United States
environmental Protection
Agency
Water
Office of Water
Regulations and Standards
Washington, DC 204SO
Jisno, 1985
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PREFACE
This document is one of a series of preliminary assessments dealing
with chemicals of potential concern in municipal sewage sludge. The
purpose of these documents is to: (a) summarize the available data for
the constituents of potential concern, (b) identify the key environ-
mental pathways for each constituent related to a reuse and disposal
option (based on hazard indices), and (c) evaluate the conditions under
which such a pollutant may pose a hazard. Each document provides a sci-
entific basis for making an initial determination of whether a pollu-
tant, at levels currently observed in sludges, poses a likely hazard to
human health or the environment when sludge is disposed of by any of
several methods. These methods include landspreading on food chain or
nonfood chain crops, distribution and marketing programs, landfilling,
incineration and ocean disposal.
These documents are intended to serve as a rapid screening tool to
narrow an initial list of pollutants to those of concern. If a signifi-
cant hazard is indicated by this preliminary analysis, a more detailed
assessment will be undertaken to better quantify the risk from this
chemical and to derive criteria if warranted. If a hazard is shown to
be unlikely, no further assessment will be conducted at this time; how-
ever, a reassessment will be conducted after initial regulations are
finalized. In no case, however, will criteria be derived solely on the
basis of information presented in this document.
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TABLE OP CONTENTS
Page
PREFACE i
1. INTRODUCTION 1-1
2. PRELIMINARY CONCLUSIONS FOR ENDRIN IN MUNICIPAL SEWAGE
SLUDGE 2-1
Landspreading and Distribution-and-Marketing 2-1
Landfilling 2-1
Incineration 2-1
Ocean Disposal 2-1
3. PRELIMINARY HAZARD INDICES FOR ENDRIN IN MUNICIPAL SEWAGE
SLUDGE 3-1
Landspreading and Distribucion-and-Marketing 3-1
Landf illing 3-1
Incineration 3-1
Ocean Disposal 3-1
Index of seawater concentration resulting from
initial mixing of sludge (Index 1) 3-1
Index of seawater concentration representing
a 24-hour dumping cycle (Index 2) 3-5
Index of hazard to aquatic life (Index 3) 3-6
Index of human toxicity resulting
from seafood consumption (Index 4) 3-8
4. PRELIMINARY DATA PROFILE FOR ENDRIN IN MUNICIPAL SEWAGE
SLUDGE 4-1
Occurrence 4-1
Sludge 4-1
Soil - Unpolluted 4-1
Water - Unpolluted 4-3
Air 4-5
Food ' 4-5
Human Effects 4-5
Ingestion 4-6
Inhalation 4-6
11
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TABLE OF CONTENTS
(Continued)
Page
Plant Effects 4-6
Phytotoxicity 4-6
Uptake 4-6
Domestic Animal and Wildlife Effects 4-6
Toxicity 4-6
Uptake 4-7
Aquatic Life Effects 4-8
Toxicity 4-8
Uptake 4-8
Soil Biota Effects 4-8
Physicochemical Data for Estimating Fate and Transport 4-8
5. REFERENCES 5-1
APPENDIX. PRELIMINARY HAZARD INDEX CALCULATIONS FOR
ENDRIN IN MUNICIPAL SEWAGE SLUDGE A-l
ill
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SECTION 1
INTRODUCTION
This preliminary data profile is one of a series of profiles
dealing with chemical pollutants potentially of concern in municipal
sewage sludges. Endrin was initially identified as being of potential
concern when sludge is ocean disposed.* This profile is a compilation of
information that may be useful in determining whether endrin poses an
actual hazard to human health or the environment when sludge is disposed
of by these methods.
The focus of this document is the calculation of "preliminary
hazard indices" for selected potential exposure pathways, as shown in
Section 3. Each index illustrates the hazard that could result from
movement of a pollutant by a given pathway to cause a given effect
(e.g., sludge -*• seawater •* marine organisms •* human toxicity). The
values and assumptions employed in these calculations tend to represent
a reasonable "worst case"; analysis of error or uncertainty has been
conducted to a Limited degree. The resulting value in most cases is
indexed to unity; i.e., values >1 may indicate a potential hazard,
depending upon the assumptions of the calculation.
The data used for index calculation have been selected or estimated
based on information presented in the "preliminary data profile", Sec-
tion 4. Information in the profile is based on a compilation of the
recent literature. An attempt has been made to fill out the profile
outline to the greatest extent possible. However, since this is a pre-
liminary analysis, the literature has not been exhaustively perused.
The "preliminary conclusions" drawn from each index in Section 3
are summarized in Section 2. The preliminary hazard indices will be
used as a screening tool to determine which pollutants and pathways may
pose a hazard. Where a potential hazard is indicated by interpretation
of these indices, further analysis will include a more detailed examina-
tion of potential risks as well as an examination of site-specific
factors. These more rigorous evaluations may change the preliminary
conclusions presented in Section 2, which are based on a reasonable
"worst case" analysis.
The preliminary hazard indices for selected exposure routes
pertinent to ocean disposal practices are included in this profile. The
calculation formulae for these indices are shown in the Appendix. The
indices are rounded to two significant figures.
* Listings were determined by a series of expert workshops convened
during March-May, 1984 by the Office of Water Regulations and
Standards (OWRS) to discuss landspreading, landfilling, incineration,
and ocean disposal, respectively, of municipal sewage sludge.
1-1
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SECTION 2
PRELIMINARY CONCLUSIONS FOR ENDRIN IN MUNICIPAL SEWAGE SLUDGE
The following preliminary conclusions have been derived from the
calculation of "preliminary hazard indices", which represent conserva-
tive or "worst case" analyses of hazard. The indices and their basis
and interpretation are explained in Section 3. Their calculation
formulae are shown in the Appendix.
I. LANDSPREADING AND DISTRIBUTION-AND-MARKETING
Based on the recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
II. LANDFILLING
Based on the recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
III. INCINERATION
Based on the recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
IV. OCEAN DISPOSAL
Slight increase in the seawater concentration of endrin are evident
in all the scenarios evaluated (see Index 1).
The seawater concentration of endrin increases in all the scenarios
evaluated. The increases are slight in most cases, except when the
disposal rate is 1650 ink/day at the worst site where the increase
is moderate (see Index 2).
The hazard to aquatic life is significantly increased for all
sludges disposed at the worst site. Slight increases also occur
for the other scenarios evaluated (see Index 3).
No increase in risk to humans from the consumption of seafood was
determined in this assessment (see Index 4).
