United States
Environmental Protection
Agency
Great Lakes National Program Office
77 West Jackson Boulevard
Chicago, Illinois 60604
E PA-905-R-02-003 <2-
June 2002
wEPA Appendix A
Screening Level Ecological
Risk Assessment for the
Lower Ottawa River, Ohio
-------
Final Report
Ecological Screening-Level
Risk Assessment
of the Lower Ottawa River
Prepared for
Limno-Tech, Inc.
501 Avis Drive
Ann Arbor, Michigan 48108
Prepared by
Parametrix
5808 Lake Washington Blvd. NE, Suite 200
Kirkland, WA 98033-7350
(425) 822-8880
www.parametrix.com
October 2001
Project No. 555-3763-001 (01/03)
-------
Ecological Screening-Level
Risk Assessment
of the Lower Ottawa River
FINAL REPORT
Prepared By:
Parametrix, Inc.
5808 Lake Washington Blvd NE, Suite 200
Kirkland, WA 98033-7350
(425)822-8880
Principal Authors:
Sue Robinson
David DeForest
Todd Pollard
October 2001
-------
TABLE OF CONTENTS
ACRONYMS iV
GLOSSARY vi
EXECUTIVE SUMMARY ix
1. INTRODUCTION 1-1
1.1 PURPOSE AND SCOPE 1-1
1.2 OBJECTIVES 1-1
1.3 REPORT ORGANIZATION 1-1
2. PROBLEM FORMULATION 2-1
2.1 OVERVIEW OF STUDY SITE 2-1
2.2 CHEMICAL SOURCES 2-1
2.3 RECEPTORS OF CONCERN 2-3
2.4 ASSESSMENT AND MEASUREMENT ENDPOINTS 2-4
2.5 CONCEPTUAL SITE MODEL 2-5
3. EXPOSURE CHARACTERIZATION 3-1
3.1 CHEMICAL CONCENTRATIONS 3-1
3.1.1 Measured Concentrations 3-1
3.1.2 Estimated Concentrations 3-2
3.2 EXPOSURE QUANTIFICATION 3-2
3.2.1 Wildlife 3-3
3.2.2 Aquatic Life 3-6
4. EFFECTS CHARACTERIZATION 4-1
4.1 WILDLIFE 4-1
4.1.1 Toxicity Thresholds 4-1
4.1.2 Water Quality Criteria for Wildlife 4-1
4.2 AQUATIC LIFE 4-2
4.2.1 Surface water 4-2
4.2.2 Sediment 4-3
4.2.3 Tissue Residues 4-4
5. RISK CHARACTERIZATION 5-1
5.1 WILDLIFE 5-1
5.1.1 Dose-Based Hazard Quotients 5-1
5.1.2 Water Quality Criteria-Based Hazard Quotients 5-9
5.2 AQUATIC LIFE 5-9
5.2.1 Hazard Quotients 5-9
5.2.2 Bioassays 5-18
5.2.3 Biological Criteria 5-20
Paramatrix SSS-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River I October 2001
-------
TABLE OF CONTENTS (Continued)
5.3 UNCERTAINTIES 5-25
6. CONCLUSIONS 6-1
7. REFERENCES 7-1
LIST OF FIGURES
E-l Ottawa River Site x
E-2 Risk Characterization Approach xiv
E-3 Ecological Hazard Quotient Comparison by River Segment xv
1-1 Ottawa River Site 1-2
1 -2 Framework for Ecological Risk Assessment 1-3
2-1 Right Bank of Ottawa River at River Mile 5.0 2-2
2-2 The Dura Avenue Landfill 2-2
2-3 Ottawa River Adjacent to Dura Avenue Landfill 2-3
2-4 Conceptual Model for Wildlife 2-7
2-5 Conceptual Model for Aquatic Life 2-8
5-1 Risk Characterization Approach 5-2
5-2 Chronic Hazard Quotients for Bald Eagles Feeding in the Ottawa River 5-4
5-3 Chronic Hazard Quotients for Common Terns Feeding in the Ottawa River 5-5
5-4 Chronic Hazard Quotients for Spotted Sandpipers Feeding in the Ottawa River 5-7
5-5 Chronic Hazard Quotients for Mink Feeding in the Ottawa River 5-8
5-6 Sediment HQs > 1.0 Based on ERMs and PELs Using 1998 Surface (< 24")
Sediment Data 5-15
5-7 Comparison of Sediment HQs Based on 1998 Surface (< 24") and Core (> 24")
Sediment Data 5-16
5-8 Sediment HQs > 1.0 Based on ERMs and PELs Using 2000 Surface Sediment Data 5-17
5-9 Chronic Hazard Quotients for Fish in the Ottawa River Using Tissue-Based TRVs 5-19
5-10 Deformed carp caught in the Lower Ottawa River 5-24
6-1 Ecological Hazard Quotient Comparison by River Segment 6-3
LIST OF TABLES
E-l Chemicals with Chronic HQs > 1.0 by Ecological Receptor and River Segment xiii
2-1 Ecological Receptors to be Evaluated in the SLRA and Their Routes of Exposure 2-4
K lwt>rtmg<37t<3
-------
TABLE OF CONTENTS (Continued)
2-2 Ecological Assessment and Measurement Endpoints Used in the Lower Ottawa
River SLRA 2-5
3-1 Summary of Chemistry Data Used in Wildlife and Aquatic Life SLRAs 3-2
3-2 Ingestion Rate and Body Weight Values Used for Avian and Mammalian
Receptors 3-4
4-1 Ohio EPA Water Quality Criteria for Wildlife 4-2
5-1 Chemicals with Individual Acute HQs Exceeding 1.0 5-11
5-2 Chemicals with Individual Chronic HQs Exceeding 1.0 5-12
5-3 EHQs for Divalent Metals in Surface Water 5-14
5-4 Location and Dates of Whole Sediment Toxicity Bioassays 5-20
5-5 Comparison of Sediment Chemistry from Bioassay Sample Site 09 to Sediment
Quality Guidelines 5-21
5-6 Summary Indices for Benthic Macroinvertebrates and Fish 5-22
5-7 Summary of Chronic HQs for Surface Water and Invertebrate and Fish Biotic
Indices 5-23
5-8 Sediment HQs and Invertebrate and Fish Biotic Indices 5-25
6-1 Chemicals with chronic HQs > 1.0 by ecological receptor and river segment 6-2
APPENDICES
A Exposure Data
B Toxicity Data
C Hazard Quotients
D Sediment HQ Maps
Paramatrix
Final Ecological SLRA of the Lower Ottawa River
iti
SSS-3763-001 (01/03)
October 2001
K:\wotUhgiSflWi3-Ml\SlM RfH>rt\rc
-------
ACRONYMS
ACR
Acute-Chronic Ratio
ANOVA
Analysis of Variance
AWQC
Acute Water Quality Criteria
AVS
Ac id-Volatile Sulphide
BAF
Bioaccumulation Factor
BCF
Bioconcentration Factor
BMF
Biomagnification Factor
BSAF
Biota-Sediment Accumulation Factor
COPC
Chemical of Potential Concern
DDD
Dichlorodiphenyldichloroethane
DDE
Dichlorodiphenyldichloroethylene
DDT
Dichlorodiphenyltrichloroethane
DELT
Deformities, Fin Erosions, Lesions/Ulcers, and Tumors
DOC
Dissolved Organic Carbon
EC10
Effects Concentration
EEC
Expected Environmental Concentration
EPA
Environmental Protection Agency
EPT
Ephemeroptera Plecoptera Trichoptera
EqP
Equilibrium Partitioning
ERL
Effects Range Low
ERM
Effects Range Median
HQ
Hazard Quotient
IBI
Index of Biotic Integrity
IR
Ingestion Rate
IWB2
Index of Well Being
Kow
Octanol-Water Partition Coefficient
LC50
Lethal Concentration
LD50
Lethal Dose
LICI
Lacustuary Invertebrate Community Index
LOAEL
Lowest Observed Adverse Effects Level
LTI
Limno-Tech, Inc.
NOAEL
No Observable Adverse Effects Level
Parametrix
Final Ecological SLRA of the Lower Ottawa River iv
555-3763-001 (01/03)
October 2001
K !»onhngJ7if3U763-001 \SIJU Jt
-------
ACRONYMS (Continued)
OEPA
Ohio Environmental Protection Agency
PAH
Polycyclic Aromatic Hydrocarbon
PCB
Polychlorinated Biphenyl
PEL
Probable Effect Level
RM
River Mile
SEM
Simultaneously Extracted Metals
SLRA
Screening Level Risk Assessment
SVOC
Semi-Volatile Organic Compound
TEL
Threshold Effect Level
TRV
Toxicity Reference Value
TU
Toxic Unit
UCL
Upper Confidence Limit
U.S. EPA
United States Environmental Protection Agency
U.S. FWS
United States Fish and Wildlife Service
WQC
Water Quality Criteria
WQS
Water Quality Standard
Paramatrix
Final Ecological SLRA of the Lower Ottawa River
V
SSS-3763-00I (01/03)
October 2001
X\worktogiJ7t3\J743-00I\SLAA RqtortWimi SLAAjvi.doc
-------
GLOSSARY
Acute Exposure
Acute Toxicity
Acute-Chronic Ratio
(ACR)
Additive effects
Assessment Endpoint
Background
Bioaccumulation
Bioavailability
Biomagnification
Chemicals of Potential
Concern (COPCs)
Chronic Exposure
Chronic Toxicity
Community
Conceptual Model
One dose or multiple doses occurring within a short time (1 to 7 days).
Significant probability of mortality or other effects from short-term (often
96 hours), relatively high-concentration exposure to toxic chemicals (Rand
1995).
The ratio of a chemical's acute toxicity to its chronic toxicity for the same
species (Rand 1995).
The potential for adverse effects on health due to the combined action of
two or more chemicals which have a similar mode of action. It assumes
that the combined effect of the subthreshold effects of several chemicals
could result in an adverse effect.
Explicit expressions of the actual environmental or societal value to be
protected, or the undesired effect whose probability of occurrence is
estimated in a risk assessment. Examples include extinction of an
endangered species, eutrophication of a lake, or the damage to a fishery by
water pollution (Parkhurst et al. 1996).
Chemical concentrations or intakes originating from chemical
concentrations in local environmental media unimpacted by human
activity.
The amount of chemical taken up by the organism attributable to both
bioconcentration and dietary accumulation (Rand 1995).
The degree to which a chemical is available to the target organism or
tissue.
The process by which the tissue concentration of a bioaccumulated
chemical increases as it passes up the food chain through at least two
trophic levels (minimum of three involved) (Rand 1995).
Chemicals that have been identified by the balance of available evidence as
posing potential risks to aquatic and wildlife receptors.
Multiple exposures occurring over an extended period, or a significant
fraction of the animal's or the individual's lifetime, up to the entire
duration of life.
Significant probability of effects on growth, yield, reproduction, or survival
from long-term exposure to toxic chemicals (Rand 1995).
An assemblage of populations of plants, animals, bacteria, and fungi that
live in an environment and interact with one another, forming a distinctive
living system with its own composition, structure, environmental relations,
development, and function.
A written description and visual representation of predicted relationships
between ecological entities and the chemicals that they may be exposed to.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
555-3763-001 (01/03)
October 2001
K:\wort*g\)7()\37f3-001\SL/lA tbporfftoot SLRA _vl.doc
-------
GLOSSARY (Continued)
Dose
Ecosystem
Effects Characterization
Expected Environmental
Concentration
Exposure
Exposure Assessment
Exposure
Characterization
Exposure Pathway
Exposure Route
Hazard Quotient (HQ)
LCSO
LD50
Lipophilic Chemical
Lowest Observed
Adverse Effect Level
(LOAEL)
The mass of a substance given to an organism and in contact with an
exchange boundary (e.g., gastrointestinal tract) per unit body weight per
unit time (e.g., mg/kg-day).
The biotic community and abiotic factors that interact within a specified
location in space and time.
The process for quantitatively defining the adverse effects on individuals,
populations, and communities elicited from exposure (Parkhurst et al.
1996).
The estimated concentration of chemicals in surface water, sediments, and
the food offish and wildlife (Parkhurst et al. 1996).
The contact or co-occurrence of a chemical with a receptor.
The determination or estimation (qualitative or quantitative) of the
magnitude, frequency, duration, and route of exposure to chemicals in
environmental media.
The process for quantitatively defining the expected environmental
concentrations/doses (EECs and EEDs) and pathways to which the
receptors are exposed (Parkhurst et al. 1996).
The course a chemical or physical agent takes from a source to an exposed
organism. An exposure pathway describes a unique mechanism by which
an individual or population is exposed to chemicals or physical agents at or
originating from a site. Each exposure pathway includes a source, or
release from a source, an exposure point, and an exposure route. If the
exposure point differs from the source, a transport/exposure medium (e.g.,
air) or media (in cases of intermedia transfer) is/are also included.
The mechanism by which a chemical or physical agent comes in contact
with an organism (i.e., by ingestion, inhalation, dermal contact).
The ratio of the concentration or dose of a chemical over the concentration
or dose at which no adverse effects of any kind are ejected. When HQs
are less than one, negligible risks are expected.
Median lethal concentration; the concentration causing death to SO percent
of the test organisms (Rand 1995).
Median lethal dose; the dose causing death to 50 percent of the test
organisms (Rand 1995).
Chemicals that have a propensity to partition into lipids (i.e., fatty tissue),
rather than water.
In dose-response experiments, the lowest exposure level at which there are
statistically or biologically significant increases in frequency or severity of
adverse effects between the exposed population and its appropriate control
group.
Param*trlx
Final Ecological SLRA of the Lower Ottawa River
vii
555-3763-001 (01/03)
October 2001
H WmUitUMJU W-OiUSiJU Ktp»mrinalSlM_vlAe
-------
GLOSSARY (Continued)
Measurement Endpoint
No Observed Adverse
Effect Level (NOAEL)
Off-River Water Bodies
Population
Problem Formulation
Receptor
Risk
Risk Characterization
Screening
Toxicity Reference Value
(TRY)
Trophic Levels
Upper Bound
An expression of an observed or measured response to a hazard; it is a
measurable environmental characteristic that is related to the valued
characteristic chosen as the assessment endpoint (Parkhurst et al. 1996).
In dose-response experiments, an exposure level at which there are no
statistically or biologically significant increases in frequency or severity of
adverse effects between the exposed population and its appropriate control;
some effects may be produced at this level, but they are not considered to
be adverse, nor precursors to specific adverse effects. In an experiment
with more than one NOAEL, the regulatory focus is primarily on the
highest one, leading to the common usage of the term NOAEL to mean the
highest exposure level without adverse effect.
Tie channels, oxbow lakes, blocked valley lakes, swamps, lagoons,
periodically flooded forest, and any other body of water that is directly
affected by the river but not part of the main stream.
A potentially interbreeding group of individuals of a single species.
The step where goals of the risk assessment are defmed and exposure
routes for stressors (chemicals) are identified.
Wildlife species for which risk from chemical exposure is being evaluated.
The likelihood of a prescribed undesired effect, such as injury, disease or
death, resulting from human actions or a natural catastrophe (Parkhurst et
al. 1996).
The process that defines the potential for or probability of adverse effects
to the receptor population given exposure to a range of expected
environmental concentrations (EECs).
A risk assessment process in which conservative estimates of exposure and
toxicity are used to identify chemicals that pose negligible risks. Chemicals
so identified are referred to as being "screened out".
Toxicity threshold for aquatic or wildlife receptor.
A functional classification of taxa within a community that is based on
feeding relationships.
An estimate of the plausible upper limit to the true value of the quantity.
This is usually not a statistical confidence limit.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
555-3763-001 (01/03)
October 2001
K: \»t>rk*it>3?i3\)763-001\SlKA RtporrfitulSLRA_vl doe
-------
EXECUTIVE SUMMARY
An ecological screening-level risk assessment (SLRA) of the lower Ottawa River was conducted as an
initial effort to prioritize chemical hot spots for possible remediation. The SLRA followed the U.S.
EPA's standard ecological risk assessment guidelines and included the following sections: (1) Problem
Formulation; (2) Exposure Characterization; (3) Effects Characterization; and (4) Risk Characterization.
The Problem Formulation stated the goals of the SLRA, described the study area, and identified the
ecological receptors evaluated. The Exposure Characterization described the chemistiy data available and
the methods for quantifying exposure of ecological receptors to chemicals. The Effects Characterization
presented the Toxicity Reference Values (TRVs) used for comparison to the chemical exposure levels.
Lastly, the Risk Characterization compared the Exposure and Effects Characterization results to estimate
whether ecological receptors are at risk from chemicals in the lower Ottawa. Multiple lines of evidence
were included in the Risk Characterization to provide an overall weight-of-evidence. The following
summarizes each of these SLRA sections.
PROBLEM FORMULATION
Potential chemical risks in the lower 9 miles of the Ottawa River were assessed (Figure E-l). Chemical
sources to this reach of the Ottawa include various industries, landfills, textile producers, and fertilizer
manufacturers. Chemicals of interest from historical investigations include polychlorinated biphenyls
(PCBs), polycyclic aromatic hydrocarbons (PAHs), and metals. For consistency with Ohio EPA
management goals, potential risks were estimated separately for five different segments of the lower
Ottawa River: river miles (RMs) 0 to 3.2,3.2 to 4.9,4.9 to 6.5,6.5 to 8.8, and > 8.8. Wildlife receptors
evaluated included the bald eagle (Haliaeetus leucocephalus), common tern (Sterna hirundo), spotted
sandpiper (Actitus macularia), and mink (Mustela vison). Potential risks to the bald eagle were also
evaluated in North Maumee Bay since there have been reports of unsuccessful breeding in this area. In
addition, potential risks to the aquatic community (fish, invertebrates) were also evaluated. These
receptors were selected because they are known to use the lower Ottawa River as habitat and/or for
feeding and they represent a range of exposure routes (e.g., fish-eaters, invertebrate-feeding probers,
direct contact with water and sediment).
EXPOSURE CHARACTERIZATION
Chemistiy data for sediment, fish tissue, and surface water samples collected during summer of 2000
were used to quantify exposure of all ecological receptors. In addition, sediment data collected in 1998
from various depths were also included in the aquatic life assessment (wildlife were considered to receive
combined exposures through sediment, tissue, and water ingestion, so only the temporally co-located data
from 2000 were used for these receptors). Both acute (short-term) and chronic (long-term) chemical
exposures were evaluated in each river segment. Conservative estimates of mean1 and upper bound2
chemical concentrations were used to approximate chronic and acute exposure concentrations,
respectively.
For aquatic life, chemical concentrations in sediment, tissue, and surface water were used directly to
estimate exposure. Wildlife exposures were estimated by calculating species-specific doses. Chemical-
specific doses for wildlife were estimated as milligram chemical per kilogram body weight per day
1 The 95 percent upper confidence limit (UCL) on the mean.
2 The 95 percentile of all the data.
Paramatrlx 5SS-3763-00J (01/03)
Final Ecological SLRA cfthe Lower Ottawa River ix October200J
K:*0er**fJT*S&LMAq><>rtrtnalSIJ
-------
R.M. Q.Q
^ Lower Ottawa River Base Map
Showing Reach Designations
Ohio
R.M. d
\
Parametrix 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa Rrver x October 2001
K \woriungtf76M763-001\SLRA Report Figuia for FINAL Dra»Flgure E 1 & I 1 doc
-------
(mg/kg/d). The doses were calculated using the chemistry data and wildlife receptor body weights and
ingestion rates (food, sediment, and water). It was conservatively assumed that wildlife receptors could
receive 100 percent of their chemical dose from an individual river segment, and that all chemicals in
each medium were completely absorbed following ingestion. Bald eagles, common terns, and mink were
assumed to feed exclusively on fish. Both of these assumptions are more likely to over- rather than
undeipredict risk potential. For sandpipers, which feed predominantly on macroinvertebrates in the
sediment, chemical concentrations in invertebrates were estimated from sediment concentrations where
recognized methods exist.3
EFFECTS CHARACTERIZATION
Toxicity data were identified for comparison to the estimated exposure levels calculated in the Exposure
Characterization. For wildlife, acute and chronic toxicity data (expressed as doses) were compiled.
These toxicity data were generally based on surrogate test animals (e.g., rats, mallards), but mink toxicity
data for some chemicals were available. The acute toxicity data were based on mortality, while chronic
toxicity data were based on mortality or sublethal endpoints such as reproduction, growth, and
development.
Sediment and tissue- and water-based toxicity data were all compiled for aquatic life. Sediment toxicity
data were compiled from numerous sources, including the scientific literature and government agencies
(e.g., Environment Canada, Ontario Ministry of the Environment). Multiple sediment guidelines for
individual chemicals were often compiled, when available. This provides a weight of evidence when
evaluating sediment risks since site-specific factors can have substantial impacts on chemical
bioavailability in sediment. Tissue-based toxicity data were also compiled for chemicals detected in fish
tissue. These toxicity data are quite limited compared to water-based toxicity data, but provide a useful
approach for assessing potential risks to fish for chemicals that are hydrophobic and/or tend be passed
through dietary pathways rather than directly from the water column (e.g., PCBs). Lastly, water-based
toxicity data were compiled for comparison to water chemistry data. When available, Ohio EPA water
quality criteria (WQC) or U.S. EPA WQC were used. These WQC are designed to be protective of
aquatic communities. If WQC were not available, the lowest chemical-specific toxicity data identified for
individual species were used to assess water column risks. Both acute and chronic water-based toxicity
data were compiled (only chronic sediment and tissue-based toxicity data were compiled because
concentrations in these media tend to represent long-term accumulation).
RISK CHARACTERIZATION
Potential risks to ecological receptors were estimated by comparing the exposure levels calculated in the
Exposure Characterization to the effects levels identified in the Effects Characterization. Thus, for
wildlife, calculated exposure doses for avian and mammalian receptors were compared to their respective
TRVs. For aquatic life, mean and upper bound exposure concentrations in sediment, tissue, or water were
compared directly to their respective media-specific TRVs. These ratios of exposure levels to toxicity
levels, for both wildlife and aquatic life, are termed hazard quotients (HQs). An HQ less than 1.0
suggested that a receptor was not at risk, while an HQ greater than 1.0 suggested a receptor may be at
3 Benthic tissue concentrations were estimated only for non-polar, lipophilic organics.
Paramatrlx
Final Ecological SLRA of the Lower Ottawa River
xi
S53-3763-001 (01/03)
October 2001
I£ Wttiftj»JU7H-007lSXJM RtporlWlml SLRA_*ldcx
-------
risk4. Given the conservative assumptions used in the SLRA, chemicals with HQs greater than 1.0 should
be further evaluated in a detailed assessment with additional site data to determine whether they are truly
of concern. Accordingly, these were referred to as chemicals of potential concern (COPCs) in the SLRA.
The COPCs for wildlife and aquatic life are discussed separately below. The risk characterization
approach is summarized in Figure E-2.
Wildlife
Chemistry Data
Acute HQs for wildlife were almost always less than 1.0. The only exceptions were a lead HQ of 3.9 for
RMs 4.9 to 6.5 and a zinc HQ of 1.1 for RMs 6.5 to 8.8. These HQs were calculated for the spotted
sandpiper and were influenced by incidental sediment ingestion (the spotted sandpiper has a high
sediment ingestion rate since it feeds by probing the sediment for food). Zinc is likely not of concern for
the sandpiper given that the HQ only slightly exceeded 1.0. However, lead appears to be a COPC within
RMs 4.9 to 6.5 because it is highly affected by a single sediment sample with an elevated lead
concentration of 13,000 mg/kg-wet (parts per million) at RM 5.5. Although acute HQs for other metals
did not exceed 1.0 for this reach, it was noted that maximum concentrations of several other metals within
this river segment were found in the same sediment sample. Accordingly, this portion of the river
represents a possible hot spot of metal contamination.
Chronic HQs for lead and PCBs exceeded 1.0 in at least one river segment for all wildlife receptors (i.e.,
bald eagle, common tern, spotted sandpiper, and mink). Like the acute assessment, the largest chronic
HQs for lead, ranging from 2.6 (bald eagle) to 254 (mink), occurred between RMs 4.9 and 6.5. Lead
chronic HQs between 1.0 and 6.0 were calculated for mink for the other river segments as well, but it is
likely that lead is not actually of concern in these segments since the HQs only slightly exceeded 1.0 and
because it was conservatively assumed that mink fed exclusively in any one of the individual river
segments. PCB chronic HQs exceeded 1.0 for all receptors between RMs 3.2 to 4.9,4.9 to 6.5, and 6.5 to
8.8. The HQs were largest for fish-eating receptors (bald eagle [1.3 to 4.4], common tern [6.7 to 22], and
mink [0.6 to 1.9]), likely reflecting the potential for PCBs to biomagnify (i.e., increase in concentration up
the food chain). The PCB HQs increase slightly from downstream to upstream, but were quite similar in
magnitude, suggesting that PCB contamination is not substantially elevated in any single river segment.
Chronic HQs for the pesticide DDT also exceeded 1.0 for the eagle, tern, and sandpiper, with HQ ranges
of 0.15 to 1.7, 0.75 to 8.7, and 0.65 to 1.7, respectively. The largest HQs for DDT occurred above RM
8.8 and decreased to less than 1.0 in the lower river miles.
To identify river segments posing the greatest potential risk, all chemical HQs greater than 1.0 (i.e., the
risk drivers) were summed by river segment and wildlife receptor (Figure E-3). As shown, Segment 3
(RM 4.9 to 6.5) poses the greatest potential to all wildlife receptors, Potential risks were also identified in
the other river segments, but at lower levels. In general, the lowest potential risk for wildlife receptors
was identified in Segment 1 at the mouth of the Ottawa River (RM 0 to 3.2). The chemicals with HQs
greater than 1.0 by river segment and wildlife receptor are shown in Table E-l. However, it should be
emphasized that the chemicals listed in Table E-l do not contribute equally to potential risk for a given
4 It is not possible to reasonably differentiate chemicals as posing low, moderate, or high potential risk for those with
HQs greater than 1.0, because the conservatism in the data and assumptions used are chemical-specific. As a
general guideline, however, HQs greater than 10 likely suggest a high potential risk.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
xii
SSS-3763-001 (01/03J
October 2001
K: \worUnf\3763\37i3-HOfSLMRtporl\rimlSLRA^l
-------
wildlife receptor and river segment. As shown by the magnitude of the HQs (Table E-l), lead and PCBs
appear to be the risk drivers for wildlife.
Using fish tissue concentration data from North Maumee Bay, potential risks to the bald eagle were also
estimated. Like the lower Ottawa River assessment, the chronic PCB HQ (2.8) exceeded 1.0. The HQs
did not exceed 1.0 for any other chemicals measured. These results suggest that potential PCB risks to
the bald eagle (and similar higher-trophic fish-eating wildlife) are fairly widespread in the lower Ottawa
River region. Accordingly, even if it were more realistically assumed that the eagles feed throughout a
much larger area than that assumed in the SLRA, potential risks would still likely be estimated.
Table E-1. Chemicals with Chronic HQs > 1.0 by Ecological Receptor and River Segment.
Receptor
Segment 1
(RM 0-3.2)
Segment 2
(RM 3.2-4.9)
Segment 3
(RM 4.9-6.5)
Segment 4
(RM 6.5-8.8)
Aquatic Life - Pelagic
Aluminum (30)®
Aluminum (25)
Aluminum (14)
Aluminum (13)
Iron (4.3)
Iron (4.2)
Iron (2.8)
Iron (1.9)
Manganese (17)
Manganese (19)
Manganese (68)
Manganese (24)
Aquatic Life - Benthic
Lead (1.2)
Lead (3.2)
Cadmium (1.2)
Chromium (1.1)
Nickel (1.3)
Nickel (1.1)
Chromium (1.2)
Copper (1.0)
PCBs (2.2)
PCBs (11)
Lead (199)
Nickel (1.2)
PCBs (11)
Lead (3.6)
Zinc (1.1)
PCBs (11)
Bald Eagle
PCBs (1.3)
PCBs (4.3)
Lead (2.6)
PCBs (3.5)
PCBs (2.9)
Common Tern
Selenium (1.1)
PCBs (22)
Lead (13)
PCBs (15)
PCBs (6.8)
DDT (1.9)
Selenium (1.2)
PCBs (18)
DDT (2.4)
DDT (4.0)
Spotted Sandpiper
Aluminum (1.7)
Aluminum (1.9)
Aluminum (1.6)
Aluminum (1.6)
PCBs (2.7)
Chromium (1.0)
Chromium (2.3)
Chromium (2.3)
Lead (1.0)
Lead (71)
Lead (1.4)
PCBs (17)
PCBs (11)
DDT (1.6)
Cyanide (1.2)
PCBs (11)
DDT (1.7)
Mink
Aluminum (16)
Aluminum (18)
Aluminum (15)
Aluminum (15)
Lead (1.7)
Iron (1.0)
Lead (254)
Lead (6.0)
Selenium (1.6)
Lead (4.1)
Selenium (1.6)
Selenium (1.1)
Thallium (1.7)
Thallium (2.1)
Thallium (1.5)
Thallium (2.7)
PCBs (1.9)
' Value in parentheses it the chronic HQ.
Paramatrix SS5-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River xiii October 200J
JC \work*&763\1763WSUU AtportVlna!SlAA_vl.dot
-------
-~Unused Data
North Maumee Bay
Lower Ottawa
River
i t
Biocriteria
Bioassays
WATER
TISSUE
Data Base
SEDIMENT
Hazard Quotients
for Wildlife
Water
Quality
Criteria
for
Wildlife
Compare to Bird
Toxicity Data
Calculate Dose
for Bald Eagle
Assess Potential
Risk to Wildlife
Compare to
Sediment
Guidelines
Hazard Quotients
for Bald Eagle
WATER
SEDIMENT
TISSUE
Hazard Quotients
for Aquatic Life
Hazard Quotients
forBenthic Aquatic
Life
Calculate Dose for
Bird and Mammal
Receptors
Calculate Summary
Statistics
Map of Key Sediment
COPCs
Compare to Bird
and mammal Toxicity
Data
Assess Potential
Risk to
Aquatic Life
Assess Potential
Risk to Bald Eagles
in Maumee Bay
Compare to Water
Quality Criteria or
Toxicity Data
(Acute & Chronic)
Identify Chemicals with a
Detection Frequency of >5%
Ottawa River
- 2000 Tissue Data
- June 2000 Sediment and Water Data
- North Maumee Bay 1999 Fish Tissue Data
-1998 Sediment Data
Parametrix, Inc. otuwa R*»rsuws55-3763-ooi/cn(03) 7/01 (k>
Figure E-2
Risk Characterization Approach
-------
Ecological Hazard Quotient Comparison by River Segment
9 Aquatic Life-Pelagic
H Aquatic Life-Benthic
D) Bald Eagle
ES Common Tern
B Spotted Sandpiper
¦ Mink
i
1
1
I
I
Segment 1
RM 0-3.2
Segment 2
RM 3.2-4.9
Segment 3
RM 4.9-6.5
Segment 4
RM 6.5-8.8
Pelagic aquatic life HQs driven by ubiquitous metals and are likely extremely conservative.
-------
Other Lines of Evidence for Wildlife Risk Potential
In addition to the dose-based HQs described above, potential risks to wildlife were estimated using Ohio
EPA WQC for wildlife. Mercury was the only chemical detected in surface water for which a wildlife
criterion was available. The mercury HQs using this line of evidence were very large, ranging from 113
to 177. These results are not consistent with the dose-based HQs above, where none of the mercury HQs
exceeded 1.0. Accordingly, potential risks posed by mercury were uncertain. The wildlife criterion for
mercury is based on mercury bioaccumulation from water into aquatic prey items, while the dose-based
HQs are calculated using mercury concentrations measured in Ottawa River fish tissue. It may be that the
wildlife criterion greatly overestimated mercury's bioaccumulation potential in the Ottawa River.
Aquatic Life
Potential risks to aquatic life were considered by separately evaluating HQs based on chemistry data for
surface water, tissue, and sediment. Sediment bioassay results and biological monitoring data were used
as additional lines of evidence for comparison to the HQs.
Surface Water
Acute HQs exceeded 1.0 for aluminum (1.5 to 4.6) and manganese (3.8 to 21.2), while chronic HQs
exceeded 1.0 for aluminum (12.7 to 30), manganese (17 to 68), iron (1.9 to 4.3), and selenium (1.3 to
3.0). The significance of the HQs for all of these metals is uncertain for various reasons. For example,
aluminum, manganese, and iron are fairly ubiquitous metals that can exist in particulate forms that are
non-bioavailable to aquatic biota. Since total metal concentrations were measured in the surface water,
non-bioavailable forms were likely included in the chemical analysis, and it is likely that the HQs for
these metals are largely overestimated. The chronic HQ for selenium is uncertain because the potential
for selenium to pose risk to aquatic life is highly site-specific. Selenium toxicity is manifested via dietary
exposure routes rather than through the water, and the amount of selenium in the diet depends on site-
specific conditions. A better way to assess potential selenium risks is through the use of tissue residue
data for fish, which is described further in the next section. Several acute and chronic HQs also exceeded
1.0 for some organic chemicals, and polycyclic aromatic hydrocarbons (PAHs) in particular. However,
these chemicals were rarely detected (detection limits were well above PAH WQC) and, when they were,
only at concentrations equal to the detection limit. Accordingly, the exposure estimates for these
chemicals are heavily influenced by the detection limits for these chemicals. Regardless, given the
hydrophobicity of these chemicals, they are more appropriately addressed through the direct evaluation of
sediment chemistry data rather than water quality data.
Tissue
As mentioned above, fish tissue chemistry data were also used to assess potential risks to aquatic life
through direct comparison to toxicity data based on tissue residue. Consistent with the general pattern
observed for wildlife receptors, HQs for lead and PCBs exceeded 1.0, with HQ ranges of 0.7 to 4.4 and
0.7 to 2.1, respectively. The lead HQs were largest above RM 8.8 and followed a generally decreasing
pattern from upstream to downstream. Since fish are mobile, it is not possible to confidently link the fish
concentrations to sources, but the data do provide confirmation that lead and PCBs appear to pose a
potential for widespread risk in the lower Ottawa. The selenium concentrations in fish tissue were below
Parametrix
Final Ecological SLRA of the Lower Ottawa River
xvi
555-3763-001 (01/03)
October 2001
K \work*t&7tMm-001'SIM HtportiFlmlSLItAjfl diK
-------
tissue-based toxicity thresholds, suggesting that the chronic HQs calculated for surface water were
overestimating the potential risk to aquatic life posed by selenium.
Sediment
Chemical concentrations in sediment were compared to sediment quality guidelines from various sources.
Sediment data collected in both 1998 and 2000 were used (separately) to assess potential risks to aquatic
life. The 1998 sampling was more widespread than the 2000 sampling, and also included the collection
of core samples. The biological relevance of these data is uncertain since they reflect concentrations from
depths greater than the biologically active zone. While fewer samples were collected in 2000, the data
reflect conditions in the biologically active top 10 cm of sediment. Accordingly, the 2000 data represent
more recent and realistic exposure conditions. Based on the 1998 surface data (depths less than 24"), the
key COPCs identified from RMs 0 to 8.8 were lead and PCBs. Cadmium and chromium were also
identified as COPCs between RMs 3.2 to 4.9. These four chemicals were all considered COPCs because
they exceeded at least one sediment guideline based on a high probability for effects. The true risks
posed by these chemicals are unknown without further study because there are a number of factors in
sediment that can influence chemical bioavailability. Hazard quotients for PAHs reached as high as 0.5
between RMs 6.5 to 8.8 using recently derived guidance. Although the highest HQ for PAHs was less
than 1.0, recent studies suggest that the number of PAHs present and potentially contributing to toxicity is
often more than the number typically measured. Accordingly, if the full suite of PAHs was measured, it
is possible that the HQ would exceed 1.0. The HQs for sediment COPCs tended to decrease at depths
greater than 24", probably as a result of the larger compositing volumes.
Using the 2000 sediment data, lead and PCBs were again identified as COPCs. Additional COPCs
identified in one or more river segments included other metals (e.g., cadmium, chromium, and nickel) and
organochlorine pesticides (e.g., DDD, DDE, dieldrin, and heptachlor epoxide). All of these COPCs
(metals, PCBs, and organochlorine pesticides) are very persistent in sediment and thus may reflect both
current and historical sources to the river. Acid volatile sulfide-simultaneously extracted metal
(AVS:SEM) data were available to assess whether cationic metals in sediment would be bioavailable to
aquatic biota (AVS is the primary partitioning phase controlling cationic metal activity and toxicity in the
sediment-pore water system). If the simultaneously extracted sum of molar concentrations of cadmium,
copper, lead, nickel, silver, and zinc are less than the molar AVS concentrations, toxicity will not be
observed. Of the 19 AVS:SEM samples, the molar ratio of SEM (based on the sum of cadmium, copper,
lead, nickel, silver, and zinc) to AVS was always greater than 1.0 (mean, minimum, and maximum were
1,664, 1.1, and 8,562, respectively). Accordingly, the AVSrSEM data could not be used to support an
absence of metal toxicity in sediment.
The sum of sediment-based HQs greats' than 1.0 for aquatic life are plotted in Figure E-3 by river
segment. Consistent with the wildlife receptors, the highest potential risk to benthic aquatic life was
identified in Segment 3 (RM 4.9 to 6.5). The driver chemical was lead in this river segment, with other
heavy metals (cadmium, chromium, nickel) and PCBs also contributing to the potential risk (Table E-l).
As mentioned previously, it should be noted that the chemicals listed in Table E-l do not contribute
equally to the potential risk for a given river segment (the HQs associated with each chemical are noted in
parentheses next to its respective chemical). Potential risks to benthic aquatic life were also identified in
the other river segments, but at lower levels. The lowest potential risk, as for wildlife, was identified at
the river mouth (Segment 1, RM 0 to 3.2) (Figure E-3).
Paranwtrlx 5JS-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River xvit October 200J
X \wortt*gV763\J763-OOJVMA
-------
Other Lines of Evidence for Aquatic Risk Potential
As mentioned above, sediment bioassays and biological monitoring results were also used as additional
lines of evidence for evaluating potential risks to aquatic life. A total of ten sediment bioassays were
conducted with either the amphipod Hyalella azteca or the oligochaete worm Lumbriculus variegatus.
All bioassays were short-term (i.e., acute toxicity) tests, and no toxicity was observed in any test. In one
sediment sample, chemistry data were also collected. Although some concentrations exceeded sediment
guidelines, the absence of toxicity from the acute bioassays does not necessarily suggest that the
guidelines are overly conservative for the site. It is possible that toxicity would have been observed if
long-term (i.e., chronic) bioassays were conducted, because these are based on more sensitive toxicity
endpoints (growth and reproduction rather than just survival).
The second additional line of evidence used in assessing potential risks to aquatic life was biological
monitoring data. These data include indices of fish and macroinvertebrate abundance and species
richness. The river segments with the highest predicted HQs did not always correspond with the locations
having the lowest (poorest) biological index scores. Nevertheless, this line of evidence confirmed that
fish and macroinvertebrate communities are being impacted in the lower Ottawa River.
CONCLUSIONS
Lead and PCBs were consistently identified as COPCs for both wildlife receptors and aquatic life. Lead
was primarily identified as a COPC due to its concentrations in sediment, but concentrations in fish tissue
also reached levels that have been shown in the laboratory to be directly toxic to fish. Based on the year
2000 sediment data, the largest lead concentration was measured at RM 5.5. This sample also contained
maximum concentrations of other metals between RMs 4.9 to 6.5. Accordingly, the river segment from
which this sample was collected (Segment 3) was identifying as posing the highest risk to both wildlife
and aquatic life (Figure E-3). The PCB HQs for wildlife were influenced by PCB concentrations in fish
tissue, which were fairly similar in magnitude along multiple river segments. Similarly, sediment-based
PCB HQs for aquatic life were comparable in magnitude across multiple river segments. Accordingly,
potential PCB risks to wildlife and aquatic life are fairly evenly distributed throughout the lower Ottawa
River. The risks posed by PAHs to bottom- dwelling aquatic organisms are more uncertain. Although
the maximum HQ calculated was 0.5, it is possible that HQs of greater than 1.0 would be calculated if all
PAHs and their substituted derivatives were measured. The biological monitoring results support that fish
and macroinvertebrate communities are being impacted. Additional data that could improve hot spot
delineation include temporally and spatially co-located chemistry sampling, with bioassays using more
sensitive (chronic) effect endpoints.
Parametrix
Final Ecological SLRA of the Lover Ottawa River
xviii
555-3763-001 (01/03)
October 2001
K \woMng\37S3\JM3-OOIUIJURtpor!finalSUU^I doc
-------
INTRODUCTION
1.1 PURPOSE AND SCOPE
The Ottawa River is an urban waterway that drains into North Maumee Bay, Lake Erie (Figure 1-1).
There are numerous potential sources of chemicals to the river, including several landfills. Being a
tributary to Maumee Bay, the Ottawa River is part of the Maumee Area of Concern, designated in 1985
by the International Joint Commission.5 In 1991, the Ohio Department of Health issued a fish
consumption/contact advisory for the lower 8.8 miles of the river (see Figure 1-1). This advisory was
based on polychlorinated biphenyl (PCB) concentrations in sediment and fish tissue. In addition to PCBs,
concentrations of heavy metals, pesticides, and other chemicals were also known to be elevated in Ottawa
River sediment and tissue. The purpose of this ecological screening-level risk assessment (SLRA) is to
assist in prioritizing areas of the lower Ottawa River for possible remediation.
1.2 OBJECTIVES
Based on the purpose and scope of the SLRA, three main objectives were identified. The first objective
was to identify die nature and magnitude of potential risks to wildlife and aquatic life under recent
conditions within the Ottawa River. The subsequent second and third objectives were to identify
chemicals of potential concern and prioritize locations within the Ottawa River for possible remediation
action.
1.3 REPORT ORGANIZATION
The general methods used in the ecological SLRA follow U.S. EPA guidelines for conducting ecological
risk assessments at Superfund sites (U.S. EPA 1997). Accordingly, this ecological SLRA consists of four
primary components: (1) Problem Formulation; (2) Exposure Characterization; (3) Effects
Characterization; and (4) Risk Characterization (Figure 1-2). The Problem Formulation focuses on
defining site issues and management goals and how these goals are incorporated in the SLRA process. As
such, the Problem Formulation section of this document describes the study area and summarizes the key
risk assessment issues and how they are evaluated to help meet the overall management goals. This
information is also used to support the ecological receptors selected and evaluated in the Exposure
Characterization, and how their exposure is estimated. The Exposure Characterization describes in detail
how chemical exposures to the ecological receptors are quantified. The Effects Characterization presents
the toxicity thresholds or guideline values that are compared to the exposure estimates. Lastly, the Risk
Characterization methods describe how screening potential risks are quantified by integrating the
Exposure and Effects Characterizations, as well as by considering other lines of evidence.
5 The Maumee Area of Concern stretches from the lower 23 miles of the Maumee River to Maumee Bay and Lake
Erie. The Area of Concern includes 3,942 miles of several streams, including the Ottawa River.
555-3763-001 (01/03)
October 2001
£ WJU7M-0W \SIAA Rtpcn\rmalSUUj»lik<
Parametrix
Final Ecological SLRA of the Lower Ottawa River
1-1
-------
RM C.0
^ Lower Ottawa River Base Map
Showing Reach Designations
R.M. 3
RM. 4.9
KM. &.
\
*5sr A
' > h
SMftUnt
Lowe OBawa rvwp"
Parametria 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River x October 2001
^ K;\working,0763\3763-001\SLRA Report\Figura for FINAL DraffcFigure E 1 & I 1 doc
-------
Itiil
I Characterization
I Of Ecological
I Effects
Characterization
Of Exposure
a*#: V ;
. Communicating Results fro
interested Parties
Planning
(Risk Assessor I
Risk Manager/.,
Interested
Parties dialogue)
Discussion Between the
Risk Assessor and Risk
Manager (Results)
Ecological Risk Management
>
<0
Z
ft»
0
(6
01
3
2 >
o rt
3 Xi
jjy C
5 I
3g
V) »
e sr
»>•> ¦
w ¦¦»
<»
I
"0
o
o
(D
Figure 1-2
Framework for Ecological Risk Assessment
(Modified from U.S. EPA 1992)
-------
2. PROBLEM FORMULATION
Ecological risk assessments are designed and conducted to provide information on ecological risk
potential to risk managers to assist in identifying management decisions appropriate to the site (U.S. EPA
1998a). Accordingly, understanding the management goals is critical and influences how issues arc
addressed in the risk assessment. A primary management goal for the Ottawa River SLRA is to identify
locations of chemical hot spots in the lower portion of the river and to prioritize these areas for possible
future remediation or additional risk assessment. The remainder of this section discusses how the river
was divided into segments and identifies the ecological receptors that were evaluated,
2.1 OVERVIEW OF STUDY SITE
The lower 9 miles of the Ottawa River represent the critical reaches of the river to be evaluated in the
SLRA (specifically, the river mouth to river mile [RM] 8.8) (see Figure 1-1). The river flows through a
primarily industrialized area in the city of Toledo, but there is limited development along the banks, and
significant riparian zones are present (OEPA 2000). LTI (2000) summarized the distinct zones over this
stretch of the river. From RMs 8.8 to 7.0, the river is relatively free-flowing with unidirectional flow.
The river flows through a transitional zone from RMs 7.0 to 2.5. In this zone, flow velocities are
considerably slower and flow reversals occur in some areas. Bathymetry data suggest that there are two
"basins" in this reach, above and below approximately RM 4.0. Downstream of RM 2.5, the magnitudes
of flows and frequencies of flow reversals increase.
Based primarily on field observations of human and wildlife uses of the river, the OEPA provided
additional characterization of the river (Williams 2000, personal communication). For example, between
river RMs 6.5 to 8.8, children have been observed fishing and wading in the river. Between RMs 4.9 to
6.5, there are signs of human use, including dirt bike trails and public access where fishing may occur.
Wildlife, including turtles and waterfowl, have also been observed between these river miles which
includes wetland habitat. Between RMs 3.2 to 4.9, a depositional zone exists with large areas of exposed
sediment under low flow conditions. Turtles and waterfowl have also been observed in this area of the
river, as well as children walking along the river banks and fishing at RM 3.6. Lastly, from RM 0 to 3.2,
the river widens and experiences high recreational use and frequent flow reversals. Wildlife, including
waterfowl, have also been observed between these river miles.
Thus, the lower Ottawa River contains a variety of habitats and potential chemical exposure pathways for
ecological receptors. The Ottawa River was delineated into five river segments based on the above
considerations: RMs 0 to 3.2 (Segment 1 [mouth]), RMs 3.2 to 4.9 (Segment 2), RMs 4.9 to 6.5
(Segment 3), RMs 6.5 to 8.8 (Segment 4), and > RM 8.8 (Segment 5). Figures 2-1, 2-2, and 2-3 show the
urban nature of the river.
2.2 CHEMICAL SOURCES
Numerous potential sources of chemical contaminants were identified in the Ottawa River Geographic
Initiative Work Plan (OEPA 2000). These sources include mostly industries and landfills, but also
include textile producers and fertilizer manufacturers. Many of these sources are shown in Figure 1-1.
Several landfills, such as the Tyler Street Landfill, Stickney Avenue Landfill, and Dura Avenue Landfill,
have been chemical sources to the Ottawa River, including heavy metals, semi-volatile organics, volatile
organics, and PCBs (OEPA 2000). Many of the potential source sites identified no longer have ongoing
operations, and several have undergone remediation. The Tyler Street, Stickney Avenue, and Dura
Avenue landfills, for example, have all been capped.
Parametrix S5S-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 2-1 October 200}
JC \working\3763lS763J)OI \S£M Rf>crt\ftnaISLRA_VI.£hc
-------
Figure 2-1 Right Bank of Ottawa River at River Mile 5.0
mmm
Figure 2-2 The Dura Avenue Landfill
Parametrix 555-3763-00I (01/03)
Final Ecological SLRA of the Lower Ottawa River 2-2 October 2001
it iwontnfU ?6]VJ7tJ-001ULRA Rtpon\rin>ISlM_yl.
-------
Figure 2-3 Ottawa River Adjacent to Dura Avenue Landfill
2.3 RECEPTORS OF CONCERN
Several receptors were evaluated in the SLRA. The avian and mammalian receptors selected for
evaluation were: (1) bald eagle (Haliaeetus leucocephalus), (2) common tern (Sterna hirundo), (3)
spotted sandpiper (Actitus macularia), and (4) mink (Mustela vison). The bald eagle was selected
because it feeds on fish and has been reported to feed in the area. Furthermore, there have been reports of
unsuccessful breeding in North Maumee Bay (DeVault 2000, personal communication). The common
tern was identified as a second fish-eating bird receptor because it is expected to feed throughout the
lower Ottawa River (Shieldcastle 2000 personal communication) and has a higher ingestion rate relative
to body weight than the bald eagle, and thus is a more highly exposed receptor. The spotted sandpiper
was selected as a representative invertebrate-eating bird and is common in reaches of the river with
appropriate habitat (Shieldcastle 2000 personal communication). The exposure potential of the sandpiper
is quite different from bald eagles or terns because invertebrates tend to bioaccumulate chemicals
differently than fish. In addition, being a probing bird, they tend to have higher sediment ingestion rates
than many other fish-eating birds. Lastly, the spotted sandpiper has a smaller home range than bald
eagles (U.S. EPA 1993a). Thus, it is likely to receive a greater portion of its diet from the Ottawa River.
In summary, bird receptors were selected that are most appropriate for chemicals that bioaccumulate in
high levels in fish tissue (eagle, tern) and that are most appropriate for chemicals that are elevated in
sediment (sandpiper).
Parametrix
Final Ecological SLRA of the Lower Ottawa River
2-3
SSS-3763-001 (01/03)
October 2001
K \workt,fJ761\37tl-001^SLRA RiponWinal SlRA_vl doc
-------
There are limited fish-eating mammals that use the Ottawa River (Shieldcastle 2000 personal
communication). The river otter is the only mammal likely to exclusively eat fish, but is unlikely to
inhabit the lower Ottawa River (Shieldcastle 2000 personal communication). Although the mink is also
unlikely to permanently inhabit the lower Ottawa, it is possible that they may feed along the river on
occasion as they move between streams which provide better habitat (Shieldcastle 2000 personal
communication). In addition, it is known to be veiy sensitive to one of the key chemicals of concern in
the river (PCBs) (Eisler 1986). Accordingly, mink was chosen as the representative mammalian receptor.
Mink feed on both fish and macroinvertebrates (e.g., crayfish), as well as birds and mammals (U.S. EPA
1993a). In this SLRA, it was conservatively assumed that they feed solely on fish from the Ottawa River.
The snapping turtle (Chelydra serpentina) is an additional wildlife receptor in the lower Ottawa for which
data are available. Being a reptile, its sensitivity to chemical contaminants compared to the other wildlife
receptors discussed above is uncertain. However, although PCB congener concentrations in turtle eggs
are available in turtle tissues, it is difficult to screen risks to reptiles due to the limited toxicological
effects data available for this class of organisms. Accordingly, the PCB data for turtle eggs are indicative
of exposure, but whether the measured egg levels are toxic is unknown. As discussed in a recent review
of reptile toxicology (Hopkins 2000), ecotoxicological studies on reptiles often document tissue
concentrations of chemicals, but seldom provide adequate insight on the biological significance of the
tissue concentrations measured. Moreover, it is difficult to screen risks based on dietary intake
estimations because reptile responses to chemical concentrations are unknown (Hopkins 2000).
Additional ecological receptors evaluated include fish and aquatic invertebrates in the river (surface water
and sediment). In addition to evaluating the overall aquatic community as a whole, piscivorous fish (e.g.,
smallmouth and largemouth bass) were identified as ecological receptors based on their potentially
different sensitivity compared to birds and mammals. Moreover, water quality standards (WQS) or
criteria (WQC) for protection of biota in surface water tend to be based on water-only exposures (i.e., gill
uptake). Evaluation of piscivorous fish allowed screening risks to be estimated for these receptors using
tissue residue data, which reflect gill uptake and dietary exposures and are particularly important for
hydrophobic organic compounds such as PCBs.
Based on the above discussions, the receptors selected for evaluation in the ecological SLRA, and the
exposure pathways for each, are summarized in Table 2-1 below.
Table 2-1. Ecological Receptors to be Evaluated In the SLRA and Their Routes of Exposure
Ecological Receptor
Exposure Pathway
Bald eagle
Tissue, water, and sediment ingestion
Common tern
Tissue, water, and sediment ingestion
Spotted sandpiper
Tissue, water, and sediment ingestion
Mink
Tissue, water, and sediment ingestion
Piscivorous fish
Tissue ingestion
Aquatic community
Direct contact with surface water and sediment
2.4 ASSESSMENT AND MEASUREMENT ENDPOINTS
Assessment endpoints are explicit statements of the environmental values to be protected at the site (U.S.
EPA 1997). The assessment endpoints are defined not only in terms of environmental entities (e.g., fish
community) and properties of those entities (e.g., species richness), but also identify the level of effect on
Parametrix
Final Ecological SLRA of the Lower Ottawa River
2-4
335-3763-001 (01/03)
October 2001
Jt *wartotgUH3
-------
those properties that should be detected or estimated (Cook et al. 1999). Cook et al. (1999), for example,
used 20 percent reduction in one of the endpoint properties in the field or a 20 percent reduction in
survivorship, growth, or reproduction in a toxicity test as potentially significant. In this SLRA, toxicity
data were based on survival, growth, or reproductive effects that were not significantly different than
control organisms. When such data were not available, low effects levels were estimated as described in
the Effects Characterization. This level is the lowest level of effects that standard field and laboratory
techniques can detect with conventionally acceptable confidence.
Measurement endpoints are the measurable characteristics that are related to the valued characteristic
chosen as the assessment endpoint (U.S. EPA 1997). In other words, the measurement endpoints
represent the types of data (exposure or toxicity; site-specific or literature-based) that are used to
determine whether there is an affect on the assessment endpoints. In this SLRA, measurement endpoints
include literature-derived chemical toxicity data and site-specific data on species richness and diversity;
bioassay tests for aquatic organisms; and sediment, water, and tissue concentration data. Multiple
measurement endpoints (i.e., lines of evidence) were evaluated, when possible, because it provides more
accurate estimates of effects and more reliable estimates about causation than exclusive reliance on
modeling risks from concentrations of chemicals in ambient media (Suter 1993). Consideration of
multiple lines of evidence in a "weight-of-evidence analysis" was the approach used in the Ottawa River
SLRA. Table 2-2 summarizes the assessment and measurement endpoints of the Ottawa River SLRA.
Table 2-2. Ecological Assessment and Measurement Endpoints Used
in the Lower Ottawa River SLRA
Receptor
Assessment Endpoint Receptor Type
Measurement Endpoints
Aquatic wildlife
Reduction in abundance
or production of
piscivorous wildlife
populations resulting
from toxicity
Bald eagle population
Common tern population
Spotted sandpiper
population
Mink population
Aquatic community
Benthic community
Receptor toxicity data (literature)
Water concentrations (site)
Sediment concentrations (site)
Tissue concentrations (site)
Aquatic biota, pelagic
Aquatic biota, sediment
Reduction in species
richness or abundance
resulting from toxicity
Reduction in species
richness or abundance
in benthic communities
resulting from toxicity
Biological survey data (site)
Receptor toxicity data (literature)
Water concentrations (site)
Tissue concentrations (site)
Biological survey data (site)
Receptor toxicity data (literature)
Bioassay data (site)
Sediment concentrations (site)
2.5 CONCEPTUAL SITE MODEL
The above information on chemical sources, ecological receptors evaluated, and assessment/measurement
endpoints were integrated into a conceptual site model. Thus, the conceptual model graphically depicts
the relationships between site-specific assessment endpoints and exposure scenarios. The conceptual
models for wildlife and aquatic life are provided in Figures 2-4 and 2-5, respectively.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
2-5
555-1763-001 (01/03)
October 2001
£ hront*l»07«lJ7«^0;UtA4 Rtport^lmlSlMjildoc
-------
As shown in the figures, chemicals enter the Ottawa River from a variety of sources, including leachate,
surface runoff, permitted discharges, and groundwater. Once in the system, chemicals may enter the
water column or sediments through resuspension/deposition and absorption/desorption. Biota may then
accumulate chemicals via exposure to either sediment or surface water.
As shown in Figure 2-4, food ingestion is a significant pathway for all wildlife receptors evaluated. For
the spotted sandpiper, sediment ingestion also represents a significant exposure pathway since they are
probing feeders; for the remaining wildlife, sediment ingestion is expected to be a complete exposure
pathway, but insignificant (see Figure 1-1). Lastly, for all wildlife receptors, surface water ingestion is
considered an insignificant exposure pathway.
