926
3.849
3.986
4.904
2.796
3.151
3.466
3.495
3.623
3.292
3.828
3.105
3.723
Cs-137
Activity
(dpm/g)
1.056
1.023
-0.067
1.364
0.915
1.583
1.434
1.628
1.236
1.178
1.886
2.284
2.265
2.595
0.101
2.740
2.512
0.433
2.768
2.368
2.086
2.176
2.775
Excess Pb-
210
Activity
(dpm/g)
16.84
16.45
15.53
16.08
10.75
5.55
5.82
9.18
5.48
4.93
3.53
5.45
5.14
3.27
3.35
5.43
6.16
5.98
2.01
3.22
5.00
3.22
2.91
67
-------
0 50 100
Chromium mg/kg
150 200 250
300 350 400
20 40
Lead mg/kg
60 80 100 120 140
160
10 -
20 -
30 -
100 J
10 -
30 -
60 -
80 -
100 J
FIGURE 4.2.2 DEPTH AND CONCENTRATION PROFILES FOR CHROMIUM AND LEAD AT STATION M-2S, MUSKEGON LAKE,
MARCH 2000.
68
-------
The radiodating results show however that stable sediments were 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 M-1S. No
exponential decay pattern is visible in core M-2S (Table 4.2.1). Instead, a mixed layer with
uniform 210Pb inventories was observed for the first 16 cm followed by a pattern of sections
with increasing and decreasing 210Pb concentrations ranging from 2.01 dpm to 6.16 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 patters of chromium and lead also have sporadic changes in
concentration indicating the influence of episodic events. Concentrations of chromium peak at
64 cm - 70 cm while lead peaks at 28 cm - 44 cm. These data suggest that that the source of
chromium is older than the source of lead. The rapidly decreasing concentrations of chromium
noted in the top 40 cm indicates that the advection and deposition of this metal has declined in
recent history. In contrast, peak lead deposition appears to occur more recently, with a
smaller peak near the base of the core. Since lead contamination may originate from both
point and nonpoint sources, the smaller peak near the bottom of the core may be related to
industrial discharges from foundry and metal finishing operations. The more recent peak of
lead deposition may be from the erosion of contaminated soils (from shoreline development)
and the use of leaded fuels. The presence of currents at M-2S plus the fact that it is located
downstream from the areas of contaminated sediments such as the Division Street Outfall
suggests that resuspension and transport mechanisms are moving contaminants to the deeper
zones of Muskegon Lake.
4.2.3 CoreM-5S
Stratigraphy and radiodating results for M-5S are presented in Table 4.2.3. Profiles of depth
and concentration for chromium and lead are shown on Figure 4.2.3 along with the calculated
dates from the 210Pb deposition model. Elevated concentrations of chromium and lead
continue beyond the estimated date of 1894, which indicates that the CRS model did not yield
credible results. The sediment layers below 30 cm from this core were fibrous in nature with
strands that appeared to resemble fiberglass. The fibrous material continued down to 90 cm.
It is likely that excessive historical inputs of waste materials diluted out the 210Pb inventory in
the deeper sections. The presence of a measurable 137Cs horizon at 18 cm indicated that the
dating of the upper sections of the core were accurate. No evidence of mixing in the upper
sediment layers was visible as the 210Pb inventories decay in the expected manner. Very high
levels of chromium (850 mg/kg) and lead (890 mg/kg) were found in the deeper sections of
the core (> 20 cm). Concentrations of both elements declined near the bottom however one
section (96 cm) contained 600 mg/kg of chromium. This section appeared to have some
metallic particles mixed with the sediment. Surficial sediments were contaminated above PEC
levels for chromium and lead. This core was collected in the near shore area of the bay that
contains the Division Street Outfall and may be protected from erosional forces from wave-
induced currents. Locations further from shore and in the marina area may be subject to
advection from boat traffic and currents.
69
-------
TABLE 4.2.3 RESULTS OF STRATIGRAPHY AND RADIODATING RESULTS FOR CORE M-5S
COLLECTED FROM MUSKEGON LAKE, MARCH 2001.
DEPTH cm
2
4
6
8
10
12
14
16
18
20
22
24
26
28
30
32
34
36
38
40
42
44
46
48
50
52
54
56
58
60
62
64
66
68
70
72
74
76
78
80
82
84
86
88
90
92
94
96
98
100
Total Lead
mg/kg
330
330
410
490
500
540
570
640
720
680
660
780
500
540
540
620
590
580
560
620
750
770
720
750
780
890
770
820
830
680
510
450
350
280
260
230
220
200
190
160
135
1 11
99
88
53
41
42
33
32
30
Total
Chrom ium
mg/kg
1 10
1 10
130
170
160
180
210
670
850
680
660
480
360
200
210
130
270
250
260
260
280
220
190
200
190
200
160
180
210
120
150
140
1 10
150
1 10
96
1 10
100
82
89
95
1 10
100
130
120
130
200
600
120
89
Total Pb-
21 0 Activity
(dpm/g)
26.472
19.997
16.288
1 1.395
1 1.640
10.049
9.832
7.205
7.972
4.815
5.870
7.564
6.845
4.929
4.222
3.61 1
5.967
5.721
5.198
6.291
6.308
5.245
6.051
3.741
6.699
8.922
5.497
2.352
6.181
3.538
3.191
5.833
3.863
5.148
4.643
4.870
3.847
Ra-226
Activity
(dpm/g)
2.547
1.797
2.340
2.529
1.962
2.384
2.572
2.359
2.992
2.980
2.339
2.612
2.169
2.612
2.614
2.090
2.342
1.839
2.187
2.040
2.205
2.737
2.272
3.260
3.326
3.093
3.514
2.890
2.446
2.737
2.637
3.869
2.526
2.856
2.888
2.469
2.869
Cs-137
Activity
(dpm/g)
1.128
0.992
1.988
1.438
2.116
1.992
4.178
8.801
10.080
5.181
3.576
2.070
1.770
2.055
2.203
2.384
2.904
2.261
2.466
2.239
1.932
2.209
1.759
1.037
0.851
0.759
0.305
-0.025
-0.542
-0.056
-0.254
-0.175
-0.331
-0.361
-0.306
-0.055
-0.495
Excess Pb-
210
Activity
(dpm/g)
24.260
17.667
13.890
8.904
9.160
7.538
7.319
4.637
5.422
2.198
3.277
5.012
4.279
2.318
1.595
0.970
3.385
3.133
2.598
3.721
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
Date at
G iven
Depth
2000
1996
1991
1986
1981
1977
1971
1966
1960
1958
1954
1947
1940
1935
1932
1930
1922
1910
1894
70
-------
0 100 200
Chromium mg/kg
300 400 500 600
700 800 900
Lead mg/kg
400 600
20 -
30 -
s.
at
Q
50 -
60 -
80 -
90 -
30 -
70 -
FIGURE 4.2.3 DEPTH AND CONCENTRATION PROFILES FOR CHROMIUM AND LEAD AT STATION M-5S, MUSKEGON LAKE,
MARCH 2001.
71
-------
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. Ruddiman Creek appeared to have a significant influence
on the deposition of heavy metals in the southwestern part of Muskegon Lake. A peak in
metals deposition was found that corresponded to the 100+ year flood that occurred in 1986.
The historical deposition was considerably higher than current rates. The deep zone off the
Car Ferry Dock was not found to be an area that accumulates sediments. High inventories of
210Pb were found near the bottom of the 80 cm core, indicating active mixing and movement
of sediments. The presence of elevated metals in the deeper strata plus the high 210Pb
inventories suggests that contaminated sediments are moved from the eastern part of
Muskegon Lake to this location where they are mixed and made available for resuspension by
the currents along the old river channel. The core from the Division Street Outfall showed
relatively stable sediments in the top 20 cm followed by a zone of heavy accumulation after
1960. Based on these results it is apparent that the removal of contaminated sediments from
Ruddiman Creek and the lagoon would reduce the loading of heavy metals to western
Muskegon Lake. The areas of high sediment contamination in the eastern part of the lake also
appear to be mixed and subject to transport.
72
-------
4.3 Toxicity Testing Results
The toxicity evaluations of the Muskegon Lake sediments were performed during November
1999. Grab sediment samples collected from 14 different sites (14 samples with one
additional field duplicate) were evaluated using the EPA (1994) solid phase testing protocol
with Hyalella azteca and Chironomus tentans.
Conductivity, hardness, alkalinity, ammonia, and pH were determined on 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 (M-15P) treatments exceeded the required 80%. Un-transformed
survival data were evaluated to determine whether they were consistent with data from a
normal distribution with a mean and standard deviation equal to the sample 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 was 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 M-15P in 3 out of 15 sediments. Sediments from site M-5P, M-6P and M-
16AP had significantly reduced survival compared to M-15P. Based on amphipod mortality,
station M-16AP had the highest mortality followed in decreasing order by M-5P, M-6P, and
M-12P. All remaining stations had amphipod survival > 80%.
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 (M-15P) exceeded the required 70%. Un-
transformed survival data were evaluated as described above with the Chi-Squared
distribution. The sample data was 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 of M-16P compared to the control. Only 25 % survival
was observed at this location. Chironomus tentans growth data is presented in Table 4.3.2.3.
Un-transformed growth data were found to be consistent with a Chi-Squared distribution at
73
-------
TABLE 4.3.1.1 SUMMARY OF HYALELLA AZTECA SURVIVAL DATA OBTAINED DURING
THE 10 DAY TOXICITY TEST WITH MUSKEGON LAKE SEDIMENTS.