2-1
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SECTION 3
PRELIMINARY HAZARD INDICES FOR ENDRIN
IN MUNICIPAL SEWAGE SLUDGE
I. LAKDSPREADING AND DISTRIBUTION-AND-MARKETING
Based on the recommendations of che experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
II. LANDFILLING
Based on the recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
III. INCINERATION
Based on the recommendations of the experts at the OURS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
IV. OCEAN DISPOSAL
For the purpose of evaluating pollutant effects upon and/or
subsequent uptake by marine life as a result of sludge disposal,
two types of mixing were modeled. The initial mixing or dilution
shortly after dumping of a single load of sludge represents a high,
pulse concentration to which organisms may be exposed for short
time periods but which could be repeated frequently; i.e., every
time a recently dumped plume is encountered. A subsequent addi-
tional degree of mixing can be expressed by a further dilution.
This is defined as the average dilution occurring when a day's
worth of sludge is dispersed by 24 hours of current movement and
represents the time-weighted average exposure concentration for
organisms in the disposal area. This dilution accounts for 8 to 12
hours of the high pulse concentration encountered by the organisms
during daylight disposal operations and 12 to 16 hours of recovery
(ambient water concentration) during the night when disposal
operations are suspended.
A. Index of Seawater Concentration Resulting from Initial Mixing
of Sludge (Index 1)
1. Explanation - Calculates increased concentrations in Ug/L
of pollutant in seawater around an ocean disposal site
assuming initial mixing.
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2. Assumptions/Limitations - Assumes that the background
seawater concentration of pollutant is unknown or zero.
The index also assumes that disposal is by tanker and
that the daily amount of sludge disposed is uniformly
distributed along a path transversing the site and
perpendicular to the current vector. The initial
dilution volume is assumed to be determined by path
length, depth to the pycnocline (a layer separating
surface and deeper water masses), and an initial plume
width defined as the width of the plume 4 hours after
dumping. The seasonal disappearance of the pycnocline is
not considered.
3. Data Used and Rationale
a. Disposal conditions
Sludge Sludge Mass Length
Disposal Dumped by a of Tanker
Rate (SS) Single Tanker (ST) Path (L)
Typical 825 mt DW/day 1600 mt WW 8000 m
Worst 1650 mt DW/day 3400 mt WW 4000 m
The typical value for the sludge disposal rate
assumes that 7.5 x 10^ mt WW/year are available for
dumping from a metropolitan coastal area. The con-
version to dry weight assumes 4 percent solids by
weight. The worst-case value is an arbitrary doubl-
ing of the typical value to allow for potential
future increase.
The assumed disposal practice to be followed at the
model site representative of the typical case is a
modification of that proposed for sludge disposal at
the formally designated 12-mile site in the New York
Bight Apex (City of New York, 1983). Sludge barges
with capacities of 3400 mt WW would be required to
discharge a load in no less than 53 minutes travel-
ing at a minimum speed of 5 nautical miles (9260 m)
per hour. Under these conditions, the barge would
enter the site, discharge the sludge over 8180 m and
exit the site. Sludge barges with capacities of
1600 mt WW would be required to discharge a load in
no less than 32 minutes traveling at a minimum speed
of 8 nautical miles (14,816 m) per hour. Under
these conditions, the barge would enter the site,
discharge the sludge over 7902 m and exit the site.
The mean path length for the large and small tankers
is 8041 m or approximately 8000 m. Path length is
assumed to lie perpendicular to the direction of
prevailing current flow. For the typical disposal
rate (SS) of 825 mt DW/day, it is assumed that this
3-2
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would be accomplished by a mixture of four 3400 mt
WW and four 1600 me WW capacity barges. The overall
daily disposal operation would last from 8 to 12
hours. For the worst-case disposal rate (SS) of
1650 mt DW/day, eight 3400 mt WW and eight 1600 mt
WW capacity barges would be utilized. The overall
daily disposal operation would last from 8 to 12
hours. For both disposal rate scenarios, there
would be a 12 to 16 hour period at night in which no
sludge would be dumped. It is assumed that under
the above described disposal operation, sludge
dumping would occur every day of the year.
The assumed disposal practice at the model site
representative of the worst case is as stated for
the typical site, except that barges would dump half
their load along a track, then turn around and
dispose of the balance along the same track in order
to prevent a barge from dumping outside of the site.
This practice would effectively halve the path
length compared to the typical site.
b. Sludge concentration of pollutant (SC)
Typical 0.14 mg/kg DW
Worst 0.17 mg/kg DW
Typical and worst values are the mean and maximum
values, respectively, from a study o-f sludge concen-
trations from 74 cities in Missouri (Clevenger et
al., 1983). Endrin was not detected in a U.S. EPA
study of 50 POTWs (U.S. EPA, 1982a).
c. Disposal site characteristics
Average
current
Depth to velocity
pycnocline (D) at site (V)
Typical 20 m 9500 m/day
Worst 5 m 4320 m/day
Typical site values are representative of a large,
deep-water site with an area of about 1500 km^
located beyond the continental shelf in the New York
Bight. The pycnocline value of 20 m chosen is the
average of the 10 to 30 m pycnocline depth range
occurring in the summer and fall; the winter and
spring disappearance of the pycnocline is not consi-
dered and so represents a conservative approach in
evaluating annual or long-term impact. The current
velocity of 11 cm/sec (9500 m/day) chosen is based
3-3
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on the average current velocity in this area (COM,
1984a).
Worst-case values are representative of a near-shore
New York Bight site with an area of about 20 km^.
The pycnocline value of 5 m chosen is the minimum
value of the 5 to 23 m depth range of the surface
mixed layer and is therefore a worst-case value.
Current velocities in this area vary from 0 to
30 cm/sec. A value of 5 cm/sec (4320 m/day) is
arbitrarily chosen to represent a worst-case value
(COM, 1984b).
4. Factors Considered in Initial Mixing
When a load of sludge is dumped from a moving tanker, an
immediate mixing occurs in the turbulent wake of the
vessel, followed by more gradual spreading of the plume.
The entire plume, which initially constitutes a narrow
band the length of the tanker path, moves more-or-less as
a unit with the prevailing surface current and, under
calm conditions, is not further dispersed by the current
itself. However, the current acts to separate successive
tanker loads, moving each out of the immediate disposal
path before the next load is dumped.
Immediate mixing volume after barge disposal is
approximately equal to the length of the dumping track
with a cross-sectional area about four times that defined
by the draft and width of the discharging vessel
(Csanady, 1981, as cited in NOAA, 1983). The resulting
plume is initially 10 m deep by 40 m wide (O'Connor and
Park, 1982, as cited in NOAA, 1983). Subsequent
spreading of plume band width occurs at an average rate
of approximately 1 cm/sec (Csanady et al., 1979, as cited
in NOAA, 1983). Vertical mixing is limited by the depth
of the pycnocline or ocean floor, whichever is shallower.
