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DRAFT-DO NOT QUOTE OR CITE
• Product Identity and Disclosure of Ingredients: EPA required submittal
of a Confidential Statement of Formula (CSF) based on the
requirements specified in 40 CFR 158.108 and 40 CFR 158.120 -
Subdivision D:Product Chemistry. Registrants who had previously
submitted still current CSFs were not required to resubmit this
information.
• Description of Beginning Materials and Manufacturing Process: Based
on the requirements mandated by 40 CFR 158.120 - Subdivision D,
EPA required submittal of a manufacturing process description for
each step of the manufacturing process, including specification of the
range of acceptable conditions of temperature, pressure, or pH at
each step.
• Discussion of the Formation of Impurities: Based on the requirements
mandated by 40 CFR 158.120 - Subdivision D, EPA required
submittal of a detailed discussion/assessment of the possible
formation of halogenated dibenzo-p-dioxins and dibenzofurans.
The second DCI (dated June 15, 1987), Data Call-In For Analytical Chemistry Data
on Polvhalogenated Dibenzo-p-Dioxins/Dibenzofurans (HDDs and HDFs). was issued for a
variety of pesticide active ingredients to the individual manufacturers of each ingredient.
(See Table 3-16.) All registrants supporting these pesticides were subject to the
requirements of this DCI unless the product qualified for various exemptions or waivers.
Pesticides regulated by the second DCI were strongly suspected to be contaminated with
detectable levels of HDDs/HDFs.
Under the second DCI, registrants whose products did not qualify for an exemption
or waiver were required to generate and submit the following types of data in addition to
the data requirements of the first DCI:
3-51 6/94
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DRAFT-DO NOT QUOTE OR CITE
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3-52
6/94
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Table 3-16. Pesticides That Are Suspected To Be Contaminated With Dioxins (continued)
en
10
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CD
Shaughnessy
Code
030033
030034
030035
030039
030052
030053
030055
030056
030062
030063
030064
030065
030066
030072
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031453
031463
Pesticide (Active Ingredient)
Triethanolamine 2,4-dichlorophenoxyacetate
Triethylamine 2,4-dichlorophenoxyacetate
Tri isopropanolamine 2,4-dichlorophenoxyacetate
N,N-Dimethyl oleyl-linoleyl amine 2,4-dichlorophenoxyacetate
Butoxyethoxypropyl 2,4-dichlorophenoxyacetate
Butoxyethy 1 2 , 4-di ch I orophenoxyacetate
Butoxypropyl 2,4-dichlorophenoxyacetate
Butyl 2,4-dichlorophenoxyacetate
Isobutyl 2,4-dichlorophenoxyacetate
Isooctyl(2-ethylhexyl) 2,4-dichlorophenoxyacetate
Isooctyl(2-ethyl-4-n»ethylpentyl) 2,4-dichlorophenoxyacetate
Isooctyl<2-octyl) 2,4-dichlorophenoxyacetate
Isopropyl 2,4-dichlorophenoxyacetate
Propylene glycol butyl ether 2,4-dichlorophenoxyacetate
4-(2,4-Dichlorophenoxy)butyric acid
Sodium 4-(2,4-dichlorophenoxy)butyrate
Dimethylamine 4-(2,4-dichlorophenoxy)butyrate
Butoxyethanol 4-(2,4-dichlorophenoxy)butyrate
Butyl 4-(2,4-dichlorophenoxy)butyrate
Isooctyl 4-(2,4-dichlorophenoxy)butyrate
2-(2,4-Dichlorophenoxy)propionic acid
Ditnethylamine 2-(2,4-dichlorophenoxy)propionate
Butoxyethyl 2-(2,4-dichlorophenoxy)propionate
Isooctyl 2-(2,4-dichlorophenoxy)propionate
CAS Number
2569-01-9
2646-78-8
32341-80-3
55256-32-1
1928-57-0
1929-73-3
1928-45-6
94-80-4
1713-15-1
1928-43-4
25168-26-7
1917-97-1
94-11-1
1320-18-9
94-82-6
10433-59-7
2758-42-1
32357-46-3
6753-24-8
1320-15-6
120-36-5
53404-32-3
53404-31-2
28631-35-8
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3-54
6/94
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DRAFT-DO NOT QUOTE OR CITE
• Quantitative Method For Measuring HDDs or HDFs: Registrants were
required to develop an analytical method for assessing the HDD/HDF
contamination of their products. The DCI established a regimen for
defining the precision of the analytical method (i.e., for internal
standard-precision within + /- 20 percent and recovery range of 50
to 150 percent, also a signal to noise ratio of at least 10:1 was
required). Target quantification limits were established in the DCI for
specific HDD and HDF congeners. (See Table 3-11.)
• Certification of Limits of HDDs or HDFs: Registrants were required to
submit a "Certification of Limits" in accordance with 40 CFR
158.110 and 40 CFR 158.120 - Subdivision D. Analytical results
were required that met the guidelines described above.
Registrants could select one of two options to comply with the second DCI. The
first option was to submit relevant existing data, develop new data, or share the cost to
develop new data with other registrants. The second option was to alleviate the DCI
requirements through several exemption processes including a Generic Data Exemption,
voluntary cancellation, reformulation to remove the active ingredient of concern, an
assertion that the data requirements do not apply, or the application/award of a low-
volume, minor-use waiver.
The data contained in CSFs, as well as any other data generated under Subdivision
D, are typically considered Confidential Business Information (CBI) under the guidelines
prescribed in FIFRA because they usually contain information regarding proprietary
manufacturing processes. In general, all analytical results submitted to EPA in response to
both DCIs are considered CBI and cannot be released by EPA into the public domain.
Summaries based on the trends identified in that data as well as data made public by EPA
are provided below.
To date, more than 100 submissions have been reviewed in response to the two
DCIs. The majority have been manufacturing process data in support of waiver requests,
3-55 6/94
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DRAFT-DO NOT QUOTE OR CITE
analytical method protocols, and sample collection protocols (telephone conversation
between S. Funk, EPA - Office of Pesticide Programs (OPP), and J. Dawson, Versar, Inc.
on 2/18/93). Analytical results on the levels of tetra- through hepta- HDDs/HDFs have
been received and reviewed for 16 distinct pesticide active ingredients (Table 3-17). In
general, the analyses have not revealed HDD/HDF concentrations in excess of the LOQs
specified in Table 3-11. For those products in which LOQs are exceeded, the identified
contamination levels were generally within an order of magnitude of the LOQ and apply
only to one or two congeners per product (telephone conversation between S. Funk, EPA/
OPP, and J. Dawson, Versar, Inc. on 2/18/93). Table 3-18 presents a summary of results
recently reported by EPA for CDDs and CDFs in eight technical 2,4-D herbicides.
3.4.4. Chlorine Production Using Graphite Electrodes
The production and use of chlorine gas has involved processes that result in the
generation of CDFs (Rappe, 1992a). Chlorine is commonly produced via electrolysis of
brine in mercury cells. High levels of CDFs have been found in the graphite electrode
sludge from this chemical process and may have been responsible for occupational
exposures among workers who handled these sludges. Svensson et al. (1992) evaluated
the relationship between blood CDF levels in chloralkali plant workers and direct exposure
of these workers to electrode sludges and to dust and earth contaminated with graphite
electrode sludge. Subjects who had been exposed by handling graphite electrode sludge
had higher levels of 2,3,7,8-substituted PeCDFs and HxCDFs than reference subjects.
Evaluations of congener distribution patterns have demonstrated that the 2,3,7,8-
substituted CDFs are the major congeners formed during the chloralkali process (Rappe et
al., 1990; Rappe, 1992a).
Until the late 1970s, graphite electrodes were the primary type of anode used in
the chloralkali industry (Curlin and Bommaraju, 1991). Since then, metal anodes have
been developed to replace graphite electrodes because of production problems associated
with their use (U.S. EPA, 1982; Curlin and Bommaraju, 1991). Currently, no U.S. facilities
are believed to use graphite electrodes in the production of chlorine gas (telephone
3-56 6/94
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DRAFT-DO NOT QUOTE OR CITE
Table 3-17. Summary of Analytical Data Submitted to-Date in
Response to Pesticide Data Call-In
Pesticide (Active Ingredient)
No, of Reviews Submitteda
1,2-Benzisothiazolin-3-one
2,4-Db
Atrazine
Bromoxynil
Chlorothalonil
Dacthal (DCPA)
Dicamba
Diclofop-Methyl
Diflubenzuron
Linuron
MCPAC
MCPB
MCPP (Mecoprop)
MCPP-p
Tetrachlorvinphos
Toclofos-Methyl
1
15
2
1
1
1
1
1
1
1
3
1
2
1
2
1
b
c
Indicates number of submissions containing analytical data that have been reviewed as
of 2/18/93 in support of each active ingredient (Personal communication - Jeff Dawson,
Versar, with Steve Funk, EPA/OPP/HED/CBRS on February 18, 1993; Schmitt, 1993;
Funk, 1994).
Includes all submissions for 2,4-D, 2,4-D esters, 2,4-DB, and 2,4-DP.
Includes submissions for MCPA-Ethylhexyl ester.
3-57
6/94
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Table 3-18. Summary of Results for CDDs and CDFs in
Technical 2,4-D Herbicides
Congener
2,3,7,8-TCDD
1,2,3,7,8-PeCDD
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
1, 2,3,4,6, 7,8-HpCDD
2,3,7,8-TCDF
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
1,2,3,4, 7,8-HxCDF
1, 2,3,6, 7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6, 7,8-HxCDF
1,2,3,4,6,7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
EPA
LOCr
{ppb}
0.1
0.5
2.5
2.5
2.5
100
1
5
5
25
25
25
25
1000
1000
Total
Number of
Technicals
8
8
8
8
8
8
8
8
7
8
8
8
8
8
8
2,4-D
Number of
Technicals
Greater Than
LOQ
2
3
0
0
0
0
0
0
0
0
0
0
0
0
0
Observed
Maximum
Concentration
(ppb)
0.13b
2.6C
0.81
0.77
0.68
1.5
0.27
0.62
0.73
1.6
1.2
1.4
1.1
8.3
1.2
Source: Schmitt (1993)
al_imit of quantitation required by the Agency.
^Average 0.07 ppb, where 50 percent of demonstrated LOQ used for analytes not found.
cAverage 0.63 ppb, where 50 percent of demonstrated LOQ used for analytes not found.
3-58
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DRAFT-DO NOT QUOTE OR CITE
conversation between L. Phillips, Versar, Inc., and T. Fielding, U.S. EPA, Office of Water,
February 1993). Although the use of graphite electrodes has been eliminated, the
potential for CDD/CDF releases from dump sites containing contaminated sludges may still
exist (Svensson et al., 1992; Rappe, 1992a).
3.4.5. Petroleum Refining Catalyst Regeneration
Catalyst regeneration in the petroleum refinery reforming process has been
identified as a source of CDDs and CDFs based on testing conducted in Canada
(Thompson et al., 1990). According to Thompson et al. (1990), "catalytic reforming is a
refinery process which is used to produce high octane gasoline. The reforming process
occurs at high temperature and pressure and requires the use of a catalyst. During the
catalytic process, a complex mixture of aromatic compounds known as coke is formed and
deposited onto the catalyst. As coke deposits onto the catalyst, its activity is decreased.
The high cost of the catalyst necessitates its regeneration. Catalyst regeneration is
achieved by removing the coke deposits via burning and activating the catalyst using
chlorinated compounds. Burning of the coke produces flue gases which contain CDDs and
CDFs along with other combustion products." Thompson et al. (1990) reported total CDD
and CDF concentrations of 8.9 ng/m3 and 210 ng/m3, respectively, in stack gas samples
from petroleum refinery reforming operations (Table 3-19). It was also found that the CDD
and CDF congener distribution patterns observed were similar to those found in municipal
waste incinerator ash and stack samples. Because flue gases may be scrubbed with
water, internal effluents may also be contaminated with CDD/CDFs. Thompson et al.
(1990) observed CDDs and CDFs in the internal wash water from a scrubber of a
periodic/cyclic regenerator (Table 3-20).
The Canadian Ministry of the Environment detected concentrations of CDDs in an
internal wastestream of spent caustic in a petroleum refinery that ranged from 1.8 to 22.2
ppb, and CDFs ranging from 4.4 to 27.6 ppb. The highest concentration of 2,3,7,8-TCDD
was 0.0054 ppb (Maniff and Lewis, 1988). CDDs were also observed in the refinery's
biological sludge at a maximum concentration of 74.5 ppb, and CDFs were observed at a
3-59 6/94
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DRAFT-DO NOT QUOTE OR CITE
Table 3-19. CDDs/CDFs in Petroleum Refinery Stack Gas from
a Continuous Regenerator Without Scrubber
Congener Group
TCD
PeCD
HxCD
HpCD
OCD
TOTAL
Concentration8 tog/m^)
CDDs PCDFs
1.6(7)
3.4 (8)
1 .9 (4)
1.2(2)
0.8
8.9
46(11)
120 (10)
31 (9)
12(4)
1.7
210
a Values represent average concentrations for three tests. Numbers in brackets indicate
number of isomers detected.
Source: Thompson et al. (1990).
3-60
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Table 3-20. CDDs/CDFs in the Scrubber Wash Water from a Petroleum
Refinery Periodic/Cyclic Regenerator
Congener
Group
TCDD
PeCDD
HxCDD
HpCDD
OCDD
TCDF
PeCDF
HxCDF
HpCDF
OCDF
No. of Positive8
Occurences
7
7
6
1
1
7
7
7
7
7
Concentration Range13 (ppq)
Low
44
15
ND(17)
ND(20)
ND(22)
150
40
20
10
23
High
110
90
160
64
56
660
330
260
160
93
No. of Congeners
Low
7
2
0
0
0
14
5
3
1
1
High
11
13
6
2
1
14
10
12
4
1
a Number of positive occurences based on seven samples analyzed.
b Numbers in parentheses are detection limits.
Source: Thompson et al. (1990).
3-61
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DRAFT-DO NOT QUOTE OR CITE
maximum concentration of 125 ppb (Maniff and Lewis, 1988). The concentration of
CDD/CDFs in the final combined refinery plant effluent was below the detection limits.
Insufficient data are available to evaluate CDD/CDF releases from these sources in
the United States. However, Beard et al. (1993) conducted a series of benchtop
experiments to investigate the mechanism(s) of CDD/CDF formation in the catalytic
reforming process. A possible pathway for the formation of CDFs was found, but the
results could not explain the formation of CDDs. Analyses of the flue gas from burning
coked catalysts revealed the presence of unchlorinated dibenzofuran (DBF) produced in
quantities of up to 220 ng/g of catalyst. Chlorination experiments indicated that
dibenzofuran and possibly biphenyl and similar hydrocarbons act as CDF precursors and
can become chlorinated in the catalyst regeneration process. Corrosion products on the
steel piping of the process plant seem to be the most likely chlorinating agent.
Furthermore, CDFs can form by de novo synthesis from chlorinated hydrocarbons like
trichloroethylene, methylene chloride, and carbon tetrachloride in the presence of
and HCI or CI2-
3.4.6. Additional Chemical Manufacturing and Processing Sources
Rappe et al. (1989) reported the formation of CDFs (tetra- through octa-chlorinated
CDFs) when tap water and double-distilled water were chlorinated using chlorine gas. The
CDF levels found in the single samples of tap water and double-distilled water were 35 and
7 pg TEQ/L, respectively. The water samples were chlorinated at a dosage rate of 300 mg
of chlorine per liter of water which is considerably higher (by a factor of one to two orders
of magnitude) than the range of dosage rates typically used to disinfect drinking water.
Rappe et al. (1989) hypothesized that the CDFs or their precursors are present in chlorine
gas. It should be noted, however, that although few surveys of finished drinking water for
CDD/CDF levels have been conducted, the few that have been published only rarely report
the presence of any CDD/CDF even at low pg/L detection limits and in those cases the
CDD/CDFs were also present in the untreated water. (See Section 4.3.)
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DRAFT-DO NOT QUOTE OR CITE
Several recent studies have been conducted to identify the source(s) of CDD/CDFs
found in textiles and at dry cleaning facilities. Horstmann and McLachlan (1994) analyzed
35 new textiles and found total CDD/CDF levels generally less than 50 pg/g; however,
some items were as high as 290,000 pg/g. The authors conclude that textile finishing
processes are not likely to be the source of the high CDD/CDF levels found because of the
apparent randomness of the textiles with high CDD/CDF levels. However, the authors
hypothesize that the use of pentachlorophenol to preserve cotton, particularly when it is
randomly strewed on bales of cotton as a preservative during sea transport, is the likely
source of the high levels occasionally observed. As discussed in Section 3.4.3, the use of
pentachlorophenol (PCP) for nonwood uses has been prohibited in the United States since
1987. However, Horstmann and McLachlan (1994) comment that PCP is still used in
developing countries, especially for purposes of preserving cotton during sea transport. As
discussed in Section 3.4.1.5, certain dyes and pigments have also been observed to
contain CDD/CDFs and may also contribute to levels found in textiles. Horstmann and
McLachlan (1994) also summarize recent research concerning CDD/CDFs in dry cleaning
residues and reach the conclusion that new textiles are the source of the CDD/CDFs
found.
3.5. MECHANISMS OF FORMATION OF DIOXIN-LIKE COMPOUNDS DURING
COMBUSTION OF ORGANIC MATERIALS
The specific molecular mechanisms by which CDDs and CDFs are initially formed
and then emitted from combustion sources remain largely unknown and are theoretical.
The theoretical basis for conjecture is derived primarily from direct observations in
municipal solid waste incinerators and from well conducted laboratory studies. Municipal
solid waste incinerators (MSWIs) have been heavily studied from the perspective of
eventually finding the specific formation mechanism transpiring within the system, and
determining ways to either significantly reduce such opportunities or ultimately hinder the
formation kinetics to preclude evolution of these chemicals. Although much has been
learned from these studies, it is still not known how to completely block the formation of
CDDs/CDFs during the combustion of certain organic materials in the presence of a source
3-63 6/94
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DRAFT-DO NOT QUOTE OR CITE
of chlorine. Adding to this complexity is the wide variability of organic materials that are
incinerated and thermally processed by a wide spectrum of combustion technologies
having variable temperatures, residence times, and oxygen requirements. However, it is
possible to identify the central chemical events participating in the formation of CDDs and
CDFs by evaluating emission test results from MSWIs in combination with laboratory
experiments.
The emission of CDDs and CDFs can be explained by three principal theories, which
should not be regarded as being mutually exclusive. The first is that CDD/CDFs are
present as contaminants in the combusted organic material. This theory is discussed in
Section 3.5.1. The second is that CDDs/CDFs are ultimately formed from the thermal
breakdown and molecular rearrangement of precursor compounds, which are defined as
chlorinated aromatic hydrocarbons having a structural resemblance to the CDD/CDF
molecule. This theory is discussed in Section 3.5.2. The third theory, similar to the
second and described in Section 3.5.3, is that CDDs/CDFs are synthesized de novo; this
means they are formed from organic and inorganic substrates comprised of singular or
mixtures of molecules bearing little resemblance to the molecular structure of CDDs or
CDFs. Section 3.5.4 discusses the generation of coplanar PCBs. Section 3.5.5 discusses
the evaluation of naturally occurring CDDs/CDFs by examinations of sediment core data,
and Section 3.5.6 provides a closing summary of the three principal theories of formation.
3.5.1. CDD/CDF Contamination in Fuel as a Source of Combustion Stack Emissions
The first theory states that CDD and CDF compounds present as contaminants in
the fuel or waste products that are fed into the combustion chamber are responsible for
dioxin and dibenzofuran emissions out the stack of the combustion process. Most work in
this area has involved the study of municipal solid waste incineration (MSWI) in which
case CDDs and CDFs have been analytically detected in the raw refuse fed into the MSWI.
Tosine, et al. (1983) first reported detecting trace amounts of HpCDD and OCDD in the
MSW fed into an MSWI in Canada. HpCDD ranged in concentration from 100 ppt to 1
ppb, and OCDD ranged from 400 to 600 ppt. Wilken et al. (1992) separated the various
solid waste fractions of MSW collected from municipalities in Germany and analyzed them
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for the presence of CDDs/CDFs and other organochlorine compounds. Total CDDs/CDFs
were detected in all MSW fractions in the following range of concentrations: paper and
cardboard = 3.1 to 45.5 ppb; plastics, wood, leather, textiles combined = 9.5 to 109.2
ppb; vegetable matter = 0.9 to 16.9 ppb; and "fine debris" (defined as particles < 8 mm)
= 0.8 to 83.8 ppb. Ozvacic (1985) measured CDDs/CDFs in the raw MSW fed into two
MSWIs operating in Canada. In one MSWI, CDDs were detected in the refuse in a range
of concentration from 10 to 30 ppb, but no CDFs were detected (detection limit: 1 pg/g).
In the MSW fed to the second MSWI, CDDs were detected in a range of 75 to 439 ppb,
and CDFs were detected only in one of three samples at a total concentration of 11 ppb.
EPA has reported on the detection of CDDs/CDFs in refuse derived fuel (RDF) burned in a
large, urban MSWI (Federal Register, 1991). From 13 MSW samples taken prior to
incineration, CDDs were detected in a range of 1 to 13 ppb, and CDFs were measured in a
range of 0 to 0.6 ppb. In these samples, OCDD predominated, and the lower chlorinated
congeners were not detected.
Despite these findings, the conditions of thermal stress imposed by the incineration
process discounts the likelihood that the total magnitude of CDDs and CDFs, as measured
in the raw MSW, can explain the total magnitude of concentration as an emission from the
stack of the MSWI (Clement et al., 1990; Commoner, 1990). Contamination, however,
may partially contribute to the stack release. Clement and coworkers (1988) performed a
mass balance involving an input versus output of dioxin at two operational MSWIs in
Canada. These mass balance calculations clearly demonstrated that the mass of CDDs
and CDFs emitted at the point of the stack was much greater than the mass in the raw
MSW incinerated at the MSWIs, and that the profiles of the distributions of CDD/CDF
congeners were strikingly different. Primarily, higher chlorinated congeners were detected
as contaminants in the waste, whereas the total array of tetra - octa CDDs/CDFs were
emitted from the stack.
Commoner and coworkers (1984; 1985; 1987) evaluated the test data of a mass
burn MSW incinerator for the concentration of CDDs and CDFs at multiple sampling points
during the combustion process: (1) exit to the furnace; (2) entry to the heat exchanger; (3)
inlet to the electrostatic precipitator (ESP); (4) exit to the ESP; and (5) exit to the
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smokestack. Lowest or nondetectable concentrations of CDDs/CDFs were found at
sampling point (1), and highest concentrations were measured at sampling point (5). From
these sampling data. Commoner concluded that: CDDs/CDFs were not formed within the
furnace region where the waste material was combusted and that usually only OCDD and
OCDF were detected in extremely low concentrations at the point of exit to the furnace (if
dioxins were detected at all). It was also concluded that the CDDs/CDFs were mostly
formed as a synthesis process catalyzed by the properties of fly ash in combination with
chlorine, and that this probably transpired within areas downstream of the combustion
zone where the combustion offgases had cooled to less than 400°C. Commoner et al.
(1984, 1987) ruled out the effectiveness of combustion as a major factor in CDD/CDF
emissions from the stack; this would be expected if waste contamination was solely
responsible for the emission. This phenomena was independently observed by
Environment Canada in a series of tests of a modular MSW incinerator (Hay, et al., 1986;
Environment Canada, 1985). On a mass balance basis, the concentration of CDDs and
CDFs measured at the stack was approximately two orders of magnitude higher as
compared to the inlet to the boiler just after exiting the secondary furnace. The
temperatures of the combustion gases at these two points of measurement were 130 and
740°C at the stack and boiler inlet, respectively (Environment Canada, 1985). For the
most part, only OCDD was present in the hot gases exiting the furnace, whereas all the
congeners were present in the stack emissions, thus giving further evidence that
CDDs/CDFs are formed after the combustion zone. Using similar protocols, EPA and
Environment Canada (1991) jointly evaluated the emission of CDDs and CDFs from a
refuse-derived fuel MSWI operating in the United States. It was found that approximately
5 milligrams of total CDDs and CDFs per metric ton of MSW burned by the facility were
measured in the raw MSW prior to combustion, but no CDDs nor CDFs were detected at
the point of exit to the furnace prior to the inlet to the economizer (i.e., the heat exchanger
used to extract additional heat from the hot gases). Once heat in the combustion gas was
extracted for energy purposes and the gases were further cooled to less than 400 °C, the
total array of tetra- through octa-CDDs and CDFs could be detected.
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These series of experiments in which the mass balance of CDD/CDF was estimated
within the entire combustor, beginning with the waste and ending with the stack, discount
the first theory of dioxin formation (i.e., that dioxin in the feed accounts for ajl emissions
of dioxin from the stack to the air). Moreover, it is expected that the conditions of thermal
stress imposed by typical incineration and other combustion sources would destroy and
reduce the CDDs and CDFs present as contaminants in the waste to levels that are 0.0001
to 10 percent of the initial concentration, depending on the performance of the combustion
source and the level of combustion efficiency. Stehl et al. (1973) demonstrated that the
moderate temperature of 800°C enhances the decomposition of CDDs at a rate of about
99.95 percent, but that lower temperatures result in a higher survival rate. Theoretical
modeling has shown that unimolecular destruction of CDDs/CDFs at 99.99 percent can
occur at the following temperatures and retention times within the combustion zone:
977°C with a retention time of 1 second; 1000°C at a retention time of 1/2 second;
1227°C at a retention time of 4 milliseconds; and 1727°C at a retention time of 5
microseconds (Schaub and Tseng, 1983). Thus, CDDs and CDFs would have to be in
parts per million concentration in the feed to the combustor to be found in the part per
billion or part per trillion levels in the stack gas emission (Shaub and Tseng, 1983).
However, it cannot be ruled out is that CDDs/CDFs in the waste or fuel may contribute (up
to some percentage) to the overall concentration leaving the stack.
3.5.2. Formation of CDDs/CDFs from Precursor Compounds
The second theory states that the production of CDDs and CDFs is a direct result of
in-situ thermal degradation of precursor compounds during or after combustion of organic
materials. Present theory is mostly derived from laboratory experiments involving the
heating of suspect precursors in quartz ampules under starved-air conditions, and in
experiments investigating the role that combustion fly ash has in promoting the formation
of CDD/CDFs from precursor compounds.
Liberti and Brocco (1982) postulated that the general reaction that may be taking
place in a typical combustion process is a thermolytic synthesis and interaction between
two families of precursors indicated by A. and g. Precursors A are aromatic compounds
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having a definite phenolic structure (e.g., phenol and polychlorinated phenols), and
precursors B are chemical species that can act as a chlorine donor (e.g., PVC and HCI).
Esposito et al. (1980) offered a chemical basis for defining a dioxin precursor:
1. The compound is comprised of an ortho-substituted (positions 1 and 2 on the
compound) benzene ring in which one of the substituents is an oxygen atom directly
attached to the ring, and
2. It then must be possible for the two substituents on the benzene ring to react
with each other to form a new and independent compound under the influences of heat
and pressure (i.e., dioxin).
Dickson and Karasek (1987) further refined this definition to be consistent with the
formation kinetics thought to occur within combustion processes. In their definition, the
term "precursor" refers specifically to chlorinated aromatic compounds that are either
already present on the surface of combustion fly ash, or are present in the gas phase prior
to entering a critical region outside the combustion zone where the gases have cooled and
where heterogeneous catalyzed reactions take place that form CDDs/CDFs. Chlorophenols
and chlorobenzenes were identified as ideal precursor compounds in these reaction
pathways.
Controlled laboratory combustion experiments involving the thermal degradation of
aromatic compounds, either singly or in mixtures, have provided useful data in identifying
ideal precursor compounds. For example, Jansson and coworkers (1977) generated CDDs
through the pyrolysis of wood chips treated with tri-, tetra-, and penta-chlorophenol in a
bench-scale furnace operated at 500-600°C. Stehl and Lamparski (1977) combusted
grass and paper treated with the herbicide 2,4,5-trichlorophenoxyacetic acid (2,4,5-T) in a
bench-scale furnace at 600-800°C and generated ppmv levels of TCDD. Ahling and
Lindskog (1982) have reported on the formation of CDDs during the combustion of tri- and
tetrachlorophenol formulations at temperatures of 500-600 °C. Decreases in oxygen
during combustion generally increased the yield, and the addition of copper salts to the
tetrachlorophenol formulation significantly enhanced the yield of CDDs. Combustion of
pentachlorophenol resulted in low yields of CDDs except when burned with an insufficient
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supply of oxygen. In that case, the investigators noted the formation of tetra- through
octa-chlorinated congeners. Buser (1979) generated CDDs/CDFs on the order of 0.001-
0.08 percent (by weight) by heating tri-, tetra-, and pentachlorobenzenes at 620°C in
quartz ampules in the presence of oxygen. It was noted that chlorophenols were formed
as combustion by-products, and Buser (1979) speculated that these were acting as
reaction intermediates in the formation of CDDs/CDFs.
Recently it has been demonstrated that CDDs and CDFs are formed from aromatic
precursor compounds adsorbed onto the reactive surface of fly ash (paniculate matter)
entrained in the combustion plasma. Moreover, formation occurs outside and downstream
of the combustion zone of a furnace to a combustion source in regions where the
temperature of the combustion off gases has cooled to between 200 and 400 °C (Vogg et
al., 1987; Bruce et al., 1991; Cleverly et al., 1991; Gullet et al., 1990a; Commoner et al.,
1987; Dickson and Karasek, 1987; Dickson et al., 1992). Vogg and coworkers (1987)
have shown that inorganic chloride ions, such as copper chloride, present in the
combustion gas may act as a catalyst to promote surface reactions on paniculate matter
to convert aromatic precursor compounds to chlorinated dioxins and dibenzofurans. After
carefully extracting organics from MSWI fly ash, Vogg et al. (1987) added a known
concentration of isotopically labeled CDDs/CDFs to the matrix. The MSWI fly ash was
then heated in a laboratory furnace at varying temperatures for 2 hours. The treated fly
ash was exposed to increasing temperatures in 50 °C increments in a temperature range of
200 to 400°C. Table 3-21 summarizes these data.
Because the relative concentration of CDDs/CDFs increased while exposed to
varying temperature, Vogg, et al. (1987, 1992) concluded that formation of CDDs and
CDFs from precursor compounds on the surface of fly ash transpires during MSW
incineration within a specific range of temperature, 250 to 450°C. Within this range, the
concentration of CDDs/CDFs increases to some maxima, and outside this range the
concentration diminishes. Vogg et al. (1987) proposed an oxidation reaction pathway
giving rise to the formation of CDDs and CDFs in the post-furnace regions of the
incinerator in the following order: (1) hydrogen chloride gas (HCI) is thermolytically derived
as a product of the combustion of heterogeneous fuels containing abundant chlorinated
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Table 3-21. Concentration of CDDs/CDFs on Municipal Incinerator Fly
Ash at Varying Temperatures.
Congener
CDO
Tetra
Penta
Hexa
Hepta
Octa
CDF
Tetra
Penta
Hexa
Hepta
Octa
CDD/CDF Concentration on Ffy Ash (ng/g)
Temperature (°Q
200°
15
40
65
100
90
122
129
61
48
12
250°
26
110
217
208
147
560
367
236
195
74
300*
188
517
1029
1103
483
1379
1256
944
689
171
350°
220
590
550
430
200
1185
1010
680
428
72
400°
50
135
110
60
15
530
687
260
112
12
Source: Adapted from Vogg et al. (1987).
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organic chemicals and chlorides; (2) oxidation of HCI, with copper chloride (CuCI2) as a
catalyst, yields free gaseous chlorine; (3) phenolic compounds (present from combustion
of lignin in the waste or other sources) entrained in the combustion plasma are substituted
on the ring structure by contact with the free chlorine; and (4) the chlorinated precursor
to dioxin (e.g., chlorophenol) is further oxidized (with copper chloride as a catalyst) to yield
CDDs and CDFs and chlorine.
Gullett and coworkers (1990a; 1990b; 1991 a; 1991b; 1992) have studied the
formation mechanisms through extensive combustion research at EPA, and have verified
the observations of Vogg et al. (1987). It was proven that CDDs and CDFs could be
ultimately produced from low temperature reactions (i.e., 350°C) between Cl2 and a
phenolic precursor combining to form a chlorinated precursor, followed by oxidation of the
chlorinated precursors (catalyzed by a copper catalyst such as copper chloride) as in
examples (1) and (2), below.
(1) The initial step in the formation of dioxin is the formation of chlorine from HCI
in the presence of oxygen (the Deacon process), as follows (Vogg et al., 1987; Bruce
etal., 1991):
A
2HCI + 1/2 02 > H20 + CI2
(2) Phenolic compounds adsorbed on the surface of fly ash are chlorinated to form
the dioxin precursor, and the dioxin is formed as a product from the breakdown and
molecular rearrangement of the precursor. The reaction is promoted by the presence of
heat and copper chloride acting as a catalyst (Vogg et al., 1987; Gullett et al., 1992):
(a) phenol + CI2 > chlorophenol (dioxin precursor)
CuCI2
(b) 2-chlorophenol + 1/2 02 > dioxin + CI2
The major direct source of chlorine available for participating in the formation of
CDDs/CDFs is gaseous HCI, which is initially formed as a combustion by-product from the
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chlorine and chlorinated organic chemicals contained in the MSW (and other fuels) (Vogg
et al., 1987; Bruce et al., 1991; Cleverly, 1984; Commoner et al., 1987). MSW contains
approximately 0.45-0.90 percent (by weight) chlorine (Domalski et al., 1986). MSW
incinerators are a major stationary combustion source of air emissions of HCI, which
average between 400 to 600 ppm in the combustion gas (U.S. EPA, 1987). HCI is
converted to chlorine vapor by the Deacon process, and the vapor phase chlorine directly
chlorinates a dioxin precursor along the aromatic ring structure. Oxidation of the
chlorinated precursor in the presence of an inorganic chloride metal catalyst (of which
copper chloride was found to be the most active) yields CDDs and CDFs. Increasing the
yield of chlorine in vapor phase from the oxidation of HCI generally causes an increase in
the rate of formation of CDDs/CDFs. Formation kinetics are most favored at temperatures
between 200 to 350°C. Reductions in chlorine production, either by limiting initial HCI
concentration or by shortening the residence time in the Deacon process temperature
window, should result in decreases in the rate and magnitude of formation of CDDs and
CDFs (Bruce et al., 1991; Gullett et al., 1990b; Commoner et al., 1987). Bruce and
coworkers (1991) observed a general increase in the formation of CDDs and CDFs with
increases in the vapor phase concentration of chlorine. Figure 3-2 shows the apparent
dependence of the extent of formation of CDDs and CDFs upon chlorine concentration in
the vapor phase. Bruce et al. (1991) verified a dependence on the concentration and
availability of gaseous chlorine in the thermolytic formation of CDDs/CDFs.
In the testing of a variety of industrial stationary combustion sources during the
National Dioxin Study in 1987, EPA made a series of qualitative observations on the
relationship between total chlorine present in the fuel/waste and the magnitude of
emissions of CDDs and CDFs from the stack of the tested facilities (U.S. EPA, 1987). In
general, combustion units with the highest CDD emission concentrations had greater
quantities of chlorine in the fuel, and, conversely, sites with the lowest CDD emission
concentrations contained only trace quantities of chlorine in the feed. The typical chlorine
content of various combustion fuels has been reported by Lustenhouwer et al. (1980) as:
coal: 1,300^g/g; MSW: 2,500/yg/g; leaded gasoline: 300-1,600/yg/g; unleaded gasoline:
1-6/yg/g.
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Chlorine Concentration Dependence for the Formation of CDDs
20"!
18-j .
§
o
79.1 158.3 316.6 633.2
Vapor Phase Chlorine Concentration (mg/cu. meter)
Chlorine Concentration Dependance for CDF Formation
2.2 n
Legend
TCDF
PeCDF
79.1 158.3 316.6 633.2
Vapor Phase Chlorine oonoentratlon (mg/cu. meter)
Figure 3-2. The Association Between Vapor Phase
the Formation of CDDs/CDFs.
and
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The role that temperature plays in the formation kinetics has been investigated by
Oberg et al. (1989) on a full-scale hazardous waste incinerator operating in Sweden.
Oberg confirmed that the formation of CDDs/CDFs occurs after the furnace. Most of the
formation transpired in the boiler used to extract heat for co-generation of energy. In this
investigation, significant increases in total concentration of dioxin TEQ occurred between
temperatures of 280-400°C, and concentrations declined at temperatures above 400°C.
This is in agreement with the experimental evidence of the temperature range defined as
the "window of opportunity" for catalytic formation of CDDs/CDFs on the surfaces of fly
ash particles.
Dickson and Karasek (1987) have demonstrated that CDDs/CDFs can be directly
formed from the thermal conversion and oxidation of chlorinated precursors, in particular
chlorophenols, on the surface of MSWI fly ash while heated in a bench-scale furnace.
Their experiment was designed to mimic conditions of MSW incineration; to identify the
step-wise chemical reactions involved in converting a precursor compound into dioxin, and
to determine if MSWI fly ash could promote these reactions. MSWI fly ash was obtained
from a facility in Canada and a facility in Japan. The MSWI fly ash was extensively
solvent-extracted for any organic constituents prior to initiating the experiment. Twenty
grams of fly ash were introduced into a bench-scale oven (consisting of a simple flow-tube
combustion apparatus) and heated at 340°C overnight to desorb any remaining organic
compounds from the matrix. 13C12 -labeled pentachlorophenol (PCP) and two
trichlorophenol isotopes (13C12- 2,3,5-T and 3,4,5-T) were added to the surface of the
clean fly ash matrix, and placed into the oven for 1 hour at 300°C. Pure inert nitrogen
gas (flow rate of 10 ml/min) was passed through the flow tube to maintain constant
temperatures. Tetra- through octa- CDDs were formed from the labeled pentachlorophenol
experiment; over 100//g/g of total CDDs were produced. The congener pattern was
similar to the congener pattern found in MSWI emissions. The 2,4,5-T experiment
primarily produced HxCDDs and very small amounts of tetra- and octa-CDD. The 3,4,5-T
experiment mainly produced OCDD and 1,2,3,4,6,7,8-HpCDD. Dickson and Karasek
(1987) proposed that the chlorinated phenol may undergo molecular rearrangement or
isomerization as a result of dechlorination, dehydrogenation, and trans-chlorination before
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condensation occurs to ultimately form CDDs on the fly ash surface. These reactions
ultimately dictate the types and amounts Of CDDs that are formed.
Nestrick and coworkers (1987) reported on the thermolytic reaction between
benzene (an unsubstituted precursor) and iron (III) chloride on a silicate surface to yield
CDDs/CDFs at temperatures > 150°C. The experimental protocol was to introduce 100 -
700 mg of native and 13C6-benzene into a macro-reactor system consisting of a benzene
volatilization chamber connected to a glass tube furnace. The investigators noted the
relevance of this experiment to generalizations about combustion processes because
benzene is the usual combustion by-product of organic fuels. Inert nitrogen gas was used
to carry the benzene vapor to the furnace area. The exit to the glass tubing to the furnace
was plugged with glass wool, and silica gel was introduced from the entrance end to give
a bed depth of 7 cm to which the FeCI3 was added to form a FeCI3/silica reagent. The
thermolytic reaction took place in a temperature range of 150-400°C at a residence time
of 20 minutes. Although di- through octa-CDD/CDF were formed by this reaction at all the
temperatures studied, the percent yields were extremely small. Table 3-22 summarizes
these data.
3.5.3. The de novo Synthesis of CDDs/CDFs During Combustion of Organic Materials
The third and last theory states that CDDs/CDFs are formed in combustion
processes from materials and/or compounds that are not structurally related to CDDs/CDFs
on a molecular level. As in Theory 2, synthesis is believed to occur in regions outside of
the furnace zone of the combustion process where the combustion plasma has cooled to a
range of temperatures considered favorable to formation kinetics. A key component to de
novo synthesis is the production of intermediate compounds (either halogenated or non-
halogenated) that are precursors to dioxin formation. However, research in this area has
produced CDDs/CDFs directly from the heating of carbonaceous fly ash in the presence of
an inorganic ion without the apparent generation of reactive intermediates. Thus, the
specific steps involved in the de novo process have not been fully and succinctly
delineated. Laboratory experimentation has proven that MSWI fly ash, itself, is not an
inert substrate, and the matrix can actually participate in the formation kinetics. Typically
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Table 3-22. CDDs/CDFs Formed From the Thermolytic Reaction of
690 mg Benzene + FeC^Silica Complex.
Congener
DiCDD
TriCDD
TCDD
PeCDD
HxCDD
HpCDD
OCDD
Total CDDs
DiCDF
TriCDF
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Total CDFs
Mass Produced
{ng)
4.9
54
130
220
170
98
20
696.9
990
7,800
12,000
20,000
33,000
40,000
74,000
187,790
Number of Moles
Produced
0.019
0.019
0.400
0.620
0.440
0.230
0.040
1.940
4.200
29.00
39.00
59.00
88.00
98.00
167
484.2
Percent Yield3
4.3 E-7
4.3 E-6
9.0 E-6
1 .4 E-5
9.9 E-6
5.2 E-6
9.0 E-7
4.4 E-5
9.5 E-5
6.6 E-4
8.8 E-4
1.3E-3
2.0 E-3
1.1 E-3
3.8 E-3
1.1 E-2
a Percent yield = (number moles CDD/moles benzene) x 100.
Source: Nestrick et al. (1987)
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the fly ash is composed of an alumina-silicate construct with 5-10 percent concentrations
of silicon, chlorine (as inorganic chlorides), sulfur, and potassium (NATO, 1988). Twenty
percent of the weight of fly ash particles are carbon, and the particles have specific
surface areas in the range of 2-4 m2 (NATO, 1988). The distinguishing feature of the de
novo synthesis over the precursor synthesis is the thermolytic breakdown and molecular
rearrangement of chemical species unrelated to CDDs/CDFs at the start of the process to
yield precursor compounds. Theory 2 starts with the precursor compounds already
adsorbed onto the surface of fly ash or present in the gas phase (Dickson et al., 1992).
By this distinction, however, one could argue that Theory 3 is really an augmentation to
Theory 2 because the generation of CDDs/CDFs mav still require the formation of a dioxin
precursor. Nevertheless, a distinction is presented here for purposes of describing
additional pathways that have been suggested for the thermal formation of these
compounds.
To delineate the de novo synthesis of CDDs/CDFs from unrelated matter, Stieglitz
and coworkers (1989a) have conducted experiments involving the heating of particulate
carbon containing adsorbed mixtures of Mg and Al-silicate in the presence of copper
chloride as a catalyst to the reaction. The authors described annealing mixtures of Mg-AI
silicate with activated charcoal (4 percent by weight), chloride as potassium chloride
(7 percent by weight), and 1 percent copper chloride (CuCI2) (in water) in a glass tube at
300°C. The retention time was varied at 15 minutes, 30 minutes, and 1, 2, and 4 hours
to obtain differences in the amounts of CDDs/CDFs that could be formed. The results are
summarized in Table 3-23.
In addition to the CDDs/CDFs formed as primary products of the de novo synthesis,
the investigators observed the formation of precursors at the varying retention times of the
experiment. In particular, similar yields of tri- though hexa-chlorobenzenes, tri- through
hepta-chloronaphthalenes, and tetra- through hepta-chlorobiphenyls, were quantified which
were seen as highly suggestive of the role these compounds may play as intermediates in
the continued formation of CDDs/CDFs. Table 3-24 summarizes the experimental yields of
chlorinated benzenes as a function of the annealing time at 300°C. Stieglitz et al. (1989a)
made the following observations:
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Table 3-23. De Nova Formation of CDDs/CDFs After Annealing Mg-AI
Silicate, 4% Charcoal, 7% Cl, 1% CuCI2.2H20 at 300°C.
Congener
TCDD
PeCDD
HxCDD
HpCDD
OCDD
Total CDD
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Total CDF
Concentrations of CDD/CDF (ng/g)
Reaction Time (hrs)
0.25
2
110
730
1700
800
3342
240
1360
2500
3000
1260
8360
0.5
4
120
780
1840
1000
3744
280
1670
3350
3600
1450
10350
1
14
250
1600
3500
2000
7364
670
3720
6240
5500
1840
17970
2
30
490
2200
4100
2250
9070
1170
5550
8900
6700
1840
24160
4
100
820
3800
6300
6000
17020
1960
8300
14000
9800
4330
38390
Source: Stieglitz et al. (1989a).
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Table 3-24. De Novo Formation of Chlorinated Benzenes (CBzs),
Polychlorinated Naphthalenes (PCNs), and Polychlorinated
Biphenyls (PCBs) after Annealing Mg-AI Silicate,
4% Charcoal, 7% Cl, 1% CuCI2.2H20
CBzs
1,2,5-TSCBz
1,2,4-TSCBz
1 ,2,3-T3CBz
1,2,4,5-T4CBz
1,2,3,5-T4CBz
1 ,2,3,4-T4CBz
P5CBz
H6CBz
PCNs
T4CN
P5CN
H6CN
PCBs
T4CB
P5CB
H6CB
H7CB
Concentrations (ng/g)
Reaction Time (hrs)
0.25
80
330
660
440
1080
2280
4240
2640
60
75
125
5
70
60
40
0.5
90
1080
2580
1700
4200
9700
—
11500
80
125
190
10
75
70
60
1
220
1620
2890
2380
6300
11250
21000
10700
130
220
270
45
160
120
90
2
290
3470
5700
5150
9400
19100
37000
18300
220
360
425
40
260
170
130
4
520
4500
6300
6000
11300
20500
40300
2138
360
440
760
35
375
210
160
Source: Stieglitz et af. (1989a).
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1. The de novo synthesis of CDDs/CDFs via the reaction of carbonaceous
particulate matter exposed to a temperature of 300°C was clearly demonstrated.
Additionally, the experiment yielded ppb-ppm concentrations of chlorinated benzenes,
chlorinated biphenyls, and chlorinated napthalenes through a similar mechanism. When
potassium bromide was substituted for potassium chloride as a source of halogen for the
organic compounds in the reaction, polybrominated dibenzo-p-dioxins and dibenzofurans
were formed as reaction products.
2. Copper chloride catalyzed the de novo synthesis of CDDs/CDFs on the surface
of particulate carbon in the presence of oxygen to yield carbon dioxide and
chlorinated/brominated aromatic compounds.
3. Particulate carbon, which is characteristic of combustion processes, may act as
the source for the direct formation of CDDs/CDFs as well as other chlorinated organics.
More recently, Stieglitz and coworkers (1991) investigated the role that particulate
carbon plays in the de novo formation of CDDs/CDFs from fly ash containing appreciable
quantities of organic chlorine. Stieglitz et al. (1991) found that the fly ash contained 900
//g/g of bound organic chlorine. Only 1 percent of the organic chlorine was extractable.
Annealing the fly ash at 300-400°C for several hours caused the carbon to oxidize leading
to a reduction in the total organic chlorine in the matrix, and a corresponding increase in
the total extractable organic chlorine (TOX) (e.g., 5 percent extractable TOX at 300°C and
25-30 percent extractable total organic chlorine at 400°C). From this, Stieglitz et al.
(1991) concluded that the oxidation and degradation of carbon in the fly ash are the
source for the formation of CDDs/CDFs, and, therefore, are essential in the de novo
synthesis of these compounds.
Addink et al. (1991) conducted a series of experiments to observe the de novo
synthesis of CDDs/CDFs in a carbon-fly ash system. In this experiment, 4 grams of
carbon-free MSWI fly ash were combined with 0.1 gram of activated carbon and placed
into a glass tube between two glass wool plugs. The glass tube was then placed into a
furnace at a specific temperature in the range 200 to 400°C. This was repeated for a
series of retention times and temperatures. The investigators observed that the formation
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of CDDs/CDFs was optimized at the temperature of 300°C and at the furnace retention
times of 4-6 hours. Figure 3-3 displays the relationship between retention time,
temperature and the production of CDDs/CDFs from the heating of carbon particulate.
Addink et al. (1991) also investigated the relationship between temperature of the furnace
CDDs/CDF* Formed at 300 Degree Centigrade
1000 •
800
E
•
w
t»
•
E
o
c
m
600-
400-
200-
Total CDDs
Total CDFs
6 8
Sourw: Addink. DrijwrOlw (1991)
Figure 3-3. The de novo Synthesis of CDD/CDFs from Heating Carbon Particulate at
300°C at Varying Retention Times.
and the production of CDDs/CDFs from the annealing of carbonaceous fly ash. Figure 3-4
displays this relationship. In general, the concentration began to increase at 250°C and
crested at 350°C, with a sharp decrease in concentration above 350°C. The authors also
noted a relationship between temperature and the CDD/CDF congener profile; at 300°C to
350°C, the lower chlorinated tetra- and penta-CDD/CDF congeners increased in
concentration, while hexa-, hepta-, and octa-CDD/CDF congeners either remained the
same or decreased in concentration. The congener profile of the original MSWI fly ash
(not subject to de novo experimentation) was investigated with respect to changes caused
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Temperature Effects on CDD/COF Production
•
E
01
o
1000
•00-
600
400
200
0-
100
Total COO
Total CDF
200 300
T«mp«rirtur*-d0grM* cwttlgrad*
400 500
Source: Addink. Driver, and Otta (1991)
Figure 3-4. Relationship Between Temperature and the de novo Formation of
CDDs/CDFs.
by either temperature or residence time in the furnace. No significant changes occurred,
leading the authors to propose an interesting hypothesis for further testing: after
formation of CDDs/CDFs occurs on the surface of fly ash, the congener profile remains
fixed and insensitive to changes in temperature or residence time indicating some form of
equilibrium is reached in the formation kinetics.
Gullett et al. (1994) developed a pilot-scale combustor to study the effect on
CDD/CDF formation of varying the combustion-gas composition, temperature, residence
time, quench rate, and sorbent (Ca[OH]2) injection. The fly ash loading was simulated by
the injection on fly ash collected from a full-scale MSWI. Sampling and analysis indicated
CDD/CDF formation or the injected fly ash at levels representative of those observed at
full-scale MSWIs. A statistical analysis of the results showed that, although the effect of
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combustor operating parameters of CDD/CDF formation is interactive and very
complicated, substantial reduction in CDD/CDF formation can be realized with high
temperature sorbent injection to reduce HCI or CI2 concentrations, control of excess air
(also affects ratio of CDDs to CDFs formed), and increased quench rate.
The de novo theory also considers the generation of CDDs/CDFs from the
combustion of PVC resin. Key to the de novo synthesis of CDDs/CDFs is the initial
formation of HCI from combustion. Paciorek and coworkers (1974) thermally degraded
pure PVC resin at 400°C and produced 550 mg/g HCI vapor as a primary thermolysis
product, which was observed as being 94 percent of the theoretical amount based on the
percent weight chlorine on the molecule. Ahling et. al. (1978) have concluded that HCI
can act as a chlorine donor to ultimately yield chlorinated aromatic hydrocarbons from the
thermolytic degradation of pure PVC, and that these yields are a function of transit time,
percent oxygen, and temperature. The data they observed from 11 separate experiments
conducted with a range of temperatures from 570-1130°C indicated that significant
quantities of various isomers of dichloro-,.trichloro-, tetrachloro-, and hexachlorobenzenes
could be produced. Choudhry and Hutzinger (1983) proposed that the radical species Cl-
and H- generated in the incineration process may attack the chlorinated benzenes thus
formed, and abstract hydrogen atoms to produce ortho-chlorine substituted chlorophenol
radicals. These intermediate radical species then react with molecular oxygen to yield
ortho-substituted chlorophenols. As a final step, the ortho-substituted chlorophenols act
as ideal precursors to yield CDDs/CDFs with heat and oxygen.
Although most of the aforementioned experiments have involved the pyrolysis of
anthropogenic substances, the de novo formation of CDDs/CDFs is theoretically proposed
to include the combustion of autochthonous (naturally occurring) organic substances
(Choudhry and Hutzinger, 1983) in the presence of a chlorine donor. This possibility was
first advanced by scientists at Dow Chemical Co. in 1978 in a proposed working
hypothesis known as "the trace chemistries of fire" (Crummett, 1982). This proposed
working hypothesis was based on the following observations:
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1. Combustion processes are seldom more than 99.9 percent efficient in
converting carbonaceous fuel into carbon dioxide.
2. The remaining 0.1 percent of the fuel is converted into traces of organic species
including complex halogenated aromatic hydrocarbons. Most of these compounds have
not been identified in combustion emissions.
3. Municipal solid waste and fossil fuels contain complex mixtures of diverse
chemical species at variable concentrations.
4. Combustion fuels contain chlorine in a range of 1-5000 parts per million.
5. Particulate matter that is emitted from oil-fired heating and power plants contain
vanadium and nickel. Particulates emitted from coal-fired power plants contain vanadium,
nickel, iron, and manganese. In combination with silicon and unburned carbon, these
species can act as catalysts in the combustion process to form halogenated aromatic
hydrocarbons.
6. Chemical reactions that occur in flames include pyrolysis, oxidation, and
reduction. Ions, electrons, free radicals, and free atoms interact in a continuously
changing environment.
7. Dow scientists found traces of CDDs/CDFs in all particulate matter samples
taken from areas that were in close proximity to combustion sources.
8. Precursors for the formation of CDDs have been experimentally proven, and
have been identified to be primarily chlorinated phenols and chlorinated benzenes.
Because the pyrolysis of polyvinyl chloride (PVC) produces chlorobenzenes, the
combustion of PVC may cause the formation of CDDs/CDFs.
Dow Chemical Co. invited the scientific community at large to give advice on ways
in which the trace chemistries of fire hypothesis could be tested. The following studies
were proposed as a means of testing the hypothesis (Crummett, 1982):
1. Determine if CDDs/CDFs are present in soils (having a relatively high carbon
content) taken from drill cores beneath ancient lake beds at depths corresponding to 5, 12,
and 35,000 years of sedimentation and deposition.
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2. Determine if CDDs/CDFs are present in ice core samples taken from the center
of an ancient glacier.
3. Determine if CDDs/CDFs are present in volcanic ash.
4. Determine if CDDs/CDFs are present in sea breezes from remote islands in the
South Pacific.
5. Determine if CDDs/CDFs can be formed by the combustion of fossil fuels in the
presence of chlorine or inorganic chloride.
6. Determine if CDDs/CDFs can be detected in fish species taken from rivers
remote from chemical manufacturing but close to incinerators and fossil-fueled power
plants.
Although these studies were proposed in 1978, only items (3), (5) and (6) have even been
partially addressed. Thus the "trace chemistries of fire" remains largely a working
hypothesis that is in need of further testing and proving through well designed and
conducted field sampling and laboratory research programs. Nevertheless, there exists
some empirical evidence in this area.
Liberti et al. (1983) showed that CDDs/CDFs could be produced from the
combustion of pure vegetable extracts in the presence of chlorine gas and oxygen.
Pyrolytic degradation of extracts of chestnut, mimosa, and tannic acid was accomplished
in a bench-scale thermal reactor. When combustion proceeded without chlorine gas,
phenolic compounds and cresol were formed as primary thermolysis products. When the
vegetable extracts were burned in association with chlorine gas or PVC plastic,
chlorophenols and CDDs/CDFs were formed. Liberti et al. (1983) postulated that the PVC
was acting as a chlorine donor in the formation of CDDs/CDFs from phenolic compounds,
and that the chlorine gas directly formed the chlorinated precursor from a phenolic (pre-
dioxin) ring structure. Table 3-25 summarizes these experiments.
There is some empirical evidence that the burning of wood, in the presence of
chlorine or inorganic chlorides, may form CDDs/CDFs, although the evidence is not
conclusive. Few of these experiments had ruled out contamination of the wood fiber by
known chlorinated precursors through extraction and chemical analysis. None of the cited
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Table 3-25. CDDs/CDFs Formed from the Combustion of Vegetable
Extracts in the Presence of Chlorine Gas.
Congener
Tri
Tetra
Penta
Hexa
Hepta
Octa
CDF 0/9/9)
Chestnut
trace
trace
101
90
28
80
Mimosa
trace
trace
62
2
6
25
Fruit
21
47
40
44
15
NO
CDD (//g/g}
Chestnut
trace
trace
trace
trace
28
38
Mimosa
trace
trace
trace
trace
10
6
Fruit
35
74
62
16
15
ND
Source: Adapted from Liberti et al. (1983).
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experiments attempted to determine if the wood fiber was contaminated by CDDs/CDFs
prior to the conduct of the experiment. If the atmosphere serves to widely distribute
CDDs/CDFs, and if CDDs/CDFs can exist in the vapor and particle phases in the ambient
air, then trees and other biomass can become reservoirs of CDD/CDF contamination by
means of particle deposition onto and vapor diffusion into the biomass. Until these
possibilities have been addressed and their impacts, if any, are quantified, experiments in
which CDDs/CDFs are generated from the combustion of wood must be interpreted with a
certain degree of caution, especially with regard to proving that CDDs/CDFs can be formed
in nature without human intervention.
Ahling and Lindskog (1982) demonstrated that the combustion of untreated wood
in an open fire can generate relatively high concentrations of chlorinated aromatic
hydrocarbons in the emissions. These compounds include established dioxin precursors
such as di- through hexa-chlorobenzene and tetra- and penta- chlorinated phenols in ppbv-
ppmv concentrations. In addition, ppmv levels of benzene were produced. The presence
of chlorinated precursors indicates that inorganic chlorides in the plant may be capable of
chlorinating unsubstituted aromatic structures. Reaction kinetic experiments involving the
formation of HCI vapor (Olie et al., 1983; Choudhry and Hutzinger, 1983) have shown that
HCI can be formed from inorganic chlorides as a result of a reaction between sulfur dioxide
and sodium chloride during combustion, as follows:
A
2 NaCI + S02 + 1/2 O2 + H20 -—> Na2S04 + HCI
or: HCI can be liberated by the catalytic reaction of NaCI and a metal oxide. The general
reaction is:
A
NaCI + H20 + (A) > (B) + HCI
where: (A) is a metal oxide, i.e.: AI203, Fe203.
Olie et al. (1983) conducted wood burning experiments in a bench-scale
combustion unit. Wood treated with pentachlorophenol was incinerated to generate
CDDs/CDFs in one experiment, and 60-year-old wood from the demolition of a residence
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was burned in a separate experiment. The authors alleged that the 60-year-old wood
predated the manufacture and use of phenoxy wood preservatives and, therefore, probably
was absent any dioxin precursors; however, this was not analytically confirmed. They did
not directly monitor the smoke emissions for the presence of CDDs/CDFs, only the
collected fly ash. CDDs/CDFs were detected in the fly ash in ppbw concentrations.
However, the authors noted that the quantified CDDs/CDFs could have occurred as a
consequence of the previous tests of burning wood treated with pentachlorophenol.
Nestrick and Lamparski (1983) conducted studies on residential wood combustion
to evaluate the possibility that CDDs may form. This was accomplished through the
evaluation of soot scrapings from the chimneys of wood burning stoves. Samples were
taken at random from the eastern, central, and western regions of the United States.
Average total CDD levels in the chimney flue scrappings were: 8.3 ppb in the eastern
region, 42.5 ppb in the central region, and 9.9 ppb in the west.
EPA tested a freestanding noncatalytic residential wood stove for chimney flue gas
emissions of CDDs/CDFs during the combustion of pine and oak (U.S. EPA, 1987d).
Through a series of tests, it was determined that the wood fiber was free of known
chlorinated precursors (e.g., PCBs, chlorinated benzenes, and chlorinated phenols). The
total chloride concentration was found to be 125 ppm for the oak and 49 ppm for the pine
wood prior to burning in the wood stove. The combustion of the wood generated ppm
levels of aromatic hydrocarbon compounds. This relatively high loading of emissions on
the sampling device interfered with any speciation of CDD/CDF compounds in the
emissions. However, combustion ash samples provided an alternative matrix for
evaluation. The analysis of ash samples from the unit showed that only OCDD was
present as a dioxin contaminant at a maximum concentration of 0.09 ppb (by weight).
Wipe samples were also taken from inside the chimney flue. OCDD and hepta-CDD were
detected in the chimney soot at a maximum concentration of 0.6 ppb and 0.04 ppb,
respectively. No lower chlorinated CDDs nor any CDFs were found in the ash or soot
wipes.
Choudhry and Hutzinger (1983) have postulated that the complex structure of lignin
in wood fiber can pyrolyze to generate CDDs/CDFs if a chlorine donor is present. This
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theory is based on the experiments of Kirsbaum et at. (1972) in which two lignin
preparations (spruce and asp) were thermally degraded in glass tubes at 475°C to yield an
array of hydrocarbons, including phenol. If phenol could be formed, and if gaseous forms
of inorganic or organic chlorine are available, then the phenol could be chlorinated to form
a chlorophenol compound. The latter is then a precursor to the ultimate formation of
CDDs/CDFs. In addition, Choudhry and Hutzinger (1983) indicated that continued
pyrolysis of other hydrocarbons identified as thermolysis products in the combustion of
lignin could ultimately yield benzene. Nestrick et al. (1987) demonstrated that benzene
can react with an inorganic chloride in the presence of heat to produce a variety of
chlorinated aromatic compounds including CDDs/CDFs. If these thermolytic pathways are
operational in lignin pyrolysis, then, in theory, it is possible that forest fires can generate
CDDs/CDFs in the smoke, which has been proposed by Clement and Tashiro (1991).
Because of the potential importance of lignin pyrolysis as a potential, yet unverified,
combustion source of CDDs/CDFs in the environment, additional research should be
directed in this area. In the conduct of combustion experiments involving the pyrolysis of
lignin, attention should be given to the identification of any CDDs/CDFs or precursor
compounds that may exist as contaminants. Only after sample contamination has been
completely ruled out can the researcher draw convincing conclusions from the experiment.
Coal is a naturally occurring substance having the potential to form CDDs when
combusted. Mahle and Whiting (1980) first reported on the results of high temperature
combustion of bituminous coal in a bench scale furnace with the addition of HCI, NaCI, or
CI2t and air to yield CDDs. Table 3-26 summarizes these experiments. In experiment III,
tetra through octa-CDDs were formed from the oxidation of coal by air which had been
bubbled through a solution of hydrochloric acid. In a review of this experiment, Choudhry
and Hutzinger (1983) postulated that the hydrochloric acid aided in the chlorination of
aromatic hydrocarbons produced as combustion byproducts. This was also the case in
experiment IV in which chlorine gas was introduced into the oxidation of coal. Experiment
IV produced the highest yield of tetra- through octa-CDDs. When coal was combusted
only with air, the exothermic reaction did not generate detectable quantities of tetra- or
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Table 3-26. CDDs/CDFs Formed from the Combustion of Coal in the
Presence of NaCI, C/ or Hydrochloric Acid.
Experiment
No.
1
II
III
IV
Condition
coal + air
coal + air + NaCL
coal + air + HCI
coal + air + CI2
Quantity Formed (ng/g of coal)
TCDDs
ND(.08)
ND(.07)
1.4(.06)
1.2(.3)
HxCDDs
ND(.1)
ND(.2)
8.4(.1)
29 (.4)
HpCDDs
0.57(.3)
0.40(.24)
25.0(.3)
91.0(2)
OCDD
1.3(.7)
2.7(.5)
64(.6)
290(.3)
ND = Not detected; detection limit in parentheses ().
Source: Mahle and Whiting (1980).
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hexa- CDDs. Experiment I yielded only hepta- and octa-CDD in quantities close to the
detection limit.
3.5.4 Theory on the Emission of Polychlorinated Biphenyls
The air emission of polychlorinated biphenyls (PCBs) from MSW incinerators is less
understood. There are virtually no theories explaining the detection of these compounds in
incinerator emissions nor other combustion sources, the exception being the intentional
destruction of PCBs in hazardous waste incinerators in which case 99.9999 percent
destruction rated efficiency (DRE) must be achieved. When this occurs, 0.0001 percent of
the initial amount of PCBs fed into the hazardous waste incinerator may be emitted out the
stack. This may indicate that some small fraction of the PCBs present in the fuel fed into
an incineration process may result in emissions of PCBs from the stack of the process.
PCBs have been measured as contaminants in the raw refuse prior to incineration in
an MSWI (Choudhry and Hutzinger, 1983; Federal Register, 1991). It is possible to use
this information to test Theory 1 involved in CDD/CDF emissions: that the PCB
contamination present in the fuel is responsible for emissions from the stack. The mass
balance of total PCB beginning with measurement in the raw refuse and ending with
measurement at the stack to an RDF MSW incinerator (Federal Register, 1991) can be
used to calculate the destruction rated efficiency (DRE) of incineration of the PCB
contaminated MSW. Using results from test number 11 at the RDF facility (Federal
Register, 1991), a computation of DRE can be made with the following equation (Brunner,
1984):
W- - W
DRE = (_? £) 100% (3-1)
wi
where:
Wj = mass rate of contaminant fed into the incinerator system
W0 = mass rate of contaminant exiting the incinerator system
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In test 11,811 nanograms of total PCBs/gram of refuse (ng/g) were measured in
the MSW fed into the incineration system, and 9.52 ng/g of total PCB were measured at
the inlet to the pollution control device (i.e., outside the furnace region, but preceding
emission control). From these measurements, a ORE of 98.8 percent can be calculated.
Therefore, it appears that PCB contamination in the raw MSW that was fed into this
particular incinerator may have accounted for the emission of PCBs from the stack of the
MSW incinerator.
PCBs can be thermolytically converted into CDFs (Choudhry and Hutzinger, 1983;
U.S. EPA, 1984). This process occurs at temperatures somewhat lower than typically
measured inside the firebox of an MSWI. Laboratory experiments conducted by EPA (U.S.
EPA, 1984) indicate that the optimum conditions for CDF formation from PCBs are near a
temperature of 675°C in the presence of 8 percent oxygen and a residence time of 0.8
seconds. This resulted in a 3 to 4 percent efficiency of conversion of PCBs into CDFs.
Because 1 to 2 percent of the PCBs present in the raw refuse may survive the thermal
stress imposed in the combustion zone to the incinerator (Federal Register, 1991), then it
is reasonable to presume that PCBs in the MSW may contribute to the total mass of CDF
emissions released from the stack of the incinerator. This is speculative, and more
definitive research is needed in this area before strong conclusions can be made regarding
the causes of PCB emissions during combustion.
3.5.5. Evaluation of Naturally Occurring CDD/CDFs by Examination of Sediment Core Data
In the review of these theories, a question arises as to the contribution made by
combustion of synthetic organic substances produced by humans versus the contribution
made by natural sources to the overall thermolytic synthesis of CDDs and CDFs. This
question can be partially addressed using the results from analyses of the temporal
distribution of CDDs/CDFs in sediment core samples taken from lakes located near the
cradle of the U.S. industrial revolution (Czuczwa et al., 1984; Czuczwa and Hites, 1985;
Czuczwa and Hites, 1986; Smith et al., 1992). Czuczwa and Hites (1985) analyzed
sediment core samples taken in Lake Huron by the Great Lakes Research Station of the
University of Michigan. Sedimentation rates within the core samples were determined by
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using Cs-137 and Pb-210 techniques of Robbins and Edgington (1973). These rates were
used as a basis of relating depth of core sample to era. CDDs/CDFs were detected in the
core samples, and the results showed no appreciable degradation of CDDs/CDFs in the
sediments over time. The most abundant CDDs/CDFs were OCDDs, and HpCDDs/CDFs.
Analysis of depth of core sample versus era showed that the CDDs/CDFs increased
steadily in concentration beginning at about 1940 and leveled off at about 1960.