Sample
M-l
M-3
M-4
M-5
M-6
M-7
M-8
M-8D
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
MIN
7
8
8
5
5
6
7
7
9
7
7
4
7
7
7
3
MAX
10
9
10
7
8
10
10
9
10
10
10
9
10
10
10
7
MEAN
8.375
8.375
9.375
6.000
6.500
8.000
8.625
8.375
9.375
8.375
8.375
7.375
8.375
8.250
8.375
4.500
Survival
VARIANCE
1.6964
1.125
0.2679
0.5536
0.5714
1.1429
1.7143
0.5714
0.2679
1.1250
1.1250
2.5536
0.8393
1.3571
1.6964
1.4286
SD
1.3025
1.0607
0.5175
0.7440
0.7559
1.0690
1.3093
0.7559
0.5175
.0607
.0607
.5980
0.9161
.1650
.3025
.1952
C.V. %
15.55
12.67
5.52
12.40
11.63
13.36
15.18
9.03
5.52
12.67
12.67
21.67
10.94
14.12
15.55
26.56
TABLE 4.3.1.2 SUMMARY OF DUNNETT'S TEST ANALYSIS OF HYALELLA AZTECA
SURVIVAL FOR THE 10 DAY TOXICITY TEST WITH MUSKEGON LAKE SEDIMENTS.
ID
M-l
M-3
M-4
M-5
M-6
M-7
M-8
M-8D
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
TRANS
MEAN
8.3750
8.3750
9.3750
6.0000
6.5000
8.0000
8.6250
8.0000
9.3750
8.3750
8.3750
7.3750
8.3750
8.2500
8.3750
4.5000
ORIGINAL
MEAN
8.3750
8.3750
9.3750
6.0000
6.5000
8.0000
8.6250
8.0000
9.3750
8.3750
8.3750
7.3750
8.3750
8.2500
8.3750
4.5000
TSTAT
0.0000
0.0000
-2.0735
4.9246
3.8878
0.7776
-0.5184
1.1047
-2.0735
0.0000
0.0000
2.1330
0.0000
0.2041
6.3278
SIG
0.05
*
*
*
Dunnett's critical value = 2.4800. 1 Tailed, alpha = 0.05.
74
-------
TABLE 4.3.2.1 SUMMARY OF CHIRONOMUS TENTANS SURVIVAL DATA OBTAINED DURING
THE 10 DAY TOXICITY TEST WITH MUSKEGON LAKE SEDIMENTS.
Sample
M-l
M-3
M-4
M-5
M-6
M-7
M-8
M-8D
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
8
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
MIN
7
7
8
5
6
7
8
7
9
7
8
6
7
7
7
1
MAX
9
10
10
9
9
10
10
9
10
10
9
8
9
10
10
4
MEAN
8.3750
8.3750
9.4286
7.7500
7.7500
8.0000
8.6250
8.0000
9.3750
8.3750
8.3750
8.0000
8.3750
8.2500
8.3750
2.5000
Survival
VARIANCE
1.4107
1.4107
0.2679
2.7857
1.6429
2.0000
0.5536
0.5714
0.2679
1.1250
1.1250
1.4286
1.1250
0.5000
0.5536
1.1429
SD
.1877
.1877
0.5175
.6690
.2817
.4142
0.7440
0.7559
0.5175
.0607
.0607
.0607
.1952
.0607
0.7440
1.0690
c.v. %
14.18
14.18
5.49
21.54
16.54
17.68
8.63
9.45
5.52
12.67
12.67
13.26
14.27
12.86
8.88
42.76
TABLE 4.3.2.2 SUMMARY OF DUNNETT'S TEST ANALYSIS OF SURVIVAL DATA
CHIRONOMUS TENTANS OBTAINED DURING THE 10 DAY TOXICITY TEST WITH
MUSKEGON LAKE SEDIMENTS.
ID
M-l
M-3
M-4
M-5
M-6
M-7
M-8
M-8D
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
TRANS
MEAN
8.3750
8.3750
9.4286
7.7500
7.7500
8.0000
8.6250
8.0000
9.3750
8.3750
8.3750
8.0000
8.3750
8.2500
8.3750
2.5000
ORIGINAL
MEAN
8.3750
8.3750
9.4286
7.7500
7.7500
8.0000
8.6250
8.0000
9.3750
8.3750
8.3750
8.0000
8.3750
8.2500
8.3750
2.5000
TSTAT
0.0000
0.0000
-1.0000
0.6250
0.6250
1.3750
-0.2500
0.7579
-1.2846
0.0000
0.0000
0.7579
0.0000
0.2526
11.8743
SIG
0.05
*
Dunnett's critical value = 2.4800. 1 Tailed, alpha = 0.05
75
-------
TABLE 4.3.2.3 SUMMARY OF CHIRONOMUS TENTANS DRY WEIGHT DATA OBTAINED
DURING THE 10 DAY TOXICITY TEST WITH MUSKEGON LAKE SEDIMENTS.
Sample
ID
M-1
M-3
M-4
M-5
M-6
M-7
M-8
M-8D
Rep
a
h
c
d
e
f
a
h
a
h
c
d
e
f
a
h
a
h
c
d
e
f
a
h
a
b
c
d
e
f
a
h
a
h
c
d
e
f
a
h
a
h
c
d
e
f
a
h
a
h
c
d
e
f
a
h
a
h
c
d
e
f
a
h
PanWt
(0)
0.9884
09883
0.9888
0.9977
09989
0.9994
0.9995
09994
0.9928
0.9964
1.0024
09957
0.9972
0.9993
09960
0.9974
1.0106
1.0083
1.0028
1.0132
1.0091
1.0130
1.0106
1.0112
09996
0.9898
0.9898
0.9970
09961
0.9966
1.0080
0.9974
0.9973
0.9928
1.0101
1.0036
1.0036
09938
1.0062
0.9953
1.0158
1.0085
1.0092
1.0037
1.0027
1.0027
0.9981
0.9910
1.0225
1.0155
1.0165
1.0083
1.0037
1.0022
1.0151
1.0087
1.0037
0.9789
0.9879
0.9883
0.9868
1.0039
1.0069
1.0020
Pan + Sample
Drv Wt (g)
09955
09982
0.9973
1.0071
1.0048
1.0082
1.0075
1.0093
1.0013
1.0041
1.0112
1.0023
1.0019
1.0081
1.0053
1.0063
1.0211
1.0167
1.0126
1.0225
1.0162
1.0202
1.0180
1.0200
1.0104
1.0002
0.9986
1.0070
1.0016
1.0029
1.0152
1.0048
1.0053
1.0010
1.0220
1.0100
1.0092
1.0033
1.0144
1.0011
1.0260
1.0155
1.0174
1.0096
1.0166
1.0092
1.0069
1.0006
1.0317
1.0223
1.0231
1.0149
1.0132
1.0116
1.0252
1.0174
1.0130
0.9891
09994
0.9962
0.9949
1.0119
1.0158
1.0102
Sample
Drv Wt (g)
0.0071
0.0099
0.0085
0.0094
0.0059
0.0088
0.008
0.0099
0.0085
0.0077
0.0088
00066
0.0047
0.0088
0.0093
0.0089
0.0105
0.0084
0.0098
0.0093
0.0071
0.0072
0.0074
0.0088
0.0108
0.0104
0.0088
0.01
0.0055
0.0063
0.0072
0.0074
0.0080
0.0082
0.0119
0.0064
0.0056
0.0095
0.0082
0.0058
0.0102
0.0070
0.0082
0.0059
0.0139
0.0065
0.0088
0.0096
0.0092
0.0068
0.0066
00066
0.0095
0.0094
0.0101
0.0087
0.0093
0.0102
0.0115
0.0079
0.0081
0.0080
0.0089
0.0082
# Survivors
10
8
8
10
9
8
7
7
10
9
8
6
8
9
8
9
9
10
9
9
10
9
9
8
7
9
8
6
10
5
9
8
7
6
8
6
9
9
9
7
9
10
7
7
9
7
6
9
10
8
8
8
9
9
8
9
9
10
9
9
9
10
10
9
Mean wt (mg)
per survivor
0.7100
1.2375
1.0625
0.9400
0.6556
1.1000
1.1429
1.4143
0.8500
0.8556
1.1000
1.1000
0.5875
0.9778
1.1625
0.9889
1.1667
0.8400
1.0889
1.0333
0.7100
0.8000
0.8222
1.1000
1.5429
1.1556
1.1000
1.6667
0.5500
1.2600
0.8000
0.9250
1.1429
1.3667
1.4875
1.0667
0.6222
1.0556
0.9111
0.8286
1.1333
0.7000
1.1714
0.8429
1.5444
0.9286
1.4667
1.0667
0.9200
0.8500
0.8250
0.8250
1.0556
1.0444
1.2625
0.9667
1.0333
1.0200
1.2778
0.8778
0.9000
0.8000
0.8900
0.9111
Sample
Mean
1.033
0.953
0.945
1.125
1.060
1.107
0.969
0.964
Sample
Std Dev
0.2564
0.1862
0.1707
0.3711
0.2806
0.2914
0.1499
0.1479
76
-------
TABLE 4.3.2.3 (CONTINUED) SUMMARY OF CHIRONOMUS TENTANS DRY WEIGHT DATA
OBTAINED DURING THE 10 DAY TOXICITY TEST WITH MUSKEGON LAKE SEDIMENTS.