Four hours after disposal, therefore, average plume width
(W) may be computed as follows:
W = 40 m + 1 cm/sec x 4 hours x 3600 sec/hour x 0.01 m/cm
= 184 m = approximately 200 m
Thus the volume of initial mixing is defined by the
tanker path, a 200 m width, and a depth appropriate to
the site. For the typical (deep water) site, this depth
is chosen as the pycnocline value of 20 m. For the worst
(shallow water) site, a value of 10 m was chosen. At
times the pycnocline may be as shallow as 5 m, but since
the barge wake causes initial mixing to at least 10 m,
the greater value was used.
3-4
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5. Index 1 Values
Disposal
Conditions and
Site Charac- Sludge
teristics Concentration
Sludge Disposal
Rate (mt DW/day)
825
1650
Typical
Worst
Typical
Worst
Typical
Worst
0.0
0.0
0.0
0.0
0.00028
0.00034
0.0024
0.0029
0.00028
0.00034
0.0024
0.0029
6. Value Interpretation - Value equals the expected increase
in endrin concentration in seawater around a disposal
site as a result of sludge disposal after initial mixing.
6. Preliminary Conclusion - Slight increases in the seawacer
concentration of endrin are evident in all the scenarios
evaluated.
B. Index of Seawater Concentration Representing a 24-Hour Dumping
Cycle (Index 2)
1. Explanation •* Calculates increased effective concentra-
tions in yg/L of pollutant in seawater around an ocean
disposal site utilizing a time weighted average (TWA)
concentration. The TWA concentration is that which would
be experienced by an organism remaining stationary (with
respect to the ocean floor) or moving randomly within the
disposal vicinity. The dilution volume is determined by
t,he tanker path length and depth to pycnocline or, for
the shallow water site, the 10 m effective mixing depth,
as before, but the effective width is now determined by
current movement perpendicular to the tanker path over 24
hours.
2. Assumptions/Limitations - Incorporates all of the assump-
tions used to calculate Index 1. In addition, it is
assumed that organisms would experience high-pulsed
sludge concentrations for 8 to 12 hours per day and then
experience recovery (no exposure to sludge) for 12 to 16
hours per day. This situation can be expressed by the
use of a TWA concentration of sludge constituent.
3. Data Used and Rationale
See Section 3, pp1. 3-2 to 3-4.
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4. Factors Considered in Determining Subsequent Additional
Degree of Mixing (Determination of TWA Concentrations)
See Section 3, p. 3-5.
5. Index 2 Values (yg/L)
Disposal Sludge Disposal
Conditions and Race (mt DW/day)
Site Charac- Sludge
teristics Concentration 0 825 1650
Typical Typical 0.0 0.000076 0.00015
Worst 0.0 0.000092 0.00018
Worst Typical 0.0 0.00067 0.0013
Worst 0.0 0.00081 0.0016
6. Value Interpretation - Value equals the effective
increase in endrin concentration expressed as a TWA con-
centration in seawater around a disposal site experienced
by an organism over a 24-hour period.
7. Preliminary Conclusion - The seawater concentration of
endrin increases in all the scenarios evaluated. The
increases are slight in most cases, except when the
disposal rate is 1650 mt/day at the worst site where the
increase is moderate.
C. Index of Hazard to Aquatic Life (Index 3)
1. Explanation - Compares the effective increased concentra-
tion of pollutant in seawater around the disposal site
(Index 2) expressed as a 24-hour TWA concentration with
the marine ambient water quality criterion of the
pollutant, or with another value judged protective of
marine aquatic life. For endrin, this value is the
criterion that will protect the marketability of edible
marine aquatic organisms.
2. Assumptions/Limitations - In addition to the assumptions
stated for Indices 1 and 2, assumes that all of the
released pollutant is available in the water column to
move through predicted pathways (i.e., sludge to seawater
to aquatic organism to man). The possibility of effects
arising from accumulation in the sediments is neglected
since the U.S. EPA presently lacks a satisfactory method
for deriving sediment criteria.
3-6
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3. Data Used and Rationale
a. Concentration of pollutant in seawater around a
disposal site (Index 2)
See Section 3, p. 3-6.
b. Ambient water quality criterion (AWQC) = 0.0023 yg/L
Water quality criteria for the toxic pollutants
Listed under Section 307(a)(l) of the Clean Water
Act of 1977 were developed by the U.S. EPA under
Section 304(a)(l) of the Act. These criteria were
derived by utilization of data reflecting the
resultant environmental impacts and human health
effects of these pollutants if present in any body
of water. The criteria values presented in this
assessment are excerpted from the ambient water
quality criteria document for endrin.
The 0.0023 Ug/L value chosen as the ' criterion to
protect saltwater organisms is expressed as a 24
hour average concentration (U.S. EPA, 1980). This
concentration, the saltwater final residue value,
was derived by using the FDA action level for mar-
ketability for human consumption of endrin in edible
fish and shellfish products (fish oil) (0.3 mg/kg),
the geometric mean of normalized bioconcentracion
factor (BCF) values (1,324) for aquatic species
tested and the 100 percent lipid content of marine
fish oil. To protect against acute toxic effects,
endrin concentration should not exceed 0.037 pg/L at
any time.
4. Index 3 Values
Disposal Sludge Disposal
Conditions and Rate (mt DW/day)
Site Charac- Sludge
teristics Concentration 0 825 1650
Typical Typical 0.0 0.033 0.066
Worst 0.0 0.040 0.080
Worst Typical 0.0 0.29 0.58
Worst 0.0 0.35 0.71
Value Interpretation - Value equals the factor by which
the expected seawater concentration increase in endrin
exceeds the marine, water quality criterion. A value > 1
indicates that a tissue residue hazard may exist for
aquatic life. Even for values approaching 1, an endrin
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residue in tissue hazard may exist thus jeopardizing the
marketability of edible saltwater organism products (fish
oil). The criterion value of 0.0023 pg/L is probably too
high because on the average, the endrin residue in 50
percent of aquatic species similar to those used to
derive the AWQC will exceed the FDA action level for
endrin (U.S. EPA, 1980).
6. Preliminary Conclusion - The hazard to aquatic life is
significantly increased for all sludges disposed at the
worst site. Slight increases also occur for the other
scenarios evaluated.
D. Index of Human Toxicity Resulting from Seafood Consumption
(Index 4)
1. Explanation - Estimates the expected increase in human
pollutant intake associated with the consumption of sea-
food, a fraction of which originates from the disposal
sice vicinity, and compares the total expected pollutant
intake with the acceptable daily intake (ADI) of the
pollutant.