Comparisons were made between this trend and the total production of synthetic
chlorinated organic chemicals, as well as the total volume of coal combusted for energy
production. If it is theoretically possible that the combustion of coal produces air
emissions of CDDs/CDFs, then this should be reflected in the sediments. The pattern of
levels of CDDs and CDFs in the sediment cores seemed to track the total volume
production of synthetic chloro-aromatics by the petrochemical industry in the United
States, whereas the consumption of coal did not show a good correlation. Czuczwa and
Hites (1985) concluded that the history of sedimentation rates of CDDs/CDFs in core
samples from Lake Huron were reflective of atmospheric deposition from the combustion
of synthetic chloro-aromatics, and, therefore, could only have come from the combustion
of anthropogenic substances.
In a separate study, Czuczwa et al. (1984) and Czuczwa and Hites (1986) reported
on the temporal variability of CDDs/CDFs in sediment core samples taken from a
wilderness lake located in an uninhabited/undeveloped island (Siskiwit Lake, Isle Royale) in
Lake Superior. Comparisons were made between the congener profiles found in the lake
sediments to congener profiles found in urban air particulates. A near perfect correlation
was found (correlation coefficient = 0.998), leading to the observation that CDDs/CDFs
entered the lake system from aerial transport and deposition. The historical record of
CDD/CDF concentration in the core samples showed that CDDs/CDFs were virtually absent
from the sediments until around 1940, therefore ruling out any significant contribution to
background from natural sources such as forest fires.
Using a similar study design. Smith et al. (1992) investigated the temporal
distribution by era in sediment core samples taken from Green Lake, New York, near
Niagara Falls. Green Lake is a State Park, and removed from direct discharge of
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CDDs/CDFs into the system. The investigators found a similar congener profile as
Czuczwa et al. (1984) and Czuczwa and Hites (1986) in the sediments, and found
excellent agreement with measured deposition flux of OCDD into the lake and the
concentration of OCDD in the most recent sediment layer. This supports the observation
of Hites (1991) on the importance of atmospheric transport and deposition as a major
pathway of entry of CDDs/CDFs into the aquatic environment. Smith et al. (1992) found
that CDDs/CDFs could be detected in sediments dating back to 1860 - 1865, although
concentrations were found to be low (e.g., CDDs = 7.0 ppt with 98 percent being OCDD;
CDFs = 2.1 ppt with 75 percent being OCDF). These low concentrations remained
essentially steady until about 1920 when concentrations significantly increased. Between
1920 and 1940, CDDs increased from about 1-10 ppt to about 250 ppt, and CDFs
increased from 5 to about 100 ppt. Between 1940 and 1960, CDDs increased to about
680 ppt, and CDFs increased to about 300 ppt. From 1960 to 1980, CDDs continued to
increase to approximately 950 ppt, whereas CDFs significantly declined to about 150 ppt.
From the work of Czuczwa et al. (1984), Czuczwa and Hites (1986), and Smith et al.
(1992), it appears that anthropogenic combustion sources, taken in their entirety, probably
represent the largest mass flux of CDDs/CDFs into the environment, and that natural
combustion activity (i.e., forest fires) probably is insignificant by comparison. For
example, if it is assumed that the 7 ppt CDDs in sediments dating back to the 1860s is
reflective more of natural sources, and if the CDDs that were found to be 950 ppt in 1980
are more reflective of human sources, then a simple comparison would indicate that
anthropogenic sources may exceed natural sources by a factor of 100:1.
3.5.6. Summary of Theories of CDD/CDF Emissions
The above section discussed the likelihood that anthropogenic sources explain the
bulk of CDD/CDFs currently in the environment. Still, the considerable research on the
complex chemistries of combustion that transpire to ultimately yield CDDs/CDFs remains
largely theoretical. The three primary theories being advanced are:
Theory 1: CDDs/CDFs present as contaminants in the combusted organic materials
or that are thermally treated by a combustion process explain the emissions of CDDs/CDFs
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out of the stack. It is proposed that some quantity of this initial contamination survives the
thermal stress imposed by the heat of the incineration or combustion process and is
subsequently emitted from the stack.
Theory 2: CDDs/CDFs are ultimately formed from the thermal breakdown and
molecular rearrangement of precursor compounds. Precursor compounds are chlorinated
aromatic hydrocarbons having a structural resemblance to the CDD/CDF molecule. Among
the precursors that have been identified are polychlorinated biphenyls (PCBs), chlorinated
phenols (CPs), and chlorinated benzenes (CBs). The formation of CDDs/CDFs is believed
to occur after the precursor has condensed and adsorbed onto binding sites on the surface
of fly ash particles. The active sites on the surface of fly ash particles somehow promote
the chemical reactions forming CDDs/CDFs as products of this reaction, which has been
observed to be catalyzed by the presence of inorganic chlorides sorbed to the particulate.
Heat in a range of 250-450°C has been identified as a necessary condition for these
reactions to occur, with either lower or higher temperatures inhibiting the process.
Therefore, the precursor theory focuses on the region of the combustor that is
downstream and away from the high temperature zone of the furnace or combustion
chamber. This is a location where the gases and smoke derived from combustion of the
organic materials have cooled down because of heat losses during conduction through flue
ducts; passing through heat exchanger and boiler tubes to recover the heat from
combustion for the co-generation of energy; after passing through some air pollution
control equipment, and while convected up the stack to be discharged to the atmosphere.
Theory 3: CDDs/CDFs are synthesized de novo in the same region of the
combustion process as described in Theory 2 (i.e., the so-called cool zone). De novo
refers to the formation of CDDs/CDFs from organic and inorganic substrates comprised of
singular or mixtures of molecules bearing little resemblance to the molecular structure of
CDDs and CDFs. In broad terms, these are nonprecursors and include such diverse
substances as petroleum products, chlorinated plastics (PVC), nonchlorinated plastics
(polystyrene), cellulose, lignin, coke, coal, particulate carbon, and hydrogen chloride gas.
Formation of CDDs/CDFs requires the presence of a chlorine donor, a molecule that
partakes a chlorine atom to the predioxin molecule, and the formation and chlorination of a
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chemical intermediate that is a precursor. The production of a chemical intermediate that
is a dioxin precursor does not neatly differentiate Theory 2 from Theory 3, and indeed
introduces some confusion into the explanation of the primary chemical events. The
primary distinction is that Theory 3 begins with the combustion of diverse substances that
are not defined as precursors, then the nonprecursor reacts on the carbonaceous
particulate to eventually yield a chlorinated aromatic hydrocarbon that is a precursor to
finally yield CDDs/CDFs. By this distinction. Theory 3 may be viewed as an augmentation
to Theory 2 as explained by the initial steps in the synthesis of CDDs/CDFs.
This review has shown that all of these theories are possible and, therefore, taken
as a whole, should not be seen as being mutually exclusive. One or more of these theories
may act in combination during the combustion of carbonaceous matter. Theory 2 and
Theory 3 require the presence of chlorine in the combustible material and in the gaseous
state in the combustion plasma.
3.6. COMBUSTION AND OTHER HIGH TEMPERATURE SOURCES
A summary of the major combustion sources that produce CDDs and CDFs is
presented in the following sections. The development of combustor emission estimates
has been coordinated with a similar effort ongoing in EPA's Office of Air Quality Planning
and Standards (OAQPS). The OAQPS effort is part of a larger EPA effort to inventory air
emissions of various toxic substances. To date, OAQPS has completed emission
inventories for about 20 chemicals and has completed a draft document entitled "Locating
and Estimating Air Emissions from Sources of Dioxins and Furans" (U.S. EPA, 1993a).
This draft OAQPS document summarizes dioxin emissions data for a variety of combustor
types. OAQPS is preparing a second report (draft not yet complete) entitled "Emissions
Inventory of Section 112 (c)(6) Pollutants: 2,3,7,8-TCDD, 2,3,7,8-TCDF and 2,3,7,8-
TCDD Toxic Equivalents." This report will combine the emission factor information in the
"Locating and Estimating" report with production values to develop actual emission rate
estimates. Since the OAQPS efforts will not be completed until after this draft report is
issued, it is possible that the second OAQPS report may reach somewhat different
conclusions. However, the Agency is striving to coordinate these efforts and make the
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outcomes as consistent as possible. Readers interested in further details about the
OAQPS efforts are encouraged to contact OAQPS directly at their location in Research
Triangle Park, NC.
3.6.1. Municipal Solid Waste Incineration
Characterization of the Industry
Municipal Solid Waste Incinerators (MSWI) operating in the United States can be
classified into four general design categories: mass burn, modular, refuse-derived fuel, and
fluidized-bed (U.S. EPA, 1992h). The first type is called mass burn because the waste is
combusted without any preprocessing other than removal of items too large to go through
the feed system. In a typical mass burn combustor, refuse is placed on a grate that moves
through the combustor. These facilities typically range in combustion capacity from 90 to
2,700 metric tons of MSW per day. Subcategories of mass burn technologies include
refractory-walled, rotary kiln, and water-wall facilities. Refractory- walled represent an
older class of MSWIs generally built in the late 1970's to early 1980's that were designed
to reduce the volume of waste in need of disposal by 70 to 90 percent. These facilities
generally lacked boilers to recover the heat of combustion for energy purposes. In the
refractory design, the MSW is delivered to the combustion chamber by a traveling grate.
Combustion air in excess of stoichiometric amounts is supplied both below and above the
grate. Mass burn water-wall facilities represent substantial design improvements over the
refractory-walled incinerators. The water-wall refers to a series of steel tubes running
vertically along the walls of the furnace. The tubes contain water, which when heated by
combustion, acts as a boiler and transfers energy to produce steam. The steam is then
used either to drive an electrical turbine generator or for other industrial needs. Because a
secondary purpose is to generate energy to sell to a customer, significant improvements
over refractory-walled MSWIs in terms of increased combustion efficiency have been
fostered. The third subcategory of mass burn MSWIs is the rotary kiln. The rotary kiln
lacks a traveling or reciprocating grate system to deliver MSW into the furnace. Rather it
employs a water-cooled rotary combustor that is essentially a rotating combustion barrel
mounted at a slight angle of decline into which the refuse is pushed by a hydraulic ram
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(Donnelly, 1992). Preheated combustion air is delivered to the kiln through various
portals. The slow rotation of the kiln (i.e., 10 to 20 rotations/hr) causes the MSW to
tumble thereby exposing more surface area for complete burn-out. These systems are also
equipped with boilers for energy recovery.
As with the mass burn type, modular incinerators also burn waste without
preprocessing. Modular MSWIs consist of two combustion chambers (e.g., a primary and
secondary chamber mounted in a vertical array). Modular combustors generally range in
combustion capacity from 4.5 to 270 metric tons/day. One of the most common types of
modular systems is the starved air (or controlled air system). In these systems, air is
supplied to the primary chamber at sub-stoichiometric levels. The incomplete combustion
products entrained in the combustion gases from the primary combustion chamber pass
into the secondary combustion chamber where excess air is added and combustion is
completed by elevated temperatures sustained by auxiliary fuel.
The third major type of MSWI technology is designed to combust refuse-derived
fuel (RDF). RDF is a general term describing MSW from which relatively noncombustible
items have been removed thereby enhancing the combustibility of the MSW. RDF is
commonly prepared by shredding, sorting, and separating metals to create a dense MSW
fuel in a pelletized form having a uniform size. RDF fuel is typically burned in a spreader
stoker-type combustion chamber (Donnelly, 1992). In the United States, RDF facilities
range in total combustion capacity from 227 to 2,720 metric tons/day. These MSWIs are
typically steam production facilities that generate salable energy.
The fourth type of MSWI is the fluidized-bed design. In this design, the waste
burns in a turbulent bed of noncombustible material, usually sand. The MSW may be fed
into the incinerator either as unprocessed waste or as a form of RDF. There are two basic
design concepts to the technology: (1) a bubbling-bed incineration unit and (2) a
circulating-bed incineration unit. Fluidized-bed MSWIs typically have capacities ranging
from 184 to 920 metric tons/day. These systems are usually equipped with boilers to
produce steam.
Currently, there are about 170 to 190 MSWI facilities located in 37 states in the
United States. (Berenyi and Gould, 1993; Burton and Kiser, 1993). This range in number
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of facilities reflects the fact that, for any given point in time, the exact population of
operating facilities is unknown. However, the best estimate is that 171 MSWI facilities
are in operation (Berenyi, 1993; Berenyi and Gould, 1993). About one-half of the
operating MSWIs were built since 1988 (Berenyi and Gould, 1993). The states with the
greatest number of facilities are: New York (16), Florida (14), Minnesota (14),
Massachusetts (8), Virginia (8), and Connecticut (7) (Berenyi and Gould, 1993). In the
most recent reporting year, 1991, EPA estimated that approximately 29.35 million metric
tons of MSW were combusted by all operating MSWIs; this represents approximately 17
percent of the annual generation of MSW in the United States (U.S. EPA, 1992c).
Gould (1991) estimated the average annual utilization capacity of typical MSWI
designs. Utilization capacity is defined as the percentage of days a facility operates during
the course of the year (U.S. EPA, 1992h). Gould (1991) estimated that existing mass
burn, modular, and RDF MSWIs had average annual utilization capacities of 87.5, 84.2,
and 83.3, respectively.
An estimated 85 percent of existing MSWIs are equipped with one or more air
pollution control devices (APCD) to remove some class of pollutants prior to release from
the stack (e.g., particulate matter, heavy metals, acid gases, and/or organic constituents)
(U.S. EPA, 1992h). These APCDs include electrostatic precipitators (ESPs), fabric filters
(FFs), dry sorbent injection (DSD, spray dryer adsorption (SDA), and wet scrubbers (WS).
The ESP is generally used to collect and control particulate matter derived from
combustion. This is accomplished by introducing a strong electrical field in the flue gas
stream, which, in turn, imparts a charge to the particles entrained in the combustion gases
(Donnelly, 1992). Large collection plates are given an opposite charge to attract and
collect the particles. Fabric filters are also particulate matter control devices. Six- to
eight-inch diameter bags made from woven fiberglass material are arranged in series. The
combustion gases are forced through the tightly woven fabric. The porosity of the fabric
is such that the bags act as a filter medium and retain small particles comprising the
particulate matter. Dry sorbent injection is designed for the control of MSWI acid gases.
DSI involves the injection of hydrated lime or soda ash into the gas stream to react with
and neutralize the acid gas constituents (Donnelly, 1992). Spray dryer adsorption involves
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both acid gas and paniculate matter control. In a typical SDA system, hot combustion
gases enter a reactor where atomized hydrated lime slurry is introduced at a controlled
velocity (Donnelly, 1992). The flue gas temperature is significantly decreased, and the
acid gas constituents quickly react with the reagent. The reaction evaporates the moisture
to produce a dried product that is removed from the bottom of the spray dryer. In general,
SDAs are used in combination with either ESPs or FFs. Greater than 95 percent reduction
and control of CDDs/CDFs in MSWI emissions has routinely been achieved with FF/SDA
systems (U.S. EPA, 1992h). Wet scrubber devices (WS) are designed for acid gas
removal, and are more common to MSWIs in Europe than in the United States. Wet
scrubber devices consist of two-stage scrubbers whereby the first stage removes HCI and
the second stage removes S02 (Donnelly, 1992). Water is used to remove the HCI, and
either caustic or hydrated lime is added to remove S02 from the combustion gases.
Table 3-27 summarizes the current estimated distribution of operating MSWIs by design
category and installed APCDs.
Estimation of MSWI Dioxin Emissions Using an Emission Factor Approach
The approach used here to estimate emissions is based on an emission factor.
Emission factors are estimates of the mass of CDD/CDF emitted from the stack per kg of
waste combusted. As shown in Table 3-28, these factors were estimated for each design
category, multiplied by the amount of waste burned within the design category and then
summed to get the total emissions.
The first step in this process is to collect emission test data representative of each
design category. EPA's Office of Air Quality Planning and Standards (OAQPS) has already
collected such a data set (U.S. EPA, 1993a). This summary presents emission testing for
dioxin-like compounds for 30 existing MSWI facilities. These tests have been reviewed by
OAQPS and determined to have used appropriate stack testing and laboratory protocols
and to have been conducted under normal operating conditions. These 30 facilities
represent a mix of MSWI designs and technologies as well as air pollution control devices
{APCDs) in actual use, providing a basis for extrapolating to all U.S. facilities. For design
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Table 3-27. Estimated Number of Operating MSWI Facilities in the United States
by Design Category and Type of Air Pollution Control Device
Type of APCD
Electrostatic Precipitator (ESP)
Dry Scrubber and ESP
Fabric Filter (FF)
Dry Scrubber and FF
Wet Scrubber
Wet Scrubber and FF
Wet Scrubber and ESP
None
Unknown
Total No. of MSWIs
Type of MSWI
Mass Burn
27
7
1
35
3
0
0
13
2
88
Type of MSWI
Modular
12
2
2
3
3
2
1
12
9
46
Type of MSWI
RDF
12
3
4
8
1
0
1
2
6
37
Totals
by APCD
51
12
7
46
7
2
2
27
17
171
Sources: Kiser and Bridges (1993); Berenyi (1993); Berenyi and Gould (1993).
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Table 3-28. Estimated MSW Incineration Emission Factors (EF) and Annual Emissions of Total CDD/CDFs
oo
i
o
M
MSWI Technology
Mass Burn Refractory
Mass Burn Refractory
Mass Burn Water-Wall
Mass Burn Water-Wall
Mass Burn Water Wall
Mass Burn Rotary
Mass Burn Rotary
RDF
RDF
RDF
Modular Starved Air
Modular Starved Air
Modular Excess Air
APCD
ESP
SD/FF
ESP
SD/ESP
SD/FF
ESP
SD/FF
ESP
SD/ESP
SD/FF
ESP
None
ESP
Avg. EF
(9/kg)
4.18e-05
3.12e-08
6.09e-07
4.68e-07
3.12e-08
6.09e-07
4.57e-08
8.86e-06
4.35e-08
1.20e-08
1.54e-06
7.86e-07
1.11e-06
#MSW»
Tested
1
1
4
2
7
0
2
2
2
3
2
1
2
Min, EF
(g/kg)
9.07e-06
2.68e-09
1.366-07
1.63e-07
2.68e-09
1.36e-07
1 .50e-08
3.14e-07
2.06e-08
2.38e-09
1 .08e-06
7.05e-07
2.856-07
Max. EF
(a/kg)
8.50e-O5
1.10e-07
2.11e-06
1.06e-06
1.10e-07
2.11e-06
7.45e-08
2.17e-05
7.25e-08
2.096-08
2.41e-06
8.95e-07
2.13e-06
Total
MSW Burned
(kg/yrl
3.10e + 09
1.456 + 08
5.26e + 09
2.13e + 09
8.47e + 09
5.046 + 08
1.10e + 09
4.88e + 09
1.486 + 09
9.116 + 08
5.156 + 08
5.02e + 08
3.59e + 08
2.94e+10
Emissions
(g/yr)
1.30e + 05
4.52e + 00
3.20e + 03
9.97e + 02
2.64e + 02
3.07e + 02
5.03e + 01
4.32e + 04
6.44e + 01
1.09e + 01
7.93e + 02
3.95e + 02
3.98e + 02
1.79e + 05
Percent
of
MSW
10.55
0.49
17.92
7.24
28.86
1.72
3.76
16.62
5.05
3.10
1.75
1.71
1.22
1 00.00
Percent
of
CDD/F
72.27
0.00
1.79
0.56
0.15
0.17
0.03
24.11
0.04
0.01
0.44
0.22
0.22
100.00
O
3J
D
O
Z
O
H
D
C
O
H
m
O
3)
O
H
m
Sources: U.S. EPA (1992h; 1993a)
O)
CO
-------
Table 3-28. Estimated MSW Emission Factors (EF) and Annual Emissions of Total CDD/CDFs
Description of Column Headings:
1) MSWI Technology: abbreviated technology descriptions including mass burn refractory, mass burn water-wall, mass burn rotary,
refuse derived fuel, modular starved air, and modular excess air.
2) APCD: air pollution control device, including electrostatic precipitator (ESP), spray dryer combined with fabric filter (SD/FF), spray
dryer combined with electrostatic precipitator (SD/ESP)
3) Avg. EF: average emission factor of g total CDD + CDF per kg municipal solid waste combusted.
4) # MSWI tested: number of municipal solid waste incinerators tested in this category.
5) Min. EF: minimum emission factor of g total CDD + CDF per kg municipal solid waste combusted. O
6) Max. EF: maximum emission factor of g total CDD + CDF per kg municipal solid waste combusted. >
7} MSW Burned: annual mass of municipal solid waste combusted per year based on utilization capacity. Zj
8) Emissions: estimated annual emissions to the air of total CDD + CDF, based on average emission factor. !
^ 9) % of MSW: percent of total municipal waste combusted by this technology and air pollution control device. O
o 10) % of CDD/F: percent of total emissions attributed to this technology and air pollution control device. ^
w O
H
Note: Emissions data was not available for the mass burn rotary kiln equipped with ESPs. The mass burn waterwafl ESP technology c:
was judged to be most similar to rotary kiln units in terms of operating performance. Therefore, the emission factor for O
MBWW-ESP was applied to this class of facilities. m
O
-33
O
H
m
O)
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categories where more than one test was available, the concentrations for each congener
were averaged across tests.
The emissions data (U.S. EPA, 1993a) are presented in concentration units of
nanogram of CDD/CDF per dry standard cubic meter of combustion gas (ng/dscm)
corrected to 7% oxygen. Emission factors were computed for each MSWI design
category by multiplying the average CDD/CDF concentration by the volume of combustion
gas that is produced per kg of waste incinerated. The gas production factor was derived
considering the typical heat content of the refuse as follows (Federal Register, 1987c):
1. Assume the heat content of typical MSW = 4500 B.t.u./lb of MSW.
2. Assume that 2.57E-7 dscm are produced per joule value of the MSW.
3. One joule = 9.47E-04 B.t.u.
4. One pound = 0.4536 kg
Then:
dscm/kg of MSW = (4500 B.t.u./lb) x (1 joule/9.47E-04 B.t.u)
x (lb/.4536 kg) x (2.57E-07 dscm/joule)
dscm/kg of MSW = 2.69
As indicated above an emission factor was estimated for each design class and
multiplied by the amount of waste burned to get the emission rate. The emission rate
estimates shown in Table 3-28 reflect all congeners of CDD and CDF. These values can
be converted to TEQs by applying a ratio of total CDD/CDF to TEQ. EPA has reviewed the
congener-specific emissions profiles of twelve MSWI technologies and has determined
that, although variable, the average ratio appears to be about 60:1 (i.e., the total mass of
CDD/CDF is roughly 60 times greater than the computed TEQ) (Radian, 1994). As a
measure of variability, the standard deviation from this analysis was +/- 20 from the mean
ratio (i.e., a ratio of 40:1 to 80:1). As noted in Table 3-28, the total CDD/CDF mass
emission from all operating 171 MSWIs is 1.8E + 05 grams. The TEQ mass emission is
estimated to be 3,000 grams TEQ/yr (assuming the average ratio of 60:1 for the TEQ
conversion from the total CDDs/CDFs).
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Discussion of Uncertainties
The procedure used to estimate national emissions of dioxin from the MSWI
industry involves uncertainties that could cause the estimate to be lower or higher than the
true value. The emission estimates were derived on the basis of emissions testing from 30
facilities. As discussed below much of the uncertainty revolves around the
representativeness of these facilities.
• How well do the 30 facilities represent the whole population of 171 facilities in terms
of technologies? The 30 facilities were selected to be representative of the range of
MSWI designs and air pollution control systems. As indicated in Table 3-28, only one of
the 13 design classes was not represented. Facilities of particular concern are those that
use ESPs which operate in a temperature range of 200°- 400°C. As discussed in Section
3.5 these conditions can promote the formation of CDDs/CDFs. Over the past few
years, some of the facilities with "hot-sided ESPs" have made changes in operating
conditions or equipment to address this problem. Although, the 30 tested facilities do
include some with "hot-sided ESPs" it is not clear if they are representative of current
conditions at all such facilities.
• How well do the 30 facilities represent the whole population of 171 facilities in terms of
timing? The emissions were largely derived from stack tests conducted during the period
1988 to 1991. Since 1991, new facilities may have become operational or changes may
have been made to existing ones. Therefore emissions today may be somewhat lower,
reflecting continued improvements in combustor design.
• For individual facilities, how representative are emission tests of long term
performance? The average emissions from a single facility are typically derived from 3-4
days of testing over the year. It is not known to what extent such short-term testing may
truly reflect long-term emissions, e.g., through the life of the facility. Most stack testing
data were collected while the MSWI was operating according to design specifications,
e.g., under normal operating conditions. Using these data would not reflect any additional
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emissions that may occur during upsets in the combustion zone, poor operations,
equipment malfunctions, or degradation in the effectiveness of the pollution control
systems.
• How accurate is the approach used to convert stack concentrations to emission
factors? As discussed earlier in this section, the approach used to convert concentration
in the combustion gas to an emission factor is based on an assumption that 2.69 dscm of
combustion gas are produced per kg of MSW burned. This quantity is variable among
facilities and is dependent on such factors as the temperature of combustion, the amount
of air supplied to combustion chamber in excess of stoichiometric requirements, the
moisture of the feed material being burned, and the heat value of the feed material being
combusted. For some technologies with relatively high amounts of excess air delivered to
the combustion chamber, the gas volume may be as high as 5.0 - 6.0 dscm/kg.
• How accurate is the procedure used to convert total CDD/CDF emissions to Toxic
Equivalents (TEQs)? The conversion ratio was based on a review of emissions from 12
MSWIs. In actuality, the ratio of total CDD/CDF to TEQ is variable from one facility to
another. It is influenced by the composition of the MSW and the operating conditions of
the combustor. It is not known how representative the generic ratio of 60:1 is of dioxin
emissions from all existing MSWIs.
Although MSWIs have the strongest emission data base of all combustion sources
evaluated in this document, it still must be considered uncertain for the reasons stated
above. Therefore, the estimated emission factors are given a "medium" confidence rating.
The amount of MSW that is annually combusted by various MSWI technologies (see
Table 3-28) is given a "high" confidence rating. These estimates are based on a recently
conducted and comprehensive survey (U.S. EPA, 1992h). Based on these confidence
ratings, the estimated range of potential annual emissions is assumed to vary by a factor
of 5 between the low and high ends of the range. Assuming that the best estimate of
annual emissions (3,000 g TEQ/yr) is the geometric mean of this range, then the range is
calculated to be 1,300 to 6,700 g TEQ/yr.
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EPA Regulatory Activities
EPA will soon propose revised emission standards for all existing and new MSWIs
with unit capacities greater than 30 metric tons per day. Once these standards have been
promulgated, and the States have fully enforced the emission limits, then EPA expects to
reduce the national emissions of dioxin emissions from all existing MSWIs by about 99 %.
All existing facilities combined should then be emitting about 30 g TEQ/yr. Full
implementation and enforcement of the rules should be achieved by the year 2000. As
the compliance date approaches and facilities are upgraded, EPA expects that emissions
from these facilities will decline significantly from current levels.
Estimated CDD/CDFs in MSWI Ash
An estimated 7 million metric tons of total ash (bottom ash plus fly ash) are
generated annually by MSWIs (telephone conversation between J. Loundsberry, U.S. EPA
Office of Solid Waste, and L. Brown, Versar Inc., on February 24, 1993). U.S. EPA
(1991b) indicates that 2.8 to 5.5 million tons of total ash are produced from MSWIs with
fly ash comprising 5 to 15 percent of the total. U.S. EPA (1990c) recently reported the
results of analyses of MSWI ash samples for CDDs and CDFs. Ashes from five state-of-
the-art facilities located in different regions of the United States were analyzed for all
2,3,7,8-substituted CDDs and CDFs. The TEQ levels in the ash (fly ash mixed with
bottom ash) ranged from 106 ng/kg to 466 ng/kg with a mean value of 258 ng/kg.
CDD/CDF levels in fly ash are generally much higher than in bottom ash. For example,
Fiedler and Hutzinger (1992) report levels of 13,000 ng TEQ/kg in fly ash. Multiplying the
mean TEQ total ash concentration by the estimated volume of MSWI ash generated
annually (7 million metric tons) yields an estimated annual TEQ in MSWI ash of 1,800 g
TEQ/yr.
The total ash generation estimate is given a "medium" confidence rating since it is
based on an expert opinion and is about twice as high as earlier published estimates. The
emission factor is given a "medium" confidence rating because it is based on direct
measurements at five facilities, although these five facilities may not be representative of
all technologies in the United States. Based on these confidence ratings, the estimated
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range of potential annual emissions is assumed to vary by a factor of 5 between the low
and high ends of the range. Assuming that the best estimate of annual emissions (1,800
g TEQ/yr) is the geometric mean of this range, then the range is calculated to be 810 to
4,000 g TEQ/yr.
Each of the five facilities sampled in U.S. EPA (1990c) had companion ash disposal
facilities equipped with leachate collection systems or some means of collecting leachate
samples. Leachate samples were collected and analyzed for each of these systems.
Detectable levels were only found in the leachate at one facility (TEQ = 3 ng/l); the only
detectable congeners were HpCDDs, OCDD, and HpCDF.
3.6.2. Hazardous Waste Incineration
EPA estimates that there are 190 Hazardous Waste Incinerators (HWIs) in the
United States. This total includes both operating facilities and facilities that are not
operating but have filed an application with EPA (Helble, 1993). The four principal
technologies employed for the combustion of hazardous waste in the United States are:
liquid injection, rotary kiln, fixed hearth and fluidized-bed incinerators (Dempsey and
Oppelt, 1993). Liquid injection incinerators are designed to burn pumpable liquid
hazardous waste. These incinerators are typically simple refractory-lined cylinders (either
horizontally or vertically aligned) equipped with one or more waste burners. The liquid
waste is injected into the combustion chamber through an atomizer, and the liquid droplets
are exposed to high temperatures in suspension. Rotary kiln incinerators are the more
common design. They have the added versatility of being able to combust hazardous
waste in any physical form (i.e., liquid, semi-solid, or solid). The rotary kiln is a horizontal
cylinder lined with refractory material. Rotation of the cylinder on a slight slope provides
for transport of the waste through the kiln, as well as enhanced mixing and exposure to
the heat of combustion. The combustion gases emanating from the kiln are usually passed
through a high temperature afterburner chamber to more completely destroy organic
pollutants arising from combustion. Fixed hearths, the third principal hazardous waste
incineration technology, are starved air or pyrolytic incinerators. These are two-stage
combustion units. Waste is ram-fed into the primary chamber and incinerated at about 50
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to 80 percent of stoichiometric air requirements. The resulting smoke and pyrolytic
combustion products are then passed though a secondary combustion chamber where
relatively high temperatures are maintained by the combustion of auxiliary fuel. Oxygen is
introduced into the secondary chamber to promote complete thermal oxidation of the
organic molecules entrained in the gases. The fourth hazardous waste incineration
technology is the fluidized-bed incinerator. This technology is similar in design to that
employed in MSW incineration. (See Section 3.6.1).
Dempsey and Oppelt (1993) summarized the results of EPA-sponsored stack testing
at six full-scale HWIs, three PCB incinerators, and one incinerator burning PCP waste.
CDD/CDFs were detected at all three PCB incinerators with TEQ emission rates ranging
from 0.3 to 1.63 ng TEQ/dscm (@ 7 percent oxygen). CDD/CDFs were detected at three
of the HWIs with TEQ emission rates ranging from 0.57 to 17.7 ng TEQ/dscm (@ 7
percent oxygen).
Helble (1993) reviewed recent data from trial burn reports on CDD/CDF emissions
from 15 HWIs. CDD/CDFs were detected in the stack emissions of 11 of the 15 facilities
at total CDD/CDF emission rates ranging from 0.1 to 1,600 ng/dscm (@ 7 percent oxygen)
with most facilities between 1 and 100 ng/dscm. Based on his evaluation of the
emissions data, Helble (1993) concluded that the CDD/CDFs observed in emissions from
HWIs are formed catalytically under low temperature conditions either through catalytic
chlorination or through catalytic condensation of dioxin-like precursors such as
chlorobenzenes and PCBs.
Emission factors are estimated based on the results of the emission tests reported
by Helble (1993). Homologue-specific emissions data, waste feed rates, and stack flow
rates (dscm @ 7 percent oxygen) were available for six of the HWIs evaluated by Helble
(1993). From these data, total CDD/CDF emission factors were calculated for each facility
(range: 10 to 6,830 ng/kg of waste feed; mean: 1,550 ng/kg of waste feed). For those
facilities with more than one test run reported, the total CDD/CDF emission rates for the
individual runs were averaged to obtain a facility average emission rate. These total
CDD/CDF emission factors were converted to TEQ emission factors using a conversion
factor of 1.75 ng TEQ/ng of total CDD/CDF that was developed by EER, Inc. for EPA's
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Office of Solid Waste (EER, 1993). The resulting mean TEQ emission factor is 27.2 ng
TEQ/kg waste feed (range = 0.18 to 119 ng TEQ/kg waste feed).
Dempsey and Oppelt (1993) estimate that between 216 and 249 million metric
tons of hazardous waste were generated in 1987 (the year for which the most
comprehensive data on waste management are available). Of this total amount, Dempsey
and Oppelt (1993) estimate that between 1.0 and 1.3 million metric tons of hazardous
waste were incinerated. Based on an estimated 1.3 million metric tons of hazardous
waste incinerated per year in the United States and the mean emission factor derived
above, it is estimated that 2,000 grams CDD/CDF per year and 35 grams TEQ/yr are
emitted from HWIs.
A "low" confidence rating is ascribed to the emission factors derived above
because stack test data were available for only 6 of the 190 HWIs in the United States
and the stack test data used represent only one hazardous waste technology (rotary kiln).
The "production" estimate has been assigned a "medium" confidence rating because it is
based on a thorough review of the various studies and surveys which have been
conducted in recent years to assess the quantity and types of hazardous waste generated
in the United States, as well as the quantities and types of wastes being managed by
various treatment, storage and disposal facilities. Based on these confidence ratings, the
estimated range of potential annual emissions is assumed to vary by a factor of 10
between the low and high ends of the range. Assuming that the best estimate of annual
TEQ emissions (35 g TEQ/yr) is the geometric mean of this range, then the range is
calculated to be 11 to 110 g TEQ/yr.
3.6.3. Medical Waste Incineration
Buonicore (1992b) has reviewed the primary incineration technologies used to burn
medical and pathological wastes in the United States. These medical waste incinerations
(MWI) fall within three broad technology categories: retort, controlled-air, and rotary kiln.
Retort incinerators are multiple chamber combustors characteristic of the "older" existing
technology. The medical waste is fed into a primary combustion chamber, and the gases
from combustion are passed into a secondary chamber. In the secondary chamber,
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secondary auxiliary fuel is burned to sustain higher temperatures and to more completely
burn the organic pollutants entrained in the combustion gas from primary combustion.
Combustion air, 100 to 300 percent in excess of stoichiometric requirements, is usually
added to the secondary chamber. Gases exiting the secondary chamber are directed to an
incinerator stack. The second principal technology is the controlled-air incinerator. This is
the most common technology used to incinerate hospital/medical waste and is often
referred to as modular incineration. Like retort incinerators, combustion occurs in two
stages. Medical waste is fed into a primary combustion chamber where air is delivered at
less than stoichiometric requirements. Under these conditions, the waste is pyrolyzed and
volatile compounds are released. A secondary chamber is located on top of the primary
unit. Auxiliary fuel is added to sustain high temperatures in a controlled-air environment.
These systems are usually automated with computer-directed controllers that are
integrated with a thermocouple. Thus, the quality of combustion is superior to the retort
technology. The third type of MWI is the rotary kiln. This is the same technology as
employed in both municipal and hazardous waste incineration. (See Sections 3.6.1 and
3.6.2).
EPA has estimated that about 4.3 million metric tons (4.76 million short tons) of
hospital/medical wastes are generated annually in the United States (U.S. EPA, 1991d).
Table 3-29 summarizes the types and number of facilities that generate medical waste,
and their corresponding annual generation rate of medical wastes. There are about 6,700
MWIs operating nationwide combusting approximately 3.72 million metric tons of medical
waste annually (U.S. EPA, 1991d). Table 3-30 summarizes the estimated population of
MWI currently operating in the United States.
CDDs and CDFs have been identified in the stack gas emissions of MWIs located at
hospitals in the United States (U.S. EPA, 1993a). Although operating on a smaller-scale,
the mechanism of CCD/CDF formation in hospital waste incineration is similar to that
described for MSWI in Section 3.6.1. To support future rulemaking, EPA has developed a
summary of annual emissions of dioxin from all existing hospital waste incinerators
operating in the United States (U.S. EPA, 1991e). This summary represents an analysis
and review of dioxin emissions measured at the stack from six MWIs (Radian, 1991 a;
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Table 3-29. Estimated Number and Type of Facilities and Quantities of Medical
Waste Generated Annually in the United States
Facility Type
Hospitals
Laboratories
Clinics
Physician offices
Dentist offices
Veterinarians
Care facilities
Blood banks
Funeral homes
Industry units
Fire and Rescue
Prisons
Police
Animal shelters
Totals
No. of Facilities
7,000
7,200
41,300
180,000
98,000
38,000
42,700
900
21,000
221,700
7,200
4,300
13,100
4KAO
,O\J\J
686,900
Infectious
Waste(tons/yr)
360,000
25,900
26,300
35,200
8,700
4,600
31,100
4,900
900
1,400
1,600
3,300
<100
504,000
Medical Waste
(tons/yrj
2,400,000
173,000
175,000
235,000
58,000
31,000
207,000
33,000
138,000
9,000
1 1 ,000
22,000
< 1 ,000
72 OOO
3,565,000
Source: U.S. EPA (1991d)
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Table 3-30. Medical Waste Incineration Facilities Operating in the United States
MWI Facilities
Hospitals
Laboratories
Veterinary hospitals
Nursing homes
Crematories/funeral homes
Animal shelters
Commercial facilities
Other/unidentified
Total
Estimated Number
of MWIs
3,150
500
550
500
1,200
500
150
150
6,700
Avg. MWI Capacity (kg/hr)
124
153
55
76
82
90
535
75
Source: U.S. EPA (1991d)
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1991b; 1991c; McCormack, 1990; Lew et al., 1988; Lew et al., 1989). From these
reports, EPA derived an average emission factor of total amount of dioxin released to the
air per kg of medical waste combusted in a typical MWI (g total CDD/CDF per kg waste),
based largely on uncontrolled emissions (U.S. EPA, 1993a). The average uncontrolled
emission factor of total CDD/CDF is 8.53E-05 g/kg (U.S. EPA, 1993a). This factor can be
compared with the average controlled emission factor of total CDD/CDF of 4.46E-06 g/kg
from one facility equipped with acid gas controls and a fabric filter (U.S. EPA, 1993a).
The ratio of controlled to uncontrolled emissions is a factor of 1:20. Table 3-31
summarizes the emission factors developed for this analysis.
In computing an estimate of national emissions of dioxin from 6,700 existing MWIs,
EPA applied an average emission factor developed for uncontrolled MWIs. Uncontrolled
emissions are defined as emissions from a MWI facility not equipped with add-on air
pollution control devices (APCD) (e.g., electrostatic precipitator, scrubber, fabric filter,
etc.). However, MWIs are modular designs consisting of both a primary and secondary
combustion chamber. The purpose of the secondary combustion chamber is the continued
destruction of organic compounds emanating from the primary chamber. Therefore MWIs
are not actually totally uncontrolled. EPA expects that the majority of the existing MWIs
are uncontrolled with respect to dioxin control measures (U.S. EPA, 1991e). EPA believes
that the selection of an average emission factor derived from uncontrolled emissions
currently represents the most accurate means of estimating the magnitude of potential
dioxin release from all 6,700 operating MWIs (U.S. EPA, 1991e).
In order to estimate national emission of total dioxin to the air from all operating
facilities, EPA categorized the population of MWIs according to the operating duty, the size
of the combustor, and the amount of medical or pathological waste combusted per year.
Table 3-32 summarizes the estimate of total dioxin emitted (g/yr) from all operating MWIs
in the United States according to this disaggregation. Emissions to air of total CDD/CDF
(i.e., tetra-chlorinated through octa-chlorinated compounds) from approximately 6,700
existing medical waste incinerators are estimated to be 3.18E + 05 grams/yr. This
emission estimate was derived from tests conducted at six facilities (considered to be
representative of the major design types), extrapolating average emissions nationwide
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Table 3-31. CDD/CDF Emission Factors for Uncontrolled Medical Waste Incinerators
Operating in the United States
Congener or
Congener Group
2,3,7,8-TCDD
Other TCDD
PeCDD
HxCDD
HpCDD
OCDD
2,3,7,8-TCDF
Other TCDF
PeCDF
HxCDF
HpCDF
OCDF
Total CDD/CDF
Average
Emission Factor
(g/kg)
5.64 E-8
8.86 E-7
2.03 E-6
4.23 E-6
6.35 E-6
4.29 E-6
2.60 E-7
6.63 E-6
1.37E-5
1.86 E-5
1.68 E-5
1.19 E-5
8.53 E-5
Minimum
Emission
Factor
(9/kg)
6.37 E-10
1.91 E-9
3.21 E-8
1.29 E-7
1.19 E-7
6.63 E-8
5.26 E-9
6. 62 E-8
2.53 E-7
2.17 E-7
1 .49 E-7
6.56 E-8
1.52 E-6
Maximum
Emission
Factor
(g/kg)
4.47 E-7
8.38 E-6
1.34 E-5
2. 13 E-5
2.67 E-5
2.61 E-5
1.65 E-6
4.79 E-5
1.22 E-4
1 .06 E-4
1 .30 E-4
5.45 E-5
3.93 E-4
Source: U.S. EPA (1993a).
Note: Emission factors (grams dioxin/kg waste) were derived as the average and range from
six tested facilities.
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Table 3-32. Estimated Annual Emission of Total CDD/CDFs (g/yr) from Incineration
of Medical Waste
Type of Waste
Pathological
Mixed Medical
Type of MWI
Batch Fed
Intermittent
Batch-small
Intermittent - small
Intermittent -medium
Intermittent - large
Semicontinuous - large
Continuous - large
Totals
Number
of MWIs
1,200
1,598
335
2,287
766
178
182
154
6,700
Waste
Burned
(kg/yr)
1.225 E + 8
4.297 E + 8
2.674 E + 8
6.150 E + 8
7.480 E + 8
4.345 E + 8
2.942 E + 8
8.131 E + 8
3.724 E + 9
CDD/CDF
Emission
Factor
(g/kg)
8.53 E-5
8.53 E-5
8.53 E-5
8.53 E-5
8.53 E-5
8.53 E-5
8.53 E-5
8.53 E-5
CDD/CDF
Emission
(g/yr)
1.04 E + 4
3.67 E + 4
2.28 E + 4
5.25 E + 4
6.38 E + 4
3.71 E + 4
2.51 E + 4
6.94 E + 4
3.18 E + 5
Sources: U.S. EPA (1991 d; 1991e; 1991f; 1993)
Description of terminology:
Pathological Batch Fed: Controlled-air MWI; operates 3,520 hrs/yr with capacity of 226.8 kg/hr;
operational at hospitals, animal shelters, nursing homes, laboratories, and veterinary hospitals.
Pathological Intermittent: Controlled-air MWI; operates 2,964 hrs/yr with capacity of 90.7 kg/hr;
operational at funeral homes/crematories.
Mixed Medical Waste:
• Intermittent: Controlled-air MWI; small: operates 2,964 hr/yr with capacity of 90.7 kg/hr;
medium: operates 3,588 hr/yr with capacity of 272.16 kg/hr; large: operates 3,588 hr/yr with
capacity of 680 kg/h; operational at hospitals, animal shelters, nursing homes, laboratories, and
veterinary hospitals.
• Batch fed: Controlled-air MWI; small: operates 3,520 hr/yr with capacity of 226.8 kg/hr;
operational at hospitals.
• Semicontinuous: Controlled-air MWI;large: operates 3,564 hr/yr with capacity of 453/6 kg/hr;
operates at hospitals and laboratories.
• Continuous: Controlled-air MWI; large: operates 7,760 hr/yr with capacity of 680.4 kg/hr;
operated by commercial medical waste incinerators.
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using the amount of waste burned in each of the design classes.
For purposes of deriving an estimate of emissions in terms of TEQ, it is necessary
to convert the total CDD/CDF emission into an estimated TEQ emission. This is done by
assuming a ratio of TEQ to total CDD/CDF using existing data on emissions from existing
facilities. The State of California Air Resources Board (GARB) has stack tested a number
of hospital waste incinerators in southern California (CARB, 1990a). Congener-specific
emissions of CDD/CDFs were measured in the stack gas emissions of seven facilities.
From these data, the ratio of TEQ to total CDD/CDF is 0.016 as an overall average of five
tested facilities. Multiplication of the annual emissions of CDD/CDF (in grams per year) by
this ratio yields an estimate of 5,100 g TEQ emitted (grams per year) for all existing MWIs
in the United States.
U.S. EPA (1993a) reports emissions testing at a number of controlled-air medical
waste incinerators with a variety of emission controls. These tests yielded a lower range
of emission factors. Based on these data, it appears possible that the national releases
from medical waste incinerators could be much lower than the "average" value identified
above. It is difficult to say how much lower, since it is unknown how representative these
tested facilities are of all 6,700 facilities in the United States.
A "medium" confidence rating is assigned to the estimate of amount of hospital
waste burned since it is based on a detailed study specific to the United States; however,
the large number of these facilities makes it difficult to estimate precisely. The emission
factor used to extrapolate to a national basis is given a "low" confidence rating, because
the average was derived from the stack sampling at a small sample of the large numbers
of MWI facilities (6 of 6,700). Based on these confidence ratings, the estimated range of
potential annual emissions is assumed to vary by a factor of 10 between the low and high
ends of the range. Assuming that the best estimate of annual emissions (5,100 g TEQ/yr)
is the geometric mean of this range, then the range is calculated to be 1,600 to 16,000 g
TEQ/yr.
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3.6.4. Kraft Black Liquor Recovery Boilers
In 1987, the U.S. EPA stack tested three kraft black liquor recovery boilers for the
emission of dioxin in conjunction with the National Dioxin Study (U.S. EPA, 1987). These
boilers are associated with the production of pulp in the making of paper using the Kraft
process. In this process, wood chips are cooked in large vertical vessels called digesters
at elevated temperatures and pressures in an aqueous solution of sodium hydroxide and
sodium sulfide (Someshwar and Pinkerton, 1992). Wood is broken down into two phases:
a soluble phase containing primarily lignin, and an insoluble phases containing the pulp.
The spent liquor (called black liquor) from the digester contains sodium sulfate and sodium
sulfide that the industry finds beneficial in recovering for reuse in the Kraft process. In the
recovery of black liquor chemicals, weak black liquor is first concentrated in multiple-effect
evaporators to about 65 percent solids. The concentrated black liquor also contains 0.5 to
4 percent chlorides by weight (U.S. EPA, 1987). Recovery of beneficial chemicals is
accomplished through combustion in a Kraft black liquor recovery furnace. The
concentrated black liquor is sprayed into a furnace equipped with a heat recovery boiler.
The bulk of the inorganic molten smelt that forms in the bottom of the furnace contains
sodium carbonate and sodium sulfide in a ratio of about 3:1 (Someshwar and Pinkerton,
1992). The combustion gas is usually passed through an electrostatic precipitator that
collects particulate matter prior to being vented out the stack. The particulate matter can
be processed to further recover and recycle sodium sulfate.
The three sites that were stack tested by EPA (U.S. EPA, 1987) were judged to be
typical of Kraft black liquor recovery boilers. The following emission factors of dioxin were
derived from the stack emissions data: average CDD/CDF = 9.34E-03 //g/kg (range:
4.88E-03 to 1.67 E-02//g/kg), and average TEQ = 9.71E-05 //g/kg (range: 3.33E-05 to
2.06E-04//g/kg). A "medium" confidence rating is ascribed to these emission factors
because the emission factors were derived from the stack testing of three Kraft black
liquor recovery boilers that were judged to be fairly representative of technologies used at
Kraft pulp mills in the U.S.
In 1989, EPA estimated that approximately 28.2 million metric tons of black liquor
solids were burned in Kraft black liquor recovery boilers in the U.S. (U.S. EPA, 1992g).
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This production estimate was given a confidence rating of "high" because it is based on a
recent industry-wide survey conducted by EPA. Assuming this is the quantity of black
liquor that is combusted each year, then it is estimated that 264 grams of CDD/CDF and
2.7 grams of TEQ are emitted to the U.S. atmosphere annually. Based on the confidence
ratings, the estimated range of potential annual emissions is assumed to vary by a factor
of 5 between the low and high ends of the range. Assuming that the best estimate of
annual TEQ emissions (2.7 g TEQ/yr) is the geometric mean of this range, then the range
is calculated to be 0.9 to 4.3 g TEQ/yr.
As discussed in Section 3.2, approximately 500 million dry kg of pulp and paper
mill wastewater sludge were incinerated in 1990 by facilities employing chlorine bleaching
of pulp (U.S. EPA, 1993e). However, insufficient data are currently available to estimate
emission factors for dioxin-like compounds from pulp and paper mill incinerators. As
discussed in Section 3.2, EPA proposed control technology standards that address
CDD/CDF emissions for non-combustion pulp and paper mill sources in December 1993
(Federal Register, 1993a) and will propose control technology standards for combustion
sources by October 1994 (U.S. EPA, 1992d).
3.6.5. Sewage Sludge Incineration
Brunner (1992) reviewed the four principal combustion technologies used to
incinerate sewage sludge in the U.S.: multiple-hearth incinerator, fluidized-bed incinerator,
electric furnace, and cyclone furnace. All of these technologies are "excess-air" processes
(i.e., they combust sewage sludge with oxygen in excess of theoretical requirements). Of
the four types of technologies, multiple-hearth incinerators are the most common. They
constitute approximately 60 percent of the 199 existing sewage sludge incineration
facilities operational in the U.S. (Federal Register, 1993b). The furnace consists of
refractory hearths arranged vertically in series, one on top of the other. Dried sludge cake
is fed to the top hearth of the furnace. The sludge is mechanically moved from one hearth
to another through the length of the furnace. Moisture is evaporated from the sludge cake
in the upper hearths of the furnace. The center hearths are the burning zone to the furnace
where gas temperatures reach 871 °C. The bottom hearths are the burn-out zone where
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the sludge solids become ash. A waste-heat boiler is usually included in the burning zone
where steam is produced to provide supplemental energy at the sewage treatment plant.
Air pollution control measures typically include a wet scrubber system for paniculate
matter control (U.S. EPA, 1987).
The fluidized-bed incinerator is a cylindrical refractory-lined shell with a steel plate
structure that supports a sand bed near the bottom of the furnace (Brunner, 1992). Air is
introduced through openings in the bed plate supporting the sand. This causes the sand
bed to undulate in a turbulent air flow, hence the sand appears to have a fluid motion
when observed through furnace portals. Sludge cake is added to the furnace at a position
just above this fluid motion of the sand bed. The fluid motion promotes mixing in the
combustion zone. Sludge ash exists the furnace with the combustion gases, therefore air
pollution control systems typically consist of high-energy venturi scrubbers.
Electric furnaces are sometimes called infrared furnaces (Brunner, 1992). This
incineration system consists of a long rectangular refractory-lined chamber. A belt
conveyer system moves the sludge cake through the length of the furnace. To promote
combustion of the sludge, supplemental heat is added by electric infrared heating elements
within the furnace that are located just above the travelling belt. Electric power is required
to initiate and sustain combustion.
Cyclonic furnaces consist of a refractory-lined cylindrical shell with a domed top
(Brunner, 1992). Air is blown in at tangential burner ports on the furnace shell which
causes a violent swirling pattern. This motion promotes good mixing of combustion air
with the sludge feed. Sludge is fed into the furnace chamber by screw conveyor.
Combustion gases exit at the top of the swirling vortex at the top of the furnace dome.
EPA has confirmed that dioxin can be emitted from sewage sludge incineration
based on the testing of three multiple-hearth sewage sludge incinerators (U.S. EPA, 1987).
Emission factors for dioxin were developed from these data. The average emission factor
of CDD/CDF was estimated to be 1.26E + 00 //g/kg of dry sewage sludge (range: 8.80E-
02 to 3.37E + 00 //g/kg). The average emission factor for TEQ was estimated to be 2.69E-
02 A/g/kg of dry sewage sludge (range: 1.17E-03 to 3.04E-02 /vg/kg) assuming perfect
congener distribution within the total CDD/CDFs measured.
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In 1992, approximately 199 sewage sludge incineration facilities combusted about
0.865 million metric tons of dry sewage sludge (Federal Register, 1993b). Given this
mass of sewage sludge incinerated/yr, the best estimates of emissions to air are 1,090
grams of CDD/CDF per year and 23 grams TEQ per year from all sewage sludge
incineration facilities.
A "medium" confidence rating is ascribed to the emission factors because they
were developed from the stack testing of three multiple hearth incinerators. Although
multiple hearth incinerators are the dominant technology in use in the U.S. today, some
uncertainty exists as to the representativeness of these derived emission estimates to
possible emissions from other sewage sludge incineration technologies. The production
estimate is assigned a "high" confidence rating because it is based on an extensive EPA
survey to support rulemaking activities. Based on these confidence ratings, the estimated
range of potential annual emissions is assumed to vary by a factor of 5 between the low
and high ends of the range. Assuming that the best estimate of annual emissions (23 g
TEQ/yr) is the geometric mean of this range, then the range is calculated to be 10 to 52 g
TEQ/yr.
3.6.6. Primary Nonferrous Metal Smelting/Refining
Nonferrous metals include aluminum, copper, nickel and magnesium. Insufficient
information is available for evaluating CDD/CDF emissions, if any, from primary
smelting/refining of nonferrous metals in the United States. However, several European
investigators have investigated the presence of CDD/CDFs at some facilities in this
industry.
Oehme et al. (1989) reported that the production of magnesium leads to the
formation of CDDs and CDFs. Oehme et al. (1989) estimated that 500 g of TEQ are
released in wastewater to the environment and 6 g TEQ are released to air annually from a
magnesium production facility studied in Norway; CDFs predominated with a CDF to CDD
concentration ratio of 10 to one. The magnesium production process involves a step in
which MgCI2 is produced by heating MgO/coke pellets in a pure chlorine atmosphere to
about 700 to 800°C. The MgCI2 is then electrolyzed to metallic magnesium and CI2. The
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CI2 excess from the MgCI2 process and the CI2 formed during electrolysis is collected by
water scrubbers and discharged to the environment.
Oehme et al. (1989) also report that certain primary nickel refining processes
generate CDDs and CDFs, primarily CDFs. Although the current low temperature process
used at the Norwegian facility studied is estimated to release only 1 g TEQ per year, a high
temperature NiCI2/NiO conversion process that had been used for 17 years at the facility is
believed to have resulted in much more significant releases based on the ppb levels of
CDFs detected in aquatic sediments downstream of the facility (Oehme et al., 1989).
Lexen et al. (1993) reported that samples of filter powder and sludge from a lagoon
at the only primary aluminum production plant in Sweden showed no or little CDD/CDF.
3.6.7. Secondary Nonferrous Metal Smelting/Refining
Secondary smelters/refiners are establishments primarily engaged in the recovery of
nonferrous metals and alloys from new and used scrap and dross. The principal metals of
this industry both in terms of volume and value of product shipments are aluminum,
copper, lead, zinc, and precious metals (U.S. DOC, 1990a). Scrap metal and metal wastes
may contain organic impurities such as plastics, paints, and solvents. Secondary
smelting/refining processes for some metals (e.g., aluminum, copper, and magnesium)
utilize chemicals such as NaCI, KCI, and other salts. The combustion of these impurities
and chlorine salts in the presence of various types of metal during reclamation processes
can result in the formation of CDDs and CDFs as evidenced by the detection of CDDs and
CDFs in the stack emissions of secondary aluminum, copper, and lead smelters (Aittola et
al., 1992; U.S. EPA, 1987; 1994b; 1994c; 1994d).
3.6.7.1 Secondary Aluminum Smelters and Refiners
Levels of 2,3,7,8-TCDF in stack gas from an aluminum reclamation facility in the
Finnish city of Vyborg have been measured at approximately 43 ng/m3 (Aittola et al.,
1992). However, no studies of CDD/CDF emissions from secondary aluminum smelters
located in the United States have been reported. Aluminum is processed at more smelters
than any other nonferrous metal in the United States. Also more aluminum undergoes
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secondary smelting than any other nonferrous metal. An estimated 1.7 million metric tons
of aluminum were produced by secondary smelters in 1987 in the United States (U.S.
DOC, 1990a).
3.6.7.2 Secondary Copper Smelters and Refiners
Stack emissions of CDD/CDFs from a secondary copper smelter were measured by
EPA during the National Dioxin Study (U.S. EPA, 1987). The tested facility recovers
copper and precious metals from copper and iron-bearing scrap. The copper and iron-
bearing scrap are fed in batches to a cupola blast furnace, which produces a mixture of
slag and black copper. Four to five tons of metal-bearing scrap were fed to the furnace
per charge, with materials typically being charged 10 to 12 times per hour. Coke was
used to fuel the furnace, and represented approximately 14 percent by weight of the total
feed. During the stack tests, the feed consisted of electronic telephone scrap and other
plastic scrap, brass and copper shot, iron-bearing copper scrap, precious metals, copper
bearing residues, refinery by-products, converter furnace slag, anode furnace slag, and
metallic floor cleaning material. Oxygen enriched combustion air for combustion of the
coke was blown through tuyeres at the bottom of the furnace. At the top of the blast
furnace were four natural gas-fired afterburners to aid in completing combustion of the
exhaust gases. Particulate emissions were controlled by fabric filters, and the flue gas
then was discharged into a common stack. The estimated emission factors derived for
this one site are: CDD/CDF = 3.89E + 04 ng/kg of scrap metal smelted (range: 3.31E + 04
to 4.05E + 04 ng/kg); TEQ = 7.79E + 02 ng/kg of scrap metal smelted (range: 7.64E + 02
to 1.04E + 03 ng/kg).
More than 0.3 million metric tons of copper were produced by the 24 secondary
copper smelters operating in the United States in 1987 (U.S. DOC, 1990a). If the
emission rates derived above are assumed to be representative of all secondary copper
smelters, then the best estimate of annual air emission of CDD/CDF released by secondary
copper smelting operations in the United States is 1.17E + 04 grams per year and the best
estimate of TEQ emission is 2.34E + 02 grams per year. A "high" confidence rating is
given to the production estimate because it is based on reliable data from the U.S. 1987
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Census of Manufactures. A "low" confidence rating is given to the emission estimates
since they are based on direct measurements at only one U.S. copper smelter. Based on
these confidence ratings, the estimated range of potential annual emissions is assumed to
vary by a factor of 10 between the low and high ends of the range. Assuming that the
best estimate of annual emissions (234 g TEQ/yr) is the geometric mean of this range,
then the range is calculated to be 74 to 740 g TEQ/yr.
3.6.7.3 Secondary Lead Smelters and Refiners
The secondary lead smelting industry produces elemental lead through the chemical
reduction of lead compounds (obtained primarily from scrap motor vehicle lead-acid
batteries) in a high temperature furnace (1,200 to 1,260 degrees C). Smelting is
performed in reverberatory, blast, rotary, or electric furnaces. Blast and reverberatory
furnaces are the most common types of smelting furnaces used by the 23 facilities that
comprise the current secondary lead smelting industry in the United States. Of the 45
operating furnaces at these 23 facilities, 15 are reverberatory furnaces, 24 are blast
furnaces, 5 are rotary furnaces, and 1 is an electric furnace. The one electric furnace and
11 of the 24 blast furnaces are co-located with reverberatory furnaces and most share a
common exhaust and emissions control system (U.S. EPA, 1994a). Furnace charge
materials consist of lead-bearing raw materials, lead-bearing slag and drosses, fluxing
agents (blast and rotary furnaces only), and coke. Fluxing agents consist of iron, silica
sand, and limestone or soda ash. Coke is used as fuel in blast furnaces and as a reducing
agent in reverberatory and rotary furnaces. The PVC plastic seperators in the batteries are
the primary source for HCI emissions from the smelters. However, the fluxing agents used
at blast and rotary furnaces also react with chlorine to form calcium chloride or sodium
chloride therby reducing HCI emissions from these furnaces relative to reverberatory
furnaces. Organic emissions from co-located blast and reverbertory furnaces are more
similar to the emissions of a reverberatory furnace than the emissions of a blast furnace
(U.S. EPA, 1994a).
The total annual production capacity of the U.S. lead smelting industry is 1.36
million metric tons. Blast furnaces not co-located with reverberatory furnaces account for
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21 percent of capacity (or 0.28 million metric tons). Reverberatory furnaces and blast and
electric furnaces co-located with reverberatory furnaces account for 74 percent of capacity
(or 1.01 million metric tons). Rotary furnaces account for the remaining 5 percent of
capacity (or 0.07 million metric tons). Actual production volume statistics by furnace type
are not available. However, if it is assumed that the total actual production volume of the
industry (0.86 million metric tons in 1990) is reflective of the production capacity
breakdown by furnace type, then the estimated actual production volumes of blast
furnaces (not co-located), reverberatory and co-located blast/electric and reverberatory
furnaces, and rotary furnaces are 180, 637, and 43 thousand metric tons, respectively
(U.S. EPA, 1994a).
CDD/CDF and TEQ emission factors can be estimated for lead smelters based on
the results of emission tests recently performed by EPA at three smelters (a blast furnace,
a co-located blast/reverberatory furnace, and a rotary kiln furnace) (U.S. EPA, 1992i;
1993g; 1993h). The air pollution control systems at the three tested facilities consisted of
both baghouses and scrubbers. Congener-specific measurements were made at the exit
points of both APCD exit points at each facility. Although all 23 active smelters employ
baghouses, only 9 employ scrubber technology. Facilities that employ scrubbers account
for 14 percent of the blast furnace (not co-located) production capacity, 52 percent of the
reverberatory and co-located furnace production capacity, and 57 percent of the rotary
furnace production capacity. From the reported data, TEQ emission factors (ng TEQ/kg
lead recovered) for each of the three furnace configurations are presented below as a
range reflecting the presence or absence of a scrubber.
• Blast furnace: 0.63 to 8.31 ng TEQ/kg lead
• Reverberatory/co-Iocated furnace: 0.10 to 0.77 ng TEQ/kg lead
• Rotary furnace: 0.28 to 0.21 ng TEQ/kg lead
If it is assumed that these emission rate ranges are representative of the range of
emission rates at the non-tested facilities with the same basic furnace configuration and
presence or absence of scrubbers, then combining these emission rate ranges with the
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estimates derived above for annual secondary lead production volumes yields a total
industry-wide estimated emission to air of 1.6 g of TEQ. The estimated contributions to
this total for each furnace configuration are:
• Blast furnaces with scrubbers: 0.02 g TEQ/yr
• Blast furnaces without scrubbers: 1.29 g TEQ/yr
• Reverberatory/co-located furnaces with scrubbers: 0.03 g TEQ/yr
• Reverberatory/co-located furnaces without scrubbers: 0.24 g TEQ/yr
• Rotary furnaces with scrubbers: 0.01 g TEQ/yr
• Rotary furnaces without scrubbers: 0.01 g TEQ/yr
A "medium" confidence rating is ascribed to the emission factors derived above
because stack test data were available for 3 of the 23 active smelters in the United States
and the stack test data used represent the three major furnace configurations. The
"production" estimate has been assigned a "medium" confidence rating because, although
it is based on a U.S. Department of Commerce estimate of total U.S. production, no
production data were available on a furnace type or furnace configuration basis.
Based on these confidence ratings, the estimated range of potential annual
emissions is assumed to vary by a factor of 5 between the low and high ends of the
range. Assuming that the best estimate of annual emissions (1.6 g TEQ/yr) is the
geometric mean of this range, then the range is calculated to be 0.7 to 3.5 g TEQ/yr.
3.6.8. Primary Ferrous Metal Smelting/Refining
Several European investigators have reported that iron ore sinter plants are sources
of CDD/CDFs (Rappe et al., 1992b; Lexen et al., 1993; Lahl, 1993). However, insufficient
information is available for evaluating CDD/CDF emissions from primary smelting/refining
of ferrous metal in the United States.
Iron is manufactured from its ores (i.e., magnetic pyrites, magnetite, hematite, and
carbonates of iron) in a blast furnace, and the iron obtained from this process is further
refined in steel plants to make steel. During iron manufacturing, iron ores undergo
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sintering to enable better processing in the blast furnace. In the sintering process, iron ore
fines are mixed with coke fines and the mixture is placed on a grate which is then heated
to a temperature of 1093-1371°C. The heat generated during combustion sinters the
small particles. Also, iron-bearing dusts and slags from other processes in the steel plant
are recycled as a feed mix for the sinter plant (Knepper, 1981; Capes, 1983). Lahl (1993)
reported that the this management practice introduces traces of chlorine and organic
compounds which are responsible for the generation of the CDD/CDFs found in these
plants.
Sinter plants in Sweden and the Netherlands were reported to emit up to 3 ng
TEQ/m3 stack gas or 2 to 4 g TEQ/yr per plant to the air (Rappe et al., 1992b; Lexen et
al., 1993). Lahl (1993) report that emission data from plants in Germany indicate TEQ
concentrations in stack gas after passage through mechanical filters and electrostatic
precipitators ranging from 3 to 10 ng TEQ/nm3. Lahl (1993) estimated that, if all European
sinter plants have stack concentrations of the same order of magnitude, then the total
emission from sintering plants would be greater than 1 kg TEQ. This total is greater than
the sum of all other identified European thermal sources of CDD/CDFs.
3.6.9. Secondary Ferrous Metal Smelting/Refining
Tysklind et al. (1989) found scrap ferrous metal processing to be a source of CDDs
and CDFs at a steel mill in Sweden. Analyses showed the presence of CDDs and CDFs in
the range of 0.1 to 1.5 ng TEQ/Nm3 dry gas in a plant with a 10-ton electric furnace. The
higher values reportedly were obtained during the melting of metal with chlorinated
materials (e.g., PVC plastics). Raw gases collected over an open-furnace during batch jobs
contained 110 ng TEQ/Nm3 dry gas when cutting oils containing chlorine were added to
the scrap metal. The congener profiles of all flue gas samples showed that CDFs were
predominant. The congener profiles also showed higher chlorine content when PVC was
used.
Insufficient data exist to estimate emission factors for the U.S.
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3.6.10. Scrap Electric Wire Recovery
The objective of wire recovery is to remove the insulating material and reclaim the
metal (e.g., copper, silver, and gold) comprising the electric wire. The reclaimed metal is
then sold to a secondary metal smelter. Wire insulation commonly consists of a variety of
plastics, asphalt-impregnated fabrics or burlap. In ground cables, chlorinated organics are
used to preserve the cable casing.
In the past, scrap electric wire was thermally treated in the United States to burn
off the insulating material. However, according to industry and trade association
representatives, current recovery operations typically no longer involve thermal treatment
but instead involve mechanical chopping into fine particles from which the insulating
material is removed by air blowing and gravitational settling of the heavier metal fraction
(telephone conversation between R. Garino, Institute of Scrap Recycling Industries, and T.
Leighton, Versar, Inc. on March 2, 1993; telephone conversation between J. Sullivan,
Triple F. Dynamics, and T. Leighton, Versar, Inc., on March 8, 1993). No independent
confirmation of this technology switch could be obtained from EPA program office
representatives.