As shown in Figure 2-5, aquatic life are primarily exposed to chemicals in surface water via their gills.
Aquatic life exposure to chemicals in tissue and sediment occurs most significantly via ingestion
pathways (see Figure 2-5).
Paramatrix
Final Ecological SLRA of the Lower Ottawa River
2-6
555-3763-001 (01/03)
October 2001
ChnHtt^JH3\37l3-001VSUU topw*f*ialSIM_viJ*K
-------
Primary
Sources
Secondary
Source/
Transport
Additional
Transport
Mechanism
Exposure
Medium
Site
Receptors
Exposure
Pathway
Bald Eagle
Common
Tern
Spotted
Sandpiper
Mink
Sediment
Sediment
Fish
Tissue
Leachate
Groundwater
Surface
Water
Surface
Water
Surface
Runoff
Permitted
Discharge
Deposition/
Resuspension
Uptake and
Bioaccumulation
Macroinvertebrate _
Tissue
o
(0
+*
c
o
o
o
0>
¦a
o
o
Li.
c
o
V)
o
O)
c
a>
E
¦o
&
cn
c
o
*3
V)
a>
O)
c
a>
I
c
o
W
a>
O)
c
©
o
o
Parzunetrix, Inc. Onaw«Rrv«rSLRA/S55~3763-001/01(M)6«1 (K)
Pathway is Complete
Figure 2-4
Pathway is Complete, Probably Insignificant Conceptual Site
Model for Wildlife
-------
Primary
Sources
Leachate
Surface
Runoff
Permitted
Discharge
Secondary
Source/
Transport
Additional
Transport
Mechanism
Exposure
Medium
Exposure
Pathway
O
Surface
Water
Deposition/
Resuspension
Groundwater
Surface
Water
c
o
s
0)
0>
U)
0
Uptake and
Bioaccumulation
Tissue
o<
Sediment
J
Sediment
O
Parametrix, Inc. cm»w» rwslfwssmt&j-ooi/oihwi &01 (K)
Pathway is Complete and Significant
HH Pathway is Complete, Probably Insignificant
(^) Pathway is Incomplete or Not Viable
Figure 2-5
Conceptual Site Model
for Aquatic Life
-------
3. EXPOSURE CHARACTERIZATION
This section describes how the exposure of ecological receptors to chemicals in various environmental
matrices (i.e., water, sediment, tissue) was quantified. The section begins with a description of the
environmental concentrations used, followed by a description of the approach used for quantifying
exposure to each receptor.
3.1 CHEMICAL CONCENTRATIONS
3.1.1 Measured Concentrations
Chemistry data for water, sediment, and tissue were available for various reaches of the lower Ottawa
River (LTI 2001). The major classes of chemicals that have been measured include metals,
polychlorinated biphenyls (PCBs), organochlorine pesticides, and polycyclic aromatic hydrocarbons
(PAHs). To address the management goals (i.e., hot spot delineation) mentioned in the Problem
Formulation, both the acute and chronic exposure potential of ecological receptors were evaluated.
The chemistry data were used to estimate both acute and chronic exposure concentrations. The sediment,
tissue, and water chemistry data used in the SLRA were derived from a variety of studies conducted over
a period of several years. Media data were reviewed to determine which data were most representative
for determining organism exposure concentrations. Some of the sediment data were quite old (e.g., from
1994), while some tissue data were based only on fillets and were thus not representative of wildlife
exposures.
Sediment chemistry has been the most extensively sampled, with recent large sampling events occurring
in 1998 and 2000. None of the sediment data from these two studies were combined in estimating
exposure concentrations because they were temporally and spatially different (i.e., collected at different
times and from a variety of different depths). The sediment data from 2000 were deemed the most
appropriate to the SLRA since they most accurately reflect current conditions and represent surface
sediments (i.e., the biologically active zone). However, the sediment data from 1998 were also used to
screen risks to aquatic life. The 1998 sediment data were composited over a variety of different depths.
For the purposes of the SLRA, the sediment composited over a depth of 0-24" was considered surficial
sediment, although it must be emphasized biota would not be exposed to sediment up to a depth of 24".
Sediment data from depths greater than 24" were also used as an estimation of potential exposure
concentrations if overlying sediment was removed from remediation activities. The 1998 sediment data
were not used for estimating exposure of wildlife receptors since their exposure represents a concurrent
combination of sediment, water, and tissue concentrations that are all in equilibrium. Accordingly, only
the sediment, water, and tissue data collected concurrently were used to screen wildlife risks. Fish tissue
data were collected in 1999 and 2000 in the Ottawa River, and in 1999 in North Maumee Bay. The 1999
data for the Ottawa River were not used in the wildlife SLRA since only fillets were analyzed and may
underestimate the whole body concentrations to which wildlife are exposed. The 2000 data, in addition to
being the most current data, also measured whole body concentrations. The 1999 North Maumee Bay
data were used to screen risks to bald eagles, as requested by the U.S. FWS. Lastly, chemistry data for
surface water were available from one sampling event in 2000. These data were used in both the wildlife
and aquatic life SLRAs. A summary of the chemistry data used in the SLRA is provided in Table 3-1.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
3-1
555-3763-001 (01/03)
October 2001
K.twoHhng\J763\3763-OOJVSUtAIi^ort^lnilSLRA^lihc
-------
Table 3-1. Summary of Chemistry Data Used in Wildlife and Aquatic Life SLRAs*
Media Year Location Chemicals Receptor Evaluated
Sediment 1998 Ottawa River (RMs 0.1-12.5) SVOCs, Metals Aquatic Life
2000 Ottawa River SVOCs, Metals Aquatic Life, Wildlife
Fish Tissue 1999 North Maumee Bay Pesticides, PCBs Bald Eagle
2000 Ottawa River Pesticides, PCBs, Metals Bald Eagle, Common Tern,
Mink
Water 2000 Ottawa River SVOCs, Metals Aquatic Life, Wildlife
* See LTI (2001) for a detailed description of the chemistry database used in the SLRA.
Consistent with U.S. EPA risk assessment guidance (U.S. EPA 1998a), data were first screened using
frequency of detection to identify which chemicals should be evaluated. On a medium-specific basis,
only those chemicals detected in more than 5 percent of the samples were evaluated in the SLRA. For
example, if a chemical was detected in sediment in more than 5 percent of the samples, but never in
surface water, ecological receptor exposures to that chemical were evaluated in sediment but not in
surface water. For those chemicals detected in more than 5 percent of the samples, chronic exposure
concentrations were estimated by river segment, using the 95 percent upper confidence limit (UCL) on
the mean. This is a typical approach used by the U.S. EPA (Suter et al. 1999). For acute exposure, the
95th percentile of the data set for a river segment was used to estimate a short-term upper bound exposure.
When a chemical was not detected in an individual sample, but was detected in more than 5 percent of the
samples, one-half the detection limit was used in the statistics. This is a common approach for handling
non-detect data (Suter et al. 1999). The statistical equations used to calculate acute and chronic exposure
concentrations are provided in Appendix A. Summary statistics for tissue, sediment, and surface water
are also provided in Appendix A.
3.1.2 Estimated Concentrations
As summarized above, concentration data were available for a variety of chemical classes and
environmental media However, to thoroughly evaluate exposure of all receptors to the chemicals likely
to be present in the Ottawa River, it was necessary to estimate the concentrations of some chemicals in
tissue. For example, no tissue chemistry data were available for macroinvertebrates in the lower Ottawa
River; however, these data were necessary for estimating potential risks to the spotted sandpiper.
Because benthos are primarily exposed to chemicals associated with sediment (e.g., pore water, detritus),
chemical concentrations in invertebrate tissue were estimated from sediment concentrations using a biota-
sediment accumulation factor (BSAF). This approach is applicable to lipophilic organic chemicals (i.e.,
chemicals that tend to partition into lipids rather than water) (Tracey and Hanson 1996). Concentrations
of inorganics in benthos could not be estimated using an analogous approach because site-specific factors
that influence metal bioavailability in sediment are highly variable (Ankley et al. 1996) and would impart
unreasonable uncertainty in the exposure estimates. BSAFs and the equation for estimating invertebrate
tissue concentrations from sediment are presented in Section A.2 of Appendix A.
3.2 EXPOSURE QUANTIFICATION
The chemistry data discussed in Section 3.1 were used to quantify exposures of wildlife and aquatic life
receptors as discussed in the following sections.
Parametrlx
Final Ecological SLRA of the Lower Ottawa River
3-2
333-3763-001 (01/03)
October 2001
X Atporfflml SIM_tl.doc
-------
3.2.1
Wildlife
Exposure of avian and mammalian receptors to chemicals in the Ottawa River were estimated using tissue
(measured and estimated), sediment, and water data. Chemical exposure of these organisms was expected
to occur primarily through food consumption, although they may also receive significant exposure via
incidental sediment ingestion (particularly for probing feeders, such as the spotted sandpiper). Water
exposures were expected to be relatively insignificant compared to dietary and sediment exposures, but
were also evaluated for completeness. Dermal and inhalation exposure pathways were not evaluated in
the SLRA. It is expected that the fur or feathers of wildlife receptors will minimize the dermal uptake of
chemicals, while inhalation is expected to be insignificant for the relatively non-volatile chemicals being
evaluated in the lower Ottawa River.
Chemical exposure of avian and mammalian wildlife receptors was evaluated by estimating daily oral
doses. These doses were expressed as milligram chemical per kilogram body weight per day (mg/kg/d).
Accordingly, estimates of receptor ingestion rates (food, sediment, and water) and body weights were
required. Conservative (i.e., worst-case) ingestion rate and body weight assumptions were used where
possible due to the screening nature of the assessment. Furthermore, it was conservatively estimated that
receptors may feed exclusively within a given river segment. The following describes the assumed
ingestion rates and body weights for each receptor.
Bald Eagle
Bald eagles are primarily carrion feeders, but will also catch live fish (U.S. EPA 1993a). In addition, they
feed opportunistically on birds and mammals that are easily scavenged or captured (U.S. EPA 1993a). In
the SLRA, it was conservatively assumed that eagles feed exclusively on fish (no bird or mammalian
tissue data were available for this study). The chemical concentrations in fish were based on samples
from Maumee Bay in 1999 and the lower Ottawa River in 2000.
Body weights of adult bald eagles were identified in the literature (Dunning 1993; Stalmaster 1987), and
assumed to represent the body weights of eagles in the study area. Mean body weights reported in these
studies ranged from 4.13 to 4.33 kg for males and 5.35 to 5.27 for females. However, no data were
identified on the differences in food ingestion rates between males and females. According to
independent studies reported in U.S. EPA (1993a) and Stalmaster (1987), the daily food ingestion rate of
adult eagles is equivalent to approximately 12 percent of their body weight on a wet-weight basis. The
mean body weight for females (5.31 kg) and food ingestion rate of 0.64 kg/day (12 percent of body
weight) were used in this SLRA.6
No data were identified on sediment ingestion rates for eagles, although it is likely they will ingest some
sediment when scavenging along shorelines. In this assessment, it was assumed that the sediment
ingestion rate is equal to 1 percent of the eagle food diet. No data on sediment ingestion rates for the bald
eagle were identified. An ingestion rate of 1 percent, on a wet-weight basis, was estimated given the
sediment ingestion rates of other birds reported in U.S. EPA (1993). Data were also not identified on bald
eagle water ingestion rates. Thus, an allometric equation based on body weight was used (U.S. EPA
1993a). The water ingestion rate was estimated as shown in Equation 1:
6 Regardless of the body weight assumed, the ingestion rate used to estimate exposure is based on 12 percent of the
body weight. Accordingly, it is irrelevant which body weight is assumed.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
3-3
553-3763-001 (01/03)
October 2001
K. *w°r**ttW«3\J7i3-001\SUlA Avon&tnal SLfU_vl.doc
-------
IRwatcr = 0.059 XBW° 67 (1)
Where: IRwater = Water ingestion rate (L/day)
BW = Body weight (kg)
The bald eagle exposure assumptions that were used are summarized in Table 3-2.
Table 3-2. Ingestion Rate and Body Weight Values Used for Avian
and Mammalian Receptors
Receptor
Exposure
Parameter
Value
Units
Reference
Bald eagle
Food IR
0.64
(12% of BW)
kg/day-wet
U.S. EPA 1993a; Stalmaster 1987
Sediment IR
0.0064
(1% of food IR)
kg/day-wet
Professional judgement
Water IR
0.18
L/day
U.S. EPA 1993a
Body Weight
5.31
kg
Dunning 1993; Stalmaster 1987
Common tem
Food IR
0.0732
kg/day-wet
U.S. EPA 1993a
Sediment IR
0.000732
(1% of food IR)
kg/day-wet
Professional judgement
Water IR
0.014
L/day
U.S. EPA 1993a
Body Weight
0.120
kg
Dunning 1993
Spotted sandpiper
Food IR
0.035
kg/day-wet
U.S. EPA 1993a
Sediment IR
0.0012
kg/day-wet
U.S. EPA 1993a
Water IR
0.0066
L/day
U.S. EPA 1993a
Body Weight
0.0379
kg
U.S. EPA 1993a
Mink
Food IR
0.229
kg/day-wet
U.S. EPA 1993a
Sediment IR
0.00458
kg/day-wet
U.S. EPA 1993a
Water IR
0.10
L/day
U.S. EPA 1993a
Body Weight
1.040
kg
U.S. EPA 1993a
IR = Ingestion rate.
Common Tern
Body weights for the common tern average approximately 0.120 kg (Dunning 1993). The common tern
food ingestion rate was estimated using an allometric equation dependent on body weight (U.S. EPA
1993a). The dry-weight ingestion rates calculated by this equation were converted to wet weights to
ensure conformity with other data used in estimating common tem risks. The wet-weight ingestion rate
was estimated based on the percent moisture in tern food items (approximately 80 percent in fish). The
allometric relationship shown in Equation 2 was used:
Parametrlx
Final Ecological SLRA of the Lover Ottawa River
3-4
535-3763-001 (01/03)
October 2001
JC JUtt J-O0/ \SLRA RtpcrtJtnalSLM_*ldoc
-------
IRfood = (0.0582xBWO6M)x
I kg wet matter
(2)
0.2 kg dry matter
Where:
Food ingestion rate (kg/day-wet)
Body weight (kg)
No data were identified on sediment ingestion rates for the tern. However, given their feeding habits,
sediment ingestion is expected to be minimal. A sediment ingestion rate equal to 1 percent of its food
ingestion rate was assumed. The water ingestion rate for the common tern was estimated using the
allometric equation presented previously for the bald eagle (Equation 1). The exposure parameter values
for the common tern are summarized in Table 3-2.
Spotted Sandpiper
Body weights of male and female spotted sandpipers were identified in the scientific literature and, as for
the bald eagles, were substantially different between sexes (0.0379 kg for males and 0.0471 kg for
females) (U.S. EPA 1993a). The spotted sandpiper food ingestion rate was estimated using the same
allometric equation used for the common tern (Equation 2). The wet-weight ingestion rate was again
estimated based on the percent moisture in sandpiper food items (assumed to be 80 percent). Because
birds with a lower body weight tend to have a higher ingestion rate to body weight ratio (as demonstrated
by this allometric equation), chemical exposures to the smaller males were conservatively estimated.
Due to their probing feeding habits, spotted sandpipers were assumed to have a significant sediment
ingestion rate. While spotted sandpiper sediment ingestion rates were not identified, they were available
for the semipalmated, Western, stilt, and least sandpipers (U.S. EPA 1993a). Sediment ingestion rates for
these four sandpipers, estimated as the percent soil in the diet on a dry-weight basis, average 18 percent.
The water ingestion rate was estimated using the same equation used for the bald eagle (Equation 1). The
sandpiper exposure values used are summarized in Table 3-2.
Mink will feed on both fish and aquatic invertebrates, as well as birds and mammals (U.S. EPA 1993a).
According to a study of mink diets in a Michigan stream, 85 percent of their diet (year-round) was
comprised of fish (U.S. EPA 1993a). The remainder of their diet included crustaceans, amphibians, birds,
and mammals. Based on the available chemistry data for the lower Ottawa River, it was assumed that fish
comprise 100 percent of the mink diet.
Mink body weights can be highly variable depending on their range (U.S. EPA 1993a). Body weights for
males in Montana have been observed to range from 1.040 to 1.233 kg for adults and 0.777 to 0.952 kg
for juveniles, depending on season (U.S. EPA 1993a). In the same study, body weights for females
ranged from 0.550 to 0.586 for adults and 0.533 to 0.582 for juveniles. The estimated year-round food
ingestion rate of 22 percent of body weight for adult males reported in U.S. EPA (1993a) was used to
estimate dietary exposures. Using the adult summer body weight of 1.0 kg results in an estimated dietary
intake of 0.229 kg/day wet weight.
No data were identified on sediment ingestion rates for mink; a sediment ingestion rate of 2 percent of
their dietary intake was assumed. Data were also not identified on water ingestion rates for the mink.
Parametrix SSS-3763-ooi (01/03)
Final Ecological SLRA of the Lower Ottawa River 3-5 October 2001
Mink
K \workin&3763\3763-001 ISZA4 toporMtnalSLRAj/lJoc
-------
Using an allometric equation for mammals based on body weight, the water ingestion rate was estimated
using the relationship shown in Equation 3 (U.S. EPA 1993a):
IRwaler =0.099 xBW°90 (3)
Where: IRwater = Water ingestion rate (L/day)
BW = Body weight (kg)
The final body weight and food, sediment, and water ingestion rates that were used to evaluate the mink
are summarized in Table 3-2.
3.2.1.1 Wildlife Dose Calculation
Using the ingestion rates and body weights identified above, and the chemistry data for receptor food
items, sediment, and water, chemical doses to wildlife receptors were estimated as shown in Equation 4:
Chemical Dose (mg/kg/d) = (Cfood X IRfot>d) + + X (4)
Where: Cf0Od = Chemical concentration in food (mg/kg wet weight)
IRfood = Food ingestion rate (kg/day wet)
C„d - Chemical concentration in sediment (mg/kg wet weight)
IR»
-------
Although less emphasis has historically been placed on the dietary uptake of chemicals by fish, it has
become increasingly realized that this pathway is more important than the water exposure typically
addressed by WQS for a variety of species and types of chemicals (Suedel et al. 1994). For example,
piscivorous fish are likely to have much greater exposure to PCBs through the dietary pathway than
through other pathways. The importance of the dietary route for metals has also received greater attention
(Szebedinszky et al. 2001) and was evaluated where data were available. Given the difficulties in
estimating chemical doses to fish, due to the lack of data, exposure was estimated by considering tissue
residue concentrations. These were compared to tissue residue toxicity thresholds, as discussed later.
Parametrix
Final Ecological SLRA of the bower Ottawa River
3-7
555-3763-001 (01/03)
October 2001
X \wertotf\J763\)7
-------
EFFECTS CHARACTERIZATION
This section presents and discusses the toxicity thresholds (hereafter referred to as Toxicity Reference
Values, or TRVs) for wildlife and aquatic life receptors. These TRVs were compared to the estimated
doses and exposure concentrations described in Section 3 to estimate potential risks to ecological
receptors.
4.1 WILDLIFE
4.1.1 Toxicity Thresholds
To evaluate a chemical's toxicity (i.e., direct toxicity and/or food chain effects) to wildlife receptors,
acute and chronic toxicological effects data were obtained from the scientific literature. The acute
toxicity data used were reported as LD50s (i.e., the dose lethal to 50 percent of the organisms tested).
Using the U.S. EPA's approach for aquatic life LC50s (Stephan et al. 1985), LD50s were divided by two
to estimate a dose that would affect much fewer than 50 percent of the organisms.
The chronic toxicity data used were No Observed Adverse Effect Levels (NOAELs). A NOAEL is the
highest concentration tested in a toxicity study that did not result in statistically significant effects when
compared to the controls. If a NOAEL was not available, a Lowest Observed Adverse Effect Level
(LOAEL) (i.e., the lowest concentration tested resulting in a statistically significant effect) was used with
a safety factor of 10 applied to estimate the NOAEL (per U.S. EPA 1997). The NOAELs or LOAELs
used were generally based on adverse effects on reproduction, growth, and development, consistent with
the toxicity endpoiats traditionally evaluated (U.S. EPA 1997). The acute and chronic TRVs are provided
in Tables B-l and B-2 of Appendix B, respectively.
With the exception of the limited toxicity data available for mink, toxicity data were not available for the
site-specific receptors being evaluated. Consequently, toxicity data for surrogate species (e.g., rat,
chicken, quail) were used. For mammals, scaling the toxicity dose based on the body weight of the test
and site-specific receptor species is recommended (Travis and White 1988; Travis et al. 1990; U.S. EPA
1992). Research has demonstrated that numerous physiological functions, such as metabolic rates and
responses to toxic chemicals, are functions of body size (Sample et al. 1996). Differences in metabolic
rates can lead to more resistance to toxic chemicals because of the rate of detoxification through
metabolism and excretion of the chemical (Sample et al. 1996). However, body weight scaling is not
considered appropriate for birds (Fischer and Hancock 1997). For birds, differences in toxicological
reactions appear to be more a factor of whether the species is passerine or non-passerine (Fischer and
Hancock 1997), although no relationships are available on the relative sensitivities of passerine and non-
passerine birds. The equation for body weight scaling of mammalian TRVs is provided in Appendix B.
4.1.2 Water Quality Criteria for Wildlife
The Ohio EPA has developed WQC for wildlife for a limited number of chemicals, typically those
substances with a propensity to biomagnify in food chains, such as DDT, mercuiy, and PCBs (OEPA
3745-1) (Table 4-1). These values were developed by back-calculating water concentrations using dietary
toxicity thresholds, bioaccumulation factors (BAFs), biomagnification factors (BMFs), and assumptions
on wildlife receptor food ingestion rates and body weights. These WQC values were used as an
additional line of evidence in characterizing risks to wildlife. It must be emphasized that the criteria
represent very low water concentrations, in many cases below the detection limits achieved in the Ottawa
River 2000 water sampling event. Accordingly, it is uncertain whether undetected levels of these
chemicals are of concern.
Paramatrix
Final Ecological SLRA of the Lower Ottawa River
4-1
555-3763-001 (01/03)
October 2001
Jt *wor**tf
-------
Table 4-1. Ohio EPA Water Quality Criteria for Wildlife
Chemical
Wildlife Criterion (pg/L)
Mercury
PCBs
DDT (and its metabolites)
0.0013
0.00012
0.000011
4.2 AQUATIC LIFE
4.2.1 Surface water
A hierarchy of sources was used for identifying water-based acute and chronic toxicity thresholds for
aquatic life:
1. Ohio Environmental Protection Agency (OEPA 3745-1)
2. U.S. Environmental Protection Agency (U.S. EPA)
3. The general scientific literature.
WQC from both the OEPA and the U.S. EPA are intended to protect at least 95 percent of the species in a
generic aquatic community. For many of the metals, the WQC is hardness-dependent. Generally
speaking, a decrease in water hardness results in an increase in the bioavailability and, subsequently, the
toxicity of certain divalent metals. Thus, the lower the hardness, the lower the WQC. In order to ensure
protection of aquatic life at a range of hardness values at the site, a conservatively low hardness based on
the lower 95 percent confidence limit on the mean hardness for the river was used (on a segment-by-
segment basis).
WQC for two other chemicals were also based on water quality parameters. The acute WQC for
ammonia and the acute and chronic WQC for pentachlorophenol are dependent upon the pH.
Additionally, the chronic WQC for ammonia is dependent upon both pH and temperature. Ammonia
exists in two forms in the environment: ionized ammonia and un-ionized ammonia. Un-ionized ammonia
is much more toxic to aquatic life than the ionized form (U.S. EPA 1998b). The equilibrium between
these two increasingly favors un-ionized ammonia as the pH and temperature increases. As pH and
temperature increase, the equilibrium between ionized and un-ionized ammonia shifts, increasing the un-
ionized fraction. Because ammonia is most toxic in the un-ionized form, conditions of elevated pH and
temperature, which cause an increase in the un-ionized fraction, correspond with a lower ammonia
criterion. In this SLRA, a conservatively high pH and temperature, based on the upper 95 percent
confidence limit on the means of pH and temperature, were used.
For pentachlorophenol, the pH relationship is the reverse of that for ammonia. As the pH decreases, the
toxicity increases and the criterion decreases. For this SLRA, a conservatively low pH based on the lower
95 percent confidence limit on the mean pH was used.
When neither OEPA nor U.S. EPA WQC were available for a chemical, a toxicity threshold was
identified from the scientific literature, generally using the U.S. EPA's AQUIRE database. Acceptable
studies were identified using U.S. EPA guidelines (Stephan et al. 1985). If chronic toxicity data were
lacking, either completely or for sensitive species, a chronic toxicity threshold was estimated using a
Parametrix
Final Ecological SLRA of the Lower Ottawa River
4-2
555-3763-001 (01/03)
October 2001
K. \»t,rk*rg\3HM7t}-001
-------
chemical specific acute-chronic ratio (ACR)7 or generic ACR of 10 (U.S. EPA 1991a). The acute and
chronic TRVs used to characterize aquatic effects are presented in Table B-3 of Appendix B.
4.2.2 Sediment
A variety of sources have published freshwater sediment quality guidelines, including:
• Ontario Ministry of the Environment and Energy (1993)
• Environment Canada (1995)
• Ingersoll et al. (1996)
• Di Toro and McGrath (2000)
The sediment guidelines from these sources are presented in Table B-4 of Appendix B. The Ingersoll et
al. (1996) guidelines identify four levels of protection. These guidelines provide sediment concentrations
where there is a low likelihood of effects (Effects Range Low [ER-L] and Threshold Effect Levels [TEL])
as well as concentrations where effects are more likely to occur (Effects Range Median [ER-M] and
Probable Effect Levels [PEL]). When a sediment concentration falls below ER-L and TEL values, effects
are rarely observed. In contrast, the probability of effects is more frequent (generally greater than 50
percent) when concentrations exceed ER-M and PEL values (Ingersoll et al. 1996; Long et al. 1998). It
should be noted that an exceedance of any one of these sediment guidelines does not necessarily mean
that aquatic life are at risk. This is because the sediment guidelines are not site-specific, are conservative,
and do not always indicate an effect will actually occur when exceeded (Long et al. 1998). Much of the
toxicity data used to develop such guidelines are based on whether effects were observed in bioassays of
field-collected samples. Accordingly, if effects were observed, the toxic effect level is assumed to be
related to the concentration of an individual chemical in the sample, when in fact, it is likely that a variety
of chemicals contributed to the observed toxicity. With these facts in mind, an approach was developed
for predicting potential risks to benthos using these guidelines and is discussed in the Risk
Characterization (Section 5).
For PAHs, only the guidelines derived by Di Toro and McGrath (2000) were used. According to Di Toro
and McGrath, the empirical guidelines (e.g., ER-L, ER-M values) for individual PAHs are one to two
orders of magnitude smaller than the narcotic concentrations that are known to cause mortality, growth, or
reproduction effects and therefore are not reflective of actual effects concentrations for these endpoints.
This likely occurs due to the presence of multiple chemicals in the toxicity studies used to drive the
guidelines for individual chemicals (see above). Moreover, for sediment PAH guidelines that are not
organic carbon-normalized (Ingersoll et al. and Environment Canada are not), there is a one order of
magnitude uncertainty due to the variation in organic carbon concentrations in sediment that they do not
account for (Di Toro and McGrath 2000). Use of the methodology presented in Di Toro and McGrath
(2000) also reflects the current state of the science by the U.S. EPA in deriving sediment quality criteria
for chemicals (U.S. EPA 2000a). Use of these guidelines also presents a method for evaluating PAH
mixtures, since many individual PAHs typically co-occur. This method, as well as the technical basis for
these guidelines, is presented in Appendix B.
7 As the name implies, an acute-chronic ratio is the ratio of the acute toxicity value for an organism to the chronic
toxicity value for the same organism. The acute and chronic values should be developed as part of the same study
(Stephan et al. 1985).
Paramatrix
Final Ecological SLRA of th* Lawtr Ottawa River
4-3
SSS-3763-001 (01/03)
Octob*r 2001
£ \»erk*rf}7i3\)763-001\SLM Rtpo»\rinalSl*A_yljlot
-------
4.2.3 Tissue Residues
As discussed, potential risks based on tissue residue data were also evaluated for fish. Accordingly, tissue
residue toxicity thresholds were identified for fish where available. Because neither the OEPA nor U.S.
EPA has developed tissue-based criteria for fish, all toxicity thresholds were identified from the scientific
literature. Tissue-based toxicity data were largely compiled using the recent thorough data summary of
Jarvinen and Ankley (1999). The residue-based toxicity thresholds for fish are summarized in Table B-4
of Appendix B.
Parametria 5SS-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 4-4 October 2001
£ R4p0rt\PinalSLRA_vI.doc
-------
5. RISK CHARACTERIZATION
The Risk Characterization integrates the Exposure and Effects Characterizations to assess whether
chemical concentrations are sufficiently high to pose unacceptable risks to ecological receptors. It should
be emphasized that this SLRA, where possible, incorporated conservatism where uncertainties were
apparent, which is typical for a screening analysis (i.e., risks are likely to be overestimated rather than
underestimated). This allows for chemicals posing negligible risk to be confidently removed from further
evaluations. The risk characterization approach is summarized in Figure 5-1. The chemicals identified as
being of potential concern (i.e., COPCs) may be evaluated further in more detailed site-specific
assessment to further characterize the risks they pose. The following sections present the risk
characterizations for wildlife and aquatic life, respectively.
5.1 WILDLIFE
Potential risks to wildlife receptors were evaluated using two lines of evidence: (1) comparison of
estimated chemical doses to TRVs; and (2) comparison of surface water concentrations to Ohio EPA
WQC for wildlife. For each line of evidence, a quotient approach (U.S. EPA 1997) was used.
5.1.1 Dose-Based Hazard Quotients
A dose-based quotient represents the ratio of the estimated chemical dose to a receptor to chemical- and
receptor-specific TRVs. In this SLRA, this ratio was termed a hazard quotient (HQ) and was derived as
shown in Equation 5:
HQ Chemi cal Dose (mg/kg/d) ^
d0" Toxicity Reference Value (mg/kg/d)
An HQ value greater than 1.0 suggests that a chemical potentially poses unacceptable risk, while an HQ
value of less than 1.0 suggests negligible risks (due to the conservative assumptions that were used in the
Exposure and Effects Characterizations)8. This approach is useful as an efficient means of identifying
high or low risk situations (U.S. EPA 1998a). As such, it is a useful tool for addressing the management
goals of identifying chemical hot spots and prioritizing portions of the lower Ottawa River for possible
additional assessment or remediation activities. Additional evaluations may be necessary to further
delineate these possible remediation areas since HQs provide limited information on the incremental
quantification of risks (i.e., an HQ of 30 does not represent "twice the risk" as an HQ of 15). The HQs for
the bald eagle, common tem, spotted sandpiper, and mink are summarized and discussed separately
below.
5.1.1.1 Bald Eagle
As discussed in Section 3, potential exposures (acute and chronic) of bald eagles to chemicals in the
Ottawa River and North Maumee Bay were evaluated. In the Ottawa River, potential chemical exposures
based on tissue, sediment, and surface water data were evaluated, while in Maumee Bay, only
concentrations in fish tissue were evaluated given the available data. Acute and chronic HQs by river
segment are provided in Appendix C, Tables C-l and C-2, respectively.
8 It is not possible to reasonably differentiate chemicals as posing low, moderate, or high potential risk for those with
HQs greater than 1.0, because the conservatism in the data and assumptions used are chemical-specific. As a
general guideline, however, HQs greater than 10 likely suggest a high potential risk.
Paramatrlx
Final Ecological SLRA of lh» Lower Ottawa Rmr
5-1
555-3763-001 (01/03)
October 2001
IL>»oik*>tUH3U7t}-O01[SUAlUportrmalSlM_?t.
-------
~Unused Data
North Maumee Bay
Lower Ottawa
WATER
TISSUE
Data Base
SEDIMENT
Bioassays
Biocriteria
Water
Quality
Criteria
for
Wildlife
Hazard Quotients
for Wildlife
Compare to Bird
Toxicity Data
Calculate Dose
Assess Potential
Risk to Wildlife
Compare to
Sediment
Guidelines
WATER
SEDIMENT
TISSUE
Hazard Quotients
for Bald Eagle
Hazard Quotients
for Aquatic Life
Hazard Quotients
for Benthic Aquatic
Life
Calculate Dose for
Receptors
Calculate Summary
Statistics
Map of Key Sediment
COPCs
Compare to Bird
and mammal Toxicity
Data
Assess Potential
Risk to
Aquatic Life
Assess Potential
Risk to Bald Eagles
in Maumee Bay
Compare to Water
Quality Criteria or
Toxicity Data
(Acute & Chronic)
Identify Chemicals with a
Detection Frequency of >5%
Ottawa River
- 2000 Tissue Data
- June 2000 Sediment and Water Data
- North Maumee Bay 1999 Fish Tissue Data
-1998 Sediment Data
Parametrix, Inc. on«w« row slra«55-3763-ooi/oi(03> 7/01
-------
Comparison of acute exposures to acute TRVs did not result in any HQs greater than 1.0. Comparison of
chronic exposure estimates to chronic TRVs did result in chronic HQs greater than 1.0 for lead, PCBs,
and DDT. The HQs for these chemicals are plotted by river segment in Figure 5-2.
A lead HQ of approximately 2.5 occurs in the river segment encompassing RMs 4.9 to 6.5; lead HQs are
less than 1.0 in the other river segments. This HQ is highly influenced by lead concentrations in the
sediment of this river segment, which range from 43 to 13,130 mg/kg-wet (a range greater than two
orders of magnitude). More specifically, the lead HQ is highly affected by the sample with the highest
measured lead concentration. The next highest concentration measured was 71 mg/kg-wet. The sample
with the lead concentration of 13,130 mg/kg-wet may reflect a hot spot of metals concentrations.
Although not at the same magnitude, maximum concentrations of cadmium, chromium, copper, mercury,
nickel, silver, vanadium, and zinc were all measured in this same sample, which suggests that the elevated
lead levels were not an artificial circumstance of the sample, such as from lead shot.
PCB HQs exceeded 1.0 in all river segments except upstream of RM 8.8. The highest HQ, approximately
4.4, was calculated in the river segment encompassing RMs 3.2 to 4.9. All PCB HQs were influenced by
Aroclor 1242 PCB levels measured in fish tissue. The fish tissue samples resulting in the highest HQ
were collected near the Hoffman Road landfill at RM 3.4.
A DDT HQ of approximately 1.7 occurs upstream of RM 8.8; DDT HQs are less than 1.0 in all other
river segments. All DDT HQs were influenced by concentration in the eagle diet (i.e., fish). The
maximum concentration measured above RM 8.8 was 33.5 pg/kg-wet in green sunflsh (upstream of the
University of Toledo dam). DDT HQs successively decline from above RM 8.8 toward RM 0.
It should be reemphasized that these HQs (lead, PCBs, and DDT) are conservative because they assumed
that eagles fed exclusively in any individual river segment over a chronic exposure duration. Actual risks
from lead are probably significantly lower and could have been below risk thresholds had feeding ranges
been considered in the analysis. Nevertheless, these results, though conservative, provide information on
locations of possible concern that were compared with other lines of evidence in lata- sections.
5.1.1.2 Common Torn
Acute HQ values for the common tern never exceeded 1.0. However, chronic HQs for lead, selenium,
PCBs, and DDT exceeded 10 in at least one river segment (Figure 5-3). These additional COPCs were
identified for the tern (and not for the bald eagle) because of its greater ingestion rate to body weight
ratio. The spatial patterns of HQs exceeding 1.0 for lead, PCBs, and DDT by river segment are similar to
those observed for the bald eagle, although the HQs for the tern are larger given its larger ingestion rate to
body weight ratio (i.e., higher exposure potential).
Selenium HQs slightly exceeded 1.0 within the river segments encompassing RMs 0 to 3.2 and RMs 4.9
to 6.5. These HQs were influenced by selenium concentrations in fish tissue, which ranged from 0.09 to
1.21 mg/kg-wet between RMs 0 to 3.2 and 0.09 to 1.65 mg/kg-wet between RMs 4.9 to 6.5. The
maximum wet-weight concentrations in each river segment correspond to dry-weight selenium
concentrations of approximately 4.8 and 6.6 mg/kg. Hazard quotients of approximately 1.0 are consistent
with the dietary EC10 of 5 mg/kg-dry derived by Fairbrother et al. (2000). According to Skorupa et al.
(1996), background selenium concentrations in fish range from less than 1 to 4 mg/kg-dry. Accordingly,
die difference between background selenium concentrations and those that may cause effects in birds is
quite small.
Raramatrlx
Final Ecological SLRA of the Lower Ottawa River
5-3
555-3763-001 (01/03)
Octob*r 2001
Jt twoWHtfUWJUW-OMiSUM ApwfWn/ttAt.v/.ifec
-------
Figure 5-2. Chronic hazard quotients for bald eagles feeding in the Ottawa River.
El Lead
£3 PCBs (total)
~ DDT
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM >8.8
Lower Ottawa River SLRA
July 2001
555-3763-001
-------
Figure 5-3. Chronic hazard quotients for terns feeding in the Ottawa River.
1
1
1
1
i
i
i
1
1
1
1
' i
i
i
1
1
1
I
1 1
i i
[i •
-i
i
i
1
1
1
1
i
i i
i i
i
i
i
•
•!
1
1
1
1
i
i
i
i
i
i
i
i
i i
i i
i •
!
1
1
1
1
i
i
i
i
i
i
!i •
1 1
i •
i i
i
1
1
1
1
i
i
i
i
i
!i •
i i
1 1
i
1
1
1
"1 1
i i
[
i
i
i
i
i
•
i •
1 •
i
l
1
1
1
1
1 1 1
1 1
1 1
i
i
i
i
i
i
i
!i '
i «
i
' i
ii
,
1
1
1
11 1
1 I
' 1 1
l i
i
i
i
i
i
i
; •
•
j i
i
1
B8:
! i i
1 i
' rra 1
!.... . i—nr. ¦
i—^77
~ Lead
EB Selenium
~ PCBs (total)
~ DDT
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM >8.8
Lower Ottawa River SLRA
July 200J
555-3763-00J
-------
Overall, there is no consistent pattern in HQs between chemicals. In general, PCB HQs decrease from the
river mouth to upstream river segments, while DDT HQs decline from upstream to downstream. The
highest HQ for lead occurs in the middle river segment.
5.1.1.3 Spotted Sandpiper
Potential exposures of spotted sandpipers to chemicals in the lower Ottawa River are quite different than
those of bald eagles and common terns. This is due to differences in food items (benthos instead of fish)
and because they are likely to ingest a greater amount of sediment since they are probing feeders. The
chemicals with HQs greater than l.O in at least one river segment were aluminum, chromium, lead,
cyanide, PCBs (Aroclor 1242), DDT, and bis(2-ethylhexyl)phthalate (Figure 5-4). The HQs for
aluminum, chromium, and lead were influenced by incidental sediment ingestion, while those for the
organic compounds were influenced by dietary exposures. Recall that dietary concentrations were
estimated from sediment concentrations using BSAFs for lipophilic organic compounds. Accordingly, all
sandpiper HQs were directly linked to the ingestion of sediment.
Aluminum HQs were between 1.0 and 2.0 in the lower four river segments. However, since background
aluminum concentrations may be elevated and no background data is available, the potential risk
associated with these HQs is uncertain and may reflect background aluminum concentrations in the river.
The highest lead HQ was approximately 71, occurring between RMs 4.9 and 6.5. Chromium HQs were
between 1.0 and 2.5, occurring in the middle three river segments. An HQ of 1.2 occurred for cyanide
between RMs 6.5 and 8.8. Cyanide HQs did not exceed 1.0 for any other river segment. The HQs for the
three organic COPCs generally decline from upstream to downstream for the spotted sandpiper (see
Figure 5-4). The maximum bis(2-ethylhexyl)phthalate HQ of approximately 3 was also influenced by
sediment concentrations at RM 8.3.
5.1.1.4 Mink
No acute HQs exceeded 1.0 for the mink. Chronic HQs exceeded 1.0 for aluminum, iron, lead, selenium,
thallium, and PCBs for at least one river segment (Figure 5-5). Hazard quotients for aluminum, lead, and
thallium were influenced by incidental sediment ingestion exposures, while HQs for selenium and PCBs
were influenced by dietary exposures. The issues associated with aluminum, lead, selenium, and PCBs
have been discussed for other receptors. Iron and thallium were not identified as COPCs for avian
receptors due to the lack of toxicity TRVs for birds. However, HQs were between 1.0 and 2.0 for the
mink. Given the conservative nature of SLRA, however, HQs of 1.0 to 2.0 are probably not of concern.
5.1.1.5 Snapping Turtle
As discussed earlier, there are currently insufficient tissue-based toxicity data with which to calculate
HQs for reptiles or reptile eggs; the latter has limited data available for PCB congeners. Furthermore,
given the unique physiology of reptiles, it is not plausible to assume that the sensitivity of reptiles is
similar to that of other classes, such as mammals or birds. PCB congener concentrations in snapping
turtle eggs ranged from 0.000049 mg/kg-wet (Congener 129) to 0.741 mg/kg-wet (Congener 66), with a
corresponding total PCB concentration of 3.683 mg/kg-wet. Accordingly, the data demonstrate that the
turtles are being exposed to PCBs, but the impact of these PCB levels in eggs on reproductive success of
the turtles is unknown.
Parametrix 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 5-6 October 2001
JC \woiting\37t3\37t3401\SUIA XtpertfinalSllUj'I.doe
-------
Figure 5-4. Chronic hazard quotients for spotted sandpipers feeding in the Ottawa River.
76
74
72
70
68
66
64
62
60
58
56
54
52
50
48
46
44
42
40
38
36
34
32
30
28
26
24
22
20
18
16
14
12
10
8
6
4
2
0
r—1 .—.
: F~
—H
-------
Figure 5-5. Chronic hazard quotients for mink feeding in the Ottawa River.
1000
100
c
.2
O
3
o
"D
re
re
~Aluminum
CD Lead
¦Selenium
~Thallium
~ PCB (Aroclor
1260)
~ Iron
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM >8.8
Lower Ottawa River SLRA
July 2001
555-3763-001
-------
5.1.2 Water Quality Criteria-Based Hazard Quotients
A second line of evidence using WQC was evaluated for wildlife. HQ values using WQC were calculated
as shown in Equation 6:
FFC
HQwnc = (6)
w wqc.M6
Where: EECwaur = Expected environmental concentration in water
WQCw.idi.fe = Water quality criterion for wildlife
Mercury was the only chemical detected in surface water with a wildlife criterion available. The HQs
ranged from 113 to 177 across the lower four river segments. These HQs considered alone suggest
mercury is posing a substantial risk to wildlife in the Ottawa River. However, compared to other lines of
evidence, these HQs appear to be overly conservative. For example, the U.S. EPA criterion for protection
of human health is 0.012 ng/L. Use of this criterion would result in HQs ten times lower, i.e., between
approximately 10 and 20. Furthermore, the mercury HQs based on the wildlife criterion are much higher
than those calculated for individual receptors, which were always less than 1.0. These HQs were based
on measured concentrations in fish tissue, 100 percent of which was assumed to be present as methyl
mercury9. Accordingly, the accumulation-based wildlife criterion may be overestimating mercury's
bioaccumulation potential in the Ottawa. Given the discrepancies in the lines of evidence for mercury,
potential risks to wildlife receptors from mercury may be considered uncertain. However, it does appear
that the extreme HQs based on the Ohio EPA wildlife criterion are overly conservative.
5.2 AQUATIC LIFE
Potential risks to aquatic life were also characterized using multiple lines of evidence. These include
HQs, the results of field studies using Ohio EPA biological criteria, and bioassays. The methods on how
each was used are discussed below.
5.2.1 Hazard Quotients
Similar to the approach for wildlife shown above, water- and sediment-based HQs for aquatic life were
calculated as shown in Equations 7 and 8, respectively:
HQ.„ = (7)
^QCaquatic life
EEC
UA _ /o\
*edirnml Sediment Guideline
9 In aquatic systems, mercury is generally present as inorganic mercury and methyl mercury. Methyl mercury is the
predominant form in fish tissue (Grieb et al. 1990).
Paramttrlx
Final Ecological SLRA of the Lower Ottawa River
5-9
53S-3763-001 (01/03)
October 200J
K: *wo/ttng\J7tJ\J74J-00JISLAA lUftrt^rinalSIJUjilebc
-------
5.2,1.1 Surface Water
Like the wildlife HQs, a surface water HQ for aquatic life greater than a value of l.O suggests that the
chemical may be present at a sufficiently high concentration to adversely affect aquatic communities.
However, an HQ greater than 1.0 does not mean that a chemical is definitely adversely affecting the
aquatic community, only that it may potentially be affecting the community and should be evaluated
further. An HQ less than 1.0 suggests negligible risks to the aquatic community.
The chemicals with individual acute and chronic HQs exceeding 1.0 are provided in Tables 5-1 and 5-2,
respectively. The HQs for all of the organic chemicals listed in the tables are highly uncertain because
these chemicals were rarely detected (usually in one of 19 samples, and never in more than three of 19
samples). For some organics, such as atrazine, the chemical was detected once in a sample with a lower
detection limit than the majority of the samples. Consistent with common risk assessment practice (Gliet
1985; Porter et al. 1988; U.S. EPA 1991b), a value of one-half the detection limit was used to calculate
risk when a chemical was not detected in a sample. Accordingly, the exposure concentration is likely
biased high using one-half the detection limit. It must be noted that the detected concentration was often
the same as the detection limit. These chemicals are italicized in Tables 5-1 and 5-2 to note the
uncertainty in the HQs. Additionally, for some chemicals, the detection limit was greater than the TRV
used to calculate HQs. Since one-half the detection limit was used to calculate HQs for samples where a
chemical was not detected, risk may be overestimated in these cases. Chemicals with detection limits
greater than their respective TRVs have been flagged in Tables 5-1 and 5-2 to note the uncertainty.
The HQs discussed in the preceding paragraph are based on the exposure concentrations and toxicities of
individual chemicals. However, chemical toxicity can be additive, particularly when the modes of toxic
action are the same. The additive toxicity of chemicals with narcosis as the mode of action (e.g., PAHs)
is a common example (e.g., Di Toro et al. 2000), as is the additive toxicity of certain divalent metals. The
toxicities of mixtures with different modes of action may also be additive, or even synergistic (Van der
Geest et al. 2000), but additivity across chemical classes was not evaluated given the lack of an
acceptable approach for site-specific chemical mixtures. Note that chemical mixtures may also possess
synergistic or antagonistic effects, but it is not possible for analyzing the possibility of these effects
without conducting testing with the chemical mixture of interest. The most common approach for
evaluating the additivity of mixtures is through the use of toxic units (TUs). Toxic units in surface water
are defined as the ratio of the concentration in a medium to the effect concentration in the medium
(Sprague and Ramsay 1965). The TU in surface water is thus defined as:
wi ~ „
WQC, i
In the equation, 'W' refers to water, T denotes the individual chemicals, and the denominator is the water
quality criterion (or similar toxicity guideline value). Note that the TU is calculated the same as the HQ
used in this SLRA. Accordingly, additivity of appropriate chemicals groups is evaluated through
summation of their HQs. Chemical additivity in this SLRA was evaluated for PAHs and divalent metals
(i.e., cadmium, cobalt, copper, lead, manganese, mercury, nickel, and zinc). It is important to note that
the effects of mixtures of metals cannot always be predicted from the effects of single metals. For
example, the relative concentrations of metals in a mixture, may influence the bioaccumulation and
toxicity of each individual metal (Harrahy and Clements 1997). The toxicity of a metal mixture may also
deviate from additivity when low concentrations of one metal are present with high concentrations of
another (Harrahy md Clements 1997). The toxicity of mixtures was termed IHQ in this analysis.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
5-10
SSS'3763-001 (01/03)
October 2001
K: **orktng\3763\3763-OOl tSL&A R^mtrnat SLKAjilikc
-------
Table S-1. Chemicals with Individual Acute HQs Exceeding 1.0 (HQ is shown in parentheses)
River Segment
0-3.2
3.2-4.9
4.9-6.5
6.5-8.8
>8.8"
Metals
Aluminum (4.6)
Manganese (3.8)
PAHs
Benzo(a)pyr&ne (2.1/
Benzo(b)fluoranthene (3.0f
Benzo(g,h,i)peryhne (4.6f
Benzo(k)fkioeanth«ne (3. if
Dibenz(a,h)anthracene (3.5/
lndono(1,2,3-cd)pymne (3.6)"
Other Organlcs
Pentachlonophenoi (5.5/
Aluminum (3.2)
Manganese (5.0)
Benzo(a)pyrene (2.1 f
Ber>zo(b)fluoranthene (3.0/
Benzo(g.h,i)peryiene (4.6f
Benzo(fc)ffuoranfhene (3.1/
Dibenz(a,h)anthracene (3.5/
lndeno( 1.2,3-cd)pyrene (3.6f
Pentachlomphanol (5.8/
Aluminum (1.9)
Manganese (21)
Benzo(a)pyrene (2. if
Benzofbjfluoranthene (3.0)"
Benzo(g,h.i)perylene {4.6)b
Benzo(k)fluoranthene (3.1/
Dfoenz(a,h)anthracene (3.5f
lndeno(1,2,3-cd)pymne (3.6/
Aluminum (1.5)
Manganese (6.1)
Benzo(a)pyrene (2.1/
Benzo(b)fluoranthene (3.0/
Benzo(g,h,i)peryiene (4.6/
Benzo(k)fluoranthene (3.1)"
Dibenz(a,h)anthracene (3.5/
lndeno(1,2.3-cd)pyrene (3.6}"
2,4-Oinitrophenol (2.5)
4.6-Dinitro-2-methylpherto/ (2.3)
Pentachlorophenol (5.8/
Phenol (1.3)
* No surface water chemistry data avaflable for this segment.
b Analytical detection limit for flris chemical was greater than the acute screening value.
Note: Italicized chemicals were rarely detected and, when detected, only at a concentration equal to the detection limit. Accordingly, the exposure concentration is largely influenced by
an uncertafci value that » one-half the detection Unit.
Pammtrix 5S5-376S-ooi (Oirn)
Final Ecological SLJtA of the Lower Ottawa River 5-11 October 2001
X: Wo/ftangtf 74 3763-00J iSLRA Rtport\FmalSLRA_ v! doc
-------
Table 5-2. Chemicals with Individual Chronic HQs Exceeding 1.0 (HQ is shown in parentheses)
River Segment
0-3.2
3.2-4.9
4.9-6.5
6.5-8.8
>8.8'
Metals
Aluminum (30)
Iron (4.3)
Manganese (17)
Pesticides
Atrazine (1.2)"
PAHs
Benzo(a)anthracene (1.3)b
Benzo(a)pyrene (4.1 f
Benzo(b)fluoranthene (6.0f
Benzo(g,h,i)pery!ene (8.9)"
Benzo(k)Huoranthene (6.1)"
Chrysene (1.4)b
Dibenz(a,h)anthracene (14)"
lndeno(1,2,3-cd)pyrene (14)"
Other Organlcs
2,4-Dinitrophenol (2.1)
4,6-Dinitro-2-methytpher>ol (1.9f
Pentachlorophenol (1.4)b
Phenol (1.1 f
Aluminum (25)
Iron (4.2)
Manganese (19)
Atrazine (1.2)b
Benzo(a)anthracene (1.3)"
Benzo(a)pyrene (4.1 f
Benzo(b)fluoranthene (6.0)"
Benzo(g,h,i)perylene (8.9/
Benzo(k)fluoranthene (6.1)"
Chrysene (1.4)"
Dibenz(a,h)anthracene (14)"
lndeno(1,2,3-cdjpyrene (14f
2,4-Dinitrophenol (2.1)
4,6-Dinitro-2-methylphenol (1.9)"
Pentachlorophenol (1.4)"
Phenol (1.1)b
Aluminum (14)
Iron (2.8)
Manganese (68)
Atrazine (1.2)"
Benzo(a)anthracene (1.3)b
Benzo(a)pyrene (4. if
Benzo(b)fluoranthene (6.0f
Benzo(g,h,i)perylene (8.9)"
Benzo(k)fluoranthene (6.if
Chrysene (1.4f
Dibenz(a,h)anthracene (14f
lndeno(1,2,3-cd)pyrene (14)"
2,4-Dinitrophenol (2.1)
4,6-Dinitro-2-methylphenol (1.9)"
Pentachlorophenol (1.4f
Phenol (1.1)"
Aluminum (13)
Iron (1.9)
Manganese (24)
Atrazine (1.2)"
Benzo(a)anthracene (1.3f
Benzo(a)pyrene (4. if
Benzo(b)fiuoranthene (6.0)"
Benzo(g,h,i)perylene (8.9)"
Benzo(k)ftuoranthene (6.1)b
Chrysene (1.4)b
Dibenz(a,h)anthracene (14)"
lndeno(1,2,3-cd)pyrene (14)"
Pyrene (1.4)
2.4.5-Trichlorophenol (1.3)
2.4.6-Trichlorophenol (1.3)
2,4-Dinitrophenol (2. if
4.6-Dinitro-2~methylphenol (1.9)b
Pentachlorophenol (1.4)"
Phenol (1. if
No surface water chemistry data available for this segment.
Analytical detection limit for this chemical was greater than the chronic screening value.
Note: Italicized chemicals were rarely detected and, when detected, only at a concentration equal to the detection limit,
an uncertain value that is one-half the detection limit..
Accordingly, the exposure concentration is largely influenced by
Parametria 555-3?63-ooi fOirni
Final Ecological SLRA of the Lower Ottawa River 5-12 October 200J
K:Wof*»vgVi763\i763-OOJ\SUUR
-------
The IHQs for divalent metals (cadmium, copper, lead, mercury, nickel, and zinc) are shown, by reach, in
Table 5-3. Acute IHQs were all less than 1.0, while chronic IHQs ranged between 1.2 and 1.5
depending on the river segment. However, these chronic IHQs were not considered significant because
only total recoverable metal concentrations (particulate bound and dissolved fraction) were available. As
discussed in previous sections, the toxicity of divalent metals is almost entirely a function of the free ion
(dissolved concentration). Accordingly, since 1993, the national AWQC promulgated by the U.S. EPA
have been based on dissolved metal (filtered through a 0.45 nm filter) (Prothro 1993). However, even
dissolved metal can be a conservative estimate of bioavailable metal because other dissolved surface
water constituents, such as dissolved organic carbon (DOC), can reduce bioavailability (Taylor et al.
2000). The bioavailable fraction of divalent metals in natural waters may be up to 26 times less than
laboratory waters that are typically used to derive aquatic life toxicity values and water quality
standards/criteria (Welsh et al. 2000). Accordingly, IHQs of 1.2 to 1.5 for divalent metals were
considered unlikely to pose risk to aquatic life from direct toxicity.
Overall, the risks posed by chemicals in lower Ottawa River surface water are uncertain. Hazard
quotients exceeded 1.0 for a number of chemicals, but uncertainty exists with each of these. For example,
HQs greater than 1.0 for aluminum, iron, and manganese are likely overconservative because these metals
are often elevated at background concentrations and largely non-bioavailable. For die organic chemicals
with HQs greater than 1.0, the risk posed to aquatic life are highly uncertain because they are largely
influenced by values one-half the detection limit. Many of these compounds, PAHs in particular, are
extremely hydrophobic, so they would not be expected to pose a high risk in surface water. Further
analyses can assist in resolving these uncertainties. For example, measurements of dissolved metal or
surface water bioassays can both provide information on metal bioavailability. For organics, achievement
of detection limits below risk-based toxicity values would allow determination of whether these
chemicals are posing unacceptable risks. Lastly, the risk characterization of hydrophobic chemicals in
sediment provide a more adequate assessment risk, so the uncertainty in the surface water risk
characterization for these compounds may be considered relatively insignificant to the overall conclusions
of the ecological SLRA.
5.2.1.2 Sediment
For sediment, a weight-of-evidence approach was also used to screen chemical risks in sediment. As
discussed in the Effects Characterization (Section 4.2.2), a variety of different types of sediment
guidelines (e.g., ER-L, ER-M) from multiple sources (e.g., Environment Canada 1995; Ingersoll et al.
1996) were used in this SLRA. The ability of these different types of guidelines to predict toxicity (or
lack of toxicity) to benthic organisms was reviewed by Long et al. (1998). Long et al. assessed the
toxicity of hundreds of field-collected sediment samples using various laboratory bioassays. Based on the
data provided in their paper, it is clearly evident that several ER-L values, and even more TEL values,
need to be exceeded before sediment toxicity is observed with any consistency.