2. Assumptions/Limitations - In addition to the assumptions
listed for Indices 1 and 2, assumes that the seafood
tissue concentration increase can be estimated from the
increased water concentration (Index 2) by a
bioconcentration factor. It also assumes that, over the
long term, the seafood catch from the disposal site
vicinity will be diluted to some extent by the catch from
uncontaminated areas.
3. Data Used and Rationale
a. Concentration of pollutant in seawater around a
disposal site (Index 2)
See Section 3, p. 3-6.
Since bioconcentration is a dynamic and reversible
process, it is expected that uptake of sludge
pollutants by marine organisms at the disposal site
will reflect TWA concentrations, as quantified by
Index 2, rather than pulse concentrations.
b. Dietary consumption of seafood (QF)
Typical 14.3 g WW/day
Worst 41.7 g WW/day
Typical and worst-case values are the mean and the
95th percentile, respectively, for all seafood
consumption in the United States (Stanford Research
Institute (SRI) International, 1980).
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Fraction of consumed seafood originating from the
disposal site (FS)
For a typical harvesting scenario, it was assumed
that the total catch over a wide region is mixed by
harvesting, marketing and consumption practices, and
that exposure is thereby diluted. Coastal areas
have been divided by the National Marine Fishery
Service (NMFS) into reporting areas for reporting on
data on seafood landings. Therefore it was conven-
ient to express the total area affected by sludge
disposal as a fraction of an NMFS reporting area.
The area used to represent the disposal impact area
should be an approximation of the total ocean area
over which the average concentration defined by
Index 2 is roughly applicable. The average rate of
plume spreading of 1 cm/sec referred to earlier
amounts to approximately 0.9 km/day. Therefore, the
combined plume of all sludge dumped during one
working day will gradually spread, both parallel to
and perpendicular to current direction, as it pro-
ceeds down-current. Since the concentration has
been averaged over the direction of current flow,
spreading in this dimension will not further reduce
average concentration; only spreading in the perpen-
dicular dimension will reduce the average. If sta-
ble conditions are assumed over a period of days, at
least 9 days would be required to reduce the average
concentration by one-half. At that time, the origi-
nal plume length of approximately 8 km (8000 m) will
have doubled to approximately 16 km due to
spreading.
It is probably unnecessary to follow the plume
further since storms, which would result in much
more rapid dispersion of pollutants to background
concentrations are expected on at least a 10-day
frequency (NOAA, 1983). Therefore, the area
impacted by sludge disposal (AI, in km2) at each
disposal sice will be considered to be defined by
the tanker path length (L) times the distance of
current movement (V) during 10 days, and is computed
as follows:
AI = 10 x L x V x 10~6 km2/m2 (1)
To be consistent with a conservative approach, plume
dilution due to spreading in the perpendicular
direction to current flow is disregarded. More
likely, organisms exposed to the plume in the area
defined by equation 1 would experience a TWA concen-
tration lower than the concentration expressed by
Index 2.
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Next, the value of AI must be expressed as a
fraction of an NMFS reporting area. In the New York
Bight, which includes NMFS areas 612-616 and 621-
623, deep-water area 623 has an area of
approximately 7200 km2 and constitutes approximately
0.02 percent of the total seafood landings for the
Bight (COM, 1984a). Near-shore area 612 has an area
of approximately 4300 km2 and constitutes
approximately 24 percent of the total seafood
landings (COM, 1984b). Therefore the fraction of
all seafood landings (FSt) from the Bight which
could originate from the area of impact of either
the typical (deep-water) or worst (near-shore) site
can be calculated for this typical harvesting
scenario as follows:
For the typical (deep water) site:
_ AI x 0.02% = (2)
c ~ 7200
10 x 8000 m x 9500 m x 10 6 km2/m2 x 0.0002 _ , s
= ' = 2.1 x 10 5
7200 knr'
For the worst (near shore) site:
FSt " AI X 24.% = (3)
4300 km2
[10 x 4000 m x 4320 m x 10~6 km2/m2] x 0.24 _ , ,„_•>
J , ' = 9.6 x 10 3
4300 km2
To construct a worst-case harvesting scenario, it
was assumed that the total seafood consumption for
an individual could originate from an area more
limited than the entire New York Bight. For
example, a particular fisherman providing the entire
seafood diet for himself or others could fish
habitually within a single NMFS reporting area. Or,
an individual could have a preference for a
particular species which is taken only over a more
limited area, here assumed arbitrarily to equal an
NMFS reporting area. The fraction of consumed
seafood (FSW) that could originate from the area of
impact under this worst-case scenario is calculated
as follows:
For the typical (deep water) site:
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For che worst (near shore) site:
FSW = ^—- = 0.040 (5)
W 4300 km2
Bioconcentration factor of pollutant (BCF) =
5,500 L/kg
The value chosen is the weighted average BCF of
endrin for the edible portion of all freshwater and
estuarine aquatic organisms consumed by U.S. citi-
zens (U.S. EPA, 1980 as revised by Stephan, 1981).
The weighted average BCF is derived as part of the
water quality criteria developed by the U.S. EPA to
protect human health from the toxic effects of
endrin induced by ingestion of contaminated water
and aquatic organisms. The weighted average BCF is
calculated by adjusting1 the mean normalized BCF
(steady-state BCF corrected to 1 percent lipid con-
tent) to the 3 percent lipid content of consumed
fish and shellfish. It should be noted that lipids
of marine species differ in both structure and quan-
tity from those of freshwater species. Although a
BCF value calculated entirely from marine data would
be more appropriate for this assessment, no such
data are presently available.
Average daily human dietary intake of pollutant (DI)
= 1.0 yg/day
The reported daily intake values of endrin range
from 0.033 to 1.0 ug/day (U.S. EPA, 1980; (Douggan
and Corneliussen, 1972)). The value chosen
represents a worst-case situation and amplifies the
potential human toxicity effects of sludge disposal.
Acceptable daily intake of pollutant (ADI) =
70 ug/day
An ADI of 70 pg/day was derived by the U.S. EPA
(1980) based on studies showing a no-observed-
effect-level (NOEL) of 0.1 mg/kg/day in rats and
dogs. Higher doses were associated with increased
organ weights. An uncertainty factor of 100 was
applied in calculation of the human ADI.
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4. Index 4 Values
Disposal Sludge Disposal
Conditions and Rate (mt DW/day)
Sice Charac- Sludge Seafood
teristics Concentration3 Intake3'^ o 825 1650
Typical Typical Typical 0.014 0.014 0.014
Worst Worst 0.014 0.014 0.014
Worst Typical Typical 0.014 0.014 0.014
Worst Worst 0.014 0.014 0.014
3 AIL possible combinations of these values are not
presented. Additional combinations may be calculated
using the formulae in the Appendix.
