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

-------
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.

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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)

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       \
a.5    a    o.s    1
        Figure 2.1  Muskegon Lake Core and PONAR Sampling Stations.
                                        10

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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

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3.0    Methods

3.1 Sampling Methods
Sediment and  benthos samples  were  collected using  the  U.S. EPA Research  Vessel
Mudpuppy.  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

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       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

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            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

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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

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3.2.3 Cadmium Analysis By Furnace
Cadmium was analyzed in accordance with the EPA SW-846 method 7060A utilizing the
Graphite Furnace technique. The instrument employed was a Perkin Elmer 4110ZL atomic
absorption  spectrophotometer.   A hollow cathode lamp was  used as  a light  source  at
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

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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

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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

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             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

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      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

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  TABLE 3.4.1  TEST CONDITIONS FOR CONDUCTING A TEN DAY SEDIMENT TOXICITY
                           TEST WITH HYALELLA AZTECA
1.      Test Type:    Whole-sediment toxicity test with renewal of overlying water
2.      Temperature (°C):	23 ± 1°C
3.      Light quality:	Wide-spectrum fluorescent lights
4.      Illuminance:	About 500 to 1000 lux
5.      Photoperiod:	16 h light, 8 h darkness
6.      Test chamber size:	300 mL high-form lipless beaker
7.      Sediment volume:	100 mL
8.      Overlying water volume:	175 mL
9.      Renewal of overlying
       water:	2 volume additions per day (i.e.,  one volume addition
                                 every 12 hours)
10.     Age of test organisms:	7 to 14 days old at the start of the test
11.     Number of 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

-------
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

-------
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

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                                                         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

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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

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                           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

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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

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                  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

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               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

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"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

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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

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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

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    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

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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

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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

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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
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1








r





M

;'<























;i '







r





•

j>
/







1=





B

1!





















•

1







r







1






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a
iy







r





•

tf























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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

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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

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              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

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              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

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         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

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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)
                                              94

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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

-------
         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

-------
             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
                                          99

-------
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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