The following rules were followed in determining whether a chemical was a COPC. First, if the
concentration of a chemical exceeded its corresponding PEL or ER-M, it was considered a COPC. For
TEL and ER-L exceedances, the analyses of Long et al. (1998) were considered to interpret the sediment
HQs. A step-wise ANOVA was conducted to determine how many ER-L values for metals need to be
exceeded before excess sediment toxicity is observed (i.e., before the degree of toxicity is significantly
different than when no ER-L values are exceeded) and bow many TEL values need to be exceeded in a
common sample before excess sediment toxicity is observed. The end result is that if four or more metals
exceed their ER-L values for a given site, or nine or more metals exceed their TEL, those metals are
considered COPCs.
Paramctrix
Final Ecolog/cal SLRA cf tht Lawtr Ottawa River
5-13
SSS-3763-001 (01/03)
October 2001
K \wt>r**tOIIStM SLKAjtl Joe
-------
Table 5-3. EHQs for Divalent Metals in Surface Water
River Segment
0-3.2
3.2-4.9
4.9-6.5
6.5-8.8
>8.8'
Acute
< 1.0
<1.0
< 1.0
< 1.0
-
Chronic
1.5
1.4
1.2
1.3
-
3 No surface water chemistry data available for this segment.
For metals, it is important to note that dry-weight sediment concentrations are not predictive of
bioavailability, while sediment pore water concentrations have been shown to be correlated with
biological effects (Ankley et al. 1996). The primary partitioning phase controlling cationic metal activity
and toxicity in the sediment-pore water system is acid volatile sulfide (AVS) (Di Toro et al. 1990, 1992).
On a molar basis, AVS binds with cationic metals, resulting in insoluble sulfide complexes with
minimum biological bioavailability (Ankley et al. 1996). According to U.S. EPA (2000b), if the
simultaneously extracted sum of molar concentrations of cadmium, copper, lead, nickel, silver, and zinc
are less than the molar AVS concentrations, toxicity will not be observed. Of the 19 AVS.SEM samples,
the molar ratio of SEM (based on the sum of cadmium, copper, lead, nickel, silver, and zinc) to AVS was
always greater than 1.0 (mean, minimum, and maximum were 1,664, 1.1, and 8,562, respectively).
Accordingly, the AVS:SEM data cannot be used to support an absence of metal toxicity in sediment. It is
important to note that exceedance of the molar AVS concentration does not necessarily suggest that the
SEM metals are present at toxic concentrations because other factors can reduce metal bioavailability as
well, such as dissolved organic carbon (which was not measured).
For sediment guidelines that are normalized to the organic carbon content of the sediment, the 93 percent
lower confidence limit on the mean oiganic carbon concentration was conservatively used for each river
segment. When only two organic carbon samples were available for a reach (such as segment four in
Inventory 20), the minimum organic carbon concentration was used.
The chemicals with HQs greater than 1.0 based on ER-Ms or PELs from the year 1998 sampling event are
shown in Figure 5-6. Lead and PCB (total) HQs consistently exceeded 1.0 for the lower four river
segments. More COPCs were identified for RMs 3.2 to 4.9, with cadmium and chromium also being
identified, but the highest HQs for PCBs were observed between RMs 4.9 to 6.5. The land adjacent to
this segment of the river contains a number of landfills and industrial facilities (see Figure 1-1).
Accordingly, based on these data, metals concentrations appeared most elevated from RMs 3.2 to 4.9, and
PCBs were most elevated from RMs 4.9 to 6.5. Using the PEL from Ingersoll et al. (1996), HQs from 0
to 24" samples were compared to those from greater than 24" (Figure 5-7). With a few exceptions, HQs
decline in the core sediment samples (i.e., greater than 24"). These lower HQs likely reflect lower
concentrations as a result of the larger compositing volume, rather than lower toxicity per se.
Based on the year 2000 sediment sampling results, HQs for those chemicals exceeding Ingersoll et al.
(1996) ER-M and PEL values or Environment Canada (1995) PEL values are shown graphically in Figure
5-8. Like the 1998 sediment HQs shown in Figure 5-6, lead and PCB HQs consistently exceed 1.0. The
highest HQ for lead occurs between RMs 4.9 and 6.5, and is largely affected by the single sample
discussed in the wildlife risk characterization. With this exception, HQs for PCBs tend to be the highest,
followed closely by organochlorine pesticides.
Parametrix 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 5-14 October 2001
K:
-------
Figure 5-6. Sediment HQs >1.0 based on ERMs and PELs using 1998 surface (<24") sediment
data.
1000
100
RM 4.9-6.5
A
RM 6.5-8.8 RM >8.8
A
RM 3.2-4.9
RM 0-3.2
&
8
Pb PCBs Cd
Cr
Pb PCBs Pb PCBs Pb PCBs None
~ Ingersol-ERM Elngersol-PEL ~ Environment Canada-PEL
Lower Ottawa River SLRA
July 2001
555-3763-001
-------
Figure 5-7. Comparison of sediment HQs based on 1998 surface (<24") and core (>24")
sediment data.a
1000
100
RM 4.9-6.5
A
RM 6.5-8.8 RM >8.8
( A
RM 3.2-4.9
RM 0-3.2
a 0-24"
ED>24"
&
Pb PCBs Cd Cr Pb
a-HQs calculated using the PEL from Ingersol et al. 1996
PCBs None
Lower Ottawa River SLRA
July 2001
555-3763-001
-------
Figure 5-8. Sediment HQs >1.0 based on ERMs and PELs using 2000 surface sediment data.
1000
RM 4.9-6.5
RM 3.2-4.9
RM 6.5-8.8
RM 0-3.2
S Ingersol-ERM H ingersol-PEL B Environment Canada-PEL
Lower Ottawa River SLRA
July 2001
555-3763-
-------
The sediment HQs, by station, were plotted on maps for three chemicals or chemical classes. (1) lead; (2)
total PCBs; and (3) total PAHs (Appendix D). Lead and total PCBs were plotted since they appear to be
the driving chemicals for potential risk to both wildlife and benthic aquatic life. Although HQs for total
PAHs did not exceed 1.0, the potential risk they pose is uncertain since all PAHs and their key derivatives
were not analyzed10. The maps were derived as a tool to visually identify potential hot spots. The
sediment data, on a sample-by-sample basis, were plotted by color to denote whether the chemicals
exceed their respective sediment guideline value. For the 1998 data, samples were also plotted by depth
(0 to 24" and greater than 24").
5.2.1.3 Tissue Residues
When tissue residue-based effects data were available for chemicals detected in fish tissue, HQs were
calculated using the concentrations measured in Ottawa River fish. As discussed in Section 3.2.2, the
dietary pathway was more important for certain chemicals (e.g., selenium, PCBs), making it more
difficult to predict effects based on water exposure and toxicity data. Chemicals with HQs exceeding 1.0
were lead and PCBs (Figure 5-9). The HQs are provided in Table C-7 of Appendix C. As presented
above, these two chemicals were identified as COPCs for aquatic life in sediment. Thus, sediment
concentrations may be sufficiently high to transfer to lower levels of the food chain and reach levels in
fish tissue that may cause adverse effects.11
5.2.2 Bioassays
Bioassay results provide a corroborative line of evidence to the HQ screening risk predictions. The
bioassays reflect site-specific conditions that can modify toxicity. For example, sediment bioassays
provide evidence on the bioavailability of chemicals to the test organism. Moreover, the bioassays assess
the toxicity of chemical mixtures, so potential antagonistic, additive, or synergistic impacts are implicitly
addressed in the measured effect. Bioassay results, thus, provide information on whether the HQ
predictions were conservative or non-conservative. In 1998, the Ohio EPA evaluated the toxicity of
Ottawa River sediment samples to the amphipod Hyalella azteca and the oligochaete Lttmbriculus
variegatus (OEPA 1998). The sediment samples were collected up to a depth of approximately 10 cm
where possible and homogenized. The H. azteca and L. variegatus bioassays were conducted for 10 and
4 days, respectively. The locations and dates of the bioassays are provided in Table 5-4.
None of the sediment samples was observed to be toxic to H. azteca or L. variegatus. H. azteca survival
was 96.3 percent at Site 09. Comparison of each of the nine Ottawa River sampling sites to the
University of Toledo reference station using Steel's many one-rank test did not indicate a significant
difference on survival of L. variegatus. Accordingly, the sediments do not appear to be acutely toxic to
either of these test organisms.
10 According to U.S. EPA (2000a), these include the PAHs on the EPA's Priority Pollutant list, as well as alkylated
naphthalenes, phenanthrenes, fluoranthenes, fluorenes, and chrysenes.
11 It should be clarified that lead and PCBs are transferred through the food chain much differently. Lead
concentrations tend to decline with increasing trophic level (Vighi 1981), while PCB concentrations tend to increase
with increasing trophic level (i.e., biomagnify) (Suedel et al. 1994).
Parametrix 515-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 5-18 October 2001
K iwoi**>t\J7i3\J763-001ISLM bat SLRA
-------
Figure 5-9. Chronic hazard quotients for fish in the Ottawa River using tissue based TRVs.
5
~ Pb
EDPCBs
Lower Ottawa River SLRA
July 2001
555-3763-00J
-------
Table 5-4. Location and Dates of Whole Sediment Toxicity Bioassays
Sample Site
Species Tested
Date Collected
Dates Tested
Site 09/Downstream Summit St.
H. azteca,
L variegatus
L. variegatus
L variegatus
L variegatus
L. variegatus
L. variegatus
L. variegatus
L. variegatus
L. variegatus
L. variegatus
12 Aug 98
17-28 Aug 98
Site 10/@ I-75
Site 11/Downstream of Stickney Ave.
Site 12/Adjacent to Stickney Ave.
Site 13/Upstream of Railroad Trestle
Site 14/@ Lagrange St.
Site 15/@ Berdari Ave.
Site 16/@ Jeep Parkway
Site 17/@ Auburn Ave.
Site 18/@ U. of Toledo (Ref/Station)
3 Aug 98
3 Aug 98
3 Aug 98
10 Aug 98
10 Aug 98
10 Aug 98
18 Aug 98
18 Aug 98
19 Aug 98
8-12 Aug 98
8-12 Aug 98
8-12 Aug 98
12-16 Aug 98
12-16 Aug 98
12-16 Aug 98
24-28 Aug 98
24-28 Aug 98
24-28 Aug 98
Chemistry data were available for Site 09. Some key chemicals detected and their concentrations are
listed in Table 5-5. Sediment TEL and PEL guidelines are provided for comparison to the metal,
organochlorine, and PCB concentrations, while the sediment quality guidelines from Di Toro and
McGrath (2000) are provided for comparison to the PAH data. Most of the metal, pesticide, and PCB
concentrations exceeded their respective TELs, and nickel, zinc, DDE, and PCB concentrations also
exceeded their respective PELs. Accordingly, toxicity in this sediment sample would have been predicted
using sediment guidelines. This may suggest that the bioavailability of the chemicals is reduced.
However, the lack of toxicity may also be due to the length of the bioassays. Ingersoll et al. (2001)
recently compared the 10- to 14-day H. azteca test, which measures survival, and the 28- to 42-day H.
azteca test, which measured survival and reproduction. The 28- to 42-day test was typically found to be
six times more sensitive than the 10- to 14-day test. Accordingly, since the H. azteca bioassay used in the
Ottawa River sample was a 10-day study, the lack of toxicity is probably more a function of the type of
test that was conducted, rather than reduced bioavailability. Accordingly, the lack of toxicity in this
sample provides only limited corroborative information for the predicted sediment HQs.
5.2.3 Biological Criteria
Biological monitoring data were used to assess whether there was a relationship between the condition of
the biological community and the HQs calculated and described above. The condition of the biological
community in the lower Ottawa River was evaluated using biological indices for benthic
macroinvertebrates and fish communities. The biological index data used in the analysis were calculated
by the Ohio EPA and no changes were made to any indices. However, means of indices were used when
more than one sample event occurred in a year and when more than one sample location fell within the
river segments evaluated in this SLRA. For example, five different benthic macroinvertebrate sample
locations were assessed by Ohio EPA between RMs 4.9 and 6.5.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
5-20
555-3763-001 (01/03)
October 2001
K: \worHngWi3\37t3-OOVSIJtA RfonxFlnal SlM_vl doe
-------
Table 5-5. Comparison of Sediment Chemistry from Bioassay Sample Site 09
to Sediment Quality Guidelines
Chemical
Concentration
(mg/kg dw)
Ingersoll etal. (1996)
TEL
PEL
Di Toro and McGrath
(2000)
Caao
Metals
Arsenic 9.76
Cadmium 1.67
Chromium 67.8
Copper 55.8
Lead 75.7
Nickel 41.8
Zinc 220
Pestlcides/PCBs
DDD 0.0185
DDE 0.0375
Aroclor 1248 2.5
Aroclor 1260 0.115
Total PCBs" 2.6
PAHs
Benzo(a)pyrene 1.2
Benzo(b)fluoranthene 1.6
Benzo(g,h,i)perylene 1.2
Benzo(k)fluoranthene 1.2
Chrysene 1.5
Fluoranthene 1.9
lndeno(1,2,3-cd)pyrene 1.3
Pyrene 1.6
11
0.58
36
28
37
20
98
0.00142*
0.032
48
3.2
120
100
82
33
540
0.00675*
0.24
50.6
51.3
57.4
51.4
44.2
37.1
58.5
36.6
TEL and PEL from Environment Canada (1905).
Total PCBs estimated by Bumming Aroclor 1248 and Aroclor 1260.
5.2.3.1 Biological Indices Evaluated
A select group of the benthic macroinvertebrates indices developed by Ohio EPA were used in this risk
assessment The indices include those that were based on quantitative (Hester Dendy sampler12) and
qualitative (kicknet) macroinvertebrate collection. The Ohio EPA (appropriately) uses both methods to
evaluate streams and rivers in their assessment. These indices include those that are important indicators
for metal stress (mayfly richness), as well as those that are important for evaluating stress from organic
chemicals (caddisfly richness). An additional summary index being developed by Ohio EPA was also
used, the Lacustuary Invertebrate Community Index (LICI). This index was used for stream and river
sites that are influenced by Lake Erie.
12 Hester Dendy samplers are artificial substrate samplers that are placed in the water column by securing the
sampler by an anchor and then held in the water column by a float.
Parametrlx 155-3763*001 (01/03)
Final Ecological SLRA of tht Larwtr Ottawa Rlvtr 3-21 Qctabtr 2001
K: brntti&HJUm-MlVUM. Rip°H
-------
Multiple indices for fish were also used. These indices include those that consider general fish
community health based on fish richness, relative abundance, and those that consider the health of
individual fish health based on external anomalies, or DELT (deformities, fin erosions, lesions/ulcers, and
tumors). Two different summary indices used by the Ohio EPA were used in this evaluation: an Index of
Well Being (IWB2) and an Index of Biotic Integrity (IBI) for lacustrine conditions.
5.2.3.2 Results
In general, the biological indices suggested that benthic macroinvertebrate and fish communities within
the lower Ottawa River are not in good condition. For benthic macroinvertebrates, the LICI values were
all much lower than the interim goal of 42 for LICI rated streams and rivers (Table 5-6) (OEPA 1998).
The IBI scores for fish were also low compared to the goal of 42 for lacustrine sites (OEPA 1998). The
IWB2 scores are also slightly below their respective goals of 8.6 for boat sites and 7.3 for wading sites
(OEPA 1999). Thus, the biological index results suggest non-attainment of aquatic life use designations
in the lower Ottawa River.
Table 5-6. Summary Indices for Benthic Macroinvertebrates and Fish
River Mile 0-^2 3.2-4.9 4.9-6.5 6.5-8.8
Benthic Macroinvertebrates
LICI 8 14 13 15
Fish
IWB2 7.1 6.2 6.1 6.6
IBI, Lacustrine 24.0 20.0 21.3 21.3
Surface water HQs from Table 5-2 were compared to benthic invertebrate and fish indices in Table 5-7.
There does not seem to be a clear relationship between many of the benthic invertebrate indices and the
surface water HQs. In general, the surface water HQs decrease from downstream to upstream, yet many
of the macroinvertebrate indices tend to increase. Most of the indices should decrease if the
macroinvertebrate community was being stressed. However, macroinvertebrate richness based on kicknet
samples increased and caddisfly richness decreased as the surface water HQs increased. Diptera richness
is often found to increase when other taxa are stressed because they tend to be more tolerant of stress. In
fact, in this evaluation, Diptera richness does increase with increasing surface water HQs. The lack of a
clear relationship for some indices may exist because the Hester Dendy sampler is a device that is used in
the water column, i.e., the sample is set in the water column. Thus, Hester Dendy results reflect
conditions in the water column but not in the sediment.
With the fish there were better relationships between surface water HQs and the indices. Most of the
indices decreased as the surface water HQs increased in a downstream manner. Contrary to most indices,
the DELT index should increase as the surface water HQs increase, however, there was no clear trend for
this index. Although a predictable pattern was not observed with the DELT index, approximately seven
percent defonnities were observed in multiple river reaches. An example of a carp exhibiting severe
deformities is provided in Figure 5-10. It is possible that PAHs are contributing to these deformities since
certain PAH compounds can induce teratogenic effects (U.S. EPA 2000). Accordingly, the comparison of
biological indices to sediment HQs in the following paragraph may be more relevant because PAHs are
hydrophobic. Ultimately, however, further studies would be necessary to determine whether PAH
Paramctrix
Final Ecological SLRA of the Lower Ottawa River
5-22
555-3763-001 (01/03)
October 2001
K: \Kork*rf\37tiM?t)-Oei tSIM Jtqx,rtflnalSUUj>l
-------
concentrations are sufficiently elevated to induce the observed deformities. Clearly, fish do seem to be
affected and the biotic indices reflect this conclusion.
Table 5-7. Summary of Chronic HQs for Surface Water and Invertebrate and Fish Biotic Indices
River Mile 0-3.2 3.2-4.9 4.9-6.5 6.5-8.8
HQs
Aluminum 30 25 14 13
Manganese 17 19 68 24
Selenium 2.9 2.0 1.5 1.3
Sum of Divalent Metals 1.5 1.4 1.2 1.3
Cyanide 1.0 1.0 2.4 0.7
Sum PAHs 56 43 77 200
Sum SVOs 6.5 6.5 6.4 30
Benzo[b]fluoranthene 6.0 4.5 8.4 21
Diber>z[a,h]anthracene 14 10 19 49
lndeno[1,2,3-cd]pyrene 14 11 20 50
2,4-Dinitrophenol 2.1 2.1 2.1 9.7
Phenol 1.1 1.1 1.1 5.2
Invertebrate Biotic Indices
Abundance, Hester Dendy 2875 814 1108 213
Taxa Richness, Hester Dendy 11 14 15 19
Taxa Richness, Kicknet 25 27 14 9
Mayfly Richness, Hester Dendy 10 0 1
Caddisfly Richness, Hester Dendy 110 0
Diptera Richness, Hester Dendy 3 5 9 11
Ephemeroptera Plecoptera Trichoptera (EPT), 2 2 0 0
Kicknet
EPT, Hester Dendy 2 10 1
ICI, Estuary 8 14 13 15
Fish Biotic Indices
Fish Richness 13 13 11 11
Cumulative Number of Fish Species 19 20 18 17
based on all sample events
Fish Abundance 624 495 362.5 400
Biomass, kg 280 133 50 55
Percentage of fish with DELT anomalies 6.8 6.3 7.5 6.4
IWB2 7.1 6.2 6.1 6.6
IBI, Lacustrine 24.0 20.0 21.3 21.3
Parametrix
Final Ecological SLRA of the Lower Ottawa River
5-23
555-3763-001 (01/03)
October 2001
JC' trarMifUftJUTVJ'00/ IS1M JUport\ftotal SUMj>l-
-------
>X'Xv
Figure 5-10 Deformed carp caught in the Lower Ottawa River
Parametrix 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 5-24 October 2001
K: lwortrigtJ7(J\J76J.0e/lSL/U ReponVmalSLRA doc
I
-------
Sediment HQs were also compared to benthic invertebrate and fish indices (Table 5-8). There appeared
to be a better relationship between the sediment HQs and the indices than there was for the surface water
HQs. When the sediment HQs increased, many of the biotic indices correspondingly decreased. Like the
surface water HQs, macroinvertebrate richness based on kicknet samples and caddisfly richness also
decreased as the HQs increased, and Diptera richness increased as the HQs tended to increase. Sediment
HQs and fish indices did show a relationship that would be expected, as the biotic indices generally
decreased as the HQs increased. Clearly, stressor conditions in the sediment are associated with
conditions in the water column for fish. Furthermore, stressor conditions in sediment are associated with
benthic macroinvertebrates.
Table 5-8. Sediment HQs and Invertebrate and Fish Biotic Indices"
River Mile 0-3.2 3.2-4.9 4.9-6.5 6.5-8.8
HQs
Cadmium 0.7 0.5 1.2 0.7
Chromium 0.5 0.5 1.1 1.0
Copper 0.9 0.6 1.0 1.0
Lead 1.2 3.2 199.1 3.6
Nickel 1.3 1.1 1.2 0.7
Zinc 0.5 0.5 0.6 1.1
PAH (total) 0.7 0.7 0.6 1.3
PCB (total) 2.2 11.2 10.6 10.7
Invertebrate Biotic Indices
Abundance, Hester Dendy 2875 814 1108 213
Taxa Richness, Hester Dendy 11 14 15 19
Taxa Richness, Kicknet 25 27 14 9
Mayfly Richness, Hester Dendy 1 0 0 1
Caddisfly Richness, Hester Dendy 110 0
Diptera Richness, Hester Dendy 3 5 8.5 11
Ephemeroptera PlecopteraTrichoptera (EPT), 2 2 0 0
Kicknet
EPT, Hester Dendy 2 10 1
ICI, Estuary 8 14 13 15
Fish Biotic Indices
Fish Richness 13 13 11 11
Cumulative Number of Fish Species 19 20 18 17
based on all sample events
Fish Abundance 624 495 363 400
Biomass, kg 280 133 50 55
Percentage of fish with DELT anomalies 6.8 6,3 7.5 6.4
IWB2 7.1 6.2 6.1 6.6
IBI, Lacustrine 24.0 20.0 21.3 21.3
* Based on data from Inventory 20 and using PEL* or Csqq.
Psramstrlx 555-3763-001 (01/03)
Pined Ecological SLRA of the Lower Ottawa River 5-25 October 2001
K: \waikhtJHS\3HS-O0i \SlAl tc
-------
5.3 UNCERTAINTIES
A discussion of uncertainties is important in any risk assessment and can be critical in making risk
management decisions. A consideration of uncertainties is also imperative in using the lines of evidence
approach discussed above. For example, the lines of evidence need to be balanced by considering the
amount of uncertainty associated with each (U.S. EPA 1998a).
Wherever possible, conservative assumptions were used in estimating receptor exposures to chemicals
and in identifying toxicity thresholds. The largest sources of data to the ecological SLRA were the
chemistry data for sediment, fish tissue, and surface water. These data were used to estimate whether
individual chemicals, and in some cases classes of chemicals, were present at sufficiently high
concentrations to pose a potential risk to ecological receptors. This approach uses site-specific chemistry
data, but assumptions are required in estimating the magnitude of exposure by biota. These assumptions
include the fraction of time a wildlife receptor feeds in a river segment and the bioavailability of
chemicals. In die SLRA, it was assumed that a wildlife receptor may feed in a given river segment 100
percent of the time over a chronic exposure duration and that chemicals were 100 percent bioavailable.
A key uncertainty in this SLRA was the effects of seiches on the screening risk estimates. Seiches likely
remobilize chemicals in sediment and increase the likelihood that exposure by ecological receptors will
occur, particularly over acute durations. As an analogous example, seiches have been shown to lift
nutrients from sediment to the water column (Korgen 2000). As nutrients are released into the water
column, organisms are attracted to these nutrients, thereby further increasing the exposure potential to
chemicals by ecological receptors. Over shorter durations, seiches may also result in greater exposure of
mudflats that certain shorebirds (e.g., spotted sandpiper) may feed upon. To further understand the
effects of seiches on chemical mobility and influences on receptors, specific studies over varying flow
conditions would be necessary.
Potential risks to the snapping turtle were also a potentially significant uncertainty. Measurement of
PCBs in snapping turtle eggs was recommended as a monitoring tool (Pagano et al. 1999), but no data are
available linking PCB congeners in eggs to toxic effects. However, it is known that snapping turtles are
capable of storing high concentrations of PCBs in their fat without any apparent detrimental effects
(Olafsson et al. 1983). Further studies would be necessary to understand whether turtles in the lower
Ottawa are at risk from PCBs or other chemicals.
The 1998 sediment data were used in the SLRA for benthic aquatic life because they represented a
thorough sampling of the lower Ottawa River. However, the relevance of these data to biological
exposures is highly uncertain because they were composited over depths much greater than the
biologically active zone (i.e., approximately the top 2 inches). Compositing sediment depths of up to 24"
or more may result in sediment exposure concentrations for benthos being under- or overestimated,
depending on the magnitude of historical chemical loading to the river sediment. Consequently, the HQ
results based on the 1998 and 2000 data should both be considered since the 2000 data are based on
sediment from the biologically active zone.
As discussed in the aquatic life SLRA for surface water, concentrations of several oiganic chemicals (e.g.,
PAHs) exceeded their toxicity reference values. However, these chemicals were infrequently detected
and the exposure concentration was influenced by the magnitude of the detection limit (because half the
detection limit was used for non-detect data). Achievement of lower detection limits for these chemicals
would confirm whether they are truly posing unacceptable risk.
Parametrix SSS-3763-ooi (Oi/o$)
Final Ecological SLRA cf the Lower Ottawa River 5-26 October 2001
K: \worHifi3f61\37t3-MJ \SJJH R*fKrt\Ftml SlRAjtlihc
-------
Lastly, conducting chronic bioassays would strengthen this line of evidence for the estimated aquatic life
risks. The most recent bioassays are based on acute exposure durations and no toxicity was observed.
These results did not corroborate with the sediment HQs calculated for benthic aquatic life which were
greater than 1.0 for multiple chemicals. These HQs were calculated using sediment quality guidelines
that were largely influenced by chronic toxicity values. Accordingly, chronic bioassays would be more
appropriate for interpreting the significance of the HQs.
Paramatrix
Final Ecological SLRA of the Lower Ottawa River
5-27
535.3763-001 (01/03)
October 2001
topwMmlStMjtt.dK
-------
6. CONCLUSIONS
Using conservative assumptions on chemical exposure and toxicity, the SLRA identified potential hot
spots of chemical risk to wildlife and aquatic life. The SLRA focused largely on sediment, surface water,
and tissue data collected in 2000, as these data are most relevant to current conditions in the Ottawa
River. However, the extensive sediment data from 1998, sediment bioassays, and aquatic community
biocriteria were also considered.
The HQ evaluation for wildlife and aquatic life identified chemicals of potential concern for multiple
segments of the lower 9 miles of the Ottawa River. Lead and PCB HQs consistently exceeded 1.0 for both
wildlife and aquatic life, although HQs for other chemicals also exceeded 1.0 for specific ecological
receptors and locations (Table 6-1). For wildlife, lead HQs were influenced by concentrations in
sediment, while PCB HQs were influenced by tissue (i.e., food item concentrations). Figure 6-1
graphically shows the sum of HQs greater than 1.0 (i.e., driver chemicals) by river segment and
ecological receptor. Segment 3 (RM 4.9 to 6.5) was identified as posing the highest risk to all ecological
receptors (Figure 6-1). The high potential risk in this river segment is largely driven by a single sediment
sample with a lead concentration of 26,000 mg/kg dry weight (based on the year 2000 data). A lead
concentration of this magnitude was not detected in the 1998 sampling event. It is interesting that
maximum concentrations of other metals were also detected in the same sample, suggesting that the lead
result is not a lead-specific anomaly. Further sampling of this location would be useful to understand the
extent of contamination.
PCB concentrations in tissue and sediment were consistently elevated, posing potential risk to wildlife
and aquatic life in the following river segments: RMs 3.2 to 4.9, RMs 4.9 to 6.5, and RMs 6.5 to 8.8.
The river locations with the highest PCB levels were quite variable and differed between the 1998 and
2000 data. In 1998, for example, the highest PCB concentrations occurred between RMs 1.8 to 3.8 in the
top 24" of sediment. In 2000, the highest PCB concentrations occurred between RMs 3.6 to 5.8. These
results suggest that identification and potential remediation of hot spots should rely most heavily on the
most current data. In addition, it should be noted that PCB and lead hot spots were not co-located,
suggesting different sources, and possibly transport, within the river.
Given that many of the lines of evidence used in this evaluation were based on independent studies from
multiple years, it is recommended that the COPCs and locations of greatest concern identified here be
further evaluated using temporally and spatially co-located chemistry data and chronic bioassays. These
studies would support whether the COPCs identified here are truly of concern and would assist in
prioritizing further remediation options.
Parametrix SS5-3763-001 /01/03)
Final Ecological SUM of the Lower Ottawa River 6-1 October 2001
K: *»orUnt376mm-aoi'81M HtpertVtrialSLIUvldix
-------
Table 6-1. Chemicals with Chronic HQs > 1.0 by Ecological Receptor and River Segment
Receptor
Segment 1
(RM 0-3.2)
Segment 2
(RM 3.2-4.9)
Segment 3
(RM 4.9-6.5)
Segment 4
(RM 6.5-8.8)
Aquatic Life - Pelagic
Aluminum (30)'
Aluminum (25)
Aluminum (14)
Aluminum (13)
Iron (4.3)
Iron (4.2)
Iron (2.8)
Iron (1.9)
Manganese (17)
Manganese (19)
Manganese (68)
Manganese(24)
Aquatic Life - Benthic
Lead (1.2)
Lead (3.2)
Cadmium (1.2)
Chromium (1.1)
Nickel (1.3)
Nickel (1.1)
Chromium (1.2)
Copper (1.0)
PCBs (2.2)
PCBs (11)
Lead (199)
Nickel (1.2)
PCBs (11)
Lead (3.6)
Zinc (1.1)
PCBs (11)
Bald Eagle
PCBs (1.3)
PCBs (4.3)
Lead (2.6)
PCBs (3.5)
PCBs (2.9)
Common Tem
Selenium (1.1)
PCBs (22)
Lead (13)
PCBs (15)
PCBs (6.8)
DDT (1.9)
Selenium (1.2)
PCBs (18)
DDT (2.4)
DDT (4.0)
Spotted Sandpiper
Aluminum (1.7)
Aluminum (1.9)
Aluminum (1.6)
Aluminum (1.6)
PCBs (2.7)
Chromium (1.0)
Chromium (2.3)
Chromium (2.3)
Lead (1.0)
Lead (71)
Lead (1.4)
PCBs (17)
PCBs (11)
DDT (1.6)
Cyanide (1.2)
PCBs (11)
DDT (1.7)
Mink
Aluminum (16)
Aluminum (18)
Aluminum (15)
Aluminum (15)
Lead (1.7)
Iron (1.0)
Lead (254)
Lead (6.0)
Selenium (1.6)
Lead (4.1)
Selenium (1.6)
Selenium (1.1)
Thallium (1.7)
Thallium (2.1)
PCBs (1.9)
Thallium (1.5)
Thallium (2.7)
* Value in parentheses is the chronic HQ.
Paranwtrlx
Final Ecological SLRA of the Lower Ottawa Rivtr
6-2
555-3763-001 (01/03)
Octobtr 2001
K: tooitmtVWUHhMtSUA AporttflMSU4_vi.dK
-------
Ecological Hazard Quotient Comparison by River Segment
300
250
200
150
100
S Aquatic Life-Pelagic
S Aquatic Life-Benthic
DO Bald Eagle
0 Common Tern
B Spotted Sandpiper
¦ Mink
Segment 1
RM 0-3.2
Segment 2
RM 3.2-4.9
I
1
i
1
I
Segment 3
RM 4.9-6.5
Segment 4
RM 6.5-8.8
Pelagic aquatic life HQs driven by ubiquitous metals and are likely extremely conservative.
-------
REFERENCES
Ankley, G.T., D.M. Di Toro, D.J. Hansen, and W.J. Berry. 1996. Technical basis and proposal for
deriving sediment quality criteria for metals. Environ. Toxicol. Chem. 15(12):2056-2066.
Bengtsson, B.E. 1980. Long-term effects of PCB (Clophen A50) on growth, reproduction, and
swimming performance in the minnow Phoxinus phoxinus, Water Res. 14:681-687.Biyson,
W.T., K.A. MacPherson, M.A. Mallin, W.E. Partin, and S.E. Woock. 1985. Hyco Reservoir
1984 bioassay report. Carolina Power and Light Company, New Hill, North Carolina. 51 pp.
Casas, G.A. and E.A. Crecelius. 1994. Relationships between acid-volatile sulfide and the toxicity of
zinc, lead, and copper in marine sediments. Environ, Toxicol. Chem. 13:529-536.
Cook, R.B., G.W. Suter II, and E.R. Sain. 1999. Ecological risk assessment in a large river-reservoir: I.
Introduction and background. Environ. Toxicol. Chem. 18(4):581-588.
Coyle, J.J., D.R. Buckler, C.G. Ingersoll, J.F. Fairchild, and T.W. May. 1993. Effect of dietary selenium
on the reproductive success of bluegills (Lepomis macrochirus). Environ. Toxicol. Chem.
12:551-565.
DeVault, D. 2000. Personal communication. U.S. Fish and Wildlife Service.
Di Toro, D M., S.M. Mahond, D.J. Hansen, K.J. Scott, A.R. Carlson, and G.T. Ankley. 1990. Toxicity
of cadmium in sediments: the role of acid-volatile sulfide. Environ. Toxicol. Chem. 9:1487-
1502.
Di Toro, D.M., S.M. Mahond, D.J. Hansen, K.J. Scott, A.R. Carlson, and G.T. Ankley. 1992. Acid-
volatile sulfide predicts the toxicity of cadmium and nickel in sediments. Environ. Toxicol.
Chem. 26:96-101.
Di Toro, D.M. and J.A. McGrath. 2000. Technical basis for narcotic chemicals and polycylic aromatic
hydrocarbon criteria II. Mixtures and sediments. Environ. Toxicol. Chem. 19:1971-1982.
Dunning, J.B., Jr. 1993. CRC handbook of avian body masses. CRC Press, Inc., Boca Raton, Florida.
371 pp.
Eisler, R. 1986. Polychlormated biphenyl hazards to fish, wildlife, and invertebrates: A synoptic review.
U.S. Fish and Wildlife Service, Laurel, Maryland. Biological Report No. 85:1.7.
Environment Canada. 199S. Interim sediment quality guidelines: Soil and sediment quality section
guidelines division. Ecosystem Conservation Directorate Evaluation and Interpretation Branch,
Ottawa, Ontario.
Ferraro, S.P., H. Lee II, R.J. Ozretich, and D.T. Specht. 1990. Predicting bioaccumulation potential: A
test of a fugacity-based model. Arch. Environ. Contain. Toxicol. 19:386-394.
Fischer, D.L. and G.A. Hancock. 1997. Interspecies extrapolation of acute toxicity in birds; Body
scaling vs. phylogeny. Poster presented at 1997 SET AC meeting, San Francisco, California.
Paramttrix
Final Ecological SLRA of the Low$r Ottawa Riv»r
7-1
555-3763-001 (01/03)
October J001
£ JUNJ-OW SLXA X*«rWMW&A(_vl*c
-------
Gliet, A. 1985. Estimation for small normal data sets with detection limits. Environmental Science and
Technology 19:1201-1206.
Grieb, T.M., C.T. Driscoll, S.P. Gloss, C.L. Schofield, G.L. Bowie, and D.B. Porcella. 1990. Factors
affecting mercury accumulation in the upper Michigan Peninsula. Environ. Toxicol. Chem.
9:919-930.
Hamilton, S.J., K.J. Buhl, N.L. Faerber, R.H. Wiedmeyer, and F.A. Bullard. 1990. Toxicity of organic
selenium in the diet of chinook salmon. Environ. Toxicol. Chem. 9.347-358.
Hare, L., R. Carignan, and M.A, Huerta-Diaz. 1994. A field study of metal toxicity and accumulation by
benthic invertebrates; Implications for the acid-volatile sulfide (AVS) model. Limnol. Oceanogr.
39(7): 1653-1668.
Harrahy, E.A. and W.H. Clements. 1997. Toxicity and bioaccumulation of a mixture of metals in
Chironomus tentans (Diptera: Chironomidae) in synthetic sediment. Environ. Toxicol. Chem.
16(2):317-327.
Hopkins, W.A. 2000. Reptile ecotoxicology: Challenges and opportunities on the last frontier in
vertebrate ecotoxicology. Environ. Toxicol. Chem. 19(10):2391 -2393.
Ingersoll, C.G, P.S. Haverland, E.L. Brunson, TJ. Canfield, F.J. Dwyer, C.E. Henke, N.E.Kemble, D.R.
Mount, and R.G. Fox. 1996. Calculation and evaluation of sediment effect concentrations for the
amphipod Hyalella azteca and the midge Chironomus riparius. J. Great Lakes Res. 22(3):602-
623.
Ingersoll, C.G., D.D. MacDonald, N. Wang, J.L. Crane, L.J. Field, P.S. Haverland, N.E. Kemble, R.A.
Lindskoog, C. Severn, and D.E. Smorong. 2001. Predictions of sediment toxicity using
consensus-based freshwater sediment quality guidelines. Arch. Environ. Contam. Toxicol. 41:8-
21.
Jarvinen and Ankley. 1999. Linkage of effects to tissue residues: Development of a comprehensive
database for aquatic organisms exposed to inorganic and organic chemicals. SETAC Technical
Publications Series. SETAC Press, Society of Environmental Toxicology and Chemistry,
Pensacola, Florida.
Korgen, B. 2000. Bonanza for Lake Superior: Seiches do more than move water. Minnesota Sea Grant,
February 2000.
Long, E.R., L.J. Field, and D.D. MacDonald. 1998. Predicting toxicity in marine sediments with
numerical sediment quality guidelines. Environ. Toxicol. Chem. 17(4);714-727.
LTI (Limno-Tech, Inc.), Intertox, and Parametrix, Inc. 2000. Proposal for the Ottawa River
environmental hot spot delineation and risk assessment. 31 pp.
LTI (Limno-Tech, Inc.). 2001. Database for Ottawa River, Ohio. Database report version 1.2. Prepared
by Limno-Tech, Inc., Ann Arbor, Michigan. 44 pp.
Parametrix 553-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 7-2 October 2001
K \vorkwJt3763\3m-O0l\SUtA AporlWaof SJJU_W.doc
-------
O'Connor, T.P., K..D. Daskalakis, J.L. Hyland, J.F. Paul, and J.K. Summers. 1998. Comparisons of
sediment toxicity with predictions based on chemical guidelines. Environ. Toxicol. Chem.
17(3):468-471.
Ohio EPA. 1987. Biological criteria for the protection of aquatic life: Volume II. User's manual for
biological field assessment of Ohio's surface waters. Division of Water Quality Monitoring and
Assessment, Surface Water Section, Columbus, Ohio.
Ohio EPA. 1998. Biological, fish tissue, and sediment study of the Ottawa River Dura Avenue Landfill
1996. Lucas County, Ohio. OEPA Technical Report MAS/1997-12-8. January 30, 1998.
Ohio EPA. 1998. A report on whole sediment toxicity of sediments from sites on the Ottawa River to
Hyalella azteca and Lumbriculus variegatus for the Great Lakes National Program Office.
Bioassay Section, Division of Environmental Services, Ohio EPA. 18 pp. + appendices.
Ohio EPA. 1999. Ohio water quality standards. OAC 3745-1-07.
Ohio EPA. 2000. Ottawa River geographic initiative (GI) work plan. June 2000.
Olafsson, P.G., A.M. Bryan, B. Bush, and W. Stone. 1983. Snapping turtles—A biological screen for
PCBs. Chemosphere 12(11/12):1523-1532.
Ontario Ministry of the Environment and Energy (OMEE). 1993. Guidelines for the protection and
management of aquatic sediment quality in Ontario. Prepared by D. Persaud, R. Jaagumagi, and
A. Hayton, Water Resources Branch, Ontario Ministry of the Environment and Eneigy. 24 pp. +
figures.
Pagano, J.L, P.A. Rosenbaum, R.N. Roberts, G.M. Sumnee, and L.V. Williamson. 1999. Assessment of
maternal contaminant burden by analysis of snapping turtle eggs. J. Great Lakes Res. 25(4):950-
961.
Parkhurst, B.R., W. Warren-Hicks, R.D. Cardwell, J. Volosin, T. Etchison, J.B. Butcher, and S.M.
Covington. 1996. Methodology for aquatic ecological risk assessment: A multi-tiered approach.
Project 91 -AER-1. Prepared for Water Environment Research Foundation, Alexandria, Virginia.
Porter, P.S., R.C. Ward, and H.F. Bell. 1988. The detection limit. Environmental Science and
Technology 22(8):856-861.
Prothro, M.G. 1993. Office of Water policy and technical guidance on interpretation and implementation
of aquatic life metals criteria. Memorandum from M.G. Prothro (Acting Assistant Administrator
for Water) to Water Management Division Directors, Environmental Services Division Directors,
and Regions I-X. October 1,1993.
Rabuck, L., M. Sandheinrich, and R. Rada. 1997. Bioaccumulation of methylmercury in fathead
minnows fed a naturally contaminated diet. Presented at the SETAC 18th Annual Meeting, 16-20
November 1997, San Francisco, California.
Rand, G.M. 199S. Fundamentals of aquatic toxicology: Effects, environmental fate and risk assessment.
Second Edition. Taylor and Francis, Washington D.C, 1125 pp.
ParwMtrix
Find Ecological SLRA of th* lowtr Ottawa Rlwr
7-3
33S-3763-001 (01/03)
Octobtr 2001
-------
Rodgers, D.W. and F.W.H. Beamish. 1982. Dynamics of dietary methylmercury in rainbow trout, Salmo
gairdneri. Aquat. Toxicol. 2:271-290.
Sample, B.E., D.M. Opresko, and G.W. Suter II. 1996. Toxicological benchmarks for wildlife: 1996
Revision. U.S. Department of Energy, ES/ER/TM-86/R3.
Shieldcastle, M. 2000. Personal communication of September 22, 2000. Wildlife officer, Crane Creek
Wildlife Research Station.
Skorupa, J.W., S.P. Morman, and J.S. Sefchick-Edwards. 1996. Guidelines for interpreting selenium
exposures of biota associated with non-marine aquatic habitats. Technical Report. U.S. Fish and
Wildlife Service, Ecological Services Field Office, Sacramento, California.
Sprague, J.B. and B.A. Ramsay. 1965. Lethal levels of mixed copper-zinc solutions for juvenile salmon.
J. Fish. Res. Board Can. 22:425-432.
Stalmaster, M.V. 1987. The bald eagle. Universe Books, New York, New York.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman, and W.A. Brungs. 1985.
Guidelines for deriving numerical national water quality criteria for the protection of aquatic
organisms and their uses. U.S. EPA, Washington, D.C. NTIS No. PB85-227049. 98 pp.
Suedel, B.C., J.A. Boraczek, R.K. Peddicord, P.A. ClifFort, and T.M. Dillon. 1994. Trophic transfer and
biomagnification potential of contaminants in aquatic ecosystems. Rev. Environ. Contam.
Toxicol. 136:21-89.
Suter, G.W., L.W. Bamthouse, R.A. Efroymson, and H. Jager. 1999. Ecological risk assessment in a
large river-reservoir: 2. Fish Community. . Environ. Toxicol. Chem. 18(4):589-598.
Suter, II, G.W. 1993. Ecological risk assessment. Lewis Publishers, Boca Raton, Florida. 538 pp.
Szebedinszky, C., J.C. McGeer, D.G. McDonald, and C.M. Wood. 2001. Effects of chronic Cd exposure
via the diet or water on internal organ-specific distribution and subsequent gill Cd updtake
kinetics in juvenile rainbow trout (Oncorhynchus my/ciss). Environ. Toxicol. Chem. 20(3): 597-
607.
Tracey, G.A., and D.J. Hansen. 1996. Use of biota-sediment accumulation factors to assess similarity of
nonionic organic chemical exposure to benthically-coupled organisms of differing trophic mode.
Arch. Environ. Contam. Toxicol. 30:467-475.
Travis, C.C., R.K. White, and R.C. Ward. 1990. Interspecies extrapolation of pharmacokinetics. J.
Theoret. Biol. 142:285-304.
Travis, C.C. and R.K. White. 1988. Interspecific scaling of toxicity data. Risk Anal. 8:119-125.
U.S. EPA. 1991a. Technical support document for water quality-based toxics control. Office of Water,
Technical Document, EN-336. EPA/505/2-90-001.
U.S. EPA. 1991b. U.S. EPA Region III guidance on handling chemical concentration data near the
detection limit in risk assessments. Roy L. Smith, Interim Final, November 4,1991.
Parametrix 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River 7-4 October 2001
& lwohhlf!*U7«MW-OOlSUM Rro*\fmoISUtA_*l doc
-------
U.S. EPA. 1992. Draft report: A cross-species scaling factor for carcinogen risk assessment based on
equivalent of mg/kg3M/day; Notice. Federal Register. 57: 24152-24173.
U.S. EPA. 1993a. Wildlife exposure factors handbook. Volume 1 of 2. Office of Research and
Development, U.S. Environmental Protection Agency, Washington, D.C. EPA/6Q0/R-93/187a.
U.S. EPA. 1993b. Sediment quality criteria for the protection of benthic organisms: Fluoranthene.
United States Environmental Protection Agency, Health and Ecological Criteria Division,
Washington, D.C. EPA-822-R-93-012.
U.S. EPA. 1993c. Sediment quality criteria for the protection of benthic organisms: Acenaphthene.
United States Environmental Protection Agency, Health and Ecological Criteria Division,
Washington, D.C. EPA-822-R-93-013.
U.S. EPA. 1993d. Sediment quality criteria for the protection of benthic organisms: Phenanthene.
United States Environmental Protection Agency, Health and Ecological Criteria Division,
Washington, D.C. EPA-822-R-93-014.
U.S. EPA. 1993e. Sediment quality criteria for the protection of benthic organisms: Dieldrin. United
States Environmental Protection Agency, Health and Ecological Criteria Division, Washington,
D.C. EPA-822-R-93-015.
U.S. EPA. 1993f. Sediment quality criteria for the protection of benthic organisms'. Endrin. United
States Environmental Protection Agency, Health and Ecological Criteria Division, Washington,
D.C. EPA-822-R-93-016.
U.S. EPA. 1994. Equilibrium partitioning approach to predicting metal bioavailability in sediments and
the derivation of sediment quality criteria for metals. U.S. EPA, Office of Water and Office of
Research and Development EPA/822-D-94-002.
U.S. EPA. 1997. Ecological risk assessment guidance for Superfund: Process for designing and
conducting ecological risk assessments. U.S. Environmental Protection Agency, Washington,
D.C. EPA 540-R-97-006.
U.S. EPA. 1998a. Guidelines for ecological risk assessment. Risk Assessment Forum, U.S.
Environmental Protection Agency, Washington, D.C. EPA/630/R-95/002F.
U.S. EPA. 1998b. 1998 Update of ambient water quality criteria for ammonia. Office of Water, U.S.
EPA, Washington, D.C. EPA 822-R-98-008.
U.S. EPA. 2000a. Equilibrium sediment partitioning sediment guidelines (ESGs) for the protection of
benthic organisms: PAH mixtures. Draft report, Washington, D.C.
U.S. EPA. 2000b. Draft implementation framework for the use of equilibrium partitioning sediment
guidelines: Guidance for using equilibrium partitioning sediment guidelines (ESGs) in water
quality programs. U.S. EPA, Office of Science and Technology. December 2000.
Van der Geest, H.G., G.D. Greve, M.-E. Boivin, M.H.S. Kraak, and C.A.M. van Gestel. 2000. Mixture
toxicity of copper and diazinon to larvae of the mayfly (Ephoron virgo) judging additivity at
different effect levels. Environ. Toxicol. Chem. 19(12):2900-2905.
Parametria
Final Ecological SLRA of the Lower Ottawa River
7-3
S5S-3763-001 (01/03)
October 2001
K: Wlim-M/VUM A*enWHitSUU_*l<*tc
-------
Vighi, M. 1981. Lead uptake and release in an experimental trophic chain. Ecotoxicol. Environ. Safety.
5:177-193.
Welsh, P.G., J. Lipton, and G.A. Chapman. 2000. Evaluation of water-effect ratio methodology for
establishing site-specific water quality criteria. Environ. Toxicol. Chem. 19(6): 1616-1623.
Williams, P. 2000. Personal communication of June 6, 2000. Ohio Environmental Protection Agency.
Wobeser, G. 1975. Prolonged oral administration of methyl mercury chloride to rainbow trout (Salmo
gairdneri) fmgerlings. J. Fish. Res. Board Can. 32:2015-2023.
Woock, S. E., W.R. Garrett, W.E. Partin, and W.T. Bryson. 1987. Decreased survival and teratogenesis
during laboratory selenium exposures to bluegill, Lepomis macrochirus. Bull. Environ. Contam.
Toxicol. 39.998-1005.
Paramatrix
Final Ecological S1MA of the Lower Ottawa River
7-6
SSS-3763-001 (01/03)
October 2001
K: \-M>i**t!i37t3\376)-OOl
-------
APPENDIX A
Exposure Data
-------
APPENDIX A - EXPOSURE DATA
As discussed in Section 3.1 of the main report, wildlife and aquatic life exposures to chemicals were
evaluated using measured chemical concentrations, where available. For some chemicals and
environmental media, however, it was necessary to estimate chemical concentrations. Measured and
estimated chemistry data are summarized in Sections A.l and A.2 below.
A.l MEASURED CHEMICAL CONCENTRATIONS
The summary statistics for chemicals with a detection frequency greater than 5 percent are provided in
Tables A-l, A-2, and A-3 for fish tissue, sediment, and surface water, respectively. The 95 percent UCL
on the mean was used to estimate chronic exposure (Equation A-l) and the 95th percentile of the data was
used to estimate acute exposures (Equation A-2).
95% UCL (Population) = Mean + 1005 xSD (A-l)
95% UCL (Mean) = Mean+ t0 05 n.,x-T= (A-2)
Vn
Where: 95% UCL (Mean)
*0.05, n-1
SD
n
Upper 95% confidence limit of the mean concentration
Critical value of the Student's t distribution at n-1
degrees of freedom, one-tailed
Standard deviation
Sample size
A.2 ESTIMATION OF TISSUE CONCENTRATIONS
As summarized in Tables A-l, A-2, and A-3, concentration data were available for a variety of chemical
classes and environmental media. However, to thoroughly evaluate exposure of all receptors to the
chemicals likely to be present in the Ottawa River, it was necessary to estimate the concentrations of
some chemicals in tissue.
No chemistry data are currently available for macroinvertebrates in the lower Ottawa River; however,
these data are necessary for estimating potential risks to the spotted sandpiper. Because benthos are
primarily exposed to chemicals associated with sediment (e.g., pore water, detritus), chemical
concentrations in invertebrate tissue were estimated using biota-sediment accumulation factors (BSAFs).
This is applicable to lipophilic organic chemicals. The BSAFs are expressed as the ratio of a chemical's
concentration in biological tissue normalized for the fraction lipid to the chemical's concentration in
sediment normalized for organic carbon13. Equation A-3 shows how benthic tissue concentrations were
estimated from sediment concentrations using BSAFs:
13 Given the multitude of site-specific factors that influence the bioaccumulation of metals from sediment, methods
do not exist for adequately estimating metal concentrations in tissue from sediment concentrations.
Paranwtrix 3J5-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River A-l October 2001
K W*W«3Wrt340I\Sl1U RipaeAfinatSlRA^vldoc
-------
BSAFxCstdxFt
(A-3)
tissue
Where:
C,
BSAF
tissue
= Chemical concentration in tissue (mg/kg wet weight)
= Biota-sediment accumulation factor (kg organic carbon/kg lipid)
= Chemical concentration in sediment (mg/kg wet weight)
- Fraction lipid in tissue
= Fraction organic carbon in sediment
The BSAFs used in this ecological SLRA were estimated using modeled data from Di Toro and McGrath
(2000) or measured data from other sources (e.g., Tracey and Hansen 1996, Ferraro et al. 1990). The
empirically derived BSAFs met the guidelines outlined by Tracey and Hansen (1996)14. The BSAFs and
the estimated macroinvertebrate tissue concentrations using this approach are provided in Table A-4.
14 These guidelines include: (1) BSAF studies must report the sediment total organic carbon, organism lipid, lipid
method, and paired tissue and sediment chemical concentrations; (2) exposures must occur from "naturally-
contaminated" (i.e., not laboratoiy-spiked) sediment*; (3) laboratory studies must be a minimum of 28 days; and (4)
aggregated chemical data are to be excluded.
Paramatrfx 3SS-)76S>Q0i (0J/03)
Final Ecological SLRA ofth* Lowr Ottawa Rtvtr
, Ocfofrw 200i
-------
REFERENCES - APPENDIX A
AQUIRE. 2001. AQUatic toxicity Information REtrieval database. Environmental Research Laboratory.
United States Environmental Protection Agency, Duluth, Minnesota. Available at:
http://www.epa.gov/ecotox/ecotox_search_driver.htm
Call, D.J., L.T. Brooke, N. Ahmad and J.E. Richter. 1983. Toxicity and metabolism studies with EPA
priority pollutants and related chemicals in freshwater organisms. PB83-263665. National
Technical Information Service, Springfield, Virginia.
Carr, K.H., G.T. Coyle, and R.A. Kimerle. 1997. Bioconcentration of [14C]butyl benzyl phthalate in
bluegill sunfish (Lepomis macrochirus). Environ. Toxicol. Chem, 16(10):2200-22Q3.
Di Toro, D.M. and J.A. McGrath. 2000. Technical basis for narcotic chemicals and polycylic aromatic
hydrocarbon criteria. II. Mixtures and sediments. Environ. Toxicol. Chem. 19:1971-1982.
Ferraro, S.P., H. Lee II, R.J. Ozretich, and D.T. Specht. 1990. Predicting bioaccumulation potential: A
test of a fugacity-based model. Arch. Environ. Contam. Toxicol. 19:386-394.
Lang, P.-Z., Y. Wang, D.-B. Chen, N. Wang, X.-M. Zhao, and Y.-Z. Ding. 1997. Bioconcentration,
elimination and metabolism of 2,4-dinitrotoluene in carps (Cyprinus carpioL.). Chemosphere
35(8):1799-1815.
McCarty, L.S. 1986. The relationship between aquatic toxicity QSARs and bioconcentration for some
organic chemicals. Environ. Toxicol. Chem. 5:1071-1080.
Tracey, G.A., and D.J. Hansen. 1996. Use of biota-sediment accumulation factors to assess similarity of
nonionic organic chemical exposure to benthically-coupled organisms of differing trophic mode.
Arch. Environ. Contam. Toxicol. 30:467-475.
U.S. EPA. 1993. Ambient aquatic life water quality criteria for 2,4-dimethylphenol (draft). Office of
Water and Office of Research and Development, U.S. EPA, Washington, D.C., Duluth,
Minnesota, and Narragansett, Rhode Island. 822/R93025.
ParwiMtriX S5S-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa Rtver A-3 October 2001
JC '<»o**tf3}63\t1t3-40rSlAAIUportr**lSlto._*ljloc
-------
Table A-la. Summary statistics for measured chemical concentrations in fish (Data from Inventory 20 (20OO|).
River Segment 1
Chemical
Units
FOD (%)
Mean
SD
Mm
Max
N
95% UCL
95Ui
Percentile
Metals
Arsenic
mg/kg
U
0.019
0.000
0.019
0.020
4
0.020
0.020
Cadmium
mg/kg
100
0.008
0.002
0.006
0.011
4
0.010
0.013
Lead
mg/kg
94
0.181
0.069
0.125
0.280
4
0.262
0.343
Mercury
mg/kg
44
0.011
0.001
0.010
o.ou
4
0.011
0.012
Selenium
mg/kg
94
0.377
0.556
0.092
1.210
4
1.030
1.684
PCBi
PCB-1242
mg/kg
83
0.774
0.077
0.686
0.873
4
0.865
0.956
PCB-1260
mg/kg
94
0.099
0.028
0.074
0.138
4
0.132
0.164
Pesticide*
4,4'-DDD
mg/kg
100
0.019
0.004
0.013
0.022
4
0.024
0.030
4,4-DDE
mg/kg
100
0.057
0.012
0.043
0.067
4
0,070
0.084
4,4'-DDT
mg/kg
$0
0.002
0.001
0.002
0.004
4
0.004
0.005
Aldrin
mg/kg
17
0.002
0.000
0.002
0.002
4
0.002
0.002
alpha-Chlordane
mg/kg
67
0.002
0.001
0.002
0.004
4
0.004
0.005
eis-Nonachlor
mg/kg
39
0.003
0.001
0.002
0.005
4
0.004
0.006
Dieldrin
mg/kg
94
0.011
0.003
0.007
0.013
4
O.OU
0.018
gamma-Chlotdaae
mg/kg
83
0.015
0.003
0.013
0.019
4
0.018
0.022
Heptaohtor
mg/kg
17
0.002
0.000
0.002
0.002
4
0.002
0.002
Heptaohtor epoxide
mg/kg
33
0.002
0.000
0.002
0.002
4
0.002
0.002
Oxyohlordane
mg/kg
56
0.006
0.004
0.002
0.011
4
O.OU
0.016
trani-Nonachlor
mg/kg
61
0.004
0.003
0.002
0.009
4
0.008
0.012
FOD - Frequency of detection
SD - Standard deviation
N - Number of samples counted
Final Ecological SLKA afth» Lowtr Ottawa Rim
PagtlefS
OetobvJOOl
JJJ-J763-0O/
-------
Table A-la. Summary statistics for measured chemical concentrations in fish (Data from Inventory 20 [2000]).