D Refers to both the dietary consumption of seafood (QF)
and the fraction of consumed seafood originating from
the disposal site (FS). "Typical" indicates the use of
the typical-case values for both of these parameters;
"worst" indicates the use of the worst-case values for
both.
5. Value Interpretation - Value equals factor by which the
expected intake exceeds the ADI. A value >1 a possible
human health threat. Comparison with the null index
value at 0 mt/day indicates the degree to which any
hazard is due to sludge disposal, as opposed to
preexisting dietary sources.
6. Preliminary Conclusion - No increase in risk to humans
from the consumption of seafood was determined in this
assessment.
3-12
-------
SECTION 4
PRELIMINARY DATA PROFILE FOR ENDRIN IN MUNICIPAL SEWAGE SLUDGE
I. OCCURRENCE
Endrin enters the environment primarily as a result of direct
applications to soil and crops. The largest single use of endrin
domestically is for the control of lepidopteron larvae attacking
cotton crops in the southeastern and Mississippi delta states. In
1978, endrin production was approximately 400,000 Ibs. Its use is
declining due to increased restrictions.
A. Sludge
1. Frequency of Detection
Endrin was not mentioned in influent,
effluent, or sludge in a U.S. EPA study
of the fate of priority pollutants in
POTWs.
Endrin was not detected in a study of
Metro Denver sewage sludge from 1969-
1975.
Endrin was detected at levels
<1 pg/L in wastewater treatment
plant effluents in Ohio and Michigan
2. Concentration
In sludge samples from 74 cities in
Missouri, endrin was detected as follows
(Ug/g DW; 1979-80 data):
Min. Max. Mean Median
0.11 0.17 0.14
0.14
Soil - Unpolluted
1. Frequency of Detection
Endrin detected in 1 of 99 soil
samples from rice-growing areas
in 5 states, (1972 data)
Endrin detected in 1 .of 380 urban
soil samples from 5 cities, (Macon,
CA; 1971 data)
U.S. EPA, 1982a
(p. 41-2)
Baxter
et al., 1983
(p. 315)
Majeti and
Clark, 1980
(p. 6)
Clevenger
et al., 1983
(p. 1471)
Carey et al.,
1980 (p. 25)
Carey et al.,
1979a (p. 19)
4-1
-------
Endrin detected in 10 of 1,483 samples
from U.S. cropland soils (37 states)
in 1971 (0.7%)
Endrin detected in 14 of 1,486 samples
from U.S. cropland soils (37 states)
in 1971 (0.9%)
% positive samples from 6 Air Force
Installations, 1975-6:
Land Use
Year
% of Samples
with Endrin
Residential 1975
1976
Non-use 1975
1976
Golf Course 1975
1976
5.0
0
0
0
0
5.9
Endrin was not detected in 34 soil
samples collected in and around
Everglades National Park (1976)
2. Concentration
U.S. Soil Levels (data 1960s)
Max Mean
(ug/g)
Orchard Soils
Cranberry Soil
Vegetable Soils
Onion Soils
12.61
1.17
0.48
2.05
6.30
0.10
0.01
0.06
Rice-growing areas, endrin at
level of 0.17 ug/g DW (1972)
Endrin was detected at a level of
0.17 Ug/g DW in 1 urban soil
Cropland soils in 1972 (ug/g DW)
Min Max
Arith.
Mean
Geom.
Mean
Carey et al.,
1979b (p. 212)
Carey et al.,
1978 (p. 120)
Lang et al.,
1979 (p. 231)
Requejo
et al., 1979
(p. 934)
Edwards, 1973
(p. 416-17)
Carey et al.,
1980 (p. 25)
Carey et al.,
1979a (p. 19)
Carey et al.,
1979b (p. 212)
0.01 2.13 <0.01 <0.001
4-2
-------
In 14 out of 1,486 samples from U.S.
cropland soils in 1971 (pg/g DU):
Min
Max
Arith.
Mean
Geom.
Mean
0.02 1.00
<0.01 <0.001
Residues from six Air Force
Installations, 1975-6:
Land Use
Range (ug/g) Avg. Year
Residential
Residential
Non-use
Non-use
Golf Course
Golf Course
ND-0.01
0
0
0
0
ND-0.04
<0.01
0
0
0
0
<0.01
1975
1976
1975
1976
1975
1976
C. Water - Unpolluted
1. Frequency of Detection
No endrin residues observed in 1974
upper Great Lakes water study
Endrin was not detected in 368 samples
from southern Florida surface waters,
1968-72
Endrin was detected in 156 out of 458
finished water samples (34%) between
1964 and 1967 from the Mississippi and
Missouri Rivers. However, the number
of samples containing concentrations
of endrin in excess of 0.1 Mg/L
decreased from 23 (102) to 0 between
1964 and 1967.
2. Concentration
a. Freshwater
0.0002 mg/L interim drinking water
standard
0.001 mg/L present ambient water
standard
Carey et al.,
1978 (p. 120)
Lang et al.,
(p. 231)
Glooshenko,
1976 (p. 63)
Mattraw, 1975
(p. 108)
U.S. EPA, 1980
(p. C-4)
U.S. EPA, 1984
(p. 1-5)
U.S. EPA, 1984
(p. 1-5)
4-3
-------
In 1968, it was reported that endrin
levels entering Tule Lake National
Wildlife Refuge were highest (50-70
Ug/L) in summer and declined to non-
detectable levels in winter.
Occasionally, ground water may
contain >0.1 Ug/L of endrin, but
levels as high as 3 Ug/L have been
correlated with precipitation and
runoff following endrin applications.
Grant, 1976
(p. 288)
97 major river basins
(1965)
Miss. River Delta (1966)
99 major river basins
(1967)
11 major western rivers
(1967)
109 major rivers (1967)
20 streams (western)
(1969)
110 surface waters
(1967)
Endrin
Max
0.094
4.23
0.116
0.040
0.069
0.070
0.133
(Ug/L)
Mean
0.005
0.541
0.002
0.001
0.004
0.0003
0.002
U.S. EPA, 1980
(p. C-4)
Edwards, 1973
(p. 440-441)
b. . Seawater
Data not immediately available.
c. Drinking water
In an area of high endrin usage in
Louisiana, drinking water was found
to contain a maximum of 0.023 Ug/L
Endrin was detected in a water plant
in New Orleans. The highest level
measured was 0.004 Ug/L.