The combustion of chlorinated organic compounds catalyzed by the presence of
wire metals such as copper and iron can lead to the formation of CDDs and CDFs (Van
Wijnen et al., 1992). CDDs and CDFs have been detected in fly ash and bottom residues
from the open-air incineration of wire scraps, and in stack samples of a wire reclamation
incinerator (Chen et al., 1986; Southerland et al., 1987). Huang et al. (1992b) detected
CDDs and CDFs in soils collected near electronic wire scrap incinerators used for the
recovery of metals. In these studies, the chlorinated compounds were considered to have
been generated thermochemically from plastics covering the wires. Small-scale (and
unpermitted) activities involving the incineration of scrap electrical wires have resulted in
increased levels of CDDs and CDFs in soil samples collected from former scrap wire and
car incineration sites within the vicinity of Amsterdam (Van Wijnen et al., 1992). Analysis
of these soil samples showed CDD and CDF levels ranging between 60 and 98,000 ng/kg
dry weight, with nine of fifteen soil samples having levels above 1,000 ng/kg dry weight.
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Dioxin-like compounds emitted to the air from scrap electric wire incineration were
measured from a facility during EPA's National Dioxin Study of combustion sources
(U.S. EPA, 1987). The tested facility was determined to be typical of this industrial
source category at that time. Insulated wire and other metal-bearing scrap material were
fed to the incinerator on a steel pallet. The incinerator was operated in a batch mode,
with the combustion cycles for each batch of scrap feed lasting between 1 and 3 hours.
Incineration of the material occurred by burning natural gas. Most of the wire had a tar-
based insulation that was thermally removed; however, PVC coated wire was also fed to
the incinerator. The estimated temperature during combustion was 650°C, and
combustion preceded in a primary and secondary chamber. The tested facility was
equipped with a high temperature afterburner to further destroy organic compounds
entrained in the combustion gases prior to discharge to the air from the stack. Emission
factors estimated for this one facility include an average emission factor for TEQ of
1.18E-02/yg/kg of scrap wire (range = 6.74E-03 to 1.69E-02//g/kg), and an average
emission for total CDD/CDF of 9.89E-01 fjg/kg of scrap wire (range = 9.89E-01 to
3.28E + 00/yg/kg). These emission factors are assigned a "low" confidence rating
because the factors were derived from measurements at only one facility operating in the
U.S. and it is not known how representative these test results are of other scrap electric
wire incinerators. Although it is uncertain how many facilities still combust scrap wire, for
purposes of this assessment, it is assumed that only minimal quantities of scrap wire are
currently burned in the United States.
3.6.11. Drum and Barrel Reclamation and Incineration
Hutzinger and Fiedler (1991b) reported that the CDDs and CDFs are emitted in
stack gases from drum and barrel reclamation facilities and that the concentration of
CDDs/Fs found in those emissions range from 5 to 27 ng/m3. Dioxin-like compounds were
measured by EPA in the stack gas emissions of a drum and barrel reclamation furnace as
part of the National Dioxin Study (U.S. EPA, 1987). These plants operate a burning
furnace to prepare used steel 55-gallon drums for cleaning to base metal. The drums
processed at these facilities come from a variety of sources in the petroleum and chemical
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industries. The cleaned drums are repaired, repainted, relined and sold for reuse. The
drum burning process subjects used drums to an elevated temperature in a tunnel furnace
for a sufficient time so that the paint, interior linings, and previous contents are burned or
disintegrated. The furnace is fired by auxiliary fuel. Used drums are loaded onto a
conveyor that moves at a fixed speed. As the drums pass through the preheat and ignition
zone of the furnace, additional contents of the drums drain into the furnace ash trough. A
drag conveyor moves these sludges and ashes to a collection pit. The drums are air
cooled as they exit they furnace. Exhaust gases from the burning furnace are drawn
through a breeching fan to a high-temperature afterburner.
Emission factors of dioxin-like compounds were developed from EPA stack tests of
a prototypical operation (U.S. EPA, 1987) yielding the following emission factors in units
of/yg/kg: minimum TEQ = 1.12E-02; mean TEQ = 1.65E-02; maximum TEQ = 2.69E-
02; mean CDD/CDF = 1.30E + 00; minimum CDD/CDF = 1.16E + 00; maximum
CDD/CDF = 1.85E + 00.
Approximately 2.8 to 6.4 million 55-gallon drums are incinerated annually in the
United States (telephone conversation between P. Rankin, Association of Container
Reconditioners, and C. D'Ruiz, Versar, Inc., December 21, 1992). This estimate is based
on the following assumptions: 1) 23 to 26 incinerators are currently in operation; 2) each
incinerator, on average, handles 500 to 1,000 drums per day; and 3) on average, each
incinerator operates 5 days per week with 14 days downtime per year for maintenance
activities. The weight of 55-gallon drums varies considerably; however, on average, a
drum weighs 38 Ibs (or 17 kg). Therefore, an estimated 48 to 109 million kg of drums are
estimated to be incinerated annually. Assuming that 109 million kg of drums are burned
each year and applying the mean emission factors developed above, the best estimates of
annual emissions are 140 grams per year of total CDD/CDF and 1.7 grams per year of
TEQ.
A "low" confidence rating is assigned to the production estimate since it is based
an expert judgement rather than a published reference. A "low" confidence rating is
ascribed to the emission factor since it is developed from stack tests conducted by EPA on
just one U.S. drum and barrel furnace and this one facility may not represent emissions
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from all current operations in the U.S. Based on these confidence ratings, the estimated
range of potential annual emissions is assumed to vary by a factor of 10 between the low
and high ends of the range. Assuming that the best estimate of annual emissions (1.7 g
TEQ/yr) is the geometric mean of this range, then the range is calculated to be 0.5 to 5.4
g TEQ/yr.
3.6.12. Tire Combustion
Emissions of dioxin-like compounds from the incineration of automobile tires were
measured from a tire incinerator stack tested by the State of California Air Resources
Board (CARB, 1991). The facility consists of two excess air furnaces equipped with steam
boilers to recovery the energy from the heat of combustion. Discarded whole tires are fed
to the incineration units at a rate of 3000 kg/hr. The furnaces are equipped to burn
natural gas as auxiliary fuel. The steam produced from the boilers is used to drive
electrical turbine generators that produce 14.4 megawatts of electricity. The facility is
equipped with a dry acid gas scrubber and fabric filter for the control of emissions prior to
exiting the stack.
Emission factors for total CDD/CDF and TEQ in units of yt/g/kg of tires combusted
were derived as average values from the one tested facility stack tested in California
(CARB, 1991). From these data, an average emission factor of CDD/CDF was estimated
to be 1.39E-02//g/kg of tires incinerated (range: 4.28E-03 to 3.05E-02 ;/g/kg), and
average emission factor of TEQ was estimated to be 5.42E-04pg/kg (range: 1.91E-04 to
1.02E-03//g/kg).
EPA's Office of Solid Waste estimates that approximately 0.50 million metric tons
of tires are incinerated in the United States annually (U.S. EPA, 1992a). This production
estimate is given a "high" confidence rating since it is based on detailed study specific to
the United States. The use of scrap tires as a fuel increased significantly during the late
1980s. In 1990, 10.7 percent of the 242 million scrap tires generated were burned for
fuel. This percentage is expected to continue to increase (U.S. EPA, 1992a).
If it is assumed that 500 million kilograms of discarded tires are incinerated annually
in the United States, then, using the emission factors derived from stack data from the one
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tested facility, an average of 6.9 grams of total CDD/CDF per year and an average of 0.3
grams of TEQ per year are estimated to be emitted to the air. It must be noted that these
may be underestimates of emissions from this source category because the one facility
tested in California is equipped with a dry-scrubber combined with a fabric filter for air
pollution control. These devices are capable of greater than 95 percent reduction and
control of dioxin-like compounds prior to discharge from the stack. It is not know to what
extent other tire incineration facilities operating in the U.S. are similarly controlled. If such
facilities are not so equipped, then the uncontrolled emission of CDD/CDF and TEQ could
be much greater than the estimates developed above. Therefore, the estimated emission
factor of dtoxin from tire incineration is given a "low" confidence rating. Based on these
confidence ratings, the estimated range of potential annual emissions is assumed to vary
by a factor of 10 between the low and high ends of the range. Assuming that the best
estimate of annual emissions (0.3 g TEQ/yr) is the geometric mean of this range, then the
range is calculated to be 0.1 to 1.0 g TEQ/yr.
Buser et al. (1991) indicated that PCDTs (polychlorinated dibenzothiophenes,
possibly a dioxin-like compound) can be formed in situations where large amounts of
sulfur and chlorine-containing compounds are incinerated or accidentally burned.
Automobile tires are known to contain sulfurous (vulcanization) compounds and certain
types of chloro compounds (e.g., chloroprene). Thus, it is possible that the burning of
used automobile tires could result in the formation of PCDTs.
3.6.13. Motor Vehicle Fuel Combustion
Some of the first evidence that CDD/CDFs might be created during the combustion
processes in gasoline- and diesel-fueled engines came from Ballschmiter et al. (1986) who
measured these compounds in used motor oil in Germany. Incomplete combustion and the
presence of a chlorine source in the form of additives in the oil or the fuel (such as
dichloroethane or pentachlorophenate) were speculated to lead to the formation of CDDs
and CDFs. The isomeric patterns were characterized as typical of combustion processes.
Marklund et al. (1987) provided the first direct evidence of these compounds in car
emissions based on tailpipe measurements on four Swedish cars running on leaded
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gasoline. They found 20 to 220 pg of TEQ per kilometer driven. For this study, a
nonleaded gasoline was used to which was added tetramethyl lead (0.15 grams of lead per
liter or 0.57 grams per gallon) and dichloroethane (0.1 g/L as a scavenger). The fuel used
may not accurately represent commercial fuels which typically contain a mixture of
chlorinated and brominated scavengers (Marklund et al., 1990). Also, the lead content of
the fuel used (0.15 g lead/L), although the normal lead content for Swedish fuels
(Marklund et al., 1990), is higher than the lead content of leaded gasoline in the United
States during the late 1980s (lowered to 0.10 g lead/gallon or 0.026 g lead/L effective
January 1, 1986). For two cars running on unleaded gasoline, CDD/CDF emissions were
below the detection limit which corresponded to approximately 13 pg of TEQ per kilometer
driven. Table 3-33 presents a summary description of this study and subsequent studies
discussed below.
Bingham et al. (1989) also analyzed 2,3,7,8-substituted CDD/CDFs in automobile
exhausts. Four cars using leaded gasoline (0.45 g/L tetramethyllead, 0.22 g/L
dichloroethane and 0.2 g/L dibromoethane) were tested and one car using lead free
gasoline was tested. Only HpCDD and OCDD were detected in the exhaust from the
vehicle using lead-free fuel. The total TEQ emission rate, based on these detected
congeners, was 1 pg/km; the detection limit for the other 2,3,7,8-substituted CDD/CDFs
was a combined 28 pg TEQ/km. 2,3,7,8-TCDF was detected in the exhaust of two of
four cars using leaded fuel. OCDD was detected in the exhaust from three of the cars and
PeCDF and HpCDD were each detected in the exhaust from one car. TEQ emission rates
for the cars using leaded fuel, based on detected congeners, was 5 to 39 pg/km.
Haglund et al. (1988) sampled exhaust gases from three different vehicles (two
cars fueled with leaded and unleaded gasoline, respectively, and a heavy diesel truck) for
the presence of brominated dibenzo-p-dioxins (BDD) and brominated dibenzofurans (BDF).
The authors concluded that the dibromoethane scavenger added to the tested gasoline
probably acted as a halogen source. TBDF emissions measured 23 ng/km in the car with
leaded gasoline and 0.24 ng/km in the car with unleaded gasoline. TBDD and PeBDF
emissions measured 3.2 and 0.98 ng/km, respectively in the car with leaded gasoline. All
BDD/Fs were below detection limits in the diesel truck emissions.
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Table 3-33. Descriptions and Results of Vehicle Emission Testing Studies for CDDs and CDFs
Study
Marklund et al. (1987)
Bingham et al. (1989)
Marklund et al. (1990)
Hagenmaier et al. (1990)
Oehme et al. (1991)
(tunnel study)
Country
Sweden
New Zealand
Sweden
Germany
Norway
Fuel Type
Unleaded
Leaded
Unleaded
Leaded
Unleaded
Leaded
Unleaded
Leaded
Diesel
Unleaded
Unleaded
Leaded
Diesel
Scavenger*
No
Yes
No
Yes
No
Yes
No
Yes
None
No
No
Yes
No
Catalyst
Equipped
Yes
No
NR
NR
No
No
Yes
No
NR
No
Yes
No
NR
Number
of Test
Vehicles
2
4
1
4
2
2
1
2
1
1
1
1
1
(c)
Emission Factor
(pg TEQ/km driven)
<13
20-220
1
5-39
0.36-0.39
2.6-6.3
0.36
1.1-2.6
not detected
5.1"
0.7"
108b
50"
520"
38d
avg = 280
9.500d
720d
avg = 5,100
Driving Cycle; Sampling Location
A10 (2 cycles); muffler exhaust
A10 (2 cycles); muffler exhaust
A10 (3 or 4 cycles); muffler exhaust
A10 (3 or 4 cycles); muffler exhaust
FTP-73 test cycle; before muffler
FTP-73 test cycle; before muffler
FTP-73 test cycle; in tailpipe
FTP-73 test cycle; in tailpipe
U.S. Federal mode 13 cycle; before muffler
Comparable to FTP-73 test cycle; in tailpipe
Comparable to FTP-73 test cycle; in tailpipe
Comparable to FTP-73 test cycle; in tailpipe
Comparable to FTP-73 test cycle; in tailpipe
Cars moving uphill (3.5% incline) at 60 km/hr
Cars moving downhill (3.5% decline) at 70 km/hr
Trucks moving uphill (3.5% incline) at 60 km/hr
Trucks moving downhill (3.5% decline) at 70 km/hr
Dichloroethane and dibromoethane, except for Marklund et al. (1987), used as scavengers.
Results reported by Hagenmaier et al. (1990) were in units of pg TEQ/liter of fuel. For purposes of this table, the fuel economy factor used by Marklund et al. (1990), 10 km/L or 24 miles/gal,
was used to convert the emission rates into units of pg TEQ/km driven for the gasoline-fueled vehicle. For the diesel-fueled truck, a factor of 2 km/L (or 5 miles/gal) was used.
Tests were conducted over portions of 4 days with traffic rates of 8,000-14,000 vehicles/day. Heavy duty vehicles ranged from 4-15% of total.
Emission factors are reported in units of pg Nordic TEQ/km driven.
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More recently, Marklund et al. (1990) tested gasoline- and diesel-fueled vehicles,
measuring CDD/CDF emissions before and/or after the muffler of Swedish vehicles
(including new and old vehicles). Marklund et al. (1990) reported the emission results in
units of pg TEQ/L of fuel consumed and also in units of pg TEQ/km driven during the test.
Based on the test driving cycle employed (i.e., 31.7 km/hr as a mean speed; 91.2 km/hr as
a maximum speed; and 17.9 percent of time spent idling), Marklund et al. (1990) observed
a fuel economy of approximately 9 to 10 km/L or 22 to 24 miles/gallon. The following
measurements were reported:
• leaded gas/cars/before muffler: 2.4 to 6.3 pg TEQ/km (or 21 to 60 pg TEQ/L
of fuel consumed)
• leaded gas/cars/in tailpipe: 1.1 to 2.6 pg TEQ/km (or 10 to 23 pg TEQ/L).
• lead-free gas/catalyst-equipped car/in tailpipe: 0.36 pg TEQ/km (or 3.5 pg
TEQ/L)
• lead-free gas/cars/before muffler: 0.36 to 0.39 pg TEQ/km (or 3.5 pg
TEQ/L)
• diesel fuel/heavy-duty truck/before muffler: not detected (i.e., less than 100
pg TEQ/L)
Regarding the diesel fuel measurement, the authors pointed out that the test fuel was a
reference fuel and may not be representative of commercial diesel fuel. Also, due to
analytical problems, a much higher detection limit (about 100 pg TEQ/L) was employed in
the diesel fuel tests than in the gasoline tests (5 pg TEQ/L). Further uncertainty is
introduced by the fact that diesel emission samples were only collected prior to the
muffler. The TEQ levels in exhaust gases from older cars using leaded gasoline were up to
six times greater when measured before the muffler than after the muffler. No muffler-
related difference in new cars running on leaded gasoline or in old or new cars running on
unleaded gasoline were observed.
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Hagenmaier et al. (1990) ran a series of tests on gasoline engines for light duty
vehicles in Germany. The following average TEQ emission rates per liter of fuel consumed
were found:
• Leaded fuel: 1.083ngTEQ/L
• Unleaded fuel (catalyst-equipped): 0.007 ng TEQ/L
• Unleaded fuel (not catalyst-equipped): 0.051 ng TEQ/L
• Diesel fuel: 0.024 ng TEQ/I
Several European studies have evaluated CDD/CDF emissions from vehicles by
measuring the presence of CDD/CDFs in tunnel air. This approach has the advantage that
it allows random sampling of large numbers of cars, including a range of ages and
maintenance levels. The disadvantage of this approach is that it relies on indirect
measurements (rather than tailpipe measurements) which may introduce unknown
uncertainties and make interpretation of the findings difficult. Concerns have been raised
that the tunnel monitors are detecting resuspended particulates which have accumulated
over time, leading to overestimates of emissions. Also, the driving patterns encountered in
these tunnel studies are more or less steady state driving conditions rather than the
transient driving cycle and cold engine starts that are typical of urban driving conditions
and which may affect emission levels. Wevers et al. (1992) found that CDD/CDF levels
inside a Belgium tunnel were about twice the levels in ambient air and estimated the
average level in vehicle emissions as 42 to 45 pg TEQ/Nm3. Rappe et al. (1988)
conducted a similar tunnel study in Sweden and Oehme et al. (1991) conducted a similar
study at a tunnel in Norway, the preliminary results of which were reported by Larssen et
al. (1990). The Oehme et al. (1991) study estimated emissions for light duty and heavy
duty vehicle classes. This was completed by counting the number of light duty vs. heavy
duty vehicles passing through the tunnel during the study. The mean emission rate
estimates from this study are:
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• Light-duty vehicles using gasoline (approximately 30 percent using leaded gas):
0.28 ng TEQ/km
• Heavy-duty diesel trucks: 5.1 ng TEQ/km
These mean values are the averages of the emission rates corresponding to two
operating modes: vehicles moving uphill on a 3.5 percent incline and vehicles moving
downhill on a 3.5 percent decline. The TEQ emission rates for the two modes differ by an
order of magnitude for both light and heavy duty vehicles. Although Oehme et al. (1991)
reported results in units of Nordic TEQs rather than l-TEQs, the results in I-TEQ should be
virtually identical because the only difference between the two TEQ schemes is the factor
assigned to 1,2,3,7,8-PeCDF (0.1 in Nordic and 0.05 in I-TEQ), a minor component of the
toxic CDD/CDFs measured in the tunnel air.
Virtually no testing of vehicle emissions in the United States for CDD/CDFs has
been published. In 1987, the California Air Resources Board (CARB) produced a draft
report on the testing of the exhausts of four gasoline-powered cars and three diesel fuel-
powered vehicles (one truck, one bus, and one car) (CARB, 1987). However, CARB has
indicated to EPA that the draft report should not be cited or quoted to support general
conclusions about CDD/CDFs in motor vehicle exhausts because of the small sample size
of the study and because the use of low rather than high resolution mass spectrometry in
the study resulted in high detection limits and inadequate selectivity in the presence of
interferences (Lew, 1993). CARB did state that the results of a single sample from the
heavy-duty diesel truck could be reported because congeners from most of the homologue
groups were present in the sample at levels that could be detected by the analytical
method and there were no identified interferences in this sample. However, it should be
noted that this test was conducted under steady state conditions and at low speeds which
are not indicative of normal driving patterns. The TEQ content of this one sample was
218 pg per dry standard cubic meter (dscm) of exhaust. The CARB results suggest that
diesel-fueled trucks do emit CDD/CDFs (Lew, 1993).
Jones (1993) estimated CDD/CDF emissions of the major vehicle types on the basis
of the studies by Larssen et al. (1990), the 1987 draft report by CARB, and Hagenmaier et
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al. (1990). Using data on vehicle miles travelled in the U.S. and an assumed emission rate
of 5.4 ng TEQ/km based on Larssen et al. (1990), Jones (1993) estimated that about
1000 g of TEQ were emitted from diesel vehicles nationwide in 1990. Jones (1993) also
suggests that human exposure to diesel emissions are exacerbated relative to stack
emissions from combustion sources on the basis that diesel emissions occur at ground
level and that, unlike stack emissions, may not undergo much dilution in air before human
contact occurs.
In 1973, EPA required refiners to meet a 0.5 gpg (gram per gallon) standard for the
average lead content of all gasoline. EPA later replaced this standard with a standard for
the lead content of leaded gasoline only. Effective November 1, 1982, large refineries
were required to meet a standard of 1.10 grams per leaded gallon (gplg). Certain smaller
refineries were subject to a 1.90 gplg standard until July 1, 1983, at which time they
would also be subject to the 1.10 gplg standard (Federal Register, 1982). EPA further
reduced the standard to 0.10 gplg effective January 1, 1986 with a[n] interim standard of
0.5 gplg effective July 1, 1985 (Federal Register, 1985). The Clean Air Act Amendments
of 1990 imposed further restrictions as follows: "After December 31, 1995, it shall be
unlawful for any person to sell, offer for sale, supply, offer for supply, dispense, transport,
or introduce in commerce, for use as fuel in any motor vehicle any gasoline which contains
lead or lead additives."
In 1985, the year before the phasedown of leaded gasoline from 1.10 gplg to 0.10
gplg, approximately 1,774 billion miles (2,855 billion km) were driven (U.S. DOC, 1992).
Because leaded gasoline accounted for 35.5 percent of the gasoline supply that year (EIA,
1993) it can be estimated that 1,013 billion of these kilometers (i.e., 35.5 percent of
2,855 billion km) were driven by vehicles powered with leaded gasoline.
The U.S. Federal Highway Administration, as reported in U.S. DOC (1992), reports
that 2,148 billion total vehicle miles (3,456 billion km) were driven in the U.S. during
1990. During 1990, automobiles and motorcycles accounted for 1,525 billion vehicle
miles (2,454 billion km). Trucks accounted for 617 billion vehicle miles (993 billion km)
and buses accounted for 5.7 billion vehicle miles (9.2 billion km) (U.S. DOC, 1992). In
1987, diesel-fueled trucks accounted for 17.2 percent of total truck vehicle km driven;
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gasoline-fueled trucks accounted for the remaining 82.8 percent (U.S. DOC, 1990b).
Applying this factor (i.e., 17.2 percent) to the 1990 km truck mile estimate (i.e., 993
billion km) indicates that an estimated 171 billion km were driven by diesel-fueled trucks in
1990. It is assumed that all other vehicle km driven (3,285 billion km) were those of
gasoline-powered vehicles. In 1990, leaded gasoline accounted for only 5.3 percent of
total gasoline supplies (EIA, 1993). These mileage estimates are given a "high"
confidence rating on the basis that they are based on U.S. Census of Transportation
studies.
Using the above literature, separate emission estimates were developed for vehicles
burning leaded gasoline, unleaded gasoline and diesel fuel:
• Leaded Gasoline: In general, the literature indicates that CDD/CDF emissions occur
from vehicles using leaded gasoline and that considerable variation occurs depending, at
least in part, on the types of scavengers used. Marklund et al. (1987) reported emissions
ranging from 20 to 220 pg TEQ/km from four cars fueled with a reference fuel (0.5 gplg)
to which lead and a chlorinated scavenger were added. Marklund et al. (1990) reported
much lower emissions in the tailpipe exhaust of two cars (1.1 to 2.6 pg TEQ/km) using a
commercial leaded fuel (0.57 gplg). Marklund et al. (1990) attribute the difference in the
emission measurements to the different scavengers used in the two studies. Hagenmaier
et al. (1990) reported TEQ emissions of 1,083 pg/L of fuel (or approximately 108 pg
TEQ/km) from a car fueled with a commercial leaded fuel (lead content not reported).
Bingham et al. (1989) reported emissions from four cars using gasoline with a lead content
of 1.7 gplg in New Zealand to range from 5 to 39 pg/km. The tunnel study by Oehme et
al. (1991) indicated that emissions from cars could be 38 to 520 pg TEQ/km. Since most
of the vehicles passing through the tunnel studied by Oehme et al. (1991) used unleaded
fuels (approximately 70 percent), the emissions from leaded fuel-powered cars were
possibly even higher.
On the basis of the three studies performed using commercial leaded fuel, an
emission factor range of 1.1 to 108 pg TEQ/km is recommended. A "low" confidence
rating is assigned to this factor range because the range is based on European fuels and
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emission control technologies which may differ from U.S. fuels and technology and also
because the factor range is based is based on tests with only seven cars. Combining this
emission factor range with the estimates for km driven by leaded fuel-powered vehicles in
1985 (1,013 billion km or 35.5 percent of total km) and in 1990 (174 billion km or 5.3
percent of the 3,285 billion km driven by gasoline-powered vehicles) suggests that about
1.1 to 109 g TEQ/yr were emitted from vehicles using leaded fuels in 1985, the year
immediately before the phasedown of leaded gasoline from 1.10 gpig to 0.10 gpig and the
year when the interim standard of 0.5 gpig became effective. By comparison, the annual
emission for 1990 from use of leaded gasoline is estimated to have ranged from 0.2 to 19
gTEQ.
• Unleaded Gasoline: The literature clearly indicates that CDD/CDF emissions are much
less from vehicles burning unleaded fuels. The Marklund et al. (1990) study is the only
one which provided an emission factor for this class of vehicles. On the basis of this
study, an emission factor of 0.36 pg TEQ/km is recommended. A "low" confidence rating
is assigned to this factor because the Swedish fuels and emission control technology used
in the Marklund et al. (1990) study may differ from U.S. fuels and technology and also
because the emission factor is based on tests with only one catalyst-equipped car.
Combining this emission factor with the above estimates for vehicle km driven in 1990 by
gasoline-powered vehicles (3,285 billion), suggests that about 1.3 g of TEQ/yr were
emitted from vehicles using unleaded fuels in 1990. Based on the low confidence rating,
the estimated range of potential annual emissions is assumed to vary by a factor of 10
between the low and high ends of the range. Assuming that the best estimate of annual
emissions (1.3 g TEQ/yr) is the geometric mean of this range, then the range is calculated
to be 0.4 to 4.1 g TEQ/yr.
• Diesel Fuel: Very few data are available upon which to base an evaluation of the extent
of dioxin emissions resulting from diesel fuel combustion. The tunnel study by Oehme et
al. (1991) generated an estimated emission factor of 5.1 ng TEQ/km. A "low" confidence
rating is assigned to this factor because the factor is based on Norwegian fuels and
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emission control technology which may differ from U.S. fuels and technology. Also,
although aggregate samples were collected representing hundreds of vehicles, the indirect
method of analysis and the more or less steady state rather than transient driving
conditions of the study introduce considerable uncertainty.
The results of only one tailpipe measurement (diesel fuel in a heavy-duty Swedish
truck) have been published (Marklund et al., 1990) and that study reported no emissions at
a detection limit of 100 pg TEQ/L. If it is assumed that the fuel economy of heavy-duty
diesel vehicles is approximately 5 miles/gallon (or 2 km/L), then 100 pg TEQ/L converts to
approximately 0.05 ng TEQ/km - a factor 100-fold lower than the emission rate reported
by Oehme et al. (1991). Because the results of Marklund et al. (1990) are based on only
one vehicle using a Swedish reference, not a commercial, diesel fuel this emission factor is
also assigned a "low" confidence rating.
To obtain an estimate of the possible range of dioxin TEQ annual emissions
resulting from diesel fuel use, the geometric mean of the emission factors derived from the
Oehne et al. (1991) and Marklund et al. (1990) was calculated (0.5 ng TEQ/km).
Combining this emission factor with the above estimate for vehicle kms driven in 1990 in
the United States by diesel-fueled trucks (1 71 billion km) yields an annual emission
estimate of 85 g TEQ/yr. Based on the low confidence ratings, the estimated range of
potential annual emissions is assumed to vary by a factor of 10 between the low and high
ends of the range. Assuming that the best estimate of annual emissions (85 g TEQ/yr) is
the geometric mean of this range, then the range is calculated to be 27 to 270 g TEQ/yr.
3.6.14. Wood Burning at Residences
Measurable levels of TCDDs have been found in chimney soot and bottom ash from
wood-burning stoves and fireplaces (Clement et al., 1985b; Wenning et al., 1992).
Chimney deposits from residential wood burning have been found to have CDD/CDF
congener profiles similar to those in flue gases from municipal waste incineration (Bacher
et al., 1992). Bacher et al. (1992) found concentrations of 2,3,7,8-substituted CDF and
CDD congeners in soot from wood burning ranging from 40 to 930 ng/kg and from 30 to
150 ng/kg, respectively. Bacher et al. (1992) reported that the CDFs dominated the CDDs
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by a factor of 5 to 10 and that the lower chlorinated CDDs/CDFs (mono-through tri-}
dominated the more chlorinated CDDs/CDFs. The TEQ content of the chimney soot was
720 ng/kg (Bacher et al., 1992).
Nestrick and Lamparski (1983) conducted a study of CDD formation in residential
wood-burning chimneys in different areas of the United States. The results of their survey
are presented in Table 3-34. As seen in Table 3-28, the eastern U.S. had overall higher
estimated levels of TCDD generation than did the central or western United States. Levels
of TCDDs in chimney soot ranged from 22 to 410 ng/kg for the eastern U.S., 21 to 294
ng/kg in the central U.S., and 2.9 to 28 ng/kg in the western U.S. Red oak and oak were
the predominant fuels used in the eastern and western U.S., and ash, birch, and oak were
the predominant fuels used in the central U.S.
Two studies have recently become available which provide direct measurement of
CDD/CDF in emissions from wood stoves. These studies are summarized below.
Schatowitz et al. (1993) measured CDD/CDF in the emissions of a variety of
residential wood burners in Switzerland. The study included three types of burners
(household stoves, automatic chip burners, and wood boilers) and a variety of wood fuels
(natural beech wood, natural wood chips, chipboard chips, waste wood chips, charcoal
and household waste). The following emission factors were derived:
• household stove with open door burning natural beech wood: 0.77 ng TEQ/kg
• household stove with closed door burning natural beech wood: 1.25 ng TEQ/kg
The open door stove can be assumed to be representative of fireplaces since both have an
uncontrolled draft. Also, Schatowitz et al. (1993) measured emissions from wood burning
fireplaces and report the same flue gas concentration as found with the open door wood
stove (i.e., 0.064 ng TEQ/m3). All of the toxic congeners of CDD/CDF were found at
levels above the detection limit.
Vikelsoe et al. (1993) studied emissions of CDD/CDFs from residential wood stoves
in Denmark. The wood fuels used in the experiments were seasoned birch, beech and
spruce harvested in Denmark. Four different types of stoves were evaluated under normal
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Table 3-34. Average Concentrations (ppt) of TCDDs in Chimney Soot from Residential
Wood-Burning Stoves in the U.S.
TCDD Isomer
2,3,7,8
1,4,6,9
1,2,6,9
1,2,6,7
1,2,8,9
1,3,6,9
1,2,4,7/1,2,4,8
1,2,7,8
1,2,6,8
1,2,3,7/1,2,3,8
1,2,7,9
1,2,4,6
1,4,7,8
1,2,3,6
1,2,3,9
1,2,4,9
1,3,6,8
1,3,7,9
1,3,7,8
1,2,3,4
Total TCDDs
Eastern
U.S.'
132
22
115
82
93
155
367
225
245
410
233
130
67
141
143
128
352
403
343
162
3948
% of Total
TCDDs
3
1
3
2
2
4
9
6
6
10
6
3
2
4
4
3
9
10
9
4
Central
U.S.b
110
21
80
42
49
150
254
168
194
294
219
60
77
56
64
83
181
166
212
36
2517
% of
Total
TCDDs
4
1
3
2
2
6
10
7
8
12
9
2
3
2
3
3
7
7
8
1
Western
U.S.*
13
2.9
8.3
4.1
5.4
17
26
17
19
28
27
7.7
11
7.5
8.1
12
17
14
23
3.4
314
% of Total
TCDDs
4
1
3
1
2
5
8
5
6
9
9
2
4
2
3
4
5
4
7
1
Source: Nestrick and Lamparski (1983)
• Ash samples from 3 masonry chimneys in which red oak was the predominant fuel.
b Ash samples from 3 masonry chimneys in which ash, birch, or oak were the predominant fuel.
° Ash samples from one chimney and five metal chimneys in which oak was the predominant fuel.
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and optimal operating conditions. Widely varying emissions were found for different
fuel/stove combinations. The emissions from spruce were about twice as high as the
emissions from birch and beech. In many of the experiments the CDD/CDF emissions
were higher when the stove was operated under normal conditions vs optimal conditions
(minimum CO). The weighted average (considering wood and stove types) emission
factor for wood stoves in Denmark was estimated to be 1.9 ng Nordic-TEQ/kg.
Based on the above studies, 1 ng TEQ/kg appears to be a reasonable average
emission factor for residential wood burning. A "medium" confidence rating was assigned
to this estimate on the basis that: (1) it is derived from only two studies; (2) both studies
used direct measurement; and (3) although the studies were conducted in Europe,
residential wood burning practices are probably sufficiently similar to apply to the United
States.
In 1990, wood provided about 2.8 percent of the total primary energy consumed in
the United States (EIA, 1991). Total wood energy consumption during 1990 is estimated
at 2,359 trillion BTU. Assuming that 1 kg of oven-dried wood (i.e., 2.15 kg of green
wood) provides approximately 19,000 BTU, then an estimated 124.2 million metric tons of
oven-dried wood equivalents were burned for energy purposes in 1990 (EIA, 1991).
Residential wood consumption in 1990 was estimated at 786 trillion BTU (41.4 million
metric tons), or 33 percent of total U.S. consumption. Industrial fuel wood consumption
in 1990 totaled 1,562 trillion BTU (82.2 million metric tons), or 66 percent of total U.S.
consumption, with the majority (1,232 trillion BTU) of this fuel wood being consumed by
the Paper and Allied Products Industry. 1990 consumption of fuel wood by the utility
sector was approximately 11.9 trillion BTU (0.6 million metric tons) (EIA, 1991). These
production estimates are given a "high" confidence rating since they are based on a
detailed published study specific to the United States.
Combining the best estimate of the emission factor (1 ng TEQ/kg wood) with the
mass of wood consumed annually by residences, indicates that the annual TEQ emissions
from this source are about 40 grams. Based on the "medium" confidence rating assigned
to the emission factor, the estimated range of potential annual emissions is assumed to
vary by a factor of 5 between the low and high ends of the range. Assuming that the best
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estimate of annual emissions (40 g TEQ/yr) is the geometric mean of this range, then the
range is calculated to be 13 to 63 g TEQ/yr.
3.6.15. Industrial Wood-Burning Facilities
Emissions of dioxin-like compounds have been measured in stack emissions from an
industrial wood-burning furnace by EPA (U.S. EPA, 1987). The tested facility was located
at a lumber products plant that manufactures overlay panels and other lumber wood
products. The wood-fired boiler tested was a three-cell dutch oven equipped with a waste
heat boiler. During normal operation, the furnace is 100 percent fired with scrap wood
from the lumber plant. The feed wood is a mixture of bark, hogged wood, and green and
dry planar shavings. The composition of the feed was estimated to be wood from fir and
hemlock. Nearly all the wood fed to the lumber plant had been stored in sea water
adjacent to the facility, and therefore had a significant concentration of inorganic chloride.
The scrap wood fed to the boiler had not been treated with chemical preservatives, e.g.,
pentachlorophenol. The wood was fed to the boiler by a screw conveyor that dumps the
feed into a pile in the primary combustion chamber. The furnace is operated at air in 50
percent excess of stoichiometric requirements. Boilers capture the heat of combustion and
transfer the heat into steam for co-generation of energy at the plant. The exhausted gases
from the boiler pass through a cyclone and fabric filter prior to discharge from the stack.
From this study, an average emission factor for CDD/CDF of 1.02 //g/kg of wood burned
(range: 5.52E-01 to 1.41E + 00 //g/kg), and an average emission factor for TEQ of
1.71E-02/yg/kg of wood burned (range: 7.34E-03 to 2.28E-02/vg/kg) are estimated.
Emissions testing at this facility demonstrated that the fabric filter was reducing dioxin
emissions by about 90 percent (U.S. EPA, 1987).
In a second study, CDD/CDF was measured in the emissions from a quad-cell
wood-fired boiler used to generate electricity (CARB, 1990b). The fuel consisted of coarse
wood waste and sawdust from nonindustrial logging operations. The exhaust gas passed
through a multicyclone before entering the stack. This study suggests an emission factor
of 5.4E-02 /yg/kg for CDD/CDF. If the same TEQ to total CDD/CDF ratio is assumed as in
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the first industrial burner study, then an emission factor of 9E-04 //g TEQ/kg can be
estimated.
To obtain an estimate of the possible range of dioxin TEQ annual emissions
resulting from industrial wood-burning facilities, the geometric mean of the emission
factors derived from the U.S. EPA (1987) and CARB (1990b) studies was calculated (3.9
ng TEQ/kg wood). Because test data are available for only two facilities and because the
emission factors measured at these two facilities vary greatly, this emission factor was
given a "low" confidence rating.
In 1990, it was estimated that 82.2 million metric tons of wood were burned in
industrial furnaces ("high" confidence rating, see discussion in Section 3.6.14). Applying
the above emission factor to the estimated annual mass of wood burned by industrial
facilities gives an estimated TEQ emission of 320 g TEQ/yr. Based on the low confidence
rating given to the emission factor, the estimated range of potential annual emissions is
assumed to vary by a factor of 10 between the low and high ends of the range. Assuming
that the best estimate of annual emissions (320 g TEQ/yr) is the geometric mean of this
range, then the range is calculated to be 100 to 1,000 g TEQ/yr.
3.6.16. Wood Burned in Forest Fires
Based on the findings of Wenning et al. (1992), Bacher et al. (1992), and Nestrick
and Lamparski (1983), indicating generation of CDDs/CDFs in ash and soot during
residential wood burning, it is reasonable to hypothesize that wood burned in forest fires
may also be a source of CDDs/CDFs. Support for this hypothesis is provided by Bumb
et al. (1980) who, in their study on trace chemistry of fire, have shown that combustion
of hydrocarbons in the presence of chlorine compounds (which are naturally found at low
levels in wood) can generate CDDs and CDFs in small amounts. Also, the pre-industrial
existence of CDDs and CDFs, presumably due to combustion sources, has been
demonstrated in analyses of ancient human tissues and ancient aquatic sediment deposits
(ECETOC, 1992).
Only one study could be found that made direct measurements of CDD/CDFs in the
actual emissions from forest fires. This study by Tashiro et al. (1990) detected levels
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ranging from about 15 to 400 pg/m3 for total CDD/CDFs. The samples were collected
from fixed collectors 10m above the ground and from aircraft flying through the smoke.
Background samples collected before and after the tests indicated negligible levels in the
atmosphere. These results were presented in the form of a preliminary report and no firm
conclusions were drawn about whether forest fires are a CDD/CDF source. Coauthor Dr.
Ray Clement presented the final report on this study at Dioxin '91. Clement and Tashiro
(1991) reported total CDD/CDF levels in the smoke of about 20 pg/m3. The authors
concluded that CDD/CDFs are emitted during forest fires but recognized that some portion
of these emissions could represent resuspension from residues deposited on leaves rather
than newly formed CDD/CDFs.
The concentrations presented by Clement and Tashiro (1991) cannot accurately be
converted to an emission factor since the corresponding rates of combustion gas
production and wood consumption are not known. As a result, three alternative
approaches were considered to develop these emission factors:
Soot-Based Approach: This approach assumes that the level of CDD/CDFs in
chimney soot are representative of the CDD/CDFs in emissions, and estimates the
CDD/CDF emission rate as the product of the soot level and the total particulate emission
rate. This involves first assuming that the CDD/CDF levels measured by Bacher et al.
(1992) in chimney soot (720 ng TEQ/kg) are representative of the CDD/CDF
concentrations of particles emitted during forest fires. Second, the total particulate
generation rate must be estimated. Ward et al.(1976) estimated the national average
particulate emission factor for wildfires as 150 Ib/ton biomass dry weight based primarily
on data for head fires. Ward et al. (1993) estimated the national average particulate
emission factor for prescribed burning as 50 Ib/ton biomass dry weight. Combining the
total particulate generation rates with the CDD/CDF levels in soot yields emission factor
estimates of 54 //g of TEQ and 18 jug of TEQ/metric ton of biomass burned in wildfires and
prescribed burning, respectively. This corresponds to a range of 54 to 18 ng TEQ/kg of
biomass. This estimate is likely to be an overestimate since the levels of CDD/CDF
measured in chimney soot by Bacher et al. (1992) may represent accumulation/enrichment
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of CDD/CDFs measured in chimney soot over time, leading to much higher levels than
what is actually on emitted particles.
Carbon Monoxide (CO) Approach: CO is a general indicator of the efficiency of
combustion and the emission rate of many emission products can be correlated to the CO
emission rate. The Schatowitz et al. (1993) data for emissions during natural wood
burning in open stoves suggests an emission rate of 10 ug TEQ/kg of CO. Combining this
factor with the CO production rate during forest fires (roughly 0.1 kg CO/kg of biomass -
Ward et al. (1993)) yields an emission factor of 1000 ng TEQ/kg biomass. This factor
appears unreasonably high since it is even higher than the soot-based factor discussed
above. Although the formation kinetics of CDD/CDF during combustion are not well
understood, it appears that CDD/CDF emissions do not correlate well with CO emissions.
Wood Stove Approach: This approach assumes that the emission factor for
residential wood burning (using natural wood and open door, i.e., uncontrolled draft)
applies to forest fires. As discussed in Section 3.6.14, this approach suggests an
emission factor of about 1 ng TEQ/kg. This value appears more reasonable than the
factors suggested by the soot and CO approaches. However, forest fire conditions differ
significantly from combustion conditions in wood stoves. For example, forest fire
combustion does not occur in an enclosed chamber and the biomass consumed in forest
fires is usually green and includes underbrush, leaves and grass. Given these differences
and the uncertainties about the formation kinetics of CDD/CDF during combustion, it is
difficult to determine whether CDD/CDF emissions would be higher or lower from forest
fires than from wood stoves. Thus, although an emission factor of 1 ng TEQ/kg appears
to be the best estimate that can be made currently, it must be considered highly uncertain
and a "low" confidence rating was assigned to this estimate.
According to the Council on Environmental Quality's 21st Annual Report (CEQ,
1990), an average of 5.1 million acres of biomass have been burned in wildfires every year
from 1950 to 1990. This value also corresponds well to the data provided by the USDA
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Forest Service for 1975 in which 4.4 million acres of biomass were burned in wildfires
(Ward et al., 1976). Yearly estimates cited in the CEO report (CEO, 1990) ranged from a
high of 15.5 million acres burned to an annual low of 1.8 million acres burned over the
forty year time period. Additionally, 5.1 million acres of biomass were burned in 1989
during prescribed burns (Ward et al., 1993). Prescribed burning is also known as managed
or controlled burning and is used as a forest management tool under exacting weather and
fuel conditions. These acreage estimates can be combined with biomass consumption
rates of 10.4 tons/acre in areas consumed by wildfires (Ward et al., 1976) and 8.2
tons/acre in areas consumed in prescribed burns (Ward et al., 1993). This combination
suggests a total of 53 million tons (or 48 million metric tons) of biomass are consumed
annually in wildfires while a total of 42 million tons (or 38 million metric tons) of biomass
are consumed annually in prescribed burns. These production estimates were assigned a
"medium" confidence rating since they are based on a combination of estimates involving
detailed historical data specific to the United States on acres burned but less accurate
estimates of biomass burned/acre.
Combining the emission factor developed using the "wood stove" approach (i.e., 1
ng TEQ/kg biomass) with the amount of biomass consumed annually in wildfires and
prescribed fires (total of 86 million metric tons) indicates that the best estimate of annual
TEQ emissions from this source is 86 g. Based on the low confidence rating given to the
emission factor, the estimated range of potential annual emissions is assumed to vary by a
factor of 10 between the low and high ends of the range. Assuming that the best
estimate of annual emissions (86 g TEQ/yr) is the geometric mean of this range, then the
range is calculated to be 27 to 270 g TEQ/yr.
Whether releases from this source result in significant human exposure is
questionable. If wood burning today is a major source of human exposure to CDD/CDFs,
then the tissues of ancient humans (who relied on wood as a fuel source more so than do
humans in industrialized settings today) should have CDD/CDF levels that are a substantial
fraction of the levels found in humans today. The 1987 NHATS study indicates that the
U.S. average CDD/CDF adipose tissue concentration is currently about 1000 ppt (U.S. EPA
1990d) and Schecter (1991) reports that the total CDD/CDF concentration in liver tissues
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today is about 400 ppt. However, with the exception of OCDD in one sample, Ligon et al.
(1989) could not detect CDD/CDFs that exceeded the analytical background (detection
limit = 0.3 to 5 ppt) in the mummified muscle tissues of nine 2,800 year old Chilean
Indians. Similarly, Schecter (1991) examined the livers of two frozen 400 year old Eskimo
women and found only HpCDD, OCDD, and HpCDF at levels only 15 percent of current
levels.
3.6.17. Coal Combustion
Fiedler and Hutzinger (1992) estimate that 1.1 g of dioxin TEQ may be released to
the atmosphere in Germany annually from residential combustion of coal. In the United
Kingdom, combustion of coal by residential, industrial, and utility sources is estimated to
account for 38 percent (1,489 g TEQ/yr) of all dioxin TEQ releases to the atmosphere
(ECETOC, 1992). The Clean Air Act requires an assessment of the emissions of toxic air
contaminants (including CDDs and CDFs) discharged from the stacks of coal-fired power
plants. The EPA is collaborating with the U.S. Department of Energy to conduct this
study. Stack testing at seven plants is currently underway and the results will be
incorporated to the extent possible in the final version of this report.
In the United States, the consumption of coal accounts for approximately 25
percent of the energy consumed from all sources (U.S. DOC, 1992). In 1991, 806 million
metric tons of coal were consumed in the United States (EIA, 1993). Of this total, 87
percent (or 701 million metric tons ) was consumed by electric utilities, 12.3 percent (or
99 million metric tons) was consumed by the industrial sector, and 0.7 percent (or 5.5
million metric tons) was consumed by residential and commercial sources (EIA, 1993).
These production estimates are assigned a "high" confidence rating since they are based
on detailed studies specific to the U.S.
Derivation of emission factors is difficult due to the extremely limited data on
emission of dioxin-like compounds from coal-fired utility boilers (NATO,1988). Most
investigations of emissions from facilities in the United States have not reported the
detection of dioxin congeners at the exit to the stack (NATO, 1988). Therefore in the
development of emission factors representative of coal-fired utility boilers (coal-fired power
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plants), the reported limit of detection of the analytical method was applied as an upper-
bound to the plausibility of emissions of dioxin from the source. If it is assumed that
burning one kg of coal in a modern power plant produces an estimated 6.2 dry standard
cubic meters (dscm) of combustion gas, then the limit of detection from the study of U.S.
power plants can be used to estimate an emission factor (NATO,1988). From the reported
limit of detection of dioxin at the stack, an upper-bound emission factor for total CDD/CDF
of 3.11E-02 /yg/kg of coal combusted and an upper-bound emission factor for TEQ of
4.22E-04 //g/kg of coal combusted can be derived. If it is assumed that 700 billion kg of
coal is combusted each year by power plants in the United States, then the upper-bound
emission factors indicate an annual emission to the air of less than 2.2E + 04 grams of
total CDD/CDF and less than 3.0E + 02 grams of TEQ/yr. The emission factors are
assigned a "low" confidence rating because the stack emission of dioxin-like compounds
from coal-fired utility boilers operating in the United States has yet to be determined.
Emissions tests reported to date have not detected these compounds. The estimated
emissions must, therefore, be considered the upper-bound of possible emissions from the
source category based on available data.
3.6.18. Combustion of Polychlorinated Biphenyls (PCBs)
The accidental or intentional combustion of PCBs in incinerators and boilers not
approved for PCB burning (40 CFR 761) may produce CDDs and CDFs. At elevated
temperature, such as those in transformer fires, PCBs can undergo reactions to form CDF
and other by-products. Several accidental fires in the U.S. and Sweden which involved the
combustion of PCBs and the generation of CDDs and CDFs are discussed in Hutzinger and
Fiedler (1991b). For example, analyses of soot samples from a Binghamton, New York
office building fire detected 20//g/g of total CDDs (0.6 to 2.8//g/g of 2,3,7,8-TCDD) and
765 to 2,160 //g/g of total CDFs with 12 to 270 fjg/g of 2,3,7,8-TCDF. At that site, the
fire involved the combustion of a mixture containing PCBs (65 percent) and chlorobenzene
(35 percent). Hutzinger and Fiedler (1991b) also reported that laboratory analyses of soot
samples from a PCB transformer fire which occurred in Reims, France indicated total CDD
and CDF levels in the range of 4 to 58,000 ng/g and 45 to 81,000 ng/g, respectively.
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The use of PCBs in new transformers in the United States has been banned and
their use in existing transformers is being phased out. Because of the accidental nature of
transformer fires it is not possible to accurately estimate annual emissions from this
source.
3.6.19. Pyrolysis of Brominated Flame Retardants
The pyrolysis and photolysis of brominated phenolic derivatives and polybrominated
biphenyl ethers used as flame retardants can generate polybrominated dibenzo-p-dioxins
(BDDs) and dibenzofurans (BDFs) (Hutzinger and Fiedler, 1991 a; Luijk et al., 1992;
Watanabe and Tatsukawa, 1987). Watanabe and Tatsukawa (1987) observed the
formation of BDFs from the photolysis of decabromobiphenyl ether. Approximately 20
percent of the decabromobiphenyl ether was converted to BDFs in samples that were
irradiated with ultraviolet light for 16 hours (Watanabe and Tatsukawa, 1987).
Decabromobiphenyl ether is used as a flame retardant in resins, textiles, and paints.
Luijk et al.(1990) studied the formation of BDD/Fs during the compounding/
extrusion of decabromodiphenyl ether into high-impact polystyrene polymer at 275°C.
HpBDF and OBDF were formed during repeated extrusion cycles, and the yield of BDFs
increased as a function of the number of extrusion cycles (Luijk et al., 1990). HpBDF
increased from 1.5 to 9 ppm (in the polymer matrix) and OBDF increased from 4.5 to 45
ppm after four extrusion cycles.
Thoma and Hutzinger (1989) observed the formation of BDFs during combustion
experiments with polybutylene-terephthalate polymers containing 9 to 11 percent
decabromodiphenyl ether. Maximum formation of BDFs occurred at 400 to 600°C with a
BDF yield of 16 percent. Although Thoma and Hutzinger (1989) did not provide specific
quantitative results for similar experiments conducted with octabromodiphenyl ether and
1,2-bis(tri-bromophenoxy)ethane, they did report that BDDs and BDFs were formed.
Insufficient data are available upon which to derive annual BDD/BDF emission
estimates from this source.
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3.6.20. Carbon Reactivation Furnaces
Granular activated carbon (GAC) is an adsorbent that is widely used to remove
organic pollutants from wastewater and in the treatment of finished drinking water at
water treatment plants. Activated carbon is manufactured from the heat treatment of nut
shells and coal under pyrolytic conditions (Buonicore, 1992a). The properties of GAC
make it ideal for adsorbing and controlling vaporous organic and inorganic chemicals
entrained in combustion plasmas, as well as soluble organic contaminants in industrial
effluents and drinking water. The high ratio of surface area to particle weight (e.g., 600 -
1600 m2/g), combined with the extremely small pore diameter of the particles (e.g., 15-25
Angstroms) increases the adsorption characteristics (Buonicore, 1992a). GAC will
eventually become saturated and the adsorption properties will significantly degrade.
When saturation occurs, the GAC usually must be replaced and discarded, which
significantly increases the costs of pollution control. The introduction of carbon
reactivation furnace technology in the mid-1980s created a method involving the thermal
treatment of used GAC to thermolytically desorb the synthetic compounds and restore the
adsorption properties for reuse (Lykins et al., 1987).
The used GAC can contain compounds that are precursors to the formation of
CDDs/Fs during the thermal treatment process. The U.S. EPA measured precursor
compounds in spent GAC used as a feed material to a carbon reactivation furnace tested
during the National Dioxin Study (U.S. EPA, 1987). The total chlorobenzene content of
the GAC ranged from 150 ppb to 6,630 ppb. Trichlorobenzene was the most prevalent
species present, with smaller quantities of di- and tetra-chlorobenzenes detected. Total
halogenated organics were measured to be about 150 ppm.
The U.S. EPA has stack tested two GAC reactivation furnaces for the emission of
dioxin (U.S. EPA, 1987; Lykins et al., 1987). One facility was an industrial carbon
reactivation plant, and the second facility was used to restore GAC at a municipal drinking
water plant. The industrial carbon regeneration plant processed 36,000 kg/day of spent
GAC used in the treatment of industrial wastewater effluents. Spent carbon was
reactivated in a multiple-hearth furnace, cooled in a water quench and, stored and shipped
back to primary chemical manufacturing facilities for reuse. The furnace fired natural gas,
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and consisted of seven hearths arranged vertically in series. The hearth temperatures
ranged from 480°C to 1000°C. The spent GAC contained about 40 percent weight
moisture. The used GAC was fed to the top hearth. In the furnace, the spent carbon was
dried and the organics adsorbed onto the carbon particles were volatilized and burned in
the heated combustion atmosphere. The regenerated carbon dropped from the bottom
hearth of the furnace to a quench tank to reduce the temperature. Air pollutant emissions
were controlled by an afterburner, a sodium spray cooler, and a fabric filter. Temperatures
in the afterburner were about 930°C.
The second GAC reactivation facility tested by U.S. EPA consisted of a fluidized-
bed furnace located at a municipal drinking water treatment plant (Lykins et al., 1987).
The furnace was divided into three sections: a combustion chamber, a reactivation section
and a dryer section. The combustion section was fired by natural gas, and consisted of a
stoichiometrically balanced stream of fuel and oxygen. These expanding gases of
combustion provided heat and suspended and fluidized the carbon. Temperatures of
combustion were about 1,038°C. The reactivation section outside the combustion
chamber allowed for the complete volatilization of the heated GAC. Off-gasses from the
reactivation/combustion section were directed through an acid gas scrubber and high-
temperature afterburner prior to discharge from a stack.
The industrial GAC reaction furnace test data indicate that an average of 5.87E-02
/yg of CDD/CDF per kg of GAC incinerated may be emitted from the stack during operation
(U.S. EPA, 1987). An average of 2.98E-03 //g TEQ per kg of GAC may be released to the
air during operation. A "medium" confidence rating is given to these emission factors,
because only one industrial GAC reactivation furnace operating in the United States has
been stack tested. In the second GAC reactivation furnace tested by EPA (Lykins et al.,
1987), measurable concentrations of dioxin-like compounds were detected in the stack
emissions. When chlorine was used in pretreatment of the surface water for preliminary
disinfection prior to filtration with GAC, the 2,3,7,8-TCDD congener was seen in the
particulate stack emission discharges to the incinerator afterburner in low concentration
[0.001-0.02 parts per trillion by volume (ppt/v)]. 1,2,6,7-TCDF was detected in two out
of four stack tests in a concentration range of 0.004-0.02 ppt/v. When no chlorine was
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used to disinfect the surface water prior to filtration with GAC, no 2,3,7,8-TCDD was
detected «0.001 ppt/v). With the afterburner operating, no CDD congeners below
HpCDD were detected in the stack emissions. Concentrations of HpCDDs and OCDD
ranged from 0.001 to 0.05 ppt/v and 0.006 to 0.28 ppt/v, respectively. All congener
groups of CDFs were detected in the stack emissions even with the afterburner operating.
Total CDFs emitted from the stack averaged 0.023 ppt/v. Measurements of the individual
CDD/CDF congeners were not performed, therefore it was not possible to derive emission
factors for this facility.
The mass of GAC that is reactivated annually in carbon reactivation furnaces is not
known. However, a crude estimate, which is given a "low" confidence rating, is the mass
of virgin GAC shipped each year by GAC manufacturers. According to U.S. DOC (1990c),
48 thousand metric tons of GAC were shipped in 1987. Applying the emission factors
developed above to this crude estimate of potential GAC reactivation volume, annual
releases of 0.14 grams of TEQ and 2.8 grams of total CDD/CDF are estimated. Based on
the "medium" confidence rating assigned to the emission factor, the estimated range of
potential annual emissions is assumed to vary by a factor of 5 between the low and high
ends of the range. Assuming that the best estimate of annual emissions (0.14 g TEQ/yr)
is the geometric mean of this range, the range is calculated to be 0.06 to 0.3 g TEQ/yr.
3.6.21. Cement Kilns
Portland cement is a fine, grayish powder consisting of a mixture of four basic
materials: lime (calcareous), silica (siliceous), alumina (argillaceous), and iron (ferriferous).
Pyroprocessing in a rotary-type kiln plays a central role in fusing the basic raw materials
into cement. The raw materials are ground into fine particles and are then either
suspended in water to form a pumpable slurry (i.e., wet process) or are fed directly (i.e.,
dry process) into a rotary kiln for processing at elevated temperatures in an oxygen-
enriched atmosphere. In the rotary kiln, evaporation of the water, calcination of the
carbonate constituents, and fusion of the minerals occurs to form clinker. Clinker is a
gray-colored, glass-hard material comprised of the cement minerals, dicalcium silicate,
tricalcium silicate, calcium aluminate, and tetracalcium aluminoferrite. The clinker is then
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ground into a fine powder and mixed with gypsum to form Portland cement.
Approximately 1,575 kg of dry raw materials are needed to produce about 1000 kg of
cement clinker (Greer et al., 1992). In 1991, the last year in which data is available,
about 66 billion kg of cement clinker was produced in the United States by 212 portland
cement kilns requiring about 103 billion kg of raw materials (U.S. EPA, 1993f; Greer et
al.,1992).
Because of the relatively high combustion temperature required to produce cement
clinker (1400° to 1510°C), coal or petroleum coke are typically used as the primary fuel
to sustain combustion in the kiln. However, some cement kilns do burn hazardous liquid
and solid waste as supplemental fuel to reduce the amount of coal that is purchased. It is
estimated that 34 of the 212 existing cement kilns (i.e., 16 percent) burn hazardous waste
as supplemental fuel (U.S. EPA, 1993f). Other types of non-hazardous liquid and solid
wastes used as supplemental fuels include tires, waste oil, and wood chips. The most
common air pollution control devices (APCD) employed on rotary kilns are those intended
to control dust and particulate matter (i.e., fabric filters and/or electrostatic precipitators).
Dioxins were first detected in stack emissions from portland cement kilns in the early
1980s (U.S. EPA, 1987; Peters, 1983; Branscome et al. 1984, 1985). Dioxin was
detected only in low amounts and was thought to be caused by the co-firing of liquid
hazardous waste with conventional fossil fuels (Peters, 1983). The EPA gave this source
category a low priority for follow-up testing in EPA's National Dioxin Study conducted in
1985-1986 (U.S. EPA, 1987). Since then, the thermolytic reactions and the conditions
favoring the formation of CDDs and CDFs in combustion processes have become better
understood. (See Section 3.5). Some aspects of this theory warrant investigation into the
formation of dioxin in portland cement kilns, including:
• Some primary combustion fuels (i.e., coal and petroleum coke) and fuel
supplements (wood chips and tires) used to sustain elevated temperatures in the kiln to
form clinker may also produce aromatic hydrocarbon compounds (e.g., benzene, phenol)
that can later become chlorinated ring structures. The oxidation of HCI gas has been
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shown to provide chlorine available for ring substitution. In addition, chlorine has been
measured directly in the combustion fuels to cement kilns (EER, 1993).
• The chlorinated aromatic compounds may act as precursor molecules to the
thermalytic formation of CDD/CDFs on the active surface of carbonaceous particulates;
• De novo synthesis of CDD/CDFs on the active surface of carbonaceous
particulates in the presence of a catalytic agent (e.g., a metal ion such as copper chloride);
• Post-kiln temperatures of the combustion gases in the APCD system are within
the range of temperatures observed in laboratory studies that promote the continued
formation of CDD/CDFs (i.e., 250° to 350°C); and
• Co-firing of liquid hazardous organic wastes with coal and petroleum coke may
lead to an increase in the amount of CDD/CDFs formed in the post-combustion zone.
Currently, cement kilns that accept and burn hazardous waste as an auxiliary fuel
are required under RCRA to characterize pollutant stack emissions, including emissions of
CDD/CDFs. EPA's Office of Solid Waste is in the process of collecting and analyzing these
emission reports to determine the extent and magnitude of CDD/CDF releases and the
need for further regulation. Preliminary stack test data are available from 14 of the 34
cement kilns burning hazardous waste and from 3 of the 178 kilns not burning hazardous
waste (EER, 1993; RTI, 1993). Table 3-35 is a summary of the available emissions data.
For kilns accepting and burning hazardous waste as supplemental fuel, it appears that the
concentration of dioxin in the stack gas (grams/dscm at 7 percent 02) is highly variable.
For example, the average stack emissions of total CDD/CDF for individual kilns range from
2 to 2000 ng/dscm, a thousand-fold difference. There appears to be no consistent pattern
to the relationship of total CDD/CDFs to the estimated dioxin TEQ, indicating a wide
variability in the distribution of toxic congeners of CDDs and CDFs in the emissions. For
example, the ratio of total CDD/CDFs to the TEQ ranges from about a factor of 5:1 to a
factor of 1000:1, indicating that some kilns have a congener distribution skewed toward
the lower chlorinated more toxic congeners and others are skewed toward the higher
chlorinated less toxic congeners. Cement kilns which do not burn hazardous waste as
supplemental fuel appear to be less variable. However, this observation must be tempered
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Table 3-35. Concentrations of Total CDD/CDFs and Dioxin TEQ (grams/dscm) Measured at the Stack of Portland
Cement Kilns Burning and Not Burning Hazardous Waste As Supplemental Fuel*
1. Cement Kilns Burning Hazardous Waste
Facility
A
B
C
D
E
F
G
H
1
J
K
L
M
N
APCD
ESP
ESP
ESP
ESP
ESP
ESP
ESP
ESP
ESP
FF
FF
FF
FF
FF
Mean
Std
CDD/CDF
Emission
(g/dscm)
2.300e-07
3.260e-07
1.043e-08
5.525e-07
NA
4.118e-09
1.983e-09
6.765e-07
1.998e-06
9.779e-08
2.100e-09
2.467e-07
NA
1.677e-08
3.469e-07
5.673e-07
TEQ Emission
tg/dscm>
1 .283e-09
3.800e-09
3.178e-10
3.828e-09
4.533e-10
6.045e-10
1.750e-11
4.455e-09
4.0916-08
8.300e-1 1
1.422e-10
4.318e-08
5.702e-1 1
2.067e-10
7.096e-09
1 .490e-08
Ratio
Total/TEQ
179.3
85.8
32.8
144.3
NA
6.8
113.3
151.9
48.8
1178.2
14.8
5.7
NA
81.1
No. Of
Tests
8
4
9
2
6
6
4
2
2
1
1
1
4
2
II. Cement Kilns Not Burning Hazardous Waste
facility
O
p
Q
APCD
ESP
ESP
ESP
CDO/CDF
Emission
(fl/dscm)
NA
NA
NA
Mean
Std
TEQ
Emission
(g/dscm)
6.929e-10
3.188e-11
1.996e-09
9.068e-10
8.158e-10
NO, Of
Tests
1
2
2
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Sources: Data compiled from EER (1993) and RTI (1993).
" Notes:
1. Names and locations of tested facilities are not given in order to preserve confidentiality.
2. APCD refers to Air Pollution Control Devices.
3. (g/dscm) is grams per dry standard cubic meter measured at 20°C, 1 atm corrected to 7 percent O2.
4. No. of tests is the number of separate stack tests performed at a facility to derive the average estimate.
5. ESP is an electrostatic precipitator.
6. FF is a fabric filter.
7. CDD/CDF is the total emission of tetra- through octa- CDDs and CDFs.
8. TEQ is the dioxin toxic equivalents calculated using the International Toxic Equivalency Procedure.
9. Mean is the arithmetic average.
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by the fact that fewer of these kilns have been stack tested.
The limited emission data suggests that the average stack concentrations of
CDD/CDFs are about eight times higher among the kilns burning hazardous waste than
those that do not. As discussed below, a similar relationship was seen in the cement kiln
dust samples from these two categories of kilns. On this basis, it was decided that
separate emission factors should be developed for the kilns burning hazardous waste and
those that do not. Given the limited emission test data, especially among the kilns that do
not burn hazardous waste, clearly more testing is needed to confirm this difference in
emission factors.
National estimates of air emissions of dioxin TEQ/yr from all operating cement kilns
were made using two different methods:
1. Dioxin emissions correlate with the total mass of materials processed and
burned at the kiln to form clinker (i.e., related to the kiln throughput); and
2. Dioxin emissions correlate with the total energy content of the fuel
(including hazardous waste) used to sustain combustion in the kiln.
Although these two methods would likely generate different emission estimates if
site-specific data (i.e., throughput and energy consumption data) were available, such data
were not available for this report and, therefore, the use of generic industry average data
resulted in identical estimates.
For the first method, three values must be known in order to calculate annual dioxin
TEQ emissions: (a) the average concentration of dioxin TEQ in the stack gas
(g TEQ/dscm); (b) the average volume of combustion gas evolved per kg of material fed to
the kiln; and (c) an estimate of the total dry weight of materials processed by all operating
cement kilns (kg/yr). Average dioxin TEQ stack emission concentrations are presented in
Table 3-35 for kilns burning and not burning hazardous waste as supplemental fuel. The
averaging gave equal weighting to all tested kilns. The average dioxin TEQ stack
concentrations are 7.1 ng/dscm and 0.9 ng/dscm for kilns burning hazardous waste and
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not burning hazardous waste, respectively. A reasonable estimate of combustion gas
volume/kg of materials processed in the kiln is 1.75 dscm/kg (RTI, 1993). This approach
suggests an emission factor of 12.4 ng TEQ/kg and 1.6 ng TEQ/kg for kilns burning and
not burning hazardous waste, respectively.
Greer et. al (1992) estimated that the ratio of the dry weight of materials charged
into the kiln to the weight of dry clinker produced is 1.575:1. Therefore, if 66 billion kg of
clinker were produced by 212 cement kilns in 1991 (U.S. EPA, 1993f), then 104 billion kg
of raw materials were consumed in that year. A final assumption is that the annual
throughput of raw materials processed is roughly proportional to the number of kilns in the
class of cement kilns (i.e., the number burning hazardous waste versus the number of
facilities not burning hazardous waste). Multiplying the emission factors by the raw
material throughput yields annual emission estimates of 210 g TEQ for kilns burning
hazardous waste and 140 g TEQ for kilns not burning hazardous waste.