River Segment 2
95th
Chemical Units Mean SD Min Max N 95% UCL Percentile
Metals
Arsenic
mg/kg
0.020
0.000
0.019
0.020
3
0.020
0.020
Cadmium
mg/kg
0.008
0.003
0.007
0.012
3
0.013
0.016
Lead
mg/kg
0.295
0.076
0.218
0.369
3
0.422
0.516
Mercury
mg/kg
0.017
0.013
0.008
0.033
3
0.040
0.057
Selenium
mg/kg
0.094
0.005
0.089
0.097
3
0.102
0.108
PCBs
PCB-1242
mg/kg
1.773
0.616
1.350
2.480
3
2.812
3.572
PCB-1260
mg/kg
0.229
0.114
0.128
0.352
3
0.421
0.561
Pesticides
4,4'-DDD
mg/kg
0.030
0.009
0.022
0.039
3
0.045
0.056
4,4'-DDE
mg/kg
0.108
0.033
0.070
0.130
3
0.164
0.205
4,4'-DDT
mg/kg
0.004
0.003
0.002
0.008
3
0.009
0.013
Aldrin
mg/kg
0.002
0.000
0.002
0.002
3
0.002
0.002
alpha-Chlordane
mg/kg
0.003
0.002
0.002
0.006
3
0.007
0.010
cis-Nonachlor
mg/kg
0.003
0.001
0.002
0.004
3
0.005
0.006
Dieldrin
mg/kg
0.010
0.003
0.007
0.012
3
0.014
0.017
gamma-Chlordane
mg/kg
0.022
0.008
0.014
0.030
3
0.036
0.047
HeptacHlor
mg/kg
0.010
0.013
0.002
0.025
3
0.032
0.048
Heptachlor epoxide
mg/kg
0.003
0.001
0.002
0.004
3
0.005
0.007
Oxychlordane
mg/kg
0.010
0.008
0.002
0.017
3
0,023
0.033
trans-Nonachlor
mg/kg
0.007
0.005
0.002
0.012
3
0.015
0.021
FOD - Frequency of detection
SO • Standard deviation
N - Number of samples counted
Final Ecological SURA of the Lower Ottawa River
Page 2 ofS
October 2001
555-3763-001
-------
Table A-la. Summary statistics for measured chemical concentrations in fish (Data from Inventory 20 (2000|).
River Segment 3
Chemical
Unit*
Mean
SD
Min
Max
N
95% UCL
95th
Percentile
Metali
Arsenic
mg/kg
0.028
0.019
0.019
0.062
5
0.046
0.069
Cadmium
mg/kg
0.015
•0.009
0.008
0.028
5
0.024
0.035
Lead
mg/kg
0.438
0.411
0.218
1.170
5
0.830
1.314
Mercury
mg/kg
0.018
0.010
0.010
0.030
5
0.028
0.039
Selenium
mg/kg
0.413
0.691
0.086
1.650
5
1.073
1.887
PCBs
PCB-1242
mg/kg
1.934
0.528
1.070
2.440
5
2.437
3.059
PCB-1260
mg/kg
0.147
0.033
0.106
0.184
5
0.179
0.218
Pnticides
4,4'-DDD
mg/kg
0.044
0.013
0.030
0.061
5
0.057
0.072
4,4'-DDE
mg/kg
0.104
0.019
0.082
0.125
5
0.123
0.145
4,4'-DDT
mg/kg
0.008
0.004
0.002
0.013
5
0.012
0.017
Aldrin
mg/kg
0.004
0.002
0.002
0.005
5
0.005
0.008
alpha-Chlordane
mg/kg
0.010
0.006
0.005
0.019
5
0.015
0.022
cii-Nonachlor
mg/kg
0.004
0.004
0.002
0.010
5
0.008
0.012
Dieldrin
mg/kg
0.015
0.003
0.012
0.020
5
0.019
0.023
gamma-Chlordane
mg/kg
0.024
0.015
0.013
0.049
5
0.038
0.055
HepUohlor
mg/kg
0.012
0.014
0.002
0.032
5
0.026
0.042
HepUchlor epoxide
mg/kg
0.003
0.002
0.002
0.007
5
0.005
0.008
Oxyohlordane
mg/kg
0.010
0.009
0.002
0.023
5
0.019
0.030
traiu-Notuchlor
mg/kg
0.012
0.006
0.002
0.018
5
0.018
0.025
FOD • Frequency of detection
SD • Standard deviation
N - Number of iample> counted
Final Ecological SLRA of th* Lowtr Ottawa Rtrmr
Pap 3 ofS
Oetob*r2QOl
SS3-S763-QQI
-------
Table A-la. Summary statistics for measured chemical concentrations in fish (Data from Inventory 20 |2000|).
River Segment 4
95th
Chemical Units Mean SD Min Max N 95% UCL Percentile
Metals
Arsenic
mg/kg
0.020
0.000
0.019
0.020
3
0.020
0.020
Cadmium
mg/kg
0.017
0.004
0.013
0.021
3
0.024
0.029
Lead
mg/kg
0.440
0.187
0.257
0.631
3
0.756
0.987
Mercury
mg/kg
0.023
0.012
0.012
0.036
3
0.043
0.059
Selenium
mg/kg
0.296
0.243
0.122
0.574
3
0.706
1.006
PCBs
PCB-1242
mg/kg
0.778
0.740
0.293
1.630
3
2.026
2.939
PCB-1260
mg/kg
0.100
0.007
0.092
0.105
3
0.113
0.122
Pesticides
4,4'-DDD
mg/kg
0.039
0.014
0.026
0.054
3
0.064
0.081
4,4'-DDE
mg/kg
0.066
0.019
0.047
0.083
3
0.097
0.120
4,4'-DDT
mg/kg
0.009
0.006
0.002
0.014
3
0.020
0.027
Aldrin
mg/kg
0.002
0.000
0.002
0.002
3
0.002
0.002
alpha-Chlordane
mg/kg
0.010
0.006
0.006
0.017
3
0.020
0.028
cis-Nonachlor
mg/kg
0.004
0.002
0.002
0.006
3
0.007
0.010
Dieldrin
mg/kg
0.016
0.004
0.012
0.020
3
0.022
0.026
gamma-Chlordane
mg/kg
0.014
0.018
0.002
0.035
3
0.044
0.066
Heptachlor
mg/kg
0.002
0.000
0.002
0.002
3
0.002
0.002
Heptaehlor epoxide
mg/kg
0.004
0.001
0.002
0.005
3
0.006
0.008
Oxychlordane
mg/kg
0.008
0.006
0.002
0.013
3
0.018
0.024
trani-Nonachlor
mg/kg
0.010
0.007
0.002
0.015
3
0.022
0.030
FOD - Frequency of detection
SD • Standard deviation
N • Number of samples counted
Final Ecological SLRA of the Lower Ottawa River
Page 4 of 5
October 2001
55S-3763-001
-------
Table A-la. Summary statistics for measured chemical concentrations in fish (Data from Inventory 20 |2000|).
River Segment 5
95th
Chemical Unita Mean SD Nlin Max N 95% UCL Percentile
Metals
Anenic
rag/kg
0.043
0.041
0.020
0.090
3
0.112
0.162
Cadmium
mg/kg
0.025
0.020
0.010
0.047
3
0.058
0.083
Lead
mg/kg
0.445
0.698
0.020
1.250
3
1.621
2.482
Mercury
mg/kg
0.049
0.028
0.022
0.077
3
0.095
0.129
Selenium
mg/kg
0.424
0.267
0.180
0.709
3
0.874
1.203
PCBi
PCB-1242
mg/kg
0.015
0.009
0.010
0.025
3
0.029
0.040
PCB-1260
mg/kg
0.033
0.008
0.025
0.038
3
0.046
0.055
Pesticide*
4,4'-DDD
mg/kg
0.039
0.020
0.018
0.059
3
0.073
0.098
4,4'-DDE
mg/kg
0.163
0.089
0.060
0.222
3
0.313
0.424
4,4'-DDT
mg/kg
0.013
0.017
0.002
0.034
3
0.043
0.064
Aldrin
mg/kg
0.003
0.002
0.002
O.OOS
3
0.006
0.008
alpha-Chlordane
mg/kg
0.011
0.009
0.005
0.021
3
0.026
0.037
cii-Nonaohlor
mg/kg
0.005
0.003
0.002
0.009
3
0.011
0.015
Dicldrin
mg/kg
0.026
0.022
0.005
0.048
3
0.062
0.089
gamma-Chlordane
mg/kg
0.006
0.004
0.002
0.010
3
0.012
0.017
Heptaohlor
mg/kg
0.003
0.002
0.002
0.005
3
0.006
0.008
Heptachlor epoxide
mg/kg
0.005
0.000
o.oos
0.006
3
0.006
0.006
Oxychlordane
mg/kg
0.005
0.003
0.002
0.008
3
0.010
0.014
tnuu-Nonaohlor
mg/kg
0.015
0.009
0.003
0.023
3
0.031
0.042
FOD • Frequency of detection
SD • Standard deviation
N - Number of lamploa sounted
Final Ecological SLRA of th* Lawtr Ottawa Rtnr
PagiJcfJ
October 2001
333-376S-001
-------
Table A-lb. Summary statistics for measured chemical concentrations in fish, whole organism, from Maumee Bay (Data from Inventory 13 |1999j).
Ckciuoil
FQD (%)
Mean
SD
Min
Max
N
95%UCL
95th Percci
FCb
PCB Arodar 1242
100
0.508
0.496
0.050
1.630
13
0.753
1.393
PCB Areolar 12S4
100
0.600
0346
0.239
1.510
13
0.772
1.217
PCS Arodar 1260
100
0.478
0.515
0.133
2.080
13
0.732
1.396
Total PCB*
100
1.587
0.993
0.578
3.920
13
2.078
3.357
rnl.H..
2.4--DDD (oj.1-)
100
0.002
0.001
0.001
0.005
13
0.003
0.005
2Jt4.X3e(o^-)
83
0.001
0.000
0.000
0.002
13
0.001
0.002
VJwrw-)
100
0.001
0.001
0.000
0.005
13
0.002
0.004
100
0.033
0.019
0.008
0.078
13
0.042
0.067
4,4,-DDE(W>'-)
100
0.101
0.063
0.024
0.248
13
0.132
0.213
4,4,-DDT(py-)
100
0.006
0.012
0.001
0.046
13
0.012
0.028
alplM-BcBZeaebenahlaade (a-BHC)
*
0.001
0.001
0.000
0.003
13
0.001
0.002
a^plH^OUonlMB
100
0.009
0.010
0.001
0.038
13
0.014
0.027
Diekfem
100
0.011
0.009
0.004
0.038
13
0.015
0.027
FiJfii
46
0.000
0.000
0.000
0.001
13
0.000
0.000
fwi»BaBaw hauoUoridc (g-BHC; Lndne)
92
0.002
0.001
0.001
0.005
13-
0.003
0.004
faMUhCUantoe
100
0.005
0.006
0.000
0.022
13
0.008
0.016
ftytMlitf ^nndb
100
0.002
0.002
0.000
0.008
13
0.003
0.005
100
0.001
0.001
0.000
0.003
13
0.001
0.002
14|mk
62
0.000
0.001
0.000
0.003
13
0.001
0.002
C^yhlwit—i
100
0.014
0.015
0.002
0.055
13
0.021
0.041
t in ir i a i
s
0.050
0.139
0.006
0.509
13
0.119
0.298
h— Nnaaahtor
100
0.010
0.008
0.003
0.033
13
0.014
0.025
FOP-F»nfiany of fctoliia
SD-Stednddeviatkui
H - HiiIm af umplra conatrH
Lamer Ottawa River SUM
Page 1 of 1
October 2001
555-3763-001
-------
Tabic A-2a. Summary statistics for measured chemical concentrations in sediment (Data from Inventory 15 11998J).
River Segment 1
Chemical UaiH FOD(%) Mean SD Mm Max N 95% UCL 95th Percentile
Ancnic
Lead
Silver
falycjrtMi AraaaaMe l^*i »i—fci—
BaBofbjftHnAcK
CKiysum
Pjwmi
rCBe
PCB Aroolar 1016
PCB Aroolor 1242
PCB Aroolar 1254
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
¦***
mgftg
¦1*1
mg/kg
mgOcg
96
86
46
100
100
47
47
12
7
7
18
13
7
34
6
6.748
85.798
1.944
55.438
6Z253
0.244
1.045
0.438
0.(32
0.141
0.353
0.247
0.015
0.442
0.013
3.596
53.303
2.092
56.441
58.424
0.298
0.715
0355
0.433
0.417
0.929
0.704
0.091
0.710
0.021
0.185
0.034
0.215
2.700
1.300
0.006
0.125
0.140
0.015
0.016
0.016
0.018
0.002
0.005
0.005
13.700
223.000
11.700
286.000
226.000
1.600
3.100
3.900
4.100
3.300
7.500
7.000
1.300
4.100
0.230
203
203
203
203
203
203
203
203
203
203
203
203
203
203
203
7.166
91.980
2.187
61.984
69.029
0.279
1.128
0.479
0.182
0.190
0.461
0.329
0.026
0.525
0.016
12.691
173.877
5.402
148.703
158.794
0.737
2.227
1.025
0.847
0.830
1.888
1.411
0.166
1.616
0.047
2»
-------
Table A-2a. Summary statistics for measured chemical concentrations in sediment (Data from Inventory 15 11998)).
River Segment 2
Chemical Unite Mean SD Min Max A[ 95% UCL 95tji Percentile
Metals
Arsenic
rog/kg
7.398
3.749
0.205
14.200
75
8.119
13.643
Barium
mg/kg
114.516
70.226
0.140
290.000
75
128.024
231.493
Cadmium
mg/kg
3.241
3.S62
0.300
16.900
75
3.984
9.675
Chromium
mg/kg
95.463
116.921
6.000
541.000
75
117.951
290.220
Lead
mg/kg
120.728
114.187
3.500
370.000
75
142.691
310.930
Mercury
mg/kg
0.452
0.628
0.012
3.200
75
0.573
1.498
Selenium
mg/kg
1.046
0.780
0.305
3.200
75
1.196
2.346
Silver
mg/kg
1.262
1.550
0.255
6.900
75
1.560
3.844
Poly cyclic Aromatic Hydrocarbons
Bcnzo[b]fluoranthene
mgtg
0.223
0.394
0.022
2.100
75
0.2 99
0.880
Chiysene
mg/kg
0.133
0.248
0.018
1.600
75
0.181
0.547
Fluoranthene
mg/kg
0.524
1.000
0.016
5.400
75
0.717
2.191
Pyrene
mg/kg
0.346
0.771
0.019
5.100
75
0.495
1.631
PCB»
PCB Aroclor 1016
mg/kg
0.447
1.600
0.008
9.900
75
0.755
3.112
PCB Aroclor 1242
mg/kg
0.640
1.650
0.011
12.000
75
0.958
3.388
PCB Aroclor 1254
mg/kg
0.038
0.081
0.005
0.540
75
0.053
0.173
Semivolattte Organic Compounds
2,4,6-Tribromoplienol
mg/kg
3.356
0.870
1.500
6.700
75
3.523
4.806
2-Fluorc.biphenyl
mg/kg
2.280
0.620
1.200
4.300
75
2.399
3.313
2-Fluorophcnol
mg/kg
3.764
0.969
2.100
7.000
. 75
3.950
5.378
bi»(2-EthylheJcylyphthalste
mg/kg
1.987
3.073
0.023
14.000
75
2.578
7.105
FOD - Frequency of detection
SD - Standard deviation
N - Number of (ample* counted
Lower Ottawa River SLRA
Page 2 of 5
Oclcjber 2001
555-3763-001
-------
Table A-2a. Summary statistics for measured chemical concentrations in sediment (Data from Inventory IS [1998]).
River Segment 3
Chemical UniU Mean SD Min Max N 95% UCL 95th Percentile
Mctab
Aitenic
mg/kg
7.359
3.889
1200
16.600
29
8.587
13.974
Barium
mg/kg
121.715
124.974
0.145
618.000
29
161.193
334.312
Cadmium
mg/kg
2.599
4.807
0.285
20.700
29
4.117
10.776
Chromium
mg/kg
131.176
377.780
8.900
2000.000
29
250.514
773.829
Lead
mg/kg
126.210
171.521
5.300
533.000
29
180.392
417.990
Mercury
mg/kg
0.376
0.594
O.OU
2.300
29
0.564
1.386
Selenium
mg/kg
0.743
1.171
0.285
6.200
29
1.112
2.735
Silver
mg/kg
1.898
2.881
0.245
10.800
29
2.808
6.798
fatycycMc AwHi HyJracarfcaqi
Benzo[bjfluoranthcnc
mg/kg
0.222
0.448
0.021
1.750
29
0.363
0.984
Ckywae
mg/kg
0.176
0.356
0,017
1.400
29
0.288
0.781
Fluoranthcne
mg/kg
0.324
0.732
0.015
3.700
29
0.555
1.569
Pyrene
mg/kg
0.309
0.713
0.019
3.400
29
0.534
1.522
PCBa
PCB Aroclor 1016
mg/kg
23.370
101.814
0.007
540.000
29
55.532
196.569
PCB Arodcr 1242
mg/kg
0.971
3.380
0.011
16.500
29
2.038
6.720
PCB Aroolor 1254
mg/kg
0.457
1.539
0.005
7.500
29
0.943
3.074
SnalvilaHh Organic
2,4,6-Tribroattophaiol
mg/kg
2.671
1.130
0.000
4.700
29
3.028
4.593
2-Fhiorobipkenyl
mg/kg
1.558
0.713
0.000
3.500
29
1.783
2.770
2-Fh>oroptiaK>J
mg/kg
2.731
1.236
0.000
5.200
29
3.121
4.833
bg(2-Ethyihotyl)phthil«lr
mg/lcg
22.171
64.113
0.022
220.000
29
42.423
131.235
FOD - Frequency of detection
SD - Standard deviation
N - N\>mber at umpio counted
Lamer Ottawa River SLRA
Page 3 of 5
October 2001
S55-3763-001
-------
Table A-2a. Summary statistics for measured chemical concentrations in sediment (Data from Inventory 15 [1998]).
River Segment 4
Chemical Units Mean SD Min Max A/ 95% UCL 95th Percentile
Metals
Arsenic
mg/kg
7.543
4.532
2.900
21.000
28
9.002
15.262
Barium
mg/kg
97.226
100.856
0.135
449.000
28
129.691
269.014
Cadmium
mg/kg
1.074
1.209
0.300
4.900
28
1.463
3.133
Chromium
mg/kg
59.386
109.413
7.200
578.000
28
94.605
245.748
Lead
mg/kg
174.668
342.080
4.800
1800.000
28
284.780
757.329
Mercury
mg/kg
0.277
0.589
0.012
3.000
28
0.467
1.281
Selenium
mg/kg
0.605
0.401
0.300
1.800
28
0.734
1.289
Silver
mg/kg
0.913
1.332
0.255
5.700
28
1.341
3.181
Poly cyclic Aromatic Hydrocarbons
Bcnzo[b]fiuoranthenc
mg/kg
0.757
1.195
0.022
4.900
28
1.141
2.793
Chrysenc
mg/kg
0.641
0.993
0.018
3.900
28
0.961
2.333
Fluoranthenc
mg/kg
1.312
2.098
0.016
8.800
28
1.988
4.886
Pyrene
mg/kg
0.985
1.414
0.020
5.700
28
1.441
3.394
PCB»
PCB Aroclor 1016
mg/kg
0.410
1.052
0.008
4.700
28
0.749
2.202
PCB Aroolor 1242
mg/kg
0.430
1.878
0.011
10.000
28
1.034
3.629
PCB Aroclor 1254
mg/kg
0.137
0.286
0.005
1.400
28
0.229
0.623
Srmivolaliie Organic Compounds
2,4,6-Tribromophcnol
mg/kg
2.600
1.062
0.000
4.800
28
2.942
4.409
2-Fluorobiphenyl
mg/kg
1.650
0.726
0.000
3.400
28
1.884
2.887
2-Fluorophenol
mg/kg
2.686
1.080
0.000
5.200
28
3.033
4.525
bis(2-Ethylhexyl)phthalatc
mg/kg
0.519
0.733
0.023
2.300
28
0.754
1.767
FOD - Frequency of detection
SD - Standard deviation
N - Number of samples counted
Lower Ottawa River SLRA
Page 4 of 5
October 2001
555-3^63-00!
-------
Table A-2a. Summary statistics for measured chemical concentrations in sediment (Data from Inventory 15 [1998)).
River Segment 5
Chemical Unite Mean SO Min Max jV 95% VCL 95th Percentile
Metab
Ancnic
mg/kg
7.400
3.569
3.200
11.600
5
10.803
15.009
Barium
mg/kg
70.347
44.425
0.135
108.000
5
112.701
165.054
Cadmium
mg/kg
0.783
0.594
0.300
1.800
5
1.349
2.048
Chromium
mg/kg
26.740
19.905
8.500
59.300
5
45.717
69.174
Lead
mg/kg
43.040
57.053
5.200
140.000
5
97.433
164.667
Mercury
mg^cg
0.085
0.102
0.012
0.240
5
0.183
0.303
Selenium
mg/kg
0.621
0.661
0.260
1.800
5
1.251
2.030
Silver
mg/kg
0.628
0.662
0.255
1.800
5
1.259
2.040
Paljrcycfic Arematic Hydrocarbons
Benzo[bjfluonaihene
mg/kg
0.139
0.203
0.022
0.500
5
0.332
0.572
Chry«ene
mg/kg
0.039
0.022
0.018
0.065
5
0.060
0.086
Fluoranthene
mg/kg
0.193
0.340
0.016
0.800
5
0.517
0.917
Pyrcae
mg/kg
0.185
0.305
0.020
0.730
5
0.476
0.836
rcBi
PCB Aroclor 1016
mg/kg
0.405
0.892
0.005
2.000
5
1.255
2.306
PCB Aroclor 1242
mg/kg
0.024
0.029
0.010
0.075
5
0.051
0.085
PCB Aroclor 12S4
mg/kg
0.043
0.066
0.005
0.160
5
0.106
0.184
Scarivalatac Organic Cam pound*
2,4,6-Tribroo ophcaol
mg/kg
4.280
2.229
2.000
6.700
5
6.405
9.031
2-Fhiorobiphenyl
mg/kg
2.420
1.314
1.100
4.300
5
3.673
5.222
2-Fluorophenol
mg/kg
3.500
1.116
1.900
4.600
5
4.564
5.879
bii(2-EthyIhexyl)phthaUte
mg/kg
0.979
1.722
0.021
4.000
5
2.621
4.651
FOD - Freqocaey of detection
St> - Standard deviation
N - Number of umples counted
Lower Ottawa River SLRA
Page 5 of 5
October 2001
555-3763-001
-------
Table A-Zb. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 [2000)).
River Segment 1
Dry Weight (mg/kg) Wet Weight (mg leg)
Chemical
FOD
(%)
Mean
SD
Min
Max
N
95%UCL
95th
Percentile
Mean
SD
Min
Max
N
95%UCL
95th
Percentile
Metal*
Atom atom
100
10252.000
3780.887
4690.000
14700.000
10
12443.710
17182.796
4410.401
1373.281
2640.470
7011.900
10
5206.467
6927.782
Antimony
35
0.558
0.190
0.320
1.000
10
0.668
0.906
0.257
0.132
0.193
0.581
10
0.334
1)499
Annuo
100
7.090
2.994
2.20©
12.300
10
8.826
12.579
3.093
1.254
1.338
5.105
10
3.820
5.392
Barium
100
99.980
33.718
44.000
141.000
10
119.526
161.789
43.027
11.798
26.752
67.257
10
49.866
64.654
Beryllium
100
0.502
0.182
0.210
0.740
10
0.608
0.836
0.216
0.068
0.128
0.353
10
0.255
0.34(1
Cadmium
100
1.541
1.103
0.320
4.400
10
2.180
3.562
0.673
0.523
0.195
2.099
10
0.976
1.631
Chromium
100
41.330
29.587
13.600
120.000
10
58.481
95.566
18.104
14.054
8.269
57.240
10
26.251
43.X66
Cobalt
100
7.980
2.264
3.100
10.300
10
9.292
12.130
3.503
1.008
1.885
5.236
10
4.087
5.351
Copper
100
65.920
45.146
18.200
172.000
10
92.090
148.677
28.228
18.280
11.066
71.380
10
38.825
61.737
Iron
100
19633.000
6398.212
8530.000
27000.000
10
23341.92}
31361.650
8467.124
2239.211
5186.240
12879.000
10
9765.153
12571.852
Lead
100
79.240
34.437
25.000
147.000
10
99.202
142.367
34.209
13.289
15.200
56.763
10
41.912
58.569
Manganese
100
354.700
113.323
151.000
480.000
10
420.391
562.433
152.706
37.899
91.808
228.960
10
174.675
222.179
Mercury
74
0.137
0.109
0.039
0.350
10
0.200
0.337
0.059
0.047
0.023
0.167
10
0.087
0.146
Nickel
100
34.480
13.250
11.900
6X300
10
42.161
58.768
15.193
6.236
7.235
29.717
10
18.80B
26.624
Selenium
96
1.997
0.768
0.870
3.300
10
2.442
3.405
0.864
0.278
0.529
1.271
10
1.025
1.374
Silver
91
0.460
0.334
0.090
1.200
10
0.653
1.072
0.197
0.151
0.055
0.572
10
0.2X4
(1.473
Thallium
100
4.110
1.470
1.600
6.400
10
4.962
6.805
1.811
0.672
0.973
2.847
10
2.201
3.042
Vanadium
100
24.180
7.345
11.600
31.200
10
28.438
37.644
10.472
2.612
6.812
14.882
10
11.986
15.260
Zinc
100
194.500
83.672
64.000
325.000
10
243.003
347.880
83.522
31.031
38.912
134.875
10
101.510
140.406
Cttgvmtinab
Cyanide
100
0.185
0.054
0.060
0.250
10
0.217
0.285
0.084
0.030
0.023
0.122
10
0.102
0.14(1
PAH.
Aatiuaoenc
IS
2.331
1.685
0.330
6.500
9
3.375
5.464
0.980
0.853
0.198
3.185
9
1.509
2.567
Beozof a)an(iiraccDC
82
1.624
2.069
0.460
6.500
9
2.907
5.472
0.732
0.999
0.170
3.185
9
1 351
2.590
Bcazo(a]pyrene
77
1.920
1.918
0.510
6.500
9
3.109
5.487
0.847
0.939
0.168
3.185
9
1.429
2.592
BenzofbJfluorwthejie
91
1.814
1.863
0.610
6.500
9
2.969
5.278
0.808
0.928
0.201
3.185
9
1.383
2.534
BenzolgJufewylene
68
2.077
1.876
0.560
6.500
9
3.240
5.566
0.885
0.916
0.241
3.185
9
1.452
2.5X7
Benzo[k]floaranthe
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 [2000|>.
Dry Weight (mg/kg)
River Segment ]
Chemical
FOD
(%)
Mean
SD
Min
Max
N
95th
95% UCL Percentile
Wet Weight (mgltg)
Mean
SD
Mm
Max
A'
95% UCL
95th
Pcrccnlili
0.156
0.046
0.096
0.227
9
0.185
0.242
0.025
0.012
0.016
0.051
9
0.032
0.047
0.003
0.003
0.002
0.010
9
0.005
0.009
0.005
0.002
0.002
0.009
9
0.006
O.OOy
0.002
0.000
0.002
0.002
9
0.002
0.002
0.005
0.002
0.003
0.008
9
0.006
<1.0(18
0.001
0.001
0.001
0.003
9
0.002
0.003
0.001
0.000
0.001
0.001
9
0.001
0.001
0.005
0.002
0.002
0.008
9
0.006
0.009
0.002
0.000
0.002
0.002
9
0.002
0.002
0.002
0.000
0.002
0.002
9
0.002
0.0(12
0.003
0.003
0.001
0.009
9
0.005
0.009
0.001
0.001
0.001
0.002
9
0.002
0.003
0.007
0.002
0.006
0.011
9
0.008
0.010
0.918
0.882
0.363
3.185
9
1.465
2.559
1.172
0.805
0.809
3.185
9
1.671
2.668
PCBi
PCB Aroclor 1242
100
0.376
0.115
0.250
0.540
9
0.447
0.589
PCB Aroclor 1260
50
0.060
0.030
0.034
0.130
9
0.078
0.116
Pesticidea
4,4'-DDD (p,p'->
68
0.008
0.007
0.003
0.026
9
0.012
0.021
4,4'-DDE (p,p'-)
86
0.012
0.006
0.004
0.023
9
0.015
0.023
4,4'-DDT (p, p'-)
18
0.004
0.001
0.003
0.005
9
0.004
0.005
Aldrin
82
0.013
0.004
0.008
0.018
9
0.015
0.020
alpha-Chlordane
64
0.003
0.002
0.002
0.009
9
0.005
0.007
delta-Benzene hexachloride
14
0.002
0.000
0.001
0.003
9
0.002
0.003
Dieldrin
68
0.012
0.006
0.004
0.021
9
0.015
0.022
Endosulfan 11
14
0.004
0.001
0.003
0.005
9
0.004
0.005
Endrin ketone
27
0.004
0.001
0.003
0.005
9
0.004
0.005
gamma-Chlordane
73
0.007
0.008
0.002
0.024
9
0.011
0.021
Heptachlor
36
0.003
0.002
0.001
0.006
9
0.004
0.006
Heptachlor epoxide
77
0.018
0.004
0.012
0.025
9
0.020
0.025
Seroivoiatile Organic
Compounds
bis(2-EthylhexyI)phthalate
91
2.113
1.759
0.920
6.500
9
3.203
5.383
Di-n-octylphthalatc
32
2.761
1.613
1.350
6.500
9
3.761
5.761
FOD - Frequency of detection
SD - Standard deviation
jV - Number of samples counted
Lower Ottawa River SLRA
Page 2 of 8
October 2001
551-3'63-001
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 (2000]).
River Segment 2
Dry Weight (mg/kg) Wet Weight (mg/kg)
Chemical
Mean
SD
Min
Max
N
95% UCL
95th
Percentile
Mean
SD
Min
Max
N
95% UCL
95th
Percentile
Metal.
Aluminum
8288.333
1695.328
5410.000
10200.000
6
9682.979
11704.502
4357.787
1613.847
2185.640
6764.640
6
5685.403
7609.768
Antimony
1.003
0.735
0.390
2.300
6
1.607
2.484
0.474
0.269
0.202
0.929
6
0.695
I.0I7
Arsenic
6.000
0.654
5.000
6.900
6
6.538
7.318
3.049
0.574
2.574
4.145
6
3.521
4 206
Barium
120.517
56.262
83.700
234.000
6
166.800
233.887
59.207
19.769
40.657
94.536
6
75.470
99.044
Boy Ilium
0.422
0.076
0.320
0.550
6
0.484
0.575
0.222
0.081
0.129
0.348
6
0.289
0.386
Cadmium
1.500
0.253
1.200
1.800
6
1.708
2.010
0.778
0.274
0.618
1.326
6
1.003
1.330
Chromium
45.550
15.553
33.300
75.600
6
58.345
76.891
23.467
9.646
15.480
39.875
6
31.402
42.904
Cobalt
6.883
0.778
5.900
8.000
6
7.524
8.452
3.562
0.979
2.384
5.057
6
4.368
5.535
Copper
55.767
8.990
46.400
65.800
6
63.162
73.882
28.179
5.387
23.896
38.466
6
32.611
39.034
Iron
17466.667
2571.899
14400.000
20400.000
6
19582.415
22649.170
9003.533
2454.376
5817.600
12683.700
6
11022.602
13949.221
Lead
145.517
138.152
75.100
427.000
6
259.166
423.899
69.539
52.904
34.353
172.508
6
113.061
176.144
Manganese
297.667
63.159
195.000
376.000
6
349.624
424.935
155.129
52.011
78.780
220.514
6
197.915
259.934
Mercury
0.126
0.063
0.046
0.210
6
0.178
0.253
0.071
0.048
0.019
0.141
6
0.110
0.168
Nickel
31.800
3.624
27.400
37.800
6
34.781
39.102
16.450
4.998
12.533
26.362
6
20.561
26.521
Selenium
1.357
0.519
0.730
2.100
6
1.784
2.403
0.650
0.109
0.469
0.783
6
0.739
0.869
Silver
0.783
0.226
0.550
1.200
6
0.969
1.238
0.402
0.150
0.283
0.671
6
0.526
0.705
Thallium
4.317
1.093
3.400
5.800
6
5.215
6.518
2.187
0.595
1.535
2.987
6
2.676
3.385
Vanadium
20.700
3.061
16.600
24.200
6
23.218
26.869
10.692
3.004
6.706
15.254
6
13.163
16.745
Zinc
224.000
77.501
165.000
373.000
6
287.755
380.168
110.934
27.087
85.044
150.692
6
133.217
165.516
Craventioaab
Cyanide
0.198
0.080
0.130
0.330
6
0.264
0.360
0.098
0.030
0.057
0.123
6
0.123
0.159
PAH.
Anthracene
2.308
0.893
0.950
3.150
6
3.043
4.108
1.158
0.501
0.437
1.643
6
1.570
2.168
Benzo{a]aalhracene
1310
1.076
0.860
3.150
6
3.195
4.478
1.160
0.576
0.415
1.643
6
1.634
2.321
Benzo[alpyrene
1.928
1.094
0.650
3.150
6
2.828
4.133
0.954
0.566
0.345
1.638
6
1.419
2.094
Be&zo[b]fluaranthene
1.667
0.866
0.860
2.850
6
Z379
3.411
0.814
0.425
0.447
1.482
6
1.164
1.670
Beazo[gJvlperylene
1.165
0.860
0.630
2.850
6
1.872
2.898
0.577
0.450
0.328
1.482
6
0.947
1.484
Benzo[lc]fluoranthene
2.165
1.180
0.790
3.600
6
3.136
4.543
1.065
0.584
0.419
1.656
6
1.546
2.243
Chryiene
1.527
1.120
0.680
3.700
6
2448
3.784
0.730
0.496
0.354
1.702
6
1.138
1.730
Dibcnzfa.hlanthraccnc
1.983
1.215
0.450
3.150
6
2.983
4.431
1.021
0.659
0.187
1.643
6
1.563
2.348
Fluoranthenc
Z663
2.530
0.980
7.700
6
4.744
7.761
1.267
1.136
0.510
3.542
6
2.201
3.556
Indeno[l ,23-cd]pyrcne
1.772
1.044
0.670
3.100
6
2.630
3.874
0.885
0.563
0.348
1.643
6
1.349
2.020
Phezianthrene
1440
1.257
0.780
3.800
6
3.474
4.973
1.219
0.639
0.398
1.748
6
1.745
2.506
Pyrene
2.350
2.022
1.100
6.300
6
4.013
6.424
1.117
0.901
0.572
2.898
6
1.859
2.934
Lower Ottawa River SLRA
Page 3 of 8
October 2001
555-3163-001
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 [2000)).
River Segment 2
Dry Weight (mg/kg) Wet Weight (mg/kg)
Chemical
Mean
SD
Min
Max
N
95%UCL
95th
Percentile
Mean
SD
Min
Max
N
95°.o UCl.
95th
Percentil
PCB»
PCB Aroclor 1242
1.717
1.057
0.440
3.400
6
2.586
3.846
0.845
0.505
0.229
1.564
6
1.260
1.862
PCB Aroclor 1260
0.062
0.036
0.032
0.120
6
0.092
0.134
0.031
0.019
0.016
0.062
6
0.046
0,069
FntkMo
4,4'-DDD (p,p'-)
0.014
0.006
0.007
0.022
6
0.019
0.027
0.007
0.003
0.003
0.011
6
0.009
0.013
4,4'-DDE (p,p'-)
0.021
0.008
0.010
0.031
6
0.028
0.037
0.010
0.004
0.005
0.016
6
0.014
0.019
4,4-DDT (p,p'-)
0.003
0.001
0.003
0.004
6
0.004
0.004
0.002
0.000
0.001
0.002
6
0.002
0.002
Aldrin
0.043
0,033
0.002
0.087
6
0.070
0.110
0.021
0.016
0.001
0.040
6
0.034
0.053
alpha-Chlordane
0.005
0.002
0.002
0.007
6
0.006
0.009
0.002
0.001
0.001
0.003
6
0.003
0.004
delta-Benzene hexachloride
0.004
0.003
0.002
0.010
6
0.006
0.010
0.002
0.002
0.001
0.005
6
0.003
0,006
Dieldrin
0.015
0.011
0.003
0.030
6
0.023
0.036
0.007
0.005
0.002
0.016
6
0.012
0.018
Endosulfan II
0.006
0.007
0.003
0.020
6
0.012
0.020
0.003
0.004
0.001
0.011
6
0.006
0.011
Hndrin ketone
0.004
0.002
0.003
0.009
6
0.006
0.009
0.002
0.001
0.001
0.004
6
0,003
0,004
gamma-Chlordane
0.013
0.006
0.007
0.020
6
0.018
0.025
0.006
0.002
0.004
0.009
6
0.008
0.011
Iicplachi or
0.004
0.003
0.002
0.010
6
0.007
0.011
0.002
0.002
0.001
0.005
6
0,004
0.006
HepUchlor epoxide
0.032
0.032
0.002
0.081
6
0.058
0.096
0.015
0.015
0.001
0.037
6
0.028
0.046
SemivoUtife Organic
Compounds
bu(2-Ethylhexyl)phthalate
3.900
3.549
1.300
11.000
6
6.820
11.052
1.874
1.603
0.676
5.060
6
3.192
5.103
Di-n-octylphthalate
2.760
1.897
0.690
5.900
6
4.321
6.582
1.366
0.895
0.359
2.714
6
2.102
3.170
FOD - Frequency of dctectic
SD - Standard deviation
N - Number of samples com
Lower Ottawa River SLRA
Page 4 of 8
October 2001
555-3"6S'00J
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 [2000]).
River Segment 3
Dry Weight (mg/kg) Wet Weight (mg/kg)
Chemical
Mean
SD
Min
Max N
95%UCL
95th
Percentile
Mean
SD
Min
Max
N
95% UCL
95th
Percentile
Metak
Aluminum
7918.000
1605.014
6160.000
9770.000 5
9448.205
11339.643
3944.650
820.708
3043.040
4933.850
5
4727.105
5694.273
Antimony
0.712
0.415
0.385
1.300 5
1.108
1.596
0.363
0.227
0.190
0.657
5
0.580
0.848
Aitenic
10.840
10.797
5.000
30.100 5
21.134
33.857
5.447
5.481
2.470
15.201
5
10.672
17.131
Barium
127.000
34.583
104.000
188.000 5
159.971
200.726
63.614
18.890
48.816
94.940
5
81.624
103.884
Beryllium
0.440
0.122
0.330
0.630 5
0.556
0.699
0.220
0.063
0.163
0.318
5
0.280
0.354
Cadmium
2300
1.655
1.200
5.200 5
3.878
5.829
1.159
0.845
0.518
2.626
5
1.965
2.961
Chromium
75.980
64.438
35.200
190.000 5
137.414
213.351
38.198
32.723
15.206
95.950
5
69.396
107.958
Cobalt
6.500
0.995
5.400
7.700 5
7.449
8.621
3.241
0.540
2.668
3.889
5
3.756
4.392
Copper
80.180
17.926
64.500
111.000 5
97.271
118.396
40.228
10.262
27.864
56.055
5
50.011
62.104
Iron
16640.000
2973.718
13000.000
20000.000 5
19475.115
22979.511
8305.840
1648.825
6422.000
10100.000
5
9877.814
11820.882
Lead
5284.000
11580.597
99.000
26000.000 5
16324.834
29972055
2667.892
5848.499
42.768
13130.000
5
8243.797
15135.994
Manganese
298.400
75.487
225.000
400.000 5
370.369
459.327
148.381
36.823
113.625
200.428
5
183.488
226.883
Mercury
0.440
0.384
0.130
1.100 5
0.806
1.259
0.218
0.195
0.073
0.556
5
0.404
0.633
Nickel
34.740
6.508
29.900
46.000 5
40.945
48.614
17.333
3.504
14.771
23.230
5
20.674
24.803
Selenium
1.738
0.676
0.990
2.800 5
2.382
3.179
0.876
0.357
0.428
1.414
5
1.216
1.637
Silver
1.460
0.555
1.000
2.400 5
1.989
2.643
0.731
0.291
0.494
1.212
5
1.008
1.350
Thallium
3.000
0.696
1.900
3.800 5
3.664
4.485
1.505
0.405
0.939
1.919
5
1.891
2.368
Vanadium
19.820
3.231
16.200
23.300 5
2X900
26.707
9.877
1.696
8.003
11.767
5
11.494
13.492
Zinc
275.400
41.095
251.000
348.000 5
314.580
363.008
137.839
25.644
110.592
175.740
5
162.288
192.507
Cimataali
Cyanide
0.316
0.279
0.120
0.800 5
0.582
0.911
0.149
0.115
0.060
0.346
5
0.258
0.393
PAH*
Anthracene
3.660
1.634
2.600
6.500 5
5.218
7.143
1.965
0.755
1.612
3.315
5
2.684
3.574
Beezo(a]anthraccnc
1.580
0.356
1.300
2.200 5
1.920
2340
0.861
0.172
0.675
1.122
5
1.025
1.228
Bcnzofajpyratc
1.620
0.217
1.500
2.000 5
1.827
2.082
0.882
0.081
0.765
0.992
5
0.960
1.055
Beozo{b]9aanathene
Z120
0.349
1.800
2.700 5
2453
2.865
1.154
0.141
0.969
1.302
5
1.288
1.454
Bozo|gjM|pa]tae
2910
2077
1.500
6.500 5
4.891
7.339
1.555
1.029
0.870
3.315
5
2.535
3.747
Batzofkjflooranthcnc
2000
0.418
1.500
2.400 5
2399
2.892
1.083
0.164
0.870
1.298
5
1.239
1.433
Cfayscac
2.480
0.370
2100
3.000 5
2.833
3.269
1.345
0.075
1.218
1.416
5
1.417
1.505
Pibem[aJi|aBthraccnc
3.660
1.634
2.600
6.500 5
5.218
7.143
1.965
0.755
1.612
3.315
5
2.684
3.574
Fftsoran these
3.740
0.680
2.800
4.700 5
4.389
5.191
2.044
0.352
1.428
2.301
5
2.380
2.795
Imkno[l ,2^-ed]pyiene
1.500
0.354
1.200
2.100 5
1.837
2.254
0.807
0.084
0.744
0.945
5
0.886
0.985
Phenanthrene
2520
2231
1.400
6.500 5
4.647
7.276
1.338
1.106
0.810
3.315
5
2.392
3.695
Pyrene
3.260
0.684
2.500
4.300 5
3.912
4.718
1.774
0.300
1.275
2.065
5
2.061
2.414
Lower Ottawa River SLRA
Page S of 8
October 200J
555-3763-001
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 (2000]).
River Segment 3
Diy Weight (mg/kg) Wet Weight (mg/kg)
Chemical
Mean
SD
Min
Max
M
95%UCL
95th
Percentile
Mean
SD
Min
Max
.V
95°o UCI.
95th
Percentile
PCB«
PCB Aroclor 1242
1.425
1.051
0.057
2.700
5
2.428
3.667
0.815
0.654
0.029
1.674
5
1.439
2.210
PCB Aroclor 1260
0.068
0.053
0.028
0.140
5
0.119
0.182
0.036
0.027
0.016
0.068
5
0.062
0.094
Pesticides
•M'-DDD (p,p'-)
0.022
0.014
0.003
0.038
5
0.036
0.053
0.012
0.008
0.002
0.024
5
0,020
0.030
4,4'-DDE (p,p'-)
0.025
0.017
0.003
0.047
5
0.041
0.061
0.014
0.008
0.002
0.022
5
0.022
0.031
4,4'-DDT (p,p-)
0.008
0.006
0.003
0.016
5
0.013
0.020
0.004
0.003
0.002
0.007
5
0.007
0.010
Aldrin
0.019
0.024
0.001
0.054
S
0.042
0.070
0.010
0.012
0.001
0.024
5
0.021
0.034
alpha-Chlordane
0.009
0.006
0.002
0.017
S
0.014
0.021
0.005
0.003
0.001
0.008
5
0.007
0.011
delta-Benzene hexachtoride
0.005
0.008
0.001
0.019
5
0.012
0.022
0.003
0.005
0.001
0.011
5
0.007
0.013
Dieldrin
0.008
0.006
0.003
0.017
5
0.013
0.020
0.004
0.003
0.002
0.010
5
0.008
0.012
Endosulfan II
0.007
0.008
0.003
0.021
5
0.014
0.024
0.004
0.005
0.002
0.012
5
0.008
0.014
F-ndrin ketone
0,005
0.002
0.003
0.008
5
0.007
0.010
0.003
0.001
0.002
0.005
5
0.004
0.006
gam ma-Chi or dan c
0.012
0.005
0.007
0.019
5
0.017
0.022
0.007
0.003
0.004
0.011
5
0.009
0.013
Hcptachlor
0.002
0.001
0.001
0.005
5
0.003
0.005
0.001
0.001
0.001
0.003
5
0.002
0.003
Heptachlor epoxide
0.010
0.017
0.001
0.040
5
0.026
0.046
0.006
0.010
0.001
0.024
5
0.015
0.027
SemivoUtite Organic
Compounds
bis(2-Ethyl)»exyl)phthalate
3.660
1.656
2.300
6.500
5
5.239
7.191
1.970
0.785
1.357
3.315
5
2.718
3.64?
Di-n-octylphthalate
2.848
2.308
0.640
6.500
5
5.049
7.769
1.481
1.119
0.378
3.315
5
2.547
3.866
FOD - Frequency of detectic
SD - Standard deviation
N - Number of samples cow
Lower Ottawa River SLRA
Page 6 of 8
Ocl'jbcr 2001
$55-3~63-00l
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 12000]).
River Segment 4
Dry Weight (mg/kg) Wet Weight (mg/kg)
Chemical
Mean
SD
Mm
Max
N
95%UCL
95th
Percentile
Mean
SD
Min
Max
N
95%UCL
95th
Percentile
Mateb
Aluminum
3830.000
1202.082
2980.000
4680.000
2
9196.686
11419.641
2269.100
537.090
1889.320
2648.880
2
4666 935
5660.151
Antimony
0.33J
0.007
0.330
0.340
2
0.367
0.380
0.201
0.012
0.192
0.209
2
0.254
0.276
Anenic
3.500
1.414
2.500
4.500
2
9.814
12.429
2.066
0.680
1.585
2.547
2
5.103
6.361
Barium
77.550
43.063
47.100
108.000
2
269.804
349.438
45.495
22.109
29.861
61.128
2
144.199
185.084
Beryllium
0.200
0.099
0.130
0.270
2
0.642
0.825
0.118
0.050
0.082
0.153
2
0.340
0.432
Cadmium
0.685
0.332
0.450
0.920
2
2.169
2.783
0.403
0.166
0.285
0.521
2
1.146
1.454
Chromium
29.750
21.425
14.600
44.900
2
125.403
165.024
17.335
11.425
9.256
25.413
2
68.341
89.468
Cobalt
3.800
0.707
3.300
4.300
2
6.957
8.264
2.263
0.242
2.092
2.434
2
3.341
3.788
Copper
41.050
13.647
31.400
50.700
2
101.978
127.215
24.302
6.214
19.908
28.696
2
52.046
63.539
Iran
10530.000
1937.473
9160.000
11900.000
2
19179.836
22762.715
6271.420
656.167
5807.440
6735.400
2
9200.873
10414.292
Lead
95.250
44.901
63.500
127.000
2
295.712
378.745
56.071
22.361
40.259
71.882
2
155.900
197.251
Manganese
196.000
39.598
168.000
224.000
2
372.785
446.012
116.648
14.334
106.512
126.784
2
180.644
207.152
Mercury
0.175
0.021
0.160
0.190
2
0.270
0.309
0.104
0.004
0.101
0.108
2
0.124
0.132
Nickel
13.000
2.263
11.400
14.600
2
23.102
27.286
7.746
0.733
7.228
8.264
2
11.016
12.371
Selenium
0.973
0.887
0.345
1.600
2
4.934
6.575
0.562
0.486
0.219
0.906
2
2.731
3.629
Silver
1.780
1.442
0.760
2.800
2
8.220
10.888
1.103
0.951
0.430
1.775
2
5.349
7.108
Thallium
2.100
0.990
1.400
2.800
2
6.520
8.350
1.236
0.493
0.888
1.585
2
3.437
4.349
Vanadium
11.400
3.394
9.000
13.800
2
26.553
32.830
6.758
1.488
5.706
7.811
2
13.403
16.155
Zinc
189.000
94.752
122.000
256.000
2
612.021
787.242
111.122
47.764
77.348
144.896
2
324.363
412.690
Cwmtlwli
Cyanide
0.550
0.453
0.230
0.870
2
2570
3.407
0.319
0.245
0.146
0.492
2
1.413
1.867
PAH*
Anthracene
1.510
1.824
0.220
2.800
2
9.655
13.028
1.042
1.240
0.165
1.918
2
6.576
8.868
Beazojajacithraocne
1.620
0.962
0.940
2.300
2
5.913
7.692
1.140
0.616
0.705
1.576
2
3.888
5.027
Beazo[aJpyrene
1.650
1.061
0.900
2.400
2
6.385
8.347
1.160
0.685
0.675
1.644
2
4.219
5.486
Benzojbjfluoranthene
1.950
1.202
1.100
2.800
2
7.317
9.540
1.372
0.773
0.825
1.918
2
4.822
6.251
Benzo{ g^i^ierylene
1.390
0.721
0.880
1.900
2
4.610
5.944
0.981
0.454
0.660
1.302
2
3.006
3.845
Benzo{k]ftti«antheac
2.050
1.344
1.100
3.000
2
8.048
10.533
1.440
0.870
0.825
2.055
2
5.323
6.931
Chryaene
2.350
1.485
1.300
3.400
2
8.979
11.725
1.652
0.957
0.975
2.329
2
5.926
7.697
Dibenz[*^]a»thr»ccne
1.525
1.803
0.250
2.800
2
9.575
12.909
1.053
1.224
0.188
1.918
2
6.516
8.779
Fhwrantheae
5.000
3.394
2.600
7.400
2
20.153
26.430
3.510
2.205
1.950
5.069
2
13 356
17.434
lndeno[ 1,2^-cdJpyrene
1.275
0.742
0.750
1.800
2
4.590
5.963
0.898
0.474
0.563
1.233
2
3.014
3.891
Fhaullutae
2.100
1.131
1.300
2.900
2
7.151
9.243
1.481
0.715
0.975
1.987
2
4 674
5.997
Pyrcne
3.550
2.051
2100
5.000
2
12.705
16.497
2.500
1.308
1.575
3.425
2
8.340
10.759
Lower Ottawa River SLRA
Page 7 of 8
October 2001
555-3~63-001
-------
Table A-2b. Summary results for measured chemical concentrations in sediment (Data from Inventory 20 [2000)).
River Segment 4
Dry Weight (mg/kg) Wet Weight (mg kg)
Chemical
Mean
SD
Min
Max
N
95%UCL
95th
Percentile
Mean
SD
Min
Max
A'
95% UCl.
95th
Percenti!
PCBs
PCB Aroclor 1242
0.318
0.385
0.045
0.590
2
2.038
2.751
0.237
0.291
0.031
0.443
2
1.536
2.075
PCB Aroclor 1260
0.128
0.088
0.066
0.190
2
0.519
0.682
0.094
0.069
0.045
0.143
2
0.401
0.528
Pesticide*
4,4'-DDD (p,p'-)
0.017
0.010
0.009
0.024
2
0.063
0.082
0.012
0.008
0.006
0.018
2
0.049
0.064
4,4'-DDE (p,p-)
0.011
0.005
0.008
0.015
2
0.034
0.044
0.008
0.004
0.005
0.011
2
0.027
0.035
4,4'-DDT (p,p'-)
0.004
0.002
0.002
0.005
2
0.014
0.018
0.003
0.002
0.001
0.004
2
0.011
0.014
Aldrin
0.002
0.002
0.001
0.004
2
0.011
0.014
0.002
0.001
0.001
0.003
2
0.007
0.009
alpha-Chlordanc
0.004
0.003
0.002
0.007
2
0.018
0.023
0.003
0.002
0.002
0.005
2
0.014
0.01 S
delta-Benzene hexachloride
0.001
0.000
0.001
0.001
2
0.001
0.001
0.001
0.000
0.001
0.001
O
0.001
0.001
Dieldrin
0.004
0.002
0.002
0.006
2
0.015
0.020
0.003
0.002
0.002
0.004
2
0.010
0.013
Endosulfan II
0.006
0.005
0.002
0.009
2
0.028
0.037
0.004
0.004
0.001
0.007
2
0.021
0.02H
Endrin ketone
0.009
0.006
0.005
0.013
2
0.036
0.047
0.006
0.005
0.003
0.010
->
0.027
0.036
gamma-Chlordane
0.008
0.000
0.008
0.008
2
0.008
0.008
0.005
0.000
0.005
0.006
2
0.007
0.007
Heptachior
0.001
0.000
0.001
0.001
2
0.001
0.001
0.001
0.000
0.001
0.001
n
0.001
0.001
Heptachlor epoxide
0.003
0.003
0.001
0.005
2
0.017
0.022
0.002
0.002
0.001
0.004
2
0.0)1
0.015
Scmivolatile Organic
Compoundi
bis(2-Ethylhexyl)phthalate
4.400
4.243
1.400
7.400
2
23.341
31.187
3.060
2.842
1.050
5.069
2
15.747
21.002
Di-n-octvlphthalatc
0.945
0.219
0.790
1.100
2
1.924
2.329
0.683
0.201
0.541
0.825
2
1.579
1.950
FOD - Frequency of detectic
SD - Standard deviation
iV - Number of sample* com
Lower Ottawa River SLRA
Page 8 of 8
October Z0()l
555-3763-00!
-------
Table A-4. Chemical concentrations in invertebrate tissues estimated from measured sediment concentrations.
Chronic 95% UCL Sediment Concentration, Study 20 Estimated Chronic Tissue Concentration - Invertebrates
(mg/kg-dry) (mg/kg-wet)
Chemical
log Kow
BSAF1
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM>8.8
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM >8.8
Mean % Total Organic Carbon (TOQ
4.5
3.7
5.5
5.8
.
.
.