Endrin was detected in 156 out of
458 finished water samples between
1964 and 1967 from the Mississippi
and Missouri Rivers. The number of
samples containing endrin in excess of
0.1 Ug/L. decreased from 23 (10%) to
0 between 1964 and 1967.
U.S. EPA, 1980
(5. 04)
U.S. EPA, 1980
(p. C-5)
U.S. EPA, 1980
(p. C-4)
4-4
-------
Air
1. Frequency of detection
Endrin occurred in 25 out of 875
samples from 9 U.S. cities. All
25 samples were from Stoneville,
Miss, (data 1960s)
2. Concentration
Boston, MA: ave = 0.20 ng/m3
data 1978
25 out of 98 air samples from
Stoneville, Miss, in 1969 contained
endrin. The maximum level was
58.5 ng/m3
E. Food
1. Total average intake
Daily Dietary Intake, mg
Stanley et al.,
1971 (p. 435)
Bidleman, 1981
(p. 623)
Stanley et al.,
1971 (p. 435)
NAS, 1977
(p. 558)
1965
1966
1967
1968
1969
1970
6 yr. ave.
Trace Trace Trace 0.001 Trace Trace
1973 average daily intake =
0.033 ug/d or 0.0005 ug/kg/day
for a 69.1 kg man
2. Food concentrations
Observed in 1 garden fruit sample at
0.002 Mg/g (Attachment E)
Levels of endrin found by food class -
summary of 5 regions in U.S., June
1971 - July 1972 (p. 96-102)
0.001
U.S. EPA, 1980
(p. C-2)
FDA, no date
Manske and
Johnson, 1975
Food
Potatoes
Garden Fruits
Fraction
of Positive
Composites
3/35
1/35
Ave.
(ug/g)
Trace
Trace
Range
-------
Levels of endrin found by food class
Summary of 5 regions in U.S., Aug.
1972 - July 1973
Food
Fraction
of Positive
Composites
Johnson and
Manske, 1976
(p. 162-166)
Ave.
(Mg/g)
Range
(Mg/g)
Potatoes1/35Trace
II. HUMAN EFFECTS
A. Ingestion
1. Carcinogenity
"No malignancies attributed to
endrin have been reported."
2. Chronic Toxicity
a. ADI
70 pg/day
b. Effects
Data not immediately available.
B. Inhalation
Data not immediately available.
III. PLANT EFFECTS
A. Phytotoxicity
Data not immediately available
B. Uptake
See Table 4-1.
IV. DOMESTIC ANIMAL AND WILDLIFE EFFECTS
A. Tozicity
A 50 percent reduction in a brown pelican
population in Louisiana in 1975 has been
attributed in a large part to endrin because
endrin residues were detected in the brains
of several pelicans and because the reduc-
tion coincided with the peak in endrin
0.005
U.S. EPA, 1980
(p. C-33)
U.S. EPA, 1980
(p. C-39)
U.S. EPA, 1984
(V-42)
4-6
-------
residues in pelican eggs. It is believed
that endrin contributed to reduced eggshell
thickness.
See Table 4-2.
B. Uptake
Endrin residues in carcasses of 168
Bald Eagles from 29 states, 1975-77
Kaiser et al.,
1980 (p. 147)
Year
1975
1976
1977
// Specimens
with
residues
5
6
5
Median
Ug/g (WW)
0.16
0.48
0.07
Range
Ug/g (W/W)
0.09-1.0
0.18-3.0
0.06-2.5
Endrin residues in brains of 168 Bald
Eagles from 29 states, 1975-77
Kaiser et al.,
1980 (p. 147)
Year
1975
1976
1977
# Specimens
with
residues
3
6
5
Median
Ug/g (WW)
0.44
0.32
0.14
Range
Ug/g (W/W)
0.12-0.50
0.15-0.71
0.05-1.2
See Table 4-3.
Endrin administered in the diet of 12
rats was quickly metabolized and
eliminated
U.S. EPA, 1984
(p. 111-20)
4-7
-------
V. AQUATIC LIFE EFFECTS
A. Toxicity
1 . Freshwater
0.0023 Ug/L as a 24 hour average U.S. EPA, 1980
concentration; not to exceed 0.18
Ug/L at any time.
2. Saltwater
0.0023 ug/L as a 24 hour average U.S. EPA, 1980
concentration; not to exceed (p. B-12)
0.037 Ug/L at any time.
B. Uptake
1. Bioconcentration factor (BCF) Stephan, 1981
BCF = 5500 L/kg for edible portion of
all freshwater and estuarine aquatic
organisms consumed by U.S. citizens.
2. Hater concentrations causing
unacceptable tissue concentrations
Data not immediately available.
VI. SOIL BIOTA EFFECTS
In a study of the influence of 5 annual applica- Martin et al.
tions of 8 organic insecticides to 2 field soils 1958
on soil biological and physical properties, endrin (p. 337-8)
exerted no measurable effect on numbers of soil
bacteria and fungi, on kinds of soil fungi devel-
oping on dilution plates, on the ability of the
soil population to perform the normal functions of
organic matter decomposition and ammonia oxidation,
on water infiltration, or on soil aggregation.
VII. PHYSICOCHEMICAL DATA FOR ESTIMATING FATE AND TRANSPORT
Specific gravity: 1.7 at 20"C U.S. EPA, 1984
Vapor pressure: 2.7 x 10'7 at 25°C (II-l, V-7)
Formula: Ci2H8cl6°
Molecular wt . : 380.93
Solubility: 0.024 mg/1 in water
Organic soil adsorption constant: 3.4 x
Soluble in nonpolar solvents
OctanoL /water partition coefficient: 2.18
4-8
-------
TABI-fc 4-1. UITAKF OF HNDKIN IIY I'l AMI'S
Ti ssue
Plant/Tissue
Alfalla
Corn
Potatoes
Carrots
Oats
Corn
Sugar beets/tops
Potatoes
Carrots
Sugar beets/tops
Soil Type
sandy lojm
sandy loam
sandy loam
sandy loam
muck
muck
muck
muck
muck
muck
Chemical Form
cndrin
endrin
endrin
endrin
endrin
cndrin
end r i n
cndrin
endrin
endr in
Soil Cone untr.it ion
(PK/t>)
0.11-0.14
0.11-0.14
0.11-0.14
0.11-0.14
5.80-5.94
5.80-5.94
5.80-5.94
5.80-5.94
5.80-5.94
5.80-5.94
CuiiLunLral ion
0
0
0
0
0
0
0
.01
T
.01
.01
0
0
.01
.02
.1)1
Bioconcentrat ion
Factor0
0
0.077
0.077
.0017
0
0
0.017
0.034
0.017
Harris
Harris
Harris
Harris
Ham s
Harris
Harris
Harris
Harris
Harris
References
and Sans,
and Sans,
and Sans,
and Sans,
and Sans,
and Sans,
and Sans,
and Sans,
and Sans,
and Sans,
1969 (p.