For the second method, it is assumed that the dioxin emissions are better
calculated on the basis of annual fuel consumption rather than the annual amount of
materials processed by the kiln. Given the diversity and mixtures of fuel types typically
used (coal, coke, liquid hazardous waste, natural gas, oil, wood chips, tires), a good
measurement of total fuel consumption is the amount of total energy consumed to
produce the clinker (U.S. EPA, 1993f). Johnson (1992) estimated that 71 trillion kcals
were consumed in the year 1991 by all operating Portland cement kilns. Dividing this
value by the total kg of raw material processed (is 104 billion kg, as reported above) yields
an average energy usage of 680 kcal/kg of raw material. Dividing this value into the
emission factors derived above (in units of ng of dioxin TEQ/kg of raw material) yields
emission factors in terms of ng of dioxin per kcal. This approach suggests an emission
factor of 2.3 pg of TEQ/kcal for kilns not burning hazardous waste and 18 pg of TEQ/kcal
for kilns which do burn hazardous waste. Finally, it is assumed that the total energy usage
can be apportioned between kilns burning hazardous waste (34 of 212 kilns) and those
that do not (178 of 212 kilns) on the basis of the number of kilns in each group.
Multiplying these energy use estimates by the energy based emission factors yields the
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following estimates of annual emissions: 210 g TEQ for kilns burning hazardous waste
and 140 g TEQ for kilns not burning hazardous waste.
Both of these methods suggest that annual dioxin emissions to air from all cement
kilns combined is about 350 grams TEQ. The estimated TEQ emission factors used to
derive this best estimate of annual TEQ emissions are given a "low" confidence rating
because the mechanisms giving rise to dioxin emissions from cement kilns are largely
unknown; very few of the existing facilities have been stack tested for emissions; and
because of the apparent high variability in the ratio of total CDD/CDFs to dioxin TEQ and
the apparent high variability in emissions between tested facilities as shown by the large
standard deviation in Table 3-35. The "production" estimate of annual raw material
throughput is given a "high" confidence rating because it is based on recent survey data.
Based on these confidence ratings, the estimated range of potential emissions is assumed
to vary by a factor of 10 between the low and high ends of the range. Assuming that the
lowest estimate of annual emissions (350 g TEQ/yr) is the geometric mean of this range,
then the range is calculated to be 110 to 1,100 g TEQ/yr.
In a recent Report to Congress (U.S. EPA, 1993f), EPA's Office of Solid Waste
establishes the factual basis for its decision making regarding the appropriate regulatory
status, under RCRA, of cement kiln dust (CKD) waste. To aid EPA in their study, the
Portland Cement Association (PCA) conducted a survey in 1991 of cement manufacturers.
Survey responses were received from 64 percent of the active cement kilns in the United
States. Based on the survey responses, EPA estimated that the U.S. cement industry
generated about 12.9 million metric tons of gross CKD and 4.6 million metric tons of "net
CKD", of which 4.2 million metric tons-was land disposed, in 1990. The material
collected by the APCD system is called "gross CKD" (or "as generated" CKD). The gross
CKD is either recycled back into the kiln system or is removed from the system for
disposal (i.e., "net CKD" or "as managed" CKD) (U.S. EPA, 1993f).
Also in support of the Report to Congress, EPA conducted sampling and analysis
during 1992 and 1993 of CKD and clinker. The purposes of the sampling and analysis
efforts were: (1) to characterize the CDD/CDF content of clinker and CKD ; (2) to
determine the relationship, if any, between the CDD/CDF content of CKD and the use of
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hazardous waste as fuel; and (3) to determine the relationship, if any, between the
CDD/CDF content of CKD and the use of wet versus dry process cement kilns. Clinker
samples from 9 kilns and CKD samples from 11 kilns (six of which burn hazardous waste)
were analyzed (U.S. EPA, 1993f).
CDD/CDFs were not detected in any of the clinker samples. Tetra- through octa-
chlorinated CDDs and CDFs were detected in the "gross CKD" samples obtained from 10
of the 11 kilns and in the "net CKD" samples obtained from 8 of the 11 kilns. The
CDD/CDF content of "gross CKD" ranged from 0.008 to 247 ng TEQ/kg and for "net
CKD" the content ranged from 0.045 to 195 ng TEQ/kg. Analyses for seven PCB
congeners were also conducted but no congeners were detected in any clinker or CKD
sample. TCLP leachate testing of the CKD samples from six kilns showed no leaching of
CDD/CDFs (detection limits ranged from 3 to 37 pg/L) except for OCDD in two samples
(110 and 170 pg/L). Statistical analysis of the results indicated that mean CDD/CDF
concentrations in "net CKD" generated by the sampled kilns burning hazardous waste are
higher (35 ng/kg) than in "net CKD" generated by the sampled facilities not burning
hazardous waste (3.0E-02 ng/kg). These calculations of mean values treated not detected
values as zero. If the not detected values had been excluded from the calculation of the
means, then the mean value for "net CKD" from kilns burning hazardous waste would
increase by a factor of 1.2 and the mean value for "net CKD" from kilns not burning
hazardous waste would increase by a factor of 1.7. One sampled kiln had CDD/CDF
concentrations more than two orders of magnitude greater than the TEQ levels found in
samples from any other kiln. If this kiln is considered to be atypical of the industry (U.S.
EPA, 1993f) and is not included in the calculation, then the mean "net CKD" concentration
for hazardous waste burning kilns decreases to 2.9 ng/kg.
From these data, an estimate of dioxin TEQ emissions to land in the form of land-
disposed "net CKD" can be made. The estimate of land-disposed CKD from the 1991 PCA
Survey, 4.2 million metric tons per year (basis year is 1990), was divided among kilns
burning hazardous waste (34 kilns) and those which do not (178 kilns) on the basis of the
number of kilns in each category. The average TEQ concentration in the net CKD from
kilns burning hazardous waste, including the potentially non-typical kiln, was 35 ng
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TEQ/kg. For kilns which do not have hazardous waste the average concentration in the
"net CKD" was 3.0E-02. Multiplying these average concentrations by the annual "net
CKD" production, yields estimates of 24 g TEQ/yr for kilns burning hazardous waste and
0.1 g TEQ/yr for kilns not burning hazardous waste, yielding a total of 24.1 g TEQ/yr for
all kilns. The "production" estimate was assigned a "high" confidence rating because it is
based on recent EPA survey data. The "emission factor" estimates are assigned a "low"
confidence rating because the sampling data upon which they are based showed high
variability among the 11 kilns sampled (out of 212 kilns in the United States). Based on
these confidence ratings, the estimated range of potential annual emissions is assumed to
vary by a factor of 10 between the low and high ends of the range. Assuming that the
best estimate of annual emissions (24.1 g TEQ/yr) is the geometric mean of this range,
then the range is calculated to be 7.6 to 76 g TEQ/yr.
3.6.22. Additional Combustion and High Temperature Sources
Although discussed as potential sources in the preceding sections, insufficient data
are available upon which to develop emission factors for the primary ferrous and primary
nonferrous metal refining/smelting industries. In addition, although emission estimates
were developed in Section 3.6.13 for diesel-powered on-highway vehicles (i.e., the largest
use of diesel fuel in the United States), because of insufficient data no estimates were
developed for off-highway transportation diesel engine fuel use (including railroad engine
fuel and fuel for agricultural machinery) or for diesel fuel use by the commercial and
industrial sectors of the economy. Also, although no estimated emissions could be
developed for residential oil, gas, and charcoal combustion because of lack of emission
rate factors, these have been identified as potential sources by Harrad et al. (1992a,
1992b) and Fiedler and Hutzinger (1991b).
3.7. RESERVOIR SOURCES
It is very difficult to estimate CDD/CDF releases that may be occurring from
reservoir sources. However, some idea of the potential magnitude of these emissions can
be gained by estimating the size of the overall reservoir. Equation 1 calculates the
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concentration of a contaminant in a reservoir given the deposition rate of the contaminant
into the reservoir and the rate of dissipation from that reservoir:
= PEP ( 1 - e* ) (Eqn< 3_
kMIX
where C is the concentration after time t, DEP is the deposition rate (in units of mass/area-
time), k is the first order dissipation rate (time"1), and MIX is the mass of the reservoir into
which DEP mixes (mass units, corresponding to area of DEP). Consider the case where
DEP has been occurring for a number of years at a steady rate. A question that might be
asked is, what is the contribution of a year's worth of deposition to the amount that is
already there. This can be estimated with a ratio of estimated concentrations C!/C2 using
Equation (1), where C, is the concentration after the number of years, and C2 is the year's
worth of deposition. Assuming DEP, MIX, and k are constant, the ratio of C,/C2 reduces
to:
~ e
(Eqn. 3-2)
1 _
where t, is the number of years that DEP has been occurring, and t2 is equal to 1 for the
one year's worth of deposition. For the sake of this discussion, if one assumes that DEP
for dioxin-like compounds has been steady since the 1940s, and one wants to evaluate a
year's worth of deposition in the 1990s, then t, equals about 50 years. A dissipation rate
of 0.0693, corresponding to a 10-year half-life was used for atmospheric deposition onto
soils for the methodologies described in Volume III. A t, of 50 and k of 0.0693 applied to
Equation (2) yields a ratio of about 14.5. This means that there would be about 14.5
times more contaminant in the reservoir than one year's contribution.
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However, the half-life of 10 years is probably too low for this exercise. This half-
life was generated from data on 2,3,7,8-TCDD applied to experimental plots as 2,4,5-T in
Agent Orange testing (Young, 1983). This might be appropriate for dissipation from a
bounded area of high soil contamination, where dissipation mechanisms such as soil
erosion, dust resuspension, or volatilization might be occurring. However, if MIX is
considered as the total reservoir of soil and surface vegetation, then losses from a
bounded area are unlikely to translate to losses from the larger system. In other words, a
more appropriate half-life for this discussion might be more like 50 years than 10 years. If
50 years is assumed in the above exercise, than the ratio increases to 36.
This analysis suggests that dioxin-like compounds already in the reservoir source
may exceed annual contributions to the reservoir source by 15 or more times. The
potential for emissions from this large source is uncertain. Dioxin-like compounds that
accumulate in deep sediments or become buried in the soil are not likely to contribute to
current emissions. However, those located near the surface could become re-entrained
into the air or water bodies.
3.8. COMPARING SOURCE EMISSIONS TO DEPOSITION ESTIMATES
As discussed in Section 3.1, several investigators have attempted to conduct
"mass balance" checks on the estimates of national dioxin releases to the atmosphere.
Basically, this procedure involves comparing estimates of the emissions to estimates of
aerial deposition. Such studies in Sweden and Great Britain have suggested that the
deposition exceeds the estimated emissions by about 10-fold. These studies are
acknowledged to be quite speculative due to the strong potential for inaccuracies in the
emission and/or deposition estimates. In addition, the apparent discrepancies could be
explained by long range transport from outside the country, resuspension and deposition of
reservoir sources, atmospheric transformations, or unidentified sources. Bearing these
limitations in mind, this procedure has been used below to compare the estimated
emissions and deposition in the U.S.
Koester and Hites (1992) measured both wet and dry deposition of CDD/CDFs at
two locations in Indiana. These measurements indicate a range of 370 to 540 ng/m2-yr on
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a total CDD/CDF basis. If perfect congener distribution is assumed for the Koester and
Hites measurements, these total deposition rates correspond to about 1 to 2 ng TEQ/m2-
yr. Based on studies of temporal trends in CDD/CDF concentrations in sediments from
Green Lake, a non-industrially impacted lake near Syracuse, New York, Smith et al. (1993)
have calculated the total CDD/CDF atmospheric deposition rate to be 375 ng/m2-yr for the
period 1986 to 1990 which is very similar to that reported by Koester and Hites (1992).
Andersson et al. (1992) estimated a deposition rate of 1 ng TEQ/m2-yr on the basis of
snow measurements in Northern Sweden.
Fernandez et al. (1992) measured the wet and dry deposition over a period of one
month at an urban/semiurban location in Great Britain. Assuming that the deposition
measured over the one month period is representative of an entire year, then the rate of
deposition is 13 ng TEQ/m2-yr (setting nondetects equal zero) or 17 ng TEQ/m2-yr (setting
nondetects at half the detection limit). Van Jaarsveld and Schutter (1992), using long
range transport modelling, estimate that national average deposition rates in Northern
European countries are in the range of 1 to 10 ng TEQ/m2-yr.
In 1992, Hiester et al. (1993) collected two month duration deposition samples in
seven urban and one rural location in Germany. The total CDD/CDF deposition rates
ranged, on an annualized basis, from 246 to 1,687 ng/m2-yr at the urban locations and
420 ng/m2-yr at the rural location. The TEQ deposition rates ranged from 3.6 to 30.3 ng
TEQ/m2-day at the urban locations and 4.4 ng TEQ/m2-day at the rural location. For these
calculations, Hiester et al. (1993) set nondetects equal to zero.
Liebl et al. (1993) reported the results of long term deposition measurements at
three locations in Germany: a rural region with some industry, a rural "background" site,
and an industrial/living area site. The deposition rates, based on 11 months of
measurement in 1992, were reported as 1.1 ng TEQ/m2-yr for the rural background site,
1.5 ng TEQ/m2-yr for the rural/industrial site (estimated from figure in the report), and 7.6
ng TEQ/m2-yr for the industrial/living area site (estimated from figure in the report).
Fiedler (1993) reports that the average deposition rate for rural areas in Germany
(defined as agriculture, forest, and water) is 4.4 TEQ/m2-yr with a range of 1.8 to 7.3 ng
TEQ/m2-yr. The estimated deposition rate in industrialized areas typically ranges from 7.3
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to 36 ng TEQ/m2-yr with even higher deposition rates (up to 1,000 ng TEQ/m2-yr) in a
small number of areas.
Broman et al. (1991) collected a two-month duration deposition sample at a remote
open coastal area in Sweden and reported a deposition rate for total CDD/CDFs of 38
ng/m2-yr. Naf et at. (1992) measured the flux of CDD/CDFs to aquatic sediments at two
remote background sites; one in the Bothnian Sea and the other in the Baltic Sea. The
measured rates for total CDD/CDFs ranged from 240 to 1,200 ng/m2-yr and for TEQ
ranged from 3 to 14 ng TEQ/m2-yr. Atmospheric deposition was presumed by the authors
to be the principal source of the measured flux because the sampling sites were located far
from coastal areas, freshwater input sources, and industrial input.
For purposes of generating a preliminary estimate of CDD/CDF deposition in the
United States, it is assumed that the deposition rate of 1 ng TEQ/m2-yr measured in
Sweden applies to Alaska (land area = 1.5 x 1012 m2). The average deposition rate for
the continental United States (land area = 7.8 x 1012m2) could be as low as 2 ng TEQ/m2-
yr (based on limited U.S. data) or perhaps about 6 ng TEQ/m2-yr (based on European data).
Based on these assumptions, total U.S. deposition can be estimated as about 20,000 to
50,000 g TEQ/yr. This range can be compared to the range of estimated annual air
emissions in the United States, 3,300 - 26,000 g TEQ/yr, as presented in Table 3-2. As
noted above however, making and interpreting such comparisons is highly speculative
considering the very limited data on emissions and deposition.
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4. LEVELS OF CDD, CDF, AND PCB CONGENERS IN ENVIRONMENTAL
MEDIA AND FOOD
4.1. INTRODUCTION
Polychlorinated dibenzo-p-dioxins (CDDs), polychlorinated dibenzofurans (CDFs),
and polychlorinated biphenyls (PCBs) have been found throughout the world in practically
all media including air, soil, water, sediment, fish and shellfish, and other food products
such as meat and dairy products. Also, not unexpectedly, considering the recalcitrant
nature of these compounds and their physical/chemical properties (i.e., low water
solubilities, low vapor pressures, and high Kows and Kocs), the highest levels of these
compounds are found in soils, sediments, and biota (ppt and higher); very low levels are
found in water and air (ppq and lower). The widespread occurrence observed is not
unexpected considering the numerous sources that emit these compounds into the
atmosphere (discussed in Chapter 3), and the overall resistance of these compounds to
biotic and abiotic transformation. (See Chapter 2.) Part-per-trillion levels of CDDs/CDFs
have been found in everyday materials that are contaminated with dust-clothes dryer lint
(2.4 to 6.0 ng TEQ/kg; vacuum cleaner dust (8.3 to 12 ng TEQ/kg); room air filters (27 to
29 ng TEQ/kg); and house furnace filter dust (170 ng TEQ/kg) (Berry et al., 1993).
Although Berry et al. (1993) only analyzed one or two samples of these materials, the
findings suggest that these compounds may be ubiquitous.
The purpose of this chapter is to provide an overview of the concentrations at
which these compounds have been found in the environment and food based on data
presented in the published literature. This literature summary is not all inclusive, but is
meant to present the reader with a general overview of values reported in the recent
literature. Only data from Government-sponsored monitoring studies and studies reported
in the peer-reviewed literature are discussed in this chapter. Data are presented as they
were presented in the original studies/reports. No attempt has been made to verify or
assess the adequacy of the quality assurance/quality control measures employed in these
studies beyond those described in the published reports. The final section of this chapter
discusses the mechanisms by which these compounds could enter the food chain.
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4.2. CONCENTRATIONS IN SOIL
Tables B-1 and B-2 (Appendix B) contain summaries of data from several of the
numerous studies in the published peer-reviewed literature regarding concentrations of
CDDs and CDFs in soil. Data on coplanar PCB congener soil concentrations were not
found in the literature; the PCB soil concentration data found in the literature were
reported as either total PCB concentrations or concentrations of Aroclor PCB mixtures.
Descriptions of several of the studies summarized in Appendix B are presented below.
4.2.1. North American Data
Soil sampled in 1987 from the vicinity of a sewage sludge incinerator was
compared with soil from rural and urban sites in Ontario, Canada, by Pearson et al. (1990).
Soil in the vicinity of the incinerator showed a general increase in CDD concentration with
increasing degree of chlorination. Of the CDFs, only OCDF was detected (mean
concentration 43 ppt). Rural woodlot soil samples contained only OCDD (mean
concentration of 30 ppt). Soil samples from undisturbed urban parkland settings revealed
only HpCDDs and OCDD, but all CDF congener groups (CI4 to CI8) were present. Those
samples showed an increase in concentration from the HpCDDs to OCDD and PeCDFs to
OCDD. The TCDFs had the highest mean value (29 ppt) of all the CDF congener groups.
Resampling of one urban site in 1988, however, showed high variability in the
concentrations of CDDs and CDFs.
Data were collected on CDD and CDF levels in soil samples from industrial, urban,
and rural sites in Ontario and some U.S. Midwestern States (Birmingham, 1990). The
levels of CDD/CDF in rural soils were primarily nondetected (ND), although the HpCDDs
and OCDD were found in a few samples. In urban soils, the tetra- through octa-congener
groups were measured for both CDDs and CDFs. The HpCDDs and OCDD dominated the
homologue profile and were two orders of magnitude greater than in the rural soils. These
soils also contained measurable quantities of the TCDDs and PeCDDs. Industrial soils did
not contain any TCDDs or PeCDDs, but they contained the highest levels of the TCDFs,
HpCDFs, and OCDF. In another study, soils from industrialized areas of a group of cities
from Midwestern and Mid-Atlantic States (Michigan, Illinois, Ohio, Tennessee,
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Pennsylvania, New York, West Virginia, Virginia) were analyzed for levels of 2,3,7,8-TCDD
(Nestrick et al., 1986). Many of the samples were taken within 1 mile of major steel,
automotive or chemical manufacturing facilities, or municipal solid waste incinerators.
Concentrations of 2,3,7,8-TCDD measured in this study ranged from ND to 9.4 ppt.
EPA conducted a 2-year nationwide study to investigate the national extent of
2,3,7,8-TCDD contamination (U.S. EPA, 1987). The results of this large study were
summarized broadly in the primary reference (i.e., the number and types of samples per
site and range of detection). The method used to analyze samples for five of the seven
"tiers" of the study had a detection limit in soil, sediment, and water of 1 part per billion
(ppb). [Each "tier" of sites is a grouping of sites with a common past or present use (e.g.,
industrialized, pristine, etc.)]. Only Tier 5 (sites where pesticides derived from 2,4,5-
trichlorophenol (TCP) have been or are being used for commercial purposes), and Tier 7
(ambient sampling for fish and soil) had detection limits of 1 ppt. Consequently, the data
from this study are not included in the tables, but some observations from this study with
regard to soil contamination are discussed below.
Soil concentrations found in most of the 100 Tier 1 and 2 sites (i.e., sites already
on or expected to be on the NPL list) were in the ppb range; although in a few sites where
concentrated 2,4,5-TCP production wastes were stored or disposed, concentrations were
as high as 2,000 parts per million (ppm). Offsite soil contamination of concern was
confirmed in 7 of the 100 Tier 1 and 2 sites, with soil concentrations in the ppb range.
Eleven of 64 Tier 3 sites (facilities and associated disposal sites where 2,4,5-TCP and its
derivatives were formulated into pesticide products) were found to have soil
concentrations exceeding 1 ppb, and in 7 of 11 sites where contamination was found,
only one or two soil samples were above 1 ppb. Fifteen of 26 Tier 5 sites (areas where
2,4,5-TCP and pesticide derivatives had been or were being used) had concentrations
above 1 ppt, and one of those had a single detection of 6 ppb. Two-thirds of all
detections at the Tier 5 sites were below 5 ppt. Three of 18 Tier 6 sites (organic chemical
and pesticide manufacturing facilities where improper quality control on production
processes could have resulted in 2,3,7,8-TCDD being introduced into the wastestreams)
had soil concentrations that exceeded the detection limit of 1 ppb, although these levels
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were limited to one or two samples per site. Seventeen of the 221 urban soil sites and 1
of the 138 rural sites from Tier 7 (background sites not expected to have contamination)
had soil concentrations exceeding 1 ppt. The highest concentration detected (11.2 ppt)
was found in an urban sample. The results from Tier 7 are consistent with the other
studies discussed above regarding soil concentrations of 2,3,7,8-TCDD in nonindustrial
settings.
4.2.2. European Data
Soil samples from rural and semi-urban sites in England, Wales, and lowland
Scotland showed a general increase in concentration from the TCDDs to OCDD, whereas
the CDF levels showed very little variation between the congener groups (Creaser et al.,
1989). Concentrations of 2,3,7,8-TCDD at those sites ranged from <0.5 to 2.1 parts per
trillion (ppt). The median values for the TCDDs to OCDD were 6.0, 4.6, 31, 55, and 143
ppt, respectively. The median values for the TCDFs to OCDF were 16, 17, 32, 15, and 15
ppt. Evaluation of soil data from urban sites in the same geographical area showed that
the mean levels for the CDD and CDF congeners were significantly greater (p<0.01) than
those for rural and semi-urban background soils (Creaser et al., 1990). Concentrations of
2,3,7,8-TCDD at the urban sites ranged from <0.5 to 4.2 ppt. The median values for the
TCDDs to OCDD were 40, 63, 141, 256, and 469 ppt, respectively. The median values
for the TCDFs to OCDF were 140, 103, 103, 81, and 40 ppt. The significantly elevated
levels of the lower congeners, together with higher overall CDD/CDF concentrations, are
indicative that local sources and short-range transport mechanisms are major contributors
of CDDs and CDFs to urban soils.
Analysis of four sites in Hamburg, Germany, contaminated by an organochlorine
pesticide manufacturing company showed patterns of CDD and CDF distribution that are
similar to the urban and industrial sites examined in England, Wales, and Scotland (Sievers
and Friesel, 1989). The study indicated that CDDs and CDFs showed a regular increase in
concentration with increasing degree of chlorination (although individual data points were
not presented). The maximum concentrations of 2,3,7,8-TCDD ranged from 900 ppt to
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874,000 ppt. The very high concentrations of 2,3,7,8-TCDD at the sites were attributed
to an admixture of wastes from 2,4,5-T production.
A soil sampling survey in Salzburg, Austria, also showed that the concentrations of
CDD/CDFs were higher in urban and industrial sites than in rural sites (Boos et al., 1992).
The total CDD content of the soils ranged from 33.7 to 1236.7 ppt for urban sites; 92.2
to 455 ppt for industrial sites; and 7.1 to 183.6 ppt for rural sites. The total CDF content
of the soils ranged from 45.6 to 260.8 ppt for urban sites; 53.0 to 355.3 ppt for industrial
sites; and 12.0 to 77.7 ppt for rural sites.
Rotard et al. (1993) measured CDD/Fs in soil samples collected from forest,
grassland, and plowland sites in western Germany. The highest mean concentration of
CDD/Fs were found in the sursoil and topsoil layers of deciduous (38.0 ng TEQ/kg dry
matter) and coniferous forests (36.9 ng TEQ/kg dry matter). Grassland and plowland sites
had mean concentrations of 2.3 ng TEQ/kg dry matter and 1.7 ng TEQ/kg dry matter,
respectively.
4.2.3. Soil Summary
Some general observations for CDD and CDF levels in soils are possible from the
data presented in the various soil studies discussed above:
• Generalizations about the prevalence of specific congeners within a congener
group are not possible.
• As the degree of chlorination increases, the concentrations increase.
Concentrations of the hepta- and octa-chlorinated congeners are generally
higher than the tetra-, penta-, and hexa-chlorinated congeners.
• Concentrations associated with industrial sites clearly are the highest, with
concentrations in the hundreds to thousands of parts per trillion.
• Concentrations in settings identified as urban are higher than those in areas
identified as rural.
Based on the above studies, 95 samples were selected as representing background
conditions in the United States. The mean TEQ level was estimated to be 8 ppt assuming
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that nondetects equal half the detection limit. Similarly, 133 background samples were
selected from the European studies and were estimated to have a mean of 9 ppt of TEQ.
4.3. CONCENTRATIONS IN WATER
Tables B-3 and B-4 (Appendix B) contain summaries of data from the limited
number of published studies regarding concentrations of CDDs and CDFs in water. Data
on coplanar PCB congener water concentrations were not found in the literature. Several
of these studies are discussed below.
4.3.1. North American Data
A survey of 49 drinking water supplies in Ontario, including supplies in the vicinity
of chemical industries and pulp and paper mills, was initiated in 1983 (Jobb et al., 1990).
As of February 1989, 4,347 congener analyses had been performed on 399 raw and
treated water samples. OCDD was detected in 36 of 37 positive results and ranged from
9 to 175 ppq in raw samples (33 positive samples) and 19 to 46 ppq in treated samples (4
positive samples). These low concentrations were found primarily in water obtained
downstream of industrialized areas in the St. Clair/Detroit River system. Concentrations of
2,3,7,8-TCDD were not detected in any sample. Because CDDs and CDFs are
hydrophobic concentrations of compounds and consequently have a tendency to sorb onto
particulate matter in water, conventional water treatment processes are expected to be
effective in removing the contaminants along with the particulates. This is substantiated
by the fact that 33 of the 37 positive results were raw water samples. Because of the
relatively low levels of CDDs detected in the samples, it is difficult to ascertain whether
the CDDs were particulate-associated or dissolved.
A survey of 20 community water systems throughout New York State was
conducted in 1986 (Meyer et al., 1989). The sampling sites were representative of the
major surface source waters in New York. They included sources receiving industrial
discharges or known to contain dioxin-contaminated fish, as well as waters in more remote
areas. TCDFs were detected in the finished water at the Lockport facility (duplicate
samples had concentrations of 2.1 and 2.6 ppq). Except for a trace of OCDF detected at
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one location, no other CDDs/CDFs were detected in finished water at any of the other 19
community water systems surveyed. Raw water sampled at the Lockport facility
contained concentrations of TCDDs (1.7 ppq) as well as TCDFs to OCDF (18, 27, 85,
210, and 230 ppq, respectively). As can be seen from the data, the CDF congener group
concentrations increased with increasing chlorine number.
4.3.2. European Data
CDDs in surface water samples collected from the Eman River in southern Sweden
generally increased in concentration from the TCDDs to OCDD; whereas the CDF levels
showed very little variation between the congener groups (Rappe et al., 1989b). In
general, however, the levels of CDFs were higher than the levels of CDDs. Concentrations
of 2,3,7,8-TCDF were 0.022 parts per quadrillion (ppq) in Jarnsjon and 0.026 ppq in
Fliseryd. The filtered water, before chlorination and distribution as drinking water, had no
detectable tetra-, penta-, or hexa-chlorinated congeners of CDDs or CDFs, but the HpCDDs
and OCDD were detected at 120 and 170 ppq, respectively.
4.3.3. Water Summary
Some general observations for CDD and CDF levels are possible from the limited
data available from the various water studies above:
• CDDs/CDFs are seldom detected in drinking water at ppq levels or higher.
• Raw water samples generally have higher concentrations of CDDs/CDFs than
finished water samples.
• The concentration of CDDs and CDFs in surface water generally increases
from the tetra-chlorinated to the octa-chlorinated congener groups.
Based on the above studies, a total of 214 samples were selected as representing
background conditions in North America. The mean TEQ level was computed as 0.0056
ppg, assuming that nondetects equal half the detection limit. It should be noted, however,
that OCDD and OCDF were the only congeners for which background data were available.
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Of the 214 samples analyzed for OCDD, 4 were positive, and 2 out of 22 samples
analyzed for OCDF were positive. No appropriate data could be found for Europe.
4.4. CONCENTRATIONS IN SEDIMENT
Tables B-5 through B-7 (Appendix B) contain summaries of data from several of the
numerous studies in the published literature regarding concentrations of CDDs, CDFs, and
coplanar PCB congeners in sediment. Several of these studies are discussed in the
following paragraphs.
4.4.1. North American Data
In sediment samples collected from estuaries adjacent to an industrial site in
Newark, New Jersey, where chlorinated phenols had been produced, the level of OCDD
was many times higher than that of 2,3,7,8-TCDD (Bopp et al., 1991). The study
indicated that there probably is a significant regional source (i.e., combustion and/or use of
a common wood preservative, pentachlorophenol) for OCDD depleted in 2,3,7,8-TCDD
relative to the local industrial source. A high correlation was found between 2,3,7,8-
TCDD and 2,3,7,8-TCDF (R^=0.87), which suggests that the industrial site was a major
source of 2,3,7,8-TCDF to the natural waters of the study area. An interesting note is
that the bottom section (108-111 cm) of one sediment core contained 2,3,7,8-TCDD at a
concentration of 21,000 ppt, the highest concentration measured in the study. This value
was consistent with deposition of that sample during the mid to later stages of active
2,4,5-T production at the site from the late 1950s to early 1960s. CDD and CDF in
Hudson River sediment samples contained primarily the higher chlorinated (CI6 to CI8) CDD
and CDF congeners (Petty et al., 1982). Concentrations of the HpCDDs and OCDD
homologues ranged from 5 to 15 ppb, and the OCDD homologue in most instances
accounted for more than half of the total CDD residue. Likewise, the HpCDFs and OCDF
occurred at the highest levels (ca. 1 ppb).
Surface sediment samples were collected from several estuaries in the United
States (Norwood et al., 1989). The sampling sites included Black Rock Harbor in
Bridgeport, Connecticut, (an industrialized urban estuary); central Long Island Sound (a
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relatively clean reference site); Narragansett Bay, Rhode Island, (where chemical industries
may have contributed to the input); New Bedford Harbor, Massachusetts, (a section of
which is a National Superfund Site because of PCS contamination); and Eagle Harbor,
Washington, (the site of a creosote wood treatment facility). The sediments in New
Bedford Harbor were reported to be more heavily contaminated with CDFs, especially with
regard to the HxCDF congeners that were greater by a factor of 40 (although individual
data points were not presented). In contrast, sediments from Eagle Harbor were
practically devoid of CDFs and showed a large increase in the HpCDD and OCDD
congeners closer to the treatment facility. Narragansett Bay and Black Rock Harbor were
similar in both concentration and distribution of CDDs and CDFs, and Black Rock Harbor
contained slightly higher levels of the tetra- to hepta-CDD and CDF congeners. Sediment
from Long Island Sound was cleaner and had a distribution of CDFs between that of
Narragansett Bay and Black Rock Harbor. Sediment with the least contamination was
collected in New Bedford Harbor, up-river from the PCB facilities; the highest OCDD
concentration (1400 ppt) was detected in Eagle Harbor.
Sediment samples from Siskiwit Lake, on Isle Royale, Lake Superior, were examined
to evaluate the atmospheric input of CDDs and CDFs to the lake (Czuczwa et al., 1984).
The water level in Siskiwit Lake is 17 meters higher than that in Lake Superior, and in
addition, there are no anthropogenic inputs in the drainage basin of Siskiwit Lake.
Consequently, the atmosphere is the only source of anthropogenic chemicals in that lake.
OCDD was most predominant, and the HpCDD and HpCDF congeners also were abundant.
The study indicated that the considerable decrease in concentration of all CDD and CDF
between 6 and 8 cm of the sediment core depth (i.e., sediment believed to have been
deposited about 1940).
Surficial sediments collected from Jackfish Bay on the north shore of Lake Superior
contained moderate concentrations of the TCDF and OCDD congeners, with trace
concentrations of other congeners (Sherman et al., 1990). The concentration of OCDD
was similar to that found in the Siskiwit Lake sediment samples. The OCDF and OCDD
profile for a sediment core collected from Moberly Bay was similar to the surficial sediment
pattern. These congener groups predominated at all depths where detectable
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concentrations occurred. In addition, low concentrations of the HpCDD and PeCDF and
HpCDF congeners were detected. The concentration profile of the HpCDF congener group
showed a relatively high value that dropped abruptly to nondetectable (< 60 ppt) below a
depth of 10 cm. This abrupt change corresponded to a section date 1973 that reflects an
operational change at the pulp mill.
A survey of surficial harbor sediments collected near a wood preserving plant in
Thunder Bay, Ontario, Canada, on the north shore of Lake Superior, found CDDs and
CDFs; the highest concentrations of which occurred at stations closest to the plant dock,
and lower concentrations at locations further from the source (McKee et al., 1990). No
CDDs or CDFs were detected below the surficial layer. TCDD and PeCDD congeners were
below analytical detection limits in all samples. However, the concentrations of the
HxCDDs to OCDD congeners increased with the degree of chlorination. The maximum
concentrations of the HxCDDs to OCDD ranged from 5,700 ppt for the HxCDDs to
980,000 ppt for the OCDD. As with the CDD distribution profile, the HxCDFs to OCDF
increased with the degree of chlorination.
Bottom surficial sediments (0-3 cm) were collected from the sedimentation basins
of Lake Ontario to assess the levels of the various PCB congeners (Oliver and Niimi, 1988).
Concentrations of 2,3',4,4',5-PeCB; 2,3,3',4,4'-PeCB; and 2,3,3',4,4',5-HxCB in the
sediment were 15, 10, and 2.1 ppb, respectively. A baseline assessment of CDDs and
CDFs was performed on the Elk River, a semi-rural area located about 25 miles northwest
of Minneapolis-St. Paul, Minnesota (Reed et al., 1990). Sediment samples were collected
from Lake Orono, a reservoir on the Elk River, and from an abandoned gravel pit. Although
none of the sediment samples contained 2,3,7,8-TCDD, the gravel pit sediments contained
measurable concentrations of TCDFs. Only one Lake Orono sample contained measurable
concentrations of 2,3,7,8-TCDF (0.31 ppt) and total TCDF (0.54 ppt). The gravel pit
samples also contained HpCDDs to OCDD and PeCDFs to OCDF. Lake Orono samples
contained HpCDDs, OCDD, and HpCDF congeners. The HpCDDs ranged from 7.3 ppt in
the lake inlet to 110 ppt in the gravel pit and the lake, near the dam. OCDD concentration
ranged from 450 ppt in the gravel pit to 600 ppt in the middle of Lake Orono. The
sediment profiles reflected combustion source influences.
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The Sheboygan River, a Wisconsin tributary to Lake Michigan, is polluted with PCBs
from the mouth to about 14 miles upstream (Sonzogni et al., 1991). That portion of the
river is a Superfund site as well as one of the Great Lakes "Areas of Concern." Sediment
cores were collected at Rochester Park, near the original source of the PCBs, about 14
miles upstream from the mouth. The PCB congeners 2,3',4,4',5-PeCB; 2,3,3',4,4'-PeCB;
and 3,3',4,4'-TCB were detected in all samples and ranged from about 5 to 1500 ppb.
The remaining coplanar PCB congeners were detected less frequently and ranged from
nondetectable to slightly over 100 ppb. The PCB congener 2,3',4,4',5-PeCB appears to be
the most common coplanar PCB in environmental samples and was found in the
Sheboygan River sediments in the highest weight percent. The eight toxic PCBs detected
in this study were present in relatively low concentrations compared to total PCBs or other
more abundant congeners.
Sediments collected from Waukegan Harbor in Lake Michigan contained the
coplanar PCB congeners 3,3',4,4'-TCB and 2,3,3',4,4'-PeCB (Huckins et al., 1988). The
percentage of 3,3',4,4'-TCB in the samples averaged (0.16 percent ± 0.15) varied by 1.4
orders of magnitude, with concentrations ranging from 13 to 27,500 ppb. The percentage
of 2,3,3',4,4'-PeCB averaged 0.66 percent ± 0.37, with concentrations ranging from 102
to 131,000 ppb. In another Lake Michigan study, sediment samples collected from Green
Bay contained concentrations of all 11 coplanar PCB congeners (Smith et al., 1990). The
dominant congeners were 2,3,4,4',5-PeCB and 2,3,3',4,4'-PeCB with concentrations of
11 and 5.8 ppb, respectively.
4.4.2. European Data
Sediment samples from the vicinity of a magnesium production plant in Norway
were analyzed for CDDs and CDFs (Oehme et al., 1989). The concentration distribution of
CDD and CDF congeners was rather homogeneous except for a slight decrease at a
sampling station further downstream of the plant. However, the deeper sediments (4-6
and 11-13 cm depth) at that site had somewhat higher levels. Another sampling station
even further downstream had concentrations that were a factor of 4 to 10 lower, thereby
indicating substantial transport of CDDs and CDFs. The TCDF congener profiles were the
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same as those for magnesium production. In addition, the PeCDF congener profiles were
very similar to those found in the wastewater.
Trapped sediments from the archipelago of Stockholm, Sweden, displayed CDD and
CDF congener distribution patterns that were very similar to those exhibited in total air and
air particulates (Rappe and Kjeller, 1987). The HpCDDs, OCDD, and HpCDF were the
dominant congener groups in the sediment.
Bottom surface sediment samples collected from the Baltic Sea showed interesting
CDD and CDF distribution patterns (Rappe et al.,1989a). The background samples, one
between the Swedish and Soviet coasts and the other between the Swedish and Finnish
coasts, contained similar levels and distribution profiles. The study indicated that the
pattern of the TCDF congeners at these sites was typical of the "incineration pattern" (i.e.,
patterns resulting from MSW incineration, car exhausts, steel mills, etc.) which also had
been found in samples of air and air particulates. However, sediment samples collected at
a distance of 4 to 30 km from a pulp mill revealed a congener distribution pattern typical
of bleaching mills. The TCDFs found in the sediment 4 km from the pulp mill contained
only two major congeners. The sediment collected 30 km from the mill displayed the
same pattern.
Surface sediments collected from 18 lake areas in central Finland were analyzed for
CDDs, CDFs, and PCBs. Although 2,3,7,8-TCDD was not detected in any samples, two
other TCDD congeners that are common and abundant in pulp mill effluents were
detected. In addition, the HxCDD to OCDD congener groups as well as the HpCDF and
OCDF congener groups not normally linked to pulp mills, also were detected. The study
suggested that these may have resulted from combustion operations in the more densely
populated and industrialized areas in south Finland. Coplanar PCBs were detected at low
background levels. The most toxic PCB congener, 3,3',4,4',5-PeCB (IUPAC No. 126), was
found only in one area located nearest to a PCB leakage point. The concentration of PCB
126 at that site was 110 ppt.
Evaluation of sediments in Hamburg Harbor in Germany revealed high
concentrations of the TCDDs through OCDD (mean concentrations of 564, 1112, 2744,
4040, and 7560 ppt, respectively) and the TCDFs through OCDF (mean concentrations of
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526, 2980, 4106, 2358, and 2712 ppt) (Gotz et al., 1990). The average concentration of
2,3,7,8-TCDD was 375.3 ppt. The high concentrations of 2,3,7,8-TCDD, especially in the
Moorfleeter Canal and the Auserer Vering Canal, were attributed to discharges from an
organochlorine pesticide manufacturing plant. The patterns of 2,3,7,8-TCDD and the other
HpCDD congeners are characteristic of the patterns resulting from the production of 2,4,5-
T and 2,4,6-trichlorophenol. In addition, the pattern of the HpCDF congeners can be
linked to emissions from thermal processes employed by chemical industries in the
production of chlorinated organic chemicals. The high concentrations of hepta- and
octa-CDDs/CDFs may also be the result of other industrial combustion processes in the
Hamburg area.
4.4.3. Sediment Summary
Some general observations for CDD and CDF levels are possible from the data
presented in the various sediment studies above:
• The CDD and CDF congener distribution patterns in sediment generally
follow those exhibited by the contaminant source.
• The concentration of hexa- to octa-chlorinated CDD and CDF congeners in
sediment is usually the result of industrial processes and generally increases
with the degree of chlorination, but decreases uniformly with distance from
the source.
Based on the above studies, seven samples were selected as representing
background conditions in the United States. The mean TEQ level was computed as 3.9
ppt assuming that nondetects equal half the detection limit. Similarly, 20 background
samples were selected from the European data with a mean of 34.9.
4.5. CONCENTRATIONS IN FISH AND SHELLFISH
Tables B-8 through B-10 (Appendix B) contain summaries of data from the
numerous studies in the published literature regarding concentrations of CDDs, CDFs, and
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coplanar PCB congeners in fish and shellfish. PCB congener data were found only for
North American species. It should be noted that some studies reported fish concentrations
on a whole weight basis and others reported concentrations for fish fillets. Whole weight
concentrations were converted to fillet concentrations assuming that the fillet contained
one-half the concentration of the whole fish (USEPA 1990; Branson et al. 1985). This
was necessary for estimating human exposures because it is assumed that fish fillets, and
not whole fish, are ingested by humans.
4.5.1. North American Data
A large quantity of fish data were collected as part of EPA's National Study of
Chemical Residues of Fish (NSCRF), more commonly referred to as the National
Bioaccumulation Study, during the period of 1986 to 1989 (U.S. EPA, 1992). Based on
these data, several summaries were prepared and are presented here. Tables B-8 and B-9
include the dioxin and furan data collected as part of the National Bioaccumulation Study.
Samples were collected from a wide variety of sites across the United States, including
314 sites thought to be influenced by point or nonpoint sources and 35 sites identified as
relatively free of influence from point and nonpoint sources. This latter group of sites can
be characterized as background per the definition used in this document. Background data
are presented in Table 4-1. Table B-10 includes similar data for the various PCB congener
groups from 362 National Bioaccumulation Study sites. Because the specific PCB
congeners could not be identified, it is not known what percentage of these concentrations
represent the PCBs identified as dioxin-like. Twenty of these sites were identified as
background sites. The total PCB, all 209 congeners, mean concentration for these
background sites was 46,900 ppt. Because the dioxin-like PCBs consist of only 11 of the
209 possible PCB congeners, it may be that they are a small percentage of the total.
However, only congener specific analysis can ultimately confirm this. As discussed at the
end of this section (in 4.5.3), this study was selected as the best basis for estimating
background fish levels in the United States.
Samples of striped bass, blue crabs, and lobsters collected from Newark Bay and
the New York Bight all contained high levels (up to 6,200 ppt) of 2,3,7,8-chlorine
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Table 4-1. Background Data from the National Bioaccumulation Study
Congener
2,3,7,8-TCDD
2,3,7,8-TCDF
1,2,3,7,8-PeCDD
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
Tot HxCDDs
Tot HxCDFs
No* of
Background
. Site* •'%
34
34
33
34
34
30
29
Concentration
Range8 (pg/g)
0.06 - 2.26
0.10- 13.73
0.15-2.67
0.10- 1.90
0.10- 1.39
ND-3.57
ND - 2.59
Mean ;
Cone.*;
{pg/gj
0.56
1.61
0.77
0.43
0.50
0.39
0.22
Standard:
Deviation1!
(pg/g)
0.38
2.51
0.54
0.31
0.36
0.8
0.66
Median
Cone.*
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substituted tetra- and penta-CDDs and CDFs (Rappe et al., 1991). The levels of 2,3,7,8-
TCDD were higher than any other New Jersey samples, and the highest sample in this
study may be the highest level of 2,3,7,8-TCDD ever reported for aquatic animals. The
crustaceans resembled one another in congener pattern. Specifically, they all contained
both a large number and large amounts of CDD and CDF congeners in addition to the
2,3,7,8-chlorine substituted compounds. The striped bass samples, on the other hand,
contained primarily the 2,3,7,8-chlorine substituted congeners.
Carp, catfish, striped bass, large mouth bass, and lake trout were collected from
sites in the Hudson River and the Great Lakes Basin that were contaminated with industrial
chemicals or contained known or suspected levels of PCBs (Gardner and White, 1990).
The congener 2,3,7,8-TCDF was detected in 12 fish at levels that ranged from
3 to 93 ppt. A 2,3,7,8-chlorine substituted PeCDF was detected in 14 fish at levels
ranging from 4 to 113 ppt. An interesting observation in this study was that 2,4,6-
chlorine substituted CDFs were detected in four fish samples, suggesting that those fish
may have been exposed to chlorinated phenols. The study indicated that the 2,4,6-
chlorine substituted CDFs occurred in the fish at levels similar to those of the 2,3,7,8-
chlorine substituted CDFs, but with less frequency.
Samples of lake trout or walleye collected from each of the Great Lakes and Lake
St. Clair were analyzed for CDDs and CDFs (De Vault et al., 1989). CDF and CDD
concentrations in lake trout were substantially different for each lake and between sites in
Lake Michigan, probably reflecting differences in types and amounts of loadings to the
lakes. In all of the sampling sites except Lake Ontario, 2,3,7,8-TCDF was the dominant
CDF congener in lake trout and ranged from 14.8 ppt in Lake Superior to 42.3 ppt in Lake
Michigan. In Lake Ontario, the dominant congener in lake trout was a 2,3,7,8-chlorine
substituted PeCDF. The distribution of CDF congeners in the Lake Erie walleye was very
similar to that of the lake trout from Lake Superior. With regard to CDDs, the
concentrations of 2,3,7,8-TCDD ranged from 1 ppt in Lake Superior to 48.9 ppt in
Lake Ontario. With the exception of Lake Ontario, the dominant CDD congener was a
2,3,7,8-chlorine substituted PeCDD. A 2,3,7,8-chlorine substituted HxCDD also
contributed significantly to the total CDD concentrations. As with CDFs, the distribution
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of CDD congeners in the Lake Erie walleye was very similar to that of the lake trout from
Lake Superior.
In another study, CDDs and CDFs were measured in four species of salmonids (lake
trout, coho salmon, rainbow trout, and brown trout) collected from Lake Ontario (Niimi and
Oliver, 1989a). Levels of 2,3,7,8-TCDD in whole fish ranged from 6 to 20 ppt, and the
HxCDD congener group was most dominant in all fish. High levels of OCDD also were
detected in lake trout and coho salmon, but not in rainbow trout or brown trout. Although
the total CDF levels were about 25 percent lower than the total CDD concentrations, the
levels of 2,3,7,8-TCDF (which was the dominant component of the TCDF congener group)
were the same range as 2,3,7,8-TCDD (6 to 20 ppt). However, the study suggested that,
although collection sites can influence chemical levels and congener composition,
comparisons of chemical levels and congener frequencies may not be suitable because of
differences resulting from localized factors. The study also indicated that the importance
of the various CDD and CDF congeners can differ with location (i.e., the same species of
fish collected at different locations in a study area may reveal that the most common
congener is different at each site).
Travis and Hattemer-Frey (1991) evaluated data generated as part of the National
Dioxin Study regarding 2,3,7,8-TCDD concentrations in fish. The fish were collected from
304 urban sites in the vicinity of population centers or areas with known commercial
fishing activity, including sites from the Great Lakes Region. Data from that study
indicated that concentrations of 2,3,7,8-TCDD in whole fish from urban sites ranged from
nondetectable to 85 ppt. In addition, only 29 percent of the fillets from urban sites had
detectable levels of 2,3,7,8-TCDD, with a geometric mean concentration of 0.3 ppt.
Whole fish samples from the Great Lakes Region had higher 2,3,7,8-TCDD levels than fish
from urban areas (e.g., 80 percent vs 35 percent detectable levels). In the Great Lakes
Region, 2,3,7,8-TCDD concentrations in whole fish samples ranged from nondetectable to
24 ppt, with a geometric mean of 3.8 ppt. These levels were 10 times higher than the
concentration in whole fish from urban areas. Likewise, the mean concentration of
2,3,7,8-TCDD in Great Lakes Region fish fillets (2.3 ppt) was about seven times higher
than the levels in the fillets from urban areas (0.3 ppt). As with the whole fish samples,
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fish fillet samples from the Great Lakes Region had higher 2,3,7,8-TCDD levels than fillets
from background urban areas (e.g., 67 percent vs 29 percent detectable levels).
Comparable levels of 2,3,7,8-TCDD were detected in whole bottom feeders and predators
from the Great Lakes Region.
Samples from all trophic levels in the Lake Ontario ecosystem were analyzed for
PCS congeners (Oliver and Niimi, 1988). Analysis revealed that the PCB concentration
increased from water to lower organisms to small fish to salmonids, demonstrating the
classical biomagnification process. In addition, the chlorine content of the PCBs increased
at the higher trophic levels. PCBs with the highest chlorine content (57 percent) were
found in sculpin, small bottom-living fish that feed on benthic invertebrates. The TrCBs
and TCBs comprised a much higher percentage of the PCBs in the lower trophic levels than
in salmonids and small fish. The percentage of PeCBs and OCPB in all samples was fairly
uniform, but the HxCBs and HpCBs comprised a much larger fraction of the PCBs in the
small fish and salmonids than in the lower trophic levels.
A study regarding the distribution of PCBs in Lake Ontario salmonids (brown trout,
lake trout, rainbow trout, and coho salmon) showed that the PeCBs and HxCBs were
dominant in all species (Niimi and Oliver, 1989b). The 10 most common PCB congeners
represented about 52 percent of the total content and did not appear to be influenced by
species or total concentration. The homologues observed averaged approximately 56
percent chlorine by weight in whole fish and muscle. The analysis of the chlorine content
suggested that the more persistent congeners tend to behave as a homogeneous mixture
instead of as individual congeners.
4.5.2. European Data
Evaluation of fish in the Baltic Sea (Gulf of Bothnia) and northern Atlantic Ocean in
the vicinity of Sweden revealed that concentrations of CDDs and CDFs in herring from the
Atlantic Ocean were lower than those in the Gulf of Bothnia (Rappe et al., 1989b).
Detectable levels of 2,3,7,8-TCDD in salmon were found in both wild homing (4.6 to 19
ppt) and hatchery-reared (0.2 to 0.3 ppt) varieties in the Gulf of Bothnia. In addition,
concentrations of the same representative congeners of the 05 to Clg CDD and CDF
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congener groups found in herring were found in both varieties of salmon. Levels of those
congeners in the wild salmon, however, were five to ten times higher than the herring
levels, while the levels in the hatched salmon essentially were the same as in the herring
samples. Perch collected at a distance of 1-6 km from a pulp mill in the southern part of
the Gulf of Bothnia contained 2,3,7,8-TCDD and 2,3,7,8-TCDF; the levels were higher in
the samples collected closer to the pulp mill. These two compounds have been identified
in bleaching effluents from pulp mills as well as in bleached pulp. Arctic char collected
from Lake Vattern, a popular fishing lake in southern Sweden, contained levels of 2,3,7,8-
TCDD (6.5 to 25 ppt), 2,3,7,8-TCDF (21 to 75 ppt), and representative congeners of the
PeCDD and PeCDF homologues. There was a good correlation between the weight of the
fish and the levels of CDDs and CDFs. The main general pollution sources of the long,
deep, narrow lake are two pulp mills.
Fish (cod, haddock, pole flounder, plaice, flounder, and eel), mussels, and edible
shrimps from a fjord area contaminated by wastewater from a magnesium factory in
Norway were analyzed for CDDs and CDFs (Oehme et al., 1989). Certain magnesium
production processes can result in the formation of substantial amounts of CDDs and CDFs
as byproducts. The congener pattern of CI4 and CI5 CDDs and CDFs released in
wastewater during the magnesium production process is very characteristic and is
dominated by congeners with chlorine in the positions 1,2,3,7 and/or 8. Fish and
shellfish differ in their ability to bioconcentrate CDD and CDF congeners. For example,
fish generally only concentrate the most toxic 2,3,7,8-substituted congeners, whereas
shellfish can usually concentrate most of the congeners. Nearly all congeners were
present in the shrimp and mussel samples. Although these organisms displayed the very
characteristic PeCDF congener pattern of the magnesium production process, some
deviations were found in the TCDF congener distribution within those species. For fish,
the concentrations of CDDs and CDFs are dependent on the exposure level, fat content,
living habit, and the species degree of movement. The highest CDD and CDF levels were
found in comparatively high fat-content bottom fish collected close to the source. Cod
and haddock, lower fat-content nonstationary fish, had much lower concentrations, even
in the vicinity of the magnesium production factory. An interesting note is that the main
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stream of the fjord follows the west coast; subsequently, cod and eel samples collected
along the west coast of the fjord had considerably higher levels of CDDs and CDFs than
those collected from the eastern fjord entrance. Similarly, the level of 2,3,7,8-TCDD in
mussels decreased by one order of magnitude from the vicinity of the magnesium
production factory to the outer region of the fjord system.
Brown trout, grayling, barbel, carp, and chub collected in the Neckar River in
southwest Germany contained much higher levels of 2,3,7,8-TCDF than in eels collected
from the same river and the Rhine River (Frommberger, 1991). In addition, eels from both
rivers showed very similar patterns for CDD and CDF congener distribution, whereas the
patterns of CDD and CDF distribution generally showed some degree of difference among
the other fish collected from the Neckar River. Perch and bream collected from various
locations in the vicinity of Hamburg Harbor, however, showed similar patterns in the
distribution of the CI4 to CIQ CDD and CDF congener groups (Gotz et al., 1990). In
general, the levels of CDFs were higher than the level of CDDs in these fish, especially
with regard to the TCDFs to HxCDFs. Pooled samples of eels collected at six different
localities in the Netherlands contained low levels of CDDs and CDFs, the major congeners
of which were 2,3,7,8-chlorine substituted (Van den Berg et al., 1987). The
concentrations of the various congeners identified in the eel samples ranged from 0.1 to
9.1 ppt. The sample with the highest concentration of 2,3,7,8-TCDD (9.1 ppt) was
collected from Broekervaart in a location that was not far from a chemical waste dump
that contained high concentrations of the same congener.
4.5.3. Fish Summary
Some general observations for CDD and CDF levels are possible from the data
presented in the various fish and shellfish studies above:
• Fish and shellfish differ in their ability to bioconcentrate CDD and CDF
congeners. Fish generally concentrate the most toxic 2,3,7,8-substituted
congeners, but shellfish can usually concentrate most congeners.
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• For fish, the concentrations of CDDs and CDFs are dependent on the
exposure level, fat content, living habits, and the degree of movement of the
species. Comparatively high fat-content bottom fish collected close to the
contaminant source generally have the highest CDD/CDF levels, whereas
lower fat content, nonstationary fish have much lower concentrations, even
in the vicinity of the contaminant source.
• The National Dioxin Study indicated that the levels of 2,3,7,8-TCDD in fish
from the Great Lakes Region were higher than those from urban areas.
Comparable levels were detected in whole bottom feeders and predators
from the Great Lakes Region.
• With regard to PCBs, concentrations increase from water to lower organisms
to small fish to salmonids, and the chlorine content of the PCBs increase at
the higher trophic levels.
The background fish data collected as part of EPA's National Bioaccumulation
Study (EPA, 1992) were selected as the best basis for identifying background levels in
U.S. fish. Sixty fish samples were collected from fresh and estuarine water at a total of
34 sites where no obvious industrial sources were present. The average TEQ (assuming
zero for the nondetects) was 0.59 ppt, and 1.2 ppt (assuming half the detection limit for
the nondetects). In the original study, some of the samples were analyzed on a whole
body basis and others on a fillet basis. However, for purposes of this document, whole
body data were converted to a fillet basis. All concentrations were expressed on a wet
weight basis. This information is based on the report and clarifications provided via a
personal communication from Annette Huber, Office of Water, to John Schaum, Office of
Research and Development, May 17, 1993. Several points should be considered in using
these estimates to assess human exposure:
• The National Bioaccumulation Study data were derived from fresh and
estuarine water fish and, therefore, are not representative of open ocean
fish. Some types of open ocean fish such as tuna and sword fish are
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commonly eaten. The cod and haddock data from Schecter et al. (1993)
could be representative of these species. (See discussion in Section 4.6.2.)
These data showed a range of 0.023 to 0.13 ppt. Presumably, the
contaminant levels in open ocean fish are lower than fresh water and
estuarine fish because they live in waters farther from dioxin sources.
• Whole fish contaminant levels are normally twice as high as fillets, which is
generally considered the edible portion. However, some small fish and shell
fish, such as clams, are typically eaten whole.
• These "background" samples may not be representative of what many
individuals consume. EPA (1992) found an average of 11 ppt of TEQ across
all 314 locations sampled. Even though these other locations were near
industrial point sources, recreational or subsistence fishermen from local
populations may consume fish from these waters.
• Market basket surveys would probably provide the best information on
dioxin levels in fish commonly consumed by the general population. Data of
this type were provided by Schecter et al. (1993). As discussed in Section
4.6.2., this study analyzed five fish collected from a supermarket and found
an average of 0.05 ppt of TEQ. These data may mean that fish exposure
levels are lower than the value selected here as representative of background
levels (i.e., 1.2 ppt). However, only a limited number of samples were
analyzed. Also the fish samples represent ocean species, whereas the
National Bioaccumulation Study sampled freshwater and estuarine fish.
4.6. CONCENTRATIONS IN FOOD PRODUCTS
Dietary intake is generally recognized as the primary source of human exposure to
CDD/Fs (Rappe, 1992). Several studies have estimated that over 90 percent of the
average daily exposure to CDD/Fs are derived from foods (Rappe, 1992; Henry et al.,
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1992; Fiirst et al., 1991). CDD/Fs in fatty foods such as dairy, fish, and meat products
are believed to be the major contributors to dietary exposures (Rappe, 1992; Henry et al.,
1992). Travis and Hattemer-Frey (1991), using a fugacity model, estimated that the food
chain, especially meat and dairy products, accounts for 99 percent of human exposure to
2,3,7,8-TCDD.
Analysis of trace levels of CDD and CDF congeners in food has in the past been
hindered by lack of sensitive analytical detection methods, extraction difficulties from the
high-lipid content food products in which these chemicals are most often found, and the
presence of other potentially interfering organochlorine compounds. As the analytical
difficulties associated with detecting CDD and CDF congeners at ppt levels or lower are
overcome (Firestone, 1991), more food data should be generated.
Tables B-11 and B-12 (Appendix B) contain summaries of data from the recent
published literature regarding concentrations of CDDs and CDFs in food products. Most of
the selected studies investigated "background" levels of CDDs and CDFs rather than
studies targeted at areas of known contamination. Table B-13 contains a summary of PCB
congener concentrations in food products.
The studies summarized in Tables B-11 and B-12 primarily examined CDD and CDF
levels in products of animal origin (i.e., fish, meat, eggs, and dairy products). Because of
their lipophilic nature, CDDs and CDFs are expected to accumulate in these food groups.
The data in the tables indicate that CDDs and CDFs are found at levels ranging from the
intermediate ppq up to the low ppt range. As expected, the highest levels reported are
those measured in foods with high animal fat content. The highest reported congener
concentrations are for the HpCDDs and OCDD. In general, for the less-chlorinated
congener groups (i.e., CI4 - Clg), the CDF levels measured were larger than the CDD levels
but were still within an order of magnitude. The situation is reversed for the CI7 and CI8
congener groups.
4.6.1. Migration of CDD/CDF from Paper Packaging Into Food
In the past, low levels of CDDs and CDFs have been detected in bleached paper.
(See discussion in Chapter 3.) Because bleached paper is sometimes used for food
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packaging, concern has been expressed that CDD/Fs may migrate from the paper into the
food.
Using refined and highly sensitive analytical methods, LaFleur et al. (1990)
observed the migration of 2,3,7,8-TCDD; 2,3,7,8-TCDF; and 1,2,7,8-TCDF from bleached
paper milk cartons into whole milk. After 12 days of exposure, 6.7 percent of the
2,3,7,8-TCDD; 18 percent of the 2,3,7,8-TCDF; and 13 percent of the 1,2,7,8-TCDF in
the milk carton leached into the milk. The concentrations of the three congeners in milk
were 8.5, 110, and 49 pg/kg for 2,3,7,8-TCDD; 2,3,7,8-TCDF; and 1,2,7,8-TCDF,
respectively. [Note: These data are not reported in Appendix B; only data for raw milk are
reported.]
The study results reported by LaFleur et al. (1990) were performed by the National
Council of the Paper Industry for Air and Stream Improvement (NCASI) at the request of
the U.S. Food and Drug Administration (FDA) as part of a cooperative Federal agency
effort to assess the risks posed by dioxin contamination of paper products (i.e., the Federal
Interagency Working Group on Dioxin-in-Paper). In addition to assessing the migration of
CDDs and CDFs from milk cartons, studies were also conducted to assess the extent of
CDD/CDF migration into food from coffee filters, cream cartons, orange juice cartons,
paper cups for hot beverages, paper cups for soup, paper plates for hot foods, dual
ovenable trays, and microwave popcorn bags. Migration of CDD/Fs from the paper into
food was observed in all studies.
The FDA report presented data on direct measurements in these paper articles,
showing TCDD and TCDF levels in the 1 - 13 ppt range. These levels were similar to the
levels measured in bleached wood pulp which averaged about 8 ppt at the time of the
study. As discussed in Section 3.2, the paper industry has made process changes that
they expect have generally reduced dioxin levels in bleached paper pulp to less than 2 ppt
of TEQ. Similar or lower levels could be expected in final paper products. NCASI reports
that essentially no detectable migration of dioxin to milk occurs from cartons at these
levels.
The results of these migration studies and an assessment of the risks to the general
population posed by migration from paper are addressed in detail in U.S. EPA (1990a).
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The CDD/CDF levels currently found in food due to any leaching of dioxin-like compounds
from paperboard containers are expected to be significantly lower than those reported in
U.S. EPA (1990a) because of process changes implemented by the pulp and paper
industry to reduce formation of CDDs and CDFs.
4.6.2. U.S. Food
The published data on measured levels of CDDs, CDFs, and dioxin-like compounds
in U.S. food products have generally come from studies of a specific food product(s) in a
specific location(s) rather than from large survey studies designed to allow estimation of
daily intake of the chemicals for a population. For example, CDD/Fs are not routinely
monitored in the U.S. Food and Drug Administration's (FDA) Surveillance Monitoring
Program for domestic and imported foods (conversation between Dr. S. Page, FDA, and G.
Huse, Versar, Inc., February 8, 1993) nor are they routinely monitored by the U.S.
Department of Agriculture (USDA) in the National Meat and Poultry Residue Monitoring
Program (conversation between Dr. E. A. Brown, USDA-FSIS, and G. Schweer, Versar,
Inc., February 8, 1993).
However, USDA has developed some site-specific, though dated (late 1970s), CDD
monitoring data. These efforts were in response to a decline in general health noted by
inspectors in several cattle herds in Michigan. Wood products in the local barns and other
cattle holding premises, presumed to be treated with pentachlorophenol (PCP), were
suspected as the cause of this health decline (Buttrill et al., no date; Tiernan et al., 1978).
PCP was suspected to contain trace CDD and CDF levels as manufacturing contaminants
at that time. In response to this incident, two national investigations were performed by
USDA. The first study involved the analysis of peritoneal adipose and liver samples
collected from beef cattle in 23 States (Tiernan et al., 1978), while the second study
involved the analysis of adipose tissue samples (body region not specified) collected from
dairy cattle in 30 States-neither study specified the cattle breeds for any sample. HxCDD,
HpCDD, and OCDD were screened for in the analyses of samples from each study. In the
beef cattle study (Tiernan et al., 1978), 220 samples were analyzed: 189 peritoneal
adipose samples and 31 liver samples. No residues were detected in any liver samples. A
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total of 19 (i.e., 10 percent) of the 189 adipose samples were found to positively contain
HxCDD, HpCDD, or OCDD levels >0.10 ppb, while 56 (i.e., 30 percent) contained levels
<0.10 ppb that were detectable based on the signal-to-noise ratio of the analytical
instrumentation. OCDD accounted for the majority of the samples that positively
contained CDDs (i.e., 17 or 9.0 percent) while only 3 samples contained HxCDD and 2
samples contained HpCDD residues, respectively. A total of 358 adipose samples were
analyzed in the dairy cattle study (Buttrill et al., no date). Nine samples (i.e., 2.5 percent)
positively contained CDD levels >0.19 ppb or the "level of reliable measurement", while
another 30 samples (i.e., 8.4 percent) contained CDD levels that were identifiable yet
below the "level of reliable measurement" (i.e., not positively identified due to low
concentration levels). As with the beef cattle study results, OCDD accounted for the
majority (eight) of positive samples. HpCDD was identified in only a single sample that
also contained OCDD. HxCDD was identified as well in only a single sample. The data
from the USDA studies are not useful for estimating CDD/F exposure for two reasons.
First, the samples were analyzed for only 3 of the 17 CDD/F congeners with dioxin-like
toxicity, and these were reported on a homolog basis rather than a congener-specific
basis. Second, the limit of detection was at or above 0.1 ppb or 100 ppt. Background
levels for individual congeners appear to be much less than 100 ppt. For example, the
highest congener levels in beef fat analyzed by Furst et al. (1990) were 5.4 ppt for OCDD.
FDA has also conducted some limited analyses for the higher-chlorinated dioxins in
market basket samples collected under FDA's Total Diet Program (Firestone et al. 1986).
Food samples found to contain PCP residues >0.05//g/g were analyzed for 1,2,3,4,6,7,8-
HpCDD and OCDD. Also, selected samples of ground beef, chicken, pork, and eggs from
the market basket survey were analyzed for these dioxin congeners, regardless of the
results of PCP residue analysis. A total of 16 ground beef samples, 18 pork samples, 16
chicken samples, and 17 eggs samples with no PCP contamination were collected
between 1979 and 1984 at various locations throughout the United States and analyzed
for 1,2,3,4,6,7,8-HpCDD and OCDD. No dioxin residues were detected in any of the
ground beef or egg samples. OCDD was observed at detectable concentrations in only 2
of the 18 pork samples (27 ppt 53 ppt) and 2 of the 16 chicken samples (29 ppt, 76 ppt).
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One chicken sample with PCP residues >0.05 //g/g had detectable residues of both
1,2,3,4,6,7,8-HpCDD (28 ppt) and OCDD (252 ppt). Egg samples from Houston, Texas
and Mesa, Arizona with PCP residues >0.05//g/g had detectable 1,2,3,4,6,7,8-HpCDD
levels ranging from 21 ppt to 588 ppt, and OCDD levels ranging 80 ppt to 1610 ppt.
These levels were attributed to local PCP contamination (Firestone et al., 1986). Milk
samples contaminated with PCP at levels ranging from 0.01 //g/g to 0.05 /yg/g PCP
contained no detectable dioxins. It should be noted that these food residue data were not
used in this assessment of dioxin exposures in the United States because the reported
limits of detection (10 to 40 ppt) for the FDA analyses were considerably higher than the
levels of dioxins observed in foods from more recent studies. Also, the study only
analyzed for residues of 2 of the 17 toxic CDD/CDF congeners. Finally, the study
focussed on samples with PCP contamination and, therefore, was not generally
representative of background exposures.