Sample
ID
M-9
M-10
M-11
M-12
M-13
M-14
M-15
M-16
Rep
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
a
h
c
r|
e
f
a
h
PanWt
(at
1 005
0.999
1.000
0999
1 006
0.994
0.996
0998
0998
0.997
0.995
0996
1 000
0.994
0.998
0999
0998
0.997
0.992
1 001
1 000
1.001
0.996
1 000
0996
0.998
0.997
0994
0992
0.995
0.995
0996
1 000
1.001
1.001
0997
1 000
0.995
0.995
0983
1 003
0.999
1.004
1 003
1 003
1.001
0999
0991
0997
0.999
0.996
0999
0998
0.998
1.018
1 006
1 013
1.007
1.006
1 005
1 013
1.000
1.008
1 004
Pan + Sample
Dry Wt (at
1 0141
1.0086
1.0088
1 0063
1 0148
1.0000
1.0081
1 0058
1 0068
1.0008
1.0052
1 0061
1 0042
1.0043
1.0079
1 0031
1 0067
1.0052
1.0065
1 0068
1 0067
1.0083
1.0036
1 0076
1 0065
1.0070
1.0026
09986
1 0080
1.0020
1.0018
1 0025
1 0050
1 0104
1.0057
1 0040
1 0071
1.0011
1.0022
09915
1 0081
1.0062
1.0116
1 0091
1 0130
1.0102
1.0058
09995
1 0040
1.0062
1.0020
1 0119
1 0092
1.0050
1.0253
1 0128
1 0141
1.0086
1.0088
1 0063
1 0148
1.0000
1.0081
1 0058
Sample
Dry Wt (a)
00092
0.0101
0.0090
00069
00085
0.0059
0.0117
00082
00086
0.0040
0.0103
00106
00046
0.0103
0.0102
00045
00084
0.0084
0.0149
00061
00063
0.0069
0.0073
00076
00110
0.0093
0.0056
00050
00162
0.0069
0.0068
00065
00051
0.0094
0.0049
00075
00074
0.0058
0.0068
00082
00054
0.0068
0.0079
00063
00101
0.0096
0.0067
00084
00068
0.0074
0.0059
00134
00110
0.0075
0.0069
00071
00012
0.0017
0.0029
00017
00015
0.0003
0.0006
00019
# Survivors
9
10
10
9
9
9
9
10
9
10
9
8
7
9
8
7
7
8
8
7
9
9
9
10
8
7
8
8
6
9
8
10
9
7
8
9
8
9
8
9
9
7
8
9
8
8
9
8
9
9
9
9
8
8
7
8
2
3
4
3
3
1
1
3
Mean wt (mq)
per survivor
1 0222
1.0100
0.9000
07667
09444
0.6556
1.3000
08200
09556
0.4000
1 1444
1 3250
06571
1.1444
1.2750
06429
1 2000
1.0500
1.8625
08714
07000
0.7667
0.8111
07600
1 3750
1.3286
0.7000
06250
27000
0.7667
0.8500
06500
05667
1.3429
0.6125
08333
09250
0.6444
0.8500
09111
06000
0.9714
0.9875
07000
1 2625
1.2000
0.7444
1 0500
07556
0.8222
0.6556
1 4889
1 3750
09375
0.9857
08875
06000
0.5667
0.7250
05667
05000
0.3000
0.6000
06333
Sample
Mean
0.927
0.943
1.003
1.124
0.836
0.939
0.988
0.561
Sample
Std Dev
0.1953
0.3389
0.3856
0.7015
0.2478
0.2386
0.2941
0.1237
77
-------
p > 0.01. Dunnett's Test (Table 4.3.2.4) showed a statistically significant (p < 0.05)
difference with the Chironomus tentans weight data for M-16 compared to the control.
Weight data for the other locations were similar to the control.
TABLE 4.3.2.4 SUMMARY OF DUNNETT'S TEST ANALYSIS OF WEIGHT DATA FOR
CHIRONOMUS TENTANS OBTAINED DURING THE 10 DAY TOXICITY TEST WITH
MUSKEGON LAKE SEDIMENTS.
ID
M-l
M-3
M-4
M-5
M-6
M-7
M-8
M-8D
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
TRANS
MEAN
1.0328
0.9528
0.9451
1.1250
1.0602
1.1067
0.9687
0.9640
0.9274
0.9430
1.0027
1.1244
0.8357
0.9394
0.9885
0.5364
ORIGINAL
MEAN
1.0328
0.9528
0.9451
1.1250
1.0602
1.1067
0.9687
0.9640
0.9274
0.9430
1.0027
1. 1244
0.8357
0.9394
0.9885
0.5364
TSTAT
-0.3370
0.2716
0.3295
-1.0373
-0.5445
-0.8982
0.1508
0.1332
0.4645
0.3453
-0.0752
-0.7194
0.8086
0.2597
2.5880
SIG
0.05
*
DUNNETT'S CRITICAL VALUE = 2.4800. 1 TAILED, ALPHA = 0.05
4.3.3 Sediment Toxicity Data Discussion
Statistically significant (p < 0.05) acute toxicity effects were observed in the sediments from
sites M-5P, M-6P, and M-16AP for the amphipod, H. azteca. In addition, statistically
significant (p < 0.05) mortality and growth were noted for the midge, C. tentans in sediment
from site M-16. Sediment from station M-16AP was toxic to both organisms and had the
highest level of total PAH compounds (143 mg/kg). Stations M-5P and M-6P had statistically
significant (p < 0.05) mortality and contained the highest levels of chromium, cadmium,
copper, lead, and zinc found in the near surface zone sediments. Concentrations of these
elements were above PEC guidelines (MacDonald et al. 2000) as shown in Table 4.1.6. The
remaining sites had levels of PAH compounds and heavy metals that did not exceed PEC
guidelines. Statistically significant mortality was not observed at these locations in the solid
phase toxicity tests for both organisms.
78
-------
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 individual replicates at selected stations were statistically analyzed
in Section 4.4.3 to determine if there were differences between locations presumably impacted
by the Division Street Outfall (M-5 through M-7) and stations influenced by the
Lakey/Teledyne Foundry complex (M-10 and M-l 1).
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 error for each station. The results for each replicate are presented in Appendix F,
Table F-l. A total of 55 taxa were identified, with an average of 10 + 2.498 taxa per station
(range 6-15, Table 4.4.1.1). The general distribution of organisms is shown in Figure 4.4.1.1.
Oligochaetes dominated the benthic macroinvertebrate assemblages at most stations. Zebra
mussels dominated the stations with sandy substrates. 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 4,649/m2 and 49,124/m2 with 12 of 15 sites having >5000
organisms/m2. Oligochaeta were the most abundant group at all but two of the sites sampled,
comprising between 2.395/m2 and 10,489/m2. Immature tubificids were 72% of the total
abundance of oligochaetes from all sampling sites; the remaining 28% included 18 positively
identified taxa (Appendix F, Table F-l). Relative oligochaete density was variable (range
12% to 87%) and exceeded 50% at 12 of the 15 sites sampled. The proportion of
oligochaetes was the lowest at sites, M-9 (26.9%) and M-12 (12.4%) where Dreissena
exceeded 15,000/m2. Three species, Aulodrilus pigueti, Limnodrilus hoffmeisteri, and
Quistadrilus multisetosus were found at most sites (Table 4.4.1). One of the more pollution
tolerant species, L. hqffmeisteri, was found at all but four sites (M-4, M-7, M-l5, and M-l6).
This oligochaete was found in lower abundances than the other two species. Howmiller and
Scott (1977) and Milbrink (1983) classified benthic macroinvertebrate assemblages dominated
by these species as enriched with organic (nutrient) materials. Sites near the mouth of the
Muskegon River (M-ll, M-l3, and M-l4), Ruddiman Creek (M-l), and the northern shore
(M-l 5) were indicative of the greatest degree of enrichment based on oligochaete densities of
> 80% of the total benthic macroinvertebrate population. The deposition of organic matter
from the Muskegon River and the eutrophic conditions present in the lake create an enriched
environment which supports high oligochaete densities. The
79
-------
TABLE 4.4.1.1 BENTHIC MACROINVERTEBRATE DISTRIBUTION IN MUSKEGON LAKE
(#/M2), OCTOBER 1999. MEAN NUMBER OF ORGANISMS (± STANDARD ERROR)
REPORTED FOR EACH STATION.
Station
Taxa
Turbellaria
Oligochaeta
Lumbriculidae
Stylodrilus heringianus
Naididae
Arcteonais lomondi
Dem digitata
Dero flabelliger
Piguetiella michiganensis
Salvina appendulata
Tubificidae
Aulodrilus americanus
Aulodrilus limnobius
Aulodrilus pigueti
Aulodrilus pluriseta
Ilyodrilus templetoni
Isocheatides freyi
Limnodrilus cervix variant
Limnodrilus hoffmeisteri
Limnodrilus maumeensis
Limnodrilus udekemianus
Potamothrix moldaviensis
Quistadrilus multisetosus
Immatures w/o hair chaetae
Immatures w/hair chaetae
Polychaeta
Manayunkia speciosa
Hirudinea
Glossiphoniidae
Alboglossiphonia heteroclita
Helobdella stagnalis
Helobdella elongata
M()II|ISC;I
Gastropoda
Amnicola sp.
Bithynia sp.
Valvata tricarinata
Valvata sincera
Bivalvia
Pisidium sp.
Sphaerium sp.
Musculium sp.