1969 (p.
1969 (p.
1969 (p.
1969 (p.
1969 (p.
1969 (p.
1969 (p.
1969 (p.
1969 (p.
184)
184)
184)
184)
184)
184)
184)
184)
184)
184)
• BF - tissue cone./soil cone.
b NR = not reported
-------
TABLE 4-2. TOXIC1TY OP ENDH1N TO DOMhSTIC AN1MAIS AND WILDLIFE
Species (Nn)a
Rats (male)
Rats (female)
Rats
Rats
Rats
Mice
Dogs (female - 7)
(male - 7)
Dogs
Rats & Mice
(pregnant )
Chemical Form
Fed
endrin
endrin
endrin
endrin
endrin
endrin
endrin
endrin
endrin
Feed
Concent ration
(MB/g)
-
-
1
5
25
0.1-4.0
2 and 4
0.5
:> 2
Water Daily
Concentration Intake Duration
(mjj/L) (rag/kg) of Study
17.8 NHb
7.5 NK
l.ile
l.ile
l.ile
Life
2 years
- 2 years
NK
Effects References
Ll)50 NAS, 1977
1.1)50 (p. 564-567)
No obvious effects
Livur enlargement
Increased mortality.
degeneration in brain,
liver, kidneys & adrenals
Increased liver weights at
2 & it ug/g and vascular
damage ol liver cells
Convulsions and pathologic
changes in the brain
Highest no-adverse-ef tect
level
Increased maternal U.S. EPA, 1984 (V-60)
mortality, increased
Rats (pregnant)
Rats
Nice
endrin
endrin
endrin
resportions, decrease in
survival of offspring
at 21 days after birth
0.0/5 NU Highest no-adverse-
cllect level in
relation to maternal
weight gain and
alterations in behavior
>0.150 NK Reduced maternal weight
0.5 Maternal liver enlarge-
ment
1.0 Reduced maternal weight
gain
1.5 Increased maternal mortality
U.S. EPA, 19B4 (V-61)
Kavlock, et al., 1981
(p. 141)
a N = number of experimental animals when reported
b NR = not reported
-------
TABLE 4-3. UPTAKE OP ENDRIN BY DOMESTIC ANIMALS AND WILDLIFE
Species
Hen
Hen
Hen
Hen
Mallard
Chemical
Form Fed
Endrin
Endrin
Endrin
Endrin
Endrin
Range of
Feed Concent rat. ion
(Pg/g)
0
0
0
0
10
.13
.13
.13
.13
.0
Tibsue
Analyzed
Meal
Liver
Kidney
Fa i
Carcass
Range
Tissue
Concent rai ion
(M8/U)
<0.0()J2-0.095
0.01 j-0.20
0.035-0.11
0.32-1.21
1.41-1.9
BioconcentraL ion
Factor8
<00.02-0.73
0.10-1.54
0.27-1.0
2.46-9.31
0.14-1.9
References
U.S.
U.S.
U.S.
U.S.
U.S.
EPA,
EPA,
EPA,
EPA,
EPA,
1984
1984
1984
1984
1984
(p.
(p.
(p.
(p.
-------
SECTION 5
REFERENCES
Baxter, J.C., M. Aquilar, and K. Brown. 1983. Heavy Metals and
Persistent Organics at a Sewage Sludge Disposal Site. J. Environ.
Qual. 12(3):311-315.
Bidleman, T.F. 1981. Interlaboratory Analyses of High Molecular Weight
Organochlorines in Ambient Air. Atmospheric Environ. 15:619-624.
Camp Dresser and McKee, Inc. 1984a. technical Review of the 106-Mile
Ocean Disposal Site. Prepared for U.S. EPA under Contract No.
68-01-6403.
Camp Dresser and McKee, Inc. 1984b. Technical Review of the 12-Mile
Sewage Sludge Disposal Site. Prepared for U.S. EPA under Contract
No. 68-01-6403. Annandale, VA. May.
Carey, A., J.A. Gowen, H. Tai, et al. .1978. Pesticide Residual Levels
in Soils and Crops, 1971 - National Soils Monitoring Program (III).
Pest. Monit. J. 12(3):117-136.
Carey, A., P. Douglas, H. Tai, et al. 1979a. Pesticide Residue
Concentration in Soils of Five United States Cities, 1971 - Urban
Soils Monitoring Program. Pest. Monit. J. 13(1):17—22.
Carey, A., J.A. Gowen, H. Tai, et al. 1979b. Pesticide Residue Levels
in Soils and Crops from 37 States, 1972. Pest. Monit. J.
12(4):209-229.
Carey, A., H.S. Yang, G.B. Wiersma, et al. 1980. Residual
Concentrations of Propanil, TCAB and Other Pesticides in Rice-
Growing Soils in the United States, 1972. Pest. Monit. J.
13(l):23-25.
City of New York Department of Environmental Protection. 1983. A
Special Permit Application for the Disposal of Sewage Sludge from
Twelve New York City Water Pollution Control Plants at the 12-Mile
Site. New York, NY. December.
Clevenger, T.E., D.D. Hemphill, K.R. William, and W.A. Mullins. 1983.
Chemical Composition and Possible Mutagenicity of Municipal
Sludges. Journal WPCF 55(12):1470-1475.
Edwards, C.A. 1973. Pesticide Residues in Soil and Water. In!
Edwards, C.A. (ed.), Environmental Pollution by Pesticides. New
York: Plenum Press.
Glooshenko, W., W.M. Strachan, and R.C. Sampson. 1976. Distribution of
Pesticides and Pol/chlorinated Biphenyls in Water, Sediments, and
Seston of the Upper Great Lakes - 1974. Pest. Monit. J. 10(2):61-
67.
5-1
-------
Grant, B. 1976. Endrin Toxicity and Distribution in Freshwater: A
review. Bui. Env. Contam. and Tox. 15(3):283-290.
Harris, C.R. and W.W. Sans. 1969. Absorption of Organochlorine
Insecticide Residues from Agricultural Soils by Crops Used for
Animal Feed. Pest. Monit. J. 3(3):283-290.
Johnson, R. and D. Manske. 1975. Pesticide Residues in Total Diet
Samples (IX). Pest. Monit. J. 9(4):157-169.
Kaiser, T., W.L. Reichel, L.N. Locke, et al. 1980. Organochlorine
Pesticide, PCB, and PBB Residues and Necropsy Data for Bald Eagles
from 29 States - 1975-77. Pest. Monit. J. 13(4):145-149.