The primary sources of information on background levels of CDD/Fs in U.S. foods
are studies conducted by the California Air Resources Board (CARB), the results of
background analysis from the NCASI study (Stanley and Bauer, 1989; LaFleur et al., 1990)
and Schecter et al. (1993). Each of these three studies is summarized below.
CARB collected multiple samples of seven types of foods from commercial food
sources in two urban areas of California (Stanley and Bauer, 1989). Foods were collected
randomly, but an emphasis was placed on food stuffs of California origin (Stanley and
Bauer, 1989). The types of food stuffs included saltwater fish, freshwater fish, beef,
chicken, pork, milk, and eggs. A total of 210 samples were collected in Los Angeles (30
individual samples of each of the 7 types of foods), and 140 samples were collected in
San Francisco (20 individual samples of each of the 7 types of foods). Food items were
composited before chemical analysis to obtain a sample that was representative of average
levels of PCDDs and PCDFs in the food stuffs, increase the probability of detection, and
reduce the cost of chemical analysis. Samples were composited separately for each type
of food stuff, within each geographical area. Each composite sample contained 6 to 10
individual food samples, and 5 to 8 composite samples were analyzed for each food type.
Beef (ground beef), pork (bacon), and chicken samples were analyzed on a lipid weight
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basis, but were subsequently converted to a wet weight basis, for the purposes of this
report, by multiplying the lipid weight concentration of CDD/CDFs by the fraction of fat
contained in the food product of interest. Milk and fish samples were also analyzed on a
lipid weight basis. Egg samples were analyzed for CDD/CDFs on a wet weight basis. The
CARB data are summarized in Table 4-2.
The NCASI study (as described by LaFleur et al., 1990; and Henry et al., 1992)
collected random food samples directly from the shelves of grocery stores located in the
southern, midwestern and northwestern regions of the United States. The samples were
analyzed for 2,3,7,8-TCDD and 2,3,7,8-TCDF. These data are summarized in Table 4-3.
Schecter et al. (1993) conducted a complete congener analyses of 18 food samples
collected directly from a supermarket in Binghamton, New York in early 1990. The
samples included five fish, three types of beef (ground beef, beef sirloin tip, and beef rib
steak), one chicken drumstick, one porkchop, one lamb, one ham, one bologna, one heavy
cream, and four types of cheese. The following ranges of TEQ levels on a whole weight
basis were found: fish: 0.01 - 0.13 ppt; meat: 0.03 - 1.5 ppt; and dairy products: 0.04 -
0.7 ppt. These data are summarized in Table 4-4.
Beef and Pork
Background TEQ concentrations of CDD/Fs in beef/veal and pork were estimated
using data from eight CARB samples (Stanley and Bauer, 1989), three NCASI background
samples (LaFleur et al., 1990), and three samples from Schecter et al. (1993). The CARB
and Schecter et al. samples were analyzed for 16 2,3,7,8-substituted CDD/F congeners;
the NCASI samples were analyzed for 2,3,7,8-TCDD and 2,3,7,8-TCDF only. At least one
congener was detected in 13 of the 14 composite beef samples. One sample had no
detectable congeners. The congeners most frequently detected in beef/veal were
1,2,3,4,6,7,8-HpCDD and OCDD, and only one congener was not detected in any of the
samples. For the purposes of this report, the total whole weight TEQ for beef was
calculated by assuming that the lipid content of beef was 19 percent and by using one-half
the detection limits to represent the concentration of nondetectable CDD/F congeners in
the samples. Using this methodology, the total background TEQ was estimated to be 0.48
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Table 4-2. Summary of Dioxin/Furan Data Collected in the California State Air Resources Board Study
Congener
2,3,7.8-TCDD
1,2,3.7,8-PeCDD
1 ,2,3.4.7,8/1 ,2,3,6,7.8-HxCDD
1.2,3,7,8,9-HxCDD
1.2.3.4,6,7,8-HpCDD
OCDD
2,3,7,8-TCDF
1 ,2,3.7.8-PeCDF
2,3,4,7,8-PeCDF
1,2,3,4,7,8-HxCDF
1,2,3,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6,7,8-HxCDF
1,2,3,4,6.7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
OCDF
Beef
Fraction of
composite
samples
that were
positive
0/8
0/8
3/8
0/8
7/8
7/8
3/8
0/8
0/8
0/8
0/8
0/8
0/8
4/8
0/8
0/8
Concentration
range of
positive
samples
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Table 4-3. Summary of U.S. Food Data from NCASI Study
Food
Number
of
Samples
2,3,7,8-TCDD Level8
(Food basis, pg/kg)
2,3,7,8-TCDD Level*
(Lipid basis, pg/kg)
2,3,7,8-TCDF Level9
(food basis, pg/kg)
2,3,7,8-TCDF Level8
(Lipid basis, pg/kg)
Milk
Half & Half
Ground beef
Corned beef hash
Beef hot dogs
Ground pork
Chicken broth
Coffee
Orange juice
1
2
3
14
3
3
3
2
3
1.8
7.2; 8.7
17; 18; 62
7.2-20
12; 15; 37
ND(5.8); ND(6.5); ND(6.5)
1.1; 1.3; 1.5
ND(0.2); 0.08
ND(0.3); ND(0.3); ND(0.4)
48
55; 67
71; 141; 352
54-144
44; 56; 128
ND(18);ND(22); ND(27)
(lipid content unknown)
NR
NR
ND
NR
ND(3.8); ND(4.8); 5.2
ND(5.9);ND(17);4.7-12
ND(7.7); 11; 11
13; 13; 20
NR
NR
NR
ND
NR
ND(16);ND(27);41
ND(39);ND(120);33-103
ND(28); 38; 41
45; 53; 62
NR
NR
NR
NOTE: ND = Not detected; NR = Not reported
a Values in parentheses are detection limits.
Sources: Henry et at. (1992); LaFleur et al. (1990)
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Table 4-4. Summary of Schecter et al. (1993) Data on U.S. Foods
.' . . ..:•*
Haddock Fillet
Crunchy Haddock
Perch
Cod
Ground Beef
Beef Rib Sirloin Tip
Beef Rib Steak
Pork Chop
Cooked Ham
Lamb Sirloin
Lebanon Bologna
Chicken
Cottage Cheese
Blue Cheese
Cream Cheese
American Cheese
Heavy Cream
TEQ (pg/s)a
Assuming
ND m 0.5 DL
0.03
0.13
0.24
0.023
1.5
0.04
0.65
0.26
0.029
0.4
0.12
0.03
0.04
0.73
0.38
0.31
0.35
: TEQtpg/g}*
Assuming
ND « 0
0.02
0.13
0.24
0.012
1.5
0.04
0.65
0.26
0.024
0.4
0.11
0.03
0.04
0.70
0.38
0.31
0.33
Number of
Samples*
2
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
ND = nondetect; DL = detection limit
a Concentrations reported on whole food, wet weight basis.
b Samples collected from a supermarket in New York.
Source: Schecter et al. (1993)
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ppt for beef on a wet weight basis. If nondetectable concentrations are assumed to be
zero; the estimated total TEQ for beef is estimated to be 0.29 ppt. All of the pork samples
analyzed by CARS, NCASI, and Schecter et al. (1993) had at least one 2,3,7,8-substituted
CDD/F at detectable concentrations. The hepta- and octa-chlorinated dioxins and furans
were detected most frequently, and only one congener was not detectable in any of the
samples analyzed. Using an assumed lipid content of 15 percent and one-half the
detection limit to represent nondetectable concentrations, the estimated total whole
weight TEQ for pork is 0.26 ppt. If nondetectable concentrations are assumed to be zero,
the estimated TEQ for pork is 0.10 ppt. Therefore, the TEQ concentration for pork is
expected to be between 0.10 ppt and 0.26 ppt.
Chicken and Eggs
Background TEQ concentrations for chicken are based on data from CARB (Stanley
and Bauer, 1989) and Schecter et al. (1993). Nine composite chicken samples were
analyzed for 16 2,3,7,8-substituted CDD/F congeners. All chicken samples contained
detectable concentrations of at least one CDD/F congener. The hepta-chlorinated CDD/Fs
and OCDD were detected most frequently, and 5 of the 16 congeners were not detected
in any of the 9 chicken samples. The total background whole weight TEQ for chicken is
estimated to be 0.19 ppt using an assumed lipid content of 15 percent and one-half the
detection limit to represent the concentration of nondetectable congeners. Using zeros to
represent nondetectable concentrations, the estimated total whole weight TEQ for chicken
is 0.07 ppt. Therefore, the TEQ for chicken is expected to be between 0.07 ppt and 0.19
ppt. Background TEQs for eggs are based on data from CARB (Stanley and Bauer, 1989).
For eggs, seven out of eight composite samples had no detectable concentrations of
2,3,7,8-substituted CDD/F congeners. Only one sample contained detectable
concentrations of OCDD, 2,3,7,8-TCDF, and 1,2,3,4,6,7,8-HpCDF. Using one-half the
detection limit for nondetectable concentrations, the estimated total TEQ for eggs is 0.14
ppt; but using zero for the nondetectable concentrations, the estimated TEQ for eggs is
only 0.0004.
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Milk and Milk Products
Background levels of CDD/Fs in U.S. milk are based on a very limited data set.
CARB (Stanley and Bauer, 1989) analyzed eight packaged milk samples and found an
average of 0.06 ppt TEQ. Becuase these samples may have been impacted by leaching of
CDD/Fs from packaging materials, they were eliminated from the analysis of background
concentrations conducted for this report.
LaFleur et al. (1990) analyzed a single background milk sample for 2,3,7,8-TCDD
and 2,3,7,8-TCDF. The sample contained 2,3,7,8-TCDD at a concentration of 0.0018 ppt
and nondetectable concentrations of 2,3,7,8-TCDF. Based on the LaFleur et al. (1990)
data, the TEQ for these two congeners is estimated to be 0.0018 ppt whether one-half the
detection limit or zero is used to represent the nondetectable concentration of
2,3,7,8-TCDF.
EPA (1991b) collected milk samples from several sites in the vicinity of a municipal
waste incinerator in Rutland, Vermont, and two background samples from a dairy farm
123 kilometers from the incinerator where no obvious industrial sources of CDD/F were
present. All samples were taken from bulk storage tanks at the farms. The report
indicated that facility emissions could not be correlated with the levels of CDD/F and other
contaminants measured in various environmental media. For all milk samples, the majority
of the congeners were not detected. It was reported that only OCDD was consistently
detected at levels from 0.2 to 2.4 pg/g in the farms near the facility. The levels in milk
from the three farms near the facility ranged from about 0.2 to 0.4 pg of TEQ/g whole
milk, and the TEQ for the background samples collected from the distant farm was 0.12
pg/g. The TEQs were calculated by EPA (1991b) by setting the nondetects equal to the
detection limit. The 0.12 ppt TEQ background value estimated by EPA is nearly 2 orders
of magnitude higher than the TEQ for milk based on the NCASI data. (This is probably due
largely to the incomplete congener analysis conducted by LaFleur et al.) Examination of
the raw data supporting this study indicated that all of the CDD/F congeners in the
background sample were nondetectable. Consequently, if nondetects are set to zero, the
total background TEQ for milk would be zero. If half the detection limits are used to
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calculate the total TEQ level, the estimated value is 0.07. Therefore, the total background
TEQ level for milk is expected to be between zero and 0.07 pg/g.
Some idea of the total TEQ level of CDD/F in milk samples can be gained by
assuming that levels in beef fat are similar to levels in milk fat. This assumption implies
that the differences in feeding/raising practices of dairy cattle vs. beef cattle do not cause
substantial differences in CDD/F exposure. Beef contains approximately 20 percent fat,
and whole milk is about 4 percent fat. Thus, on a whole food basis, CDD/F levels in beef
should be about five times higher than in milk. Support for this concept can be seen in the
German data presented in Table 4-2. This table shows that the TEQ level in milk fat is
1.35 ppt and in beef fat is 1.08 ppt. On this basis, the North American data for beef
(0.48 ppt of TEQ) suggest that milk would be about 0.1 ppt of TEQ. This lends support to
the background level reported in EPA (1991b) of 0.12 ppt, based on only two samples.
Schecter et at. (1992) reported on the analysis of 2,3,7,8-substituted CDD/Fs in
U.S. dairy products. Cottage cheese, soft cream cheese, and American cheese samples
were selected randomly from New York supermarkets and analyzed on a wet-weight basis.
All of the dairy products sampled had at least 13 detectable congeners out of the 17
evaluated. Only one congener (1,2,3,7,8,9-HxCDF) was not detectable in any of the five
dairy products. Based on these data, the total background TEQ concentration of dairy
products is estimated to be 0.36 ppt if one-half the detection limit is used to represent
nondetectable concentrations and 0.35 if zero is used to represent nondetectable
concentrations.
Fruits and Vegetables
Data on CDDs and CDFs in U.S. fruit and vegetable products are extremely limited.
The Ministry of the Environment, Ontario, conducted a study of CDDs and CDFs in locally
produced and imported fruits and vegetables, some of which originated in the United
States (Ministry of the Environment, 1988; Birmingham et al., 1989). Samples of fresh
apples, peaches, potatoes, tomatoes, and wheat products were analyzed. In general, the
minimum detection limits for these analyses were less than 1 ppt. The report indicated
that "fruit and vegetable samples were substantially free of PCDD and PCDF residues,
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especially the more toxic tetra, penta, and hexachlorinated forms" (Ministry of the
Environment, 1988). OCDD was the only congener detected in any of the samples. One
apple and one peach sample contained detectable OCDD concentrations (8 ppt and 0.6
ppt, respectively). Detectable OCDD concentrations were found at concentrations ranging
from 1 to 3 ppt in potatoes and 0.6 to 0.7 ppt in wheat samples. None of the tomato
samples contained detectable levels of any CDD or CDF congeners. Based on these
results, Birmingham et al. (1989) estimated the TEQs for fruits, vegetables, and wheat
products to be 0.004 ppt, 0.002 ppt, and 0.0007 ppt, respectively.
As discussed in Volume III, dioxin contamination of fruits and vegetables is thought
to occur primarily via particle deposition or vapor adsorption onto outer layers with little
penetration to inner portions. Plant uptake from the soil via the roots is generally
considered negligible. However, the work of Hulster and Marschner (1993) indicates that
zucchini and pumpkins were exceptions. For these plant species, it appears that root
uptake occurs and leads to a uniform concentration within the fruit. The concentration of
CDDs and CDFs in zucchini squash grown on "uncontaminated" soil (0.4 ppt TEQ soil
concentration) ranged from 0.5 to 0.7 ppt TEQ dry weight. These reported values may be
converted to whole weight TEQ concentrations by using an assumed moisture content of
93.7 percent (USDA, 1979-1984). The resulting range of whole weight concentrations for
zucchini is 0.03 to 0.04 ppt TEQ. Muller et al. (1993) also evaluated CDDs and CDFs in
vegetables (carrots, lettuce, and peas) grown at both contaminated plots and control plots.
For the control plots, the highest levels of CDDs and CDFs were observed in carrot peels:
0.55 ppt TEQ dry weight, or 0.07 ppt TEQ whole weight, assuming a moisture content for
carrots of 87.8 percent (USDA, 1979-1984). Lower concentrations were observed in
samples from the cortex of the carrots, indicating that the "contamination source for the
peel of carrots is the soil" (Muller et al., 1993). Lettuce concentrations ranged from 0.1 to
0.4 ppt TEQ dry weight. This is equivalent to a whole weight concentration range of
0.005 to 0.018 ppt TEQ, assuming a moisture content of 95.4 percent for lettuce (USDA,
1979-1984). Concentrations in peas from contaminated plots ranged from 0.04 to 0.12
ppt TEQ dry weight (0.004 to 0.013 ppt TEQ whole weight, assuming a moisture content
of 88.9 percent). Lower concentrations in peas (i.e., close to the detection limit; exact
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value not given) were reported for control plots. Similar data for vegetables grown in the
United States were not available.
Vegetable Oil
The high fat levels in vegetable oil suggest that it may be important to consider as a
source of human exposure. Vegetable oils can be made from a variety of plants including
corn, olives, peanuts, sunflower seeds, safflower seeds, linseed, and cotton seed. Many
of these items are protected from atmospheric deposition, which implies that their CDD/F
levels would be low. However, Theleen (1991) estimated that vegetable oil could
contribute about 10 percent of a person's total daily intake in the Netherlands (14 of 120
pg TEQ/d). This estimate was based on the Furst et al. (1990) study that found
nondetects for most congeners except some of the higher chlorinated congeners of CDD
and CDF (detection limit = 0.5 ppt). Half the detection limit was used for the nondetects,
and most of the congeners were not detected. Consequently, the actual value could be
much lower. No data could be found on CDD/F levels in vegetable oil in North America.
U.S. Food Summary
The U.S. food data are summarized in Table 4-5. The background TEQ estimates
are presented first assuming that nondetects equal half the detection limits and second
assuming that nondetects equal zero. For food groups such as eggs, a wide range of TEQ
estimates are seen indicating a high percent of nondetects among individual congeners.
The upper mean TEQ estimates are generally comparable to the TEQ estimates derived
from studies conducted in Germany and Canada (as discussed below). These studies did
not report TEQs based on assuming nondetects equal to zero but did report many
nondetects in some food groups. In summary, the limited number of U.S. food samples
and the high incidence of nondetects make an uncertain basis for estimating national
background levels. However, the general agreement with food level estimates reported for
Canada and Germany provides some reassurance that these U.S. values are reasonable. It
is clear, however, that a large survey is needed to confirm residue levels of CDD/F in the
U.S. food supply. For the purposes of calculating background exposures to CDD/Fs via
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Table 4-5. Summary of CDD/CDF Levels in U.S. Food (pg/g fresh weight)
Beef
Pork
Chicken
Eggs
Dairy
Products
Milk
Fish
MeanTEQ
Assuming
ND»0.5Dl
0.48
0.26
0.19
0.13
0.36
0.07
1.2
Mean TEQ
Assuming
NO «*ero
0.29
0.10
0.07
0.0004
0.35
0
0.59
Number of
Samples
14
12
9
8
5
2
60
Reference
Stanley & Bauer
(1989), LaFleuretal.
(1990), Schecter et al.
(1993)
Stanley & Bauer
(1989),
LaFleuretal. (1990),
Schecter et ai. (1993)
Stanley & Bauer
(1989),
Schecter et al. (1993)
Stanley & Bauer
(1989),
Schecter et al. (1993)
U.S. EPA (1991b)
U.S. EPA (1992)
ND = Nondetect; DL - Detection Limit
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dietary intake, the upper-range background TEQs (i.e., those calculated using one-half the
detection limit for the nondetects) were used (See Chapter 5.)
4.6.3 European Food
Relatively extensive multiyear surveys of the levels of CDDs and CDFs in food are
being undertaken in Sweden and the United Kingdom (de Wit et al., 1990 and Startin et
al., 1990). The most extensive investigations reported to date that involve testing of a
variety of randomly selected food samples collected within the framework of official food
control have been performed in the Federal Republic of Germany (Beck et al. 1989; Furst
et al., 1990). The detailed results of these studies are included in Appendix B. Furst et al.
(1990) analyzed 107 food samples collected in Germany. The results of this study are
presented in Table 4-6. All samples, except some of the milk, were randomly collected
during official food monitoring programs. The authors speculated that a source may have
been near the areas where the milk samples were collected because they appeared higher
than other milk tested in Germany which showed levels around 1 ppt TEQ. In a later
report, Furst et al. (1991) reported that a much larger survey of dairies in Germany had
been completed. This survey analyzed 168 samples of milk and milk products collected at
dairies prior to bottling. They found an arithmetic mean of 1.35 pg of TEQ/g of fat. TEQs
in these studies were estimated by assuming that nondetects equalled half the detection
limits. The percent detected was not reported. Furst et al. (1991) provided a summary of
the results of several European studies. The data summaries relevant to background levels
in meat and dairy products from Furst et al. (1991) are presented in Table 4-7. Furst et al.
(1991) report that information on CDD and CDF levels in vegetables and fruits is scarce
and that the available data indicate a background of below 1 ppt.
Becket al. (1989) analyzed 12 food samples collected randomly from food markets
in West Berlin, Germany. Chicken, eggs, butter, pork, ocean perch, cod, herring,
vegetable oil, cauliflower, lettuce, cherries, and apples were analyzed for CDD/Fs. CDD/Fs
were detected in samples of animal origin in the ppq to ppt range (fat weight basis). No
CDD/F congeners were detected at a detection limit of 0.01 ppt (whole weight basis) in
samples of plant origin.
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Table 4-6. CDD/CDF Levels in German Food
Cow's Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned Meat
Lard
Fresh Water Fish
Salt Water Fish
Fish Oil
Cod Liver Oil
Salad Oil
Margarine
Infant Formula
Mean TEQa
(pg/g fat)
1.35
0.98
0.66
1.69
3.22
<0.4
1.23
1.41
1.29
0.47
13.25
16.82
2.64
13.31
<0.4
<0.4
0.5
Number of Samples
168
10
5
3
4
3
2
2
2
4
18
15
4
4
4
6
10
a TEQ computed using one-half the detection limit for nondetects.
Sources: Milk data based on Furst et al. (1991); other data from Furst et al. (1990).
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Table 4-7. CDD/CDF Background Levels in Some European, Canadian,
and New Zealand Food
Country
Germany
United Kingdom
Netherlands
New Zealand
Germany
Canada
Food
Cow's milk
Cow's milk
Cow's milk
Cow's milk
Cow's milk
Pork
Beef
Veal
Sheep
Poultry
Canned Meat
Lard
Beef
Pork
Poultry
: Source
Background contamination
Consumer's milk
Rural area
Background contamination
Background contamination
pg TEQ/g fat
1.0- 2.8
0.8-2.6
1.3
0.7-2.5
0.18-0.22
0.5
3.5
7.4
2.0
2.3
1.7
0.8
2.9
0.2
2.6
Source: Furst et al. (1991)
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Theelen et at. (1993) collected food products from various locations in the
Netherlands and analyzed them for 2,3,7,8-chlorine substituted dioxins, furans, and planar
PCBs. Meat samples were collected from slaughter houses throughout the Netherlands.
Fish, mixed meats, and cheeses were gathered at various grocery stores. Mixtures of
foods in these categories were prepared based on the proportion of the average annual
consumption rate that different food items in these categories represented. The food
industry provided purified oils and fats. Mixtures of these items were also prepared in
proportion to their annual use in the Netherlands. The concentration of CDD/Fs in these
food products are presented in Table 4-8.
4.6.4 Canadian Food
Birmingham et al. (1989) analyzed CDD/F residues in food collected in Ontario,
Canada. Most of the food was grown in Canada, although some was from the United
States. They reported analyzing 25 composite samples from 10 food groups. The precise
number of samples in each food group was not reported. No TeCDD, PeCDD, HxCDD,
TeCDF, or PeCDF were found at detection limits of 0.1 to 7 ppt. Low ppt levels of some
of the higher chlorinated CDD/Fs were detected in some foods. TEQ levels were also
estimated for the major food groups. However, as shown in Table 4-9, these data were
reported on a homolog basis. It is unclear what procedure was used to convert the
homolog data to TEQ. The text implies that nondetects were treated as zero for purposes
of estimating TEQ. In addition to the animal food data shown in Table 4-9, measurements
were also made in potatoes, apples, tomatoes, peaches, and wheat. Only OCDD was
detected at levels ranging from 0.6 to 8 pg/g fresh weight. The TEQ totals for vegetables
were reported as 0.004 ppt for fruit, 0.002 ppt for vegetables, and 0.0007 ppt for wheat-
based products. The procedure used to develop these TEQ estimates was not clear.
4.7. CONCENTRATIONS IN AIR
Tables B-14 through B-16 (Appendix B) contain summaries of data from studies of
ambient air measurements of CDDs, CDFs, and PCBs in the United States and Europe.
Environmental levels of PCBs in air are based on a single source of information (Hoff et al.,
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Table 4-8. Concentrations of Dioxins and Furans in Food from the Netherlands
Food Category
Beef
Cow's Liver
Pork
Pig's Liver
Poultry
Chicken's Liver
Mutton
Horse Meat
Game a
Butter
Cheese a
Nuts3
Cereals a
Eggs
Fatty Sea Fish a
Lean Fish a
Eel
Fresh Water Fish a
Mixed Meat Product a
Dairy Products
Soy Bean Oil
Rape-Seed Oil
Palm Oil
Sunflower Oil
Coconut Fat
Palm Fat
Fish Oil
Items with Vegetable Oil a
Items from Food Industry a
CDDs/CDFs
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Table 4-9. Maximum CDD/CDF Levels in Foods Collected in Canada
(pg/g fresh weight) as Reported by Birmingham et al. (1989)
TCDD
PeCDD
HxCDD
HpCDD
OCDD
TCDF
PeCDF
HxCDF
HpCDF
OCDF
TEQ
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1992). Relatively few studies have been conducted to measure ambient air levels of
CDDs/CDFs because of the low analytical detection limits required to detect the expected
low concentrations of specific CDD/CDF congeners. These detection limits in ambient air
samples were not achieved until the mid 1980s. To obtain subparts-per-trillion levels of
analytical detection, sampling relatively large volumes of air (e.g., 350 to 450 cubic meters
of ambient air over a 24-hour period) is required. The results of several of these recent
studies are summarized in the following paragraphs.
4.7.1. U.S. Data
The most extensive ambient air monitoring study of CDDs/CDFs conducted to date
is a multiyear monitoring effort conducted at eight sampling locations in the Southern
California area by the Research Division of the California Air Resources Board from
December 1987 through March 1989 (Hunt et al., 1990). The monitoring network
"included a number of sites situated in primarily residential areas (San Bernadino, El Toro,
and Reseda), as well as several sites in the vicinity of suspected sources of CDDs/CDFs
(Cal. Trans, Commerce, North Long Beach, and West Long Beach)." The seven sites
mentioned above were classified as urban locations by the definitions used in this
document, while one site was classified as an industrial site (i.e., Carson--on site at
manufacturer of gas cooking equipment). Additionally, four of the eight sites were part of
the South Coast Air Quality Management District (SCAQMD) monitoring network. All
totaled, there were nine sample collection intervals throughout this study. "Typically, five
to seven stations were in contemporaneous operation during a particular session" (i.e.,
samples were not collected from each location at each interval). Total tetra- through octa-
chlorinated CDDs and CDFs were screened for in the study as well as various 2,3,7,8-
substituted CDD and CDF congeners. A total of 34 analyses were performed throughout
the study for all congeners except for OCDD and OCDF, respectively, for which only 31
analyses were performed. Samples were collected over a maximum of seven intervals at
each site throughout the study (i.e.. Reseda and El Toro--six dates, duplicate samples on
one date), while a sample was collected from the Commerce site during only a single
collection interval. Sample collection intervals generally averaged 24 hours in duration.
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Generally, higher substituted CDD and CDF congeners accounted for the majority of
positive samples containing quantifiable CDD/CDF residues in this study (i.e.. Total
HxCDD/HxCDF and above). In fact, over 90 percent of the samples collected contained
quantifiable levels of 1,2,3,4,6,7,8-HpCDD, Total HpCDD, and OCDD. Additionally,
approximately 50 to 70 percent of the samples collected contained quantifiable levels of
Total HxCDD; 2,3,7,8-TCDF; Total TCDF; Total PeCDF; Total HxCDF; 1,2,3,4,6,7,8-
HpCDF; Total HpCDF; and OCDF. For all other congeners, quantifiable residues were
detected in less than 25 percent of the samples collected. All CDD congener
concentrations ranged from nonquantifiable levels (low limit of 0.0026 pg/m3) to an upper
limit of 18.0 pg/m3. Additionally, CDF congener levels ranged from nonquantifiable levels
(low limit of 0.0040 pg/m3) to an upper limit of 2.70 pg/m3.
According to Hunt et al.(1990), "The highest concentration of CDDs/CDFs
congener class sums (04-09) and 2,3,7,8-substituted species were noted during a period
predominated by off-shore air flows in December 1987, suggesting a regional air mass and
transport phenomena. Concentrations of the CDDs/CDFs were diminished markedly in
subsequent sessions where air flow patterns were primarily off-shore or of coastal origin."
Hunt et al. (1990) indicated that the "CDD/CDF congener profiles (CI4-O8) and 2,3,7,8-
substituted isomeric patterns strongly suggest combustion source influences in the
majority" of the samples collected.
In a long-term study of CDD/Fs in the ambient air around Bloomington, Indiana,
methods were developed for measuring individual CDD/Fs at concentrations as low as
0.001 pg/m3 (Eitzer and Hites, 1989). Total CDD/F concentrations were 0.480 pg/m3 and
1.360 pg/m3 for the vapor phase and the particle-bound phase, respectively. For
individual congeners, CDFs were found to decrease in concentration with increasing levels
of chlorination, and CDD concentrations were found to increase with increasing levels of
chlorination (Eitzer and Hites, 1989).
4.7.2. European Data
Clayton et al. (1993) conducted a study of CDDs and CDFs in the ambient air of
three major cities and an industrial town in the United Kingdom. The annual average TEQ
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concentrations of CDDs and CDFs ranged from 0.04 to 0.10 pg/m3. The hepta- and
octachlorinated dioxin congeners contributed the most to the total concentration of
2,3,7,8-substituted CDD/Fs, and a large number of nondetect values were reported for the
tetra-, penta-, and hexachlorinated dioxins. The congeners that contributed most to the
total TEQ concentrations were 2,3,7,8-TCDF; 1,2,3,4,7,8-; 1,2,3,6,7,8-; and 2,3,4,6,7,8-
HxCDF. These values are relatively consistent with the concentrations in ambient German
air observed by Liebl et al. (1993) and Konig et al. (1993a). Liebl et al. (1993) analyzed
ambient air samples collected from 10 sites in Hessen, Germany, from 1990 through
1992. Concentrations ranged from 0.04 to 0.15 pg TEQ/m3. The higher concentrations
were presumed to result from direct local industrial sources. Konig et al. (1993a) collected
air samples from six sites located in Hessen, Germany. CDD/F concentrations ranged from
0.048 pg TEQ/m3 at a rural reference site to 0.146 pg TEQ/m3 at an industrial site. The
results of the study also indicated that concentrations of CDDs and CDFs are typically
higher in the winter than in the summer. Sugita et al. (1993) also observed higher
concentrations of CDDs and CDFs in winter than in summer in an ambient air study in
urban Japan. The average concentration of CDDs and CDFs was 0.788 pg TEQ/m3 in the
summer and 1 .464 pg TEQ/m3 in winter.
In a Swedish study, air samples were collected from a city center, suburb, remote
countryside, and open coastal area (Broman et al., 1991). Analyses of the samples for
dioxins and furans indicated that the concentrations of these compounds decreased with
increasing distance from the city center. Total CDD/F concentrations were 1 .40 pg/m3,
1.10 pg/m3, 0.40 pg/m3, and 0.22 pg/m3 for the city center, suburb, countryside, and
open coastal areas, respectively. Similar patterns of decreasing concentrations with
increasing distances from urban areas were also observed for individual CDD/F congeners
(Broman et al., 1991). In a study of ambient air concentrations of CDDs and CDFs in
Flanders, samples were collected and analyzed at rural, industrial, and urban sites (Wevers
et al., 1993). Average ambient air concentrations ranged from 0.0696 pg TEQ/m3 at a
rural site to 0.254 pg TEQ/m3 at a site believed to be influenced by a chemical industry
and a highway.
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PCBs have also been evaluated in European air samples (Halsall and Jones, 1993;
Konig et al., 1993b). Halsall and Jones (1993) monitored urban air at two sites in the
United Kingdom. The annual mean total PCB concentrations were 520 and 590 pg/m3.
PCBs existed in ambient air predominantly in the vapor phase. This study also indicated
that summer PCB concentrations were higher than winter concentrations. These
researchers attributed the differences in seasonal patterns to volatilization from soil during
summer months. Ambient air concentrations of PCBs in Hessen, Germany, ranged from
350 to 1630 pg/m3 during the period of 1990 to 1992 (Konig et al., 1993b). Urban areas
characterized by industry and/or heavy traffic had the highest PCB concentrations in
ambient air.
4.7.3. Air Summary
Based on the limited ambient air measurements that have been made in selected
cities in the United States and Europe, there appears to be good agreement with respect to
the magnitude of specific congeners of CDDs and CDFs in urbanized areas in the United
States and Europe. Most of these measurements tend to be very close to the current
analytical detection limit. This increases the probability that congeners indicated as not
detected (ND) may actually be present.
A total of 84 samples from the studies summarized in Tables B-14 and B-15 was
selected as representative of "background" conditions in the United States. Samples
collected from pristine sites and from rural and urban locations not expected to be
impacted by industrial point sources were assumed to represent "background" conditions.
The mean TEQ level for these 84 samples is 0.095 pg/m3 assuming that values reported
as not detected are equal to one-half the detection limit.
Based on the results of European studies, ambient air concentrations of CDDs and
CDFs appear to be similar to those found in the United States. For the purposes of this
study, a TEQ value of 0.10 pg/m3 was used to represent concentrations in Europe. This
value represents the mean of the midpoints of the European studies for which TEQ
concentrations were reported (Clayton et al. 1993; Liebl et al. 1993; Kdnig et al. 1993a;
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Wevers et al. 1993). Data for these European studies are not included in Tables B-14 and
B-15 because individual congener data were not reported.
It is interesting to compare these values with the CDD/CDF concentrations in air
recently measured by Lugar (1993) in and around McMurdo Station, Antarctica, a logistics
and staging facility with a population of about 1,100. Four locations were sampled: a site
upwind of the station, downwind of the station, in the center of the station, and a remote
unpopulated island 30 kilometers distant from the station. CDDs/CDFs were not detected
in the samples from the upwind site (congener detection limits ranged from <0.01 to 0.03
pg/m3) and the remote island sites (congener detection limits ranged from 0.001 to 0.008
pg/m3) and only sporadically at the downwind site (some congeners detected in three of
five samples). CDDs/CDFs were detected in all five samples collected from the station
center site (mean TEQ concentration of 0.0153 pg/m3).
4.8. TEMPORAL TRENDS
Small amounts of dioxin-like compounds may be formed during natural fires
suggesting that these compounds may have always been present in the environment.
However, it is generally believed that much more of these compounds have been produced
and released into the environment in association with man's industrial and combustion
practices, and as a result, environmental levels are likely to be higher in modern times than
they were in prior times. However, the trend may now be reversing (i.e., releases and
environmental levels may be gradually decreasing) due to changes in industrial practices
(Rappe, 1992). As discussed in Chapter 3, the potential for environmental releases of
dioxin-like compounds has been reduced due to the switch to unleaded automobile fuels
(and associated use of catalytic converters and reduction in halogenated scavenger fuel
additives), process changes at pulp and paper mills, improved emission controls for
incinerators, and reductions in the manufacture and use of chlorinated phenolic
intermediates and products.
Smith et al. (1992, 1993) analyzed sediment core layers from Green Lake, located
near Syracuse, New York, to determine temporal trends in the deposition of CDDs and
CDFs since the beginning of the industrial era (i.e., circa 1860). This deep lake (200-foot
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depth) is thought to be impacted only by atmospheric deposition because no industrial
inputs are present and motorboats are not allowed. Relatively constant but low
concentrations of CDDs and CDFs (10 ng/kg or less) are observed in sediments deposited
from 1860 to 1930. However, concentrations increase rapidly thereafter, reaching a peak
in the mid-1960s when total CDD concentrations exceeded 1,300 ng/kg and total CDF
concentrations exceeded 250 ng/kg. The concentrations of CDDs and CDFs have rapidly
declined since the mid-1960s, and now (1986-1990) are measured at 750 ng/kg as total
CDD/CDF. The authors speculate that the decline may be due to the switch to unleaded
fuels for vehicles. Similar trends have been reported by Czuczwa and Hites (1984) for
Great Lakes sediment.
Rappe (1991) reports testing of archived soils and plants collected in southeast
England between 1846 and 1986. CDDs and CDFs were found in all samples and showed
generally increasing levels of dioxins. Rappe further notes that the congener pattern is
typical of those for combustion sources until about 1950 when the pattern becomes more
dominated by hepta- and octa-CDDs corresponding to increases in production of
chlorinated compounds. Schecter (1991) analyzed ancient liver tissues (estimated to be
100- to 400-years old) recovered from frozen bodies of Native American (Eskimo) women.
He found that the dioxin levels were much lower than those commonly found in livers of
people currently living in industrial areas.
Studies that may be used to assess temporal trends in human exposure to dioxins
and furans are extremely limited. The use of indirect exposure assessment techniques for
detecting temporal trends is difficult because large-scale, long-term, nationally-
representative environmental monitoring for dioxins and furans has not been conducted.
Short-term studies are generally not comparable because of differences in sampling
protocols and analytical techniques used in these studies. A potentially useful study for
evaluating changes in human exposure over time is EPA's National Human Adipose Tissue
Survey (NHATS). The purpose of NHATS is to monitor the human body burden of
selected chemicals in the general U.S. population (U.S. EPA, 1991 a). NHATS uses direct
measurement techniques to estimate exposures. Nationwide samples of adipose tissue are
collected from surgical patients and autopsied cadavers and analyzed annually. In 1982,
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broadscan analysis of composited adipose tissue specimens revealed that chlorinated
dioxins and furans could be detected and quantified in the U.S. population across all
geographic regions and age groups (U.S. EPA, 1986). In 1987, NHATS specimens were
also analyzed for dioxins and furans making temporal comparisons possible. Statistical
analyses were performed to determine if significant differences existed between the
concentrations of these compounds in 1982 and 1987 adipose tissue specimens.
Table 4-10 presents the estimated national average concentrations for the two time
periods and the relative changes from 1982 to 1987. The estimated concentrations of
1,2,3,7,8-PeCDD; 2,3,4,7,8-PeCDF; and HxCDD in human adipose tissue were
significantly lower in 1987 than in 1982 (U.S. EPA, 1991 a). Similar survey designs were
used in the two studies, but changes in some of the analytical methods were made in
1987 that may account for some of the differences in estimated concentrations. These
changes include lower limits of detection and the use of additional internal quantitation
standards that provided more accurate measurements. The levels of 2,3,7,8-TCDD;
1,2,3,4,6,7,8-HpCDD; and OCDD were also lower in 1987 than in 1982, but the
differences were not found to be statistically significant. No statistical comparisons were
possible for 2,3,7,8-TCDF; HxCDF; 1,2,3,4,6,7,8-HpCDF; or OCDF because one or both of
the annual estimates were based on data that did not meet the minimum criteria for
statistical modeling (i.e., the chemical was not detected in at least 50 percent of the
composites analyzed, and/or fewer than 30 composite samples were analyzed in each
year). The results of this study indicate that exposure to certain dioxins and furan
congeners may have decreased over this 5-year time period. However, further studies are
needed to verify that these changes are not a result of protocol changes, but actual
reductions in exposures.
4.9. SUMMARY OF CDD/CDF LEVELS IN ENVIRONMENTAL MEDIA AND FOOD
This chapter has summarized data on CDD/F levels in environmental media and food
with emphasis on "background levels." Data representative of background conditions in
environmental media are considered to be those collected in rural, pristine, and urban (air
only) areas not believed to be impacted by any local sources (e.g., incinerators and
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Table 4-10. Estimated National Average Concentrations of Dioxins and Furans
from the 1982 and 1987 NHATS
2,3,7,8-TCDD
1 ,2,3,7,8-PeCDD
HxCDD c
1,2,3,4,6,7,8-HpCDD
OCDD
2,3,4,7,8-PeCDF
1382* i i
*.'
-0.499(0.628)
-62.9(20.0)
-34.8 (20.3)
-31.6(25.0)
-43.9 (84.7)
-25.7 (3.66)
a Standard errors of the estimated averages are in parentheses.
b The 1982 estimate is significantly higher than the 1987 estimate at the 0.05 level of
significance.
c Analysis results for specific isomers of HxCDD and HxCDF were combined for
comparisons.
Source: U.S. EPA (1991 a)
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highways). Only food data from the general food supply (i.e., collected from grocery
stores) were used to represent background conditions (except fish). Tables B-17 through
B-30 in Appendix B present the geometric and arithmetic averages of environmental
background monitoring data for CDD and CDF congeners in various media, compiled from
the published literature. The geometric averages are consistently lower than the arithmetic
averages. This results from the fact that the data span several orders of magnitude with
the distribution skewed toward the lower end due to the large number of not detected
values. To calculate a total TEQ for all CDD/CDFs for each media, the arithmetic mean
background concentration for each congener was multiplied by its respective TEF value,
and individual TEQs for each congener were totaled. These total TEQs are presented at
the end of Tables B-17 through B-30 and summarized in Table 4-11. These total
background level TEQs are used in Chapter 5 to estimate typical exposure levels in the
United States. Exposure levels for Europe are based on the levels of CDD/Fs in food
reported by Furst et al. (1990), and the levels in environmental media are based on data
collected from several European countries.
Standard deviations of the total mean TEQs for each media were also calculated to
depict the "range" of probable CDD/CDF levels in various media. Because the total TEQs
were actually a summation of mean TEQs for various congeners, the use of typical
methods for calculating standard deviations was not possible. Therefore, standard
deviations were based on the standard deviation of the congener that contributed most to
the total TEQ. The percentage deviation from the mean for that congener was applied to
the total mean TEQ for all congeners combined. The congeners selected for use in the
standard deviation estimates are presented in Table 4-12. The data in this table indicate
that the pentachlorinated dioxins were the highest contributors to total TEQs in most
foods in the United States.
The media levels presented in Table 4-11 are shown graphically in Figure 4-1.
Except for the TEQ levels in European food which are based on data reported for German
food by Furst et al. (1990) and the TEQ levels in European air which are based on data
repoted for air in Germany, Belgium and the United Kingdom by Konig et al. (1993), Liebl
et al. (1993), Wevers et al. (1993), and Clayton et al. (1993), all other TEQ levels
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Table 4-11. Summary of CDO/CDF Levels in Environmental Media and Food (whole weight basis)
Media
Soil, ppt:
TEQ
Sediment, ppt:
TEQ
Fish, ppt:
TEQ
Air, pg/m3:
TEQ
Water, ppq:
TEQ
Milk, ppt:
TEQ
Dairy, ppt:
TEQ
Eggs, ppt:
TEQ
Beef ppt:
TEQ
Pork, ppt:
TEQ
Chicken, ppt:
TEQ
; North America*
n = 95
7.96 ± 5.70
n = 7
3.91b
n=60
1.16 ± 1.21
n = 84
0.0949 ± 0.24
n = 214
0.0056 ± 0.0079
n = 2
0.07c-d
n = 5
0.36 ± 0.29
n = 8
0.135 ± 0.119
n = 14
0.48 ± 0.99
n = 12
0.26 ±0.13
n = 9
0.19 ± 0.29
•?•;;;. ;p"" Europe*'* ,'"'•••
n=133
8.69
n = 20
34.89b
n = 18
0.93f
n=454
0.1080
NOA
n = 168
0.05h
n = 10
0.08j
n = 1
0.1 52d
n=7
0.32'; 0.6 1k
n = 3
<0.06'
n = 2
0.211
Footnotes:
NDA = No data available.
8 Values are the arithmetic mean TEQs and standard deviations.
b Standard deviations could not be calculated because detection limits for most samples were not reported.
c Value was calculated from the raw data used in U.S. EPA (1991b) using half the detection limits for nondetects.
d Standard deviation could not be calculated because data were limited for the congener that contributed the most to
the total TEQ.
8 Soil, sediment, and air values based on data from a variety of European countries (see Tables B-17 to B-30); egg data
based on Beck et al. (1989); and other food levels based on data from Germany (FQrst et al., 1990).
f TEQ calculated from Furst et al. (1990) for fresh water fish by assuming 7% fat content (U.S. EPA, 1993).
8 TEQ assumed to be the mean of the midpoints of the ranges reported in four European studies (Clayton et at., 1993;
KOnig et al., 1993a; Liebl et al., 1993; Wevers et al., 1993).
h TEQ calculated from Furst et al. (1990) by assuming 4% fat content.
' TEQ calculated for cheese from Furst et al. (1990) by assuming 8% fat content.
' TEQ for beef calculated from Furst et al. (1990) by assuming 19% fat content.
k TEQ for veal calculated from Furst et al. (1990) by assuming 19% fat content.
' TEQ calculated from Furst et a). (1990) by assuming 15% fat content.
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Table 4-12. CDD/CDF Congeners that Contribute the Highest Percentage of
TEQ to the Total TEQ for All Congeners Combined
Media
Soil
Sediment3
Fish
Air
Water6
Milk
Dairy
Eggs
Beef & Veal
Pork
Chicken
North America
1,2,3,4,6,7,8-HpCDD
2,3,7,8-TCDD
2,3,7,8-TCDD
1,2,3,7,8-PeCDD
OCDD
2,3,7,8-TCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8-PeCDD
1,2,3,7,8-PeCDD
1,2,3,7,8-PeCDD
1,2,3,7,8-PeCDD
Percentage of
Total TEQ
24.3
80.8
29.9
16.7
56.3
32.4
19.2
29.9
23.2
30.3
28.9
NOTE: Data were not available for all congeners in all media.
a Data available for 2,3,7,8-TCDD and 2,3,7,8-TCDF only.
b Data available for OCDD and OCDF only.
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Figure 4-1 Background Environmental Levels in TEQ
CJ1
en
Soil
Sediment
Fish
•^••••••"••"^••"•••••••••liH"7
11111111111111111111111111H11111111111111 h 8.69; n=1
•••••••••••••••••••••III 1.16 ± 1.2
7j96 ± 5.70; nf=95
33
Chicken
Pork
0.01
0.1 1 10
Media Concentration (ppt of TEQ)
North America [b] MA Europe [c]
CD
[a] Based on an examination of raw data reported by EPA (1991 b); [b] Based on N. American studies;
[c] Environmental media levels based on various European studies,
Food levels based on Furst et at (1990), Egg levels based on Beck et al (1989)
100
o
o
D
O
m
O
O
H
m
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presented in Figure 4-1 are based on the data analyzed in this study. The background TEQ
levels of CDD/CDFs in water and air were found to be lower than in any of the other
environmental media evaluated and were not included in Figure 4-1. For most media, the
average levels appear to be similar between North America and Europe. However,
differences were noted in three areas:
• Sediment - The background levels in Europe were estimated to be higher
than North America. It should be noted, however, that only the 2,3,7,8-
TCDD/F and OCDD/F congeners were analyzed for background sediment
sites in the United States and Europe. The sediment data are quite variable
and can be very high in impacted areas (i.e., 2,3,7,8-TCDD levels over 1000
ppt have been measured in industrial areas). Also, it was difficult to
interpret whether some of the European data truly represent unimpacted
areas. Thus, these differences may be due more to the weakness of the
data base and interpretation difficulties, rather than real differences.
• Dairy Products - The dairy products data suggest that North America levels
are higher than European. Dairy products include a wide variety of food
items with varying amounts of fat. Thus, the CDD/F levels would vary
correspondingly. Differences in the mix of dairy products used for the North
America and European estimates could explain these differences.
• Pork - The pork data suggest that North America levels are higher than
European levels. The low number of samples collected in Europe may mean
this estimate is not representative.
In general, the differences noted above probably reflect the sparseness or
inequalities in the data rather than real differences. The human tissue data (discussed in
Section 5.4) suggest similar body burden levels in the North America, Europe, and other
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industrial countries. Thus, it seems likely the media levels would also be similar.
Large-scale market basket food surveys are clearly needed to confirm these levels.
4.10. MECHANISMS FOR ENTRY OF CDD/CDFS INTO THE FOOD CHAIN
CDD/Fs can enter aquatic systems directly from sources in effluent discharges,
indirectly from deposition of CDD/Fs in the atmosphere onto water bodies, and in
stormwater runoff from areas where dioxin-containing material has been land-applied or
atmospherically deposited. For any given water body, the dominant transport mechanism
will depend on site-specific conditions. Aquatic organisms will bioaccumulate CDD/Fs and
thereby enter the aquatic food chain.
Based on information currently available, the primary mechanism by which dioxin-
like compounds enter the terrestrial food chain is via atmospheric deposition and sorption
of vapors. Deposition can occur directly onto plant surfaces or onto soil. Deposits onto
the soil can enter the food chain via direct ingestion (e.g., soil ingestion by earthworms,
fur preening by burrowing animals, incidental ingestion by grazing animals, etc). CDD/Fs
in soil can become available to plants and thus enter the food chain by volatilization and
vapor sorption or particle resuspension and adherence to plant surfaces. Although CDD/Fs
in soil can adsorb directly to underground portions of plants, uptake from soil via the roots
into above ground portions of plants is thought to be insignificant (McCrady et al., 1990).
Support for this air-to-food hypothesis is provided by Hites (1991) who concluded
that "background environmental levels of PCD/F are caused by PCD/F entering the
environment through the atmospheric pathway." His conclusion was based on
demonstrations that the congener profiles in lake sediments could be linked to congener
profiles of combustion sources. Further argument supporting this hypothesis is offered
below:
Numerous studies have shown that CDD/Fs are emitted into the air from a
wide variety of sources and that CDD/Fs can be commonly detected in air at
low concentrations. (See Chapters 3 and 4.)
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Studies have shown that CDD/Fs can be measured in wet and dry deposition
in most locations including remote areas (Koester and Hites, 1992; Rappe,
1991).
Numerous studies have shown that CDD/Fs are commonly found in soils
throughout the world. (See Chapter 4.) Atmospheric transport and
deposition is the only plausible mechanism that could lead to this widespread
distribution.
Models of the air-to-plant-to-animal food chain have been constructed.
Exercises with these models show that measured deposition rates and air
concentrations can be used to predict food levels that are similar to levels
actually measured in food (Travis and Hattemer-Frey, 1991; also Chapter 7
of Volume III).
Alternative mechanisms of uptake into food appear less plausible:
Uptake in food crops and livestock from water is
minimal due to the hydrophobic nature of these
compounds. Travis and Hattemer-Frey (1987, 1991)
estimate water intake accounts for less than 0.01
percent of the total daily intake of 2,3,7,8-TCDD in
cattle. Experiments by McCrady et al. (1990) show
very little uptake in plants from aqueous solutions.
Relatively little impact on the general food supply is expected
from soil residues that originate from site-specific sources
such as sewage sludge and other waste disposal operations.
Sewage sludge application onto agricultural fields is not a
widespread practice. Waste disposal operations can be the
dominant source of CDD/Fs in soils at isolated locations such
as Times Beach, but are not sufficiently widespread to explain
the ubiquitous nature of these compounds.
The release of CDD/Fs to the environment from the use of
pesticides contaminated with CDD/Fs is beleived to have
declined in recent years; however, the past and current impact
of pesticide use on CDD/F levels in the food supply is
uncertain. CDD/Fs have been associated with certain phenoxy
herbicides most of which are no longer produced or have
restricted uses. EPA has issued data call-ins requiring certain
pesticide manufacturers to test their products for dioxin
content. The responses, so far, indicate that levels in these
products are below or near the limit of quantitation. (See
Chapter 3.)
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Current CDD/F levels in food resulting from the use of
bleached paper products containing CDD/Fs appears to be
minimal. In the early 1980s, testing showed that CDD/Fs
could migrate from paper containers into food. Current levels
in paper products are now much lower than in the early
1980s. Also, testing of products such as milk and beef prior
to packaging has shown detectable levels which cannot be
attributed to the packaging. (See Chapter 4.)
A related issue is whether the CDD/Fs in food result more from current or past
emissions. Sediment core sampling indicates that CDD/F levels in the environment began
increasing around the turn of the century, but also that CDF levels have been declining
since about 1980 (Smith et al. 1992). Thus, CDD/Fs have been accumulating for many
years and may have created reservoirs that continue to impact the food chain. As
discussed in Chapter 3, researchers in several countries have attempted to compare
known emissions with deposition rates. All of these studies (including this assessment)
suggest that annual atmospheric depositions exceed annual emissions by a factor of 2 to
10. One possible explanation for this discrepancy in sources may be that volatilization or
particle resuspension from these reservoir sources followed by atmospheric scavenging is
responsible. These mass balance studies are highly uncertain, and it remains unknown
how much of the food chain impact is due to current vs past emissions.
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REFERENCES FOR CHAPTER 4
Beck, H.; Eckart, K.; Kellert, M.; Mathar, W.; Ruhl, C.S.; Wittkowski, R. (1987) Levels of
PCDFs and PCDDs in samples of human origin and food in the Federal Republic of
Germany. Chemosphere 16 (8/9): 1977-1982.
Beck, H.; Eckart, K.; Mathar, W.; Wittkowski, R. (1989) PCDD and PCDF body burden
from food intake in the Federal Republic of Germany. Chemosphere 18 (1-6):
417-424.
Berry, R.M.; Lutke, C.E.; Voss, R.H. (1993) Ubiquitous nature of dioxins: a comparison
of the dioxins content of common everyday materials with that of pulps and papers.
Environ. Sci. Technol. 27(6):1164-1168.
Birmingham, B. (1990) Analysis of PCDD and PCDF patterns in soil samples: use in the
estimation of the risk of exposure. Chemosphere 20(7-9): 807-814.
Birmingham, B.; Thorpe, B.; Frank, R.; Clement, R.; Tosine, H.; Fleming, G.; Ashman, J.;
Wheeler, J.; Ripley, B.D.; Ryam, JJ. (1989) Dietary intake of PCDD and PCDF from
food in Ontario, Canada. Chemosphere 19:507-512.
Bopp, R.F.; Gross, M.L.; Tong, H.; Simpson, M.J.; Monson, S.J.; Deck, B.L.; Moser, F.C.
(1991) A major incident of dioxin contamination: sediments of New Jersey
estuaries. Environ. Sci. Technol. 25: 951-956.
Boos, R.; Himsl, A.; Wurst, F.; Prey, T.; Scheidl, K.; Sperka, G.; Glaser, O. (1992)
Determination of PCDDs and PCDFs in soil samples from Salzburg, Austria.
Chemosphere 25(3):283-291.
Branson, D.R.; Takahashi, I.T.; Parker, W.M.; Blau, G.E. (1985) Bioconcentration kinetics
of 2,3,7,8-tetrachlorodibenzo-p-dioxin in rainbow trout. Environ. Toxicol. Chem.
4(6):779-788.
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5. BACKGROUND EXPOSURES TO CDD, CDF, AND PCB CONGENERS
5.1. INTRODUCTION
The purpose of this chapter is to assess background exposures to the dioxin-like
compounds. Recent assessments of background exposures cited in the scientific literature
are summarized, and background exposures that have been estimated from the data
presented in Section 4 of this report are presented. The term "background," as applied to
exposure, can be used to represent different concepts. Two common definitions are (1)
the level of exposure that would occur in an area without known point sources of the
contaminant of concern or (2) the average level of exposure occurring in an area whether
sources are present or not. For the purposes of this document, "background" is defined as
suggested in the first definition above. To the extent possible, background exposures
estimated in this chapter are based on monitoring data obtained from sites removed from
known contaminant sources (or food data representative of the general food supply).
These data are considered to be the most useful for describing background exposure
levels.
5.2. PREVIOUS ASSESSMENTS OF BACKGROUND EXPOSURES
Several researchers have published quantitative assessments of human exposures
to CDDs and CDFs. Some of the more recent assessments are discussed below (Travis
and Hattemer-Frey, 1991; Furst et al.,1990; Furst et al., 1991; Henry et al., 1992;
Theelen, 1991; and Oilman and Newhook, 1991). It is generally concluded by these
researchers that dietary intake is the primary pathway of human exposure to CDDs and
CDFs. Over 90 percent of human exposure occur through the diet, with foods from animal
origins being the predominant sources.
Travis and Hattemer-Frey (1991) estimated that the average daily intake of 2,3,7,8-
TCDD by the general population of the United States is 34.8 pg/day. Ingestion exposures
were estimated by multiplying the concentration of 2,3,7,8-TCDD in beef, milk, produce,
fish, eggs, and water (estimated using the Fugacity Food Chain model) times the average
U.S. adult consumption values for these products reported by Yang and Nelson (1986).
The calculations assume that 100 percent of the 2,3,7,8-TCDD ingested are absorbed
through the gut. Intake via inhalation was estimated by multiplying the concentration in
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air times the amount of air inhaled per day (20 m3) assuming that 100 percent of inhaled
2,3,7,8-TCDD are absorbed through the lung. The results of their assessment,
summarized in Table 5-1, indicate that foods from animal origins comprise 95 percent of
the estimated total daily exposure. These foods include milk and dairy products, beef,
fish, and eggs. Exposure resulting from consumption of vegetables and other produce was
estimated to account for 3.4 percent of the total intake. Exposure from ingestion of
water, ingestion of soil, and inhalation of air together accounted for about 1 percent of the
total daily intake.
Furst et al. (1990) estimated human exposure to CDD/Fs based on the analysis of
107 food samples collected in the Federal Republic of Germany. The average daily TEQ
intake was estimated to be 85 pg/person/day or 1.2 pg/kg body weight/day. Furst et al.
(1990) concluded that foods of animal origin contribute significantly to the human body
burden of CDD/Fs. In a subsequent study, Furst et al. (1991) assessed human exposure
to CDDs and CDFs from foods using data from more than 300 randomly selected food
samples and food consumption data reflective of consumption habits of the German
population. These authors estimated that the German population's average daily intake of
CDDs and CDFs from food is 158 pg TEQ per person of which 25 pg is 2,3,7,8-TCDD.
Dairy products, meat and meat products (primarily beef), and fish and fish products each
contribute about 32 to 36 percent of the daily intake of TEQ. Based on the levels of
CDD/Fs observed in human samples, the average daily intake via food was estimated to be
in the range of 1 to 3 pg TEQ/kg body weight.
Henry et al. (1992) of the U.S. Food and Drug Administration estimated the average
exposure to the U.S. population from 2,3,7,8-TCDD through the food supply using the
following assumptions: (1) all dairy products have background lipid 2,3,7,8-TCDD levels
equivalent to those found in milk and half-and-half, i.e., about 55 ppq (whole dairy food
levels were estimated using percent fat in each food); (2) levels averaging 35 ppq in beef
tissue are present in all meat products; (3) ocean fish with tissue levels equal to half of the
detection limit (about 0.5 ppt) are the sole fish source in the diet; (4) average food
consumption figures (total-sample-basis) available from nationally representative data
bases were used for frequency of eating (Market Research Corporation of America's
(MRCA) Menu Census VI (1977-78)) and for serving sizes (U.S. Department of
Agriculture's 1977-78 National Food Consumption Survey). FDA's estimates of 2,3,7,8-
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Table 5-1. Predicted Average Daily Intake of 2,3,7,8-TCDD by the
General Population of the United States
Media
Inhalation
Water
Soil ingestion
Food
Produce
Milk and dairy
products
Beef
Fish
Eggs
TOTAL
Predicted
jmedta
concentration8
0.02 (pg/m3)
0.003 (pg/1)
0.96 (ng/kg)
0.06 (ng/kg)
0.03 (ng/kg)
0.20 (ng/kg)
0.38 (ng/kg)
0.01 (ng/kg)
Media intake
(person/day)
20 (m3)
!.33lb
20 mg
20 gb
266 gb
90 g°
18 gb
25 gb
Daily mtake
Of 2,3,7,8-
TCDD
(PS/day)
0.4
0.004
0.02
1.2
8.0
18.0
6.7
0.5
34.8
Percent of
•:i- -daiiy •
; Intake
1.1
0.01
0.05
3.4
23.0
51.7
19.3
1.4
100
Source: Travis and Hattemer-Frey (1991)
a Values predicted by the Fugacity Food Chain model.
b Inferred consumption rate calculated by dividing reported daily intake (column 4) by
predicted concentration (column 2).
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TCDD intake were derived by multiplying the food dioxin levels by the average amounts of
food consumed per day. The results of its assessment, summarized in Table 5-2, indicate
an average daily exposure of 15.9 pg/day of 2,3,7,8-TCDD of which 4 percent are due to
dairy and milk products, 41 percent are due to meats, and 54 percent are due to ocean
fish.
Theelen (1991), of the Netherlands National Institute of Public Health and
Environmental Protection, estimated the average daily intake of 2,3,7,8-TCDD and total
dioxin TEQ by residents of the Netherlands for various possible routes of exposure. The
results, summarized in Table 5-3, indicate an average intake of 20 pg/day of 2,3,7,8-TCDD
and 115 pg/day of total TEQ from food and 0.08 pg/day (2,3,7,8-TCDD) and 3.2 pg/day
(TEQ) from combined direct air and soil exposure. Milk and dairy products make up about
one-third of the total daily exposure. Animal fat in meat, poultry, and fish (i.e., fish oil)
also contribute about one-third. Fish consumption represents 18.5 percent of total daily
exposure. In a later study, Theelen et al. (1993) reported a median daily intake for adults
of 1 pg TEQ/kg body weight, and a 95th percentile rate of 2 pg TEQ/kg body weight.
These values were based on CDD/F residue levels in food products and food consumption
survey data.
Gilman and Newhook (1991), of the Canadian Department of National Health and
Welfare and the Ontario Ministry of the Environment, respectively, estimated an average
lifetime daily intake of 140 to 290 pg of TEQ for the typical Canadian. Their results,
summarized in Table 5-4, indicate that between 94 and 96 percent of the estimated intake
are from food sources. No breakdown of intake by food type is provided in the report.
As reported in Section 4.6.1, CDD/Fs can migrate from bleached paper packaging
and paper food-contact articles to foods. Some investigators have included this pathway
in estimates of background exposure. U.S. EPA (1990a) estimated that TEQ intake due to
leaching from paper products into food from paper packaging was in the range of 5.5 to
12.7 pg/d. Henry et al. (1992) estimated that daily intake of 2,3,7,8-TCDD due to
migration from paper to food could amount to 12 pg/d, almost as much as the daily intake
from unaffected food of 16 pg/d. (See Table 5-2.) As shown in Table 5-3, Theelen (1991)
estimated that out of a total of about 120 pg of TEQ/d, 9 pg of TEQ/d could be due to
migration from paper. These estimates are based on levels in paper before recent changes
in industry practices that are expected to substantially reduce dioxin levels in paper. As
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Table 5-2. Predicted Average Daily Intake of 2,3,7,8-TCDD from
Foods by the General Population of the United States
Media •
Milk
Cream
Sour cream
Cheese
Ice cream
Butter
Cottage
cheese
Meats
Ocean fish
Coffee
Orange juice
TOTAL
2,3,7,8-TCDD
concentration
>/ in food • . \
(ng&g)
0.0018
0.0072
0.010
0.016
0.0055
0.044
0.0021
0.035
0.500
0.0001
0.0002
Food intake
{g/person/day)
108.9
2.0
0.7
19.4
7.5
2.6
5.5
187
17.2
363.6
33.5
Daily intake of
2,3,7,8-TCDD
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Table 5-3. Daily Exposure to 2,3,7,8-TCDD and TEQ from Air, Soil, Food,
and Nonfood in the Netherlands
/V'-£M^\?VV;-.'
: ' •-..;'' ;l.--::-'-';. . . . '.':! ":'. :•. •'•'
Air inhaled
Air ingested
(particulates)
Soil dermal
Soil ingested
Uptake from air and soil
Leafy vegetables
Pork
Beef
Chicken and eggs
Milk
Cheese, butter
Sea fish
Fresh water fish
Fish oil
Vegetable oil
Intake from food
Intake from paper food
packaging
TOTAL INTAKE
i r Media Intakft
(g/person/day>
20m3
a
h
w
150 mg
27. g
15. g fat
5. g fat
2.5 g fat
8. g fat
1 2.5 g fat
0.4 g fat
0.4 g fat
5.5g
40. g
Daily Intake of
2,3,7,8-TCDD
{pg/day)
0.05
0.025
0.004
0.003
0.08
0.2-2
0.45
3
0.6
3.2
5
2
4
1.1
NDA
19.5-21.3
NDA
19.6-21.4
Daily Intake of TEQ
(pg/day)
2
1
0.15
0.10
3.2
1.8-7
4.2
13
4.8
17
26
14
10
7.2
14
112-117
9.1
121-126
a Intake rate could not be determined from Theelen (1991).
b Assumes exposure of 2,000 cm2 of skin to 1 mg of soil/cm2. Soil concentrations
assumed to be 7,000 mg TEQ/kg and 175 mg of 2,3,7,8-TCDD/kg. Dermal absorption
of 1 percent assumed.
NDA = No data available.
Source: Theelen (1991).
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Table 5-4. Estimated Lifetime Average Daily Exposure
of Canadians to Dioxin TEQ
Media
Food
Air
Soil
Water
Consumer Products
Total Estimated
Lifetime Intake6
i Daily Intake of Dioxin8 (TEQ) (pg/day)
Adult Ab :
132-282
3.5
1.75- 1.90
<0.7-3.5
<0.7
140-290
Adult Bc
291 -441
3.5
1.75- 1.90
<0.7-3.5
<0.7
300 - 450
Adult Cd
132-282
12
1.75- 1.90
<0.7-3.5
<0.7
1 50 - 300
Source: Gilman and Newhook (1991).
8 These estimates represent the lifetime average daily intake calculated by dividing the total
estimated intakes for each life stage (i.e., adult, child, infant, neonate) by the 70-year
exposure period. The estimates in this table are based on the upper range of average
national values and conservative assumptions that overestimate rather than underestimate
exposures. These estimates are only approximations and not absolute values.
b Adult A is an average 70-kg adult consuming average amounts of air (20 m3/day), water
(1 liter/day), and soil (20 mg/day). Food intakes based on Nutrition Canada 1977 survey.
c Adult B is similar to Adult A except that consumption of fish contaminated with CDDs
and CDFs is in excess of current Canadian guidelines.
d Adult C is similar to Adult A except that he/she lives in close proximity to an
incineration/combustion source.
6 These estimates have been rounded off because of the uncertainty in the data.
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discussed in Section 4.6.1, these reductions are expected to have significantly lowered the
CDD/CDF levels currently found in food due to any leaching of dioxin-like compounds from
paper.
5.3. UPDATED ASSESSMENT OF BACKGROUND EXPOSURES
Background exposures to CDD/CDFs in North America were estimated using (1) the
TEQ data on arithmetic mean levels in environmental media and food from Table 4-11, (2)
the standard contact rates for ingestion of soil, water, and food and inhalation of ambient
air, and (3) the appropriate unit conversion factors. The estimated exposures and
assumptions made concerning ingestion or contact rates are presented in Table 5-5.
The background exposures reported here were estimated using standard intake
rates representative of the general population. They do not account for individuals with
higher consumption rates of a specific food group (e.g., subsistence fishermen, nursing
infants, and subsistence farmers-these are discussed in Section 5.5). The estimates
reported here are assumed to represent typical (i.e., "central tendency") U.S. background
exposures, and do not account for these types of variations in the population as a result of
differences in intake rates of the various food groups. The fish concentration used to
estimate background exposures, represents the average value found in fish from fresh and
estuarine waters (see Section 4.5). Correspondingly, the ingestion rate used here reflects
the per capita average ingestion rate of fresh/estuarine fish (U.S. EPA, 1989). Many
individuals are likely to have higher ingestion rates of marine fish. However, the limited
data on marine species indicates that the dioxin levels may be one to two orders of
magnitude lower than fresh/estuarine water fish (also see Section 4.5).