Dreissena polymorpha
Isopoda
Caecidotea
Musk-1
14 + 14
0
14 + 14
258 + 66
0
0
0
0
172 + 50
359 + 152
1076 + 305
14 + 14
86 + 50
0
72 + 14
0
0
0
14 + 14
1378 + 25
359 + 63
0
0
29 + 14
0
0
0
0
0
0
0
0
0
0
Musk-3
14+ 14
0
0
14+ 14
0
0
0
0
14+ 14
460 + 51
0
79+59
0
0
76+ 17
14+ 14
0
0
508 + 216
3752 + 610
1215 + 299
0
0
0
0
57 + 38
0
0
0
86 + 50
29+ 14
0
29+ 14
0
Musk-4
43
0
0
0
0
0
0
0
81
570
4556
81
81
0
0
0
0
0
163
2115
814
0
0
0
0
0
0
0
0
0
0
0
0
0
Musk-5
144+ 14
0
0
14 + 14
14 + 14
0
0
0
14 + 14
1134 + 288
0
0
0
0
14 + 14
0
0
0
14 + 14
990 + 282
201 + 94
0
0
0
0
57 + 14
14 + 14
144 + 38
0
1550 + 224
43 + 25
14 + 14
359 + 175
0
Musk-6
86 + 25
0
0
0
0
0
0
14+ 14
57+ 57
1220 + 546
0
0
0
0
29+ 14
0
0
0
14+ 14
1033 + 326
144 + 63
0
0
0
0
100 + 52
14+ 14
187 + 72
0
646 + 25
0
0
316+ 123
0
Musk-7
57 + 38
0
0
14 + 14
0
0
14 + 14
0
86 + 66
344 + 132
0
0
14 + 14
0
0
0
0
0
57 + 57
1938 + 634
273 + 144
0
0
0
0
100 + 52
0
144+52
0
646 + 132
244+ 14
14 + 14
316 + 132
29 + 29
Musk-8
72 + 52
14 + 14
14 + 14
0
0
0
0
0
0
258 + 114
0
0
0
0
29 + 14
0
0
0
187 + 38
2411 + 197
545 + 94
0
0
0
0
29 + 14
0
57 + 14
0
431 + 66
201 + 80
0
14 + 14
43 + 0
Musk-9
1249 + 1035
0
0
170 + 170
0
0
114 + 114
113 + 113
57 + 57
2415 + 1942
0
0
0
0
29 + 29
0
0
0
1335 + 1120
2422 + 1003
243 + 135
0
0
0
0
144 + 103
29 + 29
43 + 43
0
258 + 114
57 + 38
14 + 14
15758 + 15715
158 + 137
80
-------
TABLE 4.4.1.1 (CONTINUED) BENTHIC MACROINVERTEBRATE DISTRIBUTION IN
MUSKEGON LAKE (#/M2), OCTOBER 1999. MEAN NUMBER OF ORGANISMS (± STANDARD
ERROR) REPORTED FOR EACH STATION.
Station
Taxa
Amphipoda
Gammarus sp.
Hyalella sp.
Echinogammarus sp.
Diptera
Ceratopogonidae*
Probezzia sp.
Chaoboridae
Chaoborus sp.
Chironomidae
Chironominae
Chironomus sp.
Cladopelma sp.
Cryptochironomus sp.
Cryptochironomus digitatus
Dicrotendipes sp.
Paratanytarsus sp.
Polypedilum spp.
Tanytarsus sp.
Orthocladiinae
Heterotrissocladius oliveri
Tanypodinae
Ablabesmyia annulata
Coelotanypus concinnus
Conchapelopia sp.
Procladius sp.
Ephenieroptera
Caenis sp.
Tricoptera
Ocetis sp.
Neureclipsis sp.
Musk-1
14+14
29+14
0
0
0
115 + 52
445 + 29
0
0
0
0
0
0
14+14
0
0
0
0
187 + 38
0
0
0
Musk-3 | Musk-4 1 Musk-5
144 + 29
0
0
0
0
129 + 75
1163 + 197
0
57 + 29
0
0
0
0
0
0
0
14+14
0
158 + 63
0
0
0
1206
43
0
0
0
0
474
86
43
0
0
0
0
0
0
0
0
0
43
0
0
0
244 + 87
43 + 43
0
0
0
29+14
14+14
0
115 + 76
0
0
0
0
0
0
0
976 + 486
0
144 + 29
0
14+14
0
Musk-6
330 + 57
29 + 29
0
0
0
57 + 38
0
0
144 + 63
0
0
0
0
0
0
0
474 + 124
0
72 + 72
0
14+14
0
Musk-7
29+14
0
0
0
14+14
57 + 29
57 + 38
0
172 + 25
0
0
0
0
0
0
0
223 + 57
0
100 + 38
0
29 + 29
0
Musk-8
57 + 29
0
0
0
14+14
158 + 29
230 + 63
0
115 + 63
0
0
0
0
0
0
0
144 + 38
0
158 + 38
0
0
0
Musk-9
57 + 38
86 + 66
57 + 38
0
0
86 + 66
115 + 29
0
144 + 29
0
14+14
0
0
0
0
14+14
215 + 86
14+14
187 + 52
0
0
14+14
81
-------
TABLE 4.4.1.1 (CONTINUED) BENTHIC MACROINVERTEBRATE DISTRIBUTION IN
MUSKEGON LAKE (#/M2), OCTOBER 1999. MEAN NUMBER OF ORGANISMS (± STANDARD
ERROR) REPORTED FOR EACH STATION.
Station
Taxa
Turbellaria
Oligochaeta
Lumbriculidae
Stylodrilus heringianus
Naididae
Arcteonais lomondi
Dero digitata
Dero flabelliger
Piguetiella michiganensis
Salvina appendulata
Tubificidae
Aulodrilus americanus
Aulodrilus limnobius
Aulodrilus pigueti
Aulodrilus pluriseta
Ilyodrilus templetoni
Isocheatides freyi
Limnodrilus cervix variant
Limnodrilus hoffmeisteri
Limnodrilus maumeensis
Limnodrilus udekemianus
Potamothrix moldaviensis
Quistadrilus multisetosus
Immatures w/o hair ohaetae
Immatures w/hair chaetae
Polychaeta
Manayunkia speciosa
Hirudinea
Glossiphoniidae
Alboglossiphonia heteroclita
Helobdella stagnalis
Helobdella elongata
Mollusca
Gastropoda
Amnicola sp.
Bithynia sp.
Valvata tricarinata
Valvata sincera
Bivalvia
Pisidium sp.
Sphaerium sp.
Musculium sp.
Dreissena polymorpha
Isopoda
Caecidotea
Musk-10
158 + 38
0
0
29 + 14
0
0
14 + 14
0
14 + 14
445 + 117
0
0
0
0
14 + 14
0
0
0
187 + 38
1507 + 538
459 + 100
14 + 14
0
0
0
172 + 75
0
43 + 25
0
1119 + 99
402 + 137
0
129 + 75
0
Musk-11
29 + 14
0
0
79 + 45
0
0
0
0
27 + 27
136 + 72
53 + 27
0
0
26 + 26
106 + 24
0
0
0
296 + 99
6404 + 597
1859 + 354
0
0
0
43 + 43
0
0
0
0
230 + 57
158 + 63
0
14 + 14
0
Musk-12
388+ 179
0
0
168+ 120
0
104+ 104
0
0
27 + 27
725 + 44
14+ 14
29 + 29
0
0
88 + 47
0
0
14+ 14
14+ 14
4654 + 937
274 + 98
0
0
0
0
115 + 14
0
29+ 14
0
459+ 150
230 + 76
0
40860 + 13976
0
Musk-13
0
0
0
14+ 14
0
0
0
0
0
177 + 91
43 + 25
0
0
26 + 26
137 + 26
0
0
0
72 + 38
4247 + 883
838 + 289
14+ 14
0
0
0
0
0
0
0
144 + 76
100 + 63
14+ 14
0
0
Musk-14
330 + 94
0
0
0
0
0
0
0
30 + 30
834 + 452
0
0
0
14 + 14
70 + 50
0
0
0
620 + 249
6335 + 1082
1191 + 254
0
0
0
0
0
0
0
0
445 + 251
431 + 217
0
14 + 14
29 + 29
Musk-15
14 + 14
0
0
150 + 82
0
0
0
0
157 + 96
1601 + 682
150 + 82
0
55 + 55
0
0
0
0
0
232+122
6951 + 1842
1193 + 466
0
0
0
0
0
0
29 + 29
0
474+155
72 + 72
0
14 + 14
0
Musk-16
201 + 63
0
34 + 34
0
0
0
0
220 + 79
121 + 80
1611 + 442
0
0
0
0
0
0
30 + 30
0
216 + 77
4192+1209
250 + 22
0
0
0
0
388 + 188
14 + 14
72 + 29
29 + 14
388 + 124
57 + 14
0
5626 + 1730
0
82
-------
TABLE 4.4.1.1 (CONTINUED) BENTHIC MACROINVERTEBRATE DISTRIBUTION IN
MUSKEGON LAKE (#/M2), OCTOBER 1999. MEAN NUMBER OF ORGANISMS (± STANDARD
ERROR) REPORTED FOR EACH STATION.
Station
Taxa
Amphipoda
Gammarus sp.
Hyalella sp.
Echinogammarus sp.
Diptera
Ceratopogonidae*
Probezzia sp.
Chaoboridae
Chaoborus sp.
Chironomidae
Chironominae
Chironomus sp.
Cladopelma sp.
Cryptochironomus sp.