_
*/• Lipids (Estimated)
-
-
-
-
1.05
1.05
1.05
1.05
PAHs
Anthracene
4.53
0.67
3.375
3.043
5.218
9.655
0.529
0.585
0.667
1.178
Bcnzo(a]anthnccne
5.67
0.61
2907
3.195
1.920
5.913
0.412
0.556
0.222
0.653
Benzojajpyrene
6.11
0.59
3.109
2.828
1.827
6.385
0.425
0.474
0.203
0.679
Benzo{bjfluoranthcnc
6.27
0.58
2.969
2.379
2.453
7.317
0.400
0.393
0.269
0.767
Benzo[ g,h,i]perylcnc
6.51
0.57
3.240
1.872
4.891
4.610
0.427
0.303
0.526
0.473
BenzolIcjfluaranlhenc
6.29
0.58
3.098
3.136
2399
8.048
0.416
0.517
0.263
0.842
Chrysene
5.71
0.61
3.157
2.448
2.833
8.979
0.446
0.425
0.327
0.988
Dibcnzfajijanthracene
6.71
0.56
3.735
2.983
5.218
9.575
0.484
0.474
0.551
0.966
Fluoranthene
5.08
0.64
4.452
4.744
4389
20.153
0.665
0.869
0.535
2.344
Indeno) l,23-cd]pyrenc
7.1
0.54
3.052
2.630
1.837
4.590
0.382
0.404
0.188
0.447
Phcnanthrcnc
4.57
0.67
3.754
3.474
4.647
7.151
0.586
0.666
0.592
0.870
Pyrcne
4.92
0.65
3.946
4.013
3.912
12705
0.598
0.746
0.484
1.498
PCBs
PCB Aroclor 1242
6.04
21
0.447
2.586
2.428
2038
0.219
1.552
0.969
0.776
PCB Aroclor 1260
6.04
Z1
0.078
0.092
0.119
0.519
0.038
0.055
0.047
0.198
Pesticide*
4,4'-DDD (p,p'-)
5.75
20
0.012
0.019
0.036
0.063
0.006
0.011
0.014
0.023
4,4-DDE (p,p'-)
5.77
2.0
0.015
0.028
0.041
0.034
0.007
0.016
0.016
0.012
4,4'-DDT (p,p'-)
5.96
20
0.004
0.004
0.013
0.014
0.002
0.002
0.005
0.005
Aldrin
5.86
20
0.015
0.070
0.042
0.011
0.007
0.040
0.016
0.004
alpha-Chlordanc
6.1
20
0.005
0.006
0.014
0.018
0.002
0.004
0.005
0.006
d-BHC
4.12
20
0.002
0.006
0.012
0.001
0.001
0.004
0.005
0.000
Dieldrin
4.62
20
0.015
0.023
0.013
0.015
0.007
0.013
0.005
0.005
Endoaulfan Q
3.62
20
0.004
0.012
0.014
0.028
0,002
0.007
0.005
0.010
Endrin ketone
5.02
20
0.004
0.006
0.007
0.036
0.002
0.003
0.003
0.013
gamma-Chlordane
6.26
20
0.011
0.018
0.017
0.008
0.005
0.010
0.006
0.003
Heptachlor
4.69
20
0.004
0.007
0.003
0.O01
0.002
0.004
0.001
0.000
Hcptachlor epoxide
3.92
20
0.020
0.058
0.026
0.017
0.009
0.033
0.010
0.006
Seinivolatile Organic!
bi»<2-Ethylhexjl)phlhalaU:
4.87
0.65
3.203
6.820
5.239
23.341
0.488
1.273
0.650
2.765
Di-n-octylphthalate
8 58
0.47
3.761
4.321
5.049
1.924
0.414
0.583
0.453
0.165
1 The BSAF* for PAH* and certain "Other Organic*" are based on a wet weight lipid concentration in biota, while the BS AFs for PCBs
and pcttiridci are based on a dry weight lipid concentration. When a dry weight BSAF was used, the concentration was calculated back
to wet weight using an estimated percent moisture of 80%.
October 2001
Lower Ottawa River SLRA PaSe J of 2 555-3 ~6S- Oft I
-------
Table A-4 Chemical concentrations injnvertebrate tissues estimated from measured sediment concentrations.
Acute 95% UCL Sediment Concentration, Study 20 Estimated Acute Tissue Concentration - Invertebrates
(nig/kg-dry) (mg/kg-wet)
Chemical
log Kow
BSAF1
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM>8.8
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM >8 8
Mean % Total Organic Carbon (TOC)
4.5
3.7
5.5
5.8
.
.
% Lipids (Estimated)
-
-
-
-
1.05
1.05
1.05
1.05
PAHs
Anthracene
4.53
0.67
5.464
4.108
7.143
13.028
0.857
0.790
0.914
1.590
Benzo(a]*nthraccnc
5.67
0.61
5.472
4.478
2.340
7.692
0.776
0.779
0.271
0.850
Benzo(a|pyrcne
6.11
0.59
5.487
4.133
2.082
8.347
0.749
0.692
0.232
0.887
Benzo(bJfluora«thene
6.27
0.58
5.278
3.411
2.865
9.540
0.711
0.563
0.315
1.000
Benzo( gXilperytene
6.51
0.57
5.566
2.898
7.339
5.944
0.734
0.468
0.789
0.610
Benzol k]tluoranthcne
6.29
0.58
5.599
4.543
2.892
10.533
0.753
0.749
0.317
1102
Chryaene
5.71
0.61
5.681
3.784
3.269
11.725
0.803
0.656
0.377
1.291
Dibenz}a,h (anthracene
6.71
0.56
5.906
4.431
7.143
12909
0.765
0.704
0.755
1.302
Fluoraathcne
5.08
0.64
7.720
7.761
5.191
26.430
1.153
1.422
0.633
3.074
Indenol 1,2^-cdJpyieae
7.1
0.54
5.457
3.874
2.254
5.963
0.683
0.595
0.230
0.581
Pltcaanthrene
4.57
0.67
5.906
4.973
7.276
9.243
0.923
0.953
0.927
1.124
Pyiene
4.92
0.65
6.967
6.424
4.718
16.497
1.056
1.194
0.583
1.946
PCBs
PCB Aroclor 1242
6.04
21
0.589
3.846
3.667
2751
0.288
2308
1.464
1.048
PCS Aroclor 1260
6.04
2.1
0.116
0.134
0.182
0.682
0.057
0.081
0.072
0.260
Pesticides
4,4'-DDD (pj>'-)
5.75
20
0.021
0.027
0.053
0.082
0.010
0.015
0.020
0.030
4,4'-DDE (pj)'-)
5.77
20
0.023
0.037
0.061
0.044
0.011
0.021
0.023
0.016
4,4'-DDT (pji1-)
5.96
20
0.005
0.004
0.020
0.018
0.002
0.003
0.008
0.007
Aldrin
5.86
20
0.020
0.110
0.070
0.014
0.009
0.063
0.027
0.005
ilpha-Oiiordane
6.1
20
0.007
0.009
0.021
0.023
0.003
0.005
0.008
0.008
d-BHC
4.12
20
0.003
0.010
0.022
0.001
0.001
0.006
0.008
0.000
Diekkin
4.62
20
0.022
0.036
0.020
0.020
0.010
0.021
0.008
0.007
Endoeulfan II
3.62
20
0.005
0.020
0.024
0.037
0.002
0.011
0.009
0.013
Endrin ketone
5.02
20
0.005
0.009
0.010
0.047
0.002
0.005
0.004
0.017
gamma-Chlordanc
6.26
20
0.021
0.025
0.022
0.008
0.010
0.014
0.009
0.003
Heptachlor
4.69
20
0.006
0.011
0.005
0.001
0.003
0.006
0.002
0.000
Hcptachlor epoxide
3.92
20
0.025
0.096
0.046
0.022
0.012
0.055
0.017
0.008
Scsaivolatile Or{iaks
bis(2-Ethylhexyl)phthaUte
4.87
0.65
5.383
11.052
7.191
31.187
0.819
2063
0.893
3.694
Di-n-octyIphthal»te
8.58
0.47
5.761
6.582
7.769
2329
0.634
0.888
0.697
0.199
October 2001
555-3-63-001
The BSAFs fur PAH> and certain "Other Organics" are based on a wet weight lipid concentration in biota, while the BSAFs for PCBs
and pesticide* are based on a dry weight lipid concentration. When a dry weight BSAF was used, the concentration was calculated back
to wet weight using an ettinuted percent moisture of 80%.
Lower Ottawa River SLRA P"ge 2 of 2
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 [2000)).
River Segment 1
Chemical Units FOD % Mean SD Min Max N 9S°oUCL 95th percentile
Metals
Aluminum
Hg/L
100
2170.44
695.71
934.00
2790.00
9
2601.68
3464.15
Antimony
(ig/L
5
1.05
0.00
1.05
1.05
9
1.05
1.05
Arsenic
(ig/L
16
1.53
0.78
1.15
3.30
9
2.01
2.98
Barium
100
61.56
3.10
54.20
64.20
9
63.48
67.32
Cadmium
itg/L
16
0.14
0.07
0.10
0.30
9
0.18
0.27
Chromium
(ig/L
100
4.17
1.20
2.00
5.40
9
4.91
6.39
Cobalt
(tg/L
89
1.14
0.39
0.25
1.70
9
1.38
1.87
Copper
(ig/L
100
11.76
1.28
8.90
13.20
9
12.55
14.14
Iron
Hg^
100
3624.44
1109.00
1710.00
4640.00
9
4311.86
5686.68
Lead
Cg'L
100
6.43
1.80
2.00
7.80
9
7.55
9.78
Manganese
100
85.06
9.89
63.00
100.00
9
91.18
103.44
Mercury
100
0.14
0.02
0.12
0.17
9
0.15
0.17
Nickel
Hg/L
100
7.47
1.17
5.10
8.50
9
8.19
9.63
Selenium
Hg/L
84
4.79
1.79
2.90
8.00
9
5.90
8.12
Thallium
KgA*
5
1.92
0.97
1.60
4.50
9
2.52
3.72
Vanadium
Mg/L
100
5.97
1.47
3.40
7.40
9
6.88
8.69
Zinc
f»g/L
100
20.44
5.74
9.40
30.50
9
24.00
31.12
Conventional]
Ammonia
mg/L
95
0.21
0.05
0.13
0.30
9
0.24
0.30
Cyanide
Mg/L
100
4.58
1.09
3.20
5.90
9
5.26
6.61
Hardness
mg/L
100
232.67
16.84
212.00
252.00
9
243.11
263.99
pH (95% UCL / 95% LCL)
-
100
7.41
0.23
7.17
8.00
9
7.55
6.98
Temperature
°C
100
24.33
0.96
23.10
25.50
9
24.93
26.12
Poly cyclic Aromatic Hydrocarbons
Benzo[a]anthracene
Mg
-------
Table A^3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 J2000]).
River Segment 1
Chemical Unto FOP % Mean SD Mm Max N 95% UCL 9SUi percentile
Pesticides
Atrazine
Semivoiatiic Orfsolc Contpoimdi
l,l'-Biphenyl
2.4.5-Trichloroptienol
2.4.6-T richlorophenol
2,4-Dichlaroplieaol
2,4-Dim ethy Iphenol
2,4-Dinitrophenol
2-Chlorophcnol
2-Methylphenol
2-Nitrophenol
3,3'-Diciiloro6etizidine
4,6-Oinitro-2-metbyl()henol (DNOC)
4-Chioro-3-metiiyIphcnol
4-Methylpheool
4-Nitrophcnoi
hii(2-Ethylhcxyl)phthalatc
ButylbaizylphthaUtc
Dimethyl phthalate
Di-n-octytphthaiate
Peatachlorophenol (PCP)
Phenol
lig/L 5 4.56
jig/L 5 5.00
fig/L 5 12.50
figL 5 5.00
Hg/L 5 5.00
(ig/L " 5 5.00
fig/L 5 12.50
ftg/L 5 5.00
fig/L 5 5.00
fig/L 5 5.00
Hg/L 5 5.00
|ig/L 5 12.50
ftg/L 5 5.00
(ig/L 5 5.00
ftg/L 5 12.50
pg/L 21 5.00
fig/L 5 5.00
(ig/L 5 5.00
Hg/L 16 5.56
Hg!L 5 12.50
fig/L S 5.00
1.33 1.00 5.00
0.00 5.00 5.00
0.00 12.50 12.50
0.00 5.00 5.00
0.00 5.00 5.00
0.00 5.00 5.00
0.00 12.50 12.50
0.00 5.00 5.00
0.00 5.00 5.00
0.00 5.00 5.00
0.00 5.00 5.00
0.00 12.50 12.50
0.00 5.00 5.00
0.00 5.00 5.00
0.00 12.50 12.50
0.00 5.00 5.00
0.00 5.00 5.00
0.00 5.00 5.00
1.67 5.00 10.00
0.00 12.50 12.50
0.00 5.00 5.00
9 5.38 7.03
9 5.00 5.00
9 12.50 12.50
9 5.00 5.00
9 5.00 5.00
9 5.00 5.00
9 12.50 12.50
9 5.00 5.00
9 5.00 5.00
9 5.00 5.00
9 5.00 5.00
9 12.50 12.50
9 5.00 5.00
9 5.00 5.00
9 12.50 12. SO
9 5.00 5.00
9 5.00 5.00
9 5.00 5.00
9 6.59 8.65
9 12.50 12.50
9 5.00 5.00
FOD • Frequency of detection
SD - Standard deviation
N - Number of umples counted
Lower Ottawa River SLRA
Page 2 of 8
October 2001
555-3763-001
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 [2000]).
River Segment 2
Chemical
Units
Mean
SD
Min
Max
N
95% UCL
93th percent
.Metals
Aluminum
2012.50
149.75
1870.00
2170.00
4
2188.71
2364.92
Antimony
Mg/L
1.05
0.00
1.05
1.05
4
1.05
1.05
Arsenic
W1^
1.81
1.33
1.15
3.80
4
3.37
4.93
Barium
ml-
60.75
7.24
55.20
71.40
4
69.27
77.80
Cadmium
Mg'L
0.10
0.00
0.10
0.10
4
0.10
0.10
Chromium
ng'l'
3.35
0.70
2.90
4.40
4
4.18
5.01
Cobalt
Mg'^
1.13
0.31
0.95
1.60
4
1.50
1.87
Copper
Hg'L
11.03
0.29
10.60
11.20
4
11.36
11,70
Iron
3387.50
657.74
2910.00
4320.00
4
4161.45
4935.41
Lead
fgL
4.90
2.02
2.90
7.30
4
7.28
9.66
Manganese
69.10
27.39
52.30
110.00
4
101.33
133.56
Mercury
ng'L
0.15
0.02
0.13
0.18
4
0.17
0.20
Nickel
ng'1*
6.58
1.09
5.90
8.20
4
7.86
9.14
Selenium
Mg1-
3.13
2.34
1.10
5.20
4
5.88
8.63
Thallium
tlg^
1.60
0.00
1.60
1.60
4
1.60
1.60
Vanadium
Cg'L
5.43
0.53
5,00
6.10
4
6.05
6.68
Zinc
Mg'L
18.15
3.76
14.80
22.90
4
22.57
26.99
Conventional*
Ammonia
mg/L
0.21
0.06
0.17
0.30
4
0.29
0.36
Cyanide
Hg^-
4.08
0.93
3.30
5.40
4
5.17
6.26
Hardness
mg/L
263.75
29.60
246.00
308.00
4
298.58
333.41
pH (95% UCL / 95% LCL)
-
7.37
0.06
7.32
7.43
3
7.47
7.21
Temperature
°C
22.00
0.98
21.20
23.10
3
23.66
24.88
Polycyclic Aromatic Hydrocarbon#
Benzo[a]anthracene
Hg^
5.00
0.00
5.00
5.00
4
5.00
5.00
Benzo[a|pyrene
Hg'L
5.00
0.00
5.00
5.00
4
5.00
5.00
Benzo(b]fluoranthene
(ig'L
5.00
0.00
5.00
5.00
4
5.00
5.00
Benzo[g,jh,iJperylene
5.00
0.00
J.00
5.00
4
5.00
5.00
Benzo[k}fJuoran!Jiene
fg'l-
5.00
0.00
5.00
5.00
4
5.00
5.00
Chrysene
Hg/L
5.00
0.00
5.00
5.00
4
5.00
5.00
Dibenz[a?hjanlhracene
US'1-
5.00
0.00
5.00
5.00
4
5.00
5.00
Indeno(K2,3-cdlpyrene
Hg't-
5.00
0.00
5.00
5.00
4
5.00
5.00
Pyrene
fg'L
5.00
0.00
5.00
5.00
4
5.00
5.00
Lower Ottawa River SLRA
Page 3 of 8
October 2001
551-3763-001
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 29 {2000}).
River Segment 2
Chemical
Units
Mean
SD
Mia
Max
N
95%UCL
95th percentile
Pesticides
Atrazine
fg/L
5.00
0.00
5.00
5.00
4
5.00
5.00
Scniivolatile Organic Compounds
1 ,L'-B [phenyl
fg/L
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4,5-Trichlorophenol
I2.S0
0.00
12.50
1X50
4
1Z50
12.50
2,4,6-T richlorophenol
Cg/L
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4-Dich ion> phenol
Mg^
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4-Dimethylphenol
fg'L
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4-Dinitrophenol
Hg'"L
12.50
0.00
12.50
1X50
4
1X50
12.50
2-Chlorophenol
Mg/L
5.00
0.00
5.00
5.00
5.00
5.00
2-Methylphenol
Cg/L
5.00
0.00
5.00
5.00
4
5.00
5.00
2-Nitrophenol
Mg/'L
5.00
0.00
5.00
5.00
4
5.00
5.00
3,3'-Dich!orobenzidine
5.00
o.oo
5.00
5.00
4
5.00
5.00
4,6-Dinitro-2-methylphenol (DNOC)
fg/L
12.50
0.00
1X50
12.50
4
1X50
12.50
4-Chloro-3-niethylphenol
Pg/L
5.00
0.00
5.00
5.00
4
5.00
5.00
4-Methylpheriol
Mg'l-
5.00
0.00
5.00
5.00
4
5.00
5.00
4-Nitrophenol
WT-
12.50
0.00
1X50
1Z50
4
1X50
1X50
bis(2-EthylhexyI)phthalate
fgfl-
4.25
1.50
XOO
5.00
4
6.02
7.78
Butylbenzylphthalate
J»g/L
5.00
0.00
5.00
5.00
4
5.00
5.00
Dimethyl phthalate
Hg>1-
5.00
0.00
5.00
5.00
4
5.00
S.Ob
Di-n-octylphthalate
fg-'L
5.00
0.00
5.00
5.00
4
5.00
5.00
Pentachlorophenol (PCP)
t»g^L
12.50
0.00
1X50
12.50
4
1X50
12.50
Phenol
Hg^
5.00
o.oo
5.00
5.00
4
5.00
5.00
FOD - Frequency of detection
SD - Standard deviation
N - Number of samples counted
Lower Ottawa River SLRA
Page 4 of 8
October 2001
555-3763-001
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 (2000|).
River Segment 3
Chemical Units Mean SD Min Max N 95%UCL 95th percentile
Metals
Aluminum
Hgl-
1084.75
132.28
889.00
1170.00
4
1240.40
1396.04
Antimony
Hg"L
1.05
0.00
1.05
1.05
4
1.05
1.05
Arsenic
UgL
1.15
0.00
1.15
1.15
4
1.15
1.15
Barium
67.70
15.63
57.60
90.60
4
86.09
104.48
Cadmium
Mgl-
0.14
0.09
0.10
0.27
4
0.24
0.34
Chromium
MgL
2.23
0.60
1.80
3.10
4
2.93
3.63
Cobalt
0.77
0.42
0.25
1.20
4
1.26
1.75
C oppcr
f»g"L
9.38
1.40
8.30
11.40
4
11.02
12.67
iron
Hg'L
2140.00
515.95
1470.00
2620.00
4
2747.10
3354.21
Lead
figL
3.88
2.22
1.90
5.90
4
6.49
9.11
Manganese
f»g"L
162.80
174.17
46.20
415.00
4
367.74
572.68
Mercury
MgL
0.14
0.01
0.13
0.16
4
0.16
0.17
Nickel
6.13
2.28
4.30
9.20
4
8.81
11.49
Selenium
Hg'1*
3.73
1.79
1.10
5.10
4
5.83
7.94
Thallium
M-g/L
1.60
0.00
1.60
1.60
4
1.60
1.60
Vanadium
Kg1-
3.30
0.40
2.70
3.50
4
3.77
4.24
Zinc
Hg'1-
19.38
8.46
9.30
28.30
4
29.33
39.28
Conventional
.Ammonia
mg/L
1.00
1.80
0.09
3.70
4
3.12
5.24
Cyanide
6.08
5.57
2.90
14.40
4
12.63
19.18
Hardness
mg/L
350.25
69.43
310.00
454.00
4
431.94
513.64
pH (95°o UCL / 95% LCL)
-
7.58
0.12
7.48
7.71
3
7.78
7.23
Temperature
°C
21.13
0.06
21.10
21.20
3
21.23
21.30
Polyeyclic Aromatic Hydrocarbons
Benzo[a)anthracene
Hg-1-
5.00
0.00
5.00
5.00
4
5.00
5.00
Benzojajpyrene
HgL
6.25
2.50
5.00
10.00
4
9.19
12.13
Benzo(b]fluoranthene
fig'L
6.25
2.50
5.00
10.00
4
9.19
12.13
Benzo[g,h,i Jperylene
Hg'l-
6.25
2.50
5.00
10.00
4
9.19
12.13
Benzo(k]fIuoranthene
Hg'L
6.25
2.50
5.00
10.00
4
9.19
12.13
Chrysene
Mg'*L
5.00
0.00
5.00
5.00
4
5.00
5.00
Dibenzj a,h ) anthracene
6.25
2.50
5.00
10.00
4
9.19
12.13
Indeno[l,2,3-cdjpyrene
Mgl-
6,25
2.50
5.00
10.00
4
9.19
12.13
Pyrene
('gl-
5.00
0.00
5.00
5.00
4
5.00
5.00
Lower Ottawa River SLRA
Page 5 of 8
October 2001
555-3763-001
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 (2000J).
River Segment 3
Chemical
Units
Mean
SD
Min
Max
N
95% UCL
95th percentile
Pesticides
Atrazine
Hg'"L
5.00
0.00
5.00
5.00
4
5.00
5.00
Seniivolatile Organic Compounds
l,l'-Biphenyl
Vtfr-
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4,5-Trichlorophenol
Hg"L
12.50
0.00
12.50
12.50
4
1X50
12.50
2.4,6 -T richlorophenol
Mgl-
5.00
0.00
5.00
5.00
4
5.00
5 00
2,4-Dichlorophenol
Hg-'L
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4-Dimethylphenol
5.00
0.00
5.00
5.00
4
5.00
5.00
2,4-Dinitrophenol
Mg'L
1X50
0.00
12.50
1X50
4
1X50
12.50
2-ChIorophcnol
Hg'L
5.00
0.00
5.00
S.00
4
500
5.00
2-Methylphenol
fg-L
5.00
o.oo
5.00
5.00
4
5.00
5.00
2-Nilrophenol
^g'L
5.00
0.00
5.00
5.00
4
5.00
5.00
3,3'-Dichlorobenzidine
Cg^L
5.00
Q.00
5.00
5.00
4
5.00
5.00
4.6-Dinitri>-2-methylphenol (DNOC)
Cg^L
12.50
0.00
12.50
1250
4
1X50
12.50
4-Chloro-3-methylphenol
Cg'L
5.00
0.00
5.00
5.00
4
5.00
5.00
4-Melhylphenol
fg"L
5.00
0.00
5.00
5.00
4
5.00
5.00
4-Nitrophenol
Hg-T-
12.50
0.00
1X50
12.50
4
1X50
12.50
bis(2-Ethvlhexyl)phthaIate
Mg'l-
4.25
1.50
XOO
5.00
4
6.02
7.78
Butylbenzy Iphthalate
Hg'L
5.00
0.00
5.00
5.00
4
5.00
5.00
Dimethyl phthalate
I'g'L
5.00
0.00
5.00
5.00
4
5.00
5.00
Di-n-octy Iphthalate
t»g'"L
6.25
2.50
5.00
10.00
4
9.19
12.13
Pentachlorophenol (PCP)
Hgl-
12.50
0.00
12.50
12.50
4
12.50
12.50
Phenol
Ugl*
5.00
0.00
5.00
5.00
4
5.00
5.00
FOD - Frequency of detection
SD - Standard deviation
N - Number of samples counted
Lower Ottawa River SLRA
Page 6 of 3
October 2001
555-3763-002
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 12000]).
River Segment 4
Chemical Units Mean SD Min Max N 95% UCL 95th percentile
Metals
Aluminum
fg'L
1040.00
14.14
1030.00
1050.00
2
1103.14
1129.29
Antimony
Mg'L
1.68
0.88
1.05
2.30
2
5.62
7.26
Arsenic
Mgl-
1.15
0.00
1.15
1.15
2
1.15
1.15
Barium
60.90
2.12
59.40
62.40
2
70.37
74.29
Cadmium
0.10
0.00
0.10
0.10
2
0.10
0.10
Chromium
fg/L
1.75
0.35
1.50
2.00
o
3.33
3.98
CobaJt
0.71
0.07
0.66
0.76
2
1.03
1.16
Copper
I^ST-
8.35
1.63
7.20
9.50
2
15.61
18.62
Iron
Hg'T-
1810.00
14.14
1800.00
1820.00
2
1873.14
1899.29
Lead
Hg'T-
1.85
0.78
1.30
2.40
2
5.32
6.76
Manganese
54.05
17.32
41.80
66.30
2
131.39
163.43
Mercury
Kg1-
0.14
0.02
0.12
0.15
2
0.23
0.27
N'ickel
fg'T-
4.45
0.49
4.10
4.80
2
6.66
7.58
Selenium
Hg'T*
6.00
0.14
5.90
6.10
2
6.63
6.89
Thallium
Mg^
1.60
0.00
1.60
1.60
2
1.60
1.60
Vanadium
Hg'L
3.00
0.14
2.90
3.10
2
3.63
3.89
Zinc
Hg'L
10.80
5.80
6.70
14.90
2
36.69
47.41
Conventionals
Ammonia
tng/L
0.04
0.06
0.00
0.08
2
0.31
0.42
Cyanide
Mg^
3.10
0.14
3.00
3.20
2
3.73
3.99
Hardness
mg-L
316.50
4.95
313.00
320.00
2
338.60
347.75
pH (95% t'CL / 95% LCL)
-
7.61
0.05
7.57
7.64
2
7.83
7.29
Temperature
°C
20.50
0.14
20.40
20.60
2
21.13
21.39
Polycyclic Aromatic Hydrocarbons
Benzofajanthracene
Hg/L
7.50
3.54
5.00
10.00
2
23.28
29.82
Benzo(a]pyrcne
fg'1-
7.50
3.54
5.00
10.00
2
23.28
29.82
Benzo|bJfluoranthene
fg'L
7.50
3.54
5.00
10.00
2
23.28
29.82
Benzo[g,h,i]pcr>iene
Hg'T-
7.50
3.54
5.00
10.00
2
23.28
29.82
Benzo(k]fluoranthene
fg'L
7.50
3.54
5.00
10.00
2
23.28
29.82
Chrysene
m1^
7.50
3.54
5.00
10.00
2
23.28
29.82
Dibenzja.hjanthracene
Mg'1-
7.50
3.54
5.00
10.00
2
23.28
29.82
Indeno[l,2,3-cd}pyrene
Mg^
7.50
3.54
5.00
10.00
2
23.28
29.82
Pyrene
Mg-L
7.50
3.54
5.00
10.00
2
23.28
29.82
Lower Ottawa River SLFL4
Page 7 of 8
October 2001
555-3765-001
-------
Table A-3. Summary statistics for measured chemical concentrations in surface water (Data from Inventory 20 J2000]).
River Segment 4
Chemical Unite Mean SD Min Max N 95%UCL 95th percentile
Pesticides
Atrazine fig'L 5.00 0.00 5.00 5.00 2 5.00 5.00
Semivolatile Organic Compounds
U'-Biphenyl jig/L 7.50 3.54 5.00 10.00 2 23.28 29.82
2.4.5-Trichlorophenol fig/L 18.75 8.84 1 2.50 25.00 2 58.21 74.56
2.4.6-Trichlorophenol Hg/L 7.50 3.54 5.00 10.00 2 23.28 29.82
2,4-DichIorophenoI jig/L 7.50 3.54 5.00 10.00 2 23.28 29.82
2,4-Dimethy Iphenol ng'l 7.50 3.54 5.00 10.00 2 23.28 29.82
2,4-Dinitrophenol (ig/L 18.75 8.84 12.50 25.00 2 58.21 74.56
2-Chlorophenol jig/L 7.50 3.54 5.00 10.00 2 23.28 29.82
2-Methylphenol ugL 7.50 3.54 5.00 10.00 2 23.28 29.82
2-Nitrophenol fjg'L 7.50 3.54 5.00 10.00 2 23.28 29.82
3,3'-Dichlorobenzidine (ig/T. 7.50 3.54 5.00 10.00 2 23.28 29.82
4,6-Dinilro-2-methylphenol (DNOC) jig/L 18.75 8.84 12.50 25.00 2 58.21 74.56
4-Chloro-3-methylphenol ng/L 7.50 3.54 5.00 10.00 2 23.28 29.82
4-Methylphenol ^g/L 7.50 3.54 5.00 10.00 2 23.28 29.82
4-N'itrophcno! fig/L 18.75 8.84 12.50 25.00 2 58.21 74.56
bis(2-Ethylhexyl)phthalate jigL 6.50 4.95 3.00 10.00 2 28.60 37.75
B uty lbenzy Iphthalate jig/L 7.50 3.54 5.00 10.00 2 23.28 29.82
Dimethyl phthalate pg/L 5.00 0.00 5.00 5.00 2 5.00 5.00
Di-n-octy Iphthalate Hg/L 7.50 3.54 5.00 10.00 2 23.28 29.82
Pentachlorophenol (PCP) ng/L 18.75 8.84 12.50 25.00 2 58.21 74.56
Phenol (ig/L 7.50 3.54 J.00 10.00 2 23.28 29.82
FOD - Frequency of detection
SD - Standard deviation
N - Number of samples counted
Lower Ottawa River SLRA
Page 8 of 8
October 2001
555-3763-001
-------
APPENDIX B
Toxicity Data
-------
APPENDIX B - TOXICITY DATA
The toxicity data used for wildlife receptors and aquatic life are presented in this appendix. Issues
associated with the wildlife and aquatic life toxicity data are discussed separately below.
B.l WILDLIFE
The acute and chronic toxicity data for wildlife receptors (birds and mammals) are provided in Tables B-l
and B-2, respectively. As mentioned in Section 4.1, the toxicity data for mink were scaled for the relative
weight of mink to the laboratory test organism. The equation for body weight scaling, from Sample et al.
(1996), is as follows:
B.2 AQUATIC LIFE
The acute and chronic surface water toxicity data for aquatic life are presented in Table B-3; the sediment
guidelines used are provided in Table B-4.
The toxicity of PAH mixtures in surface water and sediment were also evaluated using the target lipid
narcosis model derived by Di Toro et al. (2000) and Di Toro and McGrath (2000). Di Toro et al. (2000)
provided a method for deriving PAH criteria for surface water and Di Toro and McGrath (2000) provided
a method for deriving PAH criteria for sediments and mixtures. The methods for these approaches,
summarized from their respective papers, are provided below.
PAHs are type I narcotic chemicals. Accordingly, the toxicity of a mixture of PAHs should be additive.
The target lipid model was developed to describe the toxicity of all type I narcotics. This model relates
narcotic lethality to the target tissue of an organism, in this case, the lipid. The partitioning of the
narcotics into the lipid is assumed to be species independent, but the threshold at which the narcotic
concentration in the lipid results in mortality is species specific and dependent on chemical differences.
However, the slope of the relationship between toxicity and the chemical's octanol-water partition
coefficient (Kow) is essentially constant between species. Using this relationship, species-specific body
burdens can be used to calculate water quality criteria using an approach analogous to the U.S. EPA's
current guidelines. Acute and chronic toxicity values using this approach are provided in Table B-2 of
Appendix B.
The target lipid model can also be applied to sediments and PAH mixtures. Using the chronic water-
based toxicity values described in the preceding paragraph, equilibrium partitioning (EqP) can be used to
calculate sediment guidelines. EqP theory holds that nonionic chemicals in sediment partition between
sediment organic carbon, interstitial water, and benthic organisms (Di Toro et al. 1991). At equilibrium,
if the concentration of one phase is known, the concentrations in the others can be predicted. Di Toro et
Parametrlx 555-3763-001 (01/03)
BW
NOAEL = NOAEL. —
IbwJ
(B-l)
Where:
NOAELw
NOAELt
BW,
BWw
No Observed Adverse Effects Level for mammalian wildlife receptor
No Observed Adverse Effects Level for mammalian test species
Body weight of mammalian test species
Body weight of mammalian wildlife receptor
Final Ecological SLRA of the Lower Ottawa River
October 2001
K t»ortnt\Jl6MHl-OOVSLKA R^>n\fmalSLltA^l doc
-------
al. (1991) reported that the biological responses of benthic organisms to nonionic chemicals in sediments
are different across sediments when the sediment concentrations are reported on a dry-weight basis, but
similar when the concentrations are normalized for the organic carbon content of the sediment.
Accordingly, the use of narcosis theory and EqP allows sediment guidelines to be readily developed for
nonionic chemicals, such as PAHs, with only data on the chemicals' Kow.
Param«tri*
Final Ecological SLRA of the Lower Ottawa River
B-2
iSS-3763-001 (01/03)
October 2001
JC faporWInal SlAA^vlekc
-------
REFERENCES - APPENDIX B
Ahdaya, S.M., P.V. Shah, and F.E. Guthrie. 1976. Thermoregulation in mice treated with Parathion,
Carbaryl, or DDT. Toxicol. Appl. Pharmacol. 35:575-580.
Ambrose, A.M., P S. Larson, J.F. Borzelleca, and G.R. Hennigar, Jr. 1976 Long-term toxicologic
assessment of nickel in rats and dogs. J. Food Sci.Tech. 13:181-187.
AQUIRE. 2000. AQUatic toxicity Information REtrieval database. Environmental Research Laboratory.
United States Environmental Protection Agency, Duluth, Minnesota. Available at:
http://www.epa.gov/ecotox/ecotox_search_driver.htm
ATSDR. 1989. Toxicological profile for pentachlorophenol. U.S. Department of Health and Human
Services, ATSDR, Atlanta, Georgia.
ATSDR. 1989. Toxicological profile for phenol. U.S. Department of Health and Human Services,
ATSDR, Atlanta, Georgia.
ATSDR. 1989. Toxicological profile for di-n-butyl phthalate. U.S. Department of Health and Human
Services, ATSDR, Atlanta, Georgia.
ATSDR. 1990. Toxicological profile for 2-methylphenol. U.S. Department of Health and Human
Services, ATSDR, Atlanta, Georgia.
ATSDR. 1991. Toxicological profile for cyanide. U.S. Department of Health and Human Services,
ATSDR, Atlanta, Georgia.
ATSDR. 1991a. Toxicological profile for selected PCBs (Aroclor-1260, -1254, -1248, -1242, -1232, -
1221, and -1016). U.S. Department of Health and Human Services, ATSDR, Atlanta, Georgia.
ATSDR. 1991b. Toxicological profile for aldrin/dieldrin. U.S. Department of Health and Human
Services, ATSDR, Atlanta, Georgia.
ATSDR. 1991c. Toxicological profile for heptachlor/heptachlor epoxide. U.S. Department of Health
and Human Services, ATSDR, Atlanta, Georgia.
ATSDR. 1992a. Toxicological profile for 4,4'-DDT, 4,4'-DDE, and 4,4'-DDD. U.S. Department of
Health and Human Services, ATSDR, Atlanta, Georgia.
ATSDR. 1992b. Toxicological profile for alpha, beta, gamma, and delta hexachlorocyclohexane. U.S.
Department of Health and Human Services, ATSDR, Atlanta, Georgia.
ATSDR. 1992c. Toxicological profile for methoxychlor. U.S. Department of Health and Human
Services, ATSDR, Atlanta, Georgia.
ATSDR. 1992d. Toxicological profile for vanadium. U.S. Department of Health and Human Services,
ATSDR, Atlanta, Georgia.
Parametrix 555-3763-00! (01/03)
Final Ecological SLRA of the Lower Ottawa River B-3 October 2001
K iwoHuog\J7i}\J7t3-OOJ 1SUA SlMj/1 doc
-------
ATSDR. 1993. Toxicological profile for endosulfan. U.S. Department of Health and Human Services,
ATSDR, Atlanta, Georgia.
ATSDR. 1994. Toxicological profile for mercury. U.S. Department of Health and Human Services,
ATSDR, Atlanta, Georgia.
ATSDR. 1997a. Toxicological profile for chlorophenols. U.S. Department of Health and Human
Services, Agency for Toxic Substances and Disease Registiy. Atlanta, Georgia.
ATSDR. 1997b. Toxicological profile for manganese. U.S. Department of Health and Human Services,
Agency for Toxic Substances and Disease Registiy. Atlanta, Georgia.
ATSDR. 1997c. Toxicological profile for 2,4-dinitrotoluene and 2,6-dinitrotoluene. U.S. Department of
Health and Human Services, Agency for Toxic Substances and Disease Registiy. Atlanta,
Geoigia.
Aulerich, R.J., R.K. Ringer, M.R. Bleavins, et al. 1982. Effects of supplemental dietary copper on
growth, reproductive performance and kit survival of standard dark mink and the acute toxicity of
copper to mink. J. Animal Sci. 55:337-343.
Battelle. 1980. Subchronic toxicity study: Naphthalene (C52904), B6C3F1 mice. Report to U.S.
Department of Health and Human Services, National Toxicology Program, Research Triangle
Park, North Carolina, by Battelle's Columbus Laboratories, Columbus, Ohio.
Bedford, C.T., D.H. Hutson, and I.L. NatofT. 1975. The acute toxicity of Endrin and its metabolites to
rats. Toxicol. Appl. Pharmacol. 33:115-121.
Begearmi, M.M., H E. Ganther, and M.L. Sunde. 1980. Toxicity of mercuric chloride in Japanese quail
as affected by methods of incorporation into the diet. Poult. Sci. 59(10):2216-2220.
Cain, B.W., and E.A. Pafford. 1981. Effects of dietary nickel on survival and growth of Mallard
ducklings. Arch. Environm. Contam. Toxicol. 10:737-745.
Carriere, D., K.L. Fischer, D.B. Peakall, and P. Anghern. 1986. Effects of dietary aluminum sulfate on
reproductive success and growth of ring doves. Can. J. Zool. 64:1500-5.
Cecil, H.C., J. Bitman, R.J. Lillie, G.F. Fries, and J. Verrett. 1974. Embiyotoxic and teratogenic effects on
unhatched fertile eggs from hens fed PCBs. Bull. Environ. Contam. Toxicol. 11:489-495.
Di Toro, D.M. et al. 1991. Technical basis for the equilibrium partitioning method for establishing
sediment quality criteria. Environ. Toxicol. Chan. 11 .1541-1583.
Di Toro, D.M., J.A. McGrath, and D.J. Hansen. 2000. Technical basis for narcotic chemicals and
polycylie aromatic hydrocarbon criteria. 1. Water and tissue. Environ. Toxicol. Chem. 19:1951-
1970.
Di Toro, D.M. and J.A. McGrath. 2000. Technical basis for narcotic chemicals and polycylic aromatic
hydrocarbon criteria. II. Mixtures and sediments. Environ. Toxicol. Chem. 19:1971-1982.
Paramatrix
Final Ecological SLRA of th* Lawt r Ottawa Rivtr
B-4
SSS-3763-001 (01/03)
Octobtr 2001
-------
Dieter, M.P., M.I. Luster, G.A. Boorman. C.W. Jameson, J.H. Dean,and J.W. Cox. 1983. Immunological
and biochemical responses in mice treated with mercuric chloride. Toxicol. Appl. Pharmacol 68:
218-228.
DOTN (Department of the Navy). 1997. Development of toxicity reference values as part of a regional
approach for conducting ecological risk assessments at naval facilities in California. DOTN, San
Bruno, California. 134p.Eco-SSL (Ecological Soil Screening Level). 2000a. Ecological soil
screening level guidance-wildlife TRVs. Appendix 4-6. Available at:
http.Wvvww.epa.aov/oerrpaKe/suDerfund/proerams/risk/. 79 pp.
Eco-SSL (Ecological Soil Screening Level). 2000. Ecological soil screening level guidance. Available
at: http:Wwww.epa.gov/oerrDage/superfund/proerams/risk/. 113 pp.
Edens, F., W.E. Benton, S.J. Bursian, and G.W. Morgan. 1976. Effect of Dietary Lead on Reproductive
Performance in Japanese Quail, Coturnix coturnix japonica. Toxicol. Appl. Pharmacol. 38:307-
314.
Eisler, R. 1985. Toxaphene hazards to fish, wildlife, and invertebrates: A synoptic review. U.S. Fish
and Wildlife Service, Laurel, Maryland. Biological Report No. 85:1.4.
Eisler, R. 1986. Polychlorinated biphenyl hazards to fish, wildlife, and invertebrates: A synoptic review.
U.S. Fish and Wildlife Service, Laurel, Maryland. Biological Report No. 85:1.7.
Eisler, R. 1988. Arsenic hazards to fish, wildlife, and invertebrates: A synoptic review. U.S. Fish and
Wildlife Service, Laurel, Maryland. Biological Report No. 85:1.12.
Eisler, R. 1989. Molybdenum hazards to fish, wildlife, and invertebrates: A synoptic review. U.S. Fish
and Wildlife Service, Laurel, Maryland. Biological Report No. 85:1.19.
Eisler, R. 1990. Chlordane hazards to fish, wildlife, and invertebrates: A synoptic review. U.S. Fish and
Wildlife Service, Laurel, Maryland. Biological Report No. 85 :1.21.
Environment Canada. 1995. Interim sediment quality guidelines: Soil and sediment quality section
guidelines division. Ecosystem Conservation Directorate Evaluation and Interpretation Branch,
Ottawa, Ontario.
Gersich, F.M., E.A. Bartlett, P.G. Murphy, and D.P. Milazzo. 1989. Chronic toxicity of biphenyl to
Daphnia magna Straus. Bull. Environ. Contain. Toxicol. 43:355-362.
HEAST (Health Effects Assessment Summary Tables). 1995. Office of Solid Waste and Emergency
Reponse, U.S. EPA. EPA/540/R-95/036.
Heinz, G.H., D.J. Hoffman, A.J. Krynitsky, and D.M.G. Weller. 1987. Reproduction in mallards fed
selenium. Environ. Toxicol. Chem. 6:423-433.
Hill, E. F. 1981. Inorganic and organic mercury chloride toxicity to coturnix: Sensitivity related to age
and quantal assessment of physiological responses. Ph.D. Thesis, Univ. Maryland, College Park.
221 pp.
Parametrix
Final Ecological SLHA of the Lower Ottawa River
B-5
155-3763-001 (01/03)
October 2001
K •mork*>%\3763\376i-0011SLM topertirtnalSlRA vl doc
-------
Hill, E. F. and M. B. Camardese. 1986. Lethal dietary toxicities of environmental contaminants and
pesticides to Coturnix. U.S. Fish and Wildlife Service. Tech. Report No. 2.
Hudson, R.H., M A. Haegele, and R.K. Tucker. 1979. Acute oral and percutaneous toxicity of pesticides
to mallards: correlations with mammalian toxicity data. Toxicol. Appl. Pharmacol. 47:451-460.
Hudson, R.H., R.K. Tucker, and M.A. Haegele. 1984. Handbook of toxicity of pesticides to wildlife.
U.S. Fish Wildl. Serv. Resour. Publ. 153. 90 pp.
Ingersoll, C.G., P.S. Haverland, E.L. Brunson, T.J. Canfield, F.J. Dwyer, C.E. Henke, N.E. Kemble, D.R.
Mount, and R.G. Fox. 1996. Calculation and evaluation of sediment effect concentrations for the
amphipod (Hyalella azteca) and the midge (Chironomus riparius). J. Great Lakes Res.
22(3):602-623.
Johnson, D., Jr., A.L. Mehring, J.R., and H.W. Titus. 1960. Tolerance of chickens for barium. Proc.
Soc. Exp. Biol. Med. 104:436-438.
Keplinger, M.L., O.E. Fancher, and J.C. Calandra. 1971. Toxicologic studies with polychlorinated
biphenyls. Toxicol. Appl. Pharmacol. 19:402-403.
Kostial, K. M. Blanusa, and T. Maljkovic. 1989. Effect of a metal mixture in diet on the toxicokinetics
and toxicity of cadmium, mercuiy and manganese in rats. Toxicol. Ind. Health 5(5):685-698.
Laskey, J.W., G.L. Rehnberg, J.F. Hein, and S.D. Carter. 1982. Effects of chronic manganese (MnsCM
exposure on selected reproductive parameters in rat. J. Toxicol. Environ. Health 9:677:687.
Lillie, R.J., H.C. Cecil, J. Bitman, G.F. Fries, and J. Verret. 1975. Toxicity of certain polychlorinated
and polybrominated efficiency of caged chickens. Poult. Sci. 54:1550-1555.
Linder, R.E., T.B. Gaines, and R.D. Kimbrough. 1974. The effect of polychlorinated biphenyls on rat
reproduction. Food Cosmet. Toxicol. 12:63-77.
Mackenzie, K.M. and D.M. Angevine. 1981. Infertility in mice exposed in utero to benzo(a)pyrene.
Biol. Reprod. 24:183-191.
Mackenzie, R.D., R.U. Byerrum, D.F. Decker, C.A. Hoppert, and R.F. Langham. 1958. Chronic toxicity
studies, II. Hexavaient and trivalent chromium administered in drinking water to rats. Am. Med.
Assoc. Arch. Ind. Health. 18:232-234.
Matuk, Y., M. Ghosh, and C. McCulloch. 1981. Distribution of silver in the eyes and plasma proteins of
the albino rat. Can J. Ophthalmol. 16:145-150.
Mehring, A.L., J.H. Brumbaugh, A.J. Sutherland, and H.W. Titus. 1960. The tolerance of growing
chickens for dietaiy copper. Poult. Sci. 39:713-719.
National Research Council (NRC). 1980. Mineral tolerance in domestic animals. National Academy of
Sciences Press, Washington, D.C.
Oak Ridge National Research Laboratory (ORNRL). 1996, Toxicological Benchmarks for Wildlife:
1996 Revision. ES/ER/TM-86/R3. Health Sciences Research Division, Oak Ridge, Tennessee.
Param*trlx
Final Ecological SLRA of (he Lower Ottawa River
B-6
SSS-3763-001 (01/03)
October 2001
£
-------
Ondreicka, R., E. Ginter, and J. Kortus. 1966. Chronic toxicity of aluminum in rats and mice and its
effects on phosphorus metabolism. Brit. J. Ind. Med. 23:305-313.
Ontario Ministry of the Environment and Energy. 1993. Guidelines for the protection and management
of aquatic sediment quality in Ontario. Prepared by D. Persaud, R. Jaagumagi, and A. Hayton,
Water Resources Branch, Ontario Ministry of the Environment and Energy. 24 pp. + figures.
U.S. EPA. 1999b. 1999 update of ambient water quality criteria for ammonia. Federal Register.
December 22, 1999 (Volume 64, Number 245), page 71974.
Patton, J.F. and M.P. Dieter. 1980. Effects of petroleum hydrocarbons on hepatic function in the duck.
Comp. Biochem. Physiol. 65C:33-36.
Perry, H.M., E.F. Perry, M.N. Erlanger, and S.J. Kopp. 1983. Cardiovascular effects of of chronic
barium ingestion. In: Proc. 17th Ann. Conf. Trace Substances in Environ. Health, Vol. 17.
University of Missouri Press, Columbia, Missouri.
Podowski, A.A., B.C. Baneijee, and M. Feroz. 1979. Photolysis of heptachlor and cis-chlordane and
toxicity of their photoisomers to animals. Arch. Environ. Contam. Toxicol. 8:509-518.
Ringer, R.K.. 1983. Toxicology of PCBs in mink and ferrets. Pages 227-240 in F.M. D'ltri and M.A.
Kamrin, editors. PCBs: human and environmental hazards. Butterworth Publishing, Woburn,
Massachusetts.
RTECS (Registry of Toxic Effects of Chemical Substances). 1995. On-line computer database. NIOSH:
U.S. Dept of Health and Human Services, Center for Disease Control.
RTECS (Registry of Toxic Effects of Chemical Substances). 1997. On-line computer database. NIOSH:
U.S. Dept of Health and Human Services, Center for Disease Control.
Sample, B.E., D.M. Opresko, and G.W. Suter II. 1996. Toxicological benchmarks for wildlife: 1996
Revision. U.S. Department of Energy, ES/ER/TM-86/R3.
Schafer, Jr., E.W., W.A. Bowels, Jr., and J. Hurblet, 1983. The acute and oral toxicity repellency and
hazard potential of 998 chemicals to one or more species of wild and domestic birds. Arch.
Environ. Contam. Toxicol. 12(3):355-382.
Schafer, Jr., E.W., and W.A. Bowles, Jr. 1985. Acute oral toxicity and repellency of 933 chemicals to
house and deer mice. Arch. Environ. Contam. Toxicol. 14(1): 111-129.
Schlicker, S.A. and D.H. Cox. 1968. Maternal dietary zinc, and development and zinc, iron, and copper
content of the rat fetus, J. Nutr. 95:287-294.
Schroeder, H.A. and M. Mitchener. 1971. Toxic effects of trace elements on the reproduction of of mice
and rats. Arch. Environ. Health 23:102-106.
Stahl, J.L., J.L. Greger, and M.E. Cook. 1990. Breeding-hen and progeny performance when hens are
fed excessive dietary zinc. Poult. Sci. 69:259-263.
Parametrix
Final Ecological SLRA of the Lower Ottawa River
B-7
555-3763-001 (01/03)
October 200J
K: W«**igU7
-------
Szebedinszky, C., J.C. McGeer, D.G. McDonald, and C.M. Wood. 2001. Effects of chronic Cd exposure
via the diet or water on internal organ-specific distribution and subsequent gill Cd updtake
kinetics in juvenile rainbow trout (Oncorhynchus mykiss). Environ. Toxicol. Chem. 20(3) 597-
607.
Tewe, O.O., and J.H. Maner. 1981. Long-term and carry-over effect of dietary inorganic cyanide (KCN)
in the life cycle performance and metabolism of rats. Toxicol. Appl, Pharmacol. 58:1-7
Tucker, R.K., and M.A. Haegele. 1971. Comparative acute oral toxicity of pesticides to six species of
birds. Toxicol. Appl. Pharmacol. 20(l):57-65.
U.S. EPA. 1980a. Ambient aquatic life water quality criteria for thallium. Office of Water, Regulations
and Standards, Criteria and Standards Division. United States Environmental Protection Agency,
Washington, D.C. EPA 440/5-80-074.
U.S. EPA. 1980b. Ambient aquatic life water quality criteria for polychlorinated biphenyls. Office of
Water, Regulations and Standards, Criteria and Standards Division. United States Environmental
Protection Agency, Washington, D.C. EPA 440/5-80-068.
U.S. EPA. 1980c. Ambient aquatic life water quality criteria for aldrin/dieldrin. Office of Water,
Regulations and Standards, Criteria and Standards Division. United States Environmental
Protection Agency, Washington, D.C. EPA 440/5-80-019.
U.S. EPA. 1980d. Ambient aquatic life water quality criteria for DDT. Office of Water, Regulations and
Standards, Criteria and Standards Division. United States Environmental Protection Agency,
Washington, D.C. EPA 440/5-80-038.
U.S. EPA. 1980e. Ambient aquatic life water quality criteria for heptachlor. Office of Water,
Regulations and Standards, Criteria and Standards Division. United States Environmental
Protection Agency, Washington, D.C. EPA 440/5-80-052.
U.S. EPA. 1980f. Ambient aquatic life water quality criteria for hexachlorocyclohexane. Office of
Water, Regulations and Standards, Criteria and Standards Division. United States Environmental
Protection Agency, Washington, D.C. EPA 440/5-80-054.
U.S. EPA. 1984. Health effects assessment for iron (and compounds). Office of Research and
Development. United States Environmental Protection Agency, Cincinnati, Ohio. EPA/540/1-
86-054.
U.S. EPA. 1986a. Quality criteria for water 1986. Office of Water, Regulations and Standards. United
States Environmental Protection Agency, Washington, D.C. EPA 440/5-86-001.
U.S. EPA. 1986b. Ambient aquatic life water quality criteria for toxaphene. Office of Water,
Regulations and Standards, Criteria and Standanls Division. United States Environmental
Protection Agency, Washington, D.C. EPA 440/5-86-006.
U.S. EPA. 1988. Ambient aquatic life water quality criteria for aluminum. Office of Water, Regulations
and Standards, Criteria and Standards Division. United States Environmental Protection Agency,
Washington, D.C. EPA 440/5-88-008.
Paramctrix
Final Ecological SLRA of the Lower Ottawa River
B-S
555-3763-001 (01/03)
October 2001
X JtrerffimJSLAA_vl.doc
-------
U.S. EPA. 1991. Water quality criteria summary chart. Office of Science and Technology, Health and
Ecological Criteria Division. Washington, D C.
U.S. EPA. 1993a. Sediment quality criteria for the protection of benthic organisms: Fluoranthene.
United States Environmental Protection Agency, Health and Ecological Criteria Division,
Washington, D C. EPA-822-R-93-012.
U.S. EPA. 1993b. Sediment quality criteria for the protection of benthic organisms: Acenaphthene.
United States Environmental Protection Agency, Health and Ecological Criteria Division,
Washington, D.C. EPA-822-R-93-013.
U.S. EPA. 1993c. Sediment quality criteria for the protection of benthic organisms: Phenanthene.
United States Environmental Protection Agency, Health and Ecological Criteria Division,
Washington, D C. EPA-822-R-93-014.
U.S. EPA. 1993d. Sediment quality criteria for the protection of benthic organisms. DieJdrin. United
States Environmental Protection Agency, Health and Ecological Criteria Division, Washington,
D.C. EPA-822-R-93-015.
U.S. EPA. 1993e. Sediment quality criteria for the protection of benthic organisms: Endrin. United
States Environmental Protection Agency, Health and Ecological Criteria Division, Washington,
D.C. EPA-822-R-93-016.
U.S. EPA. 1995a. Integrated risk information system (IRIS) on-line computer database. Information
system updated regulary by United States Environmental Protection Agency, Washington, D.C.
U.S. EPA. 1995b. Final water quality guidance for the Great Lakes system; final rule. Federal Register,
Vol. 60, No.56. March 23, 1995. pp. 15366-15425.
U.S. EPA 1995c. Office of Pesticide Programs. Environmental Effects Database (EEDB).
U.S. EPA. 1996. 1995 updates: Water quality criteria documents for the protection of aquatic life in
ambient water. Office of Water, U.S. Environmental Protection Agency, Washington, D.C.
EP A-820-B-96-001.
U.S. EPA. 1999. National recommended water quality criteria - correction. Office of Water, U.S. EPA.
EPA/822-Z-99-001.
U.S. FWS. 1964. Pesticide-wildlife studies. 1963: A review of Fish and Wildlife Service investigations
during the calendar year. FWS Circular 199.
Walsh, G.M., and G.B. Fink. 1972. Comparative toxicity and distribution of Endrin and Dieldrin after
intravenous administration in mice. Toxicol. Appl. Pharmacol. 23:408-416.
White, D.H., and M.T. Finley. 1978. Uptake and retention of dietary cadmium in mallard ducks.
Environ. Res. 17:53-59.
Parametrix 555-3763-001 (01/03)
Final Ecological SLRA of the Lower Ottawa River B- 9 October 200J
£ \workwrf\3763 U763-001\SLRA Rtport\fitulSmA_vI.doc
-------
Table B-l. Acute toxicity screening doses for wildlife.
Mammalian
Chemical
Test Test Species LD50 Mink normalized
Species body wt (kg) (tng/tg/day) LP50 (mg/tg/day)
M«**b
Antimony
Aisenic
Yjatiutn
Ber>iiium
Caii«!'um
t 'hI;>TlllU5^
C.opP«
Iron
Lea"1
^an&ancse
Mercury
Methyl Mercury
Nickel
Sckrinno
SiWei
Thallium
"Vanadium
Z.mc
Convent*0**
^mtnoma
Cyanic
pAH5
mouse
rat
mouse
guinea pig
mouse
mouse
rat
rat
mouse
mouse
rat
rat
rat
guinea pig
rat
rat
mouse
mouse
mouse
mouse
003
035
0.03
003
003
0.35
0.35
0.03
0.03
0.35
035
0.35
0.35
0.35
0.03
0.03
0.03
003
0.35
222
30'
3
50
69
36.8
42
750
69
360
>725 5
332
259
17
26
32
32
42
32
42
27
92.39
23 07*
1.25
2 87
15.32
32.30
576.87
28.72
149 82
55803
255.36
1992
20.00
2.46
13.32
17.48
13.32
17.48
2.08
Anthracene
Benzo(a)anthracene
Beazo(a)pyreni:
Benzo(b)fluoranthene
Renzofg.h.Operylene
Be nzo(k)fluoranthenc
Chrysene
Dibenzo(a,h)anthracene
mouse
mouse
mouse
mouse
mouse
mouse
0.03
0.03
0 03
003
003
0.03
8500
800
800
800
800
800
3537.52
332.94
332.94
332.94
33294
332.94
Lower 0/ta*-a River S/JIA
Pag11 of3
Acute Threshold*
Mammalian Avian
(mg/lcg/day) (rog/kg/day)
Test
Organisms References
46.20
23.07
0.62
25
1.44
7.66
16.15
288 44
1436
74.91
>55803
127.68
9.96
8.5
10.00
1.23
6.66
8.74
666
8.74
1.04
>3537 52
166.47*
166.47"
166 47'
166.47'
166.47'
2498 5
21
1254
50.6
1,108
>2250
128
96
10.5
>2250
12.9
mouse, quail RTECS1997. OPP1995
rat ATSDR1991
mouse, quail Sthafer and Bowies 1985, OPP 1995
guinea pig, quad RTECS 1997, OPP 1995
mouse RTECS 1997
mouse, chicken RTECS 1997
rat RTECS 1997
rat ATSDR 1990
mouse, quail RTECS 1997
mouse, quail FDA 1975, OPP 1995
rat, quail RTECS 1997, Hill and Camardese 1986
rat ATSDR 1997
rat. quail ATSDR 1994, Hill 1981
guinea pig, quail RTECS 1997
rat RTECS 1997
ret RTECS 1997
moose, quail RTECS 1997, OPP 1995
mouse Schafer and Bowles 1985
mouse ATSDR 1992
mouse, quail RTECS 1997, Schafer and Bowles 1985
rat/ kestrel
ATSDR 1991, HSDB 1995
mouse, red-winged
50.5' blackbird RTECS 1997, Schafer ctal 1983
mouse RTECS 1997
mouse RTECS 1997
mouse RTECS 1997
mouse RTECS 1997
mouse RTECS 1997
July 2001
555-3763-001
-------
Table B-l. Acute toxicity screening doses for wildlife.