The contact rates for ingestion of fish, soil, and water, and inhalation were derived
from the Exposure Factors Handbook (U.S.EPA, 1989). For food products such as milk,
dairy, eggs, beef, pork, and poultry, a different approach was taken because there is some
evidence that consumption rates have changed since the data for the Exposure Factors
Handbook were collected. Contact rates for these food groups were derived from
commodity disappearance data from the United States Department of Agricultures's
(USDA) report on Food Consumption, Prices, and Expenditures between 1970 and 1992
(USDA, 1993), and intake data from USDA's Nationwide Food Consumption Survey
(NFCS) (USDA, 1992). The average of USDA disappearance and NFCS intake rates were
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Table 5-5. Estimated Background Exposures in the United States
01
i
CD
Media
Soil ingestion
Fish ingestion
Inhalation
Water ingestion
Milk ingestion
Dairy ingestion
Eggs ingestion
Beef ingestion
Pork ingestion
Poultry ingestion
North America
Cone.
TEQa
8.0 ppt
1 .2 ppt
0.095 pg/m3
0.0056 ppq
0.07d ppt
0.36 ppt
0.14 ppt
0.48 ppt
0.26 ppt
0.19 ppt
Contact
rateb
100 mg/day
6.5 g/day
23 m3/day
1 .4 L/day
251 g/day
67 g/day
29 g/day
77 g/day
47 g/day
68 g/day
Total
Daily
intake"
mg/day
8.0 x 10'10
7.8 x 10'9
2.2 x 10"9
7.8 x 10'12
1.8x 10'8
2.4 x 10'8
4.1 x 10'9
3.7x 10'8
1.2x 10'8
1.3x 10-8
1.19 x 10'7
Dally
intake
pg/day
0.8
7.8
2.2
0.008
17.6
24.1
4.1
37.0
12.2
12.9
119
%
of
total
0.7
6.6
1.8
0.01
14.8
20.3
3.4
31.2
10.3
10.9
100
CO
Footnotes: NA = Not applicable, NDA = No Data Available.
a Values from Table 4-10.
b Values for soil ingestion, fish ingestion, inhalation, and water ingestion from Exposure Factors Handbook (USEPA, 1989)
(fish ingestion rate represents average per capita non-marine fish consumption rate). All other contact rates are based on
data from USDA (1992) and USDA (1993).
c Daily intake = Contact rate x Cone. TEQ x Unit Conversion (soil unit conversion = 10" , all other media unit
conversion = 10~9).
d Value was calculated from data in U.S., EPA (1991 a).
o
o
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o
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m
O
31
O
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DRAFT-DO NOT QUOTE OR CITE
used in this study to represent typical contact rates in the United States. USDA (1 993)
estimated per capita consumption rates using disappearance data (i.e., the quantity of
marketable food commodities utilized in the United States over a specified time period)
divided by the total population. Consumption rates were calculated for several
commodities including meats, eggs, milk and dairy products. For meats, the boneless
equivalent quantity was calculated by adjusting the carcass weight based on the amount
of fat and bone removed at different market levels. USDA (1992) reported one-day MFCS
intake data for several meat categories. These included: beef; pork; poultry; frankfurters,
sausages, and luncheon meats; fish and shellfish; and mixtures containing meat, poultry,
and fish. Total intake rates for beef, pork, and poultry were estimated by assuming that
the rate of consumption of these meats in (1) frankfurters, sausages, and luncheon meats,
and (2) meat mixtures was proportional to the intake of these meats on an individual basis.
Thus, the intake in these categories was apportioned among the meat groups. In general,
intake rates based on MFCS data are lower than those based on USDA disappearance data.
NFCS data are believed to underestimate consumption for the general population because
they may not adequately account for consumption of foods contained in mixtures (i.e., the
intake rate for eggs may include eggs eaten separately or as a main ingredient in a dish,
but may not be counted if they are an ingredient in a cake). Additional uncertainty is
associated with the use of data for only one day during the Spring of 1 988 and the use of
survey data based on recall. In contrast to NFCS data, disappearance data may
overestimate per capita consumption because they are based on the quantity of
marketable commodity utilized, divided by the total population. Disappearance data do not
account for losses from the food supply from waste or from the production of items not
intended for human consumption (i.e., pet foods). Thus, the average of USDA
disappearance and NFCS intake rates were believed to be representative of typical contact
rates in the United States.
Background exposure levels are also presented for Germany based on data from
Furst et al. (1990; 1991). The total background TEQ exposure shown in Table 5-5 is 1 19
pg/day for North America. Based on Furst et al. (1990; 1991), the estimated total TEQ
background exposure for Germany is 79 pg/day (Table 5-6). However, it should be noted
that the estimated background level for the United States and Germany are based on
limited data, and exposure to all food groups was not considered. Also, the addition of
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Table 5-6. Background Exposures via Consumption of German Food
. ,': ''I. FOOd ' -:. ':'5: :! ''•
Cow's milk
Cheese
Butter
Beef
Veal
Pork
Chicken
Canned meat
Lard
Salad oil
Margarine
Fish and Fish Products
Fresh water fish
Salt water fish
Fish oil
Cod liver oil
Total TEQ
'•" ':-., TEQa
'concentration
* (fat basis}
1.35
0.98
0.66
1.69
3.22
<0.4
1.41
1.29
0.47
<0.4
<0.4
13.25
16.82
2.64
13.31
Intake Rateb :
g fat/day
6.0
5.2
12
10
0.1
14
1
2
1.5
5
14
1.8
[TCDO -
Equivalent3
llpgAJay)
8.1
5.1
7.9
16.9
0.3
5.6
1.4
2.6
0.7
1
2.8
27
79.4
" Milk data based on Furst et al. 1991; other data based on Fiirst et al. 1990.
b Based on data reported by Furst et al. 1990.
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TEQs for multiple pathways presumes that individuals are exposed by all pathways, and
assumes that the fraction absorbed into the body is the same for all pathways. The
following sections present observations about CDD/CDF exposures in North America,
comparisons between exposure estimates from this and previous studies, and comparisons
between North American and European exposures to CDD/CDFs.
5.3.1. North American Exposures
Based on the data collected for this study, the total background CDD/CDF TEQ
exposure for North America was estimated to be 119 pg/day, for all media combined.
Exposure to 2,3,7,8-TCDD accounts for approximately 10.5 percent (12.0 pg/day) of the
total TEQ exposure. Estimated exposures based on total CDD/CDF TEQs from the various
exposure pathways are presented in Figure 5-1. The highest exposures were estimated to
occur via ingestion of CDD/CDFs in beef (37 pg/day) which accounted for over 30 percent
of the total TEQ exposure. The ingestion of foods accounted for over 97 percent of the
total TEQ exposure. Exposure to CDD/CDFs via ingestion of water appears to be very low.
Exposure via inhalation and soil ingestion are 2.2 and 0.8 pg/day, respectively. These
exposures account for approximately 2.0 percent and < 1.0 percent of the total CDD/CDF
TEQ exposure in North America.
5.3.2. Comparison of Previous North American Studies to This Study
Previous studies of CDD/CDF exposures in North America were presented in
Section 5.2 of this report. These studies reported CDD/CDF exposures based on the most
toxic congener, 2,3,7,8-TCDD, and not on the total TEQ value for all congeners combined.
For the purposes of comparison, mean background levels of 2,3,7,8-TCDD in North
America from this assessment were used to calculate exposure via various pathways.
Background exposures were calculated using background environmental levels of 2,3,7,8-
TCDD, standard contact rates, and appropriate unit conversion factors, as described
previously. Total 2,3,7,8-TCDD exposure for all pathways combined was 12.0 pg/day for
the current assessment compared to 15.9 and 34.8 pg/day for the two previous studies of
2,3,7,8-TCDD exposure in North America (Henry et al., 1992; and Travis and Hattemer-
Frey, 1991). Figure 5-2 depicts the comparisons of the percent contribution of various
exposure pathways to total exposure to 2,3,7,8-TCDD for the current assessment and for
5-12 4/94
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Figure 5-1 Background TEQ Exposure for North America by Pathway
Total Exposure = 119 pg/day
Beef Ingestion
Dairy Ingestion
Milk Ingestion
Chicken Ingestion
Pork Ingestion
Fish Ingestion
Egg Ingestion
Inhalation
Soil Ingestion
Water Ingestion Negligible
37.0
^
CD
0.0 10.0 20.0 30.0 40.0
North America Daily Intake (pg/day) of TEQ
Note: Only two congeners available for water; milk ingestion based on data reported by EPA(1991b).
For a discussion of the uncertainty and variability associated with the media values and
contact rates used to calculate these exposures, see Figure 4-1 and Sections 4.9 and 5.3.
o
3)
o
o
D
c
o
m
O
3D
O
H
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Figure 5-2 Percent Contribution of Various Media
to 2,3,7,8-TCDD Exposure in North America
01
Dairy & Milk
23%
Meats [a]
57%
Dairy & Milk
21%
Dairy & Milk
4%
o
31
O
O
z
o
D
c
o
m
O
20
o
H
m
35 pg/day 12.0 pg/day
Source: Travis & Hattemer-Frey, 1991 Source: This Assessment
15.9 pg/day
Source: Henry et al, 1992
CD
[a] Beef, Chicken, and Pork
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DRAFT-DO NOT QUOTE OR CITE
previous North American studies. Figure 5-2 indicates that exposure via ingestion of
meats accounted for a large portion of the exposure in all three studies. However, fish
accounted for a higher percentage, and dairy products accounted for a lower percentage of
the total 2,3,7,8-TCDD exposure in the Henry et al. (1992) study than in the Travis and
Hattemer-Frey (1991) study and the current assessment. These differences reflect
differences in assumptions for food ingestion rates as well as in TCDD levels. All three
studies indicate that beef, dairy products, and fish comprise over 94 percent of the total
exposure. Because of the data base weaknesses noted earlier, it is not known if these
differences can be considered significant.
5.3.3. Comparison of Previous European Studies to this Study
European CDD/CDF exposure studies may also be compared to the exposures
estimated in U.S. reports and in the current assessment. Comparisons may be made
based on the 2,3,7,8-TCDD congener or on total TEQ exposures (Table 5-7). Exposures to
2,3,7,8-TCDD in North America range from 12.0 pg/day to 34.8 pg/day based on the
current assessment and two other U.S. studies. These values are comparable to the
2,3,7,8-TCDD exposures reported in Germany and the Netherlands by Furst et al. (1991)
and Theelen (1991). Furst et al. (1991) reported an estimated 2,3,7,8-TCDD exposure of
25 pg/day based on ingestion of dairy products, meat, and fish; Theelen (1991) reported
an estimate of 20 pg/day based on dairy, meat, poultry, and fish intake. Total CDD/F TEQ
background exposure estimates for North America range from 119 pg/day for the current
assessment to 140 to 290 pg/day based on Oilman and Newhook's (1991) Canadian
study. For Europe, total TEQ exposure estimates range from 79 pg/day based on Furst et
al. (1990) to 158 pg/day based on Fiirst et al. (1991). Figure 5-3 depicts the
contributions of various exposure pathways to total background TEQ exposures for North
America, Germany, and the Netherlands based on data from the current assessment, Furst
et al. (1990) and Theelen (1991). For all three geographic regions, over 90 percent of the
exposures were attributed to ingestion of CDD/Fs in foods.
Based on the data presented in Figure 5-3, it is reasonable to expect that the
CDD/CDF body burden in vegetarians would be lower than the body burden in non-
vegetarians because vegetarians avoid the consumption of meat and fish and their
derivative products. Welge et al. (1993) tested this hypothesis by comparing the
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Table 5-7. Comparisons of Predicted Average Daily Intake of
2,3,7,8-TCDD and Total CDD/CDF TEQs
location
United States3
United States*5
North America0
Canadad
Germany6
Germany*
Netherlands0
: Daily Intake of
2,3,7,8-TCDD ;
(pg/day)
34.8
15.9
12.0
25.0
20.0
Daily Total TEQ
intake
{pg/day)
--
—
119
140-290
85 (79)
158
121-126
Media
beef, milk, produce,
fish, eggs, water,
inhalation
dairy, meat, fish
dairy, eggs, meat,
poultry, fish,
inhalation, soil
ingestion
air, water, soil, food
dairy, meats, fish
dairy, meat, fish
dairy, meat, poultry,
fish
a
b
c
d
e
f
g
Travis and Hattemer-Frey (1991)
Henry et al. (1992)
Current Assessment
Gilman and Newhook (1991)
Furst et al. (1990); value in parentheses is the corrected TEQ value based on the milk
data from Furst et al. (1991)
Furst etal. (1991)
Theelen (1991)
5-16
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Figure 5-3 Comparison of Background TEQ Exposures
01
i
•sj
Meats/Fish/Eggs
62%
Milk/Dairy
35%
\
s
Meats/Fish
69%
Milk/Dairy
26%
Meats/Fish/Eggs
45%
Milk/Dairy
37%
NORTH AMERICA [a]
119 pg/day
GERMANY [b]
79 pg/day
NETHERLANDS [c]
117 pg/day
o
o
z
o
D
O
H
m
O
3)
O
[a] Current Assessment. See Table 5-5. Other category includes inhalation (1.8%). soil ingestion (0.7%), and
water (0.01%)
[b] Based on Furst et al. (1090,1991). See Table 5-6. Other Category includes salad oil (1.3%) and margarine (3.5%)
[c] Based on Theelen (1991). See Table 5-3. Other refers to inhalation(2.5%), soil ingestion (0.2%), leafy vegetables
(3.4%), and vegetable oil (11.9%)
^
(B
Note: Percentages were rounded to the nearest whole number
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CDD/CDF levels in the blood of 24 German vegetarians with the blood levels of 24 non-
vegetarians, matched for age, sex, body weight, and height. With the exception of two
individuals, all vegetarians had practiced a diet without meat and fish for at least 3 years.
The CDD/CDF levels in the vegetarian group ranged from 14.64 to 52.85 pg TEQ/g
(lipid basis) with a mean of 32.60 pg TEQ/g. In the non-vegetarian group, the CDD/CDF
levels ranged from 14.26 to 97.98 pg TEQ/g (lipid basis) with a mean of 34.32 pg TEQ/g.
There was no significant difference (or = 0.05) between the vegetarian and non-vegetarian
group in the mean levels of any of the 2,3,7,8-substituted congeners, in the total CDD
levels, in the total CDF levels, in the total CDD/CDF levels, or in the total TEQ levels (each
on a lipid and on a whole weight basis). Welge et al. (1993) suggested several reasons
why no differences were found. First, all tested vegetarians had at one time been non-
vegetarians. The higher levels of exposure during this non-vegetarian period coupled with
the long biological half-life of CDD/CDFs may be responsible for the apparent similarity in
body burdens using blood as the measure of body burden. Second, the vegetarians may
have a higher level of consumption of dairy products than the non-vegatarians and thus
have a similar CDD/CDF exposure even without consumption of fish and meat.
5.4. ASSESSMENT OF BACKGROUND EXPOSURES ON THE BASIS OF BODY BURDEN
DATA
5.4.1. Human Adipose Tissue and Blood Data
Examination of body burden data provides another, potentially more accurate, way
to estimate exposures of humans to CDD/CDFs. However, these data may not represent
only background exposure to CDD/CDFs as defined here because the sampled individuals
may have lived in areas where dioxin sources were present. The most extensive U.S.
study of CDD/F body burdens is the National Human Adipose Tissue Survey (NHATS)
(EPA, 1991b). This survey analyzed for CDD/Fs in 48 human tissue samples that were
composited from 865 samples. Each composite contained an average of 18 specimens.
These samples were collected during 1987 from autopsied cadavers and surgical patients.
The sample compositing prevents use of these data to examine the distribution of CDD/F
levels in tissue among individuals. However, it did allow conclusions in the following
areas:
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• National Averages - The national averages for all TEQ congeners were
estimated as listed in Table 5-8. Nondetects were treated as half the
detection limit for averaging purposes. As shown in this table, all congeners
except some of the CDFs had a very low frequency of nondetects. Thus,
the overall TEQ estimate is not sensitive to how nondetects were treated in
the averaging.
• Age Effects - Tissue concentrations of CDD/Fs were found to increase with
age.
• Geographic Effects - In general the average CDD/F tissue concentrations
appeared fairly uniform geographically. Only one TEQ congener was found
to have a significant difference among geographic regions of the country.
This compound, 2,3,4,7,8-PeCDF, was found at the lowest level in the West
(4.49 pg/g) and the highest in the Northeast (13.7 pg/g).
• Race Effects - No significant difference in CDD/F tissue concentrations was
found on the basis of race.
« Sex Effects - No significant difference in CDD/F tissue concentrations was
found between males and females.
• Temporal Trends - The 1987 survey showed decreases in tissue
concentrations relative to the 1982 survey for all congeners. However, it is
not known whether these declines were due to improvements in the
analytical methods or actual reductions in body burden levels. The percent
reductions among individual congeners varied from 9 percent to 96 percent.
New information on levels of dioxin-like compounds in human tissue/blood has
recently been published (Patterson et al., 1994). Human adipose from 28 individuals was
collected. The individuals studied were ones that died suddenly in the Atlanta area during
1984 or 1986. Their ages ranged from 19 to 78 yr and averaged 49 yr. The tissue data
are summarized in Table 5-9. This table shows that the mean PCB levels generally
exceeded the mean 2,3,7,8-TCDD level and PCB-126 exceeded the 2,3,7,8-TCDD level by
over an order of magnitude. The mean TEQ levels for these coplanar PCBs summed to
about 17 ppt (using the toxic equivalency factors proposed by Safe, 1990). A complete
CDD/F congener analysis was conducted on tissues of five of the individuals, resulting in
an average of 25 ppt on a TEQ basis. These tissue samples were also analyzed for PCBs
77, 126 and 169. The TEQ levels for these coplanar PCBs summed to 8.2 ppt (using the
toxic equivalency factors proposed by Safe, 1990). Thus, the PCBs contributed 24% of
the total TEQs. Patterson et al. (1994) also studied serum collected by the CDC blood
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Table 5-8. NHATS Mean Adipose Tissue Data
Congener
2,3,7,8-TCDD
2,3,7,8-PeCDD
2,3,7,8-HxCDD
2,3,7,8-HpCDD
OCDD
2,3,7,8-TCDF
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
2,3,7,8-HxCDF
2,3,7,8-HpCDF
OCDF
TOTAL
• :':;'C0ngener%,
Concentration
(pg/g)
5.38
10.7
86.8
110
724
1.88
0.31
9.7
14.2
16
2.28
TE0 Concentration
..:,..„ :{p0/fi) -' .
5.38
5.35
8.68
1.1
0.72
0.19
0.016
4.85
1.42
0.16
0.002
27.9
Percent Detected3
97
97
97
100
100
100
14
95
2 to 92
4 to 89
30
a Based on analysis of 48 samples composited from 865 samples
Source: U.S. EPA (1990b)
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Table 5-9. Human Adipose Tissue Data
Chemical
2,3,7,8-TCDD
PCB 77
PCB 126
PCB 1 69
PCB 81
Range (ppt)
1 .6 to 38
Nondetect to 27.9
14.6 to 371
29. 5 to 174
1.5 to 21.3
- Mean (ppt)
10.4
11.7
135
69
10.5
Source: Patterson et al. (1994)
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bank in Atlanta during 1982, 1988 and 1989. These samples were pooled from over 200
donors. The average levels for 2,3,7,8-TCDD and PCBs are summarized in Table 5-10.
The serum data appears to indicate a decrease in exposure to PCBs from 1982 to
1988/1989. In general, the Patterson et al. (1994) data suggests that the coplanar PCBs
can contribute significantly to body burdens of dioxin-like compounds. The data suggest
that the coplanar PCBs can increase the total background body burden to over 40 ppt of
TEQ. This conclusion is uncertain because the people studied by Patterson et al. (1994)
may not be representative of the overall U.S. population, and the toxic equivalency factors
proposed by Safe (1990) have been acknowledged to be conservative.
Schecter et al. (1993) reported on the comparison of the congener-specific
measurement of CDDs, CDFs, and dioxin-like PCBs in whole blood samples of four
individuals with known exposures to that of the general population. In this comparison,
the analytical results of separate 450 ml blood samples collected from 50 Michigan
residents, and a pooled blood sample from 5 donors at a blood bank in Missouri were used
as the control group. Two of the exposed individuals were pulp and paper plant workers
with potential exposure to dioxins, and the other two were Michigan residents who had
elevated blood PCB levels from consuming contaminated fish. It was found that the
control group and the pulp and paper mill workers who had no known exposures to PCBs
had relatively high levels of coplanar, mono-ortho and di-ortho PCBs in their whole blood.
On average, the Michigan and Missouri control samples showed a mean CDD/CDF TEQ
concentration of 27 ppt and 25 ppt, respectively. These same samples showed PCB-TEQ
(based on Safe, 1990) mean concentrations of 66 ppt for the Michigan controls, and 45
ppt for Missouri controls.
Levels of these compounds found in human tissue/blood appear similar in Europe
and North America. Schecter (1991) compared levels of dioxin-like compounds found in
blood among people from U.S. pooled samples from 100 subjects and Germany (85
subjects). Although mean levels of individual congeners differed by as much as a factor of
two between the two populations, the total TEQ averaged 42 ppt in the German subjects
and was 41 ppt in the pooled U.S. samples. In a later report, Schecter et al. (1994a)
reported human blood levels for the general population from various countries. These data
are presented in Table 5-11. Schecter (1991) reports adipose tissue levels in various
countries, as summarized in Table 5-12. The adipose tissue data show more variation
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Table 5-10. Mean Levels in Human Serum (ppt)
Chemical
2,3,7,8-TCDD
PCB 77
PCB 1 26
PCB 1 69
Total PCBs
1988
0.159
0.481
0.183
0.151
3,100
1989
0.0165
0.251
0.135
0.192
Not Measured
1982
Not Measured
1.38
0.281
0.282
Not Measured
Source: Patterson et al. (1994)
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Table 5-11. CDD/CDF Levels in Human Blood from Various Countries
Country
USA
Germany
S. Vietnam (Ho Chi Minn)
S. Vietnam (Dong Nai)
N. Vietnam (Hanoi)
Guam
Soviet Union (St. Petersburg)
Siberia (Baikalsk)
Mean Blood Level
(ppt of TEQ, lipid) I
41
42
28
49
12
32
17
18
Number of Samples
100
85
50
33
32
10
50
8
Source: Schecter et al. (1994a)
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Table 5-12. Dioxin Levels in Human Adipose Tissues from Various Countries
Country
USA
Germany
China
Japan
Canada
S. Vietnam
N. Vietnam
Mean Tissue Level
(ppt of TEQ)
24
69
18
38
36
30
4
Number of Samples
15
4
7
6
46
41
26
Source: Schecter (1991)
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between countries but also involved much fewer samples, reducing confidence in the
accuracy of the mean. Beck et al. (1994) reported on levels of CDD/CDFs in adipose
tissue from 20 males (mean age-50 years) from Germany. TEQs ranged from 18 ppt to
122 ppt with a mean of 56 ppt, on a fat weight basis. Beck et al. (1994) also observed
that CDD/CDF levels were found to be dependent on the age of the individual. 2,3,7,8-
TCDD was found to increase at a rate of 0.12 pg/g fat per year, and TEQs increased at a
rate of 0.77 pg/g fat per year. Beck et al. (1994a) also reported on CDD/CDF levels in
various organs of the body. In comparison to adipose tissue, the concentrations of
CDD/CDFs in brain and placental tissue were found to be low. Accumulation of CDD/CDFs
was not found to occur in the thymus, spleen, and liver, based on whole weight
concentrations. Schecter et al. (1994a) also reported on TEQ levels in organs of two
autopsy patients from New York. The highest concentrations of CDD/CDFs were found in
adipose tissue (28 ppt TEQ), adrenal tissue (14 ppt TEQ), and liver (12 ppt TEQ), on a
whole weight basis. Lower concentrations were observed in spleen (4.6 ppt TEQ), muscle
(2.4 ppt TEQ), and kidney (0.8 ppt TEQ). Schecter et al. (1994b) reported PCB levels for
these two autopsy potients. Total PCBs in adipose tissue were 280.7 ppb on a wet
weight basis and 344.2 ppb on a lipid weight basis.
In Chapter 6, the level of 2,3,7,8-TCDD found in human adipose tissue is assumed
to average about 5.0 to 6.7 ppt in the United States based on data from a variety of
studies. These adipose tissue data were used to estimate the associated exposure levels
using a simple pharmacokinetic model that back calculates the dose needed to achieve the
observed adipose tissue levels under the assumption of steady state exposure/dose. This
model requires an estimate of the elimination rate constant. Based on available data, this
elimination rate constant was assumed to be about 5 to 7 years which yielded a
background dose rate of about 10 to 31 pg/day. This estimate agrees very well with the
background exposure estimates (to 2,3,7,8-TCDD only) of 35 pg/day by Travis and
Hattemer-Frey (1991), 25 pg/day by Furst et al. (1991) and 12 pg/day from this
assessment, all derived using typical media levels and contact rates. Further discussion of
body burden data and associated exposures is presented in Chapter 6. Chapter 6 presents
biologically-based pharmacokinetic models to estimate body burden levels. Some less
sophisticated approaches have also been presented in the literature. For example, Travis
and Hattemer-Frey (1988) developed linear relationships between the bioaccumulation of
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organic chemicals in human tissues and the octanol-water partition coefficients (Kow) of
the chemicals. The biotransfer factors (BTFs) that can be calculated using this relationship
can be used to estimate adipose tissue and breast milk concentrations of organics. The
BTF for human adipose tissue (Bf) is defined as the concentration of an organic in adipose
tissue (mg/kg) divided by the average daily intake of that organic (mg/day). The human
breast milk BTF (Bm) is defined as the concentration of an organic in breast milk (mg/kg)
divided by the average daily intake of that organic (mg/day). Adipose tissue and milk
concentrations are assumed to be equilibrium concentrations resulting from long-term,
consistent daily intake of an organic.
Measured tissue concentrations and either measured or estimated daily chemical
intakes were used to estimate the BTFs (12 chemicals for Bf and 6 chemicals for Bm).
Geometric mean regression analysis was used to ascertain the correlation between Kow
values and the calculated BTFs. The results of the analyses are as follows:
Bf = 3.2 x 10-4 Kow n = 12 r = 0.98
Bm = 6.2 x 10-4 Kow n = 6 r = 0.94
The high correlation coefficients demonstrate that the BTFs for human adipose tissue and
breast milk are strongly, positively correlated with the octanol-water coefficient. While the
data upon which these correlations are based are limited both in terms of number of
chemicals and the extent of measured vs. estimated intakes, the results are consistent
with results reported by Travis and Hattemer-Frey (1988) for beef and dairy cattle.
5.4.2. Dermal Exposure
Horstman and McLachlan (1994) measured CDD/F levels in human skin using an
adhesive tape stripping method. Skin samples of the stratum corneum were collected
from the backs of eight volunteers of varying age and sex. Two additional layers of
increasing depth were collected from 5 people. All showed a decrease in CDD/F levels
with depth. The concentration in the first layer ranged from 1,000 to 7,800 pg/g on a
total CDD/F basis. The second layer was an average of 43 percent lower and the third
layer was an average of 33 percent lower. OCDD was the dominant congener in all three
layers. Also, non-2,3,7,8 substituted congeners were identified, congeners which are not
normally present in human tissue.
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In addition, samples of the epidermis and subcutis were analyzed. These analyses
indicated that levels of the non-2,3,7,8 substituted congeners were much higher in the
stratum corneum than in the epidermis and none were identified in the subcutis. The
authors argue that because these congeners could not be transported from inside the body
to the stratum corneum, the CDD/F in the stratum corneum must originate from external
sources. Horstman and McLachlan (1994) hypothesized that textiles could be the source
of skin contamination. Thirdy-five new textiles, primarily cotton products, were analyzed
and found to have a total CDD/F level that was generally less than 50 ng/kg, but several
colored T-shirts had high levels, with concentration up to 290,000 pg/g. The homolog
patterns in the textiles were similar to the patterns found in the skin. Experiments were
then conducted measuring the CDD/F levels in human skin before and after wearing T-
shirts. Significant increases in CDD/F levels in the skin occurred after wearing the highly
contaminated shirts for 1-2 weeks and significant decreases in CDD/F levels in the skin
occurred after wearing the uncontaminated shirts for 1-2 weeks.
Thus, this work strongly suggests that dermal exposure to textiles may be
contributing to background exposures to CDD/Fs. Horstman and McLachlan (1994)
comment that although the levels of most CDD/F congeners in humans can be explained
on the basis of diet, the origins of OCDD in humans is less clear. Since OCDD was found
to be the dominant congener in textiles and skin, they speculate that the human body
burden of this congener may result from dermal absorption. Horstman and McLachlan
(1994) further discuss that human scale (stratum corneum) contributes to house dust and
could lead to exposure via inhalation.
5.5. HIGHLY EXPOSED POPULATIONS
Certain groups of people may have higher exposures to the dioxin-like compounds
than the general population. The following sections discuss higher exposures that result
from dietary habits. Other population segments can be highly exposed due to occupational
conditions or industrial accidents. For example, several epidemiological studies have
evaluated whether elevated dioxin exposure has occurred to certain workers in the
chemical industry, members of the Air Force who worked with Agent Orange, and
residents of Seveso, Italy who were exposed as a result of a pesticide plant explosion.
These epidemiological studies are fully discussed in the Epidemiology Chapter of the Dioxin
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Health Reassessment Document (EPA, 1994) and should be consulted if further details are
desired.
5.5.1. Nursing Infants
Schecter et al. (1992) reports that a study of 42 U.S. women found an average of
16 ppt of TEQ (3.3 ppt of 2,3,7,8-TCDD) in the lipid portion of breast milk. A much larger
study in Germany (n= 526) found an average of 29 ppt of TEQ in lipid portion of breast
milk (FCirst et al., 1994). Bates et al. (1994) analyzed breast milk samples from 38
women in New Zealand and reported mean lipid-based TEQs of 16.5 ppt for urban women
and 18.1 ppt for rural women. The age of the mother was found to be positively
correlated with the concentration of CDD/CDFs in breast milk. Beck et al. (1994) reported
a mean TEQ of 30 ppt in the milk fat based on 112 human milk samples from Germany.
The congeners that contributed the most to the total TEQ were 2,3,4,7,8-PeCDF (35
percent), total HxCDD (22 percent), and 1,2,3,7,8-PeCDD (21 percent). Beck et al.
(1994) observed that CDD/CDFs levels decreased with the number of children and the
duration of breast feeding, but increased with the age of the mother. Beck et al. (1994)
also compared the adipose tissue levels of breast-fed and bottle-fed infants who had died
of sudden infant death syndrome. The breast-fed infants had higher tissue levels (5.4 to
22 pg/g fat; n = 4) than the bottle-fed infants (2.1 to 4.4 pg/g fat; n = 2).
The levels in human breast milk can be predicted on the basis of the estimated
dioxin intake by the mother. Such procedures have been developed by Smith (1987) and
Sullivan et al. (1991) and are also presented in Chapter 6. The approach by Smith
assumes that the concentration in breast milk fat is the same as in maternal fat and can be
calculated as:
_ 777 h f\
Cmilk '*
0.693 f2
where,
Cmj|k fat = concentration in maternal milk (pg/kg of milk fat)
m = average maternal intake of dioxin (pg/kg of body weight/day)
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h = half-life of dioxin in adults (days)
f i = proportion of ingested dioxin that is stored in fat
\2 ~ proportion of mother's weight that is fat (kg maternal fat/kg total
body weight)
This steady-state model assumes that the contaminant levels in maternal fat remain
constant. Though not described here. Smith (1987) also presents more complex
approaches that account for changes in maternal fat levels during breast feeding. The
model developed by Sullivan et al. (1991) is a variation of the models proposed by
Smith (1987). The Sullivan model considers changes in maternal fat levels and predicts
chemical concentrations in milk fat as a function of time after breast feeding begins. The
model proposed by Smith assumes that infant fat concentration at birth is zero, whereas
Sullivan assumes that the infant fat concentration at birth is equal to the mother's fat
concentration.
As discussed in Chapter 6, the half-life of 2,3,7,8-TCDD in humans is estimated to
be 5 to 7 years. For the purpose of this preliminary analysis, it is assumed that a 7-year
half-life applies to all of the dioxin-like compounds. Smith (1987) suggests values of 0.9
for f1 and 0.3 for f2. Using these assumptions and a background exposure level of 1 to 3
pg of TEQ/kg-d (derived from diet analysis, see Section 5.3), the concentration in breast
milk fat is predicted to be about 10 to 30 ppt of TEQ, which agrees well with the
measured values.
Using the estimated dioxin concentration in breast milk, the dose to the infant can
be estimated as follows:
where,
ADDinfant = Average daily dose to the infant (pg/kg/d)
IRmilk = Ingestion rate of breast milk (kg/d)
ED = Exposure duration (yr)
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BWinfant = Body weight of infant (kg)
AT = Averaging time (yr)
f3 = Fraction of fat in breast milk
f4 = Fraction of ingested contaminant that is absorbed
This approach assumes that the contaminant concentration in milk represents the average
over the breast feeding time period. If the dynamic models mentioned above are used, the
dose can be estimated using an integration approach to account for the changes in
concentration over time.
Smith (1987) reports that a study in Britain found that the breast milk ingestion rate
for 7 to 8-month old infants ranged from 677 to 922 ml/d and that a study in Houston
measured the mean production of lactating women to range from 723 to 751 g/d. Smith
(1987) also reports that breast milk ingestion rates remain relatively constant over an
infant's life, that the milk can be assumed to have a 4 percent fat content, and that
90 percent of the ingested contaminant are absorbed. The National Center for Health
Statistics (1987) reports the following mean body weights for infants:
6-11 months: 9.1 kg
1 year: 11.3 kg
2 year: 13.3kg
Using Equation 5.2 and assuming that an infant breast feeds for 1 year, has an
average weight during this period of 10 kg, ingests 0.8 kg/d of breast milk, and that the
dioxin concentration in milk fat is 20 ppt of TEQ, the ADD to the infant over this period
(i.e., AT = 1 yr) is predicted to be about 60 pg of TEQ/kg-d. This value is much higher
than the estimated range for background exposure to adults (i.e., 1-3 pg of TEQ/kg-d).
However, if a 70 year averaging time is used, then the LADD (Lifetime Average Daily
Dose) is estimated to be 0.8 pg of TEQ/kg-d, which is near the lower end of the adult
background exposure range. On a mass basis, the cumulative dose to the infant under this
scenario is about 210 ng compared to a lifetime background dose of about 1700 to 5100
ng (suggesting that 4 to 12 percent of the lifetime dose may occur as a result of breast
feeding). Traditionally, EPA has used the LADD as the basis for evaluating cancer risk and
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the ADD (i.e., the daily exposure per unit body weight occurring during an exposure event)
as the more appropriate indicator of risk for noncancer endpoints. This issue is discussed
further in Chapter 6 and in the companion document on dioxin health effects.
The simplified procedure described above contains a number of uncertainties. A
tendency toward overestimates of the dose to the infant is caused by the assumption that
reductions do not occur in maternal fat levels during breast feeding. Sullivan et al. (1991)
estimates that the steady-state assumption may lead to overestimates of 20 percent.
Uncertainty is also introduced by the assumption that the assumed half-life rate and
partitioning factors apply to all the dioxin related compounds. Although these properties
are likely to be similar among the various congeners, some variation is expected. It is
unknown whether the net effect of these uncertainties would lead to over or under
estimates of dose. However, the simple model appears to provide reasonable predictions
of background levels found in breast milk and was judged adequate for purposes of a
preliminary analysis. For detailed assessments, readers should consider using the more
complex models and developing chemical-specific property estimates.
Travis and Hattemer-Frey (1988) presented an alternative approach to estimating
breast milk contaminant levels. They proposed a biotransfer approach:
Cm = Bml (Eqn. 5-3)
where:
Cm = contaminant concentration in breast milk (mg/kg)
Bm = biotransfer factor for breast milk (kg/d)
I = maternal intake of contaminant (mg/d)
They also argue that the biotransfer factor is primarily a function of the octanol-
water partition coefficient (Kow ) and developed the following geometric mean regression:
Bm = 6.2»10~4Kow (Eqn. 5-4)
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This regression was derived from data on 6 lipophilic compounds (log Kow range: 5.16 to
6.5), but did not include any dioxins or furans. Assuming a log KQW of 6.6 for 2378-
TCDD, a Bm of 3700 kg/d is predicted. Combing this value with a maternal intake of 10
pg/d (or 10~7 mg/d), a breast milk concentration of 37 ppt is predicted. This prediction is
about 10 times higher than what has been measured in the U.S. Thus, this approach does
not appear to work as well as the earlier approach suggested by Smith et at (1987).
5.5.2 Subsistence Fishers
The possibility of high exposure to dioxin as a result of fish consumption is most
likely to occur in situations where individuals consume a large quantity of fish from one
location where the dioxin level in the fish are elevated above background levels. Most
people eat fish from multiple sources and even if large quantities are consumed they are
not likely to have unusually high exposures. However, individuals who fish regularly for
purposes of basic subsistence are likely to obtain their fish from one source and have the
potential for elevated exposures. Such individuals may consume large quantities of fish.
EPA (1989) presents studies that indicate that recreational anglers near large water bodies
consume 30 g/day (as a mean) and 140 g/day (as an upper estimate). Wolfe and Walker
(1987) found subsistence fish ingestion rates up to 300 g/day in a study conducted in
Alaska.
Svensson et al. (1991) found elevated blood levels of CDDs and CDFs in high fish
consumers living near the Baltic Sea in Sweden. Three groups were studied:
nonconsumers (n = 9), moderate consumers (n = 9, 220 to 500 g/wk) and high consumers
(n = 11, 700-1750 g/wk). The high consumer group was composed of fishermen or
workers in the fish industry who consumed primarily salmon (30 - 90 pg TEQ/g) and
herring (8-18 pg TEQ/g) from the Baltic Sea. The TEQ blood level was found to average
about 60 pg TEQ/g lipid among the high consumers and 20 pg TEQ/g lipid for the
nonconsumers. This difference was particularly apparent for the PeCDFs.
Studies are underway to evaluate whether native Americans living on the Columbia
River in Washington have high dixoin exposures as a result of fish consumption. These
tribes consume large quantities of salmon from the river. A recent study (Columbia River
Intertribal Fish Commission, 1993) suggests that these individuals have an average fish
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consumption rate of 30 g/day and a 95th percentile rate of 170 g/day. Currently studies
are underway to measure dioxin levels in fish from this region.
Dewailly et al. (1994) observed elevated levels of coplanar PCBs in the blood of
fishermen on the north shore of the Gulf of the St. Lawrence River who consume large
amounts of seafood. Of the 185 study samples, the 10 samples with the highest total
PCB levels were analyzed for coplanar PCBs. Samples from Red Cross blood donors in
Ontario served as controls. Coplanar PCB levels were 20 times higher among the 10
highly exposed fishermen than among the controls. Based on these results of the 10
highest samples, Dewailly et al. (1994) estimated that for the entire fishing population
studied, coplanar PCB levels would be eight to ten times higher than the control group.
Dewailly et al. (1994) also observed elevated levels of coplanar PCBs in the breast milk of
Inuit women of Arctic Quebec. The principal source of protein for the Inuit people is fish
and sea mammal consumption. Breast milk samples were collected from 109 Inuit women
within the first three days after delivery and analyzed for di-ortho-coplanar PCBs during
1989 and 1990. Subsets of 35 and 40 randomly selected samples were analyzed for
mono-ortho coplanar and non-ortho coplanar PCBs, respectively. Samples from 96
Caucasian women from Quebec served as controls. The levels of non-ortho coplanar PCBs
for Inuit women ranged from 24.7 to 220.9 ppt. These values were 3 to 7 times higher
than those observed in the control group. For mono-ortho and di-ortho coplanar PCBS, the
levels among the Inuit women were three to ten times higher than in the control group.
5.5.3. Subsistence Farmers
The possibility of high exposure to dioxin as a result of consuming meat and dairy
products is most likely to occur in situations where individuals consume a large quantity of
these foods from one location where the dioxin level is elevated above background levels.
Most people eat meat and diary products from multiple sources and even if large quantities
are consumed they are not likely to have unusually high exposures. However, individuals
who raise their own livestock for purposes of basic subsistence have the potential for
elevated exposures. No epidemiological studies were found in the literature that evaluated
this issue. However, Volume III of this document presents methods for evaluating this
type of exposure on a site-specific basis.
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REFERENCES FOR CHAPTER 5
Bates, M.N.; Hannah, D.J.; Buckland, S.J.; Taucher, J.A.; Van Maanen, T. (1994)
Chlorinated organic contaminants in breast milk of New Zealand women.
Environmental Health Perspectives. Vol. 102, Suppl. 1:211-217.
Beck, H.; Dross, A.; Mathar, W. (1994) PCDD and PCDF exposure and levels in humans in
Germany. Environmental Health Perspectives. Vol. 102, Suppl. 1:173-185.
Columbia River Intertribal Fish Commission (1993) A fish consumption survey of the
Umtilla, Nez Perce, Yakima, and Warm Springs tribes of the Columbia River basin.
Peer Review Draft Report.
Dewailly, E.; Ryan, J.J.; Laliberte, C.; Bruneau, S.; Weber, J.P.; Gingras, S.; Carrier, G.
(1994) Exposure of remote maritime populations to coplanar PCBs. Environmental
Health Perspectives. Vol. 102, Suppl. 1:205-209.
Furst, P.; Fiirst, C.; Groebel, W. (1990) Levels of PCDDs and PCDFs in food stuffs from
the Federal Republic of Germany. Chemosphere 20(7-9): 787-792.
Furst, P.; Furst, C.; Wilmers, K. (1991) Body burden with PCDD and PCDF from food. In:
Gallo, M.; Scheuplein, R.; Van der Heijden, K. eds. Biological basis for risk
assessment of dioxins and related compounds. Banbury Report #35. Plainview,
NY: Cold Spring Harbor Laboratory Press.
FCirst, P.; Furst, C.; Wilmers, K. (1994) Human milk as a bioindicator for body burden of
PCDDs, PCDFs, organochlorine pesticides, and PCBs. Environmental Health
Perspectives. Vol. 102, Suppl. 1:187-193.
Oilman, A.; Newhook, R. (1991) An updated assessment of the exposure of Canadians to
dioxins and furans. Chemosphere 23(11-12): 1661-1667.
Henry, S.; Cramer, G.; Bolger, M.; Springer, J.; Scheuplein, R. (1992) Exposures and risks
of dioxin in the U.S. food supply. Chemosphere 25(1-2):235-238.
Hites, R.A. (1991) Atmospheric transport and deposition of polychlorinated dibenzo-p-
dioxins and dibenzofurans. Prepared for the U.S. Environmental Protection Agency,
Methods Research Branch, Atmospheric Research and Exposure Assessment
Laboratory, Office of Research and Development, Research Triangle Park, NC.
EPA/600/3-91/002.
Horstmann, M.; McLachlan, M.S. (1994) Textiles as a source of polychlorinated dibenzo-p-
dioxins and dibenzofurans (PCDD/F) in human skin and sewage sludge. Environ. Sci.
and Pollut. Res. 1(1): 15-20.
Koester, C.J.; Hites, R.A. (1992) Wet and dry deposition of chlorinated dioxins and
furans. Environ. Sci. Technol. 26:1375-1382.
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McCrady, J.K.; McFarlane, C.; Gander, L.K. (1990) The transport and fate of 2,3,7,8-
TCDD in soybean and corn. Chemosphere 21:359-376.
Patterson, D.G.; Todd, G.D.; Turner, W.E.; Maggio, V.; Alexander, L.R.; Needham, L.L.
(1994) Levels of nonortho-substituted polychlorinated biphenyls, dibenzo-p-dioxins,
and dibenzofurans in human serum and adipose tissue. Environmental Health
Perspectives. Vol. 101,Suppl. 1:195-204.
Safe, S. (1990) Polychlorinated biphenyl, dibenzo-p-dioxins, dibenzofurans, and related
compounds: environmental and mechanistic consideratins which support the
development of toxic equivalency factors. CRC Crit. Rev. Toxicol. 21:51-88.
Schecter, A. (1991) Dioxins and related chemicals in humans and in the environment. In:
Gallo, M.; Scheuplein, R.; Van der Heijden, K. eds. Biological basis for risk
assessment of dioxins and related compounds. Banbury Report #35. Plainview,
NY: Cold Spring Harbor Laboratory Press.
Schecter, A.; di Domenico, A.; Tirrio-Baldassarri, L.; Ryan, J. (1992) Dioxin and
dibenzofuran levels in milk of women from four geographical regions in Italy as
compared to levels in other countries. Presented at: Dioxin '92, 12th International
symposium on Chlorinated Dioxins and Related Compounds; Tampere, Finland;
August 1992.
Schecter, A.; DeVito, M.J.; Stanely, J.; Boggess, K. (1993) Dioxins, dibenzofurans and
dioxin-like PCBs in blood of Americans. Presented at: Dioxin '93, 13th
International Symposium on Chlorinated Dioxins and Related Compounds; Vienna,
Austria; September, 1993.
Schecter, A.; Furst, P.; Furst, C.; Papke, 0.; Ball, M.; Ryan, J.; Cau, H.D.; Dai, L.C.;
Quynh, H.T.; Cuong, H.Q.; Phuong, N.T.N.; Phiet, P.H., Biem, A.; Constable, J.;
Startin, J.; Samedy, M.; Seng, Y.K. (1994a) Chlorinated dioxins and dibenzofurans
in human tissue from general populations; a selective review. Environmental Health
Perspectives Vol. 102, Suppl. 1:159-171.
Schecter, A.; Stanley, J.; Boggess, K.; Masuda, Y.; Mes J.; Wolff, M.; Furst, P.; Furst, C.;
Wilson-Yang, K.; Chisholm, B. (1994b) Polychlorinated biphenyl levels in the tissues
of exposed and nonexposed humans. Environmental Health Perspectives. Vol. 102,
Suppl. 1:149-158.
Smith, A.H. (1987) Infant exposure assessment for breast milk dioxins and furans derived
from waste incineration emissions. Risk Analysis. 7(3):347-353.
Smith, R.M.; O'Keefe P.; Briggs, R.; Hilker, D.; Connor, S. (1992) Measurement of PCDFs
and PCDDs in air samples and lake sediments at several locations in upstate New
York. Chemosphere 25:1-2, pp. 95-98.
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Svensson, B.C.; Nelsson, A.; Hansson, M.; Rappe, C.; Akesson, B.; Skerfving, S. (1991)
Exposure to dioxins and dibenzofurans through the consumption of fish. New
England Journal of Medicine. 324(1):8-12.
Sullivan, M.J.; Custance, S.R.; Miller, C.J. (1991) Infant exposure to dioxin in mother's
milk resulting from maternal ingestion of contaminated fish. Chemosphere 23(8-
10):1387-1396.
Theelen, R.M.C. (1991) Modeling of human exposure to TCDD and I-TEQ in the
Netherlands: background and occupational. In: Gallo, M.; Scheuplein, R.; Van der
Heijden, K. eds. Biological basis for risk assessment of dioxins and related
compounds. Banbury Report #35. Plainview, NY: Cold Spring Harbor Laboratory
Press.
Theelen, R.M.C.; Liem, A.K.D.; Slob, W.; Van Wijnen, J.H. (1993) Intake of 2,3,7,8
chlorine substituted dioxins, furans, and planar PCBs from foods in the Netherlands,
median and distribution. Chemosphere. 27(9):1625-1635.
Travis, C.C.; Hattemer-Frey, H.A. (1987) Human exposure to 2,3,7,8-TCDD.
Chemosphere 16:2331-2342.
Travis, C.C.; Hattemer-Frey, H.A. (1988) Relationship between dietary intake of organic
chemicals and their concentrations in human adipose tissue and breast milk. Arch.
Environ. Contam. Toxicol. 17:473-478.
Travis, C.C.; Hattemer-Frey, H.A. (1991) Human exposure to dioxin. Sci. Total Environ.
104:97-127.
U.S. Department of Agriculture (1992) Food and nutrient intakes by individuals in the
United States, 1 day, 1987-88: Nationwide Food Consumption Survey 1987-88.
Washington, DC: USDA Human Nutrition Information Service. NFCS Rpt. No. 87-I-
1 in preparation.
U.S. Department of Agriculture (1993) Food consumption, prices, and expenditures, 1970-
1992. Washington, DC: USDA Economic Research Service. Statistical
Bulletin 867.
U.S. Environmental Protection Agency (1989) Exposure factors handbook. Washington,
DC: Office of Health and Environmental Assessment. EPA/600/8-89/043.
U.S. Environmental Protection Agency (1990a) Background document to the integrated
risk assessment for dioxins and furans from chlorine bleaching in pulp and paper
mills. Washington, DC: Office of Toxic Substances. EPA 560/5-90-014.
U.S. Environmental Protection Agency (1990b) Chlorinated dioxins and furans in the
general U.S. population: NHATS FY1987 results. Washington, DC: Office of
Toxic Substances. EPA 560/5-91-003.
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U.S. Environmental Protection Agency (1991a) Feasibility of environmental monitoring and
exposure assessment for a municipal waste combustion: Rutland Vermont Pilot
Study. Washington, DC: Office of Research and Development. EPA-600/8-91/007.
U.S. Environmental Protection Agency (1991b) Chlorinated dioxins and furans in the
general U.S. population: NHATS FY87 results, Washington, DC: Office of Toxic
Substances. EPA-560/5-91-003.
U.S. Environmental Protection Agency. (1994) Health Assessment for 2,3,7,8-TCDD and
related compounds, Washington, DC: Office of Research and Development. EPA
600/BP-9 2/001.
Welge, P.; Wittsiepe, J.; Schrey, P.; Ewers, U.; Exner, M.; Sclenka, F. (1993) PCDD/F-
levels in human blood of vegetarians compared to those of non-vegetarians.
Presented at: Dioxin '93, 13th International Symposium on Chlorinated Dioxins and
Related Compounds; Vienna, Austria; September 1993.
Wolfe, R.J.; Walker, R.J. (1987) Subsistence Economics in Alaska: Productivity, Geography
and Developmental Impacts. Arctic Anthropology 24(2):56-81.
Yang, Y-Y.; Nelson, C.R. (1986) An estimation of daily food usage factors for assessing
radionuclide intake in the U.S. population. Health Phys. 50(2):245-257.
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6. PHARMACOKINETICS
6.1. INTRODUCTION
The pharmacokinetic profiles of CDDs and the CDFs are quite complex. A thorough
analysis and understanding of these pharmacokinetic data would be very helpful in
ensuring that exposure assessments for these compounds are reliable. In addition, such
information would be useful in providing enhanced knowledge and understanding for the
purposes of risk assessment. Previous drafts of this chapter included a discussion on
bioavailability of CDD/Fs. Since this topic is only loosely related to pharmacokinetics, it
was decided to move this discussion to an appendix and it now appears in Appendix C of
this Volume.
Exposure to 2,3,7,8-TCDD and related compounds results in numerous species and
tissue specific toxic and biological responses. Many, if not, all of these responses are
mediated by a soluble intracellular protein, the aryl hydrocarbon (Ah) receptor, to which
2,3,7,8-TCDD binds with high affinity. After 2,3,7,8-TCDD and related compounds bind
to this Ah receptor the complex undergoes a transformation process involving dissociation
of hsp90. The transformed receptor complex is then able to bind with high affinity to a
specific DNA sequence referred to as a dioxin responsive enhancer (DRE). The conserved
nature of the DRE and Ah receptor is also indicated by the ability of transformed 2,3,7,8-
TCDD: Ah receptor complexes from a wide variety of species to bind to the DRE. Studies
also indicate a similarity in DNA recognition by Ah receptor from a variety of species
suggestive of a functional role of this sequence in 2,3,7,8-TCDD responsiveness (Denison
et al., 1991; Gasiewicz and Henry, 1991; Perdew and Hollenbeck, 1990; Andersen and
Greenlee, 1991). Thus the definition of "disposition" may have to be extended to include
suborgan or subcellular sites in order to more fully describe the congener, species, and
train specific pharmacokinetics (dosimetry) of these compounds.
Pharmacokinetic analysis may be used in several ways to aid in the exposure and
dose assessment of foreign chemicals. They may, for example, allow for predicting the
time and profile of elimination of chemicals from the body. The redistribution of CDDs
among the various tissues and organs, which may occur during elimination, can be
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accounted for and tracked. Effects on disposition which may result from altered
physiology, such as sudden weight loss or from lactation, can be incorporated and thus
adequately considered in exposure and risk assessments. Lactation is known to be an
efficient route for the transfer of many of these chemicals from mother to offspring (Nau
et al., 1986; Bowman et al., 1989).
Pharmacokinetic analyses can be used to estimate background exposure levels from
body burden data. They can also be used to estimate uptake rates from various food
sources, elimination rates and times from the body, and to estimate tissues levels from
blood and adipose tissue monitoring. In addition, with the appropriate data on several
congeners, estimates can be made for other congeners about which less data are available.
The remainder of this chapter will cover areas of pharmacokinetics pertinent to
exposure assessment. Background levels and daily uptake of 2,3,7,8-TCDD will be
reviewed and discussed; a method for the calculation of uptake of other congeners from
food will be outlined; use of a compartmental model to estimate daily uptake will be
demonstrated; a method will be outlined and reviewed for determining internal tissue
concentrations from monitored blood and/or adipose tissue; exposure through lactation will
also be discussed.
6.2. DAILY BACKGROUND LEVELS
6.2.1. Basis for Calculation
Physiologically based pharmacokinetic (PBPK) models are convenient and useful
methods for describing and predicting disposition of foreign chemicals in the body. These
models take into account physiologic and biochemical processes such as blood flows,
metabolism, and renal clearance, and describe the body according to its normal anatomy.
PBPK models can, given adequate data, predict disposition from one exposure scenario to
another and even from species to species. One such model was developed for 2,3,7,8-
TCDF (King et al., 1983) and is used here with some modifications. The anatomic regions
depicted in the King model are the blood, liver, fat, skin, and muscle. The remaining
organs of the body are lumped together as the "carcass." Input may be by a variety of
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routes, but for the purposes of this discussion is considered to occur through the
gastrointestinal system by continuous chronic dosing. This is consistent with the findings
of Chapters 4 and 5 that most of these compounds enter the body through the
gastrointestinal tract as a result of the consumption of products containing animal fat.
The pertinent equations follow.
For the liver:
dCr
dt
CL
Cr
-±
RL
(6-1)
Where,
KL
D
Volume of the liver
Concentration of toxin in blood
Concentration of toxin in liver
Time
Blood flow to liver
Equilibrium concentration ratio between liver and blood
Clearance term (L/time)
Input or dosing function
The clearance in the liver is considered to be by metabolic processes.
For the fat:
dCF
-
dt
(6-2)
Where all terms are analogous as those in Equation 6-1.
Note that there is no metabolic elimination assumed. The only disappearance of material
from the fat is assumed to be diffusion driven and is accounted for in the above mass
balance equation. Equations for the skin, carcass, and muscle are analogous to that for
fat.
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The equation for the blood is:
at
Where,
Q = Blood Flows
C = Concentrations
R = Equilibrium Concentration Ratios between tissue and blood
Subscripts:
B, L, F, M, S, C refer to blood, liver, fat, muscle, skin and carcass.
Some assumptions may be made to simplify the model for use to estimate daily
background doses. If steady state is assumed, then the equations for the individual organs
can be summed. The resultant equation for the liver is then:
D - (6-4)
RT
and at steady state
and
RF
and hence
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(6-7)
When clearance is expressed in days, D is the daily intake. Clearance can be approximated
from the half-life information according to the following equations:
KL = keVd
(6-8)
Where,
ke
vd
and
First order elimination rate constant
Volume of distribution
In2
'1/2
(6-9)
Where,
Biological half-life of compound in body
The volume of distribution may be estimated as in King et al., (1983) according to:
Where,
v-
R;
Volume of distribution of organ, i
Actual volume of organ, i
Equilibrium concentration ratio between organ i and blood
With substitution equation (6-7) becomes:
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D =
In2
/1/2
Where,
Vj = Volume of the organ in which toxin is measured
Cj ss = Steady state concentration of toxin in organ
It is important to note that two major assumptions are in effect when the above
formula is used to calculate average daily uptake. First steady state conditions are
assumed. Given that the half-life of some of these compounds (e.g., 2,3,7,8-TCDD) are at
least 5 years, it would take well over 15 years to reach 90 percent of steady state, and
over 30 years to reach 99 percent of steady state levels. Thus, the assumption of steady
state is only reasonable if background environmental concentrations are relatively similar
and constant throughout the nation. Under such conditions even the normal movement
from one geographical location to another would result in relatively constant exposures.
Also implicit in this assumption is that bioavailability is relatively constant through the
nation. Given that the source of this background exposure is believed primarily due to
consumption of foods containing animal fat (see Chapters 4 and 5), the assumption of
steady state for adults might be considered a reasonable assumption. Exceptions are
those individuals who may for a portion of their adult lives be consuming foods with
unusually high levels of these compounds. It would be expected, however, that those
individuals would have higher than average body burdens, and hence would not be
considered to have only average background exposure, but would rather be considered
part of a source-specific exposure group. Conditions such as sudden weight loss and
lactation would also alter the steady state condition. However, for purposes of calculating
daily background exposure levels the sampling of tissues for body burden must be so
designed to account for such deviations in the average. In summary, for adults (over 25
years of age) not in a source-specific exposure group, the steady state assumption is a
reasonable approximation. It should be remembered, however, that the longer the
biological half-life the longer it would take to reach steady state. A compound with a half
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life of 10 years, for example, would take over 50 years to reach 90 percent of the steady
state value.
The second major assumption is that these compounds are eliminated from the
body by monophasic kinetics. Biphasic elimination is very possible for many of these
compounds. Data gathered to calculate elimination rates or half-lives would only reveal
biphasic elimination profiles if gathered several years after the last exposure. Using only
the short term half-life would result in an underestimated value for half-life and an
overestimate of daily intake. This is particularly problematic for those compounds with
extremely long half-lives and for which few data exist. In Section 6.2.2., an approach to
calculating half-lives for some of these compounds will be presented. Also, the elimination
kinetics are assumed to be constant over the entire life of the individual. Sudden weight
loss and lactation would, for example, be conditions which violate that assumption.
Again, it would be assumed that for calculation of daily intake due to background exposure
the body burden data from such individuals would be identified and calculations handled
accordingly.
6.2.2. Daily Intakes
D
In2_
'1/2
D =
ln2
5.%years
»L ,000 £] J6.72M] [_1
D = 0.44 pglkglday
70KG 365days
Figure 6-1: Sample Calculation of Daily Intake for 2,3,7,8-TCDD
Figure 6-1 shows a sample calculation for 2,3,7,8-TCDD using the above
procedure. A fat volume of 14 L was chosen, representing 20 percent of the body weight.
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Also, for the purposes of this example, 1 ml of tissue was assumed to be equivalent to
1 gm.
Table 6-1 shows the estimated daily intake of 2,3,7,8-TCDD at several conditions.
The range of daily intakes calculated are in agreement with those reported elsewhere
(Furst etal., 1991; U.S. EPA, 1994).
In order to perform similar calculations for other congeners three pieces of
information are necessary. First, concentrations in the adipose tissues must be known.
Second, the half-lives of the compounds within the body must be known. Third, some
understanding of the kinetics and exposure conditions to assure that steady state
conditions were achieved at the time of monitoring.
Concentrations of various congeners in adipose tissues can be found in several
sources (Stanley et al., 1986; Schecter, 1991). Values range from around 2 ppt for
2,3,7,8-TCDF to several hundred ppt for 1,2,3,4,6,7,8,9-OCDD.
Half-lives could be determined from elimination data, if available. Methods have
been suggested to determine the half-lives of such compounds from uptake data relative
to 2,3,7,8-TCDD. Schlatter (1991) has proposed one such method. The following has
been adapted from that proposed method. Manipulation of Equation 6-11 results in:
r DTCDD
CTCDD =
Where,
CTCDD = Concentration of TCDD in body
DTCDD = Dai|V 'ntake °f TCDD
t1/2,TCDD = Half-life of TCDD in body
V ' = Volume of body compartment
For some other congener x:
C = * iri* (6-13)
* M2
Where symbols are same as for equation (6-12) and subscript x applies to compound x.
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Table 6-1. Calculated Daily Intakes for 2,3,7,8-TCDD
Half-life
(years)
5.8
7.0
5.8
7.0
5.8
7.0
5.8
7.0
• Fit Volume . '.'•%
; (liters) I :
14.0
14.0
14.0
14.0
7.0
7.0
7.0
7.0
'"': ':•;,:, &t--::,. '"•'•
Concentration
•v .:
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Thus the ratio of concentrations of TCDD to x can be described by:
CTCDD
cx
DTCDD
fl/2,TCDD V
In2
In2
v DX tm*
(6-14)
With algebraic manipulation and simplification Equation 6-14 becomes:
DTCDD
CTCDD
D
(6-15)
Assuming intake, D, to be mostly from the food, especially animal fat products, D can be
related to absorption from these foods according to:
DTCDD = (ka,TCDo) (ATCDD)
(6-16)
Where,
ka,TCDD
ATCDD
and
Absorption rate constant for TCDD
Concentration of TCDD in animal fat (diet)
(6-17)
Where,
ka,x
Absorption rate constant for x
Concentration of x in animal fat (diet)
As a result the half-life for compound x can be described by:
= f\l2JCDD
ATCDD
CTCDD
cx
AX
ka,TCDD
*a^c
(6-18)
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When the absorption rate constants for each congener are equal or when the difference
between them is small compared to differences in other parameters (concentration, half-
lives). Equation 6-18 can be further simplified to:
= fm,TCDD
ATCDD
CTCDD
(6-19)
Before using the above approach to calculate half-lives for some of the other
substances of interest it is well to briefly highlight one of the assumptions in this
approach. The relationship of half-life to elimination as described in Equation 6-9 only
applies to simple single compartment kinetics. These compounds would not necessarily be
expected to behave in such a manner. However, the error introduced by such an
assumption is not great if the one phase predominates over the other, or if it is
remembered that the calculation applies to one phase only. In fact, as will be discussed in
a subsequent section, it is believed that for these chemicals the relationship between half-
life and elimination as described here is a reasonable approximation.
It should be noted that for some of these substances exposure is expected from
other than food sources. For such cases Equation 6-18 would be modified to include
these other sources as follows:
~ fm,TCDD
y^ ka,i,TCDD At,TCDD
CTCDD
(6-20)
Where,
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ka,i,TCDD = Absorption rate constants for TCDD from each of the i media
Ai,TCDD = Concentration of TCDD in each of the i media
ka'j x = Absorption rate constants for x from each of the i media
Aj'x = Concentration of x in each of the i media
Other symbols: As previously defined
Again, if the differences between the absorption rate constants for TCDD and x are judged
to be small, then the variation of Equation 6-19 can be used, presented as Equation 6-21,
Table 6-2 shows the results of some half-lives calculated in this manner.
'1/2,* = rl/2,TCDD
'TCDD
(6-21)
The half-lives calculated using Equation 6-19 for the first three compounds in Table
6-2 agree with those calculated by Schlatter (1991). The large difference in the two
calculations for OCDD is due to significant differences in absorption rates between the
TCDD and the OCDD. Schlatter (1991) notes that for some compounds, including OCDD,
corrections were made of differences in absorption. No explanation was offered on how
this was done. In U.S. EPA (1993), results are summarized that indicate a possible
several-fold greater oral
absorption of TCDD over OCDD. This adjustment would result in a calculated half-life
closer to that calculated by Schlatter.
In summary, this section illustrates a method for calculating the half-lives of similar
behaving compounds. Several pieces of information are necessary: 1) the concentration
in the body of 2,3,7,8-TCDD; 2) the half-life of 2,3,7,8-TCDD; 3) the concentration of the
substance of interest in the body; 4) the concentration of the substance of interest in the
media from which exposure occurs; and 5) the differential absorption rates for TCDD and
the substance of interest.
From the half-life information, average daily intakes may be calculated, when
steady state can be assumed, by using Equation 6-12. Caution should be exercised when
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Table 6-2. Half-life Calculations
Congener
2378-TCDD
2378-TCDF
12378-PeCDD
23478-PeCDF
OCDD
Concentration
in Food3
{ppt}
0.23
0.84
0.7
1.4
19.2
Concentration
in Bodyb
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calculating daily intakes for those compounds with very long half-lives such as OCDD in
the above example.
6.3. COMPARTMENTAL MODELING
As previously discussed and also discussed elsewhere (U.S. EPA, 1994), PBPK
models are very useful for describing and predicting the disposition of chemicals in the
body. They are generally designed for predicting some measure of dose at a target site.
They are also used to extrapolate from one species to another, between different doses,
and between different routes of exposure. Several PBPK models have been published
specifically for 2,3,7,8-TCDD (Leung et al., 1990; Leung et al., 1988). Also, as previously
discussed, a model for 2,3,7,8-TCDF (King et al., 1983) is also available and from which
were derived the equations for estimating daily intake from body concentrations at steady
state conditions. Most of these models have been developed to describe in great detail the
metabolism and binding of TCDD within the body, for the purpose of estimating target
tissue dose.
6.3.1. Pharmacokinetic Model
Assuming a linear relationship between the concentrations in the fat and the body
at low exposure concentrations and the near linear elimination profile, a simpler model
relating exposure, whole body elimination, and whole body concentration is developed
here. As described earlier, after a prolonged exposure most of the body's organs can be
assumed to have very similar kinetic profiles and can thus be lumped together. The fat,
while sharing such a similar profile, is kept separate because of its important role in storing
most of the body burden and because it has been the most typically monitored tissue. The
three compartments in this model are blood, fat, and a "body" representing all other
tissues. The model is a flow- or perfusion-limited model with the assumption that the
toxin is well stirred or uniformly distributed within each compartment. The pertinent
equations for the model follow. The rate of change of concentration of toxin in the body is
estimated by:
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jr Qbo
dcbo
r Cbo
CB ~ ~p-
Rbo
- K(Cbo) + D
dt Vhn
(6-22)
Where:
dCbo/dt
Qbo
bo
V
bo
Rate of change of concentration of toxin in body (bo)
Blood flow (volume/time) to body
Concentration of toxin in blood (B)
Equilibrium concentration ratio of toxin between body and blood
Clearance (volume/time) of toxin from body
Volume of body
Intake of toxin
The rate of change of concentration of toxin in the fat is estimated by Equation 6-
23 below:
dCF
~~dT
QF
(6-23)
Where,
dCp/dt
Vr
= Rate of change of concentration of toxin in fat (F)
Blood flow (volume/time) to fat
Equilibrium concentration ratio of toxin between fat and blood
Volume of fat
The integral of the above differential equation (Eq. 6-23) over time gives the actual
concentration.
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The rate of change of concentration of toxin in blood is estimated by Equation 6-24
below:
dCB
dt
QF
CF
RF
+ QBO
Cbo
Rbo
- CB(QF H
V*
>Qbo>
(6-24)
Where,
dCb/dt
Rate of change of concentration of toxin in blood (B)
It should be noted that the description of intake is somewhat different than what is
typically found in most PBPK models. D here is actually a dose rate. That is, D is in terms
of pg/kg/day coming into the body as a dose, not just a concentration in the food, drinking
water, or air. The usual description for gastrointestinal absorption of toxin from food
would be
-Vc
(6-25)
Where,
k.
Absorption rate constant
Concentration of toxin in food
In this case, because of inadequate knowledge regarding the absorption rate constants for
many of the congeners, a dose rate is used instead. This does not allow for estimation of
body burden directly from environmental concentrations (e.g., Fc in Equation 6-25). As
more data are collected, more accurate values of the parameters and descriptions of
absorption functions can be input into Equation 6-22. For the present, other approaches
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can be used to relate concentration in the environmental media to daily intake (see Section
6.4.1).