Cryptochironomus digitatus
Dicrotendipes sp.
Paratany 'tarsus sp.
Polypedilum spp.
Tanytarsus sp.
Orthocladiinae
Heterotrissocladius oliveri
Tanypodinae
Ablabesmyia annulata
Coelotanypus concinnus
Conchapelopia sp.
Procladius sp.
Ephemeroptera
Caenis sp.
Tricoptera
Ocetis sp.
Neureclipsis sp.
Musk- 10
43 + 25
0
0
0
14+ 14
215 + 90
14+ 14
0
14+ 14
0
0
0
0
0
0
14+ 14
474 + 217
0
43 + 43
0
0
0
Musk- 11
43 + 25
0
0
0
0
57+ 14
258 + 43
0
144 + 29
0
0
0
0
0
0
0
187+57
0
244 + 57
0
0
0
Musk- 12
502+ 152
14+ 14
100+ 14
0
0
0
43 + 25
0
29+ 14
0
0
0
29 + 29
0
0
0
0
0
172+ 114
29 + 29
14+ 14
0
Musk- 13
0
0
0
29 + 29
14+ 14
187+ 100
244 + 52
0
43 + 25
0
0
0
0
0
0
29+ 14
43 + 25
0
273 + 100
0
0
0
Musk- 14
57 + 38
29 + 29
0
43 + 43
14 + 14
43 + 25
100 + 38
0
144+ 14
0
0
0
0
0
0
57 + 14
86 + 25
0
244 + 115
0
0
Musk- 15
172 + 25
0
0
0
0
100 + 52
431 + 132
0
72 + 38
14+ 14
0
14+ 14
0
0
0
0
43 + 43
0
86 + 66
0
0
0 0
Musk- 16
0
14 + 14
0
0
0
57 + 38
287+ 87
0
43 + 0
0
0
0
0
0
14 + 14
0
0
0
57 + 29
0
43 + 25
0
TABLE 4.4.1.2 MEAN ABUNDANCE (#/M ) AND RELATIVE DENSITIES (%) OF MAJOR
TAXONOMIC GROUPS IN MUSKEGON LAKE, OCTOBER 1999.
Station
M-l
M-3
M-4
M-5
M-6
M-7
M-8
M-9
M-10
M-ll
M-12
M-13
M-14
M-15
M-16
Oligochaetes
3802(81.8)
6132(76.5)
8461(81.4)
2395(38.0)
2511(50.4)
2740(55.0)
3458(66.7)
6898(26.9)
2669(48.2)
8986(86.5)
6111(12.4)
5554(83.0)
9094(81.5)
10489(87.2)
6674(47.8)
Chironomids
646(13.9)
1392(17.4)
646(6.2)
1249(19.8)
690(13.9)
559(11.2)
647(12.5)
703(2.7)
559(10.1)
833(8.0)
273(0.6)
632(9.4)
631(5.7)
660(5.5)
401(4.1)
Sphaeriids
0(0)
115(1.4)
0(0)
1607(25.5)
646(13.0)
904(18.2)
632(12.2)
329(1.3)
1521(27.5)
388(3.7)
689(1.4)
258(3.9)
876(7.8)
546(4.5)
445(3.2)
Amphipods
43(0.9)
144(1.8)
1249(12.0)
287(4.6)
359(7.2)
29(0.6)
57(1.1)
200(0.8)
43(0.8)
43(0.4)
616(1.3)
0(0)
86(0.8)
172(1.4)
14(0.1)
Dreissena
0(0)
29(0.4)
0(0)
359(5.7)
316(6.3)
316(6.3)
14(0.3)
15758(61.5)
129(2.3)
14(0.1)
40860(83.2)
0(0)
14(0.1)
14(0.1)
5626(40.3)
Other
158(3.4)
200(2.5)
43(0.4)
402(6.4)
458(9.2)
430(8.6)
373(7.2)
1723(6.7)
616(11.1)
129(1.2)
575(1.2)
244(3.6)
459(4.1)
143(1.2)
804(5.8)
Total
4649
8012
10399
6299
4980
4978
5181
25611
5537
10393
49124
6688
11160
12024
13964
83
-------
FIGURE 4.4.1.1 GENERAL DISTRIBUTION OF BENTHIC MACROINVERTEBRATES IN
MUSKEGON LAKE, OCTOBER 1999.
50000-i 1
45000-
40000-
35000-
30000-
ro
§• 25000-1
E
E 20000-
15000-
10000-
5000-
0
Ik
(kH
Ik
t
D Total Organisms
D Zebra Mussels
D Total Oligochaetes
DTotal Chironomids
M-1 M-3 M-4 M-5 M-6 M-7 M-8 M-9 M-10 M-11 M-12 M-13 M-14 M-15 M-16
Station
station near Ruddiman Creek (M-1) was historically influenced by the discharge of paper mill
effluent and would also have organically enriched sediments. Sites with the highest levels of
contaminants (M-5, M-6, and M-16) had lower oligochaete densities (« 50%). While the
sandy substrate and lower levels of organic carbon at M-16 would tend to reduce oligochaete
densities, the sediments near the Division Street Outfall (M-5 and M-6) had higher levels of
organic carbon (4.1 mg/kg and 5.3 mg/kg) the stations with the highest oligochaete
populations (M-14, 2.3 mg/kg and M-15, 2.5 mg/kg).
Densities of Chironomidae ranged between 1,392/m2 and 273/m2 and this taxa group was the
second most abundant group at 7 of the 15 of the stations sampled (Table 4.4.2). A total of
14 taxa were identified (Table 4.4.1.1). Chironomus spp. and Procladius spp. were found at
all sites except M-6. Abundance of Chironomus spp. ranged 0/m2 to 1163/m2) and was
generally the most common chironomid encountered. Procladius spp. abundance was low
and did not exceed 273/m2. With the exception of Coelotanypus concinnus and
Cryptochironomus spp., the remaining species were found infrequently and were generally
84
-------
low in abundance. Cryptochironomus spp. was present at all sites except M-l and generally
in lower abundance than Chironomus spp. Organisms from this genus 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 spp. was the most abundant midge genera in the enriched stations with the
highest oligochaete densities.
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 and 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. Trophic Indices for the benthic
populations are shown in Figure 4.4.2.1. Lower scores for total organisms, oligochaetes, and
TABLE 4.4.2.1 SUMMARY OF DIVERSITY AND TROPHIC STATUS METRICS FOR THE
BENTHIC MACROINVERTEBRATES IN MUSKEGON LAKE, OCTOBER 1999.
Metric
Hilsenhoff
Oligochaete
Chironomid
Shannon- Wfeaver
Margalefs richness
Evenness
J
Total Organisms
Zebra Mussels
Total oligochaetes
Total Chironomids
Taxa richness
Chiro/Oligo Ratio
Chironomid Detritivores
Chironomid Predators
M-1
8.3865
8.2854
9.3378
1.9464
1.8947
0.4120
0.6870
4650
0
3803
761
17
0.1698
445
201
M^3
8.8546
8.9614
9.4052
1.8849
1.8912
0.3659
0.6521
8013
29
6133
1521
18
0.2270
1163
230
M^f
6.0045
6.2585
9.3067
1.5637
1.5136
0.3184
0.5774
10399
0
8461
646
15
0.0763
560
86
M-5
6.8754
6.9419
7.8069
2.1258
2.5148
0.3643
0.6780
6300
359
2397
1277
23
0.5210
14
1234
M-6
6.7584
6.9170
7.6896
2.1697
1.9969
0.4864
0.7507
4980
316
2512
746
18
0.2743
0
689
M-7
6.4994
5.5842
7.9128
2.2149
2.5842
0.3983
0.7064
4980
316
2741
631
23
0.2042
72
502
M-8
8.3561
8.9156
8.5689
1.9476
2.1094
0.3691
0.6615
5081
14
3358
818
19
0.1923
244
416
M-9
7.0702
7.7809
8.1020
1.5125
2.6600
0.1621
0.4539
25605
15758
6890
789
28
0.1021
129
574
M-10
7.4549
8.3180
7.7385
2.2021
2.3203
0.4307
0.7233
5540
129
2669
789
21
0.2097
29
545
M-11
9.1667
9.3893
8.5500
1.7772
1.8380
0.3285
0.6149
10395
14
8988
890
18
0.0926
258
574
M-1 2
7.1698
8.8738
8.5684
0.7375
2.1292
0.0871
0.2320
49125
40860
6112
273
24
0.0446
43
230
M-1 3
8.9730
9.1560
8.7841
1.6583
1.8176
0.3088
0.5853
6652
0
5547
832
17
0.1138
258
388
M-1 4
8.5295
8.9780
8.0182
1.8104
1.9321
0.3217
0.6149
11118
14
9094
689
19
0.0694
115
531
M-1 5
8.3145
8.4430
8.9804
1.5016
1.9159
0.2363
0.5100
12027
14
10492
761
19
0.0629
431
230
M-1 6
7.4694
8.0726
9.0607
1.6967
2.0955
0.2598
0.5573
13966
5626
6675
459
21
0.0602
287
115
85
-------
9.500 -f
9.000-'
8.500-'
8.000-'
01
3
j5 7.500-'
X
•S 7.000-'
_c
6.500-'
6.000-'
5.500-'
5.000 -r
•
I
^
r=
p
ill
-
^
1
1 1 <• 1
i i
r
M-1 M-3 M-4 M-5 M-6 M-7 M-8 M-9 M-10 M-11 M-12 M-13 M-14 M-15 M-16
Station
FIGURE 4.4.2.1 SUMMARY OF TROPHIC INDICES FOR THE BENTHIC
MACROINVERTEBRATES IN MUSKEGON LAKE, OCTOBER 1999.
chironomids were noted at M-5, M-6, and M-7 than most of the other locations in Muskegon
Lake. This indicates that organisms less tolerant of organic enrichment were present in this
area. A further analysis of the chironomid populations is shown in Figure 4.4.2.2. When the
chironomids are split into detritivores and predators, sediment feeding organisms in the
Chironominae group are reduced in the area of the Division Street Outfall. When the
chironomids are split into detritivores and predators, sediment feeding organisms in the
Chironominae group are reduced in the area of the Division Street Outfall. In contrast,
predatory chironomids in the Tanypodinae group are abundant at this location. This pattern is
reversed at the other locations, as sediment feeding genera are greater in number. The
presence of more predatory chironomids may indicate toxicity in the sediments as sediment
feeding organisms are reduced. A similar shift in benthic populations was noted in a highly
contaminated area of White Lake (Rediske et al. 1998) that was impacted by elevated
concentrations of chromium, arsenic, and mercury.