Kavlock, R., N. Chernoff, R.C. Hanisch, et al. 1981. Perinatal
Toxicity of Endrin in Rodents. II. Fetotoxic Effects of Prenatal
Exposure in Rats and Mice. Toxicology 21:141-150.
Lang, J., L.C. Rodringuex, and J.M. Livingston. 1979. Organochlorine
Pesticide Residues in Soils from Six U.S. Air Force Bases, 1975-76.
Pest. Monit. J. 12(4):230-233.
Majeti, V. and C. Clark. 1980. Potential Health Effects from Persis-
tent Organics in Wastewater and Sludges Used for Land Application.
EPA 600/1-80-025.
Manske, D. and R. Johnson. 1975. Pesticide Residues in Total Diet
Samples - VIII. Pest. Monit. J., 9(2):94-105.
Martin, J.P. 1972. Side Effects of Organic Chemicals on Soil
Properties and Plant Growth. In; Goring, C. A. and Hamaker, J. W.
(eds.), Organic Chemicals in the Environment. New York: Marcell
Dekker Inc.
Mattraw, H. 1975. Occurrence of Chlorinated Hydrocarbon Insecticides,
Southern Florida - 1968-72. Pest. Monit. J. 9(2):106-114.
National Academy of Sciences. 1977. Drinking Water and Health.
Washington, D.C.: NAS; National Review Council Safe Drinking Water
Committee.
NOAA Technical Memorandum NMFS-F NEC-26. Northeast Monitoring Program
106-Mile Site Characterization Update. U.S. Department of Commerce
National Oceanic and Atmospheric Administration. August.
Requejo, A. G., R.H. West, P.G. Hatcher, and P.A. McGillivary. 1979.
Polychlorinated Biphenyls and Chlorinated Pesticides in Soils of
the Everglades National Park and Adjacent Agricultural Areas. Env.
Sci. & Tech. 13(8):931-935.
Standford Research Institute International. 1980. Seafood Consumption
Data Analysis. Final Report, Task 11. Prepared for USEPA under
Contract No. 68-01-3887. Menlo Park, California.
5-2
-------
Stanley, C.W., J.E. Barney, M.R. Helton, and A.R. Yobs. 1971.
Measurement of Atmospheric Levels of Pesticides. Env. Sci. & Tech.
5(5):430-435.
Stephan, C.E. Memorandum dated May 26, 1981, to J.F. Stara, U.S. EPA,
ECAO-Cincinnati.
Stickel, L. 1973. Pesticide Residues in Birds and Mammals. In;
Edwards, C.A. (ed.), Environmental Pollution by Pesticides. New
York: Plenum Press.
United States Environmental Protection Agency. 1980. Ambient Water
Quality Criteria for Endrin. EPA 440/5-80-047. U.S. EPA,
Washington, D.C.
United States Environmental Protection Agency. 1982a. Fate of Priority
Pollutant's in Publicly-Owned Treatment Works. Volume 1. EPA
400/1-82/303. U.S. EPA, Washington, D.C.
United States Environmental Protection Agency. 1982b. Test Methods for
Evaluating Solid Waste. SW-846. U.S. EPA, Washington, D.C.
United States Environmental Protection Agency. 1984. Air Quality
Criteria for Lead. External Review Draft. EPA 600/8-83-028B.
Environmental Criteria and Assessment Office. Research Triangle
Park, NC. September.
United States Food and Drug Administration. No date. FY78 Total Diet
Studies-Adult (7205.003).
5-3
-------
APPENDIX
PRELIMINARY HAZARD INDEX CALCULATIONS FOR ENDRIN
IN MUNICIPAL SEWAGE SLUDGE
I. LANDSPREADING AND DISTRIBUTION-AND-MARKETING
Based on Che recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
II. LANDFILLING
Based on the recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
III. INCINERATION
Based on the recommendations of the experts at the OWRS meetings
(April-May, 1984), an assessment of this reuse/disposal option is
not being conducted at this time. EPA reserves the right to
conduct such an assessment for this option in the future.
IV. OCEAN DISPOSAL
A. Index of Seawater Concentration Resulting from Initial Mixing
of Sludge (Index 1)
1. Formula
SC x-ST x PS
Index 1 =
W x D x L
where:
SC = Sludge concentration of pollutant (mg/kg DW)
ST = Sludge mass dumped by a single tanker (kg WW)
PS = Percent solids in sludge (kg DW/kg WW)
W = Width of initial plume dilution (m)
D = Depth to pycnocline or effective depth of mixing
for shallow water site (m)
L = Length of tanker path (m)
2. Sample Calculation
0 00028 Ug/L = °'14 mg/kgDW x 1600000 kgWW x 0.04 kgDW/kg WW x 1Q3
200 m x 20 m x 8000 m x 10^
A-l
-------
B. Index of Seavater Concentration Representing a 24-Hour Dumping
Cycle (Index 2)
1. Formula
SS x SC
Index 2 =
V x D x L
where:
SS = Daily sludge disposal rate (kg DW/day)
SC = Sludge concentration of pollutant (mg/kg DW)
V = Average current velocity at site (m/day)
D = Depth to pycnocline or effective depth of
mixing for shallow water site (m)
L = Length of tanker path (m)
2. Sample Calculation
0 000076 y /L = 82500° kS DW/day x 0.14 mg/kg DW x IP3 Ug/mg
9500 m/day x 20 m x 8000 m x 103 L/m3
C. Index of Hazard to Aquatic Life (Index 3)
1. Formula
where:
\2 = Index 2 = Index of seawater concentration
representing a 24-hour dumping cycle (jag/L)
AWQC = Criterion expressed as an average concentration to
protect the marketability of edible marine
organisms (ug/L)
2. Sample Calculation
0.000076 ug/L
0.0023 ug/L
D. Index of Human Toxicity Resulting from Seafood Consumption
(Index 4)
1. Formula
(I 2 x BCF x 10~3 kg/g x FS x QF) + DI
Index 4 =
ADI
A-2
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where:
l£ = Index 2 = Index of seawater concentration
representing a 24-hour dumping cycle (yg/L)
QF = Dietary consumption of seafood (g WW/day)
FS = Fraction of consumed seafood originating from the
disposal site (unitless)
BCF = Bioconcentration factor of pollutant (L/kg)
DI = Average daily human dietary intake of pollutant
(ug/day)
ADI = Acceptable daily intake of pollutant (yg/day)
2. Sample Calculation
0.014 =
(0.000076 ug/L x 5500 L/kg x 10"3 kg/g x 0.000021 x 14.3 g WW/dav) * 1.0 Ug/dav
70 yg/day
A-3
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