6.3.2. Model Utilization
Most of the model's parameters are known or can be estimated from experimental
data for many of these toxins. For example, the equilibrium concentration ratios between
the fat and the body and between the fat and the blood for 2,3,7,8-TCDD are
approximately 10 and 100, respectively, on a tissue basis. The blood flows and
compartment volumes are well known. One parameter that had to be estimated when
applying this model to 2,3,7,8-TCDD was the clearance term K. This was done by first
allowing the model to simulate elimination as though exposure was suddenly terminated (D
becomes zero). Initial concentrations for the tissues were taken as those typically
expected in the general population (7.0 ppt in the fat). The value of K was then adjusted
until the model predicted a half-life of 7 years. Values of clearance for the other
compounds in this series would be determined similarly. The necessary information
includes the equilibrium concentration distribution ratios, the half-lives of the compounds,
and some reasonable approximation of steady state fat concentrations.
With an estimated value for the clearance, the model can now be used with various
exposure inputs to establish body burdens of toxin. The model can also be used to
estimate elimination profiles from the body. In addition, events such as lactation can be
incorporated into the model with knowledge about the appropriate parameters.
Figure 6-2 shows the results of the model run describing the elimination of 2,3,7,8-
TCDD from fat. The clearance rate was adjusted to predict a half-life of 7 years. The
same clearance value was used with different starting conditions (concentration of TCDD
in tissues) and the model produced a half-life of 7 years. Next, the model was used with a
constant daily intake as an input. Figure 6-3 shows the resulting profile of 2,3,7,8-TCDD
in the fat. Figure 6-3 shows the results of a model run using an input of 0.44 pg/kg/day.
Note that the steady state fat concentrations are approximately 7.0 ppt. The clearance
rate used in this model run had been independently determined in the previous run based
on reported half-life values. Thus, for these conditions this model does an adequate job of
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101T
d
CL
o
u
CD
10°-:
10-1
0.0
TCDD ELIfllNflTION FROM FRT
5.0
—I h-
10.0 15.0
time-years
20.0
25.0
Figure 6-2. Model Estimates of Elimination of 2,3,7,8-TCDD from Fat
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FflT CON. WITH DRILY: 0.44PG/KG/DRY
10
20 30 40 50
time~years
60
70
Figure 6-3. Accumulation of TCDD in Fat with 0.44 pg/kg/day dose - Human
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predicting tissue levels of 2,3,7,8-TCDD. Figure 6-4 shows a similar profile for a 0.30
pg/kg/day dose. The daily intakes chosen were similar to those calculated by the steady
state equations in Section 6.1.2 (Table 6-1). Note that the steady state fat levels
predicted by the pharmacokinetic model agree closely with those used as a starting point
for the steady state calculation using seven years for the half-life. This three compartment
model appears to provide reasonable approximations of body burden, at least under the
circumstances that have been tested. The necessary information for use with other
substances in this series include the equilibrium distribution ratios between fat and blood
and between fat and the rest of the body. An estimate of the half-life is also needed in
order to establish an appropriate value for the clearance term used in the model. Table 6-3
shows the results when the model was adjusted for other substances. The congener-
specific TEQ intakes can be added together to arrive at a TEQ-based total daily intake for
all the congeners of interest to a particular assessment.
Under certain circumstances, it might also be possible to use the compartmental
model on a total TEQ basis. Considering, for example, a mixture of dioxins and furans
whose collective biophysical properties are similar to those of 2,3,7,8-TCDD the model
could be applied to approximate daily intake from steady-state fat levels. For example,
Schecter (1991) reports the blood lipid levels in a sample of 85 persons from Germany to
be 42 ppt TEQ (CDDs and CDFs). Using that figure and the parameters of 2,3,7,8-TCDD,
the model calculates a daily intake of 2.64 pg TEQ/d/kg. Furst et. al (1991), based on
food consumption patterns of the German population, estimated a daily intake of 2.3 pg
TEQ/d/kg. Obviously great caution should be taken before using such an approach. Such
estimates should only be relied upon if there is strong evidence that the mix of congeners
is such that the collective properties of the mixture result in properties similar to those of
2,3,7,8-TCDD.
6.3.3. Determining Liver Concentrations from Fat Levels
As mentioned previously, higher resolution PBPK models are necessary to estimate
and predict concentration at cellular and sub-cellular targets (vidae supra). At the present
time, many of the data necessary to develop and apply these models to estimate target
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FRT CON, WITH DRILY: 0.30 PG/KG/DRY
5.0 n
10 20
30 40 50
time-years
60
Figure 6-4. Accumulation of TCDD in Fat with 0.30 pg/kg/day dose - Human
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Table 6-3. Model-Determined Daily Intakes
Congener
OCDD
1,2,3,7,8-
PeCDF
2,3,4,7,8-
PeCDF
Half-life
(yrs)*
50C
8
8
Fat Concentration
(ppt)b
1174.0
2.8
13.0
Intake
(pg/kg/day}
23.48
0.55
0.93
Intake-TEQ
(pg/kg/day)
0.02
0.03
0.47
a Taken from Table 6-2.
b Taken from Schecter (1991).
c Value determined by Schlatter (1991).
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tissue or cellular dose in humans are lacking. Andersen and Greenlee (1991) provide an
approach that uses the equations of a PBPK model (Leung et al., 1990) to predict liver
concentrations from monitored fat concentrations. It should also be noted that blood or
milk concentrations expressed on a per lipid basis could also be used. Basically the
approach calculates the ratio of fat to liver concentration by dividing the tissue
concentration equations of the PBPK model as follows:
PF
1
BMl
VD _i_ /"M/T
A/Jj + CKLr
BM2(7)
XB2 + CVL
CVL
CVF
(6-26)
Where,
CL,CF
CVL, CVF
PL,PF
VL
BM1r KB1
BM2(T)
KB2
Concentrations of toxin in liver and fat
Concentrations of toxin in venous blood from liver and fat
Liver:blood and Fat:blood partition coefficients of toxin
Volume of Liver compartment
Forward and reverse binding constants for binding of toxin with Ah
receptor
Forward binding constant with microsomal binding protein - time
dependent upon the amount of inducible microsomal binding protein
Reverse binding constant for microsomal binding protein
Andersen and Greenlee (1991) further simplify Equation 6-26 for various limiting
conditions. For the case of very low doses where CVL<
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For the case where KB2< >KB1, KB£, Equation 6-26 becomes:
^Hf n
^L "L
~CF = ^F
Andersen and Greenlee (1991) provide values for each of the above conditions for
experimental animals. It can be readily observed from examining Equation 6-26 that when
binding levels are very small the ratio of concentration between liver and fat is influenced
mostly by the ratio of partitioning coefficients.
With this approach and by knowing the necessary parameters Equation 6-26 can be
used to estimate liver concentrations from fat (including blood lipid and milk lipid)
concentrations. Andersen and Greenlee (1991) further suggest that most of the necessary
binding parameters can be determined from in-vitro studies. Further, the pharmacokinetic
model from which Equation 6-26 was derived can be used to estimate and predict cellular
concentrations (both free and bound) under various exposure conditions. The equations
used by Leung et al. (1990) or other like equations provide estimates of amount bound to
intracellular receptors sites, and can thus provide a relationship between multiple binding
sites. Denison et al. (1991) suggest that binding to the Ah receptor is only one of several
steps necessary for 2,3,7,8-TCDD to have an intracellular toxic effect. As further
knowledge becomes available about the mechanism and kinetics of each step, the model
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can be expanded to include these other processes such as DMA enhancing and hormonal
modulation. The pharmacokinetic model will therefore become a pharmacodynamic model
which will more explicitly link exposure to effect. Also, other tissues can be more
specifically described in the model, if the mechanism of action data so warrant.
6.4. INTAKES THROUGH DAILY EXPOSURE
6.4.1. Determination of Daily Intake Dose from Exposure Concentrations
As was discussed in Section 6.3.1, it would be most advantageous to know more
about the kinetics of absorption in the various animal species and the human. This is
necessary for both extrapolation between species in the risk assessment and for
determining body burdens from levels in the exposure media. For the time being, until
more data become available regarding the kinetic absorption constants, a slightly modified
approach can be used. Basically, the needed information is the concentration of the toxins
in the media, the fraction of toxin absorbed from each of the media, and the amount of
media coming into contact with the body. The following equation describes this in more
detail.
D = / U (6-30)
Where,
Daily Intake
Fraction absorbed from various i media
Concentration in various i media
Amount of contact of i media, (gm/time for food, L/time for air, etc.)
This approach should be used with caution. The major assumption which impacts
upon Equation 6-30 is that the fraction absorbed is constant across various concentrations
and doses. As discussed in Section 6.4.2 and in U.S. EPA (1994), this assumption cannot
always be considered to be sound. It most probably only applies at low doses and within
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any one species. It is an approach which, with care, can be used for certain conditions to
give estimates until more reliable kinetic absorption data become available.
6.4.2. Dose Through Lactation
There is great concern regarding the potential dose resulting from lactation. Given
the body burdens discussed in previous chapters and sections, lipid soluble substances
might be expected to compartmentalize into milk and thus be transferred to nursing
infants. Methods are needed to assess this potentially important route of exposure into
the body.
6.4.2.1. Concentration in the Milk
The first step to calculating the daily intake for infants is to determine the levels in
mother's milk. There are two general methods that can be used as a basis. The first
assumes that levels in maternal fat remain at steady-state and reach an equilibrium with
milk fat. Under these assumptions. Equation 5-1 (repeated here as Equation 6-31) can be
used to calculate the levels in maternal milk:
Cmilkfat = (6-31)
where,
cmilk fat = Concentration in maternal milk (pg/kg of milk fat)
m = Average maternal intake of dioxin (pg/kg body weight/day)
h = Half-life of dioxin in adults (days)
f^ = Proportion of ingested dioxin that is stored in fat
f2 = Proportion of mother's weight that is fat
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Application of this equation to 2,3,7,8-TCDD, where an intake of 0.5 pg/kg/day, a half-life
of 2555 days (7 years), 0.9 for f j and 0.3 for f2 are assumed, results in a concentration
in maternal milk fat of 5.6 ppt. This is higher than the 3.3 ppt. reported by Schecter
etal., (1989).
A second and theoretically more accurate approach uses some type of
physiologically based pharmacokinetic model to estimate the dynamically changing
concentrations in mother's milk. One way to accomplish this is to add a mammary
compartment to the compartmental model described in Section 6.3. The model is then
extended to depict the toxin's transport into the milk. In the simplest form the following
two equations would be added:
-) """ I /77/» ~-^ "— / /r+ f\ f\ \
, Rm! (6-32)
dt V,
ma
where,
dCma /dt = Change in the concentration of dioxin in mammary compartment
Qma = Blood flow to mammary compartment
Cb = Concentration of dioxin in blood
Rma = Mammary tissue to blood partition coefficient for dioxin
Fmj = Flow of milk
Rmj = Milk to mammary tissue partition coefficient for dioxin
Vma = Volume of mammary compartment
and
dCmi m'~Rml (6-33)
~dT =VW~~
where.
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dCmj/ /dt = Change in concentration of dioxin in mother's milk
Vmj = Volume of milk
Other symbols as previously defined.
When the model is actually implemented, the changes in proportion of body fat in
the mother that normally occur during lactation are taken into account. Observation of the
two previous equations quickly shows that several new parameters are now added to the
compartmental model. Many of these parameters have not been determined for most of
the congeners of interest. In fact, even some of the physiologic and anatomic parameters
are not readily available. Thus, for the time being it may be best to use some type of
steady-state model and Equation 6-31 or to actually use monitored data for calculating
dose to a lactating infant. It should be noted that the model was applied for 2,3,7,8-
TCDD and parameters were adjusted to predict levels near the 3.3 ppt value published by
Schecter et al. (1989). This is not a validation of the model or its parameters; of interest,
however, is that the model predicted the same ratio between milk lipids and plasma lipids
as reported by Schecter et al. (1989).
6.4.2.2. Dose to Infant
There are a number of measures of dose that can be used to compare the impact of
exposure through lactation versus exposure through background. A common measure of
dose, described in Chapter 5, is to calculate an average daily dose (ADD). Equation 5-2
(repeated here as Equation 6-34) describes such a calculation for the infant:
= Cmilk fat f3 U mmilk E° (6-34)
Bwinfant A r
where,
ADDinfant = Average daily dose to the infant (pg/kg/d)
IRmilk = 'ngestion rate of breast milk (kg/d)
ED = Exposure duration (year)
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BWinfant = Body weight of infant (kg)
AT = Averaging time (year)
f3 = Fraction of fat in breast milk
f4 = Fraction ingested contaminant which is absorbed
Assuming a concentration of 2,3,7,8-TCDD in milk fat of 3.3 ppt, values for f3 and f4 of
0.04 and 0.9, respectively, an average infant body weight of 10 kg, an exposure duration
of one year, an ingestion rate of milk of 800 g/d, and an averaging time of one year, an
ADD equal to 9.5 pg/kg/d is calculated. Using the same assumptions, except for an
averaging time of 70 years (the entire assumed lifetime), an ADD equal to 0.135 pg/kg/d is
calculated. Thus, depending upon the averaging time, lactation results in ADD similar to
that resulting from background (0.135 pg/kg/d compared to 0.51 pg/kg/d) or an ADD over
an order of magnitude higher (9.5 pg/kg/d compared to 0.51 pg/kg/d). Little agreement
exists regarding the appropriate choice of an averaging time for less than lifetime
exposures. This is especially true for cases where exposure is occurring in a particularly
sensitive developmental period. Lifetime averaging may be used for long time or even
lifetime exposures, but the logic of applying it to short exposures is not clear.
Equally unclear is the utility of the ADD calculation itself. The ADD is actually an
average intake over an arbitrarily chosen period of time. The significance of the ADD is
not apparent, especially in cases of compounds, such as the CDDs and CDFs, that reach
steady-state levels during chronic exposure.
It is recommended that other measures of dose be examined. As advanced and
new mechanistic knowledge develops, new measures of dose should be used and
examined. Recent studies (Andersen and Greenlee, 1991; Andersen et al., 1993) show
the importance of receptor-mediated processes. The actual lexicologically relevant dose
may be related to the induced production of specific hepatic proteins. Scientific research is
still needed to determine the exact role these play in the various toxic responses that may
be caused by the CDDs and CDFs. As this type of mechanistic information develops, and
its relevance to humans becomes better established, pharmacokinetic models will be
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expanded to become pharmacodynamic models and then more realistic measures of dose
can be determined.
For the time being, macroscopic measures other than the ADD should also be
examined for assessment purposes. One approach to estimating such measures is to use
the compartmental model described in Section 6.3. For the case of infants and children,
the model is modified to account for the changing body weight of the child during the first
20 years of life. The model is used here under each of the three following exposure
conditions for 2,3,7,8-TCDD:
• One year lactational exposure at levels corresponding to a milk fat
concentration of 3.3 ppt followed by 69 years exposure at levels
corresponding to background daily intakes of 0.51 pg/kg/d.
• 70 year exposure at levels corresponding to background daily intakes of
0.51 pg/kg/d.
• One year lactation exposure at milk fat concentration of 3.3 ppt.
Results of the simulation reveals several things. Figures 6-5 through 6-7 show the
fat concentration profiles after the above three exposure scenarios for 2,3,7,8-TCDD.
Figure 6-5 shows the fat level to peak quickly during the lactation period and then diminish
until it reaches the steady-state level of about 8.0 ppt (8000 pg/kg). This is contrasted to
Figure 6-6 where only background (no lactation exposure) is simulated. Note that in both
cases the steady-state fat levels are 8.0 ppt. Lactation causes a temporary peak that
diminishes over the next several years. Figure 6-7 shows the results of the simulation for
the lactational phase only. This scenario assumed no further exposure after lactation
ceased and was performed to investigate the impact of the lactational exposure apart from
background exposure. Note that the half-life during the childhood years is shorter than
that for adults (discussed in previous sections). This shorter half-life may be attributed to
the changing size of the body and the compartments represented in the model. In fact,
after age 20 (after which the body weight is assumed to remain constant) the model
predicts the same half-life as previously discussed (7 < t1/2 ^ 8 years). Careful
inspection
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10
20
30 40 50
TIME years
60
70
Figure 6-5. Combined Exposure Adipose Tissue Concentration
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10 20 30 40
TIME years
50
60
70
Figure 6-6. Background Exposure Adipose Tissue Concentration
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8 12
TIME years
16
20
Figure 6-7. Concentration After Lactational Exposure Only
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of Figures 6-5 and 6-6 also reveals that the time to reach steady-state is the same as
discussed in previous sections {> 30 years).
Other measures of dose can also be used for comparison purposes. Care should be
taken when ascribing meaning to different measures of dose, especially when exposure
patterns of widely different duration are compared. Additional complexity is added by the
fact that the lactational exposure occurs during the early developmental period of the
individual. Given, these caveats, it may still be worthwhile to look at time integral (area
under the curve or AUCs) measures of mass that has resided in the body throughout the
exposure period. This is not a simple calculation of intake, but rather a measure of
cumulative mass within the body as calculated by the model. The time integral of the
mass in the body compartment (AUCBO) is used here for discussion and comparison.
Lactation exposure during the first year and background exposure during the remaining 69
years results in an AUCBO at 70 years of 3.01 X 106 pg-years. Seventy years of
background exposure with no lactational exposure results in 2.95 X 106 pg-years. The
one year lactation exposure results in 7,862 pg-year at the one year mark. Obviously, in
terms of pg-years the contribution from lactation is minor compared to background
exposure.
It is not clear, however, whether this is an appropriate measure of dose to compare
exposure patterns occurring at very different times of the lifetime. This same measure of
dose can be averaged over the exposure time and then compared. The results appear
different when the above three AUCBOs are converted to a pg/kg/day basis. The AUCBO
averaged over exposure for the combined lactation and background exposure is 1.68
pg/kg/day ([3.01 X 106 pg-years]/70 kg/[365 d X 70 years]), 1.64 pg/kg/day for the
background only case, and 2.15 pg/kg/day {[7,862 pg-years]/10 kg/365 d X 1 year]) for
the lactational portion of exposure. Using this time-averaged measure, it appears that the
one year lactational phase contributes slightly more, on a daily average basis, than the 69
year background phase. In addition, for some toxic end-points the first year of life may be
more vulnerable than later years. How any of these measures are related to risk remains
unknown and caution should be exercised before drawing conclusions. The goal here is to
present different methods that might be used for comparison purposes. As mentioned
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previously, as the mechanisms of action become better elucidated other more appropriate
measures of dose should be used to make relative risk comparisons.
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REFERENCES FOR CHAPTER 6
Andersen, M.E.; Mills, J.J.; Gargas, M.L.; Kedderis, L; Birnbaum, L.S.; Neuber, D.;
Greenlee, W.F. (1993) Modelling receptor-mediated processes with dioxin:
implications for pharmacokinetics and risk assessment.
Andersen, M.E.; Greenlee, W.F. (1991) Biological determinants of TCDD pharmacokinetics
and their relation a biologically based risk assessment. In: Biological Basis for Risk
Assessment of Dioxins and Related Compounds; Michael, G.; Scheuplein, R.; Van
Der Heijden, K. eds.; Banbury Report 35, Cold Spring Harbor Laboratory Press.
Bowman, R.E.; Schantz, S.L.; Weerasinghe, N.C.A.; Gross, M.L.; Barsotti, D.A. (1989)
Chronic dietary intake of 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) at 5 or 25
parts per trillion in the monkey: TCDD kinetics and dose-effect estimate of
reproductive toxicity. Chemosphere 18(1-6):243-252.
Denison, M.S.; Phelphs, C.L.; Dehoog, J.; Kim, H.J.; Bank, P.A.; Yao, E.F. (1991) Species
variation in Ah receptor transformation and DMA binding. In: Biological Basis for
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Der Heijden, K. eds.; Banbury Report 35, Cold Spring Harbor Laboratory Press.
Furst, P.; Fiirst, C.; Wilmers, K. (1991) Body burden with PCDD and PCDF from food. In:
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Scheuplein, R.; Van Der Heijden, K. eds.; Banbury Report 35, Cold Spring Harbor
Laboratory Press.
Gasiewicz, T.A.; Henry, B.C. (1991) Different forms of the Ah receptor: possible role in
species- and tissue-specific responses to TCDD. In: Biological Basis for Risk
Assessment of Dioxins and Related Compounds; Gallo, M.; Scheuplein, R.; Van Der
Heijden, K. eds.; Banbury Report 35, Cold Spring Harbor Laboratory Press.
King, F.G.; Dedrick. R.L.; Collins, J.M.; Matthews, H.B.; Birnbaum, L.S. (1983)
Physiological model for the pharmacokinetics of 2,3,7,8-tetra-chlorodibenzofuran in
several species. Toxicology and Applied Pharmacology 67:390
Leung, H.; Paustenbach, J. (1987) A proposed occupational exposure limit for 2,3,7,8-
tetrachlorodibenzo-p-dioxin. Palo Alto, CA: Environmental Health and Safety,
Syntex, U.S.A. Inc.
Leung, H-W.; Ku, R.H.; Paustenbach, D.J.; Andersen, M.E. (1988) A physiologically based
pharmacokinetic model for 2,3,7,8-tetra-chlorodibenzo-p-dioxin in C57BL/6J and
DBA/2J mice. Toxicology Lett. 42:15-28.
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Leung, H-W.; Poland, A.; Paustenbach, D.J.; Murray, F.J. Andersen, M.E. (1990)
Pharmacokinetics of [125l]-2-iodo-3,7,8-trichlorodibenzo-p-dioxin in mice: analysis
with a physiological modeling approach. Toxicology and Applied Pharmacology
103:411-419.
McConnell, E.E.; Lucier, G.W.; Rubaugh, R.C.; et al. (1984) Dioxin in soil: bioavailability
after ingestion by rats and guinea pigs. Science 223:1077-1079.
Nau, H.; Bab, R.; Neuber, D. (1986) Transfer of 2,3,7,8-tetrachlorodibenzo-p-dioxin
(TCDD) via placenta milk, and postnatal toxicity in mouse. Arch. Toxicol. 59:36-
40.
Perdew, G.H.; Hollenbeck, C.E. (1990) Analysis of photoaffinity labeled aryl hydrocarbon
receptor heterogeneity by two dimensional gel electrophoresis. Biochemistry 29:
6210-6214.
Schecter, A.; Furst, P.; Ryan, J.J.; Furst, C.; Meemken, H.A.; Groebel, W.; Constable, J.;
Vu, D. Polychlorinated dioxin and dibenzofuran levels from human milk from several
locations in the United States, Germany, and Vietnam. Chemosphere 19(1-6):979-
984.
Schecter, A. (1991) Dioxins and related chemicals in humans and in the environment. In:
Biological Basis for Risk Assessment of Dioxins and Related Compounds; Gallo, M.;
Scheuplein, R.; Van Der Heijden, K. eds.; Banbury Report 35, Cold Spring Harbor
Laboratory Press.
Schlatter, C. (1991) Data on kinetics of PCDDs and PCDFs as a prerequisite for human risk
assessment. In: Biological Basis for Risk Assessment of Dioxins and Related
Compounds; Gallo, M.; Scheuplein, R.; Van Der Heijden, K. eds.; Banbury Report
35, Cold Spring Harbor Laboratory Press.
Stanley, J.S.; Boggess, K.; Onstot, J.; Sack, T.; Remmers, J.; Breen, J.; Kutz, F.W.;
Robinson, P.; Mack, G. (1986) PCDDs and PCDFs in human adipose tissues from
the EPA FY82 NHATS repository. Chemosphere 15:1605-1612.
U.S. Environmental Protection Agency (1994) Health assessment for 2,3,7,8-
tetrachlorodibenzo-p-dioxin (TCDD) and related compounds. Washington, DC:
Office of Health and Environmental Assessment. Public review draft. EPA/600/EP-
92/001.
Whitlock, J.P., Jr. (1991) Mechanism of dioxin action: relevance to risk assessment. In:
Biological Basis for Risk Assessment of Dioxins and Related Compounds; Gallo, M.;
Scheuplein, R.; Van Der Heijden, K. eds.; Banbury Report 35, Cold Spring Harbor
Laboratory Press.
6-37 4/94
-------
DRAFT-DO NOT QUOTE OR CITE
APPENDIX A. ENVIRONMENTAL CHEMISTRY
The tables in this appendix are discussed in Chapter 2. References listed at the end
of each table are included in the reference list at the end of Chapter 2. Following are the
tables included in this Appendix:
Page
Table A-1. Physical and Chemical Properties For the Dioxin, Furan,
and PCS Congeners A-2
Table A-2. Rankings For the Physical and Chemical Property
Literature A-17
-------
Table A-l. P-Chem Properties for the Dioxin, Furan, and PCB Congeners
Chemical
CAS No.
1,2,3,4-TCDD
30746-58-8
1,2,3,6-TCDD
71669-25-5
1,2,3,7-TCDD
67028-18-6
1,2,3,8-TCDD
53555-02-5
1,2,3,9-TCDD
71669-26-6
1,2,4,6-TCDD
71669-27-7
1,2,4,7-TCDD
71669-28-8
1,2,4,8-TCDD
71669-29-9
1,2,4,9-TCDD
71665-99-1
1,2,6,7-TCDD
40581-90-6
1,2,6,8-TCDD
67323-56-2
Water
Solubility
nag/I"
4.70E-07-
6.30E-04
4.30E-04
WS
Temp.
25
20
WS
Ref.
5,38,46
6
Vapor
Pressure
mm Hg*
VP
Temp.
VP
Ref.
Henry's
Constant
atm-m'/mol"
Henry's
Constant
Ref.
Log
K^'
Tettachlorodibenzo-p-dioxins (MW = 32 1 .98)
1.81E-08-
4.80E-08
(7.5E-09)
25
25
9,33
9
(3.7E-05)
(7.4E-06)
5
19
(5.9)-
(8.8)
6.86
6.48-
(8.5)
6.48
6.39
6.10
6.25
6.25
6.10
6.43
Log
K-
Ref.
Log
K«'
Log
K«
Ref.
Photo
Quantum
Yield*
5,7,8,10
,26,29
10
7,8,10,
26
10
10
10
10
10
10
10
5.97
45
5.42E-04C
Photo
Quant.
Yield
Ref.
24
A-2
-------
Table A-l (continued)
Chemical
CAS No.
1,2,6,9-TCDD
40581-91-7
1,2,7,8-TCDD
34816-53-0
1,2,7,9-TCDD
71669-23-3
1,2,8,9-TCDD
62470-54-6
1,3,6,8-TCDD
33423-92-6
1,3,6,9-TCDD
71669-24-4
1,3,7,8-TCDD
50585-46-1
1,3,7.9-TCDD
62470-53-5
1,4,6,9-TCDD
40581-93-9
1,4,7,8-TCDD
40581-94-0
2,3,7,8-TCDD
1746-01-6
Congener Group Average
Water
Solubility
mg/P
3.20E-04-
(6.0E-04)
7.91 E-06-
4.83E-04
(3.5E-04)
WS
Temp.
20-25
17-22
25
WS
Ref.
6,7,38
1,2,27,
36,50
20
Vapor
Pressure
mmHg*
(5.2E-09)-
4.03E-06
(6.3E-09)
7.40E-10-
3.38E-08
(8.1E-07)
VP
Temp.
20-25
25
25
25
VP
Ref.
7,9
9
2,3,9,
34
20
Henry's
Constant
atm-m'/mol*
6.81E-05
(1.6E-05)
(3.2E-05)
Henry's
Constant
Ref.
7
2,3
20
Log
K..'
6.38
6.86
6.29-
(9.0)
6.25
6.30
6.39-
7.06
6.38
6.39
6.42-
(7.0)
(6.4)
Log
K«
Ref.
10
10
7,8,10,
26
10
10
8,10
10
10
2,4,8,10
50
20
Log
K-'
5.68-
7.42
(6.2)
Log
K«
Ref.
32,47
48,49
50
20
Photo
Quantum
Yteld*
2.17E-031
2.2E-03"-
3.3E-02d
Photo
Quant.
Yield
Ref.
24
22,30
A-3
-------
Table A-l (continued)
Chemical
CAS No.
Water
Solubility
mg/1*
ws
Temp.
WS
Ref.
Vapor
Pressure
mm Hg*
VP
Temp.
VP
Ref.
Henry's
Constant
atm-m'/mol'
Henry's
Constant
Ref.
Log
K..'
Log
K«
Ref.
Log
K«'
Log
K«
Ref.
Phofo
Quantum
Yield'
Photo
Quant.
Yield
Ref.
Pentachlorodibenzo-p-dioxins (MW= 356.42)
1, 2,3,4,6 PeCDD
67028-19-7
1,2,3,4,7-PeCDD
39227-61-7
1,2,3,6,7-PeCDD
71925-15-0
1,2,3,6,8-PeCDD
71925-16-1
1,2,3,6,9-PeCDD
82291-34-7
1,2,3,7,8-PeCDD
40321-76-4
1,2,3,7,9-PeCDD
71925-17-2
1,2,3,8,9-PeCDD
71925-18-3
1,2,4,6,7-PeCDD
82291-35-8
1,2,4,6,8-PeCDD
71998-76-0
1,2,4,6,9-PeCDD
82291-36-9
1.20E-04-
(1.7E-04)
20-25
6,38
(6.6E-10)
(4.4E-10)-
9.48E-10
25
25
9
9,33
(2.6E-06)
19
6.30
6.60-
(9.7)
6.74
6.53
6.24
6.64
6.40
6.60
10
7,8,10,
26
10
10
10
10
10
10
5.68
45
9.8E-05C
23
A-4
-------
Table A-l (continued)
Chemical
CAS No.
1,2,4,7,8-PeCDD
58802-08-7
1,2,4,7,9-PeCDD
82291-37-0
1,2,4,8,9-PeCDD
82291-38-1
Congener Group Average
Water
Solubility
rag/1'
(1.2E-04)
WS
Temp.
20
WS
Ref.
20
Vapor
Pressure
mmHg*
(5.8E-10)
(7.3E-10)
VP
Temp.
25
25
VP
Ref.
9
20
Henry's
Constant
atm-nrVmoP
(2.6E-06)
Henry's
Constant
Ref.
20
Log
K~'
6.20
(6.6)
Log
K«
Ref.
10
20
Log
K«'
(5.7)
Log
K«
Ref.
20
Photo
Quantum
Yield*
Photo
Quant.
Yield
Ref.
Hexachlorodibenzo-p-dioxins(MW=390.87)
1,2,3,4,6,7-HxCDD
58200-66-1
1,2,3,4,6,8-HxCDD
58200-67-2
1,2,3,4,6,9-HxCDD
58200-68-3
1,2,3,4,7,8-HxCDD
39227-28-6
1,2,3,6,7,8-HxCDD
57653-85-7
1,2,3,6,7,9-HxCDD
64461-98-9
1,2,3,6,8,9-HxCDD
58200-69-4
4.40E-06
20
6
(3.8E-11)-
1.01E-10
(3.6E-11)
25
25
9,33
9
(1.2E-05)
19
6.85
7.79-
(11)
7.59
7.59
10
7,8,26
10
10
5.92
45
1.1E-04'
23
A-5
-------
Table A-l (continued)
Chemical
CAS No.
1,2,3,7,8,9-HxCDD
19408-74-3
1,2,4,6,7,9-HxCDD
39227-62-8
1,2,4,6,8,9-HxCDD
58802-09-8
Congener Group Average
Water
Solubility
mg/r
(4.4E-06)
ws
Temp.
20
WS
Ref.
20
Vapor
Pressure
mm Hg*
(4.9E-11)
(5.1E-11)
(5.9E-11)
VP
Temp.
25
25
25
VP
Ref.
9
9
20
Henry's
Constant
atm-m'/mol1
(1.2E-05)
Henry's
Constant
Ref.
20
Heptachlorodibenzo-p-dioxins (M W = 425 .31)
1,2, 3,4,6,7, 8-HpCDD
35822-46-9
1,2,3,4,6,7,9-HpCDD
58200-70-7
Congener Group Average
2.40E-06
(2.4E-06)
20
20
6
20
(5.6E-12)-
3.21E-11
(3.2E-11)
25
25
9,33
20
(7.5E-06)
(7.5E-06)
19
20
Log
K.."
6.85
6.85
(7.3)
8.20-
(12)
(8.2)
Log
K«
Ref.
10
10
20
Log
K«'
(5.9)
Log
K«
Ref.
20
Photo
Quantum
Yield'
Photo
Quant.
Yield
Ref.
7,8,26
20
1.53E-05C
23
Octachlorodibenzo-p-dioxin(MW=460.76)
1,2,3,4,6,7,8,9-OCDD
3268-87-9
7.4E-08-
4.00E-07
20-25
5,6,7
8.25E-13-
6.54E-08
20-25
7,9,
33
(6.7E-06)
5
(7.5)-
(13)
5,7,8,26
,29
2.26E-05'
23
TetrachJorodibenzofurans (MW= 305.98)
1,2,3,4-TCDF
30402-14-3
1,2,3,6-TCDF
83704-21-6
(3.1E-08)
25
21
6.17
6 15
10
10
A-6
-------
Table A-l (continued)
Chemical
CAS No.
1,2,3,7-TCDF
83704-22-7
1,2,3,8-TCDF
62615-08-1
1,2,3,9-TCDF
83704-23-8
1,2,4,6-TCDF
71998-73-7
1,2,4,7-TCDF
83719-40-8
1,2,4,8-TCDF
64126-87-0
1,2,4,9-TCDF
83704-24-9
1,2,6,7-TCDF
83704-25-0
1,2,6,8-TCDF
83710-07-0
1,2,6,9-TCDF
70648-18-9
1,2,7,8-TCDF
58802-20-3
1,2,7,9-TCDF
83704-26-1
Water
Solubility
rng/1-
WS
Temp.
WS
Ref.
Vapor
Pressure
mm Hg*
(3.2E-08)
(2.1E-08)
(2.2E-08)
(2.0E-08)
(1.8E-08)
(2.5E-08)
VP
Temp.
25
25
25
25
25
25
VP
Ref.
21
21
21
21
21
21
Henry's
Constant
atm-mVmoI*
Henry's
Constant
Ref.
Log
K~*
6.15
6.06
6.31
6.25
6.23
6.25
Log
K«
Ref.
10
10
10
10
10
10
Log
K«'
Log
K«
Ref.
Photo
Quantum
Yield-
Photo
Quant.
Yield
Ref.
A-7
-------
Table A-l (continued)
Chemical
CAS No.
1,2,8,9-TCDF
70648-22-5
1,3,4,6-TCDF
83704-27-2
1,3,4,7-TCDF
70648-16-7
1,3,4,8-TCDF
92341-04-3
1,3,4,9-TCDF
83704-28-3
1,3,6,7-TCDF
57117-36-9
1,3,6,8-TCDF
71998-72-6
1,3,6,9-TCDF
83690-98-6
1,3,7,8-TCDF
571 17-35-8
1,3,7,9-TCDF
64560-17-4
1,4,6,7-TCDF
66794-59-0
1,4,6,8-TCDF
82911-58-8
Water
Solubility
mg/1*
WS
Temp.
WS
Ref.
Vapor
Pressure
nun Hg*
(2.8E-08)
(2.7E-08)
(1.9E-08)
(2.6E-08)
VP
Temp.
25
25
25
25
VP
Ref.
21
21
21
21
Henry's
Constant
atm-nrVmoI"
Henry's
Constant
Ref.
Log
K..'
6.31
6.23
6.13
5.89
6.37
6.34
6.34
6.15
Log
K..
Ref.
10
10
10
10
10
10
10
10
Log
K»
«
Log
K«
Ref.
Photo
Quantum
Yield-
Photo
Quant.
Yield
Ref.
A-8
-------
Table A-l (continued)
Chemical
CAS No.
1,4,6,9-TCDF
70648-19-0
1,4,7,8-TCDF
83704-29-4
1,6,7,8-TCDF
83704-33-0
2,3,4,6-TCDF
83704-30-7
2,3,4,7-TCDF
83704-31-8
2,3,4,8-TCDF
83704-32-9
2,3,6,7-TCDF
57117-39-2
2,3,6,8-TCDF
57117-37-0
2,3,7,8-TCDF
51207-31-9
2,4,6,7-TCDF
57117-38-1
2,4,6,8-TCDF
58802-19-0
3,4,6,7-TCDF
57117-40-5
Water
Solubility
mg/1*
4.19E-04
WS
Temp.
22.7
WS
Ref.
11
Vapor
Pressure
mm Hg*
(4.0E-08)
(2.9E-08)
(2.8E-08)
(2.1E-08)
(2.0E-08)
8.96E-09-
(1.5E-08)
(3.3E-08)
(2.0E-08)
VP
Temp.
25
25
25
25
25
25
25
25
VP
Ref.
21
21
21
21
21
21,33
21
21
Henry's
Constant
atm-m}/mol*
(8.6E-06)
Henry's
Constant
Ref.
19
Log
K..'
5.60
6.17
6.11
6.06
6.31
6.73
5.82-
6.53
6.25
6.17
Log
K..
Ref.
10
10
10
10
10
10
8,10
10
10
Log
K«'
Log
K«
Ref.
Photo
Quantum
Yield"
Photo
Quant.
Yield
Ref.
A-9
-------
Table A-l (continued)
Chemical
CAS No.
Congener Group Average
1,2,3,4,6-PeCDF
83704^7-6
1,2,3,4,7-PeCDF
83704-48-7
1,2,3,4,8-PeCDF
67517-48-0
1,2,3,4,9-PeCDF
83704-49-8
1, 2,3,6,7 -PeCDF
57117-42-7
1,2,3,6,8-PeCDF
83704-51-2
1,2,3,6,9-PeCDF
83704-52-3
1,2,3,7,8-PeCDF
57117-41-6
1,2,3,7,9-PeCDF
83704-53-4
1,2,3,8,9-PeCDF
83704-54-5
Water
Solubility
rog/1'
(4.2E-04)
WS
Temp.
22.7
WS
Ref.
20
Vapor
Pressure
mm Hg*
(2.5E-08)
VP
Temp.
25
VP
Ref.
20
Henry's
Constant
atm-m'/mol'
(8.6E-06)
Pentachlorodibenzofurans (MW= 340.42)
(2.7E-09)
(3.6E-09)
(2.2E-09)
(1.7E-09)-
2.72E-09
25
25
25
25
21
21
21
21,33
Henry's
Constant
Ref.
20
Log
K..'
(6.2)
6.53
6.79
6.26
6.33
6.79
Log
K«
Ref.
20
10
10
10
10
10
Log
K«'
Log
K«
Ref.
Photo
Quantum
Yield-
Photo
Quant.
Yield
Ref.
A-10
-------
Table A-l (continued)
Chemical
CAS No.
1,2,4,6,7-PeCDF
83704-50-1
1,2,4,6,8-PeCDF
69698-57-3
1, 2,4,6,9 PeCDF
70648-24-7
1,2,4,7,8-PeCDF
58802-15-6
1,2,4,7,9-PeCDF
71998-74-8
1,2,4,8,9-PeCDF
70648-23-6
1,2,6,7,8-PeCDF
69433-00-7
1,2,6,7,9-PeCDF
70872-82-1
1,3,4,6,7-PeCDF
83704-36-3
1,3,4,6,8-PeCDF
83704-55-6
1,3,4,6,9-PeCDF
70648-15-6
1.3,4,7,8-PeCDF
58802-16-7
Water
Solubility
mg/1'
WS
Temp.
WS
Ref.
Vapor
Pressure
nun Hg*
(3.5E-09)
(2.3E-09)
(1.5E-09)
(2.6E-09)
(1.9E-09)
(2.7E-09)
(4.3E-09)
VP
Temp.
25
25
25
25
25
25
25
VP
Ref.
21
21
21
21
21
21
21
Henry's
Constant
atm-m'/mol"
Henry's
Constant
Ref.
Log
K..'
6.27
6.34
6.59
6.26
6.19
6.42
6.51
6.19
6.24
6.34
Log
K«
Ref.
10
10
10
10
10
10
10
10
10
10
Log
K-'
Log
K«
Ref.
Photo
Quantum
Yield1
I.30E-02"
Photo
Quant.
Yield
Ref.
25
A-ll
-------
Table A-l (continued)
Chemical
CAS No.
1,3,4,7,9-PeCDF
70648-20-3
1,3,6,7,8-PeCDF
70648-21-4
1,4,6,7,8-PeCDF
83704-35-2
2,3,4,6,7-PeCDF
57117-43-8
2,3,4,6,8-PeCDF
67481-22-5
2,3,4,7,8-PeCDF
57117-31-4
Congener Group Average
Water
Solubility
rag/1*
2.36E-04
(2.4E-04)
WS
Temp.
22.7
22.7
WS
Ref.
11
20
Vapor
Pressure
mmHg*
(2.4E-09)
(1.9E-09)
(2.6E-09)-
3.29E-09
(2.7E-09)
VP
Temp.
25
25
25
25
VP
Ref.
21
21
21,33
20
Henry's
Constant
atm-mj/mol*
(6.2E-06)
(6.2E-06)
Henry's
Constant
Ref.
19
20
Log
K..'
6.33
6.53
6.47
6.59
6.92
(6.4)
Log
K..
Ref.
10
10
10
10
10
20
Log
K«'
Log
K«
Ref.
Photo
Quantum
Yield'
Photo
Quant.
Yield
Ref.
Hexach1orodibenzofurans(MW = 374.87)
1,2,3,4,6,7-HxCDF
79060-60-9
1,2,3,4,6,8-HxCDF
69698-60-8
1,2,3,4,6,9-HxCDF
91538-83-9
1,2,3,4,7,8-HxCDF
70648-26-9
8.25E-06
22.7
11
(2.4E-10)
(2.2E-10)
(4. IE- 10)
(2.4E-10)
25
25
25
25
21
21
21
21
(1.4E-05)
19
6.96E04h
25
A-12
-------
Table A-l (continued)
Chemical
CAS No.
1,2,3,4,7,9-HxCDF
91538-84-0
1,2,3,4,8,9-HxCDF
92341-07-6
1,2,3,6,7,8-HxCDF
57117-44-9
1,2,3,6,7,9-HxCDF
92341-06-5
1,2,3,6,8,9-HxCDF
75198-38-8
1,2,3,7,8,9-HxCDF
72918-21-9
1,2,4,6,7,8-HxCDF
67562-40-7
1,2,4,6,7,9-HxCDF
75627-02-0
1,2,4,6,8,9-HxCDF
69698-59-5
1,3,4,6,7,8-HxCDF
71998-75-9
1,3,4,6,7,9-HxCDF
92341-05-4
2,3,4,6,7,8-HxCDF
60851-34-5
Water
Solubility
mg/1'
1 .77E-05
WS
Temp.
22.7
WS
Ref.
11
Vapor
Pressure
mm Hg*
(2.8E-10)
(2.2E-10)
(3.4E-10)
(1.8E-10)
(2.6E-10)
(5.7E-10)
(1.8E-10)
(2.3E-10)
(2.0E-10)
VP
Temp.
25
25
25
25
25
25
25
25
25
VP
Ref.
21
21
21
21
21
21
21
21
21
1
Henry's
Constant
atm-nrVmoI*
(6.1E-06)
Henry's
Constant
Ref.
19
Log
K..'
Log
K™
Ref.
Log
K«'
Log
K«
Ref.
Photo
Quantum
Yield-
Photo
Quant.
Yield
Ref.
A-13
-------
Table A-l (continued)
Chemical
CAS No.
Congener Group Average
Water
Solubility
mg/1*
(1.3E-05)
WS
Temp.
22.7
WS
Ref.
20
Vapor
Pressure
mmHg1
(2.8E-10)
VP
Temp.
25
VP
Ref.
20
Henry's
Constant
atm-m3/mol*
(l.OE-05)
Henry's
Constant
Ref.
20
Log
K..'
Log
K..
Ref.
Log
K.,'
Log
K.
Ref.
Photo
Quantum
Yield-
Photo
Quant.
Yield
Ref.
Heptachlorod ibenzofurans (MW = 409. 3 1 )
1,2,3,4,6,7,8-HpCDF
67562-39-4
1, 2,3,4,6,7, 9-HpCDF
70648-25-8
1,2,3,4,6,8,9-HpCDF
69698-58-*
1,2,3,4,7,8,9-HpCDF
55673-89-7
Congener Group Average
1.35E-06
(1.4E-06)
22.7
22.7
11
20
(3.5E-11)-
1.33E-10
(5.8E-11)
(4.6E-11)-
1.07E-10
(9.9E-11)
25
25
25
25
21,33
21
21,33
20
(5.3E-05)
(5.3E-05)
19
20
7.92
(7.9)
10
20
Octachlorodibenzofurans (MW=444.76)
1,2,3,4,6,7,8,9-OCDF
39001-02-0
(1.2E-06)
25
11
3.75E-12
25
21
(1.9E-06)
19
(7.0)-
(13)
8,26,29
Tetrachloro-PCB (MW=291.99)
3,3',4,4'-TCB
32598-13-3
3,4,4',5-TCB
70362-50-4
(1.6E-06)
-(1.1E-02)
8.43E-06-
(2.9E-03)
25
25
12,13,17,
28,35,38,
40,44
17,41
(7.5E-10)
-1.37E-07
(2.6E-10)-
2.80E-10
25
25
13,18
18,41
9.40E-05-
(l.OE-04)
1.28E-04-
(1.5E-04)
13,35,39
16,35,41
5.62-
6.21
(6.4)
8,15,31
15
A-14
-------
Table A-l (continued)
Chemical
CAS No.
Water
Solubfflty
mg/1-
WS
Temp.
WS
Ref.
Vapor
Pressure
mm Hg*
VP
Temp.
VP
Ref.
Henry's
Constant
atm-m'/mol'
Henry's
Constant
Ref.
Log
K..'
Log
K«,
Ref.
Log
K«P
Log
K«
Ref.
Photo
Quantum
Yield*
Photo
Quant.
Yield
Ref.
Pentachloro-PCB (MW= 326.44)
2,3,3',4,4'-PeCB
32598-14^1
2,3,4,4',5-PeCB
74472-37-0
2,3',4,4',5-PeCB
31508-00-6
3,3',4,4',5-PeCB
57465-28-8
(1.9E-03)-
(I.IE^B)
3.69E-06-
(I.IE42)
4.27E-06-
(1.1E-02)
(1.0E^)3)
25
25
25
25
17,35,37
17,35,37,
41
17,35,37,
41
17
(3.7E-09)
5.96E-10-
(2.1E-09)
8.45E-10-
(2.7E-09)
(2.9E-06)
25
25
25
25
18
18,41
18,41
18
(6.0E-05)-
(9.9E-05)
6.9E-05-
(1.4E-04)
8.5E-05-
4.0E-04
(5.4E-05)-
(8.2E-05)
Hexachloro-PCB (MW=360.88)
2,3,3',4,4',5 HxCB
38380-08-4
2,3,3',4,4',5'-HxCB
69782-90-7
2,3',4,4',5,5'-HxCB
52663-72-6
3,3',4,4',5,5'-HxCB
32774-16-6
7.44E-07-
(2.4E-03)
(3.6E-04)
(3.6E4M)-
(2.4E-03)
(3.6E-05)-
(2.5E-03)
25
25
25
25
17,37,41
17
17,37
17,35,37
(1.4E-06)
(1.2E-06)
(2.0E-06)
(1.5E-06)
25
25
25
25
18
18
18
20
(2.2E-05)
-8.7E-04
(6.6E-05)
-5.8E-04
(1.1E-04)-
(1.2E-04)
(5.9E-05)-
(6.5E-05)
16,35
16,35,41
16,35,41,
43
16,35
16,35,43
16,35,43
16,35
16,35
Heptachloro-PCB (MW=396.33)
2,3,3',4,4',5,5'-HpCB
39635-31-9
(4.5E-05)-
(5.4E-04)
25
17,35,37
(3.0E-07)
25
18
(6.6E-05)
35
(6.3)-
(6.6)
(6.3)-
(6.6)
(6.2)-
7.12
(6.9)
(6.6)-
(7.2)
7.16-
(7.2)
(6.6)-
(7.3)
(6.6)-
7.47
(7.0)-
(7.7)
15,37
15,37
15,31,37
15
14,15,37
14,15
14,15,37
14,15,37
15,37
(5.7)
42
A-15
-------
Table A-l (continued)
Footnote References
* Values are presented as they appeared in the referenced articles. Subcooled liquid values were converted to solid values (33). Values in () are calculated.
h Tested in solution of wateracetonitrile (1:1 v/v) at 313 nm.
c Tested in solution of wateracetonitrile (2:3 v/v) at 313 nm.
d Tested in vapor phase at 250-360 nm.
1. Marpleetal. (1986a)
2. USEPA(1990)
3. Podoll et al. (1986)
4. Marple et al. (1986b)
5. Shiu et al. (1988)
6. Friesenetal. (1985)
7. Webster et al. (1985)
8. Burkhard and Kuehl (1986)
9. Rordorf(1987)
10. Sijm et al. (1989)
11. Friesenetal. (1990)
12. Dickhutet al. (1986)
13. Dunnivant and Elzerman (1988)
14. Risby et al. (1990)
15. Hawker and Connell (1988)
16. Sabljic and Gunsten (1989)
17. Abramowitz and Yalkowsky (1990)
18. Foreman and Bidleman (1985)
19. Calculated by the VP/WS ratio technique
20. Average of all literature values (measured and calculated) within a congener group
21. Rordorf (1989)
22. Dulin et al. (1986)
23. Choudhry and Webster (1987)
24. Choudhry and Webster (1989)
25. Choudhry et al. (1990)
26. Samaetal. (1984)
27. Adams and Blaine (1986)
28. Mackayetal. (1980)
29. Doucette and Andren (1988a)
30. Orth et al. (1989)
31. Rapaport and Eisenreich (1984)
32. Lodge and Cook (1989)
33. Eitzer and Hites (1988)
34. Rordorf (1985)
35. Dunnivant et al. (1992)
36. Lodge (1989)
37. Patil (1991)
38. Nirmalakhandan and Speece (1989)
39. Dunnivant et al. (1988)
40. Opperhuizen et al. (1988)
41. Murphy et al. (1987)
42. EPRI (1990)
43. Murphy et al. (1983)
44. Yalkowsky et al. (1983)
45. Webster et al. (1986)
46. Doucette and Andren (1988b)
47. Walters and Guiseppi-Elie (1988)
48. Jackson et al. (1986)
49. Pun etal. (1989)
50. Marple et al. (1987)
A-16
-------
Table A-2. Rankings for the P-Chem Property Literature
Reference
Number
1
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
Ranking8
Water
Solubility
2
2
2
2
2
1
1
5
5
Vapor
Pressure
2
2
2&5
4
5
5
2&5
Henry's
Constant
4
4
2
2
5
5
5
Log
KO*
1
1
4
4
1 &2
3
2&5
5
5
Log
K*
5
Photo
Quantum
Yield
2
2
2
2
A-17
-------
Table A-2 (continued)
Reference
Number
27
28
29
30
31
32
33
34
35
36
37
38
39
40
41
42
43
44
45
46
47
48
49
50
Ranking8
Water
Solubility
2
5
5
2
5
5
2
2
5
2
1
Vapor
Pressure
4
4
2
Henry's
Constant
5
2
4
4
Log
K™
5
4
5
1
Log
*~
1
4
2
1
1
2
1
Photo
Quantum
Yield
2
A-18
-------
Table A-2 (continued)
Footnote References
" P-chem properties with two ranks indicates that some of the values for the chemicals in the reference had been verified by
another laboratory, and some values have not been verified yet. It also indicates that more than one methodology may have
been used in the reference to determine the p-chem property.
1. Marpleetal. (1986a)
3. Podoll et al. (1986)
4. Marple et al. (1986b)
5. Shiu et al. (1988)
6. Friesen et al. (1985)
7. Webster et al. (1985)
8. Burkhard and Kuehl (1986)
9. Rordorf (1987)
10. Sijm et al. (1989)
11. Friesen et al. (1990)
12. Dickhut et al. (1986)
13. Dunnivant and Elzerman (1988)
14. Risby et al. (1990)
15. Hawker and Connell (1988)
16. Sabljic and Gunsten (1989)
17. Abramowitz and Yalkowsky (1990)
18. Foreman and Bidleman (1985)
19. Calculated by the VP/WS ratio technique
20. Average of all literature values (measured and calculated)
within a congener group.
21. Rordorf (1989)
22. Dulin et al. (1986)
23. Choudhry and Webster (1987)
24. Choudhry and Webster (1989)
25. Choudhry et al. (1990)
26. Sarna et al. (1984)
27. Adams and Elaine (1986)
28. Mackay et al. (1980)
29. Doucette and Andren (1988)
30. Orth et al. (1989)
31. Rapaport and Eisenreich (1984)
32. Lodge and Cook (1989)
33. Eitzer and Kites (1988)
34. Rordorf (1985)
35. Dunnivant et al. (1992)
36. Lodge (1989)
37. Patil (1991)
38. Nirmalakhandan and Speece (1989)
39. Dunnivant et al. (1988)
40. Opperhuizen et al. (1988)
41. Murphy et al. (1987)
42. EPRI (1990)
43. Murphy et al. (1983)
44. Yalkowsky et al. (1983)
45. Webster et al. (1986)
46. Doucette and Andren (1988)
47. Walters and Guiseppi-Elie (1988)
48. Jackson et al. (1986)
49. Puri et al. (1989)
50. Marple et al. (1987)
A-19
-------
DRAFT-DO NOT QUOTE OR CITF
APPENDIX B. ENVIRONMENTAL CONCENTRATIONS
The tables in this appendix are discussed in Chapter 4. References listed at the end
of each table are included in the reference list at the end of Chapter 4. Following are the
tables included in this Appendix:
Page
Table B-1. Environmental Levels of Dioxin in Soil (ppt) B-3
Table B-2. Environmental Levels of Dibenzofuran in
Soil (ppt) B-9
Table B-3. Environmental Levels of Dioxins in Water (ppq) B-15
Table B-4. Environmental Levels of Dibenzofurans in
Water (ppq) B-17
Table B-5. Environmental Levels of Dioxins in
Sediments (ppt) B-19
Table B-6. Environmental Levels of Dibenzofurans in
Sediments (ppt) B-27
Table B-7. Environmental Levels of PCBs in Sediment (ppt) B-35
Table B-8. Environmental Levels of Dioxins in Fish (ppt) B-38
Table B-9. Environmental Levels of Dibenzofurans in
Fish (ppt) B-60
Table B-10. Environmental Levels of PCBs in Fish (ppt) B-88
Table B-11. Levels of Dioxins in Food Products (ppt) B-92
Table B-12. Levels of Dibenzofurans in Food Products (ppt) B-112
Table B-13. Environmental Levels of PCBs in Food (ppt) B-137
Table B-14. Environmental Levels of Dioxins in Air (pg/m3) B-140
Table B-15. Environmental Levels of Dibenzofurans in
Air (pg/m3) B-154
Table B-16. Environmental Levels of PCBs in Air (pg/m3) B-171
Table B-17. Mean Background Environmental Levels of Dioxins
in Soil (ppt) B-172
B-1
4/94
-------
DRAFT-DO NOT QUOTE OR CITF
Table B-18. Mean Background Environmental Levels of
Dibenzofurans in Soil (ppt) B-175
Table B-19. Mean Background Levels of Dioxins in
Water (ppq) B-178
Table B-20. Mean Background Environmental Levels of Dioxins
in Sediments (ppt) B-179
Table B-21. Mean Background Environmental Levels of
Dibenzofurans in Sediment (ppt) B-181
Table B-22. Mean Background Environmental Levels of PCBs
in Sediment (ppt) B-183
Table B-23. Mean Background Environmental Levels of Dioxins
in Finfish (ppt) B-185
Table B-24. Mean Background Levels of Dibenzofurans in
Finfish (ppt) B-187
Table B-25. Mean Background Levels of Dioxins in Food
Products (wet wt. ppt) B-189
Table B-26. Mean Background Levels of Dibenzofurans in
Food Products (wet wt. ppt) B-197
Table B-27. Mean Background Levels of PCBs in Food
Products (wet wt. ppt) B-208
Table B-28. Mean Background Levels of Dioxins in
Air (pg/m3) B-211
Table B-29. Mean Background Levels of Dibenzofurans in
Air (pg/m3) B-213
Table B-30. Mean Background Environmental Levels of PCBs in
Air (pg/m3) B-216
B-2
4/94
-------
Table B-l. Environmental Levels of Dioxms in Sofl (ppt)
Chemical
2,3,7,8-TCDD
TCDDs
Ntantor
sample*
Number
positive
•unpin
77
3
2
23
62
13
22
4
NR
33
11
20
8
4
12
19
1
77
NR
NR
NR
NR
NR
0
2
23
59
1
6
0
NR
33
9
13
8
0
12
6
1
NR
NR
NR
NR
NR
Concentration
range
ND-2.1
ND(0.2-2.0)
2.4-0.84
10-36000
ND-270
ND-2
ND-5
ND(l.O)
NR
41-52000
ND-590
ND-9.4
0.6-3.1
ND(3.75)
1-7
ND-4.2
3.2
ND-69
200
2.8
0.9
874
Cone.
Tetrachlorox
<0.5
NA
1.62
2133
55
<1
1
NA
2
4300
145
2
2
NA
3
1
3.2
9.4
NR
NR
NR
NR
Location
Kk»i«MUi_jti/viiiMa/1ljfW'«'t^l OJft
British Isles
Various parti of Europe
Various parts of Europe
Midland, MI
Midland, MI
Henry, IL
Middletown, OH
MN
Finland
Midland, MI
Midland, MI
VS
Sweden
Elk River, MN
England
England
Various parts of Europe
British Isles
Muggenburger st.
Hamburg,Oermany
Kirchsteinbek,
Hamburg, Germany
Ochsenwerder
Landscheideweg,
Hamburg.Germany
Moorefleeter Brack
Hamburg, Germany
Location
descnpttDB
Background
Rural
Industrial
Industrial
Residential
Residential
Residential
Pristine
Industrial
Industrial
Industrial
Industrial
Urban
Rural
Residential
Urban
Rural
Background
Industrial
Industrial
Contaminated site
Contaminated site
Sample
year
NR
NR
NR
NR
1985
1985
1985
1985
Ref.
no.
11
10
10
1
1
1
1
1
2
3
3
3
5
6
7
8
10
11
12
12
12
12
Conuiiftnls
Urban area
Near Stockholm
Agriculture
Rural
Maximum contents
reported
Maximum contents
reported
Maximum content*
reported
Maximum contents
reported
B-3
-------
Table B-l. EnrirmmMntal Lereb of Dttados in Sofls (ppt) (contimied)
Chemical
TCDDs (continued)
1,2,3,7,8-PeCDD
PeCDDs
Number
sample*
47
2
1
7
5
3
NR
11
12
53
29
8
4
12
19
NR
8
4
19
77
1
2
77
47
Number
positive
samples
11
2
1
5
0
0
NR
NR
NR
0
NR
8
0
12
19
NR
8
0
7
NR
1
2
NR
7
Concentration
range
ND-430
11.2-55.5
320
ND-290
ND(1.0)
ND(1.0)
NR
ND-7
ND-430
ND(55)
ND-1200
37-217
ND(3.75)
17-120
9-160
NR
2.6-18.3
ND(3.75)
ND-11
ND-2.4
4.6
220-270
ND-46
ND-580
Cone,
mean
40.3
33.4
320
109
NA
NA
89
<1
69
NA
69
98
NA
42
65
Pentachioroc
15
10
NA
2
<0.5
4.6
245
6.6
38.4
Location
Ontario and U.S. Midwestern
States.
Various parts of Europe
Midland, MI
Midland, MI
Middletown, OH
MN
Finland
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
England
l5be*XHMBoxh»(MW-356.42)
Finland
Sweden
Elk River, MN
England
British Isles
various parts of Europe
various parts of Europe
British Isles
Ontario and U.S. Midwestern
States.
Location
Urban
Industrial
Industrial
Residential
Residential
Pristine
Industrial
Rural
Urban
Urban
Agriculture
Residential
Urban
Industrial
Urban
Rural
Urban
Background
Rural
Industrial
Background
Urban
Sample
yaat
NR
NR
Ref,
no.
13
10
1
1
1
1
2
4
4
4
4
5
6
7
8
2
5
6
8
11
10
10
11
13
c—
Near Incinerator
Near Incinerator
Near Stockholm
Rural
Near Stockholm
Agriculture
B-4
-------
Table B-l. Environmental Lev* of Dkntms it Saab fart) (continued)
Chemical
PeCDDs (continued)
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
Number
samples
1
6
5
3
NR
11
12
53
29
8
4
12
19
13
6
5
NR
8
4
NR
8
4
NR
8
4
Nttfnbtf
potitiv*
•amptef
1
2
0
0
NR
NR
NR
0
NR
8
1
12
19
13
6
5
NR
8
0
NR
8
1
NR
8
2
Concentration
range
240
ND-120
ND(1.0)
ND(l.O)
NR
ND-580
ND-540
ND(55)
ND-130
46-476
ND-38
4-50
6-190
33.7-1264
7.1-184
92.2-455
NR
4.3-8.0
ND(3.75)
NR
3.3-32.2
ND-14
NR
1.6-16.6
ND-9.9
Cone,
tnfiafl '
NA
37
NA
NA
900
53
81
NA
23
159
10
20
69
302
49.9
181
! Location
Midland, MI
Midland, MI
Middletown, OH
MN
Finland
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
England
Salzburg, Auitria
Salzburg, Auatria
Salzburg, Auatria
Hexachforodibeazo-p-dk>xini(MW»'390.87)
<2
6
NA
2100
12
4
700
8
9
Finland
Sweden
Elk River, MN
Finland
Sweden
Elk River, MN
Finland
Sweden
Elk River, MN
Location
description :
Induitrial
Reiidential
Residential
Pristine
Industrial
Rural
Urban
Urban
Rural
Residential
Urban
Urban
Rural
Industrial
Sample
yew
90-91
90-91
90-91
Ref.
no.
1
1
1
1
2
4
4
4
4
5
6
7
8
14
14
14
Industrial
Urban
Rural
Industrial
Urban
Rural
Industrial
Urban
Rural
2
5
6
2
5
6
2
5
6
Commoofs
Near Incinerator
Near Incinerator
Near Stockholm
Agriculture
Rural
Near Stockholm
Agriculture
Near Stockholm
AOriculture
Near Stockholm
Agriculture
B-5
-------
Table B-l. Environmental Lev* of Dwnns in Soft (ppt) (continued)
Chemical
HxCDDi
1,2,3,4,6,7,8-HpCDD
1,2,3,4,6,7,9-HpCDD
HpCDDs
Number
simple*
1
2
77
47
20
1
7
5
3
NR
11
12
53
29
8
4
12
19
NR
8
4
NR
3
2
77
30
47
20
Number
positive
•ample*
1
2
NR
13
8
1
5
1
0
NR
NA
NA
0
0
8
4
12
19
NR
8
4
NR
1
2
NR
3
25
19
Concentration
HWge
4.7
200-330
2.8-165
ND-410
ND-240
4000
ND-410
ND-72
ND{1.0)
NR
ND-170
ND-70
ND(55)
ND(55)
43-349
12-99
8-43
23-340
NR
43-492
37-360
NR
ND-17
370-1600
7.5-234
ND-91
ND-2400
ND-5000
Cone*
4.7
265
38
38.12
44.1
4000
172
14
NA
7200
15
9
NA
NA
156
48
23
154
4700
144
194
7100
9.0
985
66
5.4
212
1197
•-!*&• '
Various parts of Europe
Various parts of Europe
British Isles
Onurio and V.S. Midwestern
Sutei.
Canada and U.S.A.
Midland, MI
Midland, MI
Middktown, OH
MN
Finland
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
England
llDCnXO p OKMUttt(MW 4i3JI}
Finland
Sweden
Elk River, MN
Finland
Various parts of Europe
Various parts of Europe
British Isles
Onurio and U.S. Midwestern
Sutei.
Onurio and U.S. Midwestern
SUtei.
Canada and U.S.A.
Location
description
Rural
Industrial
Background
Urban
Industrial
Industrial
Residential
Residential
Pristine
Industrial
Rural
Urban
Urban
Rural
Residential
Urban
Industrial
Urban
Rural
Industrial
Rural
Industrial
Background
Rural
Urban
Industrial
Sample
y**r
NR
NR
Ref.
no.
10
10
11
13
13
1
1
1
1
2
4
4
4
4
5
6
7
8
2
5
6
2
10
10
11
13
13
13
Commenu
Near Incinerator
Near Incinerator
Near Stockholm
Agriculture
Rural
Near Stockholm
Agriculture
B-6
-------
Table B-l. Environmental Levels «f Dknrins in Safe (ppt) (continued)
Chemical
HpCDDs (continued)
1,2,3,4,6,7,8,9-OCDD
Number
sample*
1
7
5
3
11
12
53
29
8
4
12
19
1
2
77
30
47
20
1
7
5
3
NR
11
12
53
29
8
4
Number
positive
tampte*
1
7
5
3
NR
NR
0
NR
8
4
12
19
Concentration
wage
75000
150-2400
23-200
25-91
ND-390
ND-300
ND(55)
ND-1100
83-904
62-640
20-130
77-5500
1
2
NR
17
38
20
1
7
5
3
NR
NR
NR
NR
NR
8
4
14
140-160
29-832
44-810
ND-12000
15-26000
375000
330-12000
170-10600
25-91
NR
ND-3500
ND-1500
ND-100
ND-16000
113-2659
340-3300
Cone,
mftHfl
75000
930
113
54
90
43
NA
93
277
346
64
817
Uooatiott
Midland, MI
Midland, MI
Middletown, OH
MN
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
Fngl«n^
Location
description
Industrial
Residential
Residential
Pristine
Rural
Uiban
Uiban
Rural
Residential
Urban
Ck^blorodib«nzo-jMlioxiB
-------
Table B-l. Environmental Levels of Worms fat Soils (ppt) (continued)
Cbotmcil
1,2,3,4,6,7,8,9-OCDD
(continued)
Number
samples
12
19
Number
positive
4£lttp$eA
12
19
Cooceotratioa
Mttge
20-150
176-99000
Cone.
meat*
58
9980
Location
England
England
Location
description
Residential
Urban
Sample
y«r
Ref.
ftO.
7
8
Cfoftuxwntt
Rural
Footnote References
NOTES: Summary statistics provided in or derived from references; when reference did not compute mean, it was computed using one-half the detection limit for non-detects;
NA ~ Not applicable;
ND - Non-detect;
MR - Not reported;
Detection limits varied by study and as was different for different compounds, but generally were 1 to 5 ng/kg (ppt). Descriptions provided were those given by reference or surmised from study description when not given.
Sources:
1. EPA (1985)
2. Kitunen and Salkinoja-Salonen (1990).
3. Nestrick, et al. (1986).
4. Peanon, et al. (1990).
5. Broman, et al. (1990).
6. Reed, et al. (1990).
7. Stenhouseand Badsha (1990).
8. Greaser, et al. (1990)
10. Rappe and Kjeller (1987)
11. Greaser, etal. (1989)
12. Sievera and Friesel (1989)
13. Birmingham (1990)
14. Boot, et al. (1992)
B-8
-------
Table B-2. Environmental Leyeb of Dibenzofunuu in Sofl (ppt)
Chemical
Number
samples
Number
positive
samples
Concentration
f*U1£&
Cone*
mean
Location
Location
description , :,.
Sample
3»«r
Ref.