Test
Chemical Species
Fluoranlhenc rat
IndenoCi^-cdjpyrene mouse
Phenanthrene mouse
Pyrene mouse
PCB*
ArocIorl242 rat
Aroclorl254 rat
Aroclor 1260 rat
PCB5 (Totai) mouse
Pesticides
4,4-DDD dog
4,4-DDE rat
4,4-DDT rat
Aldnn rat
delta-BBC
gamma-BHC (Lindane) rat
Chlordane rat
alpha-Chlordane
gam m a-Chlordane
cis-Nonachlor
trans-Nonachlor
Dieldnn rat
Endosuitan rat
Endnn Ketone
Heptachlor rat
Heptachlor epoxide rat
Oxychlordane
Semivolatile Organic*
1,1-Biphenyl
2,4,5 Trichlorophenol rat
Mammalian
Test Species LD50 Mink normalized
body wt (kg) (mg/kg/day) LD50 (mg/k^day)
0.35 2000 1538 32
0.03 800 332.94
0.03 700 291.33
0.03 800 332.94
0.35 4250 3268.93
0.35 842 647.63
035 1300 999.91
0.03 15 6.24
12.7 50 94.39
0.35 880 676.86
0 35 750 57687
0.35 49 37.69
0.35 88 67.69
0.35 83 63.84
0.35 5.3 4.08
0.35 100 76.92
0.35 72 55.38
0.35 60 46.15
0.35 2960 2276.72
Lower Ottawa River SLRA
Pag* 2 of 3
Acute Threshold^
Mammalian Avian Test
(mg/kg/day) (mg/kg/day) Organisms References
769 16 50 5" RTECS1997, Schafortal 1983
blackbird
166.47b - mouse RTECS 1997
mouse, red-winged
145 66 50.5* blackbird RTECS 1997, Schafer etal 1983
166 47b - mouse RTECS 1997
1634.47 150 rat, pheasant AT SDR 1991a, Eisler 1986
323.82 79 rat, pheasant Hudson etal 1984, Eisler 1986
499 95 91 rat, pheasant Eisler 1986
3.12 29 mouse, N. bobwhite Eisler 1986
47 19 290 dog, pheasent ATSDR 1992a, RTECS 1995
338 43 - rat ATSDR 1992a, RTECS 1995
288 44 297.5 mouse, quail Ahdaya et al 1976, USFW 1984
18 84 3 6 rat, starling ATSDR 1991b, RTECS 1995
rat, red-winged black
33.84 37.5 bird ATSDR 1992b, OFP1995
31.92 12 ret>pheasant Podowskietal 1979, Eisler 1990
204 11.7 rat,chukar Bedford et al 1975, Tucker et al 1971
3846 13 9 rat,mallard RTECS 1995
1.96 47 rat, quail ATSDR 1991c, RTECS 1995
2.96 - rat ATSDR 1991c, RTECS 1995
1138 36 nrt ATSDR 1997
July 2001
555-3763-001
-------
Table B-l. Acute toxicity screening doses for wildlife.
Mammalian
Acute Threshold1
Chemical
Test
Species
Test Species LD50 Mink normalized
body wt (kg) (mg/kg/day) LD50 (mg/kg/day)
Mammalian
(mgdcgMay)
Avian
(mg/kg/day)
Test
References
2,4,6-Tnchlorophenol
2,4-Dichlorophenol
2,4-Dune thy Iphenol
2,4-Dinitrophenol
2-Chlorophenoi
2-Methylphenol
2-Nitrophcnol
3,3-Dichlorobenzidine
4,6-Dinitro-2-methylphenol
4-ChIoro-3-methylphenol
4-Methylphenol
4-Nitrophenol
bis(2-Ethylhexyl)phthalate
Butylbenzyiphthalate
Dimethylphthalate
Di-n-octylphthalate
Pentachlorophcnol
Phenol
rat
mouse
rat
rat
rat
mouse
0.35
0.03
0.35
0.35
0.35
035
0.35
003
30
346
1350
3820
1800
31000
50
300
23.07
144 00
1038.37
2938.19
1384.49
2384398
38.46
124.85
11.54
72 00
519 18
1469.10
692.24
1192199
19.23
62.43
57
57
314
rat NIOSH1985
mouse; red-winged ATSDR 19g7 et j j9g3
blackbird
rat
rat
ATSDR 1990
ATSDR 1997
rat / red-winged Diechmaan & Withenip 1944,
blackbird Schaefer et al 1983
rat NIOSH 1985
ret; quail
mouse
ATSDR 1989, COT* 1995
ATSDR 1989
1 Acute toxicity is the lethal dose to 50 percent of the organisms tested (LD50) divided by 2. This is consistent with EPA's guidance for aquatic LC50s
(Stephan et al 1985). If a LD50 was not available, a LDLo (the lowest concentration to cause deaths) was used.
"No effect level estimated using "surrogate" low molecular weight PAH.
bNo effect level estimated using "surrogate" high molecular weight PAH.
cLOAEL for decreased survival divided by 10.
- = Not available
Lower Ottawa River SLRs4
Pag* 3 of3
July 2001
355-3763-001
-------
Table &-2. Chronic toxicity screening doses for wildlife.
Mammalian
Chemical
Test Test Species NOAEL Mink normalized
Species body wt (kg) (mg/Va/day) NOAEL (BiK/lotAfay)
Metals
Alvromum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Qiromium
Cobalt
Copper
Iron
Lead
Manganese
Mercury
Methyl Mercury
Nickel
Selenii*n
Silver
Thalhctn
Vanadium
Zinc
CoavNitioMis
Ammonia
Cyanide
rat
rat
mouse
tat
rat
mouse
mouse
mouse
rat
rat
Tat
moise
0.35
0.35
0.3S
003
0.35
0.35
0.03
0.03
003
035
035
0.35
0.35
003
035
1.93
0.32
5.10
0.66
3.30
1.20
267
120.00
0.38
0.10
4000
2220
034
160 00
68.70
1.48
0.25
3.92
0.27
254
0.92
Ml
49.94
0.15
0.08
30.77
17.08
065
66.59
52.84
PAH*
Anthracene
Benzoic )anthrBcenc
BenzoOOpyrene
Benzo(b)fluoranthene
Betuo(&,h,i)perylei>e
Benzo(Jc)fliJoranthene
mouse
mouse
0.03
0.03
0.03
125.00
100
1.00
52.02
0.42
0.42
Lower Ottawa River SL/iA
Chrome Threshold x,i
Mammalian Avian
(mg/kgfttoy) (mgflcj^dgy^ Effect (Mstnmal, Bud) TertOypaw Reft
148
100
growth, reproduction
rat, ringed turtle do*e
USEPA 1999
0.052
-
lifespan
mouse
ORNL 1996
0.25
55
growth, growth
rat, mallard
Na*y BTAO1997
3.92
208
growth, mortality
rat, chicken
Idaaca at al 1960, Pwy otal 1983
0.27
-
lystem*: effects
mouse
Sdraada sodbMcfaener 1971
0.742
145
reproduction, reproducticsi
rat. mallard
ORNL 1996
2.54
1
growth, reproduction
rat, black dock
Mackenzie et al 1958, Sample etal 1996
0.92
1.3
growth, growth
rat, chicken
Nary BT AG 1997, EcoSSLs (USEPA) 2000
Ml
2.3
growth, growth
moiae, chicken
Nary BTAO 1997
49.94
-
tenitogenecity
mouse
USEPA 1984
0.15
385
mortality, reproduction
mouse, ncncnkeatrelSdsoedsr sod Mitchenar 1971, ORNL1996
68
997
reproduction, growth
rat, jepanese quail
ORNL 1996
0.027
0.039
mortality, reproduction
in ink, mallard
Navy BTAO 1997
0.0S
2.6
reproduction
rat /kestrel
ATSDR 1999. PesUl ami Linear 1972
30.77
65
reproduction, mortality
rat, Cotunix quail
Ambrose at allOT* USEPA 1999
0,154
0.57
reproduction, reproduction
rat, mallard
ORNL 1996^ Mary BTAO 1997
17.08
-
lyitemic effect*
rat
Mat* etal 1981
0006
-
reproduction
rat
ORNL 1996
0.65
11 4
reproduction, body wt
rat. mallard
ATSDR 1992, ORNL 1995
6659
17.2
survival, reproduction
movae, mallard
Schlicker sndCox 19S8. Navy BTAO 1997
5284
0.04
litter size, birth weight of
pups, mortality
rat, am en can kestrel Tewe sndMaacr 1981, USEPA1999
58.02*
o.«k
0.42fc
0.42'
280* systemic effects, mortality
reproduction
reproduction
reproduction
mouse
mouse
HEAST1995
Madcmrie wad Angevin* 1981
ORNL1996
Mackenzie nd Angerine 1981
Pagt I of 3
October 2001
355-3763-001
-------
Table B-2. Chronic toxicity screening doses for wildlife.
Mammalian
Chein ical
Teat Test Species NOAEL Mink normalized
Species body wt (kg) (mg/kg/day) NOAHL (mg^/day)
Chrysene
D \ ben zo( a, h )an tl ira c e ne
Fluor anthene
lndeno(l ,2,3-cdipyrene
Phenanthrene
Pvrene
mouse
mouse
mouse
mouse
mouse
mouse
0.03
0.03
0.03
0.03
003
0.03
100
1.00
125.00
1.00
125.00
75.00
0.42
0.42
52 02
0.42
52.02
31.21
PCBs
Aroclor 1242
Arodor 1254
Aroclc* 1260
PCB (total)
rat
rat
0.35
0.35
0.75
006
0.58
0.05
Pesticides
4,4-DDD
4,4-DDE
4,4-DDT
Aldrin
delta-BHC
gamma-BHC (Lindane)
Chloidane
alpha-Chlordane
gumma-Chlordane
c*j-NonachJor
trans-Nonachlor
Dieldnn
Endosulfan
Etidrin Ketone
Heptachlor
Heptachlor epoxide
Oxychlordane
rat
mouse
rat
dog
0.35
G.Q3
0.35
12.70
28 00
34,00
0.04
013
21.54
14 15
0.03
0.24
Semivolatilr Organic*
1,1-Biphenyl
2.4.5 Trichloropheriol
Lower Ottawa River SLR4
Chrcruc Threshold u
Mammalian Avian
(mg/kg/day) (mg/kg/day) Effect (Mammal, Bird) Test Organism References
0.42" - reproduction mouse Mackenzie and Angevine 1981
0.42fc - reproduction mouse Mackenzie and Angevin* 1981
52.02" 280* systemic effects, mortaiity mouse HEAST1995
0.42b - reproduction mouse Mackenzie and Angevine 1981
52.02* 280* mortality mouse, mallard Patton and Dieter 1980
31.21 - systemic effects mouse HEAST 1995
0.6 0.46* hatchability chicken Lillie et al 1975
0.58 0.18 litter size, hatchability rat, chicken Linder et al 1974, Cecil et al 1974
0.05 - survival of pups rat Keplinger etal 1971
0.09 egg production chicken Navy BTAG 1997
21.54 - development rat ATSDR 1992a
14.15 0.845 reproduction, mortality mouse, Coturux quail ATSDR 1992s, USEPA1999
0 03 0.003 fertility, reproduction rat, pelican ATSDR 1992», USEPA1995
0.154 - reproduction rat ORNL1996
0 014 0 56 kit mortality, growth, egg mink, quail Sample et al 1996
hatchability
6.15 2 reproduction rat, mallard ORNL 1996
19 21 reproduction, mortality ORNL 1996
0.015 0 077 reproduction rat, bam owl ORNL 1996
0.12 10 reproduction ret, partridge ORNL 1996
0.1 0 065 reproduction, mortality mink, Cotumix quail ORNL 1996
0.24 - pup survival dog USEPA 1995
Page 2 of 3
October 2001
555-3763-001
-------
Table B-2. Chronic toxicity screening doses for wildlife.
Mammalian Chrome Threshold ~
Chemical
Test
Species
Test Species
body wt (kR)
NOAEL
(mfc/kg/day)
Mink normalized
NOAEL (mR/k*/tfay)
Mammalian
(mn/Wday)
Avian
(mg/knAfay)
Effect (Mammal, Bird)
Test GtRanjam
References
2,4,6 Trichlorophenol
rat
0.35
120 00
92.30
92.3
tedded body wt
rat
ATSDR1997
2,4-Dichlorophenol
mouse
0,03
1300 00
541.03
541.03
_
reproduction
mouse
ATSDR 1992
2,4-Dimethylpfienol
-
-
-
.
.
-
-
-
2,4-Dinitropheno)
rat
035
60
4615
4615
-
reproduction
rat
ATSDR 1993
2-ChJorophenol
rat
0.35
3 00
2.31
2.31
.
reproduction
wt
RTBCS1995
2-MethyVphei»l
-
-
-
-
219
-
reproduction
mink
ORNL1995
2-Nitxophenol
-
-
.
.
-
-
3,3- Dichlorobenzidme
.
.
.
_
_
_
-
4,6-Dinitro-2-m«!thylphenol
-
-
.
-
.
_
.
-
4-Chloro-3-meUiylphenol
-
-
-
-
_
-
-
-
t-Methylpheno!
rat
0.35
450 00
346.12
346.12
-
reproduction
rat
ATSDR 1996
4-Nitrophenol
-
-
-
-
.
-
-
-
bis(2-Ethylhexyl)phthalate
-
-
-
-
7.6
1.1
reproduction
mouse, ringed dove
ORKL1996, IWcall 1974
Btfylbenzylphthalate
rat
0.35
159 00
122.30
122.3
-
increased Hver to body wt
ratio
rat
IRIS, USEPA, Jan 1994
Dimethylphthalate
rat
0.35
1000 00
769.16
769 16
Iritfaey effects
rat
HBAST1994
Di-n-octylphthalate
mouse
0.03
7500
3121.34
3121.34
.
reproduction
mouse
USHPA1999
Penlachlcrophcno}
-
-
-
-
0.185
4.03
reproduction, mortality
rat, Cotraix quail
ORNL1996^ USEPA 1999
Phenol
mouse
003
140 00
58.27
58.27
-
fetal body wt
mouse
ASTDR1989
1 The toxic effects Jevel represents the NOAEL. If the NOAEL was not available, it was estimated by dividing the LOAEL by a factor of 10.
2 Chronic screening values which do not show a mink NOAEL derivation were either already derived by the reference or were taken from a test with mink as the test specie*.
* No effect level estimated using "surrogate" LPAH.
k No effect level estimated using "surrogate" HP AH.
' A ctual constituent reported as A1232, A1242, A1248.
-" Not available.
Lower Ottawa River SLRA
Pag€ 3 of3
Octobtr 2001
3SS-3763-001
-------
Table B-3. Acute and chronic surface water toxicity screening Values for aquatic life.
Chemical
Acute1
Chronic*
Value (ug/L)
Comment
Value (ug/L)
Comment
Reference
Metals
Aluminum
750
-
87
-
USEPA 1988a
Antimony
88
as Antimony (ID)
30
as Antimony(III)
USEPA 1988b
Arsenic
340
-
150
-
OEPA 3745-1
Barium
7250
Lowest acute value divided by 2
1430
ACRoflO
Bicsingcr and Christcnsca 1972
Cadmium
4.5
Hardness dependent1
2.5
Hardness dependent1
OEPA 3745-1
Chromium
16
as Chrom 'mm(VT)
11
at Chnxnimn(VI)
OEP A 3745-1
Cobalt
555
Lowest acute value divided by 2
74
Ocomean of lowest NOEC St LOEC
Bicsinger and Christcnscn 1972, Lind et si 1978
Copper
14
Hardness dependent*
9.3
Hardness dependent1
OEPA 3745-1
Iron
-
-
1,000
-
USEPA 1986a
Lead
120
Hardness dependent1
6.4
Hardness dependent1
OEPA 3745-1
Manganese
27
Lowest acute value divided by 2
5.4
ACRoflO
AQU IRE 2000
Mercury
1.7
-
0.91
-
OEPA 3745-1
Nickel
470
Hardness dependent1
52
Hardness dependent1
OEPA 3745-1
Selenium
19.34
-
5
-
USEPA 1996, OEPA 3745-1
Thallium
700
Lowest acute value divided by 2
<40
Lowest chronic value
USEPA 1980a
Vanadium
310
Lowest acute value divided by 2
62
ACRoflO
Krishnalremari et al 1983
Zinc
120
Hardness dependent3
120
Hardness dependent3
OEPA 3745-1
Conventional*
Ammonia
36100
atpHof 7
4150
at pH of 7, temp, of 20° C
USEPA 1999b
Cyanide
22
Free cyanide
5.2
Free cyanide
OEPA 3745-1
PAHs
Bcnzo(a)anthrHcenc
9.6
Estimated FAV divided by 2
3.8
Estimated FCV
Di Toro ct al 2000
Benzo{a)pyrene
4.1
Estimated FAV divided by 2
1.6
Estimated FCV
Di Toto et al 2000
Benzo(b)fluoranthene
2.89
Estimated FAV divided by 2
1.1
Estimated FCV
DiToto et al2000
Bcnzo(ghi)perylene
1.88
Estimated FAV divided by2
0.74
Estimated FCV
Di Toro et al 2000
Benzo(k)fluoranthene
2.77
Estimated FAV divided by 2
1.09
Estimated FCV
Di Toco et al 2000
Chrysene
8.8
Estimated FAV divided by 2
3.47
Estimated FCV
Di Two et al 2000
Dibenz(a,h)anthracene
2.45
Estimated FAV divided by 2
0.48
Estimated FCV
Di Toro et al 2000
Indeno(l ,2,3-cd)pyrcne
2.38
Estimated FAV divided by 2
0.47
Estimated FCV
Di Ton et al 2000
Pyrcne
43.7
Estimated FAV divided by 2
17
Estimated FCV
Di Toro et al 2000
Pes tic ides
Atrazine
18.5
•
4.J
.
Solomon et al 1996
October 2001
Lower Ottawa River SLRA Page 1 of2 555-3763-001
-------
1 able B-3. Acufe and chronic surface water toxicity screening values for aquatic life.
Chemical
Acute'
Chronic
Value (u«/L)
Comment
Value (ug/L)
Comment
Reference
Semivolatile Organics
l,l'-Biphenyl
230
Set equal to chronic SV 5
230
MATC
Gersichetal 1989
2,4,5-Trichlorophenol
225
Lowest acute value divided by 2
45
ACRoflO
Buccaftuco et al 1981
2,4,6-Trichlorophenol
90
Lowest acute value divided by 2
18
ACRoflO
Yoahiolca et al 1986
2,4-Dichlorophenol
620
Lowest acute value divided by 2
<99.4
Lowest chronic value
Birge et al 1979, Hodson et al 1991
2,4-Dimethylphenol
1050
Lowest acute value divided by 2
210
ACRoflO
LeBlanc 1980
2,4-Di n iirophen ol
30
Lowest acute value divided by 2
6
ACRoflO
Daleketal 1980
2-ChIorophenoi
500
Lowest acute value divided by 2
100
ACRoflO
LeBlanc 1980
2-Methylphcnol
2500
Lowest acute value divided by 2
500
ACRoflO
Paifchurst et al 1979
2-Nitrophenof
800
Lowest acute value divided by 2
160
ACRoflO
Yoshioka et al 1986
J,3'-I)ichlorohctt/idirie
525
Lowest acute value divided by 2
105
ACRoflO
Brooke 1991
4,6-Dinitro-2-m eth ylphcn ol
33
Lowest acute value divided by 2
6.6
ACRoflO
Johnson and Finley 1980
4-Chloro-3-methylpheno]
458.5
Lowest acute value divided by 2
91.7
ACRoflO
USEPA 1995
4-Methylphcnol
700
Lowest acute value divided by 2
140
ACRoflO
Parkhunt el at 1979
4-Nitrophenol
550
Lowest acute value divided by 2
110
ACRoflO
Yoshioka et al 1986
bis(2-Ethylhexyl)phthalate
400
Solubility limit
360
-
USEPA 1987
Butylbenzylphthalale
390
Lowest acute value divided by 2
60
Lowest chronic value divided by 2
Adams et al 1995, USEPA 1978
Dimethylphthalate
16500
Lowest acute value divided by 2
14859
Geomean of NOEC and LOEC
LeBlanc 1980, Rhodes et al 1995
Di-n-octylphthalate
-
-
93.2
Geomean of NOEC and LOEC
Rhodes et al 1995
Pentachloropheno I
14
at pH of 7.5
11
at pH of 7.5
OEPA 3745-1
Phenol
22.5
Lowest acute value divided by 2
4.5
ACRoflO
Stephenson 1983
1 For OEPA WQC, Outside Mixing Zone Maximujj).
2 For OEPA. WQC, Outside Mixing Zone Average,
3 Hardness-dependent criteria arc normalized to a hardness of 100 mg/L in this tabic. Criteria are normalized to the site-specific hardness for hazard quotient calculations.
4 Final acute values derived prior to 1985 are divided by 2, for consistency with current USEPA methods.
5 Set equal to chronic SV because the LC50 for this species, divided by two, was less than the chronic SV.
FAV - Final Acute Value.
FCV = Final Chronic Value.
Lower Ottawa River SLRA
Page 2 of2
October 2001
555-3763-001
-------
Table B-4. Sediment toxicity screening values for aquatic life.
Ingcraoll ct al. (1996)
ERL
ERM
TEL
PEL
Chemical
(ug/g - dry)
(ug/g - dry)
(ug/g - dry)
(ug/g - dry
Metals
Aluminum
—
38,000
—
Antimony
—
—
—
—
Arsenic
13
50
11
48
Barium
—
—
—
Beryllium
—
_
—
—
Cadmium
0.7
3.9
0.58
3.2
Chromium
39
270
36
120
Cobalt
—
—
—
Copper
41
190
28
100
Iron
200,000
280,000
190,000
250,000
Lead
55
99
37
82
Manganese
730
1,700
630
1,200
Mercury
—
—
—
—
Nickel
24
45
20
33
Selenium
—
—
—
—
Silver
—
—
—
Thallium
—
Vanadium
—
—
—
Zinc
110
550
98
540
Conventionats
Cyanide
—
—
—
—
P AH J
Anthracene
0.01
0.14
0.01
0.17
Benzo[a]anthracene
0.019
0.3
0.016
0.28
Benzo{aIpyrene
0.084
0.47
0.032
0.32
Bcnzo[b)fluoranthenc
_
—
—
—
Benzo[g,h,i]perylene
0.013
0.28
0.016
0.25
Bcnzo|k)fluoranthene
—
—
—
—
Chiysene
0.03
0.5
0.027
0.41
Dibenz(a,h [anthracene
0.01
—
0.01
—
Fluoranthene
0.033
0.18
0.031
0.32
indenojl ,2,3-c,d]pyrene
0.03
0.25
0.017
0.24
Phenanthrene
0.027
0.35
0.019
0.41
Pyrene
0.04
0.35
0.044
0.49
Lower Ottawa River SLRA
IXTooctat
Environment Canada (1995) Ontario (1993) USEPA (1993fr-c) QWW)
TEL PEL LEL SEL1 SQC* cajo
(ugfe- dry) (ug/g-dry) (ug/g-dry) Wg-*T) (Bg/g-
-------
Table B-4. Sediment toxicity screening values for aquatic life.
Chemical
ERL
(ug/g - dry)
Ingersoll el al. (1996)
ERM
(ug/g - dry)
TEL
(ug/g - dry)
PEL
(ug/g. dry)
Environment Canada (1995)
TEL PEL
(ug/g • dry) (ug/g - dry)
Ontario (1993)
LEL
(ug/g - dry)
SEL'
(ug/g-dry)
USEPA(1993a-c)
SQC'
(ug/g - dry)
Di Toro et al
(2000)
Csqa
(nag/Kg OC)
PCBs
Axoclor 1016
Arocior 1242
Arocior 1254
Aroclor 1260
Total PCBs
Pesticides
4,4'-DDD
4,4'-DDE
4,4 -DDT
Aldrin
alpha-Chlordane
gamma-Chlordane
dclU-BHC
Dieldrin
Endosulfan
Endrin Ketone
f ieptachlor
Hcptachlor epoxide
Seniivolatile Orgiuiics
2,4,6-T ribrom ophenol
2-Ffuorobiphenyl
2-FluorophenoI
his(2-Ethylhe\yl)phlhalat6
Di-n-octylphthalate
0.0S
0.73
0.032
0.24
0.0341
0.00354
0.00142
0.00698
0.00285
0.0006
0.277
0.00851
0.00675
4.45
0.00667
0.00274
0.007
0.06
0.005
0.07
0.008
0.005
0.007
0.002
0.002
0.005
53
34
24
530
6
19
12
8
91
11
Values for PCBs, organochlorines, and PAHs arc normalized for organic carbon.
ERL - Effects range-low
ERM = Effects range-median
TEL = Threshold effect level
PEL = Probable effect level
LEL = Lowest effect level
SEL — Severe effect level
SQC = Sediment quality criteria
Lower Ottawa River SLRA
Page 2 of 2
October 2001
555-3763-001
-------
Table B-5. Residue-based tissue toxicity screening values for fish.
Chemical
Sjjecw
Whole Body Tissue
Residue Threshold
Endpoint (nig/kg - wet)
Comment
Reference
Metals
Arsenic
Cadmium
Lead
Mercury
Selenium
PCBs
PCB Aroclor 1242
PCB Aroclor 1260
Tout PCBs1
Pesticides
4,4'-DDD (p.p'-)
4,4'-DDE (p,p'-)
4,4'-DDT (p,p'~)
Total DDT • Metabolites
A1 drin
alpha- Chlordane
gamma-Chlordanc
cis-Nonachlor
Dieldrin
[alpha, gammaj-Chlordane'
Heptachlor
Heptachlor epoxide
Oxychlordane
trans-Nonachlor
Rainbow trout (Oncorhynchus mykiss )
Brook trout (Salvelinus fontinalis )
Brook trout (Salvelinus fontinalis )
Rainbow trout (Oncorhynchus mykiss )
Bluegill (Lepomis macrochirus)
Lake trout (Salvelinus namaycush )
Rainbow trout (Oncorhynchus mykiss )
Survival
Growth
Hatchability
Growth
Larval mortality
Survival
Rainbow trout (Oncorhynchus mykiss ) Survival
Survival
1.7
0.2S
0.37
8.6
2.25
.53
1.27
1.76
at5°C
McGcachy sad Dixon 1990
Bcnoit et al. 1976
Holcofnbe et al. 1976
Rodgcn and Beamish 1982
as methvl mercurv
EC 10 calculated from multiple studies Deforest etaL 1999
Berlin etaL 1981
Hopkins etaL 1969
Shubat and Curtis 1986
1 Total PCBs - sum of A1242 and A1260 concentrations.
1 [alpha, gammaJChlordanc - sum of alpha and gamma Chlordane isomer concentrations.
3 Based on the assumption that methyl mercury is the predominant mercury species found in fish tissue.
EC 10 = 10% effect concentration.
Lower Ottawa River. SLRA
Page 1 of 1
October 2001
5S5-3763-001
-------
APPENDIX C
Hazard Quotients
-------
APPENDIX D
Sediment HQ Maps
-------
Table C-J. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
___^SAP«cimtile>Sedjm2j>CanceiitiBtiOT;_Sto8.8
Metal*
Aluminum
6927.782
7609.768
5694.273
5660.151
Aatmoay
0.499
1.017
0.848
0.276
Ancnie
5.392
4.206
17.131
6.361
Barium
64.654
99.044
103.884
185.084
Bcryllnm
0.340
0.386
0.354
0.432
Cadmium
1.631
1.330
2.961
1.454
Chromium
43.866
42.904
107.958
89.468
Cobalt
5351
5.535
4.392
3.788
Caliper
61.737
39.034
62.104
63.539
Iran
12571.852
13949.221
11820.882
10414.292
Lead
58.569
176.144
15135.994
197.251
Mutgaacac
222.179
259.934
226.883
207.152
Mercury
0.146
0.168
0.633
0.132
Methyl Mercury
-
-
-
-
Nickel
26.624
26.521
24.803
12.371
Sefcwaat
1.374
0.869
1.637
3.629
Silver
0.473
0.705
1.350
7.108
Thallium
3.042
3.385
2368
4.349
Vanadium
15.260
16.745
13.492
16.155
Zinc
140.406
165.516
192.507
412.690
Amasoeia
.
.
Cyanide
0.140
0.159
0.393
1.867
FAHa
AliOMK
2.567
2.168
3.574
8.868
Beazo(a}M>thraoenc
2-590
2321
1.228
5.027
Bcazofajpyreac
Z592
2.094
1.055
5.486
Bes^o{b]fiuoranllicne
2.534
1.670
1.454
6.251
Bcazofg^Mlperylcne
Z587
1.484
3.747
3.845
Be»ao{klflnoomrtvmf
2.619
2.243
1.433
6.931
Chryseac
2.664
1.730
1.505
7.697
Dhn(aJl)ailb«MK
2.707
2.348
3.574
8.779
Ftuoraotkcac
3.393
3.556
2.795
17.434
Lower Ottawa River SLRA
Page 1 of 12
95th Percentile Surface Water Concentration (^ig l-)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
3464.15
2364.92
1396.04
1129.29
1.05
1.05
1.05
7.26
2.98
4.93
1.15
1.15
67.32
77.80
104.48
74.29
0.27
0.10
0.34
0.10
6.39
5.01
3.63
3.98
1.87
1.87
1.75
1.16
14.14
11.70
1Z67
18.62
5686.68
4935.41
3354.21
1899.29
9.78
9.66
9.11
6.76
103.44
133.56
572.68
163.43
0.17
0.20
0.17
0.27
9.63
9.14
11.49
7.58
8.12
8.63
7.94
6.89
3.72
1.60
1.60
1.60
8.69
6.68
4.24
3.89
31.12
26.99
39.28
47.41
0.30
0.36
5.24
0.42
6.61
6.26
19.18
3.99
5.00
5.00
5.00
29.82
8.65
5.00
12.13
29.82
8.65
5.00
12.13
29.82
8.65
5.00
12.13
29.82
8.65
5.00
12.13
29.82
5.00
5.00
5.00
29.82
8.65
5.00
12.13
29.82
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
95th Percentile Sediment Concentration, Study 20 (mg/lcg-wet)
Chemical RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Indcno[l ,2,3-cd|pyrene
2.549
2.020
0.985
3.891
Phenanthrene
2.706
2.506
3.695
5.997
Pyrcnc
3.125
2.934
2.414
10.759
PCBa
PCB Aroclor 1242
0.242
1.862
2.210
2.075
PCB Aroclor 1260
0.047
0.069
0.094
0.528
PCB (total)1
0.289
1.931
2.304
2.603
Pesticide*
4,4-DDD Cp,p'-)
0.009
0.013
0.030
0.064
4,4-DDE (p,p'-)
0.009
0.019
0.031
0.035
4,4-DDT (pj>'-)
0.002
0.002
0.010
0.014
Aldrin
0.008
0.053
0.034
0.009
alpha-Chlordane
0.003
0.004
0.011
0.018
cis-Nonachlor
-
-
-
-
d-BHC
0.001
0.006
0.013
0.001
Dicldrin
0.009
0.018
0.012
0.013
Endosulfan II
0.002
0.011
0.014
0.028
Endrin ketone
0.002
0.004
0.006
0.036
gamma-Chlordane
0.009
0.011
0.013
0.007
[alpha, gammajChlordanc^
0.012
0.01 J
0.024
0.025
Heptachlor
0.003
0.006
0.003
0.001
Heptachlor epoxide
0.010
0.046
0.027
0.015
Oxychlordane
tranj-Nonachlor
Semtvolatile Organic*
l.l'-Biphenyl
2-Ch loroph cnoi
2.4.5-Trichlorophenol
2.4.6-Trichlorophcnol
2,4-Dichlorophenol
2,4-Dimethylphenol
2,4-DinitrophenoI
2-Methylphenol
Lower Ottawa River SLRA
Page 2 of 12
95th Percentile Surface Water Concentration (ng/L)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8.8
8 65 5.00 12.13 29.82
5.00 5.00 5.00 29.82
5.00
5.00
5.00
29.82
5.00
5.00
5.00
29.82
12.50
12.50
12.50
74.56
5.00
5.00
5.00
29.82
5.00
5.00
5.00
29.82
5.00
5.00
5.00
29.82
12.50
12.50
12.50
74.56
5.00
5.00
5.00
29.82
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
95th Percentile Sediment Concentration, Study 20 (mg/kg-wct) 95th Percentile Surface Water Concentration (ng/L)
Chemical
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM>8.8
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM >8.8
2-Nitrophcaol
_
_
.
5.00
5.00
5.00
29.82
3,3'-Djchlorobcnzidinc
- '
-
-
-
5.00
5.00
5.00
29.82
4,6-Dinitio-2-methyipiienol
-
-
-
-
1X50
12.50
12.50
74.56
4-Chloro-3-methylphenol
-
-
-
-
5.00
5.00
5.00
29.82
4-Methylphenol
2.668
1252
3.574
6.251
5.00
5.00
5.00
29.82
4-N'ctrophenol
-
-
-
-
12.50
12.50
12.50
74.56
b»(2-Ethylhexyl)phth»Ulr
2.559
5.103
3.643
21.002
5.00
7.78
7.78
37.75
Butyibcnzylphth*lalc
2.668
2.215
3.574
6.251
5.00
5.00
5.00
29.82
Dimethyl pfcthalatc
-
-
-
-
5.00
5.00
5.00
5.00
D»-g-ootylphfhala?e
2.668
3.170
3.866
1.950
8.65
5.00
12.13
29.82
Peataohlarophcnol
-
-
-
-
12.50
12.50
12.50
74.56
Phenol
-
-
-
"
5.00
5.00
5.00
29.82
' - FCB (total) - ram of A1242 and A1260 concentration*
2 - [alpha, gammaJChlordanc = turn of alpha and gamma Chlordanc isomer concentration!
Lower Ottawa River SLRA
Page 3 of 12
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
Chemical
9Sth Percentile Tissue Concentration (mg/kg-wct)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Metab
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Chromium
Cobalt
Copper
iron
Lead
Manganese
Mercury
Methyl Mercury
Nickel
Selenium
Silver
Thallium
Vanadium
Zinc
0.020
0.013
0.343
0.012
0.012
1.684
0.020 0.069 0.020 0.162
0.016 0.035 0.029 0.083
0.516
0.057
0.057
0.108
1.314
0.039
0.039
1.887
0.987
0.059
0.059
1.006
2.482
0.129
0.129
1.203
Canventioaab
Ammonia
Cyanide
PAH*
Anthracene
Benzo[a]anthraoene
Benzo[a)pyrenc
Bcnzofbjfluoranthene
Beruo[gJi,i}perylene
Benzo[k)fluonmthene
Chryaene
Dibenzfajijanthracenc
Fluoranthene
Lower Ottawa Rivar SLRA
Pago 4 of 12
(Estimated)
95th Percentile Invertebrate Tissue Concentration (mg/kg-wet)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8.8
0.857
0.776
0.749
0.711
0.734
0.753
0.803
0.765
1.153
0.790
0.779
0.692
0.563
0.468
0.749
0.656
0.704
1.422
0.914
0.271
0.232
0.315
0.789
0.317
0.377
0.755
0.633
1.590
0.850
0.887
1.000
0.610
1.102
1.291
1.302
3.074
October 2001
555-3763-001
-------
Table C-I. Acute hazard quotients for wildlife receptors in die lower Ottawa River.
93th Percentile Tiime Concentration (mg/kg-vret)
r-w.;,-! rm 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
h4on(1^3-et)roe
PhenandueDC
Pyreac
PCB.
PCB Arocior 1242
0.956
3.572
3.059
2.939
0.040
PCB Aroolor 1260
0.164
0.561
0.218
0.122
0.055
PCB (total)1
1.120
4.133
3.277
3.061
0.095
fuDiHn
4,4'-DDD (p,p'-)
0.030
0.056
0.072
0.081
0.098
4,4'-DDE (pj)'-)
0.084
0.205
0.145
0.120
0.424
4,4-DDT 8.8
0.683 0.595
0.923 0.953
1.056 1.194
0.288 2.308
0.057 0.081
0.345 Z389
0.010 0.015
0.0U 0.021
0.002 0.003
0.009 0.063
0.003 0.005
0.001 0.006
0.010 0.021
0.002 0.011
0.002 0.005
0.010 0.014
0.013 0.019
0.003 0.006
0.012 0.055
0.230 0.581
0.927 1.124
0.583 1.946
1.464 1.048
0.072 0.260
1.536 1.307
0.020 0.030
0.023 0.016
0.008 0.007
0.027 0.005
0.008 0.008
0.008 0.000
0.008 0.007
0.009 0.013
0.004 0.017
0.009 0.003
0.017 0.011
0.002 0.000
0.017 0.008
-------
Table C-l. Acute hazard quotients for wildlife receptors in die lower Ottawa River.
(Estimated)
9.5th Percentile Tissue Concentration (mg/kg-wct) 95th Percentile Invertebrate Tissue Concentration (mg/Vg-wet)
Chemical RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM6.5-8.8 RM>8-8 RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8.8
2-Nitrophcnol
3,3'-DichIorobcnzidine
4,6-Dinitro-2-methylphenol
4-Chloro-3-methylphenol
4-Mcthylphenol
4-Nitrophcnol
bii(2-£thylhexyl)phthalate
Butylbenzylphthalate
Dimethyl pltthalate
Di-n-octylphthabtc
Pentachlorophenol
Phenol
' - PC8 (total) = «um of A1242 and i
1 - [alpha, gammaJChlordane = sum •
1.130
0.819
0.878
1.343
1.059
2.063
0.788
1.881
1.143
0.893
0.888
1.477
1.457
3.694
1.131
0.422
Lower Ottawa River SLRA
Page 6 of 12
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the Iowa* Ottawa River.
Acatc Wildlife Hazard Quotient* for the Bald Eagle Hazard Quotients for the Common Tern
Screening Doae
(mg/lcg/day) RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8 RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8.8
n.—in«l M«—"I Bird Combined Combined Combined Combined Combined Combined Combined Combined Combined Combined
Aluminum
Antimony
Ancaio
Beryllium
Cobalt
Copper
Iron
Lead
Monvy
Methyl Mercury
Nickel
Silver
Zme
46.2
23.07
0.62
25
1.44
7.66
16.15
288.44
14.36
74.91
>558.03
127.68
9.96
8.5
10
1.23
6.66
8.74
6.6
8.74
2498.5
21
1254
50.6
1108
>2250
128
9.6
10.5
>2250
12.9
3.39E-03 3.70E-03 2.77E-03 2.75E-03
4.27E-04 3.64E-04 1.38E-03 4.82E-04 9.27E-04
6.40E-05 9.73E-05 1.03E-04 1.80E-04
6.90E-05 7.08E-05 1.55E-04
6.76E-05
6.82E-03
8.77E-04
1.89E-05
1.38E-04
4.28E-05
7.55E-03
2.15E-03
Z17E-05
6.49E-04
6.79E-05
6.38E-03
1.44E-01
8.01E-05
4.50E-04
1.03E-04 1.97E-04
6.97E-05
5.61E-03
2.79E-03 2.34E-03
1.75E-05
6.73E-04
Z53E-07 3.78E-07 7.23E-07 3.81E-06
1.32E-02 1.55E-02 1.81E-02 3.87E-02
1.48E-03
1.71E-02 1.87E-02 1.40E-02 1.39E-02
2.16E-03 1.83E-03 6.97E-03 2.44E-03 4.69E-03
3.21E-04 4.89E-04 5.15E-04 9.07E-04
3.49E-04 3.58E-04 7.84E-04 5.23E-04 9.98E-04
3.41E-04 2.16E-04 3.43E-04
3.44E-02 3.81E-02 3.22E-02
4.44E-03 1.09E-02 7.28E-01
3.52E-04
2.83E-02
1.41E-02 1.18E-02
9.48E-05 1.09E-04 4.05E-04 8.70E-05
7.01E-04 3.29E-03 2.28E-03 3.4IE-03 7.49E-03
1.28E-06 1.91E-06
6.67E-02 7.85E-02
3.66E-06
9.14E-02
1.93E-05
1.96E-01
Cyanide
FAHa
BeazofaJmAiaocac
Boio(i|i}icw
Baizo{b)ffaoranthcnc
BaaltMpajieK
BeazofkJQooraathcac
Cbyieae
Diben7[a,hlanthraca>c
FtaratkM
1.04
>3537.52
166.47
166.47
166.47
166.47
166.47
796.16
50.5
50.5
1.97E-04 2.02E-04 5.62E-04 1.19E-03
6.I3E-05 5.17E-05 8.53E-05 2.12E-04
8.10E-05 8.49E-05 6.67E-05 4.16E-04
8.13E-04 8.49E-04
2.32E-03
4.10E-04 4.30E-04 3.38E-04
5.93E-03
3.10E-04 2.62E-04 4.32E-04 1.07E-03
2.11E-03
Lower Ottawa River SLRA
Page 7 of 12
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
Acute Wildlife Hazard Quotient! for the Bald Eagle Hazard Quotients for the Common Tern
Screening Dose
(mg/kg/day) RM0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8 RM 0-3.2 RM 3.2-4.9 RM4.9-6.S RM 6.5-8.8 KM >X.X
Chemical Mammal Bird Combined Combined Combined Combined Combined Combined Combined Combined Combined Combined
Indenotl ,2,3-cd|pyxene
Phot an titrate
Pyrcne
166.47
145.66
166.47
50.5
6.46E-05
5.98E-05 8.82E-05
1.43E-04
3.27E-04 3.03E-04 4.46E-04
7.24E-04
PCB*
PCB Aroclor 1242
PCB Aroclor 1260
PCB (total)1
Pesticide*
4,4-DDD (p,p'-)
4,4-DDE (p,p'-)
4,4'-DDT (p,p'-)
Aldrin
alpha-Chlordane
cis-Nonachlor
d-BHC
DicJdrin
Endosutfan II
Endrin ketone
gamma-Chlordanc
(alpha, gamma]Chlordanc'
Hcptachlor
Heptachlor epoxide
Oxychlordane
tram-Nonachior
Scaivabltlk Orjiitla
l,l'-Biphenyl
2-Chlorophenol
2,4,5 -Trichlorophenol
2,4,6-Trichlorophenol
2,4-Dichtorophenol
2,4-Dimelhylphenoi
2,4-Dinitrophenol
2-Methylphenol
1634.47
499.95
3.12
47.19
338.43
288.44
18.84
2.04
38.46
31.92
1.96
2.96
72
1138.36
11.54
519.18
150
91
29
290
297.5
3.6
11.7
13.9
12
47
7.70E-04
2.18E-04
4.67E-03
1.23E-05
1.98E-06
7.10E-05
1.83E-04
1.44E-07
2.65E-04
5.30E-06
2.97E-06
2.89E-03
7.44E-04
1.73E-02
5.41E-06
8.66E-05
1.8IE-04
9.11E-07
5.74E-04
1.24E-04
2.48E-03
2.90E-04
1.37E-02
6.91E-06
2.63E-04
2.34E-04
1.20E-06
7.81E-04
1.09E-04
2.97E-06 2.97E-06
2.38E-03
1.68E-04
1.28E-02
2.34E-05 3.02E-05 3.41E-05
1.1 IE-OS
7.10E-05
2.73E-04
2.44E-06
9.45E-04
5.23E-06
1.77E-05
3.20E-05
7.34E-05
3.96E-04
4.07E-05
2.61E-05
2.66E-04
9.18E-04
5.41E-04
2.04E-05
3.90E-03
1.10E-03
2.36E-02
1.00E-05
3.60E-04
9.25E-04
7.29E-07
1.34E-03
2.68E-Q5
1.02E-05
1.46E-G2
3.76E-03
8.73E-02
I.25E-02
1.47E-03
6.94E-02
2.74E-05
4.38E-04
9.18E-04
4.61E-06
2.90E-03
6.30E-04
1.02E-05
3.50E-05
1.33E-03
1.19E-03
6.05E-06
3.95E-03
5.52E-04
1.02E-05
1.20E-02
8.52E-04
6.49E-02
6.23E-05 1.18E-04 1.53E-04 1.73E-04
5.64K-05
3.59E-04
1.38E-03
1.24E-05
4.78E-03
2.65E-05
6.10E-05
1.62E-04
3.72E-04
2.00E-03
2.06E-04
1.32E-04
1.35E-03
4.64E-03
2.74E-03
1.03E-04
Lower Ottawa River SLRA
Page 8 of 12
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the Iowa* Ottawa River.
Chemical
Acute Wildlife
Screening Doec
(mg/kg/day)
Hazard Quotients for the Bald Eagle
Hazard Quotients for the Common Tern
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5 RM 6.5-8.8
RM >8.8
RM 0-3.2
RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8.8
Mammal
Bird
Combined
Combined
Combined Combined
Combined
Combined
Combined Combined Combined Combined
2-Nitrophenol
_
_
3^-D»Uoiiibnadne
1469.1
-
-
-
-
-
-
4,6-Dinitro-2-methylphcnol
-
-
-
-
-
-
-
4-CWoro-3-methylphenol
-
-
-
-
-
-
-
4-Methylpheaol
692.24
57
5.94E-05
5.06E-05
7.86E-05 1.50E-04
2.96E-04
2.51E-04 3.93E-04 7.30E-04
4-Nitrophenol
-
-
-
-
-
-
-
bi»(2^thylhexyl)phthalale
11921.99
•
-
-
-
-
-
Butylbeazylphliialate
-
-
-
-
-
-
-
Dim ethyl phltalatr
-
-
-
-
-
-
-
Di-n-octyiphthalalc
-
-
-
-
-
-
-
Pealadtlorophenol
19.23
314
1.35E-06
1.35E-06
1.35E-06 8.05E-06
4.64E-06
4.64E-06 4.64E-06 2.77E-05
Phenol
62.43
-
-
-
-
-
-
1 - PCB (total) = ram of A1242 and;
1 - [alpha, gaaunaJChlortJanc = >0111 •
Lower Oflaws River SLRA
Pago 9 of 12
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
Hazard Quotients for the Spotted Sandpiper
Chemical
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 KM >8.8
Combined Combined Combined Combined Combined
Mcteb
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Chromium
Cobalt
Copper
Iron
Lead
Manganese
Mercury
Methyl Mercury
Nickel
Selenium
Silver
Thallium
Vanadium
Zinc
Conventional!
Ammonia
Cyanide
FAH»
Anduaocne
Benzo{a]anthraccne
Benzo[a]pyrene
Benzo[b]fluoranthene
Benzo[g>,i]perytene
Bcnzo[k]fluoranthenc
Chiyicne
Dibenz(aji]anthracene
Fluormthene
9.24E-02 1.01E-01 7.59E-02 7.54E-02
8.56E-03 6.70E-03 2.71E-02 1.0lEr02
1.72E-03 2.64E>03 2.77E-03 4.92E-03
1.O7E-03 8.74E-04 1.95E-03 9.56E-04
1.85E-03 1.I7E-03 1.87E-03 1.91E-03
1.86E-01 2.06E-0L 1.75E-0I 1.54E-01
1.52E-02 4.58E-02 3.93E+00 5.12E-02
5.08E-04 5.84E-04 2.20E-03 4.61E-04
6.99E-06 1.04E-05 2.00E-05 1.05E-04
3.62E-01 4.27E-01 4.97E-01 1.06E+00
2.91E-03 3.18E-03 8.21E-03 3.14E-02
1.74E-02 1.59E-02 1.91E-02 3.49E-02
2.33E-02 2.83E-02
1.34E-02 6.77E-02
Lower Ottawa River SLRA
Page 10 of 12
Hazard Quotients for the Mink
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Combined Combined Combined Combined Combined
6.94E-01
7.60E-01
5.68E-01
5.64E-01
-
1.Q4E-04
2.06E-04
1.73E-04
8.62E-05
-
4.76E-02
3.92E-Q2
1.52E-01
5.46E-02
5.97E-02
1.21E-02
1.85E-02
1.94E-02
3.42E-02
-
1.08E-03
1.23E-03
1.13E-03
1.37E-03
-
1.35E-03
1.29E-03
2.83E-03
1.73E-03
2.47E-03
1.25E-02
1.22E-02
3.06E-02
2.54E-02
-
8.56E-05
8.85E-05
7.03E-0J
6.05E-05
-
1.98E-02
1.25E-02
1.99E-02
2.04E-02
-
7.76E-01
8.59E-01
7.27E-01
6.39E-01
-
6.23E-04
1.66E-03
1.25E-01
2.03E-03
1.02E-03
8.O5E-03
9.43E-Q3
8.59E-03
7.56E-03
-
6.88E-05
7.91 E-05
2.93E-04
6.33E-05
-
3.25E-04
1.52E-03
1.06E-03
1.58E-03
3.47E-03
1.23E-02
1.22E-02
1.15E-02
5.74E-03
-
3.19E-01
2.40E-02
3.58E-01
2.01E-01
2.24E-01
3.25E-04
4.85E-04
9.29E-04
4.89E-03
-
1.64E-03
1.79E-03
1.26E-03
2.30E-03
-
1.07E-02
1.17E-02
9.43E-03
1.13E-02
-
7.39E-02
8.70E-02
1.01E-01
2.17E-01
-
1.25E-03
1.30E-03
3.58E-03
8.60E-03
-
3.32E-06
2.81E-06
4.63E-06
1.15E-05
-
7.43E-05
6.68E-05
3.68E-05
1.56E-04
-
7.65E-05
6.06E-05
3.63E-05
1.69E-04
-
7.49E-05
4.90E-05
4.73E-05
1.90E-04
-
7.63E-05
5.06E-05
4.44E-05
2.30E-04
-
7.97E-05
6.76E-05
1.06E-04
2.59E-04
-
1.95E-05
2.05E-05
1.61 E-05
1.00E-04
-
October 2001
555-3763-001
-------
Table C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
Hazard Quotients for flic Spotted Sandpiper
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.3 RM 6.5-8.8 RM>8.8
Chemical Combined Combined Combined Combined Combined
Indcno[ 1,2,3-cd]pyrcne
Pyrene
I.S7&02 1.91E-02 1.94B-02 2.45EX>2
PCB*
PCB Aroclor 1242
PCB Aroclor 1260
PCB (total)1
Pesticides
4,4'-DDD (ptf-)
4,4*-W«(n'-)
4,4,-DDT (pj>'->
AMria
dpIu-CMadac
cia-NonaclUor
d-BHC
Dieldria
PinVwral&B H
Hadna ketone
lilffci, g—aJCMonfaae
Hcptnlilnr epoxide
OxycUordsne
kas-Nouddw
l.l'-Biphcnyl
2-CManffcanl
2.4.5-TrkUoropkcnoI
2.4.6-Tncfcloropfccnol
2,4-DieUo(D(ihcaoi
2,4-Dimcllty l}jbtaul
2,4-Dmitropheaol
2-Mcthyipbcaoi
1.83E-03
S.91E-04
1.13E-02
7.74E-06
2.46E-03
8.42E-04
1.66E-04
1.04E-03
6.03E-05
1.53E-05
1.46E-02
8.43E-04
7.83E-02
9.50E-03
7.70E-04
5.16E-02
8.17E-06
1.66E-02
1.68E-03
7.79E-04
1.53E-03
1.28E-04
2.46E-0S
7.16E-03
6.35E-04
6J3&04
1.34E-03
4.02E-05
6.91E-03
2.83E-03
4.46E-02
3.29E-05 4.99E-05 6.75E-05 1.02B-04
2.18E-05
1.39EM53
5.97E-04
9.S6E-04
9.40E-04
8.63E-06
1.53E-05 1.53B-05 9.11E-05
Lower Ottawa River SLRA
Page 11 of 12
Hazard Quotients for the Mink
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Combined Combined Combined Combined Combined
7.53E-05
8.51E-05
8.90E-05
5.86E-05
7.88E-05
8.37E-05
3.44E-05
1.16E-04
6.94E-05
1.25E-04
1.89E-04
3.14E-04
1.35E-04
7.56E-OS
8.26E-02
5.06E-04
2.57E-04
3.06E-01
4.35E-04
1.01E-04
2.44E-01
4.18E-04
6.07E-05
2.29E-01
5.58E-06
2.54E-05
6.99E-03
1.44E-04
5.68E-05
3.89E-06
2.68E-05
2.73E-04
1.39E-04
1.06E-05
3.79E-05
3.54E-04
9.8SE-05
1.36E-05
9.96E-05
4.01E-04
8.18E-05
2.19E-05
2.69E-05
4.75E-04
2.87E-04
5.11E-05
9.67E-05
2.00E-03
1.98E-07
2.00E-03
1.25E-06
2.57E-03
1.64E-06
2.99E-03
3.36E-06
1.00E-02
1.90E-04
2.44E-04
1.74E-04
4.11E-04
5.68E-03
6.15E-04
5.59E-04
4.97E-03
6.40E-04
6.77E-04
2.40E-04
6.20E-04
3.87E-04
9.30E-04
4.92E-04
6.94E-06
1.10E-06
6.94E-06
1.10E-06
6.94E-06
1.10E-06
4.14E-05
6.55E-06
1.08E-04
9.63E-07
1.08E-04
9.63E-07
1.08E-04
9.63E-07
6.46E-04
5.74E-06
October 2001
555-3763-001
-------
Tabic C-l. Acute hazard quotients for wildlife receptors in the lower Ottawa River.
Hazard Quotient* for the Spotted Sandpiper Hazard Quotient* for the Mink
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8.8 RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Chemical Combined Combined Combined Combined Combined Combined Combined Combined Combined Combined
2-Nitrophenol
3,3'-Dichlorobenzidine
4,6-Diiiitn>-2-methylphenol
4-CKIoro-3-methylphenol
4-Mcthylphenol
4-Nitrophenol
bU(2-Ethylhexyl)phthalatc
Butylbcnzy iphthalate'
Dimethyl phthalate
Di-n-octylphth&late
Pcntachlorophenol
Phenol
1 - PCS (total) = turr. of A1242 and i
1 - (alpha, gammajChlordane = sum •
1.99E-02 1.85E-02 2.06E-02
6.93E-06 6.93E-06 6.93E-06
3.40E-07
2.73E-02 - 1.84E-05
1.03E-06
4.13E-05 - 6.50E-05
8.01B-06
3.40E-07 3.40E-07 2.03E-06
1.56E-05 2.44E-05 4.57E-05
2.03E-06 1.46E-06 8.38E-06
6.J0E-O5 6.J0E-05 3.88E-04
8.01E-O6 8.0IE-06 4.78E-05
Lower Ottawa River SLRA
Page 12 of 12
October 2001
555-3763-001
-------
Table C-2. Chronic hazard quotients for wildlife receptors In die lower Ottawa River.