Data for the Shannon-Weaver Diversity and Pielou's J Indices are shown in Figure 4.4.2.3.
Stations M-5, M-6, M-7, and M-10 had Shannon-Weaver Diversity values in excess of 2.0.
Benthic macroinvertebrate populations from these locations were characterized by lower
numbers of oligochaetes and more predatory chironomids. All stations with the exception of
86
-------
FIGURE 4.4.2.2 SUMMARY OF CHIRONOMID DETRITIVORES AND PREDATORS FOR THE
BENTHIC MACROINVERTEBRATES IN MUSKEGON LAKE, OCTOBER 1999.
1400-
1200-
5 1000-
S! soo-
ro
o-
1 6°°-
E
3
z 400-
200-
f
fa
\
c
c
L
"
ii
;!
•i
:|
i
I?
i
,1
1
r
M
;'<
;i '
r
•
j>
/
1=
B
1!
•
1
r
1
e
a
iy
r
•
tf
i
B
T
^ Detritivores
•Predators
M-1 M-3 M-4 M-5 M-6 M-7 M-8 M-9 M-10 M-11 M-12 M-13 M-14 M-15 M-16
Station
FIGURE 4.4.2.3 SUMMARY OF DIVERSITY AND THE J INDEX VALUES FOR THE BENTHIC
MACROINVERTEBRATES IN MUSKEGON LAKE, OCTOBER 1999.
0)
_3 1.500-
15
x
01
M-1 M-3 M-4 M-5 M-6 M-7 M-8 M-9 M-10 M-11 M-12 M-13 M-14 M-15 M-16
Station
87
-------
M-12, which was highly impacted by zebra mussels, had diversity values ranging from 1.5 -
2.0. Very little variation was noted in the J value with the exception of M-12 that was
influenced by excessive numbers of zebra mussels.
4.4.3 Benthic Macroinvertebrate Analyses Based On Location Groups
The benthic macroinvertebrate data were further analyzed to determine if statistically
significant differences existed between locations potentially impacted by the Division Street
Outfall (M-5 through M-7) and stations potentially influenced by the Lakey/Teledyne Foundry
complex (M-10 and M-ll). The same metrics in Table 4.4.2.1 were utilized except that the
values were calculated based on the individual replicates.
For the purpose of statistical analysis, the following groups were examined:
• Control (M-13, M-14, and M-15)
• Group 1 - Division Street Outfall (M-5, M-6, and M-7)
• Group 2 - Foundry (M-10 and M-ll)
Group 1 locations were in the Division Street Outfall area and had the highest reported values
for heavy metals; Group 2 locations were in the vicinity of the Lakey/Teledyne foundry
complex. Station M-12 was not included in the analysis due to the sandy substrate and the
presence of a large zebra mussel population. The calculated data for the above metrics are
summarized in Table 4.4.3.1. Box plots of the data for the Oligochaete Index, N, the
Oligochaete/Chironomid ratio, and total Oligochaetes are shown in Figures 4.3.1-4.3.4,
respectively. Stations in the Division Street Outfall area have fewer total organisms, a smaller
oligochaete population, and a higher proportion of chironomids to oligochaetes compared to
the control or foundry locations. The box plot of the Oligochaete Index (Fig 4.4.3.1) suggests
that more pollution intolerant species are present (lower index value); however the data are
skewed by the larger populations present at the control and foundry sites.
A separate Analysis of Variance (ANOVA) for each of the metrics was used to investigate
differences between the three groups of sites. The null hypothesis is that the mean diversity
measures for each group are equal. The null hypothesis was rejected if statistically significant
p values (p < 0.05) were obtained. Post hoc comparisons on the means of the above groups
were then performed using the Student-Newman-Keuls (SNK) test. The results of the
ANOVA and SNK ranks are summarized in Table 4.4.3.2. All analyses were performed using
SAS and SPSS.
88
-------
TABLE 4.4.3.1 SUMMARY STATISTICS FOR THE ANALYSIS OF INDIVIDUAL BENTHIC
MACROINVERTEBRATE SAMPLES FROM MUSKEGON LAKE, OCTOBER 1999.
Division Street Outfall
Total Oligochaetes
Total Chironomids
Total Chironomid Predators
Total Chironomid Detritivores
Hilsenhoff index
Oligochaete index
Chironomid index
Shannon- Weaver
Margalef's richness
Evenness
J
N
Taxa richness
Chiro/Oligo
M-5 A
3230
1636
1636
0
7.342
8.597
7.726
2.060
1.851
0.461
0.727
5683
16
0.507
M-5B
1808
1851
1851
0
6.790
6.040
7.821
1.780
1.280
0.494
0.716
5382
11
1.024
M-5C
2153
258
215
43
7.121
8.095
8.217
1.817
1.754
0.385
0.655
5167
15
0.120
M-6 A
775
301
301
0
6.832
8.526
7.600
1.872
1.164
0.650
0.813
2282
9
0.389
M-6B
3014
603
603
0
6.471
6.463
7.550
1.890
1.518
0.473
0.716
5253
13
0.200
M-6C
3832
1163
1163
0
6.954
6.961
7.785
2.024
1.482
0.541
0.767
6458
13
0.303
M-7 A
2196
474
344
129
8.076
8.483
8.145
1.850
1.700
0.398
0.667
6803
15
0.216
M-7B
474
517
517
0
7.793
8.908
7.900
2.115
1.820
0.518
0.763
3789
15
1.091
M-7C
560
689
646
43
7.543
8.403
7.763
2.116
1.722
0.553
0.781
3401
14
1.231
Foundry Area
Total Oligochaetes
Total Chironomids
Total Chironomid Predators
Total Chironomid Detritivores
Hilsenhoff index
Oligochaete index
Chironomid index
Shannon- Weaver
Margalef's richness
Evenness
J
N
Taxa richness
Chiro/Oligo
Total Oligochaetes
Total Chironomids
Total Chironomid Predators
Total Chironomid Detritivores
Hilsenhoff index
Oligochaete index
Chironomid index
Shannon- Weaver
Margalef's richness
Evenness
J
N
Taxa richness
Chiro/Oligo
M-10A
2971
215
215
0
7.463
8.330
7.700
2.003
1.510
0.530
0.759
5468
13
0.072
M-13A
3186
818
474
344
9.050
9.758
8.753
1.742
1.531
0.408
0.660
4865
14
0.257
M-10B
1508
947
904
43
7.279
8.285
7.786
2.131
1.416
0.648
0.831
4780
12
0.628
M-13B
6503
431
215
215
8.789
8.839
8.410
1.150
1.016
0.316
0.499
7020
10
0.066
M-10C
3532
517
517
0
7.676
8.422
7.667
1.895
1.725
0.416
0.683
5986
16
0.146
Control
M-13C
6890
646
474
172
8.891
9.026
9.073
1.521
0.999
0.458
0.661
8182
10
0.094
M-11 A
10027
818
603
215
9.161
9.425
8.532
1.308
1.389
0.264
0.496
11577
13
0.082
M-14A
12487
947
775
172
8.238
8.739
8.436
1.694
1.445
0.363
0.626
16146
15
0.076
M-11B
8220
990
775
215
9.029
9.234
8.387
1.414
1.309
0.316
0.551
9597
13
0.120
M-14B
8909
517
431
86
8.881
9.191
7.808
1.285
1.193
0.301
0.517
10071
12
0.058
M-11C
8772
689
344
344
9.471
9.672
8.806
1.468
1.303
0.334
0.572
10020
13
0.079
M-14C
5900
431
388
43
8.734
9.258
7.350
1.879
1.688
0.409
0.678
7234
16
0.073
M-15A
8568
1033
344
689
7.646
7.596
8.904
1.226
0.868
0.378
0.558
10032
9
0.121
M-15B
8389
474
215
258
8.434
8.643
9.327
1.678
1.412
0.383
0.636
9982
13
0.056
M-15C
33511
474
129
344
7.370
7.384
8.800
1.634
1.242
0.366
0.619
35018
14
0.014
89
-------
10
61
OM15A
OM15C
N =
g
Control
Division St.
Foundry
FIGURE 4.4.3.1 Box PLOT OF THE OLIGOCHAETE INDEX DATA FOR MUSKEGON LAKE
BENTHIC MACROINVERTEBRATE STATIONS (Box = 25%-75% DATA DISTRIBUTION),
OCTOBER 1999.
40000
30000
20000
10000
•XM15C
O/I14A
N =
g
Control
Division St. Foundry
FIGURE 4.4.3.2 Box PLOT OF THE TOTAL NUMBER OF ORGANISMS FOR MUSKEGON
LAKE BENTHIC MACROINVERTEBRATE STATIONS (Box = 25%-75% DATA
DISTRIBUTION), OCTOBER 1999.
90
-------
1.2
1.0
ro
a:
o
o
5 6
.4
.2
0.0
N =
•XM10B
•XM13A
g
Control
Division St.
Foundry
FIGURE 4.4.3.3 Box PLOT OF THE OLIGOCHAETE/CHIRONOMID RATIO FOR MUSKEGON
LAKE BENTHIC MACROINVERTEBRATE STATIONS (Box = 25%-75% DATA
DISTRIBUTION), OCTOBER 1999.
40000
30000
ro
.c
o
o
= 20000
10000
0,
•WI15C
N =
9
Control
9
Division St.
6
Foundry
FIGURE 4.4.3.4 Box PLOT OF THE TOTAL OLIGOCHAETE NUMBERS FOR MUSKEGON
LAKE BENTHIC MACROINVERTEBRATE STATIONS (Box = 25%-75% DATA
DISTRIBUTION), OCTOBER 1999.
91
-------
TABLE 4.4.3.2 RESULTS OF ANOVA AND SNK EVALUATIONS OF BENTHIC
MACROEMVERTEBRATE DATA FOR MUSKEGONLAKE, OCTOBER 1999.
Diversity Measure
Shannon-Weaver
Evenness
J
Margalef s Richness
Oligochaete Index
Chironomid Index
Hilsenhof
Total Chironomids
Total Predators
Taxa Richness***
Chironomid to
Oligochaete Ratio***
Total Number of
Organisms***
Total
Oligochaetes***
Total Detritivores***
ANOVA
p-value*
.0035
.0054
.0023
.0570
.0124
<.0001
<.0001
.5050
.1866
.3715
.0328
.0011
.0441
.0004
SNK post-hoc
SNK Grouping
A
B
B
SNK Grouping
A
B
B
SNK Grouping
A
B
B
results**
Mean
1.9471
1.7032
1 .5343
Mean
0.49700
0.41800
0.37578
Mean
0.73389
0.64867
0.60600
N
9
6
9
N
9
6
9
N
9
6
9
group
Division Street
Foundry
Control
group
Division Street
Foundry
Control
group
Division Street
Foundry
Control
SNK Grouping
A
A
B
SNK Grouping
A
B
C
SNK Grouping
A
A
B
Mean
8.8947
8.7149
7.8307
Mean
8.5401
8.1463
7.8341
Mean
8.4481
8.3465
7.2136
N
6
9
9
N
9
6
9
N
9
6
9
group
Foundry
Control
Division Street
group
Control
Foundry
Division Street
group
Control
Foundry
Division Street
SNK Grouping
A
B
B
SNK Grouping
A
A
B
SNK Grouping
A
B A
B
SNK Grouping
A
B
C
Mean
18.278
11 .917
7.111
Mean
17.333
13.667
6.889
Mean
10483
5838
2373
Mean
258.33
136.34
23.92
N
9
6
9
N
9
6
9
N
9
6
9
N
9
6
9
group
Division Street
Foundry
Control
group
Control
Foundry
Division Street
group
Control
Foundry
Division Street
group
Control
Foundry
Division Street
* Reject the null hypothesis and conclude that at least one group has a different mean and p < 0.05. If you reject
Ho then run the post-hoc SNK procedure.
** Different letters indicate a statistically significant difference in the means of the groups.
*** Nonparametric ANOVA done on the ranks of the data.
92
-------
Based on the ANOVAs and SMC groupings, the following conclusions can be drawn:
• The Division Street Outfall group had a significantly higher mean than either the Foundry
or the Control groups for Shannon-Weaver, Evenness, J, and Chironomid to
Oligochaete Ratio. The Foundry and Control groups were not significantly different.
• The Division Street Outfall group had a significantly lower mean than either the Foundry
or the Control groups for the Oligochaete Index, Hilsenhof Index, and Total Number of
Organisms. The Foundry and Control groups were not significantly different.
• The Control group had a significantly higher mean than the Foundry group, which had a
significantly higher mean than the Division Street group for the Chironomid Index and
Total Detritivores.
• For Total Oligochaetes the Control group had a significantly higher mean than the
Division Street Outfall group. The Control group and the Foundry group were not
significantly different. The Foundry group and the Division Street Outfall group were
also not significantly different.
4.4.4. Benthic Macroinvertebrate Data Summary
The benthic macroinvertebrate community of Muskegon Lake is characterized by organisms that are
tolerant of organic (nutrient) enrichment. The presence of organic deposition from the Muskegon
River, the eutrophic conditions in the lake, and the historical anthropogenic enrichment from the
paper mill and the wastewater treatment plant all act to increase the densities pollution tolerant
organisms. To this extent, detritivores such as tuberficids 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 Muskegon Lake. The only sites that do not fit this
characterization were from the Division Street Outfall, the lakeshore industrial area, and one site
near the abandoned foundry complex. These locations had fewer total organisms and consequently,
better scores for most diversity metrics. The most notable difference with respect to this group of
stations was a change in chironomid species from detritivores to predators. A shift to more
opportunistic organisms has previously been attributed to contaminant impact (Dauer 1991). 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. These
stations had similar TOC and grain size distributions when compared to the control group so
response to contamination is the most likely explanation.
93
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4.5 Sediment Quality Triad Assessment
Sediment Quality Triads for the areas of sediment contamination in Muskegon Lake were calculated
using chemistry, toxicity, and diversity metrics (Canfield et al. 1998, Del Valles and Chapman
2000). For the chemistry metric of the triad, concentrations of chromium, lead, cadmium, copper,
and mercury were summed. PAH compounds were not included since they were present at very
high levels in only one location and would bias the chemistry assessment. As a result, a triad
diagram was not prepared for location M-16. Sediments at this location were toxic to amphipods
and midges and PAH levels were in excess of 5X the PEC guidelines. For the toxicity component,
amphipod and midge mortality were used. The diversity metric included the following metrics:
Shannon-Weaver, oligochaete trophic index, chironomids trophic index, Hilsenhof trophic index, J,
Margalef s Richness, evenness, N, taxa richness, Chironomid/Oligochaete ratio, total chironomids,
total oligochaetes, total predatory chironomids, and total chironomid detritivores. The actual
diversity measures used were the absolute deviation from the average of the reference sites M-13,
M-14, and M-15. These reference sites have benthic macroinvertebrate assemblages that were
characteristic of organic enrichment in the sediments. The Sediment Quality Triad diagrams for the
Ruddiman Creek area, the Division Street Outfall, and the former foundry complex are shown in
Figures 4.5.1, 4.5.2, and 4.5.3, respectively. Triad diagrams for the Division Street Outfall (Fig
4.5.2) show the greatest deviation from the reference locations for chemistry, toxicity, and diversity.
At these locations, heavy metals exceeded PEC guidelines, statistically significant toxicity to
amphipods was observed at two of the three sites, and benthic macroinvertebrate populations were
reduced in total organisms and found to contain more predatory genera. The area downstream of
Ruddiman Creek (Fig 4.5.1) showed moderate differences in chemistry, toxicity, and diversity when
compared to the reference locations. Stations near the former foundry complex (Fig 4.5.3) showed
the least amount of difference from the reference conditions for chemistry and toxicity. The
deviation in diversity at M-10 from the reference sites was 71% of the maximum observed deviation
indicating that the benthic community structure was impacted. This location was also characterized
by a reduction in total numbers and a shift to more predatory genera. There is insufficient
information available to determine an environmental reason for diversity differences at this site.
The individual site Triads were analyzed for correlations between the three component
measurements. The results are summarized below:
Chemistry
Toxicity
Diversity
Chemistry
1.000
0.869 (.0002)
0.793 (.0021)
Toxicity
1.000
0.664 (.0186)
Diversity
1.000
(p value)
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M1
46.5
Toxicity
Chemistry
34.3
46.1
Diversity
M4
M3
Chemistry
19.8
Toxicity
Chemistry
1
46.5
Toxicity
43.9
Diversity
FIGURE4.5.1. SEDIMENT QUALITY TRIAD DIAGRAMS FOR THE RUDDIMAN CREEK AREA OF
MUSKEGONLAKE.
95
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100 '
Toxicity
s 100
Diversity
Chemistry
37.9
89.6
Toxicity
71.2
Diversit'
Diversity
FIGURE 4.5.2. SEDIMENT QUALITY TRIAD DIAGRAMS FOR THE DIVISION STREET OUTFALL
AREA OF MUSKEGON LAKE.
96
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M10
Chemistry
23.9
46.5
Toxicity
71.4
Diversity
M11
Chemistry
18.7
46.5
Toxicity
Diversity
FIGURE 4.5.3. SEDIMENT QUALITY TRIAD DIAGRAMS FOR THE FORMER FOUNDRY COMPLEX
AREA OF MUSKEGON LAKE.
97
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A positive correlation was found between each pair of measures. Sites with high levels of
metals were also high in toxicity. Sites with elevated levels of heavy metals also had diversity
values that were unlike the reference sites. Similarly, sites with high toxicity had diversity
metrics that were dissimilar to the reference sites.