95%UCL Sediment Concentration, Study 20 (mg/kg-wet)
Chemical RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 KM >8.8
MM
Ahm>in«ai
5206.467
5685.403
4727.105
4666.935
Antiaaony
0.334
0.695
0.580
0.254
Aiaeak
3.820
3.521
10.672
5.103
Bam®
49.(66
75.470
81.624
144.199
Bcrytthm
0.255
0.289
0.280
0.340
Caduna
0.976
1.003
1.965
1.146
OutMBiam
26.251
31.402
69.396
68.341
Cobalt
4.087
4.368
3.756
3.341
Copper
38.825
32.611
50.011
52.046
Iron
9765.153
11022.602
9877.814
9200.873
Lead
41.912
113.061
8243.797
155.900
Mnvtamnc
174.675
197.915
183.488
180.644
Menay
0.087
0.110
0.404
0.124
Mdkjrl Mawy
-
-
-
-
Nickd
18.808
20.561
20.674
11.016
Sfkaint
1.025
0.739
1.216
2.731
Silver
0.284
0.526
1.008
5.349
Thattan
2.201
2.676
1.891
3.437
Vanatfam
11.986
13.163
11.494
13.403
Zin
101.510
133.217
162.288
324.363
Aamcuia
Qmude
0.102
0.123
0.258
1.413
PAH*
Anthracene
1.509
1.570
2.684
6.576
Baoa(i)a>ti>ocac
1351
1.634
1.025
3.888
Bcna(a|p)mM
1.429
1.419
0.960
4.219
BawWflwMtMe
1.383
1.164
1.288
4.822
BoaabMmte
1.452
0.947
2.535
3.006
Bcna^lBMSMlne
1.413
1.546
1.239
5.323
CbjMe
1.450
1.138
1.417
5.926
Dlsan|^|t|attmaK
1.639
1.563
2.684
6.516
Ftmanttieae
1.953
2.201
2.380
13.356
Lower Otbmr* fiiver SLRA
Page 1 of 12
9S% UCL Surface Water Concentration (t»g/L)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
2601.68
2188.71
1240.40
1103.14
1.05
1.05
1.05
5.62
Z01
3.37
1.15
1.15
63.48
69.27
86.09
70.37
0.18
0.10
0.24
0.10
4.91
4.18
2.93
3.33
1.38
1.50
1.26
1.03
1X55
11.36
11.02
15.61
4311.86
4161.45
2747.10
1873.14
7.55
7.28
6.49
5.32
91.18
(01.33
367.74
131.39
0.15
0.17
0.16
0.23
8.19
7.86
8.81
6.66
5.90
5.88
5.83
6.63
Z52
1.60
1.60
1.60
6.88
6.05
3.77
3.63
24.00
22.57
29.33
36.69
0.24
0.29
3.12
0.31
5.26
5.17
12.63
3.73
5.00
5.00
5.00
23.28
6.59
5.00
9.19
23.28
6.59
5.00
9.19
23.28
6.59
5.00
9.19
23.28
6.59
5.00
9.19
23.28
5.00
5.00
5.00
23.28
6.59
5.00
9.19
23.28
October 2001
555-3763-001
-------
Tabic C-2. Chronic hazard quotients for wildlife receptors in the lower Ottawa River.
95% UCL Sediment Concentration, Study 20 (mg/kg-wet)
Chemical RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Indeao[l ,2,3-cdjpyrene
1.380
1.349
0.886
3.014
PHcnanthrcne
1.657
1.745
2.392
4.674
Pyn»
1.758
1.8S9
2.061
8.340
PCB*
PCB Aroclor 1242
0.185
1.260
1.439
1.536
PCB Aroclor 1260
0.032
0.046
0.062
0.401
PCB (total)1
0.217
1.307
1.501
1.937
FnUcMn
4,4'-DDD (p,p'-)
0.005
0.009
0.020
0.049
4,4-DDE (p,p'-)
0.006
0.014
0.022
0.027
4,4'-DDT (p,p"-)
0.002
0.002
0.007
0.011
Akhin
0.006
0.034
0.021
0.007
alpha-Chlordane
0.002
0.003
0.007
0.014
cii-Notiachlor
-
-
-
-
d-BHC
0.001
0.003
0.007
0.001
Dieldrin
0.006
0.012
0.008
0.010
Endoaulfan 11
0.002
0.006
0.008
0.021
Endrin
-
-
-
-
Endrin ketone
0.002
0.003
0.004
0.027
gamma-Chlordane
0.005
0.008
0.009
0.007
I alpha, gamma]-Chlordane'
0.007
0.011
0.017
0.020
HcpUchlor
0.002
0.004
0.002
0.001
Heptachlor epoxide
0.008
0.028
0.015
0.011
Oxychlordanc
trau-Nonaehlor
Scmivotatitc Orjanln
l.l'-Biphenyl
2-Chlorophetiol
2.4.5-TrichiaropiienoJ
2.4.6-Trichlorophcnol
2,4-DichlocophenoI
2,4-Dimethylphenol
2,4-Dinitrophcnoi
Lower Ottawa River SLRA
Page 2 of 12
95% UCL Surface Water Concentration (ug l¦)
RM 0-3.2 RM 3-2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
6.59 5.00 9.19 23.28
5.00 5.00 5.00 23.28
5.00
5.00
5.00
23.28
5.00
5.00
5.00
23.28
12.50
12.50
12.50
58.21
5.00
5.00
5.00
23.28
5.00
5.00
5.00
23.28
5.00
5.00
5.00
23.28
12.50
12.50
12.50
58.21
October 2001
555-3763-001
-------
Tabic C-2. Chronic hazard quotients for wildlife receptors in die lower Ottawa River.
95% VCL Sediment Concentration, Study 20 (mg/kg-wet) 95% UCL Surface Water Concentration ((ig/L)
Chemical
RM 0-3.2
RM 3.2-4.9
RM 4.9-6-3
RM 6.5-8.8 RM>8.8
RM 0-3.2
RM 3.2-4,9
RM 4.9-6.5
RM 6.5-8.8 RM >8.8
2-Methylpheool
_
_
_
5.00
5.00
5.00
23.28
2-hfitrophcaol
-
-
-
-
5.00
5.00
5.00
23.28
3,3'-D»chk>robeiizi)
1.671
1.689
2.684
4.822
5.00
5.00
5.00
23.28
4~NjtrophcnoI
-
-
-
-
12.50
1250
12.50
58.21
bi«(2-EJhylhexyI)pbtil»l*te
1.465
3.192
2.718
15.747
5.00
6.02
6.02
28.60
BotjrHieazylphlfaaWc
1.671
1.578
2.684
4.822
5.00
5.00
5.00
23.28
Dimethyl phthalate
-
-
-
-
5.00
5.00
5.00
5.00
Di-*-octylphtlul«te
1.671
2102
2.547
1.579
6.59
5.00
9.19
23.28
PmlxJiliinnJi'iiol
-
-
-
-
12.50
12.50
1Z50
58.21
HmoI
-
-
-
-
5.00
5.00
5.00
23.28
1 - PCB (total) - ram of A.1242 and A.1260 concentration*.
(»<[*« gmniJCUordne c turn of ftlplu and gamma Chlordane vomer concentration*.
Lower Ottawa f®wr SLAM
Page 3 of 12
October 2001
555-3763-001
-------
Tabic C-2. Chronic hazard quotients for wildlife receptors in the lower Ottawa River.
Chemical
95% UCL Fish Tissue Concentration (mg/kg-wet) Estimated 95% UCL Invertebrate Tissue Concentration (mg/kg-wet)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8 RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 R\1 >8.8
Mctab
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Chromium
Cobalt
Copper
Iron
Lead
Manganese
Mercury
Methyl Mercury
Nickel
Selenium
Silver
Thallium
Vanadium
Zinc
0.020
0.262
0.011
0.011
1.030
0.020 0.046 0.020 0.112
0.010 0.013 0.024 0.024
0.422
0.040
0.040
0.102
0.830
0.028
0.028
1.073
0.756
0.043
0.043
0.706
0.058
1.621
0.095
0.095
0.874
CwiwnHwih
Ammonia
Cyanide
PAH.
Anthracene
Benzo(a}anthraoene
Benzo(a]pyrcnc
Benzo|b]fh>oranthenc
Benzo[g>h,i]pcrylene
Benzofkjfluoranthene
Chiytene
Dibcnz[aji]anthracene
Fluoranthene
0.529
0.585
0.667
1.178
0.412
0.556
0.222
0.653
0.425
0.474
0.203
0.679
0.400
0.393
0.269
0.767
0.427
0.303
0.526
0.473
0.416
0.517
0.263
0.842
0.446
0.425
0.327
0.988
0.484
0.474
0.551
0.966
0.665
0.869
0.535
2.344
Lower Ottawa River SLRA
Page 4 of 12
October 2001
555-3763-001
-------
TaMe C-2. Chronic hazard quotients for wildlife receptors in the lower Ottawa River.
95% UCL Fiah Tiaauc Concentration (mg/kg-wet)
RM 0-3.2 RM 3.2-4 9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Indeao[l>23-od]pyrciw
-
*
-
-
-
FScnanthrcnc
-
-
-
-
-
Pyicac
-
-
-
-
-
PCB.
PCB Arocior 1242
0.865
2.812
2.437
2.026
0.029
PCB Arocior 1260
0.132
0.421
0.179
0.113
0.046
PCB (total)1
0.997
3.232
2.616
2.139
0.075
fMbkbt
4,4'-DDD (p4>'-)
0.024
0.045
0.057
0.064
0.073
4,4'-DDE (p4>'-)
0.070
0.164
0.123
0.097
0.313
4.4,-DDT(W.-)
0.004
0.009
0.012
0.020
0.043
AMrb
0.002
0.002
0.005
0.002
0.006
alpha-CMotthne
0.004
0.007
0.015
0.020
0.026
cia-Nonarhlnr
0.004
0.005
0.008
0.007
0.011
d-BHC
-
-
-
-
-
DkUrin
0.014
0.014
0.019
0.022
0.062
Ewkmlfaa J1
-
-
-
-
-
Eadria
-
-
-
-
-
Hfidnn ketatte
-
-
-
-
guuu-CUordanc
0.018
0.036
0.038
0.044
0.012
[alpha, gauuKUortW'
0.022
0.044
0.053
0.065
0.038
HeptasUor
0.002
0.032
0.026
0.002
0.006
Heptacklor epoxide
0.002
0.005
0.005
0.006
0.006
OxycUordaate
0.011
0.023
0.019
0.018
0.010
ft — NanadUar
0.008
0.015
0.018
0.022
0.031
ScflrivBlatite
l,l'-Biph«yt
2-Ckk*ophc»ol
2,4^-TncUorof)i»u>i
2,4,6-Triohloroptienol
2,4-Dickloropiicnol
2,4-Dimethylpfaeaol
2,4-Dinitrophcnol
Lower Ottawa River SLRA
Page 5 of 12
Estimated 95% IJCI. invertebrate Tissue Concentration (mg/kg-wct)
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
0.382
0.404
0.188
0.447
0.586
0.666
0.592
0.870
0.598
0.746
0.484
1.498
0.219
1.552
0.969
0.776
0.038
0.055
0.047
0.198
0.257
1.607
1.017
0.974
0.006
0.011
0.014
0.023
0.007
0.016
0.016
0.012
0.002
0.002
0.005
0.005
0.007
0.040
0.016
0.004
0.002
0.004
0.005
0.006
0.001
0.004
0.005
0.000
0.007
0.013
0.005
0.005
0.002
0.007
0.005
0.010
0.002
0.003
0.003
0.013
0.005
0.010
0.006
0.003
0.007
0.014
0.012
0.009
0.002
0.004
0.001
0.000
0.009
0.033
0.010
0.006
October 2001
555-3763-001
-------
Table C-2. Chronic hazard quotients for wildlife receptors in die lower Ottawa River.
95% UCL Fish Tissue Concentration (mg/kg-wct) Estimated 95% UCL Invertebrate Tissue Concentration (mg/kg-wet)
Chemical RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8 RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
2-Methylphenol
2-Nitrophenol
3,3-Dichlorobenzidine
4,6-Dinitro-2-methylphcnoI
4-Chloro-3-methylphenol
4-Methylphenol
4-NitrophenoI
bi«(2-Ethyihexyl)phthalate
Butylbenzylphthalate
Dimethyl phthalate
Di-n-octylphthalate
Pentachlorophenol
Phenol
1 - PCB (total) = sum of A1242 anc
1 - [alpha, gamma]Ch!ordane = sun
0.738
0.488
0.573
0.877
0.803
1.273
0.572
1.235
0.835
0.650
0.648
0.960
1.117
2.765
0.868
0.349
Lower Ottawa Rrvor SLRA
Page 6 of 12
October 2001
555-3763-001
-------
Table C-2. (Ironic hazard quotients for wildlife receptors in the lower Ottawa River.
Chronic Wildlife ^Hazard Quotients for the Common Tem
Screening Dote
(mgAg/day) RM 0-3.2 RM 3.2-4.9 RM 4-9-6-5 RM 6.5-g.g RM>8.8 RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 65-8.8 RM >8.8
Hwiinl Mammal Bird Combined Combined Combined Combined Combined Combined Combined Combined Combined Combined
Mctab
Ahaunom
1.48
100
6.36E-02
6.93E-02
5.74E-02
5.66E-02
-
3.21E-01
3.49E-01
2.90E-01
2.86E-01
-
Antimony
0.052
-
-
-
-
-
-
-
-
-
-
-
Aneaio
0.25
5.5
1.28E-03
1.23E-03
3.36E-03
1.56E-03
2.44E-03
6.45E-03
6.17E-03
1.70E-02
7.88E-03
1.24E-02
Bam
3.92
208
2-99E-04
4.49E-04
4.87E-04
8.47E-04
-
1.50E-03
2.25E-03
2.44E-03
4.27E-03
-
Bcrylliom
0.27
-
-
-
-
-
-
-
-
-
-
-
0.742
1.45
1.68E-03
1.92E-03
3.66E-03
2.95E-03
4.83E-03
8.51E-03
9.72E-03
1.85E-02
1 49E-02
2.45E-02
Ctnaiai
154
1
3.18E-02
3.80E-02
8.37E-02
8.25E-02
-
1.61E-01
1.92E-0!
4 24E-01
4.I7E-01
-
Cobalt
0.92
1.3
3.83E-03
4.09E-03
3.51E-03
3.12E-03
-
1.93E-02
2.06E-02
1.77E-02
1.58E-02
-
Copper
1.11
2.3
2.05E-02
1.73E-02
2.64E-02
2.75E-02
-
1.04E-01
8.71E-02
1.33E-01
1.39E-01
-
Iran
49.94
-
-
-
-
-
-
-
-
-
-
-
Lead
0.15
3.85
2.14E-02
4.87E-02
2.61E+00
7.25E-02
5.07E-02
1.08E-01
2.46E-01
I.32E+01
3.67E-01
2.57E-01
Maagaaeae
68
997
214E-04
2.43E-04
2.34E-04
2.23E-04
-
1.08E-03
1.22E-03
l.lTErOi
1.12E-03
-
Mcnay
0.027
0.039
2.80E-03
3.57E-03
1.26E-02
4.02E-03
-
1.40E-02
1.78E-02
6.36E-02
2.00E-02
-
Methyl Memory
0.08
Z 6
5.27E-04
1.85E-03
1.27E-03
2.01E-03
4.41 E-03
2.67E-03
9.39E-03
6.45E-03
1 02E-02
2.23E-02
Nickel
30.77
65
3.53E-04
3.85E-04
3.88E-04
2.08E-04
-
1.78E-03
1.94E-03
1.96E-03
1.05E-03
-
0.154
0.57
2.20E-01
2.35E-02
2.30E-01
1.55E-01
1.85E-01
1.11E+00
1.18E-01
1.16E+00
7.86E-01
9.35E-01
Silvor
17.08
-
-
-
-
-
-
-
-
-
-
-
Tlnlliiiia
0.006
-
-
-
-
-
-
-
-
-
-
-
"iinitiiiiii
0.65
11.4
1.29E-03
1.41E-03
1.23E-03
1.43E-03
-
6.48E-03
7.11E-03
6.19E-03
7.21E-03
-
Ziao
66.59
17.2
7.16E-03
9.38E-03
1.14E-02
2.28E-02
-
3.62E-02
4.74E-02
5.78E-02
1.15E-01
~
Aantooia
_
.
_
.
Cyanide
5Z84
0.04
7.53E-03
8.08E-03
1.85E-02
4.57E-02
-
3.09E-02
3.38E-02
7.62E-02
2.26E-01
-
FAHa
Aaduaocnc
58.02
280
6.50E-06
6.76E-06
1.16E-05
2.83E-05
-
3.29E-05
3.42E-05
5.85E-05
1.43E-04
-
0.42
-
-
-
-
-
-
-
Beag>(al|ijKai
0.42
-
-
-
-
-
-
-
Bcazo)b]ftiim anthi n
0.42
-
-
-
-
-
-
-
BwMbJMka^cu
-
-
-
-
-
-
-
-
BenzoMfluunnllw itu
-
-
-
-
-
-
-
-
CtayaeBc
0.42
-
-
-
-
-
-
-
-
Dhu{iJi|MtnocM
0.42
-
-
-
-
-
-
-
-
Fisorasthene
32.02
280
8.41 E-06
9.48E-06
1.02E-05
5.75E-05
-
4.26E-05
4.80E-05
5.19E-05
2.91 E-04
.
Lower Ottawa RivarSLRA
Page 7 of 12
October 2001
555-3763-001
-------
Table C-2. Chronic hazard quotients for wildlife receptors in the lower Ottawa River.
Chemical
Chronic Wildlife
Screening Dose
(mg/kg/day)
Mammal
Bird
Hazard Quotients for the Bald Eagle
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM6.5-8.il RM>8.8
Combined Combined Combined Combined Combined
Hazard Quotient* for the Common Tem
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Combined Combined Combined Combined Combined
Indcnoj 1,2,3-cdjpyrcne
Phenanthrene
Pyrene
PCBa
PCB Aroclor 1242
PCB Aroclor 1260
PCB ftotal)1
Pesticides
4,4-DDD (p,p'-)
4,4'-DDE (pj>'-)
4,4-DDT (p,p'-)
Aldrin
alpha-Chlordane
cis-Nonschlor
d-BHC
Dieldrin
Endoaulfan II
Endrin
Hadrin ketone
gamma-Chlordane
[alpha, gamma]-Chlordane'
Heptachlor
Heptachlor epoxide
Oxychlordane
trau-Nonaclilor
SemivslatUe Orjuiki
M'-Biphcnyl
2-Chlorophenol
2.4.5-TrichIorophenol
2.4.6-Triehlorophenol
2,4-Dichlorophenol
2,4-Dimethylphenol
2,4-Dinitrophenol
0.42
52.02
31.21
0.6
0.05
21.54
14.15
0.03
0.154
0.014
0.015
0.12
0.038
1.9
0.1
0.24
2.31
92.3
541.03
46.15
280
0.46
0.09
0.845
0.003
0.56
0.077
10
0.01
2.1
0.065
7.13E-06
7.51E-06 1.03E-05
2.01E-05
3.61E-05
3.80E-05 5.21 E-05
1.02E-04
2.27E-01 7.40E-01 6.42E-01 5.35E-01 7.66E-03
1.34E+00 4.35E+00 3.52E+00 2.89E+00 1.01E-0I
1.00E-02
1.48E-01
1.84E-06
2.24E-02
1.99E-07
1.26E-03
3.75E-03
2.35E-02
3.75E-01
7.28E-06
2.22E-02
7.41E-07
2.52E-03
5.95E-02
1.75E-02
4.75E-01
1.55E-05
2.92E-02
9.93E-07
3.07E-03
4.76E-02
1.39E-02
7.90E-01
2.18E-06
3.43E-02
2.55E-06
3.72E-03
3.73E-03
4.47E-02
1.72E+00
9.76E-02
2.18E-03
1.08E-02
1.15E+00 3.75E+00 3.25E+00 2.71E+00 3XXF.-02
6.77E+00 2.20E+01 1.78E+01 1.46E+01 5.1 IE-Ill
5.07E-02 1.19E-01 8.86E-02 7.04E-02 2.26E-0I
7.50E-01 1.90E+00 2.40E+00 4.00E+00 8.71 E^ 00
9.30E-06 3.68E-05 7.86E-05 1.11 E-05
1.13E-01 1.13E-01 I.48E-01 1.74E-01 4.94E-01
1.01E-06 3.75E-06 5.03E-06 1.29E-05
6.38E-03 1.28E-02 1.56E-02 1.88E-02 1.10E-02
1.90E-02 3.01E-01 2.41E-01 1.89E-02 5.49E-02
Lowor Ottawa River SLRA
Page 8 of 12
October 2001
555-3763-001
-------
Table C-2. Chronic hazard quotients fo^ wildlife receptors in the lower Ottawa River.
Chronic Wildlife Hazard Quotient* for the Bald Eagle Hazard Quotients for the Common Tern
Screening Doae
(mg/kg/day)
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM>8.8
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8 RM >8.8
Chemical
Mammal
Bin)
Combined
Combined
Combined
Combined
Combined
Combined
Combined
Combined
Combined Combined
2-Mcthylphcaol
219
.
.
.
_
.
.
.
_
2-NitrophcaoI
-
-
-
-
-
-
-
-
-
-
-
3^'-Dichlorobcnzidjne
-
-
-
-
-
-
-
-
-
-
-
4,6-Dinitro-2-methyiphenol
-
-
-
-
-
-
-
-
-
-
-
4-Chbxo-3-metiiyl{ilicnol
-
-
-
-
-
-
-
-
-
-
-
4-Mc«hyIphenol
346.12
-
-
-
-
-
-
-
-
-
-
4-Nteophcool
-
-
-
-
-
-
-
-
-
-
-
btt(2-£thyIhexyI)phthaUU
7.6
1.1
1.76E-03
3.68E-03
3.16E-03
1.81E-02
-
8.66E-03
1.83E-02
1.57E-02
9.04E-02
ButyBxnzylphihalate
122.3
-
-
-
-
-
-
-
-
-
-
Dimethyl phthalrtr
769.16
-
-
-
-
-
-
-
-
-
-
Di-n-ootylphthalatc
3121.34
-
-
-
-
-
-
-
-
-
-
Pealachlorophenol
0.185
4.03
1.05E-04
1.05E-04
1.05E-04
4.90E-04
-
3.62E-04
3.62E-04
3.62E-04
1 69E-03
Pheaol
58.27
-
-
-
-
-
-
-
-
-
-
' - PCB (total) = sum of A1242 ant
1 - (alpha, gaai ill ajChlordaoc = nan
lower Ottawa River SLRA
Page 9 of 12
October 2001
555-3763-001
-------
Table C-2. Chronic hazard quotients for wildlife receptors in the lower Ottawa River.
Hazard Quotient for Ihc Spoiled Sandpiper
Chemical
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM>8.8
Combined Combined Combined Combined Combined
Mdib
Aluminum
Antimony
Araenic
Barium
Beryllium
Cadmium
Chromium
Cobalt
Copper
Iron
Lead
Manganese
Mercury
Methyl Mercury
Nickel
Selenium
Silver
Thallium
Vanadium
Zinc
1.74E+00 1.89E+O0 1.57E+00 1.55E+00
2.32E-02
8.02E-03
2.24E-Q2
8.74E-01
1.0JE-0J
5.62E-01
3.62E-01
5.84E-03
7.45E-02
9.64E-03
6.16E-02
3.S1E-02
1.96E-01
2.I4E-02
1.21E-02
2.30E-02
1.04E+00
U2E-01
4.72E-01
9.77E-01
6.62E-03
9.50E-02
1.05E-O2
4.49E-02
3.85E-02
2.58E-01
6.45E-02
1.31E-02
4.51E-02
2.31E+0O
9.62E-02
7.24E-01
7.12E+0I
6.18E-03
3.4JE-01
I.O6E-02
7.27E-02
3.36E-02
3.14E-01
3.09E-02
2.31E-02
2.63E-02
2.27E+00
8.56E-02
7.53E-01
1.35E+00
6.05E-03
1.07E-O1
5.6JE-03
1.61E-01
3.91E-02
6.27E-01
ConvMillonab
Ammonia
Cyanide
1.08E-01 1.25E-01 2.70E-01 1.19E+00
PAH*
Anthiaccne
Beazo(a]attthiaccne
Benzo[a]pyrane
Benzo[b|fluoranthene
BcnzofeJulperylcnc
Benzoffcjfluonathenc
Cluyacne
Dibenzjaji) anthracene
Fluorsnthcac
i .92E-03 2.I2E-03 2.J2E-03 4.67E-03
2.43E-03 3.13E-03 2.05E-03 9.32E-03
Lowar Ottawa River SLRA
Page 10 of 12
Hazard Quotients for the Mink
RM 0-3.2 RM 3.2-4.9 RM4.9-6.S RM 6.5-8.8 RM>8.8
Combined Combined Combined Combined Combined
1.63E+01
3.14E-02
8.87E-02
5.99E-02
4.33E-03
9.27E-03
4.75E-02
2.05E-02
1.61E-01
9.04E-01
1.70E+00
1.19E-02
] .52E-02
3.26E-02
2.83E-03
1.57E+00
7.61E-05
1.72E+00
8.55E-02
7.02E-03
1.88E-05
I.I9E-04
I.59E-02
1.71E-02
1.67E-02
1.70E-02
1.94E-02
1.72E-04
1.77E+01
6.33E-02
8.40E-02
8.99E-02
4.90E-03
1.02E-02
5.68E-02
2.19E-02
1.36E-01
I.02E+00
4.13E+0G
I.35E-02
1.94E-02
1.15E-01
3.09E-03
1.77E-01
1.41E-04
2.07E+00
9.37E-02
9.20E-03
2.04E-05
1.24E-04
1.90E-02
1.67E-02
1.39E-02
I.36E-02
I.82E-02
1.94E-04
1.47E+01
5.31E-02
2.38E-01
9.76E-Q2
4.75E-03
1.97E-02
1.25E-01
i,88E-02
2.07E-01
9.1IE-0t
2.54E+02
1.29E-02
6.91 E-02
7.87E-02
3.11E-03
1.63E+00
2.70E-04
1.47E+00
8.16E-02
1.12E-02
4.63E-05
2.12E-04
1.24E-02
1.27E-02
1.62E-02
1.66E-02
3.15E-02
2.10E-04
1.45E+01
3.32E-02
1.12E-01
1.70E-01
5.77E-03
1.45E-02
1.23E-01
1.67E-02
2.16E-01
8.48E-01
5.95E+00
1.24E-02
2.18E-02
1.24E-01
1.66E-03
1.14E+00
1.43E-03
2.65E+00
9.50E-02
2.24E-02
1.30E-04
5.19E-04
4.79E-02
5.15E-02
5.81E-02
7.02E-02
7.66E-02
1.18E-03
1.02E-0.1
1.79E-02
2.49E+00
2.72E-01
1.30E+00
October 2001
555-3763-001
-------
Table C-2. Chronic hazard quotients for wildlife receptors in die tower Ottawa River.
Hazard Quotient! for the Spotted Sandpiper
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM6.5-8.il RM>8.8
Ckcffiicat Combined Combined Combined Combined Combined
lBdeooll.23-cT (p4>'-)
Aldrin
alph»-Chlnrd—r
w-Noudifar
d-BHC
Dieldria
Eadoanlbo II
Eadris
Eadrin kctoae
gamaa-CMordaae
(•^{MaKUaidnc1
HeptaaUor
Heptaddor epoxide
OxyoUardane
traoa-NonacMor
8.11E-03
6.51E-01
1.81E-03
8.77E-02
1.95E-04
3.38E-03
2.98E-02
1.78E-02
6.92E-01
6.29E-03
1.6SE-01
6.42E-04
6.30E-03
5.98E-02
1.79E-02
1.63E+00
8.26E-03
6.38E-02
5.30E-04
5.47E-03
1.98E-02
1.47E-02
1.66E+00
7.18E-04
6.95E-02
9.98E-04
4.39E-03
6.19E-03
M'-Bipfcenyi
2-CMowmhcaol
2A5-TrioUaropJK»oi
2,4,6-Trichlaropfcaioi
2,4-Dicbkvoplicaot
2,4-Dimeftylpheaol
2,4-Dinitropfcenol
Lower Ottawa River SLRA
Page 11 of 12
Hazard Quotients for the Mink
RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8 RM >8 8
Combined Combined Combined Combined Combined
1.66E-02
1.46E-04
2.74E-04
1 59E-02
1.54E-04
Z89E-04
1.19E-02
2.1 IE-04
3.18E-04
3.84E-02
4.12E-04
1.30E-03
3.32E-01
6.05E-01
1.08E+00
1.93E+00
9.41E-01
8.26E-01
7.85E-01
5.53E-01
1.12E-02
2.11E-01
2.59E-04
1.14E-03
2.83E-02
3.16E-03
4.83E-04
2.67E-03
7.14E-02
4.01E-03
6.08E-04
1.99E-03
9.08E-02
8.77E-03
6.86E-04
1.58E-03
1.51E-01
3.19E-03
7.74E-04
5.07E-03
3.27E-01
8.70E-03
2.79E-04
Z19E-01
6.29E-05
1.1IE-03
2.I9E-01
2-35E-04
2.36E-03
2.86E-0I
3.15E-04
3.32E-04
3.36E-01
8.07E-04
9.52E-01
Z65E-03
4.67E-03
2.07E-03
5.31E-03
7.36E-02
5.54E-03
6.48E-03
5.88E-02
S.14E-03
7.83E-03
4.63E-03
5.89E-03
4.57E-03
1.34E-02
5.61E-03
2.16E-04 2.16E-04 2.16E-04 1.01E-03
5.42E-06 5.42E-06 5.42E-06 2.52E-05
9.24E-07 9.24E-07 9.24E-07 4.30E-06
2.71E-05 2.71E-05 2.71E-05 1.26E-04
October 2001
555-3763-001
-------
Table C-2. Oironic hazard quotients for wildlife receptors in the lower Ottawa River.
Hazard Quotients for the Spotted Sandpiper Hazard Quotients for the Mink
Chemical
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM>8.8
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM >8.8
Combined
Combined
Combined
Combined
Combined
Combined
Combined
Combined
Combined
Combined
2-Mcthylphcnol
_
_
.
.
-
2.28E-06
2.28E-06
2.28E-06
1.06E-05
2-Nitrophenol
-
-
-
-
-
-
-
-
-
3,3'-Dichlorobcnzidinc
-
-
-
-
-
-
-
-
-
4,6-Dinitro-2-methylphenol
-
-
-
-
-
-
-
-
-
4-Chloro-3-methylphenol
-
-
-
-
-
-
-
-
-
4-Methylphenol
-
-
-
•
-
2.35E-05
2.38E-05
3.70E-05
7.05E-05
4-Nitrophenol
-
-
-
-
-
-
-
-
-
bis(2-EthyUiexyl)phthalale
4.54E-01
1.17E+00
6.29E-01
2.80E+00
-
9.49E-04
2.00E-03
1.72E-03
9.87E-03
Butylbenzylphthalate
-
-
-
-
-
6.66E-05
6.32E-05
1.05E-04
2.00E-04
Dimethyl phthalate
-
-
-
-
-
6.50E-07
6.50E-07
6.50E-07
6.50E-07
-
Di-n-octylphthalate
-
-
-
-
-
2.66E-06
3.25E-06
4.03E-06
3.06E-06
-
Pentachlorophenol
5.40E-04
5.40E-O4
5.40E-04
2.52E-03
-
6.76E-03
6.76E-03
6.76E-03
3.15E-02
-
Phenol
-
-
-
-
-
8.58E-06
8.58E-06
8.58E-06
4.00E-05
-
' - PCB (total) = sum of A1242 anc
1 - [alpha, gamma ]ChIordane = sun
Lowar Ottawa Rivor SLRA
Pago 12 of 12
October 2001
555-3763-001
-------
Table C-3. Acute and chronic hazard quotients for bald eagles feeding on fish species in Maumee Bay.
Tissue Concentration Wildlife Screening Doses Estimated Doses
(mg/kg-wct) (mgAg/day) (mg/lcg/day) Hazard Quotients
ClnrH 95% UCL 95th Percentile Chronic Bird Acute Bird Chronic Acute Chronic Acute
PCBs
PCS Arodor 1242
0.75
1.39
0.46
150
9.08E-02
J.68E-01
1.97E-01
1.12E-03
PCB Areolar 1254
0.77
1.22
0.18
79
9.30E-02
1.47E-01
5.17E-01
1.86E-03
PCB Arodor 1260
0.73
1.40
-
91
8.83E-02
1.68E-01
-
1.85E-03
Total PCBs
2.08
3.36
0.09
29
2.50E-01
4.05E-01
2.78E+00
1.40E-02
Ov^MMcfclnrinc PesticMes
2.4--DDD (ojj-)
0.0029
0.0047
-
-
3.49E-04
5.63E-04
-
-
2,4'-DDE (o4>'-)
0.0010
0.0016
-
-
1.26E-04
1.98E-04
-
-
2,4'-DDT (041'-)
0.0020
0.0038
-
-
2.44E-04
4.58E-04
-
-
4,4'-DDD (p4>'~)
0.042
0.067
-
290
5.11E-03
8.08E-03
-
-
4.4,-DDE(W>1-)
0.13
0.21
0.845
-
1.59E-02
2.57E-02
1.89E-02
8.87E-05
4,4'-DDT (p4>'-)
0.012
0.028
0.003
297.5
1.47E-03
3.36E-03
4.90E-01
1.13E-05
aipha-BHC
0.0010
0.0019
0.56
-
1.22E-04
2.27E-04
2.18E-04
-
s|pMUadiK
0.014
0.027
-
-
1.68E-03
3.24E-03
-
-
Dicldria
0.01S
0.027
0.077
11.7
1.83E-03
3.19E-03
2.37E-02
2.73E-04
Endrin
0.0001S
0.00035
0.01
>140
2.19E-05
4.21E-05
2.19E-03
3.01E-07
ganuaa-BHC (Lindane)
0.0025
0.0042
2
37.5
3.07E-04
5.09E-04
1.54E-04
1.36E-05
gam«*CWoed*e
0.0078
0.016
-
-
9.36E-04
1.89E-03
-
-
[alpha, ganunsJChlonianc
0.022
Z1
12
2.61E-03
-
1.24E-03
-
HcptacUor epoxide
0.0026
0.0052
-
-
3.19E-04
6.28E-04
-
-
HrTThkimhcnTrnr.
0.0011
0.0020
0.225
-
1.38E-04
2.45E-04
6.12E-04
-
16a
0.00082
0.0017
-
2400
9.83E-05
2.08E-04
-
8.67E-08
OxycUonkne
0.021
0.041
-
-
2.57E-03
4.91E-03
-
-
Taofkew
0.12
030
-
5.95
1.43E-02
3.59E-02
-
6.03E-03
trans-NonacUor
0.014
0.025
-
-
1.72E-03
2.97E-03
-
_
Lower Ottawa RivtrSUiA
Page 1 of 1
October 2001
555-3763-001
-------
Tabic C-4. Anlte and chraok hazard quotient! far aquatic life tmrd on turfact wattr cipoiura.
Acctt Scrmiiir^Vittti^^^ 9Sth P«c
-------
Tabic C-4. Acute and chronic hazard quotients for aquatic life baaed on surface water exposures.
Acute Screening Value 95th Percentile Surfoce Water Concentration (u&U Acute HQ
RM
RM
RM
RM
RM
RM
RM
RM
RM
RM
RM
RM
Chemical
0-3.2
3.2-4.9
4 9-6 5
6.5-88
0-3.2
3.2-4.9
4.9-6.5
6 5- 8.8
0-3.2
3.2-4.9
4.9-6.5
6 5-88
Pesticides
Atrame
185
18.5
18.5
18.5
7.03
5.00
5.00
5 00
3.80E-0!
2.70E-01
2.70E-01
2.70E-OI
SeaitvolaUle Orgeelc*
l.l'-Biphenyi
230 00
230 00
230.00
230.00
5.00
5.00
500
29.82
2.17E-02
2.17E-02
2.I7E-02
1.30E-01
2-Chlorophenol
500.00
500.00
500 00
500.00
5.00
5.00
500
29.82
1 OOE-02
1.0OE-02
1.00E-02
5.96E-02
2,4,5-Trichlarophenal
225.00
225.00
225.00
225.00
12.50
12.50
12.50
74.56
5.56E-02
5.56E-02
5.56E-02
3.31E-01
2,4,6-Tnchlorophenoi
90.00
90.00
90.00
90.00
5.00
5.00
500
29.82
5.56E-02
5.56E-02
5.56E-02
3.31E-01
2,4-DtcUorophenol
620.00
620.00
620.00
620.00
5.00
5 00
5.00
29.82
8.06E-03
8.06E-03
8 06E-03
4.81E-02
2,4-DuB«thyiphenal
105000
1050.00
1050.00
1050.00
5.00
500
5.00
29.82
4.76E-03
4.76E-03
4.76E-03
2.84E-02
2,4- Dudtropbenoi
30.00
30 00
30.00
30 00
12.50
12.50
12.50
74.56
4.I7E-01
4.17E-01
4.17E-01
249E+00
2-Metiiyipfcenol
2500.00
2500.00
250000
2500.00
5.00
5.00
5.00
29.82
2 00E-03
2.00E-03
2.00E-03
1.19E-02
2-Nitropkeo al
800.00
800.00
800 00
800.00
5 00
5 00
5.00
29.82
625E-03
6.25E-03
6 25E-03
3.73E-02
33'*Dichk>robcnzidine
525.00
525.00
525 00
525.00
5.00
500
5.00
29 82
9.52E-03
9.52E-03
9.52E-03
5.68E-02
4,6-Dinitro-2-«ethyipbe«ol
33.00
3300
33.00
3300
12.50
12.50
1250
74.56
3.79E-0I
3.79E-0I
3.79E-01
2.26E+00
4-CMaro-3 -netiiyipfaienol
458.50
458.50
458.50
458.50
5.00
5.00
5.00
29.82
1.09E-02
1.09E-02
1.09 E-02
6.50E-02
4-MethyiphmaI
700.00
700.00
700.00
700.00
5.00
5.00
5.00
29.82
7.14E-03
7 14E-03
7.14E-03
4.26E-02
4-Nitrc$bcaol
550.00
550.00
550.00
550.00
12.50
12.50
12.50
74.56
2.27E-02
2.27E-02
2.27E-02
1.36E-01
bie(2-EtkyIhexyi)phtludmte
400 00
400.00
400.00
400.00
5.00
7.78
7.78
37.75
1.25E-02
1.95E-02
I.95E-02
9.44E-02
390.00
390.00
390.00
390.00
500
5.00
5.00
29.82
1 28E-02
1.28E-02
1.28E-02
7.65E-02
Dimediyjphthelate
16500.00
16500.00
16500.00
16500.00
5.00
5.00
5.00
5.00
3.03E-04
3.03E-04
3.03E-04
3.03E-04
D»-«-octyiphth*l*te
-
-
-
8.65
5.00
12-13
29.82
-
-
-
hatacUoroplMK)!
11.39
11.56
12.72
1283
1250
12.50
12.50
74.56
1.10E+00
1.08E+00
9.82E-01
5 81E+00
Riwol
22.50
22.50
22 50
2250
5 00
5.00
5.00
29.82
2.22E-G1
2.22E-01
2.22E-01
1.33E+00
RM - River Mile
HQ * Hazard Quotient
UCL * Upper Confidence Limit
Lower Ottawa Rrvtr SLRA
Page 2 of 4
October 200!
555-3^63 001
-------
Table C-4. Arab aad chreek iaurd qwtkaU for static Ufc baaed oa ttaface water cipeturu.
KM
RM
RM
RM
RM
RM
RM
RM
CVwirJ
0-3.2
3-2 - 4.9
4 9-6.5
6.5-8.8
0-3.2
3 2-4.9
4.9-6 5
6.5-88
Umtah
87
87
87
87
2601.68
2188.71
1240.40
1103.14
Aatwwy
30
30
30
30
105
1.05
1.05
5.62
Anwc
ISO
150
150
150
2.01
3.37
1.15
1.15
Bm
1450
1450
1450
1450
63.48
69 27
86.09
70.37
Tiifcai—i
4.6
4.7
5.3
5.7
0.18
0 10
024
0.10
Oram
U
11
11
11
4.91
4.18
2.93
3.33
Cobalt
74
74
74
74
1.38
1 50
1.26
103
Copr«
18
19
22
23
12.55
11.36
11.02
15.61
bom
1000
1000
1000
1000
4311.86
4161.45
2747.10
1873.14
U*
18
18
23
25
7.55
7.28
6.49
532
TlnirTri
5-4
5.4
54
5.4
91.18
101.33
367.74
13139
ll«raqr
0.91
0.91
0.91
0.91
015
0.17
016
0.23
lttcfaal
103
105
120
130
8J9
7.86
8.81
6.66
SMh
2
3
4
5
5.90
5.88
5.83
6.63
TMfaua
<40
<40
<40
<40
232
1.60
1.60
1.60
VmMiii
62
62
62
62
6.88
6.05
3.77
3.63
Zmk
236
242
277
299
24.00
2237
2933
36.69
C>aytii««l»
Aaf«i«
2124
2491
2121
2011
0.24
0.29
3.12
031
Cpmidm
5.2
5.2
5.2
5.2
5.26
5.17
12.63
3.73
H***e^e/U9S%LCL)
-
-
-
-
222.23
228.92
26836
294.40
10 <95%UCL)
-
-
-
-
735
7.47
7.78
7 83
pH(95*LCL)
•
-
-
-
7.27
7.28
738
738
-
-
-
*
244
23.7
2U
21.1
FAHi
3*
18
3.8
3*
500
5.00
5.00
23.28
Hiam|iJ|ijiii
1.6
1.6
1.6
1.6
6.59
500
9.19
23.28
BMBfbJlHalM
1.10
1.10
1.10
1.10
6.59
5.00
9.19
23.28
0.74
0.74
0.74
0.74
639
5.00
9.19
23-28
a—n^vjf iii^i
1.09
109
1.09
1.09
639
5.00
9.19
23.28
Ckrjmm
3.47
*47
3.47
3.47
5 00
500
5 00
23.28
ri1aitO>^Hia«
048
0.48
0.48
0.48
639
500
9.19
23.28
047
0.47
0.47
0.47
6.59
5 00
9.19
23.28
iy>M
17.00
17.00
17.00
17.00
5.00
5.00
3.00
23-28
lower Ottawa River SUM
Page i of 4
RM
0-3.2
Chrome HQ
RM RM
3.2-4.9 4.9-6.5
RM
6.5 - 8 8
299E+01
2.52E+01
I.43E+01
1.27E+01
3.50E-02
3.50E-02
3.50E-02
1.87E-01
1.34E-02
2.25E-02
7.67E-03
7.67E-03
4.38E-02
4.78E-02
5.94E-02
4.85E-02
3.93 E-02
2.12E-02
4.53E-02
1.74E-02
4.46&-01
3.80E-01
2.66E-0I
3.03E-01
1.87E-02
2.03 E-02
170E-02
139E-02
6.80E-01
6 00E-01
5 08E-01
6.65E-01
431E+00
4.16E+00
2.75E+O0
1.87E+00
4.25E-01
3.95E-01
2.88E-01
2.10E-01
169E+0I
J.88E+01
6.81E+01
2.43E+01
1.62E-01
1.91E-01
I.73E-01
252E-01
7.99E-02
7.48E-02
7.32B-02
5.12E-02
2.95E+00
1.96E+00
146E+00
1 33E+00
630E-02
4.00E-02
4.00E-02
400E-02
M1E-01
9.76E-02
6.08E-02
586E-02
1.02B-01
9.34E-02
1.06E-01
123E-01
1.11E-04
1.15E-04
1.47E-03
1.53E-04
t.OlE+OO
9.94E-01
2.43E+00
7.18E-01
1J2E+O0
1.32E+00
132E+00
6.13E-HK)
4.12E+00
3J3E+00
5.74E+00
I.46E+01
5.99E+00
455E+00
836E+00
2.I2E+01
8.93E+O0
6.78E+O0
1.25E+01
3.16E+01
6.06E+00
4.60E+00
8.46E+00
2.14E+0J
1.44E+00
1.44E+00
1.44E+00
6.71E+00
137E+01
1.04E+01
1.91E+01
4.85E+01
M1E+0I
107E+0!
1.97E+01
4.98E+01
2.94E-01
2.94 E-01
2.94E-01
137E+00
-------
Tabic C-4. Acute and chronic hazard quotient* for aquatic life based on surface water exposures.
Chronic Screwing ViJuc »5H UCL Sur&ot'W^cf Concentration Qig/L) Chronic HQ
RM
RM
RM
RM
RM
RM
RM
RM
RM
RM
RM
RM
Chemical
0-5.2
3.2-4 9
4.9-6.5
6.5-8.8
0-3.2
3.2-4.9
4.9-6.5
6.5-8.8
0-32
3 2-4.9
4.9-6.5
6.5-88
Pesticides
AblBM
4.5
45
4 5
4.5
5.38
500
5.00
5.00
1.20E+00
1 11E+00
1 UE+00
I UE+00
SswIroletUs Orgulcs
l,i'-Btph«nyi
230.00
230.00
230.00
230.00
5.00
5.00
5.00
23.28
2.17E-02
2.17E-02
2.17E-02
1 01E-01
2-Cbcnfknoi
too.oo
100.00
100.00
100.00
5.00
500
5.00
23.28
5.00E-02
5.00E-02
500E-02
2.33E-01
2,4,5-Tricfa2oropfcenoi
45.00
45.00
45.00
45.00
12-50
12 SO
12.50
58.21
2.78E-01
2.78E-01
2.78E-01
1.29E+00
2,4,6-TncUoroplMBal
18.00
1800
18.00
18.00
5 00
5.00
5.00
23.28
2.78E-01
2.78E-01
2.78E-01
1.29E+00
2,4*IkcUaiopbMol
<95.4
<994
<99.4
<99.4
5.00
5.0Q
5.00
23.28
5.03E-02
5.03E-02
5.03E-02
2.34E-01
2,4'DuBetfcyiphenol
210.00
210.00
21000
210.00
5.00
500
5.00
23.28
238E-02
2.38E-02
2.38E-02
1 1IE-01
2,4-DuutroplNnol
6.00
6.00
6.00
6.00
1250
12.50
12.50
58.21
2.08E+00
2.08E+00
2.08E+00
9.70E+00
2-Methyipbaeioi
500.00
500.00
500.00
500.00
5.00
5.00
5.00
23 28
l.OOE-02
1.00E-02
1.00E-02
4.66E-02
2-Nitropfaeaai
160.00
J 60.00
160.00
160.00
5.00
5.00
5.00
23.28
3.13E-02
3.13E-02
3.13E-02
1.46E-0I
3^,"CHcUo(otwBcidiiM
105.00
105.00
105.00
105.00
5.00
5.00
5.00
23.28
4.76E-02
4.76E-02
4.76E-02
2.22E-01
4,6-Duutro-2-aietfiyi|>beacl
6.60
6.60
660
6.60
1250
12.50
1250
58.21
189E+00
1.89E+00
1.89E+00
882E+00
4*ddoih3-««d^lp)woi
91,70
91,70
91.70
9170
5.00
5.00
5.00
23.28
5.45E-02
5.45E-02
5.45E-02
2.54E-01
4'M«dq4plMol
140.00
140.00
140 00
14000
5.00
5.00
5.00
23.28
3.57E-02
3.57E-02
3.57E-02
1 66E-01
4-Nitropheaol
110.00
110.00
110.00
110.00
12 50
12.50
1250
58.21
1.14E-01
U4E-G1
1 14E-01
5.29E-01
bu(2-EtJiyIii«xyi)phth*Ut*
360.00
360.00
360.00
360.00
5.00
6.02
6.02
28.60
1.39E-02
! 67E-02
1.67E-02
7.94E-02
Bafylbenzyiphthslrts
60.00
60.00
60.00
60.00
5.00
5.00
5.00
23.28
8.33E-02
8.33E-02
833E-02
3.88E-01
Diaetfcy^hthald*
14859.34
1485934
14859.34
14859.34
5.00
5 00
5 00
5.00
3.36E-04
3.36E-04
3.36E-04
3.36E-04
Di-fi-octyiphtkklate
93.20
93.20
93-20
93.20
6.59
5 00
9.19
23.28
7.07E-02
5.36E-02
986E-02
2.50E-01
PstttocUocopheaol
8 74
8.87
9.76
9.84
12-50
12.50
1250
58.21
1.43E+00
1.41E+00
1.28E+00
5.91E+00
Phenol
4.50
4.50
4.50
4.50
500
5.00
5.00
23.28
1.11E+00
1.11E+00
I 11E+00
5.17E+00
RM - River Mil*
HQ * Uizard Qnotieat
UCL — Upper Confidence Limit
lower Ottawa After SLRA
Page 4 of 4
-------
Table C-5. Hazard quotients for aquatic fife based on sediment exposures (Data from Inventory IS 11998)).
95% UCL
Chemical
Depth (inchct)
Unit*
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.3
RM 6.5-8.8
RM >8.8
Metmb
Aneoic
Barinm
Chromium
Lead
Meronry
Sdcsima
Silver
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mgAg
mg/kg
mgAcg
mg/kg
mg/kg
mg/kg
9.18
5.39
122.42
58.70
3.04
0.60
86.83
17.90
105.29
23.96
0.38
0.17
1.24
1.17
0.57
0.45
9.23
7.34
146.46
108.08
4.89
Z18
135.25
63.60
175.36
116.28
0.64
0.33
1.26
1.35
139
2.28
6.59
10.60
104.86
162.59
2.32
3.88
7Z92
271.97
144.95
196.32
0.19
0.72
0.39
1.32
1.22
2.93
9.53
6.34
103.69
57.42
1.14
0.58
63.55
64.24
139.06
183.37
0.22
0.24
0.56
0.67
1.24
0.31
11.60
10.20
85.80
103.00
0.76
0.60
29.20
23.10
49.00
14.60
0.14
0.02
0.35
1.80
0.30
0.50
PAH«
' Bcazo|b)flaaanlhcoc
OqfKK
Ftaarantfccac
Pjiwe
0-24
>24
0-24
>24
0-24
>24
0-24
>24
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mgftg
mg/kg
mg/kg
0.232
0.056
0.262
0.054
0.614
0.090
0.455
0.062
0.514
0.167
0.289
0.133
1.246
0.120
0.668
0.145
0.593
0.287
0.475
0.221
1.345
0.320
1.307
0.243
0.945
0.322
0.893
0.270
2.113
0.241
1.586
0.299
0.500
0.031
0.021
0.031
0.800
0.031
0.730
0.036
rcs»
PCS Arodor 1016
PCB Aroclor 1242
0-24
>24
0-24
>24
mg/kg
mg/kg
mg/kg
mg/kg
0.014
0.008
1.160
0.014
1.136
0.246
0.946
1.680
38.263
0.028
Z709
0.420
0.586
0.009
2.221
0.013
0.009
0.005
0.013
0.010
October 2001
Lower Ottawa River SLRA Page 1 of14 553-3763-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS [1998]).
95% UCL
Chemical
Depth (inches)
Units
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM >8.8
PCB Aroclor 1254
0-24
mg/kg
0.022
0.035
1.263
0.426
0.160
>24
mg/kg
0.010
0.126
0.318
0.006
0.010
PCB (total)3
0-24
mg/kg
1.20
2.12
42.24
3.23
0.18
>24
mg/kg
0.03
2.05
0.77
0.03
0.02
Scmivolatile Orjanlci
2,4,6-Tribromophenol
0-24
mg/kg
4.724
3.601
3.007
3.293
2.600
>24
mg/kg
5.406
3.806
3.580
3.062
6.700
2-Fluorobiphenyl
0-24
mg/kg
2.976
2.318
1.629
2.050
1.500
>24
mg/kg
3.267
2.694
2.251
1.886
4.300
2-Fluorophcnol
0-24
mg/kg
3.722
3.780
3.041
3.354
2.900
>24
mg/kg
4.001
4.398
3.558
2.879
4.600
bis(2-Ethyihexyl)phthalate
0-24
mg/kg
1.044
3.064
70.148
0.921
0.810
>24
mg/kg
0.043
3.392
75.696
0.354
0.021
Auxiliary Parameters
Total Organic Caibon (95%LCL)
0-24
%
3.2
2.6
1.1
1.2
0.5
>24
%
5.2
3.4
0.8
0.8
5.8
'Units are mg/kg OC for PCBs and PAHs, mglcg dw sediment for all other chemicals.
'The sediment guideline! expressed on an organic carbon basis are adjusted using the mean total organic carbon concentration for each river segment in the HQ calculations.
'Total PCBs was estimated by summing the concentrations of Aroclor 1016,1242, and 1260.
dw = dry weight
OC = Organio Carbon
RM = River Mile
Lower Ottawa River SLRA
Page 2 of 14
October 2001
553-3763-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 15 |1998|).
Sediment Guidelines
Di Toro et a!
IngenoU et aL (1996) Environment Canada (1995) Ontario (1993) (2000)
ERL ERM TEL PEL TEL PEL LEL SEL
Chemical Depth (inchct) (mg/kgdw) (mg/kg dw) (mg/kg dw) (mg/kgdw) (mg/kgdw) (mg/kgdw) (mg/kgdw) (mg/kg)'"' (mg/kg OC/
Mctab
Aneaic
0-24
13
50
11
48
5.9
17
6
33
-
>24
13
50
11
48
5.9
17
6
33
-
Bariaa
0-24
-
-
-
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
-
-
Cadmium
0-24
0.7
3.9
0.58
3.2
0.596
3.53
0.6
10
-
>24
0.7
3.9
0.58
3.2
0.596
3.53
0.6
10
-
Cboninm
0-24
39
270
36
120
37.3
90
26
110
.
>24
39
270
36
120
37.3
90
26
110
-
Lead
0-24
55
99
37
82
35
91.3
31
250
-
>24
55
99
37
82
35
91.3
31
250
-
Mercury
0-24
-
-
-
-
0.174
0.486
0.2
2
-
>24
-
-
-
-
0.174
0.486
0.2
2
-
Selenium
0-24
-
-
-
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
-
-
Silver
0-24
-
-
-
-
• -
-
-
-
-
>24
-
-
-
-
-
-
-
-
-
PAH*
Bcnzofbjfloccanthcnc
0-24
-
-
-
-
-
-
-
-
1656
>24
-
-
-
-
-
-
-
-
1656
Chyaenc
0-24
0.03
0.5
0.027
0.41
0.0571
0.862
0.34
460
1427
>24
0.03
0.5
0.027
0.41
0.0571
0.862
0.34
460
1427
Fluorantheae
0-24
0.033
0.18
0.031
0.32
0.111
2.355
0.75
1020
11%
>24
0.033
0.18
0.031
0.32
0.111
2.355
0.75
1020
11%
Pyrene
0-24
0.04
0.35
0.044
0.49
0.053
0.875
0.49
850
1180
>24
0.04
0.35
0.044
0.49
0.053
0.875
0.49
850
1180
PCBa
PCB Aroelor 1016
0-24
-
-
-
-
-
-
0.007
53
-
>24
-
-
-
-
-
-
0.007
53
-
PCB Aroctor 1242
0-24
-
-
-
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
.
.
Lower Ottawa River SLRA
Page 3 of14
October 2001
555-3763-001
-------
Table C-S. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS [1998]).
Sediment Guidelines
Di Toro et al
Ingcrsoll ct al. (1996) Environment Canada (1995) Ontario (1993) (2000)
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
CsQG
Chemical
Depth (inches)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg)'-1
(mg/kg OC):
PCB Aroclor 1254
0-24
.
0.06
34
>24
-
-
-
-
-
-
0.06
34
.
PCB (total)5
0-24
0.05
0.73
0.032
0.24
0.0341
0.277
0.07
530
>24
0.05
0.73
0.032
0.24
0.0341
0.277
0.07
530
•
ScmivolatUt Organic!
2,4,6-Tribrotnophenol
0-24
-
-
-
-
-
.
>24
-
-
-
-
.
„
2-FIuorobiphcnyl
0-24
-
-
-
-
>24
-
-
-
.
.
2-Fluorophcnol
0-24
-
-
-
-
.
>24
-
-
-
.
bu(2-Ethylhexyl)phthalate
0-24
-
-
-
-
_
>24
-
-
-
*
-
Auxiliary Parameter*
Total Organic Caibon (9S%LCL)
0-24
-
-
-
-
-
-
_
>24
-
-
-
-
-
-
-
-
-
'UniU arc mg/kg OC for PCBs and PAHs, rag/kg dw sedimcn
iThe sediment guidelines expressed on an organic carbon basi
JTotal PCBi was estimated by summing the concentrations of
dw = dry weight
OC = Organic Caibon
RM = River Mile
Lower Ottawa River SLRA
Page 4 of 14
October 2001
555-^63-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS [1998]).