The data making up the Sediment Quality Triad were also examined by Principal Component
Analysis (PCA) to examine the similarity between sediment sampling sites. Standardized
values were computed for each site and measurement used in the Triad by subtracting the
mean and dividing the result by the standard deviation. Separate PCAs were run on the six
chemistry variables, the two toxicity variables, and the 14 diversity measures. Principal
component scores were then calculated for each site for the chemistry, toxicity, and diversity
PCAs.
The principle component scores were then used to develop a distance matrix for each pair of
sites. The distance site /' is from site j equaled the sum of the absolute values of the
differences in the principal component scores for chemistry, toxicity, and diversity. A cluster
analysis was then performed on the distance matrix. The results of the PCA and Cluster
Analysis is shown in Figure 4.5.4. Three distinct clusters were present: Cluster 1 - M5 and
M6; Cluster 2 - Ml, M7, M8, and M10; Cluster 3 - M3, M4, Mil, M13, M14, and M15.
Two of the three Division Street Outfall sites (M5 and M6) form Cluster 1. The three
reference sites were all contained in Cluster 3, along with two Ruddiman Creek sites. The two
sites in the area near the former Foundry Complex (M10 and Mil) were not in the same
cluster.
10.
5 -
0 J
FIGURE 4.5.4 RESULTS OF A CLUSTER ANALYSIS PERFORMED ON PRINCIPAL
COMPONENT SCORES FOR SEDIMENT QUALITY TRIAD MEASURES FOR MUSKEGON LAKE
SEDIMENT.
98
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These results of the Sediment Quality Triad and Cluster Analysis show that the near shore
locations at the Division Street Outfall (M-5 and M-6) exhibit the greatest degree of
anthropogenic perturbation with respect to sediment chemistry, toxicity and diversity. The
deep basin down stream from Ruddiman Creek (M-l), the more exterior stations at the
Division Street Outfall (M-7 and M-8), and the foundry site M-10 were strongly impacted by
anthropogenic disturbance. Although Sediment Quality Triad diagrams were not prepared
for M-l6 due to the high levels of PAH compounds, this location would rank very high with
respect to chemistry and toxicity.
In addition to triad diagrams, an assessment matrix (Chapman 1992) has been used to examine
the relationship between sediment chemistry, toxicity, and benthic macroinvertebrate data. An
assessment matrix for the Muskegon Lake data is presented in Table 4.5.1. Stations
exceeding the PEC (MacDonald et al. 2000) were classified as having a potential impact from
TABLE 4.5.1 SEDIMENT QUALITY ASSESSMENT MATRIX FOR MUSKEGON LAKE DATA,
OCTOBER 1999. ASSESSMENT MATRIX FROM CHAPMAN (1992).
Station
M-5 M-6 M-16
M-3M-4M-9M-11
M-12M-13M-14
M-15
M-8 M-1
M-10
M-7
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
= Indicator classified as affected; as determined based on comparison to the PEC or control site
Indicator not classified as affected; as determined based on comparison to the PEC or control site
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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 Division Street Outfall (M-5, M-6 and M-7) and the
lakeshore industrial area (M-16) were likely to be impacted by contaminated sediments. At
these locations, sediment chemistry was elevated, laboratory toxicity was observed, and
impacted benthic communities were noted. The remaining stations
4.6 Summary And Conclusions
A preliminary investigation of the nature and extent of sediment contamination in Muskegon
Lake was performed using Sediment Quality Triad methodology. Sediment chemistry, solid-
phase toxicity, and benthic macroinvertebrates were examined at 15 locations. In addition,
three core samples were evaluated using radiodating and stratigraphy to assess sediment
stability and contaminant deposition. High levels of cadmium, copper, chromium, lead, and
mercury were found in the Division Street Outfall area. These levels exceeded the Probable
Effect Concentrations (PECs) for current sediment quality guidelines. Most of the heavy
metals were found in the top 80 cm of the core samples. Deeper layers of contamination were
only found near the former Teledyne foundry and downstream from Ruddiman Creek. High
concentrations of PAH compounds were found at a location down gradient from the former
lakeshore industrial area. These levels also exceeded PEC guidelines. Sediment toxicity was
observed at two stations in the Division Street Outfall area and at the lakeshore industrial
area. These locations had the highest concentrations of metals and PAH compounds,
respectively. Benthic macroinvertebrate communities throughout Muskegon Lake were found
to be indicative of organically enriched conditions. The locations in the Division Street
Outfall area were significantly different than reference sites, as indicated by fewer numbers
and a smaller population of detritivores.
Sediment Quality Triad diagrams were prepared and significant correlations were obtained
between chemistry and toxicity and chemistry and diversity (p < .01). Toxicity and diversity
also were positively correlated (p < .05). Based on the results of this investigation, the
Division Street Outfall and the location down gradient from the lakeshore industrial area are
priority areas for further investigation and potential remediation due to adverse ecological
effects, toxicity, and high contaminant levels.
Stratigraphy and radiodating analyses conducted on sediment cores provided important
information related to depositional history. Ruddiman Creek appears to have a significant
influence on the deposition of heavy metals in the southwestern part of Muskegon Lake. A
peak in metals deposition was found that corresponded to the 100+ year flood that occurred
in 1986. The historical deposition was considerably higher than current rates. The deep zone
off the Car Ferry Dock was not found to be an area that accumulates sediments. High
inventories of 210Pb were found near the bottom of this 80 cm core, indicating active mixing
and movement of sediments. The presence of elevated metals in the deeper strata plus the
high 210Pb inventories suggest that contaminated sediments are moved from the eastern part of
Muskegon Lake to this location where they are mixed and made available for resuspension by
the currents traveling along the old river channel. The core from the Division Street Outfall
showed relatively stable sediments in the top 20 cm followed by a stable zone of heavy
100
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accumulation after 1960. Based on these results it is apparent that the removal of
contaminated sediments from Ruddiman Creek and the lagoon would reduce the loading of
heavy metals to western Muskegon Lake. The areas of high sediment contamination in the
eastern part of the lake also appear to be mixed and subject to transport.
4.7 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.
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.
Chapman, P.M. 1992. Sediment quality triad approach. In: Sediment Classification Methods
Compendium. EPA 823-R-92-006. USEPA. Washington, D.C.
Del Vails, T.A. 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.
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 Muskegon Lakes in Muskegon County, Michigan The
1950s to the 1980s. Michigan Department of Natural Resources. MI/DNR/SWQ-
92/261. 91pp.
Dauer, D.M. 1991. Biological criteria, environmental health, and estuarine macrobenthic
community structure: Mar. Pollut. Bull. 26:249-257.
Hilsenhoff, W.L. 1987. An Improved Biotic Index of Organic Stream Pollution. Great Lakes
Entom. 20:31-39.
Howmiller, R.P., M.A. Scott. 1977. An environmental index based on the relative abundance
of oligochaete species. J. Water Pollut. Cont. Fed. 49: 809-815.
Krebs, C. J. (1989). Ecological methodology. New York: Harper & Row. 325 pgs.
Lauritsen, D.D., S.C. Mozley, 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.
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MacDonald, D.D., C.G. Ingersoll, T. A. Berger. 2000. Development and Evaluation of
Consensus-Based Sediment Quality Guidelines for Freshwater Ecosystems. Arch.
Environ. Contam. Toxicol. 39(1):20-31.
Milbrink, G. 1983. An improved environmental index based on the relative abundance of
oligochaete species. Hydrobiologia 102: 89-97.
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,
Michigan. U.S. Environmental Protection Agency. EPA-905-R-98-004.
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.
Limnol. Oceanogr. 40:918-929.
Schloesser, Don W., Trefor B. Reynoldson, Bruce A. Manny. 1995. Oligochaete fauna of
western Lake Erie 1961 and 1982: signs of sediment quality recovery: J. Great Lakes
Res. 21(3):294-306.
Winnell, M.H., D.S. White. 1985. Trophic status of southeastern Lake Michigan based
on the Chironomidae(Diptera). J. Great Lakes Res. 11:540-548.
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5.0 Recommendations
Three areas of significant sediment contamination were identified in this investigation. The
contaminated areas and recommendations are provided below:
1. Division Street Outfall. This area has the highest concentration of heavy metals,
significant sediment toxicity, and an impacted benthic invertebrate community. There
is also indirect evidence that sediments from this area are being transported into the
central region of Muskegon Lake. The chemical and physical composition of
sediments in the Division Street Outfall should be further delineated and carefully
examined for remediation. Since there are a number of abandon brownfield sites in the
area and the presence of a large urban storm drain, potential sources of the sediment
contamination need to be evaluated and if necessary, controlled as part of the
remediation program.
2. Lakeshore Industrial Area. The presence of elevated levels of PAH compounds and
high sediment toxicity at this location makes this a priority area for further
investigation. The extent of sediment contamination needs to be delineated and the
possibility of a venting groundwater plume or the leaching of contaminants form a
submerged deposit needs to be evaluated. If an impacted groundwater plume is
identified, source control will be necessary to prevent contaminants from entering the
lake. Because of the environmental significance of PAH compounds and the high
concentrations present at the site, this location should also be evaluated for
remediation after the source is identified.
3. Ruddiman Creek. The presence of heavy metals near the confluence of Ruddiman
Creek and in the downstream deposition basin suggests that this small watershed is a
continuing source of sediment contamination. Investigations and remediation
evaluations by the MDEQ and USACOE are in process. Preliminary results from
these investigations suggest that a combination of sediment removal and source
control will be necessary to complete the remediation. The findings of this
investigation should assist in assessing the priority status of sediment remediation in
Ruddiman Creek.
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