Hazard Quotients - RM 0-3.2
^JngOToll_et«l^(I996)^
Chemical
Depth (mchea)
ERL
ERM
TEL
PEL
Mitab
Arieaic
Barium
Cadmium
Chromium
Lead
Mercury
Selenium
Silver
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0.71
0.41
4.34
0.86
2.23
0.46
1.91
0.44
0.18
0.11
0.78
0.15
0.32
0.07
1.06
0.24
0.83
0.49
5.24
1.04
2.41
0.50
2.85
0.65
0.19
0.11
0.95
0.19
0.72
0.15
1.28
0.29
Environment Canada (199S)
TEL PEL
1.56
0.91
5.10
1.01
2.33
0.48
3.01
0.68
2.19
0,96
0.54
0.32
0.86
0.17
0.96
0.20
1.15
0.26
0.78
0.34
Ontario (1993)
LEL
1.53
0.90
5.07
1.00
3.34
0.69
3.40
0.77
1.91
0.84
SEL
0.28
0.16
0.30
0.06
0.79
0.16
0.42
0.10
0.19
0.08
Di Toro et al
(2000)
CsQO
PAH*
Benzo{bjfhio«*nthene
Cluyaeae
Fborantheae
Pyrene
PCS*
PCB Aroclor 1016
PCB Aroclor 1242
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
8.72
I.81
18.60
2.73
II.38
1.55
0.52
0.11
3.41
0.50
1.30
0.18
9.69
2.01
19.80
2.90
10.35
1.41
0.64
0.13
1.92
0.28
0.93
0.13
4.58
0.95
5.53
0.81
8.59
1.17
0.30
0.06
0.26
0.04
0.52
0.07
0.77
0.16
0.82
0.12
0.93
0.13
2.00
1.21
0.018
0.004
0.019
0.003
0.017
0.002
0.008
0.005
0.004
0.001
0.006
0.00!
0.016
0.002
0.012
0.002
Lower Ottawa River SLRA
Page 5 of 14
October 2001
555-3763-00]
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 15 (1998]).
Hazard Quotients • RM 0-3.2
Ingeisoll et al. (1996)
Environment Canada (1995)
Ontario (1993)
Di Toro et al
(2000)
Chemical
Depth (inches)
ERL
ERM TEL
PEL
TEL PEL
LEL SEL
<-SQG
PCB Aroclor 1254
PCB ftotal)1
0-24
>24
0-24
>24
23.91
0.66
1.64 37.37
0.05 1.03
4.98
0.14
35.06 4.32
0.97 0.12
0.37 0.021
0.17 0.010
17.08 0.072
0.47 0.002
-
SemivelatHe Organic*
2,4,6-Tribromophenol
2-Ftuorobipheny!
2-FluorophcnoI
bis(2-Ethylhexyl)phthalate
0-24
>24
0-24
>24
0-24
>24
0-24
>24
-
-
-
-
-
"
Auxiliary Panmrtm
Total Organic Carbon (95%LCL)
0-24
>24
-
-
-
-
_
_
'Units arc mg/kg OC for PCBs and PAHs, mg/kg dw scdimen
iTTic sediment guidelines expressed on an organic carbon basi
'Total PCBs was estimated by summing the concentrations of
dw = dry weight
OC = Organic Carbon
RM = River Mile
Lower Ottawa River SLRA
Page 6 of 14
October 2001
555-3763-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS [1998J).
Hazard Quotient! - RM 3.2-4.9
Ingenoll et iL (1996)
Chemical
Depth (incheQ ERL
ERM
TEL
PEL
Environment Canada (1995)
TEL PEL
Mctafa
Arienic
Barium
Cadmium
Chromium
Lead
Mercury
Selenium
Silver
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0.71
0.56
6.99
3.12
3.47
1.63
3.19
2.11
0.18
0.15
1.25
0.56
0.50
0.24
1.77
1.17
0.84
0.67
8.44
3.76
3.76
1.77
4.74
3.14
0.19
0.15
1.53
0.68
1.13
0.53
2.14
1.42
1.56
1.24
8.21
3.66
3.63
1.71
5.01
3.32
3.70
1.92
0.54
0.43
1.39
0.62
1.50
0.71
1.92
1.27
1.32
0.69
Ontario (1993)
LEL
1.54
1.22
8.16
3.64
5.20
2.45
5.66
3.75
3.22
1.67
SEL
0.28
0.22
0.49
0.22
1.23
0.58
0.70
0.47
0.32
0.17
Di Toro et al
(2000)
CsQG
FAB*
Bagofl>ffhoi»atbenc
Ouytcae
Fluoranthese
Pyrene
rCBa
PCB Arocior 1016
PCB Aroclor 1242
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
9.65
4.42
37.76
3.63
16.70
3.63
0.58
0.27
6.92
0.67
1.91
0.41
10.72
4.92
40.19
3.86
15.18
330
0.71
0.32
3.89
0.37
136
0.30
5.07
132
11.22
1.08
12.60
2.74
0.34
0.15
0.53
0.05
0.76
0.17
0.85
0.39
1.66
0.16
1.36
0.30
162.22
35.18
0.02
0.01
0.05
0.00
0.03
0.01
0.83
0.18
0.01
0.00
0.008
0.004
0.04
0.00
0.02
0.00
October 2001
Lower Ottawa River SLFA Page7ofl4 555-3763-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data (ram Inventory IS J1998]).
Hazard Quotients - RM 3.2-4.9
Ingereoll et al. (1996)
Environment Canada (1995)
Ontario (1993)
Di Toro el al
(2000)
Chemical
Depth (inches)
ERL
ERM TEL
PEL
TEL PEL
LEL SEL
('sQG
PCB Aroclor 1254
PCB (total)3
0-24
>24
0-24
>24
42.32
41.04
2.90 66.13
2.81 64.12
8.82
8.55
62.06 7.64
60.18 7.41
0.58 0.04
2.10 0.14
30.23 0.16
29.31 0.15
"
SemivolatUe Organic*
2,4,6-TribromophenoI
2-Fluorobiphcnyl
2-Fluorophenol
bis(2-Ethylhcxyl)phthalat«
0-24
>24
0-24
>24
0-24
>24
0-24
>24
-
-
-
•
-
"
Auxiliary Parameter*
Total Organic Caifcon (95%LCL)
0-24
>24
-
-
-
-
-
'Unit* are mg/kg OC for PCBs and PAHs, mg/kg dw sedimen
^Thc sediment guidelines expressed on an organic carbon basi
^otal PCBs was estimated by summing the concentrations of
dw = dry weight
OC = Organic Carbon
RM = River Mile
Lower Ottawa River SURA
Page 8 of 14
October 2001
555-3^63-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS [1998]).
Hazard Quotients - RM 4.9-6.5
Ingcnoll et al. (1996)
Chemical
Depth (inchct)
ERL
ERM
TEL
PEL
Environment Canada (1995)
TEL PEL
Ontario (1993)
LEL
SEL
Di Toro et al
(2000)
Mctab
Anenic
Barium
Cadmium
Chrominm
Lead
Mercury
Selenium
Silver
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0-24
>24
0.51
0.82
3.31
5.55
1.87
6.97
2.64
3.57
0.13
0.21
0.59
1.00
0.27
1.01
1.46
1.98
0.60
0.96
3.99
6.69
103
7.55
3.92
SJ1
0.14
0.22
0.72
1.21
0.61
2.27
1.77
2.39
1.12
1.80
3.89
6.51
1.95
7.29
4.14
5.61
1.10
4.15
0.39
0.62
0.66
1.10
0.81
3.02
1.59
2.15
0.39
1.49
1.10
1.77
3.86
6.47
2.80
10.46
4.68
6.33
0.96
3.61
0.20
0.32
0.23
0.39
0.66
2.47
0.58
0.79
0.10
0.36
PAH*
Bcazo{l>]fhHnndtcae
Chrysenc
Fluoranthene
Pyrate
0-24
>24
0-24
>24
0-24
>24
0-24
>24
15.82
7.37
40.74
9.70
3X68
6.08
0.95
0.44
7.47
1.78
3.73
0.69
17.58
8.19
43.37
10.32
29.70
5.53
1.16
0.54
4.20
1.00
2.67
0.S0
8.31
3.87
1111
2.88
24.66
4.59
0.55
0.26
0.57
0.14
1.49
0.28
1.40
0.65
1.79
0.43
2.67
0.50
0.10
0.05
0.12
0.03
0.15
0.03
0.03
0.02
0.03
0.01
0.11
0.03
0.10
0.02
res*
PCB Araelor 1016
PCB Aroclor 1242
0-24
>24
0-24
>24
5466.13
3.95
68.10
0.05
Lower Ottawa River SLRA
Page 9 of 14
October 2001
555-3763-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS [1998)).
Hazard Quotients - RM 4.9-6.5
Di Toro ct ai
Ingersoll et al. (1996) Environment Canada (1995) Ontario (1993) (2000)
Chemical
Depth (inches)
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
Qjqg
PCB Aroclor 1254
0-24
.
_
.
.
21.05
3.50
>24
-
-
-
-
-
-
5.31
0.88
.
PCB (totaJ)5
0-24
844.71
57.86
1319.86
175.98
1238.58
152.47
603.36
7.52
>24
15.31
1.05
23.93
3.19
22.45
2.76
10.94
0.14
-
Semivolatik Organic*
2,4,6-Tribromophenol
0-24
-
-
-
-
-
-
-
.
>24
-
-
-
-
-
-
-
.
2-FhiorobiphenyI
0-24
-
-
-
-
-
-
.
>24
-
-
-
-
•
-
_
_
2-FluorophenoI
0-24
-
-
-
-
-
-
.
.
>24
-
-
-
-
-
-
_
_
bis(2-Ethy!hexyl)phthaIate
0-24
-
-
-
-
-
-
-
.
>24
-
-
-
-
-
¦
-
-
Auxiliary Parameters
Total Organic Caibon (95%LCL)
0-24
-
-
-
-
-
-
-
.
.
>24
•
-
-
-
-
-
-
-
-
'Units are mgAtg OC for PCBs and PAHs, mg/kg dw sedimen
'The sediment guideline* expressed on an organic carbon basi
^otal PCBs was estimated by summing the concentrations of
dw = dry weight
OC = Organic Carbon
RM = River Mile
Lower Ottawa River SLRA
Page iO of 14
October 2()01
555-3763-001
-------
Tabic C-5. Hazard quotients for aquatic life based at sediment exposures (Data from Inventory IS [1998]).
Hazard Quotients - RM 6.5-8.8
Di Toro et al
Ingetioll et at (1996) Environment Canada (1995) Ontario (1993) (2000)
Chemical
Depth (inches)
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
CSQG
Metab
Ancaic
0-24
0.73
0.19
0.87
0.20
1.62
0.56
1.59
0.29
>24
0.49
0.13
0.58
0.13
1.08
0.37
1.06
0.19
_
Barium
0-24
-
-
-
-
-
-
.
_
>24
-
-
-
-
-
.
_
Cadmium
0-24
1.62
0.29
1.96
0.36
1.91
0.32
1.89
0.11
>24
0.82
0.15
0.99
0.18
0.97
0.16
0.96
0.06
_
Chromium
0-24
1.63
0.24
1.77
0.53
1.70
0.71
2.44
0.58
_
>24
1.65
0.24
1.78
0.54
1.72
0.71
2.47
0.58
Lead
0-24
2.53
1.40
3.76
1.70
3.97
1.52
4.49
0.56
_
>24
3.33
1.85
4.96
2.24
5.24
2.01
5.92
0.73
Mercury
0-24
-
-
-
-
1.27
0.45
1.10
0.11
>24
-
-
-
-
1.36
0.49
1.18
0.12
_
Selenium
0-24
-
-
-
-
-
-
.
.
.
>24
-
-
-
-
-
-
.
*
_
Silver
0-24
-
-
-
-
-
-
-
.
.
>24
-
-
-
-
-
-
-
-
-
rAHa
Bcaxo[b]flaanB&cac
0-24
-
-
-
-
-
-
-
-
0.05
>24
-
-
-
-
-
-
-
-
0.02
Cluyieac
0-24
29.75
1.79
33.06
2.18
15.63
1.04
2.63
0.16
0.05
>24
9.01
0.54
10.01
0.66
4.74
0.31
0.80
0.05
0.02
Fluannthcnc
0-24
64.04
11.74
68.17
6.60
19.04
0.90
2.82
0.17
0.14
>24
7.31
1.34
7.79
0.75
2.17
0.10
0.32
0.02
0.02
Pyraw
0-24
39.64
4.53
36.04
3.24
29.92
1.81
3.24
0.15
0.11
>24
7.48
0.86
6.80
0.61
5.65
0.34
0.61
0.03
0.02
rak
PCB Arock* 1016
0-24
-
-
-
-
-
-
83.69
0.90
_
>24
-
-
-
-
-
-
1.26
0.01
PCB Afoclar 1242 0-24
>24
Lower Ottawa River SLRA
Page II of 14
October 2001
555-3763-001
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory IS |1998|).
Hazard Quotients - RM 6.5-8.8
Di Toro et al
Ingersoll et al. (1996) Environment Canada (199S) Ontario (1993) (2000)
Chemical
Depth (inches)
ERL
ERM TEL
PEL
TEL
PEL
LEL
SEL
QG
PCB Aroclor 1254
0-24
_
7.10
1.02
>24
-
-
"
-
-
0.10
0.01
-
PCB (total)'
0-24
64.67
4.43 101.04
13.47
94.82
11.67
46.19
0.50
.
>24
0.56
0.04 0.88
0.12
0.82
0.10
0.40
0.00
•
Semi volatile Organic*
2,4,6-Tribromophenol
0-24
-
-
-
-
-
-
-
>24
-
-
-
-
-
.
.
2-Fluorobiphenyl
0-24
-
-
-
-
-
-
>24
-
-
-
-
-
.
2-Fluorophenol
0-24
-
-
-
-
-
.
,
>24
-
-
-
-
-
.
bis(2-Ethylhcxyl)phthalate
0-24
-
-
-
-
-
-
.
>24
-
-
-
-
-
-
-
Auxiliary Parameters
Total Organic Carbon (95%LCL)
0-24
-
-
-
-
-
-
.
>24
-
-
-
-
-
-
-
-
'Units are mg/ltg OC for PCBs and PAHs, mg/kg dw sedimen
''The sediment guidelines expressed on an organic carbon basi
'Total PCBs was estimated by summing the concentrations of
dw - dry weight
OC = Organic Cuboo
RM = River Mile
Lower Ottawa River SLRA
Page 12 of 14
October 2001
SSS-3~63-OOl
-------
Tabic C-5. Hazard quotients for aquatic life based mi sediment exposures (Data from Inventory IS [1998]).
Hazard Quotients . RM >8.8
Di Toro et al
Ingcrsoll et «L (1996) Environment Canada (1995) Ontario (1993) (2000)
Chemical Depth (inches) ERL ERM TEL PEL TEL PEL i.pt.
Metab
Arsenic
0-24
0.89
0.23
1.05
0.24
1.97
0.68
1.93
0.35
>24
0.78
0.20
0.93
0.21
1.73
0.60
1.70
0.31
_
Barium
0-24
-
-
-
-
-
_
.
>24
-
-
-
-
-
.
_
_
Cadmium
0-24
1.09
0.19
1.31
0.24
1.28
0.22
1.27
0.08
.
>24
0.86
0.15
1.03
0.19
1.01
0.17
1.00
0.06
Chromium
0-24
0.75
0.11
0.81
0.24
0.78
0.32
1.12
0.27
.
>24
0.59
0.09
0.64
0.19
0.62
0.26
0.89
0.21
.
Lead
0-24
0.89
0.49
1.32
0.60
1.40
0.54
1.58
0.20
>24
0.27
0.15
0.39
0.18
0.42
0.16
0.47
0.06
.
Mercury
0-24
-
-
-
-
0.80
0.29
0.70
0.07
.
>24
-
-
-
-
0.13
0.05
0.12
0.01
Selenium
0-24
-
-
-
-
.
.
.
>24
-
-
-
-
-
-
_
_
Silver
0-24
-
-
-
-
-
.
.
_
>24
-
-
-
-
-
-
-
-
-
PAHs
B24
-
-
-
-
-
-
-
-
0.00
Chyacne
0-24
0.68
0.04
0.76
0.05
0.36
0.02
0.06
0.01
0.00
>24
1.03
0.06
1.15
0.08
0.54
0.04
0.09
0.01
0.00
Fhior«nthcnc
0-24
24.24
4.44
25.81
2.50
7.21
0.34
1.07
0.15
0.13
>24
0.94
0.17
1.00
0.10
0.28
0.01
0.04
0.01
0.00
Pyreac
0-24
18.25
2.09
16.59
1.49
13.77
0.83
1.49
0.17
0.12
>24
0.90
0.10
0.82
0.07
0.68
0.04
0.07
0.01
0.01
rcB.
PCB Aroctor 1016
0-24
-
-
-
-
-
-
1.21
0.03
.
>24
-
-
-
-
-
-
0.67
0.02
PCB Axodor 1242 0-24
Lower Ottawa River SLRA
Page 13 of 14
October 2001
555-3763-WJl
-------
Table C-5. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 15 |1998]).
Hazard Quotients - RM >8.8
Di Toro el al
IiiRcnoll et aL (1996) Environment Canada (1995) Ontario (1993) (2000)
Chemical
Depth (inches)
ERL
ERM TEL
PEL
TEL
PEL
LEL
SEL
Qsqg
PCB Aroclor 1254
0-24
_
.
.
.
2.67
0.90
>24
-
-
-
-
-
0.16
o.os
.
PCB (total)1
0-24
3.62
0.25 5.66
0.75
5.31
0.65
2.59
0.07
-
>24
0.47
0.03 0.74
0.10
0.70
0.09
0.34
0.01
-
Semivolatile Organ ka
2,4,6-T ribromophenol
0-24
-
•
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
.
2-Fluorobiphenyl
0-24
-
-
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
.
2-Fluorophcnol
0-24
-
-
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
bis(2-Ethy!hexyl)phthaIate
0-24
-
-
-
-
-
-
-
-
>24
-
-
-
-
-
-
-
-
Auxiliary Paramrteri
Total Organic Carbon (95% LCL)
0-24
-
-
-
-
•
-
-
.
>24
-
-
-
-
-
-
-
-
'Unit* are mg/kg OC for PCBs and PAHs, mg/kg dw sedimen
'The sediment guideline! expressed on an organic carbon basi
'Total PCBs was estimated by summing the concentrations of
dw = dry weight
OC = Organic Carbon
RM = River Mile
Lower Ottawa River SLRA
Page 14 of 14
October 2001
555-3763-001
-------
Tabic C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 (2009]).
9S%UCL
Chemical Unite RM 0-3.2 RM 3.2-4.9 RM 4.9-6.5 RM 6.5-8.8
Metals
Ahmnom mg/kg dw
Antimony mg/kg dw
Ancnie mg/kg dw
Barium mg/kg dw
Beryllium mg/kg dw
Cadmium mg/kg dw
Chromium mg/kg dw
Cobalt mg/kg dw
Copper mg/kg dw
Iron mg/kg dw
Lead mg/kg dw
Manganese mg/kg dw
Meroary mg/kg dw
Niokd mg/kg dw
Selcaram mg/kg dw
Saver mg/kg dw
Thallium mg/kg dw
Vanadium mg/kg dw
Zinc mg/kg dw
Cyanide mg/kg dw
PAHs
Anftiaoau mg/kg dw
Bww{a|n<>iwnic mg/kg dw
Benzo{a]pyrc»e mg/kg dw
Bcazo{b]flaanatiHnc mg/kg dw
Baizo{gjM^>crytcac mg/kg dw
Bcnza(k)fiBanBthenc mg/kg dw
Chrysaic mg/kg dw
Dibenzfajijantfcraccac mg/kg dw
FtxnAeM mg/kg dw
Indcno{ 1 ^3-cd|pyrenc mg/kg dw
12443.71 9682.98 9448.21 9196.69
0.67 1.61 1.11 0.37
8.83 6.54 21.13 9.81
119.53 166.80 159.97 269.80
0.61 0.48 0.S6 0.64
2.18 1.71 3.88 2.17
58.48 58.34 137.41 125.40
9.29 7.52 7.45 6.96
92.09 63.16 97.27 101.98
23341.92 19582.41 19475.12 19179.84
99.20 259.17 16324.83 295.71
42039 349.62 370.37 372.78
0.20 0.18 0.81 0.27
42.16 34.78 40.94 23.10
2.44 1.78 Z38 4.93
0.65 0.97 1.99 8.22
4.96 5.22 3.66 6.52
28.44 23.22 22.90 26.55
243.00 287.76 314.58 612.02
0.22 0.26 0.58 Z57
3375 3.043 5.218 9.655
2.907 3.195 1,920 5.913
3.109 2.828 1.827 6.385
2.969 2379 2.453 7.317
3.240 1.872 4.891 4.610
3.098 3.136 2.399 8.048
3.157 2.448 2.833 8.979
3.735 2.983 5.218 9.575
4.452 4.744 4.389 20.153
3.052 2.630 1.837 4.590
lower Ottawa River SLRA
Page lofl2
October 2001
555-3763-001
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 (2000]).
95%UCL
Chemical
Units
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
Phenanthrene
mg/kg dw
3.754
3.474
4.647
7.151
Pyreue
mg/kg dw
3.946
4.013
3.912
12.705
PCBs
PCB Aroclor 1242
mg/kg dw
0.447
2.586
2.428
'2.038
PCB Aroclor 1260
mg/kg dw
0.078
0.092
0.119
0.519
PCB (total)
mg/kg dw
0.53
2.68
2.55
2.56
Organochtorine Pestirtdes
4,4-DDD (p,p'-)
mg/kg dw
0.012
0.019
0.036
0.063
4,4'-DDE(p,p'-)
mg/kg dw
0.015
0.028
0.041
0.034
4,4'-DDT (p,p'-)
mg/kg dw
0.004
0.004
0.013
0.014
Aldrin
mg/kg dw
0.015
0.070
0.042
0.011
alpha-Chlordane
mg/kg dw
0.005
0.006
0.014
0.018
delta-BHC
mg/kg dw
0.002
0.006
0.012
0.001
Dieldrin
mg/kg dw
0.015
0.023
0.013
0.015
Endosulfan II
mg/kg dw
0.004
0.012
0.014
0.028
Endrin ketone
mg/kg dw
0.004
0.006
0.007
0.036
gamma-Chlordane
mg/kg dw
0.011
0.018
0.017
0.008
Heptachlor
mg/kg dw
0.004
0.007
0.003
0.001
HcpUcHlor epoxide
mg/kg dw
0.020
0.058
0.026
0.017
Sent ivola tile Organic*
mg/kg dw
bis(2-Ethylhexyl)phthalatc
mg/kg dw
3.203
6.820
5.239
23.341
Di-n-octylphthalate
mg/kg dw
3.761
4.321
5.049
1.924
AuiHlarj Parameters
Total Organic Carbon (95% LCL or minimum)
%
4.5
3.7
5.5
5.8
'Uniti arc mg/kg OC for PCBi, organochlorinc pesticides, and PAHs; mg/kg dw sediment for all other chemicals.
iThe sediment guidelines expressed on an OC basis are adjusted in the HQ calculations using the mean TOC concentration for each river segment,
dw = dry weight
OC — Organic Cartoon
RM = River Mile
Lower Ottawa River SLRA
Page 2 of 12
October 200J
555-3763-001
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 (2000]).
Chemical
ERL
Sediment Guidelines
Ingereoll ct al. (1996)
ERM
TEL
PEL
Environment Canada (1995)
TEL PEL
Ontario (1993)
LEL
SEL
(mg/kgdw) (mg/kgdw) (mg/kg dw) (mg/kgdw) (mg/kgdw) (mg/kgdw) (mg/kg dw) (mg/kg)'-
Di Toro el al
(2000)
CsQG
(mg/kg OC^
Antimony
Annie
13
38,000
50
11
48
5.9
17
33
Bayfltnai
Cobalt
Copper
boa
Lead
Maaganw
Morasy
Nickel
0.7
39
41
200,000
55
730
24
3.9
270
190
280,000
99
1,700
45
0.58
36
28
190,000
37
630
20
3.2
120
100
250,000
82
1,200
33
0.596
37.3
35.7
35
0.174
18
3.53
90
197
91.3
0.486
35.9
0.6
26
16
20,000
31
460
0.2
16
10
110
no
40,000
250
1,100
2
75
Silver
ThaiUam
Zinc
110
550
98
540
123
315
120
820
Cyanide
PAH*
Aatncac
Beazo{a}antiuaocae
Bcnzo{a]pynac
Baao[b|fliM aatfcene
Bcazo(gJufe>crylc
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 [2000]).
Sediment Guidelines
Di Toro et al
Ingcrsoll et al. (1996) Environment Canada (1995) Ontario (1993) (2000)
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
CsQG
Chemical
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg dw)
(mg/kg)'"'
(mg/Vg OC/
Phenanthrcne
0.027
0.35
0.019
0.41
0.0419
0.515
0.56
950
1008
Pyrene
0.04
0.35
0.044
0.49
0.053
0.875
0.49
850
1180
PCB*
PCB Aroclor 1242
-
-
-
-
-
-
-
.
.
PCB Aroclor 1260
-
-
-
-
-
-
0.005
24
.
PCB (total)
0.05
0.73
0.032
0.24
0.0341
0.277
0.07
530
-
OrganacMorine Pesticides
4,4'-DDD (p>p'-)
-
-
0.00354
0.00851
0.008
6
-
4,4-DDE (p,p'-)
-
-
0.00142
0.00675
0.005
19
-
4,4'-DDT (p,p'-)
-
-
0.00698
4.45
0.007
12
.
Aldrin
-
-
-
-
0.002
8
.
alpha-Chlordane
-
-
-
-
-
-
-
delta-BHC
-
-
-
-
-
-
.
Dieldrin
-
-
0.00285
0.00667
0.002
91
Endoeulfan 11
-
-
-
-
-
.
Endrin ketone
-
-
-
-
-
-
.
gamma-Chlordane
-
-
-
-
-
-
.
Heptachlor
-
-
-
-
-
-
-
Heptachlor epoxide
-
-
0.0006
0.00274
0.005
5
-
Semivoiatilc Organic*
bis(2-Ethylltexyl)phthalatc
-
-
-
-
-
-
-
-
.
Di-n-octylphthalatc
-
-
•
-
-
-
-
-
-
Auxiliary Parameter*
Total Organic Carbon (95% LCL or minimum)
"
*
•
-
-
-
-
-
-
'Uniti are mg/Vg OC for PCB«, organochlorine pcstici
'The sediment guideline* expressed on an OC basis ar
dw - dry weight
OC = Organic Carbon
RM = River Mile
Lower Ottawa River SLRA
Page 4 of 12
October 2001
55S-3-'6*-001
-------
Table C4, Hazard quotients for aquatic fife based on sediment exposures (Data from Inventory 2d [2000]).
ERL
Ingcnoll ct aL (1996)
ERM
TEL
Hazard Quotient - RM 0-3.2
PEL
Environment Canada (1993)
TEL PEL
Ontario (1993)
LEL
SEL
Di Toro et al
(2000)
CSQG
Mctab
Antimony
Aneaio
Barium
Beryllium
Cobah
Copper
Iroo
Lad
Mcrcary
Nickel
Silver
Ziac
0.68
3.11
1.50
2.25
0.12
1.80
0.58
1.76
2.21
0.21
0.18
0.56
0.22
0.48
0.08
1.00
0.25
0.94
0.44
0.80
3.76
1.62
3.29
0.12
2.68
0.67
2.11
2.48
0.18
0.68
0.49
0.92
0.09
1.21
0.35
1.28
0.45
1.50
3.66
1.57
2.58
2.83
1.15
2.34
1.98
0.52
0.62
0.65
0.47
1.09
0.41
1.17
0.77
1.47
3.63
2.25
5.76
1.17
3.20
0.91
1.00
2.64
2.03
0.27
0.22
0.53
0.84
0.58
0.40
0.38
0.10
0.56
0.30
FAHs
Bca2o[a}ariHascac
Bcamfafarcae
BeazofbJOoanalbeae
Bfg7f>[g>.ilperykne
Bcazopcpaanaliwae
QqMK
Dibcaz{ajijaatbraccne
lndeao{ I ^3-odJpyreae
337.55
152.99
37.01
249.21
105.22
373.54
134.92
101.75
24.11
9.69
6.62
11.57
6.31
24.74
12.21
337.55
181.68
97.16
202.49
116.92
373.54
143.63
179.56
19.86
10.38
9.72
12.96
7.70
13.91
12.72
91.70
97.47
55.28
40.11
7.55
3.98
3.66
1.89
15.34
9.08
8.40
19.06
12.91
9.28
62.26
5.94
.15.26
0.20
0.04
0.05
224.71
0.05
0.15
0.64
0.10
0.21
0.07
0.05
0.04
0.04
0.04
0.04
0.05
0.04
0.08
0.04
Lower Ottawa River SLRA
Page 5 of 12
October 200J
555-3763-001
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 12000]).
Hazard Quotients - RM 0*3.2
Di Toro et al
tngcrsoll ct al. (1996) Environment Canada (1995) Ontario (1993) (2000)
Chemical
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
CSQG
Phenanlhrene
139.03
10.73
197.57
9.16
89.59
7.29
6.70
0.09
0.08
Pyrcne
98.65
11.27
89.68
8.05
74.45
4.51
8.05
0.10
0.07
FCBa
PCB Arocior 1242
-
-
-
-
-
-
-
-
-
PCB Aroclor 1260
-
-
-
-
-
-
15.66
0.07
-
FOB (total)
10.50
0.72
16.41
2.19
15.40
1.90
7.50
0.00
¦
Ortanochlorinc FatfcMa
4,4'-DDD (p,p'-)
-
-
3.50
1.46
1.55
0.05
-
4,4'-DDE (p,p'-)
-
-
10.86
2.29
3.08
0.02
-
4,4-DDT (p,p'->
-
-
0.63
0.00
0.63
0.01
-
Aldrin
-
-
-
-
7.52
0.04
-
alpha-Chlordane .
-
-
-
-
-
-
-
delta-BHC
-
-
-
-
-
-
-
Dieldrin
-
-
5.33
2.28
7.60
0.00
.
Endoculfan II
-
-
-
-
-
-
.
Endrin ketone
-
-
-
-
-
-
.
gamma-Chlordane
-
-
-
-
-
-
-
Heptachlor
-
-
-
-
-
-
-
Heptachlor epoxide
-
-
33.45
7.32
4.01
0.09
-
Semfcolatilc Organies
bis(2-EthylhexyI)phthalate
-
-
-
-
-
-
-
-
-
Di-n-octylphthalate
-
-
-
-
-
-
-
-
Auxiliary Parameters
Total Organic Caibon (95% LCL or minimum)
-
"
-
¦
-
-
-
-
-
'Unit! are mg/kg OC far PCBs, organochlorine pestici
''The sediment guideline* expressed on an OC basis ar
dw = dry weight
OC = Organic Caibon
RM = River Mile
Lower Ottawa River SLRA
Page 6 of 12
October 2001
555-3763-001
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 [2000]).
Chemical
ERL
Hazard Quotient! - RM 3.2-4.9
Ingcrsoll ct al- (1996)
ERM
TEL
PEL
Environment Canada (1995)
TEL PEL
Ontario (1993)
LEL
SEL
Di Toro ct al
(2000)
CSQG
Mctab
Aluminum
Antimony
Ancaic
Bctytlium
Cadmium
Chromium
Cobalt
Copper
Iroa
Lead
Manganeac
Mercury
Niokel
Sdeuaa
Silver
Thallium
Zinc
o.so
2.44
1.50
1.54
0.10
4.71
0.48
1.45
2.62
0.17
0.13
0.44
0.22
0.33
0.07
2.62
0.21
0.77
0.52
0.59
2.95
1.62
2.26
0.10
7.00
0.55
1.74
2.94
0.14
0.53
0.49
0.63
0.08
3.16
0.29
1.05
0.53
1.11
2.87
1.56
1.77
7.40
1.02
1.93
2.34
0.38
0.48
0.65
0.32
2.84
0.37
0.97
0.91
1.09
2.85
2.24
3.95
0.98
8.36
0.76
0.89
2.17
2.40
0.20
0.17
0.53
0.57
0.49
1.04
0.32
0.09
0.46
0.35
PAHi
Bcnzo{a]anlhnceac
Bcazofajpyrcoc
BaaWhnwHwe
BcnoitlMlrcqkK
Btazo|k|fiKfmftcK
Chryscac
Dibeaz(aJi]aatliraoaie
Fhwranthcne
Indcnojl,2,3-cd|pyrcnc
304.29
168.16
33.67
144.03
81.60
298.27
143.77
87.67
21.74
10.65
6.02
6.69
4.90
26.36
10.52
304.29
199.69
88.38
117.02
90.67
298.27
153.05
154.71
17.90
11.41
8.84
7.49
5.97
14.83
10.96
100.79
88.66
42.87
42.74
8.30
3.62
2.84
2.01
13.83
9.98
7.64
11.01
13.07
7.20
49.71
6.33
13.15
0.22
0.06
0.05
159.25
0.06
0.14
0.62
0.13
0.22
0.08
0.06
0.05
0.04
0.03
0.05
0.05
0.04
O.U
0.04
Lower Ottawa Rrver SLRA
Page 7 of 12
October 200J
555-3763-00!
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 [2000]).
Hazard Quotients - RM 3.2-4.9
Di Toro ct al
Ingcreoll et al. (1996)
Environment Canada (1995)
Ontario (1993)
(2000)
Chemical
ERL
ERM TEL
PEL
TEL
PEL
LEL
SEL
CSQG
Phenanthrenc
128.68
9.93 182.86
8.47
82.92
6.75
6.20
0.10
0.09
Pyrene
100.33
11.47 91.21
8.19
75.72
4.59
8.19
0.13
0.09
rcB*
PCB Aroolor 1242
-
-
-
-
-
-
-
-
PCB Aroclor 1260
-
-
-
-
-
18.32
0.10
-
PCB (total)
53.55
3.67 83.67
11.16
78.52
9.67
38.25
0,01
-
OrganocMortnc Pertktdea
4,4'-DDD (p,p-)
-
-
-
5.45
2.27
2.41
0.09
-
4,4'-DDE (p,p'-)
-
-
-
19.44
4.09
5.52
0.04
-
4,4'-DDT (p,p'-)
-
-
-
0.55
0.00
0.55
0.01
-
Aldrin
-
-
-
-
-
35.00
0.24
-
alpha-Chlordane
-
-
-
-
-
-
-
-
delta-BHC
-
-
-
-
-
-
-
-
Dieldrin
-
-
-
8.21
3.51
11.70
0.01
-
Endoautfan II
-
-
-
-
-
-
-
-
Endrin ketone
-
-
-
-
-
-
-
.
gamma-Chlordanc
-
-
-
-
-
-
-
-
Heptachior
-
-
-
-
-
-
-
-
Heptachior epoxide
-
-
-
96.34
21.10
11.56
0.31
-
Seahrolatile Organic*
bi«(2-EthyIheiyl)ptithalaie
-
-
-
-
-
-
-
-
Di-n-octyiphthaUtc
-
-
-
-
-
-
-
-
Auxiliary Parameter!
Total Organic Caifcon (95% LCL or minimum)
-
-
-
-
-
-
-
-
'Units are mg/kg OC for PCBs, organocblorinc pestici
^TTic sediment guide tines expressed on an OC basis ar
dw - dry weight
OC - Organic Carbon
RM - River Mile
Lower Ottawa River SLRA
Page 8 of 12
October 2001
555-3^63-001
-------
Tabic C-6. Hazard quotients for aquatic tffe based on sediment exposures (Data from Inventory 20 [2000]).
Chemical
ERL
Hazard Quotient* - RM 4.9-6.5
Ingenoll et al (1996)
ERM
TEL
PEL
Environment Canada (1995)
TEL PEL
Ontario (1993)
LEL
SEL
Di Toro et al
(2000)
CSQG
Metal.
Ahunnom
Antimony
Arsenic
1.63
0.16
0.42
1.92
0.44
3.58
1.24
3.52
0.64
Beryllium
Cadmium
Chromium
Cobalt
Copper
boa
Lead
Manganese
Mtnoy
Nickel
5.54
3.52
2.37
0.10
296.82
0.51
1.71
0.99
0.51
0.51
0.07
164.90
0.22
0.91
6.69
3.82
3.47
0.10
441.21
0.59
Z05
1.21
1.15
0.97
0.08
199.08
0.31
1.24
6.51
3.68
2.72
466.42
4.63
2.27
1.10
1.53
0.49
178.80
1.66
1.14
6.46
5.29
6.08
0.97
526.61
0.81
4.03
2.56
0.39
1.25
0.88
0.49
65.30
0.34
0.40
0.55
Silver
Zinc
2.86
0.57
3.21
0.58
2.56
1.00
2.62
0.38
Cyanide
FAHs
Aathnocae
Beazo{a)aatiraocnc
Bcazo{a]pyrcac
Bcmo(b|flmn inltyae
Bcazo{&JM]pcryiaie
Bcazo{k)Qaanaftcae
Chiywme
Dibcaz[ajb {anthracene
Fluonmifacne
lndeiio(l,2^-cd]pyrene
521.76
101.04
21.75
376.20
94.43
52176
132.99
61.24
37.27
6.40
3.89
17.47
5.67
24.38
7.35
521.76
119.99
57.08
30S.66
104.92
521.76
141.57
108.06
30.69
6.86
5.71
19.56
6.91
13.71
7.65
60.56
57.26
49.61
39.54
4.99
2.34
3.29
1.86
23.72
6.00
4.94
28.77
10.00
8.33
86.96
5.85
9.19
0.26
0.02
0.02
276.69
0.03
0.11
073
0.08
0.10
0.09
0.02
0.02
0.03
0.05
0.03
0.04
0.05
0.07
0.02
Lower Ottawa River S2JIA
Page 9 of 12
October 2001
555-3763-001
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 [2000]).
Hazard Quotients - RM 4.9-6.5
Di Tore et al
Ingeraoli ct al. (19%) Environment Canada (1995) Ontario (1993) (2000)
Chemical
ERL
ERM TEL
PEL
TEL
PEL
LEL
SEL
CSQG
Phenanthrene
172.11
13.28 244.58
11.33
110.91
9.02
8.30
0.09
0.08
Pyrene
97.81
11.18 88.91
7.98
73.82
4.47
7.98
0.08
0.06
PCBs
PCB Aroclor 1242
-
-
-
-
-
-
-
-
PCB Aroclor 1260
-
-
-
-
-
23.72
0.09
PCB (total)
50.93
3.49 79.57
10.61
74.67
9.19
36.38
0.00
-
Organachlortne Pesticides
4,4-DDD (p,p'-)
-
-
10.19
4.24
4.51
0.11
-
4,4'-DDE (p,p'-)
-
-
28.90
6.08
8.21
0.04
-
4,4'-DDT (p,p'-)
-
-
1.91
0.00
1.90
0.02
-
Aldrin
-
-
-
-
20.88
0.09
_
alpha-Chtordane
-
-
-
-
-
-
-
dclta-BHC
-
-
-
-
-
-
.
Dieldrin
-
-
4.66
1.99
6.63
0.00
.
EndoaulfanQ
-
-
-
-
-
-
_
Endrin ketone
-
-
-
-
-
-
.
gamma-Chlordane
-
-
-
-
-
-
.
Heptachlor
-
-
-
-
-
-
-
Heptachlor epoxide
¦
¦
43.59
9.55
5.23
0.09
"
SeadvotetBe Organics
bi«(2-Ethylhexyl)phthslate
-
-
-
-
-
-
-
.
Di-n-octylphthalate
-
-
-
-
-
-
-
-
Auxiliary PararoHen
Total Organic Carbon (95%LCL or minimum)
¦
~
-
-
-
-
-
-
'Unit* are mg/lcg OC for PCBs, organochlorinc pestici
''The sediment guidelines expressed on an OC basis ar
dw =
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 [2000]).
Hazard Quotient* - RM 6.5-8.8
Di Toro et al
Ingenoll ct at. (1996)
Ontario (1993)
Chemical
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
CSQG
Metaka
Aluminum
-
0.16
-
-
-
-
-
-
-
Antimony
-
-
-
-
-
-
-
¦
-
Aneoie
0.75
0.20
0.89
0.20
1.66
0.58
1.64
0.30
-
Bain
-
-
-
-
-
-
-
-
-
Beryllium
-
-
-
-
-
-
-
-
-
Cafeuom
3.10
0.56
3.74
0.68
3.64
0.61
3.61
0.22
-
Chromium
3.22
0.46
3.48
1.05
3.36
1.39
4.82
1.14
-
Cobalt
-
-
-
-
-
-
-
-
-
Copper
2.49
0.54
3.64
1.02
2.86
0.52
6.37
0.93
-
Iron
0.10
0.07
0.10
0.08
-
-
0.96
0.48
-
Lead
5.38
2.99
7.99
3.61
8.45
3.24
9.54
1.18
-
Magaot
0.51
0.22
0.59
0.31
-
-
0.81
0.34
-
Mcrcory
-
-
-
-
1.55
0.55
1.35
0.13
-
Nickel
0.96
0.51
1.16
0.70
1.28
0.64
1.44
0.31
-
Selenium
Silver
-
-
.
-
-
.
.
.
Thallium
-
-
-
-
-
-
-
-
-
Vanadium
Zinc
5.56
1.11
6.25
1.13
4.98
1.94
5.10
0.75
-
Cyanide
-
-
-
-
-
-
-
-
-
FAB*
An&nceae
965.47
68.96
965.47
56.79
-
-
43.89
0.45
0.17
Bcszofajaatfuaocne
311.23
19.71
369.58
21.12
186.54
15.36
18.48
0.07
0.07
Benzo(alpyrene
76.02
13.59
199.54
19.95
200.17
8.17
17.26
0.08
0.07
-
-
-
-
-
-
-
-
0.08
BcnzoJgAilperylcae
354.62
16.46
288.13
18.44
-
-
27.12
248.89
0.04
Bozo0i|flMnallne
-
-
-
-
• -
•
33.53
0.10
0.08
ChryKae
299.31
17.96
33X57
21.90
157.26
10.42
26.41
0.34
0.11
Dibcnt{a.h]«nrtiraccne
957.50
-
957.50
-
-
-
159.58
1.27
0.09
Ftuoranlhrar
610.70
111.96
650.10
62.98
181.56
8.56
26.87
0.34
0.29
In
-------
Table C-6. Hazard quotients for aquatic life based on sediment exposures (Data from Inventory 20 [2000]).
Hazard Quotient* - RM 6.5-8.8
Di Toro ct al
Ingereoll ct al. (1996) Environment Canada (1995) Ontario (1993) (2000)
Chemical
ERL
ERM
TEL
PEL
TEL
PEL
LEL
SEL
CSQC.
Phenanthrene
264.85
20.43
376.37
17.44
170.67
13.89
12.77
0.13
0.12
Pyrene
317.62
36.30
288.75
25.93
239.72
14.52
25.93
0.26
0.19
PCBs
PCB Aroclor 1242
-
-
-
-
-
-
-
-
-
PCB Aroclor 1260
-
-
-
-
-
-
103.89
0.37
-
PCB (total)
51.15
3.50
79.92
10.66
75.00
9.23
36.53
0.00
-
OrgaaocMorine Pesticides
4,4-DDD (p,p'-)
-
-
-
17.81
7.41
7.88
0.18
-
4,4'-DDE (p,p'-)
-
-
-
24.22
5.10
6.88
0.03
-
4,4-DDT (p,p'-)
-
-
-
1.98
0.00
1.97
0.02
-
Aldrin
-
-
-
-
-
5.30
0.02
.
alpha-Chlordane
-
-
-
-
-
-
-
-
delta-BHC
-
-
-
-
-
-
-
-
Dieldrin
-
-
-
5.26
2.25
7.50
0.00
-
Endotulfan II
-
-
-
-
-
-
-
.
Endrin ketone
-
-
-
-
-
-
.
-
gamma-Chlordanc
-
-
-
-
-
-
.
-
Heptachlor
-
-
-
-
-
-
-
-
Heptachlor epoxide
-
-
-
28.04
6.14
3.36
0.06
-
Snnivolatik Or{uifci
bis(2-Ethylhexyl)phthalate
-
-
-
-
-
-
-
-
.
Di-n-octylphthalate
-
-
-
-
-
-
-
-
-
Auxiliary Parameter*
Total Organic Carbon (95% LCL or minimum)
-
-
-
-
-
-
-
-
-
'Units are mg/kg OC for PCBs, organochlorine pestici
iFhe sediment guideline* expressed on an OC basis ar
dw = dry weight
OC = Organic Carbon
RM = River Mile
Lover Ottawa River SLRA
Page 12 of 12
October 2001
555-3763-001
-------
Table C-7. Tissue residue-based hazard quotients for aquatic life.
Screening 95% UCL Tiwue Concentration (agftj-wet) HQ
Chemical
Value
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM>8.8
RM 0-3.2
RM 3.2-4.9
RM 4.9-6.5
RM 6.5-8.8
RM >8 S
Mcteb
Ancoic
1.7
0.020
0.020
0.046
0.02a
0.112
0.011505638
0.011644391
0.027116478
0.011642352
0.06560966
Cadmium
0.25
0.010
0.013
0.024
0.024
0.058
0.04
0.05
0.10
0.10
0.23
Lead
0.37
0.262
0.422
0.830
0.756
1.621
0.71
1.14
2.24
2.04
4.38
Moomy
8.6
0.011
0.040
0.028
0.043
0.095
0.001
0.005
0.003
0.005
0.01)
Selenium
2.25
1.030
0.102
1.073
0.706
0.874
0.46
0.05
0.48
0.31
0.39
pcb.
-
-
-
.
_
PCB Arodor 1242
-
0.865
2.812
2.437
2.026
0.029
-
-
-
-
.
PCB Arooior 1260
-
0.132
0.421
0.179
0.113
0.046
-
-
-
-
-
Total PCB.
1.53
0.997
3.232
2.616
2.139
0.07J
0.65
2.11
1.71
1.40
0.05
rwlkMca
4,4'-DDO (p,p-)
0.024
0.045
0.057
0.064
0.073
-
-
-
-
-
4,4'-DDE'-)
0.070
0.164
0.123
0.097
0.313
-
-
-
-
-
4,4-DDT
-------
APPENDIX D
Sediment HQ Maps
-------
;
PCS Concentration in Sediment
Rivers and WatertxxSes Below TEL <0.032 mg/kg,
i—| ~ Between TEL (0.032mg7kg) and
County and District Boundary PEL (0.24 mg/kg)
04 Mites Above PEL (0.24 mg/kg)
River KSIe 3.2
Maumee Bay
Lead Concentration in Sediment
¦ Below TE L (37 mg&g)
Between TEL (37 mgfcg) and
PEL (82 mg/kg)
Above PEL (82 mg/kg)
Figure E-3
Lead and PCB
Concentrations in Sediment:
June 2000 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll etal. 1996)
-------
i
~k
i, I
River Mile 5£
4
River Mile 0
KM MM 4 B
R MM B 5
River Mile 3.2
Maumee Bay
hhc OI»»>ri>aM*«3>UirurT«iiM
~
Rivers and Waterbodies
County and District Boundary
0.2 0 0 2 0.4 Mies
Lead Concentration in Sediment
• Below TEL (37 mg*g)
Between TEL (37 mg/kg) and PEL (82 mg/kg)
« Abwe PEL (82 mgAg)
Figure D-1
Lead Concentrations in Sediment:
June 2000 Data Compared to Threshold
and Probable Effects Levels
(lngersoll et ai. 1996)
-------
)
River Mile 0
Rjver Mire 3.2
River Mile 4.9
River Mile 6 .5
L
River Mile 3B
J
I •"
f
IN
A
Rivers and Waterbodies
County and District Boundary
PCB Concentration in Sediment
a Below TEL (0.032 mg/kg)
Between TEL (0.032mg/kg) and PEL(0.24 mg/kg)
• Above PEL (0.24 mg/kg)
Maumee Bay
02 o 0.2 a4
Figure D-2
PCB Concentrations in Sediment:
June 2000 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et al. 1996)
-------
J
River Mile 0
River Mile 4.9
h;
*
River Mile 3.2
\
Maumee Bay
j\
River Mile 6.5 « ,
- \ "
-r-'-Y
m n
v
River Mile 8
^fii
~\
N
A
en
Rivers and Waterbodies
County and District Boundary
0.2
0.2 0.4 Miles
Total PAH's Concentration in Sediment
• Beiow Sediment Quality Guideline
• Above Sediment Quality Guideline
Figure D-3
Total PAH's in Sediment:
June 2000 Data Compared to
Sediment Quality Guidelines
(DiToro et al. 2000)
-------
J
/
/
5«
N Lead Concentration in Sediment,
t _. J11, . _ Core Depth-Surface(0-24 inches)
1 Rivers and Waterbodies Below TEL (37 mg/fcg)
i—i ,, „ • Between TEL (37 mg/kg) and
, ^ l_i County and District Boundary PEL (82 mg/kg)
o 01 0.2 Mtes Above PEL (82 mg/kg)
River Mile 0
Maumee Bay
Lead Concentration in SetSment,
Core Depth - Deep (greater than 24 inches)
¦ Below TE L (37 mg/kg)
Between TEL (37 mg/kg) and
PEL (82 mg/kg)
s Above PEL (82 mg/kg)
Figure D-4a : River Mile 0-3.2
Lead Concentrations in Sediment:
1998 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et al. 1996)
-------
;
0.1
N
A
Rivers and Waterbodies
County and District Boundary
0.1
0.2 Miles
Lead Concentration in Sediment.
Core Depth - Surface (0 - 24 inches)
Below TEL (37 mg*g)
• Between TEL (37 mg/kg) and
PEL (82 mg/kg)
Above PEL (82 mg/kg)
Lead Concentration in Sedment.
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (37 mg/kg)
Between TEL (37 mg/kg) and
PEL (82 mg/kg)
- Above PEL (82 mg/kg)
Figure D-4b : River Mile 3.2 - 4.9
Lead Concentrations in Sediment:
1998 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et al. 1996)
-------
J
River Mile 6.5
--r
V"
\
id It** Sur»*«fOCJau*l>»l JT
N Lead Concentration in Sediment,
\ „ ^ Core Depth - Surface (0- 24 inches)
I Rivers and WatertxxSes . Bet0wTEL(37 mg/kg)
* I—i _ • Between TEL (37 mg*g) and
/ H I County and Distnct Boundary DCI
0.1 0 0.1 01 m*» pel I82 ">9*8)
Above PEL (82 mg/Vg)
River Mile 4.9
i#*
M
Lead Concentration in Sediment,
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (37 mgAg)
Between TEL (37 mg/kg) and
PEL (82 mg/kg)
¦ Above PEL (82 mg/kg)
Figure D-4c : River Mile 4.9 - 6.5
Lead Concentrations in Sediment:
1998 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et a! 1996)
-------
i
i // ¦
\jM'
River
MiteSJB
Lead Concentration in Sediment,
... __ ^ Core Depth - Surface (0 - 24 inches)
Rivers and Waterbodies Below TEL (37 mgAcg)
~ • Between TEL (37 ma*g) and
County and District Boundary D_.
i 02 Mtes PEL(82mg/kg)
Above PEL (82 mg/kg)
Lead Concentration in Sediment,
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (37 mg^g)
Between TEL (37 mg/kg) and
PEL (82 mg/kg)
B Abcve PEL (82 mgikg)
Figure D-4d : River Mile 6.5 - 8.8
Lead Concentrations in Sediment:
1998 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et al 1996)
-------
J
ma ,
' n u
' ¦ a
River Mile 3.2
»i I
~
N
4
n
Rivers and Waterbodies
County and District Boundary
0.1 0 0.1 0.2 Mies
PCB Concentration in Sediment,
Core Depth - Surface (0 - 24 inches)
Below TEL (0.032 mg/kg)
. Between TEL (0.032mg/kg) and
PEL (0.24 mg/kg)
Above PEL (0.24 mg/kg)
Maumee Bay
PCB Concentration in Sediment
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (0.032 mgd
-------
i
/
River
Mile8.8
N
A
Rivers and Waterboties
County and District Boundary
0.1
0.2
PCB Concentration in Sediment
Core Depth - Surface (0 - 24 inches)
Below TEL (0.032 mg/kg)
. Between TEL (0.032mg/kg) and
PEL (0.24 mg/kg)
Above PEL (0.24 mg/kg)
PCB Concentration in Sediment
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (0.032 mg*g)
Between TEL (0.032mg/kg) and
PEL (0.24 mg/kg)
Above PEL (0.24 mg/kg)
Figure D-5b : River Mile 3.2 - 4.9
PCB Concentrations in Sediment:
1998 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et al. 1996)
-------
River Mile 6.5
-V-
M
0.1
~
0.2 Mies
Rivers and Waterfcodies
County and District Boundary
PCB Concentration in Sediment,
Core Depth - Surface (0 - 24 inches)
Below TEL (0.032 mgfcg)
. Between TEL (0.032mg/kg) and
PEL (0.24 mg/kg)
Above PEL (0 24 mg/kg)
River Mile 4.9
PCB Concentration in Sediment.
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (0.032 mg/kg)
Between TEL (0.032mg/kg) and
PEL (0.24 mg/kg)
• Above PEL (0.24 mg/kg)
A
11
Figure D-5c : River Mile 4.9 - 6.5
PCB Concentrations in Sediment:
1998 Data Compared to Threshold
and Probable Effects Levels
(Ingersoll et al. 1996)
-------
River
Mile 8.8
/ }/'
I / i /
I !&
m
River Mile 6.5
<¦
K
\
¦ _
• T •
v-
. V"
N
A
CZj
Rivers and Watertvocfces
County and District Boundary
0.1
0.2 Mies
PCS Concentration in Sediment.
Core Depth - Surface (0 - 24 inches)
Below TEL (0.032 mg/kg)
. Between TEL (0.032mgAg) and
PEL (024 mg/kg)
Above PEL (0.24 mg/kg)
PCB Concentration in Sediment,
Core Depth - Deep (greater than 24 inches)
¦ Below TEL (0.032 mg/kg)
Between TEL (0.032mgll
-------
Maumee Bay
fen. SteuRx! tcw«*toaarear37r>oet»jtn9is )tffr.toiuuRHiMi
N
A
Rivers and Waterbodes
County and District Boundary
Total PAH's Concentrator! in Segment,
Core Depth - Surface (0 - 24 inches)
Below Sediment Quality Guideline
Above Sediment Quality Guideline
o.i
0.1 0.2 Miles
Total PAH's Concentration in Sediment,
Core Depth - Deep (greater than 24 inches)
¦ Below Sediment Quality Guideline
Above Sediment Quality Guideline
Figure D-6a : River Mile 0 - 3.2
Total PAH's in Sediment:
1998 Data Compared to
Sediment Quality Guidelines
(DiToro et a I. 2000)
-------
River Mile 4.9
M, K^»*H HU'UHII1I *>•>**.
Rivers and Watertoodies
County and District Boundary
0.1
0.2 Miles
Tctai PAH's Concentration in Sediment,
Core Depth - Surface (0-24 inches)
Below Sediment Quality Guideline
Abcwe Sediment Quality Guideline
River Mile 3.2
}
/
/
i
I
Figure D-6b : River Mile 3.2 - 4.9
Total PAH's in Sediment:
1998 Data Compared to
Sediment Quality Guidelines
(DiToro et a I. 2000)
Total PAH's Concentration in SecSment.
Core Depth - Deep (greater than 24 inches)
¦ Below Sediment Quality Guideline
¦ Above Sediment Quality Guideline
-------
, 1
River Mile 6.5
N
A
Rivers and Waterbodies
County and District Boundary
0.1
0.2 Mies
Total PAH's Concentration in Secfiment.
Core Depth - Surface (0 - 24 inches)
« Below Sediment Quality Guideline
Abewe Sediment Quality Guideline
¦
River Mile 4.9
*
-f
I
Total PAH's Concentration in Sediment.
Core Depth - Deep (greater than 24 inches)
¦ Below Sediment Quality Guideline
¦ At)ewe Sediment Quality Guideline
Figure D-6c : River Mile 4.9 - 6 5
Total PAH's in Sediment:
1998 Data Compared to
Sediment Quality Guidelines
(DiToro etal. 2000)
-------
/
River
Mite 8.8
—
. ..
River Mile 6.5
A
//
A '
)' / x
/ /
I i'i>
ALh
—v-
¦
¦
JX
\
\ '
.rtjT3Tay37Mosrsj«jj,»i; hmtfimintai
N
y
01 o
\
Rivers and Watertoodies
I County and District Boundary
01
0.2 Miles
Total PAH's Concentratoriin Sediment.
Core Depth - Surface (0 - 24 inches)
Below Sediment Quality Guideline
Above Sediment Quality Guideline
Total PAH's Concentration in Sediment,
Core Depth - Deep (greater than 24 inches)
¦ Below Sediment Quality Guideline
a Above Sediment Quality Guideline
Figure D-6d: River Mile 6.5 - 8.8
Total PAH's in Sediment:
1998 Data Compared to
Sediment Quality Guidelines
(DiToro etal. 2000)
------- |