CODUDBQbl
TetracUoro
-------
Table B-2. Environmental Levels of Dibenzororam in Sou (pot) (continued)
Cbwnkal
TCDFs (continued)
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
1,2,3,7,8/1,2,3,4,8-PeCDF
PeCDFs
Nuraber
•ample*
19
4
12
NR
8
4
12
NR
8
3
77
47
20
2
1
8
5
NR
11
12
S3
29
Nmnbw
positive-
samples
19
0
12
NR
8
0
12
NR
8
3
NR
4
5
2
1
2
0
NR
0
0
0
NR
Concentration
range
29-950
Pent
ND(3.75)
1-10
NR
3.1-26.5
ND0.75)
1-5
NR
7.4-32.1
6.7-14
ND-185
ND-110
ND-285
200-450
900
ND-110
ND
NR
ND(55)
ND(55)
ND(55)
ND-160
Cone*
mean
232
ichloToolbciisa
NA
4
580
13
NA
2
82
16
11.2
23
41.5
86
325
900
19
NA
27000
NA
NA
NA
35
Location
England
Location
description
Urban
jfiirans (MW»340.42)
Elk River, MN
England
Finland
Sweden
Elk River, MN
England
Finland
Sweden
Various parts of
Europe
British Isles
Ontario and U.S.
Midwestern states
Ontario and U.S.
Midwestern states
Various parts of
Europe
Midland, MI
Midland, MI
Middletown, OH
Finland
Canada
Canada
Canada
Canada
Rural
Residential
Industrial
Urban
Rural
Residential
Industrial
Urban
Rural
Background
Urban
Industrial
Industrial
Industrial
Residential
Residential
Industrial
Rural
Urban
Sample
year
Ref.
no.
S
6
7
2
5
6
7
2
5
10
11
13
13
10
1
1
1
2
4
4
4
4
GonuDcnti
Agriculture
Rural
Near Stockholm
Agriculture
Rural
Near Stockholm
Near Incinerator
Near Incinerator
B-10
-------
Table B-2. Environmental Lercb of DtbauofanM in Soil (ppt) (continued)
Chemical
PeCDFi (continued)
Number
samples
8
4
12
19
13
6
5
Number
positive
•ampler
8
3
12
19
13
6
5
Concentration
ftflge
36-457
18-45
6-70
19-830
45.6-261
12.0-77.7
53-355
Cone;
mean
149
35
31
189
115
46.5
182
Location
Sweden
Elk River, MN
England
England
Salzburg, Aiutria
Salzburg, Auatria
Salzburg, Austria
Location
description
Urban
Rural
Residential
Urban
Urban
Rural
Industrial
Sonptft
yea*
90-91
90-91
90-91
B»L
.. |H>, .
5
6
7
8
14
14
14
CortuncOThi
Near Stockholm
Agriculture
Rural
Hexachiorodft>enzofcnns(MW»>374.87)
1,2,3,4,7,8/1,2,3,4,7,9-
HxCDF
1,2,3,4,7,8-HxCDF
1,2,3,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6,7,8-HxCDF
HxCDFi
MR
8
4
MR
8
4
NR
8
4
NR
4
3
77
47
20
NR
8
0
NR
8
0
NR
8
0
NR
1
3
NR
6
7
NR
7.8-29.1
ND(3.75)
NR
7.7-28.9
ND(3.75)
NR
0.5-3.8
ND(3.75)
NR
ND-7.1
11-16
4.3-212
ND-260
ND-420
920
16
NA
<2
14
NA
<2
1
NA
<2
2
13
41
94.8
178
Finland
Sweden
Elk River, MN
Finland
Sweden
Elk River, MN
Finland
Sweden
Elk River, MN
Finland
Elk River, MN
Varioui part* of
Europe
British Isles
Ontario and U.S.
Midweitern ttates
Ontario and U.S.
Midweitern Mates
Industrial
Urban
Rural
Industrial
Urban
Rural
Industrial
Urban
Rural
Industrial
Rural
Rural
Background
Urban
Industrial
2
5
6
2
5
6
2
5
6
2
6
10
11
13
13
Near Stockholm
Agriculture
Near Stockholm
Agriculture
Near Stockholm
Agriculture
Agriculture
B-11
-------
Table B-2. Environmental Levels of Dibauofbnms fat Soil (ppt) (continued)
Chemical
HxCDFs (continued)
1,2,3,4,6,7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
HpCDFs
Number
•ample*
2
1
8
5
3
NR
11
12
53
29
8
4
12
19
NR
8
4
NR
8
4
3
2
77
Number
pootive
samples
2
1
3
0
0
NR
0
0
0
NR
8
4
12
19
NR
8
4
NR
8
0
3
2
NR
Concentration
range
270-1900
15400
64-260
ND(l.O)
ND(1.0)
NR
ND(55)
ND(55)
ND(55)
ND-120
53-308
7-150
6-50
17-660
ti**t
fWp\
NR
31-134
11-80
NR
1.0-6.3
ND(3.75)
14-22
260-4500
1.5-138
Cone.
1085
15400
62
NA
NA
7200
NA
NA
NA
9
145
66
24
156
•chlorodlbena
4700
73
47
<5
3
NA
18
2380
26
Location
Various part* of
Europe
Midland, MI
Midland, MI
Middletown, OH
MN
Finland
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
England
uftlrtOS(MW«409Jl)
Finland
Sweden
Elk River, MN
Finland
Sweden
Elk River, MN
Various parts of
Europe
Various parts of
Europe
British Isles
Location
description
Industrial
Industrial
Residential
Residential
Pristine
Industrial
Rural
Urban
Urban
Rural
Residential
Urban
Industrial
Urban
Rural
Industrial
Urban
Rural
Rural
Industrial
Background
Sample
year
R*f.
no.
10
1
1
1
1
2
4
4
4
4
5
6
7
8
2
5
6
2
5
6
10
10
11
Comments.
Near Incinerator
Near Incinerator
Near Stockholm
Agriculture
Rural
Near Stockholm
Agriculture
Near Stockholm
Agriculture
B-12
-------
Table B-2. Environmental Levels of Dibouofunms in Soil (ppt) (contmned)
Chemical
HpCDFi (continued)
Nun*er
sample*
47
20
1
8
5
3
11
12
53
29
8
4
12
19
Number
positive
. Wnptet
10
15
1
6
1
0
NR
0
0
NR
8
4
12
19
Coocentntton
wag*
ND-120
ND-3750
75000
ND-820
ND-43
ND(1.0)
ND-180
ND(55)
ND(55)
ND-410
31-187
30-260
4-59
16-458
Cone;
...mean..
283
733
75000
300
9
NA
30
NA
NA
29
81
100
20
152
Location
OnUrio and U.S.
Midwestern dates
OnUrio and U.S.
Midweftern dates
Midland, MI
Midland, MI
Middletown, OH
MN
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
England
Location :
description
Urban
Industrial
Industrial
Residential
Residential
Pristine
Rural
Urban
Urban
Rural
Residential
Urban
Sample
. .. year. .
R«f.
no.
13
13
1
1
1
1
4
4
4
4
5
6
7
8
Comments
Near Incinerator
Near Incinerator
Near Stockholm
Agriculture
Rural
OcWchkwoda>«)Zoftinm.(MW-444.76)
1,2,3,4,6,7,8,9-OCDF
1
77
47
20
2
1
8
5
1
NR
15
15
2
1
6
1
5.7
ND-144
ND-660
ND-5200
68-71
8600
ND-660
ND-50
5.7
27
185
843
69.5
8600
240
10
Various parts of
Europe
British Islei
Canada and USA
Canada and USA
Various parts of
Europe
Midland, MI
Midland, MI
Middletown, OH
Rural
Background
Urban
Industrial
Industrial
Industrial
Residential
Residential
10
11
13
13
10
1
1
1
B-13
-------
TaWe E-2. Enrironmental Levels of Dibenxoraram in Soil (ppt) (contained)
Chemical
1,2,3,4,6,7,8,9-OCDF
(continued)
Nim*«r
. sample*
3
NR
11
12
53
29
8
4
12
19
Number
positive
•ample*
0
NR
NR
NR
0
NR
8
3
12
19
Concentration
range
ND(1.0)
NR
ND-33
ND-230
ND(55)
ND-600
2.9-19.0
60-270
10-90
7-1100
Cone.
«*«tt
NA
3000
4
43
NA
SO
8
113
30
196
Location
MN
Finland
Canada
Canada
Canada
Canada
Sweden
Elk River, MN
England
England
Location
description
Pristine
Industrial
Rural
Urban
Urban
Rural
Residential
Urban
Sample
JWM,,
Ref.
no.
1
2
4
4
4
4
5
6
7
8
Commedtt
Near Incinerator
Near Incinerator
Near Stockholm
Agriculture
Rural
Footnote References
NOTES: Summary statistics provided in or derived from references; when reference did not compute mean, it was computed using one-half the detection limit for non-detects;
NA = Not available;
NR - Not reported;
ND - Non-detect.
Detection limits varied by study and were different for different compounds, but generally were 1 to 5 ng/kg (ppt). Descriptions provided were those given by reference or surmised from study description when not given.
Sources: 1. EPA (1985)
2. Kitunen and Salkinoja-Salonen (1990.
3. Nestrick, el at. (1986).
4. Pearson, et al. (1990).
5. Broman, et al. (1990).
6. Reed.etal. (1990).
7. Stenhouse and Badsha (1990).
8. Creaser, et al. (1990)
10. Rappe and Kjeller (1987)
11. Creaser, et al. (1989)
12. Sievers and Friend (1989)
13. Birmingham (1990)
14. Boos, et al. (1992)
B-14
-------
TabteB-3. Environmental Lereb of Dioxms in Water (ppq)
Chemical
Numbet
tampion
Number
pwitlv*
. mnptes
Concentration
range
Cone.
metai
Location
Location
description
Sa«f>.
"' jr«r
!*<*;
: OO.
_.:• • Comtneau
Tetr»chlorodibcnzo-p-8) • ..-'.':
2,3,7,8-TCDD
TCDDs
i
2
185
22
1
2
0
0
1
0
1
2
ND(0.7)
ND(.02-.024)
NEMO
ND(.4-2.6)
1.7
.05-.084
NA
NA
2.70
NA
1.7
.067
Lockport, New York
Eman River, Sweden
Ontario, Canada
New York State
Lockport, New York
Eman River, Sweden
NR
PCB contaminated
NR
NR
NR
PCB contaminated
88
NR
83-89
86-88
88
NR
2
3
1
2
2
3
Pen««chloiodibenzo-p-dkjxin»(MW-356.42) I
1,2,3,7,8-PeCDD
PeCDDt
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
1
2
1
22
2
0
0
0
0
2
1
2
1
2
1
2
0
1
0
1
0
1
ND(l.O)
ND(.025-.039)
ND(l.O)
ND(1. 2-7.4)
.067-. 12
NA
NA
NA
NA
.094
Lockport, New York
Eman River, Sweden
Lockport, New York
New York State
Eman River, Sweden
NR
PCB contaminated
NR
NR
PCB contaminated
88
NR
88
86-88
NR
2
3
2
2
3
He3t»ohk>rodibenzo-p-dioxini(MW««390.87) :
ND(1.8)
ND-.054
ND(1.5)
ND-.12
ND{1.5)
ND-.075
NA
.027
NA
.06
NA
.038
Lockport, New York
Eman River, Sweden
Lockport, New York
Eman River, Sweden
Lockport, New York
Eman River, Sweden
NR
PCB contaminated
NR
PCB contaminated
NR
PCB contaminated
88
NR
88
NR
88
NR
2
3
2
3
2
3
raw surface drinking water
raw wrface drinking water
nw wrface drinking water
treated wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
treated wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
nw wrface drinking water
B-15
-------
Table B-3. Environmental Levels of Diorins in Water (ppq) (continued)
Chemical
HxCDDs
Number
samples
1
22
2
Number
lamptei
0
0
2
1,2,3,4,6,7,8-HpCDD
HpCDDs
1,2,3,4,6,7,8,9-OCDD
1
2
1
22
2
185
214
0
2
0
0
2
Concenuttion
range
ND(1.5)
ND(.4-4.7)
.13-.67
ND<2.8)
.15-.30
ND(2.8)
ND(.4-6.8)
.17-.64
Cone.
mean
NA
NA
.4
Heptaca
NA
.22
NA
NA
.40
Odachl
32
4
ND-175
ND-46
10.6
3.16
Location
Lockpoit, New York
New York State
Eman River, Sweden
Lockpoit, New York
Eman River, Sweden
Lockpoit, New York
New York Stale
Eman River, Sweden
orodibenZo-j>-dk)Xu»(>IV
Ontario, Canada
Ontario, Canada
Location
description
NR
NR
PCB contaminated
W-425.31)
NR
PCB contaminated
NR
NR
PCB contaminated
fw 460.76)
NR
NR
Samp.
year
88
86-88
NR
Kef.
no.
2
2
3
Comment*
raw surface drinking water
treated surface drinking water
raw surface drinking water
88
NR
88
86-88
NR
8349
83-89
2
3
2
2
3
raw surface drinking water
raw surface drinking water
raw surface drinking water
treated surface drinking water
raw surface drinking water
1
1
raw surface drinking water
treated surface drinking water
Footnote Ref<
NOTES: Summary statistics provided in or derived from referencei; when reference did not compute mean, one-half the limit of detection was used in non-delects. Therefore, it is possible to have mean concentration* greater than
the range (e.g., reported detection limit for nondetects greater than the positive sample).
NA = not applicable;
ND = non-detected (limit of detection);
NR = not reported;
Descriptions provided were those given by reference or surmised from study description when not given.
Sources: 1. Jobb, et al. (1990)
2. Meyer, et al. (1989)
3. Rappe, et al. (1989b)
B-16
-------
Table B-4. Environmental Levels of Dibenzofonuis in Water (ppq)
Chemical
2,3,7,8-TCDF
TCDFs
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
1,2,3,4,8/1,2,3,7,8-PeCDF
PeCDFs
Num&et
sample*
2
1
22
1
2
Number
poi&ve
•ample*
2
0
1
1
2
1
2
1
2
1
22
2
1
2
0
2
1
0
2
Concentration
range
.022-.026
ND(0.7)
ND-2.6
18
.21-.23
2.0
.014-.019
ND(1.0)
.013-.025
27
NO(0.3-4.0)
.13-.21
1,2,3,4,7,8-HxCDF
1,2,3,6,7,8-HxCDF
2,3,4,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
1
1
2
1
2
1
2
1
1
2
0
1
0
1
39
9.2
.019-.025
ND(l-3)
ND-.027
ND(1.2)
ND-.022
Cow-
mean
T«t
.024
NA
0.12
18
0.22
Location
nrchJorodibenzofiirani(MNl
Eman River, Sweden
Lockpoit, New York
New York State
Lockpoct, New York
Eman River, Sweden
Location
description
r-305<98)
PCB contaminated
NR
NR
NR
PCB contaminated
Pentachlorodibenzofurani (MW=340.42)
2.0
.016
NA
.019
27
NA
.17
Lockpoit, New York
Eman River, Sweden
Lockpoit, New York
Eman River, Sweden
Lockpoit, New York
New York State
Eman River, Sweden
B»*w.htnr«vtttv>n7nfiimi»/VrV
39
9.2
.022
NA
.014
NA
.011
Lockpoit, New York
Lockpoit, New York
Eman River, Sweden
Lockpoit, New York
Eman River, Sweden
Lockpoit, New York
Eman River, Sweden
NR
PCB contaminated
NR
PCB contaminated
NR
NR
PCB contaminated
Samp.
year
NR
88
86*88
88
NR
88
NR
88
NR
88
86-88
NR
feef,
\ no.
3
2
2
2
3
2
3
2
3
2
2
3
V-374.S7)
NR
NR
PCB contaminated
NR
PCB contaminated
NR
PCB contaminated
88
88
NR
88
NR
88
NR
2
2
3
2
3
2
3
Continent*
raw surface drinking water
raw surface drinking water
treated surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
treated surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
B-17
-------
Table B-4. Environmental Lercfa of Dibenzofarami in Water (ppq) (continued)
Chemical
1,2,3,4,7,9/1,2,3,4,7,8-HxCDF
HxCDFs
1,2,3,4,6,7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
HpCDFs
Number
2
1
22
2
1
2
2
1
22
2
Number
positive
samples
2
1
0
2
1
2
2
1
0
2
Concentration
tinge
.021-.026
85
ND(.3-4.4)
.17-. 19
210
.083-. 13
.03-.058
210
ND(.S-6.6)
.18-.35
Cone.
.024
NA
NA
.18
210
.11
.044
210
NA
.26
Location
Eman River, Sweden
Lockport, New York
New York State
Eman River, Sweden
Lockport, New York
Eman River, Sweden
Eman River, Sweden
Lockport, New York
New York State
Eman River, Sweden
Location
description
PCB contaminated
NR
NR
PCB contaminated
Samp.
yew
NR
88
86-88
NR
V-409.31)
NR
PCB contaminated
PCB contaminated
NR
NR
PCB contaminated
88
NR
NR
88
86-88
NR
Ret
no.
3
2
2
3
2
3
3
2
2
3
Comments
raw surface drinking water
raw surface drinking water
treated surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
raw surface drinking water
treated surface drinking water
raw surface drinking water
Octachkwd&eozoftjran* (MW «• 444.76)
1,2,3,4 ,6,7,8,9-OCDF
22
1
2
2
1
2
ND-0.8
230
.15-.36
2.45
230
.26
New York State
Lockport, New York
Eman River, Sweden
NR
NR
PCB contaminated
86-88
88
NR
2
2
3
treated surface drinking water
raw surface drinking water
raw surface drinking water
Footnote Refi
NOTES: Summary statistics provided in or derived from references; when reference did not compute mean, one-half the detection limit was used for non-detects. Therefore, it ii possible to have mean concentrations greater than
the range (e.g., reported detection limit for nondetects greater than the positive sample).
NA = not applicable;
ND — non-detected (limit of detection);
NR " not reported.
Descriptions provided were those given by reference or surmised from study description when not given.
Sources: 2. Meyer, et al. (1989)
3. Rappe, et al. (1989b)
B-18
-------
Table B-5. Environmental Levels of Dioxms in Sediments (ppt)
Chemical
Number
sample* .
Number
positive
samptef
Concentration
.... range
Cow.
mean
Wt,
basis
Location
Location
Sample
Ref,
Comments*
T«twd«l«Modib«nzo-p-dioxitw (MW-321 -V8)
2,3,7,8-TCDD
18
9
4
2
1
1
2
3
3
1
2
1
1
12
4
4
2
3
4
4
0
8
4
2
1
1
2
1
3
1
1
1
0
6
0
0
2
2
4
1
ND
ND-730
75-2500
190-1200
680
150
660-1100
ND-7600
390-2900
93
ND-7600
21,000
ND
ND-57
ND
ND
1.0-1.4
ND-2.4
1.9-26
ND-3
NA
236
1769
695
680
150
880
367
1227
93
3800
21000
NA
13
NA
NA
1.2
1.5
9.6
1.19
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
NR
Dry
NR
Dry
NR
South Central Finland
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Long bland Sound
New England
Seattle, WA
Central Minnesota
Baltic Sea
Stockholm Sweden
Iggesund Sweden
Data River, Sweden
Various
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Reference Site
Industrial
Industrial
Rural
Reference Site
Various
Industrial
Industrial
88/89
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
NR
NR
NR
NR
NR
NR
NR
88
1
2
2
2
2
2
2
2
2
2
2
2
4
4
4
5
13
12
13
17
A,B
0-2", A,C
2-4", A,C
4-8", A,C
12-16", A,C
20-24", A,C
24-28", A,C
28-32", A,C
32-36", A,C
40-44", A,C
48-52", A,C
108-1 11",A,C
A
A/3 sites
A
A
A
A
0-1 cm
B-19
-------
Table B-5. Environmental Levels of Dwrins in Sediments (ppt) (continued)
Chemical
2,3,7,8-TCDD (continued)
TCDDs
Number
• samples
6
5
4
1
1
5
18
1
1
1
4
25
12
3
4
2
4
Number
positive
'ttmpwfl
6
3
4
1
1
5
14
1
1
0
0
0
7
3
4
2
4
Concentration
range
1.2-32
ND-110
0.03-0.11
0.04
0.01
3.4-1,500
ND-1,400
26
12
ND
ND
ND
ND-44
21-69
21-66
19-35
1.4-6.7
CotK.
mean
12.0
28.1
0.06
0.04
0.01
375
372
26
12
NA
NA
NA
17
38
45
27
4.2
Wt.
basil
NR
NR
Dry
Dry
Dry
NR
Dry
Dry
Dry
Dry
NR
NR
NR
NR
Dry
Dry
Dry
Location
Lake Vattera, Sweden
Lake Vanern, Sweden
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Fjord between Demark,
Sweden, and Norway
Hamburg Germany
South Central Finland
Sitkiwit Lake, late Royale,
Lake Michigan
Sitkiwit Lake, We Royale,
Lake Michigan
Siskiwit Lake, Isle Royale,
Lake Michigan
Central Minnesota
Ontario Canada
NY/Mass
Stockholm Sweden
Iggesund Sweden
Baltic Sea
Fjord between Denmark,
Sweden, and Norway
Location
description
Industrial
Industrial
Industrial
Industrial
Industrial
Urban
Various
Pristine
Pristine
Pristine
Rural
Industrial
NR
Various
Industrial
Reference Site
Industrial
Sample
year
88
88
87
87
87
NR
88/89
NR
NR
NR
NR
88
NR
NR
NR
NR
87
Ref.
no.
17
17
14
14
14
15
1
3
3
3
5
8
10
12
13
13
14
CoflntdfctttF
0-1 cm
0-1 cm
0-1 cm, E
4-6 cm, E
9-13 cm, E
AB
0-0.5 cm, A,D
5-6 cm, A,D
8-9 cm, A,D
A/4 sites
A/25 sites
A
A
A/paper mill
A
0-2 cm, E
B-20
-------
Table B-5. Environmental Levels of Diorins in Sediments (ppt) (continued)
Chemical
TCDDs
(continued)
Number
samples
I
1
5
Number
positive
MLfnpl&s
i
i
5
Concentration
range
13
5.0
80-1,700
Cone.
me*a
13
5.0
564
Wt,
baste
Dry
Dry
NR
Location
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Hamburg Germany
Location
ocacripboti
Induitrial
Industrial
Urban
Sample
year
87
87
NR
Ret
no.
14
14
15
Comment**
4-6 cm, E
9-13 cm, E
Pent»chk)rodR)enzo-p^ioxin»(MW»356.42)
1,2,3,7,8-PeCDD
PeCDDs
4
6
5
1
1
1
4
25
12
3
4
2
4
3
6
4
1
1
0
0
0
7
3
4
2
4
ND-25
7.4-95
ND-100
12
11
ND
ND
ND
ND-235
86-230
52-500
52-100
1.7-41
7.68
44.1
49.6
12
11
NA
NA
NA
50
138
209
76
19
NR
NR
NR
Dry
Dry
Dry
NR
NR
NR
NR
Dry
Dry
Dry
Dala River, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Sisltiwit Lake, Itle Royale,
Lake Michigan
Siskiwit Lake, ble Royale,
Lake Michigan
Siikiwit Lake, ble Royale,
Lake Michigan
Central Minnesota
Ontario Canada
NY/Man
Stockholm Sweden
Iggesund Sweden
Baltic Sea
Fjord between Denmark,
Sweden, and Norway
Induitrial
Induitrial
Induitrial
Pristine
Pristine
Pristine
Rural
Industrial
NR
Various
Industrial
Reference Site
Industrial
88
88
88
NR
NR
NR
NR
88
NR
NR
NR
NR
87
17
17
17
3
3
3
5
8
10
12
13
13
14
0-1 cm
0-1 cm
0-1 cm
0-0.5 cm, A,D
5-6 cm, A,D
8-9 cm, A,D
A/4 sites
A/25 sites
A
A
A/paper mill
A
0-2 cm, E
B-21
-------
Table B-5. Environmental Leveb of Mourns in Sedbnents (ppt) (continued)
Chemktt
PeCDDs
(continued)
Number
•ample*
1
1
5
Number
positive
samples
1
1
5
Concentration
range
6.6
15
260-2,700
Cone.
mean
6.6
15
1,112
Wt,
basi*
Dry
Diy
NR
Location
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Hamburg Germany
Location
description
Industrial
Industrial
Urban
Sample
year
87
87
NR
Ref.
no.
14
14
15
Comments*
4-6 cm, E
9-13 cm, E
: Hex»chlorodibenzo-jMlioxiin(MWa»390.87)
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
HxCDD»
4
6
5
4
6
5
4
6
5
1
1
1
4
25
3
6
5
4
6
5
4
6
5
1
1
0
2
6
ND-19
6.1-33
14-94
4.9-120
21-450
36-600
3.9-51
18-200
18-330
10
8
ND
ND-14
ND-5,700
6.68
20.5
36.0
36.4
188
236
18.1
95.5
149
10
8
NA
5.2
1,157
NR
NR
NR
NR
NR
NR
NR
NR
NR
Diy
Dry
Dry
NR
NR
Dala River, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Dala River, Sweden
Lake Vattem, Sweden
Lake Vanern, Sweden
Dala River, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Siakiwit Lake, ble Royale,
Lake Michigan
Siskiwit Lake, ble Royale,
Lake Michigan
Siakiwit Lake, ble Royale,
Lake Michigan
Central Minnesota
Ontario Canada
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Pristine
Pristine
Pristine
Rural
Industrial
88
88
88
88
88
88
88
88
88
NR
NR
NR
NR
88
17
17
17
17
17
17
17
17
17
3
3
3
5
8
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-0.5 cm, A.D
5-6 cm, A,D
8-9 cm, A,D
A/4 sites
A/25 sites
B-22
-------
Table B-5. Environmental Leveb of Dioxms in Sediments (ppt) (continued)
Chemical
HxCDDs
(continued)
Number
samples
12
3
2
4
4
1
1
5
Number
positive
sample*
10
3
2
4
4
1
1
5
Concentration
range
ND-1,335
16-49
120-170
130-1,900
2.3-27.0
16
14
580-7,500
Cone.
mean
399
28
145
608
14
16
14
2,744
Wt,
basi*
NR
NR
Dry
Dry
Dry
Dry
Dry
NR
Location
NY/Man
Stockholm Sweden
Baltic Sea
Iggesund Sweden
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Hamburg Germany
Location
description . . .
NR
Various
Reference Site
Industrial
Industrial
Industrial
Industrial
Urban
Sample
year
NR
NR
NR
NR
87
87
87
NR
Ref.
no.
10
12
13
13
14
14
14
IS
Comments*
A
A
A
A/paper mill
0-2 cm, E
4-6 cm, E
9-13 cm, E
Hept*chlorodibem»iM»o»n»(MW«425.31) :
HpCDDi
4
25
12
3
2
4
4
1
4
20
11
3
2
4
4
1
7.3-110
ND-320,000
ND-18,950
880-5,700
79-210
90-340
2.2-19
7.2
71
51,680
4,168
2,233
145
190
12.4
7.2
NR
NR
NR
NR
Dry
Dry
Dry
Dry
Central Minnesota
Ontario Canada
NY/Mass
Stockholm Sweden
Baltic Sea
Iggesund Sweden
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Rural
Industrial
NR
Various
Reference Site
Industrial
Industrial
Industrial
NR
88
NR
NR
NR
NR
87
87
5
8
10
12
13
13
14
14
A/4 sites
A/25 sites
A
A
A
A/paper mill
0-2 cm, E
4-6 cm, E
B-23
-------
Table B-5. Environmental Levels of Dioxms in Sediments (ppt) (continued)
Chemical
HpCDDi (continued)
Number
•ample*
1
5
Number
positive
uinp tea
1
5
Concentration
range
7.1
1,300-8,600
Cone.
mean
7.1
4,040
Wt,
ba»i*
Dry
NR
Location
Fjord between Denmark,
Sweden, and Norway
Hamburg Germany
Location
description
Industrial
Urban
Sample
year
87
NR
Ret
no.
14
15
Comments*
9-13 cm, E
Octochlorodib*nzo|>-
1,2,3,4,6,7,8,9-OCDD
18
9
4
2
1
1
2
2
3
1
2
1
1
1
1
3
9
4
2
1
1
2
2
3
1
2
1
1
1
1
ND-42
3,100-14,000
5,300-23,000
10,000-31,000
7,500
5,900
11,000-19,000
5,500-22,000
5,600-42,000
5,500
4,400-24,000
38,000
560
390
54
6.1
8,100
14,100
20,500
7,500
5,900
15,000
13,800
17,800
5,500
14,200
38,000
560
390
54
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
South Central Finland
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Siskiwit Lake, Isle Royale,
Lake Superior
Siikiwit Lake, ble Royale,
Lake Superior
Siikiwit Lake, Iile Royale,
Lake Superior
Various
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Pristine
Pristine
Pristine
88/89
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
NR
NR
NR
1
2
2
2
2
2
2
2
2
2
2
2
3
3
3
A,B
0-2% A,C
2-4', A,C
4-8", A,C
12-16', A,C
20-24", A,C
24-28% A,C
28-32', A,C
32-36% A,C
40-44% A,C
48-52% A,C
108-11 1%A,C
0-0.5 cm, A,D
5-6 cm, A,D
8-9 cm, A,D
B-24
-------
Table B-5. Environmental Lereb of Dkndns in Sediments (ppt) (continued)
chenfcat
1,2,3,4,6,7,8,9-OCDD
(continued)
Number
samples
4
25
12
7
3
2
4
4
6
5
4
1
1
5
Number
positive
samplei
4
20
12
7
3
2
4
4
6
5
4
1
1
5
Concentration
range
450-600
ND-980,000
1,990-15,500
12-250
260-3,100
89-250
96-330
180-16,830
800-2200
1320-6090
3.6-45
10
6.9
2,800-15,000
Co«.
mean
518
141,420
8,201
145
1,290
170
194
5195
1775
3040
24
10
6.9
7,560
Wt,
butt
NR
NR
NR
Dry
NR
Dry
Dry
NR
NR
NR
Dry
Dry
Dry
NR
Locution
Central Minnesota
Ontario Canada
NY/Mass
Jackfish Bay, Lake
Superior
Stockholm Sweden
Baltic Sea
Iggesund Sweden
Data River, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Fjord between Denmark,
Sweden, and Norway
Hamburg Germany
Location
description
Rural
Industrial
NR
Various
Various
Reference Site
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Urban
Simple
year
NR
88
NR
NR
NR
NR
NR
88
88
88
87
87
87
NR
Kef.
no.
5
8
10
11
12
13
13
17
17
17
14
14
14
15
Comfiifetttir
A/4 sites
A/25 sites
A
Papermill,
atmospheric
contamination
A
A
A/paper mill
0-1 cm
0-1 cm
0-1 cm
0-2 cm, E
4-6 cm, E
9-13 cm, E
B-25
-------
Table B-5. Environmental Levels of Dioxins in Sediments (ppt) (continued)
* Key: A LOD (Ref 1) = 20 to 50 ppt, LOD (Ref 2) = 22 to 60 ppt, LOD (Ref 3) = 0.4 ppt, LOD (Ref 4) = 0.7 to 12.0 ppt, LOD (Ref 5) = 0.61 to 4.1 ppt, LOD (Ref 8) = 10 to 500 ppt, LOD (Ref 10) = 3 ppt,
LOD (Ref 12) = 1 to 20 ppt, LOD (Ref 13) = 1 to 6.6 ppt.
B Dry surface sediments from 18 lakes.
C Industry produced 2,4,5-Trichlorophenate (2,4,5-T precursor).
D No anthropogenic inputs into drainage basin—only atmospheric sources into lake.
E Mg-Production Facility.
Notes
NR = Not Reported
NA = Not Applicable
ND = Not Detected
ppt — Parts per trillion
Sources:
1. Koistinen et al. (1990)
2. Bopp et al. (1991)
3. Czuczwa et al. (1984)
4. Norwood et al. (1989)
5. Reed et al. (1990)
6. Sonzongietal. (1991)
7. Oliver and Nilmi (1988)
8. McKee et al. (1990)
9. Huckins et al. (1988)
10. Petty et al. (1982)
11. Sherman et al. (1990)
12. Rappe and Kjeller (1987)
13. Rappe et tl. (1989a)
14. Oehme et al. (1989)
15. Gotz and Schumacher (1990)
16. Smith et al. (1990)
17. Kjeller et »l. (1990)
B-26
-------
Table B-6. Environmental Lereb of Dibenzornraus in Sediment (ppt)
^frhfliftf aft
Number
••upfe*
Number
positive
samples
Concentration
xao£Q
Cone.
mean
Weight
bum
Location
Location
description
Stttpte
year
Ref*
no.
Commenu*
TeJr»chioroda>«nzofiir»n8(MW»305.9S) :
2,3,7,8-TCDF
18
9
4
2
1
1
2
3
3
1
2
1
1
12
4
4
2
4
4
6
0
9
4
2
1
1
2
2
3
1
2
1
1
12
0
1
2
4
4
6
ND(20-50)
24-490
150-1,400
580-1,200
370
300
300-390
ND-530
190-730
140
80-3,100
4,500
15
8.8-1,400
ND(0.7-12)
ND-0.31
8.3-14
11-210
4.9-170
41-320
NA
232
855
890
370
300
345
243
370
140
1,590
4,500
15
566
NA
0.08
11
72
46.5
176
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Dry
NR
Dry
Dry
NR
NR
South Central Finland
Newark, NI
Newark, NJ
Newark, NI
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Newark, NJ
Long Island Sound
New England
Seattle, WA
Central Minnesota
Baltic Sea
Iggesund Sweden
Dala River, Sweden
Lake Vattern, Sweden
Various
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Reference Site
Industrial
Industrial
Rural
Reference Site
Industrial
Industrial
Industrial
88/89
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
85/86
NR
NR
NR
NR
NR
NR
88
88
1
2
2
2
2
2
2
2
2
2
2
2
4
4
4
5
13
13
17
17
A,B
0-2", A,C
2-4", A,C
4-8", A,C
12-16", A,C
20-24", A,C
24-28", A,C
28-32", A,C
32-36", A,C
40-44", A,C
48-52", A,C
108-1 11",A,C
A
A/3 rites
A
A/4 sites
A
A/papermill
0-1 cm
0-1 cm
B-27
-------
Table B-6. Environmental Levels of Dibcsuoftmns in Sediment (ppt) (continued)
chemical
2,3,7,8-TCDF (continued)
TCDFs
Nu}tib#f
•ample*
5
4
1
1
1
1
1
4
25
12
7
3
2
4
4
Number
positive
samples:
5
4
1
1
1
1
0
2
0
11
7
3
2
4
4
Concentration
range
54-810
0.7-9.6
13
5.2
15
18
ND(0.4)
ND-0.54
ND(10-700)
ND-200
2.4^,223
120-290
87-130
79-360
6.7-54
Coac*
mean
241
5.2
13
5.2
15
18
NA
0.21
NA
58
1,260
187
109
180
30
Weight
basil
NR
Dry
Dry
Dry
Dry
Dry
Dry
NR
NR
NR
Dry
NR
Dry
Dry
Dry
Location
Lake Vanern, Sweden
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Siakiwh Lake, Isle
Royale, Lake Superior
Siskiwit Lake, Isle
Royale, Lake Superior
Siskiwit Lake, Isle
Royale, Lake Superior
Central Minnesota
Ontario Canada
NY/MASS
Jackfish Bay, Lake
Superior
Stockholm Sweden
Baltic Sea
Iggesund Sweden
Fjord between Sweden,
Norway and Denmark
Location
descnpfion
Industrial
Industrial
Industrial
Industrial
Pristine
Pristine
Pristine
Rural
Industrial
NR
Various
Various
Reference Site
Industrial
Industrial
Sample
year
88
87
87
87
NR
NR
NR
NR
88
NR
NR
NR
NR
NR
87
Ret
no.
17
14
14
14
3
3
3
5
8
10
11
12
13
13
14
Comments"
0-1 cm
0-2cm, E
4-6cm, E
9- 13cm, E
0-0.5cm, A,D
5-6cm, A,D
8-9cm, A,D
A/4 sites
A/25 sites
A
Papermill/
atmospheric
contamination
A
A
A/papermill
0-2cm, E
B-28
-------
Table B-6. Environmental Lends of
in Sediment (ppt) (continned)
Chemic*!
TCDFs
(continued)
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
PeCDFi
Number
•unpin
1
1
5
4
6
5
4
6
5
1
1
1
4
25
12
3
2
Number
potitiv*
samples
1
1
5
4
6
5
4
6
5
1
1
0
2
0
9
3
2
rangg •
63
23
170-1070
Cone,
mean
63
23
526
Weight
: fettB
Diy
Diy
NR
.' "•• toc*tton
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Hamburg Germany
PenUcfalofodD>enzoiunD«(MW«s 340.42)
5.6-110
27-120
50-300
7.8-99
25-110
36-250
5.0
2.0
N D(0.4)
ND-25
ND(10-700)
ND-193
130-260
66-125
34.4
74.3
120
34.7
74.2
108
5.0
2.0
NA
7.4
NA
64
177
%
MR
NR
NR
NR
NR
NR
Diy
Dry
Dry
NR
NR
NR
NR
Dry
Dala River, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Dala River, Sweden
Lake Vattem, Sweden
Lake Vanern, Sweden
Siikiwh Lake, Iile
Royale, Lake Michigan
Siikiwit Lake, ble
Royale, Lake Michigan
Siikiwit Lake, Isle
Royale, Lake Michigan
Central Minnesota
Ontario Canada
NY/MASS
Stockholm Sweden
Baltic Sea
Location
dciiciij)fioK[
Industrial
Industrial
Urban
Simple
yew
87
87
NR
R«t
oo.
14
14
15
Cotiuueuts*
4-6cm, E
9-13cm, E
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Pristine
Pristine
Pristine
Rural
Industrial
NR
Various
Reference Site
88
88
88
88
88
88
NR
NR
NR
NR
88
NR
NR
NR
17
17
17
17
17
17
3
3
3
5
8
10
12
13
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-0.5cm A,D
5 -6cm A,D
8-9cm A,D
A/4 sites
A/25 rites
A
A
A
B-29
-------
Table B-6. Environmental terete of Dibtmoftiram in
(ppt) (continued)
Chemical
PeCDFi (continued)
1,2,3,4,7,8-HxCDF
1,2,3,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6,7,8-HxCDF
Number
Minplei
4
4
1
1
5
4
6
5
4
6
5
4
6
5
4
6
5
Number
positive
sample*
4
4
1
1
5
4
6
5
4
6
5
3
2
2
4
6
5
Concentration
range
48-58
7.7-81
24
44
1,300-5,200
9.3-120
28-170
32-460
3.7-73
15-110
25-140
ND(2)-25
ND-4.4
ND-14
1.8-78
32-130
36-110
Cone,
mean
55
47
24
44
2,980
Hexachtoro
44.3
89.5
163
26.7
64.7
73.4
9.38
1.58
5.68
26.2
77.7
70.8
Weight
basic
Diy
Dry
Dry
Dry
NR
IwfilUEtHlIttttt-
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Location
Iggeaund Sweden
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Hamburg Germany
(MW«374.«7)
Dak River, Sweden
Lake Vattem, Sweden
Lake Vanern, Sweden
Dal* River, Sweden
Lake Vattem, Sweden
Lake Vanern, Sweden
Dab River, Sweden
Lake Vattem, Sweden
Lake Vanern, Sweden
Dala River, Sweden
Lake Vattem, Sweden
Lake Vanem, Sweden
Location
description
Industrial
Industrial
Industrial
Industrial
Urban
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Sample
year
NR
87
87
87
NR
88
88
88
88
88
88
88
88
88
88
88
88
Ret
no.
13
14
14
14
15
17
17
17
17
17
17
17
17
17
17
17
17
Comment*"
A/papermill
0-2cm, E
4-6cm, E
9- 13cm, E
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
0-1 cm
B-30
-------
Table B^S. EoTironmental Ler«b of DibauoAraH •
(opt) (continued)
—
HxCDFs
1,2,3,4,6,7,8-HpCDF
Number
sampks
1
1
1
4
25
12
3
2
4
4
1
1
5
8
12
10
Number
positive
1
1
0
1
17
10
3
2
4
4
1
1
5
8
12
10
Concentration
range
2.0
2.0
ND(0.4)
ND-12
ND-6,500
ND-377
92-250
78-150
59-150
23-283
166
131
930-8,600
59-2180
130-1030
21-8400
Cone*
mean'
2.0
2.0
NA
3.0
1,339
133
187
114
104
148
166
131
4,106
Heptachlorc
558
584
1764
Weight
basis
Dry
Dry
Dry
NR
NR
NR
NR
Dry
Dry
Dry
Dry
Dry
NR
NR
NR
NR
*-..;
Siskiwh Lake, Isle
Royale, Lake Michigan
Siskiwh Lake, Isle
Royale, Lake Michigan
Siskiwh Lake, Isle
Royale, Lake Michigan
Central Minnesota
Ontario Canada
NY/MASS
Stockholm Sweden
Baltic Sea
Iggesund Sweden
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Hamburg Germany
Data River, Sweden
Lake Vattem, Sweden
Lake Vanern, Sweden
Location
description
Pristine
Pristine
Pristine
Rural
Industrial
NR
Various
Reference Site
Industrial
Industrial
Industrial
Industrial
Urban
Industrial
Industrial
Industrial
Sample
year
NR
NR
NR
NR
88
NR
NR
NR
NR
87
87
87
NR
88
88
88
ftftf.
no.
3
3
3
5
8
10
12
13
13
14
14
14
15
17
17
17
«—
0-0.5cm, A,D
5-6cm, A,D
8-9cm, A,D
A/4 sites
A/25 sites
A
A
A
A/papermill
0-2cm, E
4-6cm, E
9-13cm, E
0-1 cm
0-1 cm
0-1 cm
B-31
-------
Table V-6. EnTinnmental Levels off Dibeiuofaram • Sedhnent (ppt) (contmned)
Chemical
1,2,3,4,7,8,9-HpCDF
HpCDFi
Number
•ample*
4
6
5
4
25
12
3
2
4
4
1
1
5
Number
positive
•ample*
3
6
4
3
20
10
3
2
4
4
1
1
5
Concentration
• •• tangc
ND-42
4.3-91
ND-260
ND-30
ND-53,000
ND-2,436
190-1,500
79-180
11-410
20-158
43
192
560-4,300
Coac,
mean
14.2
33.2
78.3
16
11,715
1,039
997
130
178
100
43
192
2,358
Weight
basil
NR
NR
NR
NR
NR
NR
NR
Dry
Dry
Dry
Dry
Dry
NR
Location
Dala River, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Central MinneioU
Onurio Canada
NY/MASS
Stockholm Sweden
Baltic Sea
Iggeaund Sweden
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Hamburg Germany
Location
description
Industrial
Industrial
Industrial
Rural
Industrial
NR
Various
Reference Site
Industrial
Industrial
Industrial
Industrial
Urban
Sampte
year
88
88
88
NR
88
NR
NR
NR
NR
87
87
87
NR
Re£
no.
17
17
17
5
8
10
12
13
13
14
14
14
15
Comments*
0-1 cm
0-1 cm
0-1 cm
A/4 sites
A/25 sites
A
A
A
A/papennill
0-2cm, E
4-6cm, E
9-13cm, E
Oot«chlorod!beniofiir«a(MW».444.76}
1,2,3,4,6,7,8,9-OCDF
18
1
1
3
1
1
ND-160
4
3.2
14
4
3.2
Dry
Dry
Dry
South Central Finland
Siikiwit Lake, Isle
Royale, Lake Michigan
Siskiwit Lake, ble
Royale, Lake Michigan
Various
Pristine
Pristine
88/89
NR
NR
1
3
3
A,B
0-0.5cm, A,D
5-6cm, A,D
B-32
-------
Table B-6. Environmental Levels of Dibeniofuram in Sediment (ppt) (continued)
Chwafed
1,2,3,4,6,7,8,9-OCDF
(continued)
Number
samples
1
4
25
12
3
2
4
4
6
5
4
1
1
5
Number
positive
sample*
1
1
21
11
1
1
2
4
6
5
4
1
1
5
Concentration
range
1.1
ND-23
ND-400,000
ND-1,010
ND-39
ND-3.8
ND-15
150-4250
170-1310
230-79,250
58-151
43
192
660-5,200
Cone, ..
mean
1.1
5.8
34,912
460
14
1.9
5
1212
602
19,356
96
43
192
2,712
Weight
baii*
Dry
NR
NR
NR
NR
Dfy
Dry
NR
NR
NR
Dry
Dry
Dry
NR
Location
Siskiwit Lake, ble
Royale, Lake Michigan
Central Minnesota
Ontario Canada
NY/MASS
Stockholm Sweden
Baltic Sea
Iggesund Sweden
Dala River, Sweden
Lake Vattem, Sweden
Lake Vanera, Sweden
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Fjord between Sweden,
Norway and Denmark
Hamburg Germany
Location
description
Pristine
Rural
Industrial
NR
Various
Reference Site
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Uifaan
Sample
year
NR
NR
88
NR
NR
NR
NR
88
88
88
87
87
87
NR
Ret
no.
3
5
8
10
12
13
13
17
17
17
14
14
14
15
Comment**
8-9cm, A,D
A/4 sites
A/25 sites
A
A
A
A/Papermill
0-1 cm
0-1 cm
0-1 cm
0-2cm, E
4-6cm, E
9-13cm, E
•Key: A LOD (Ref. 1) = 20 to 50 ppt, LOD (Ref. 2) = 32 ppt, LOD (Ref. 3) - 0.4 ppt, LOD (Ref. 4) = 0.7 to 12.0 ppt, LOD (Ref. 5) - 0.61 to 4.1 ppt, LOD (Ref. 8) - 10 to 700 ppt, LOD (Ref. 10)
= 3 ppt, LOD (ref. 12) = 1 to 20 ppt, LOD (Ref. 13) = 1 to 6.6 ppt.
B Dry surface sediments from 18 lakes.
C Industry produced 2,4,5 trichlorophenate (2,4,5T precursor).
D No anthropogenic inputs into drainage basin — only atmospheric sources into lake.
E Mg-production facility.
B-33
-------
Notes
NR = Not Reported
NA = Not Applicable
ND = Not Detected
ppt = Parti per trillion
Table B-6. Environmental Levels of Dibenzofurans in Sediment (ppt) (continued)
Sources:
1. Koutinen et al. (1990)
2. Bopp et al. (1991)
3. Czuczwaetal. (1984)
4. Norwood et al. (1989)
5. Reed et al. (1990)
6. Sonzoogietal. (1991)
7. Oliver and Nitari (1988)
8. McKee et al. (1990)
9. Huckins et al. (1988)
10. Petty et al. (1982)
11. Sherman etal. (1990)
12. Rappe and Kjeller (1987)
13. Rappe etal. (1989»)
14. Oehme et al. (1989)
15. Gotz and Schumacher (1990)
16. Smith et al. (1990)
17. Kjeller et al. (1990)
B-34
-------
Table B-7. EnTiromncntal Levels of PCBs in Sediment (ppt)
IUPAC Chemical
flumfref
Jfambcr •
tAfnptat
Number
positive
ample*
Concentration
range
Cone.
mean
Wt. basis
Tetr»chtoro-PCB
-------
Table B-7. Environmental Levels of PCBs in Sediment (ppt) (continned)
iUPAC Chemical
number
114 2,3,4,4',5-PeCB
118 2,3',4,4',5-PeCB
156 2,3,3',4,4',5-HxCB
167 2,3',4,4',5,5'-HxCB
169 3,3',4,4',5,5'-HxCB
Number
samples
8
NR
8
38
NR
2
Number
positive
sunpMMi
1
NR
8
NR
NR
0
38
NR
8
NR
18
8
NR
NR
NR
2
NR
0
3
NR
Concentration
range
ND-1 10,000
NR
86,000-
1.48M
NR
NR
0.01
Cone*
mean
13,750
1,000
351,620
15,000
11,000
0.01
Wt basil
Dry
Dry
Dry
Dry
Dry
Dry
HeMchloro-PCB(MW=
NR
NR
ND-80,000
NR
ND(20-50)
ND-19,000
NR
2,100
1,700
15,500
ND<500)
NA
4,800
ND(500)
Dry
Dry
Dry
Dry
Dry
Dry
Dry
Location
Eastern Wisconsin
Green Bay, Lake
Michigan
Eastern Wisconsin
Lake Ontario
Green Bay, Lake
Michigan
Alicante, Spain
description
Industrial
Various
Industrial
Various
Various
Coastal
=360.88)
Lake Ontario
Green Bay, Lake
Michigan
Eastern Wisconsin
Green Bay, Lake
Michigan
South Central
Finland
Eastern Wisconsin
Green Bay, Lake
Michigan
Various
Various
Industrial
Various
Various
Industrial
Various
Sample
year
88/89
NR
88/89
81
NR
89/90
Ref,
no. '
6
16
6
7
16
17
CoOttnftnttr
A,D
A
A,D
Bottom Sediment
A
81
NR
88/89
NR
88/89
88/89
NR
7
16
6
16
1
6
16
Bottom Sediment
A
A,D
A
A,B
A,D
A
Heptachloro-PCB (MW-396.33)
189 2,3,3',4,4',5,5'HpCB
NR
NR
NR
ND(500)
Dry
Green Bay, Lake
Michigan
Various
NR
16
A
B-36
-------
Table B-7. Environmental Levels of PCBs in Sediment (ppt) (contmned)
*Key: A LOD (Ref. 1)=20 to 50 ppt, LOD (Ref. 6)=l,000ppt, LOD (Ref. 16)=500ppt.
B Dry Surface Sediments from 18 lakes.
C All collected samples not analyzed.
D Superfund/Michigan "Area of Concent" Site.
NOTES:
NR = Not Reported
NA = Not Applicable
ND = Not Detected
ppt = Parts per trillion
Sources:
1. Koistinen, et al. (1990) 9. Huckin», et al. (1988)
6. Sonzongi, et al. (1991) 16. Smith, et al. (1990)
7. Oliver and Nilmi (1988) 17. Prats, et al. (1992)
B-37
-------
Table B-8. Enriromnotfal Lercb •(Dions • Ffafc
'• —
Fish
specie?
2,3,7,8-TCDD
Eel
Eel
Trout
Grayling
Barbel
Carp
Chub
Eel
Bream
Perch
Herring
Herring
Herring
Salmon
Salmon
Perch
Artie Char
Pike
Pike
Ch. Catfish
Ttwue
Liver
Fillet
Fillet
Fillet
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Muscle
Muscle
NR
NR
Muscle
Muscle
Filleu
Number
sample*
6
5
1
1
1
1
1
5
14
3
1
2
2
2
2
3
5
8
1
8
Number
positive
samples
6
5
1
1
1
1
0
5
14
3
0
0
0
2
2
3
5
8
1
8
Concentration
range
Tetrachtorodfix
1.2-9.1
2.4-3.3
1.4
3.8
5.1
2.5
ND(2.3)
0.9-1.5
1.4-94.4
1.8-8.1
ND(0.1)
ND(0.1)
ND(0.1)
4.6-19.0
0.2-0.3
2.6-19
6.5-25
40-833
78
28-695
COJtt, :-•
mnMHlioftia*
3.32
3.04
1.4
3.8
5.1
2.5
NA
1.3
18.0
5.9
NA
NA
NA
11.8
0.25
11.5
14.3
186
78
157
bMi*
(MW— 32
NR
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fvcn
Fresh
Freah
Fresh
Freah
Fresh
Freah
Freah
Freah
Fat
Fat
NR
tocMfew'
1.98)
Various, Netherlands
Rhine River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Hamburg, Germany
Hamburg, Germany
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Lake Vattern, Sweden
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Various, Michigan
Location
description
NR
NR
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Pristine
Urban
Industrial
NR
NR
NR
NR
Industrial
Industrial
NR
^.
NR
88
88
88
88
88
88
87-88
84
84
NR
NR
NR
NR
NR
NR
NR
88
88
78
no.
1
2
2
2
2
2
2
2
4
4
5
5
5
5
5
5
5
19
19
7
Comment*
one sample near dump site
up A downstream Basal
composite sample
composite sample
composite 5-10 fish
composite 5-10 fish
composite 5-10 fish
wild salmon
hatched salmon
caught near pulp mill
samples composite 2-5 fish
composite 5 fish
B-38
-------
Table B-8. Environmental Letefe of Dianas • fish (apt) (continued)
Chemical
2,3,7,8-TCDD
(continued)
Rub
specie**
Carp
Y. Perch
Sm. M. Baui
Sucker
Lake Trout
Carp
Carp
Carp
Blue Crab
Lobster
Sir. Ban
Lake Trout
Lake Trout
Lake Trout
Walleye
Walleye
Lake Trout
Lake Trout
Br. Trout
Br. Trout
Rb. Trout
Tissue
Fillet*
Fillet*
Fillets
Fillet*
Fillets
Whole
Whole
Whole
Meat
Meat
Fillet*
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Fillet*
Whole
Number
sample*
14
6
2
4
2
3
3
2
2
2
2
1
1
3
1
1
1
10
1
1
1
Number
positive
sample*
10
3
2
3
0
0
0
2
2
2
2
1
1
3
1
1
1
10
1
1
1
Concentt*t$on
range
20-153
10-20
7-8
4-21
ND(5.0)
ND(6.6)
ND(6.6)
3-28
106-116
4.7-6.3
83.9-734
1.0
8.6
3.5-5.8
1.8
6.6
48.9
3.0-8.7
6
5
14
Cone.
mean
55
13
8
10
NA
NA
NA
16
111
5.5
409
1.0
8.6
4.4
1.8
6.6
48.9
4.2
6
5
14
V\ffc
basis
NR
NR
NR
NR
NR
NR
NR
NR
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
NR
NR
NR
Location*
Various, Michigan
Various, Michigan
Various, Michigan
Various, Michigan
Various, Michigan
Mississippi River, MN
Lake Orooo, MN
Lake Huron
Passaic River, NJ
New York Bight
Newark Bay, NJ
Lake Superior
Lake Huron
Lake Michigan
Lake Erie
Lake St. Clair
Lake Ontario
Lake Michigan
Lake Ontario
Lake Ontario
Lake Ontario
Location
description
NR
NR
NR
NR
NR
Industrial
Industrial
NR
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Samp.
year
78
78
78
78
78
NR
NR
NR
NR
NR
NR
84
84
84
84
84
84
84
NR
NR
NR
Ref.
no.
7
7
7
7
7
8
8
18
10
10
10
11
11
11
11
11
11
11
12
12
12
Comment*
Elk River power station
Elk River power station
samples composite 3-5 fish
former sewage sludge
mean 5 sample*
mean 5 sample*
range 3 sample sites
mean 5 samples
mean 5 samples
mean 5 samples
composite 3 samples
composite 3 samples
composite 3 samples
B-39
-------
Table B-8. Environmental Lertfc of DMOM in Ffah (ppt) (continued)
Chemical
2,3,7,8-TCDD
(continued)
Fish
species*
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Cod
Haddock
P. Flounder
Plaice
Flounder
Eel
Muiael
Shrimp
Cod
Various
Sucker
LmBau
Rock Bass
RockBau
TlMMe
RUeU
Whole
Fillets
Whole
Filleu
Fillet*
Filleu
Filleta
Filleta
Filleu
Fdleu
Muacle
Muacle
Filleu
Mixed1
Whole
Fillet
Whole
Fillet
Nutnpef
sampiei
1
1
1
1
1
4
1
1
1
1
4
3
2
6
314
15
4
2
1
Number
positive
umples
1
1
1
1
1
0
0
0
0
0
1
0
0
MR
220
6
0
0
0
Concentration
range
5
18
8
20
6
ND(1.0)
ND(0.2)
ND(0.2)
ND(0.5)
ND(0.5)
ND-1.4
ND(0.5)
NEK2.0)
ND-3.8
NR
ND- 0.85
ND( 0.74-
1.39)
ND( 0.96-
1.49)
ND( 1.17)
COW.
mean
5
18
8
20
6
NA
NA
NA
NA
NA
0.35
NA
NA
NR
6.84
0.45
NA
NA
NA
wt,
buii
NR
NR
NR
NR
NR
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Wet
Wet
Wet
Wet
Wet
Location'
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Orenlandsfjord.Sweden
Orenlandsfjord.Sweden
Frierfjord, Sweden
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
NR
NR
NR
NR
NR
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Various
Background
Background
Background
Background
Samp.
year
NR
NR
NR
NR
NR
88
88
88
88
88
87-88
87
88
87
86-89
86-89
86-89
86-89
86-89
R*fc
no.
12
12
12
12
12
17
17
17
17
17
17
17
17
17
20
20
20
20
20
Comments
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 10 samples
composite 10 samples
composite 10 samples
composite 10 samples
only cone, range given
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-40
-------
Table B-8. ErmromnenUl Levels of Dioxms in Fish (ppt) (continued)
Chemical
2,3,7,8-TCDD
(contiued)
Bib
species*
SmBass
Redeye Ban
Clip
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Walleye
Chain Pickerel
Black Cnppie
Tiwue
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Number
•ample*
2
1
5
2
1
2
2
1
1
1
1
1
3
3
1
Number
ponitiv*
uraplet
0
0
2
0
0
0
2
0
0
0
1
0
0
0
0
Concentration
range
NEK 0.99-
1.10)
ND( 1.00)
ND-0.46
NEK 1.15-
2.35)
ND( 0.27)
NEK 0.34-
0.75)
1.87-2.26
NEK 0.58)
NEK 0.20)
NEK 0.99)
0.31
NEK 0.30)
NEK 0.10-
1.00)
NEK 0.10-
0.11)
NEK 0.16)
Cone.
mean
NA
NA
0.48
NA
NA
NA
2.06
NA
NA
NA
0.31
NA
NA
NA
NA
wt,
tunic
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
LocatJon"
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ret
BO.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
umples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
simples composite 3-5 fish
Samples composite 3-5
fish
Samples composite 3-5
fish
simplei composite 3-5 fish
simples composite 3-5 fish
simples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-41
-------
Table B-8. Environmental Levels of Dwrins in Ffah (ppt) (continued)
Clttttfcftt ;
2,3,7,8-TCDD
(continued)
TCDDi
•;f.. :/*»:;:, :
':. ::{:jfrCCie 1* -...,;:-..
Sea Catfish
North
Hogsucker
Summer
Flounder
DoOyVanlen
Composite
Bottom
Winter
Flounder
Bfaefish
White Catfish
Crayfish
Bieam
Ptefch
Cafp
Cup
BmeCiab
Lobster
Str. Bm
Br. Trout
HWM>
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
NR
NR
Whole
Whole
Meat
Meat
Fillet*
Whole
Number
•ample*
1
1
1
2
1
2
1
1
1
13
2
3
3
2
2
2
1
Number
positive
samples
0
0
0
0
0
1
1
1
0
13
2
1
0
2
2
2
1
Concentration
range
ND( 1.00)
ND( 1.00)
ND( 1-02)
ND(1.04-
1.11)
ND( 1-01)
ND-1.20
0.75
0.75
NEK 0.99)
2.5-102
9.0-10.5
ND-3.9
NEK6.6)
118-150
6.6-8.3
85.4-734
11
Cone.
mean
NA
NA
NA
NA
NA
1.02
0.75
0.75
NA
17.6
9.8
1.3
NA
134
7.4
410
11
Wt
tMUNff
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Freah
Freih
NR
NR
Wet
Wet
Wet
NR
Location'
Varioui, US
Various, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Hamburg, Germany
Hamburg, Germany
Mississippi River, MN
Lake Orono, MN
Passaic River, NI
New York Bight
Newark Bay, NI
Lake Ontario
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Urban
Urban
Industrial
Industrial
Urban
Dump Site
Urban
NR
Sump.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
84
84
NR
NR
NR
NR
NR
NR
Rfrf*
no.
20
20
20
20
20
20
20
20
20
4
4
8
8
10
10
10
12
Comments
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
Elk River power station
Elk River power station
former sewage sludge
composite 3 samples
B-42
-------
Table B-8. Environmental Leveb of Dkmns in Fish (pot) (continued)
Chemica!
TCDDs (continued)
Fish
specie*
Br. Trout
Rb. Trout
Rb. Trout
lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Ttttue
Fillets
Whole
FilleU
Whole
Fillet*
Whole
Fillets
Nult)0£f
•ample*
1
1
1
1
1
1
1
Number
positive
simples
1
1
1
1
1
1
1
Concentration
range
9
29
11
32
12
22
9
Cone.
mean
9
29
11
32
12
22
9
wt,
basis
NR
NR
NR
NR
NR
NR
NR
Location*
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Location
description
NR
NR
NR
NR
NR
NR
NR
Sftttlp*
ye*ir
NR
NR
NR
NR
NR
NR
NR
R*f.
no.
12
12
12
12
12
12
12
Comment*
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
Pent»chlofodfl>«nzo-p-dk>xini(MW»=356.42)
1,2,3,7,8-PeCDD
Carp
Pike
Pike
Herring
Herring
Sucker
Lin Ban
Rock Bass
Rock Bau
Sm Ban
Redeye Ban
Whole
Mutcle
Muscle
Whole
Whole
Whole
Fillet
Whole
Fillet
Fillet
Fillet
2
8
1
1
2
15
4
2
1
2
1
2
8
1
1
2
2
0
0
0
0
0
2-11
70-250
39
0.6
1.1-2.8
ND- 0.54
ND( 0.75-
2.18)
ND( 2.74-
2.99)
ND( 1.85)
ND( 0.92-
0.95)
ND( 0.92)
6
129
39
0.6
1.95
0.72
NA
NA
NA
NA
NA
NR
Fat
Fat
Freah
Fresh
Wet
Wet
Wet
Wet
Wet
Wet
Lake Huron
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
NR
Industrial
Industrial
Pristine
Urban
Background
Background
Background
Background
Background
Background
NR
88
88
NR
NR
86-89
86-89
86-89
86-89
86-89
86-89
18
19
19
5
5
20
20
20
20
20
20
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 5-10 fish
composite 5-10 fish
sample* composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-43
-------
Table B-8. Environmental Leveb of Dioxins in Rsh (ppt) (continued)
Chemical
1,2,3,7,8-PeCDD
(continued)
R«h
species*
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redbone
Black
Redbone
Golden
Redhone
Longear
Sunfish
Walleye
Chain Pickerel
Black Crappie
Sea Catfish
North
Hogsucker
TlttUe
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Number
simple*
5
2
1
2
2
1
1
1
1
1
3
3
1
1
1
rfttlmtef
positive
samples
1
0
0
0
0
0
0
0
1
0
0
0
0
0
0
Concentration
range
NEM).38
NEK 1.94-
5.33)
ND( 0.97)
NEK 0.48-
0.70)
NEK 1.11-
1.50)
NEK 1.75)
NEK 0.62)
NEK 1.10)
0.57
NEK 1.40)
ND( 0.37-
0.92)
NEK 0.19-
0.49)
NEK 0.20)
NEK 0.92)
NEK 0.97)
Cone.
mean
0.80
NA
NA
NA
NA
NA
NA
NA
0.57
NA
NA
NA
NA
NA
NA
Wt,
IMUH8
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location11
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Rtfc
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-44
-------
Table B-S. Environmental Leveb of Dioxms in Fish (ppt) (continued)
Chemical
1,2,3,7,8-PeCDD
(continued)
PeCDDs
Rah
species*
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefiih
White Catfish
Crayfish
Herring
Various'
Bream
Perch
Carp
Carp
Blue Crab
Lobster
Str. Bass
Br. Trout
Br. Trout
Tissue
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
Whole
Whole
Meat
Meat
Fillets
Whole
Fillets
Number
samples
1
2
1
2
1
1
1
2
34
13
2
3
3
2
2
2
1
1
Number
positive
samples
0
0
0
0
0
0
0
2
34
13
2
3
0
2
2
2
1
1
Concentration
range
ND(1.21)
ND( 0.92-
0.95)
ND( 0.95)
NEK 1.20-
1.24)
ND( 1.61)
NEK 1-01)
ND< 0.92)
2.0-4.7
0.15-2.67
3.2-27.8
9.8-29.8
3.5-4.5
NEK6.6)
17.2-18.0
10.0-11.0
5.2-10.6
8
6
Cone.
mean
NA
NA
NA
NA
NA
NA
NA
3.35
0.77
12.1
19.8
3.9
NA
17.6
10.5
7.9
8
6
Wt,
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fresh
Wet
Fresh
Fresh
NR
MR
Wet
Wet
Wet
NR
NR
Location"
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Gulf of Bothnia, Sweden
Various, US
Hamburg, Germany
Hamburg, Germany
Mississippi River, MN
Lake Orono, MN
Passaic River, NI
New York Bight
Newark Bay, NJ
Lake Ontario
Lake Ontario
Location
description
Background
Background
Background
Background
Background
Background
Background
Industrial
Background*
Urban
Urban
Industrial
Industrial
Urban
Dump Site
Urban
NR
NR
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
NR
86-89
84
84
NR
NR
NR
NR
NR
NR
NR
Ret
no.
20
20
20
20
20
20
20
5
20
4
4
8
8
10
10
10
12
12
Comment*
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
composite 5-10 fish
samples composite 3-5 fish
Elk River power station
Elk River power station
former sewage sludge
composite 3 samples
composite 3 samples
B-45
-------
Table B-8. Environmental Levels of Dioxms in Fish (ppt) (continued)
Chemical
PeCDDs (continued)
Ksh
specie*
Kb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Tn«ue
Whole
Fillets
Whole
Fillets
Whole
Fillets
Number
samples
1
1
1
1
1
1
Number
positive
samples
1
1
1
1
1
1
Concentration
range
31
15
39
9
6
5
Cow.
OMNUS
31
15
39
9
6
5
Wt,
bans
NR
NR
NR
NR
NR
NR
Location'
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Location
description
NR
NR
NR
NR
NR
NR
Samp.
year
NR
NR
NR
NR
NR
NR
Ref.
no.
12
12
12
12
12
12
Comment*
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
Hexachlorodibenzo-p-dM(MW«390.87)
1,2,3,4,7,8-HxCDD
Caip
Pike
Pike
Herring
Herring
Herring
Sucker
Lm Bass
Rock Bass
Rock Bass
Sm Bass
Redeye Bass
Whole
Muscle
Muscle
Whole
Whole
Whole
Whole
Fillet
Whole
Fillet
Fillet
Fillet
2
8
1
1
2
2
15
4
2
1
2
1
2
8
1
0
2
0
2
0
0
0
0
0
3-5
6.7-22
11
ND(0.2)
0.2-0.3
ND(0.2)
ND-0.24
ND(0.90-
2.47)
ND( 2.47-
2.87)
ND(1.25)
ND( 2.47)
ND( 2.47)
4
12.8
11
NA
0.25
NA
0.81
NA
NA
NA
NA
NA
NR
Fat
Fat
Fresh
Fresh
Fresh
Wet
Wet
Wet
Wet
Wet
Wet
Lake Huron
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Various, US
Various, US
Various, US
Various, US
Varioui, US
Various, US
NR
Industrial
Industrial
Pristine
Urban
Industrial
Background
Background
Background
Background
Background
Background
NR
88
88
NR
NR
NR
86-89
86-89
86-89
86-89
86-89
86-89
18
19
19
5
5
5
20
20
20
20
20
20
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 5-10 fish
composite 5-10 fish
composite 5-10 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-46
-------
Table B-8. Environmental terete of Dioxins in Fish (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDD
(continued)
F«h
species*
Cup
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longest
Sunfiah
Walleye
Chain Pickerel
Black Cnppie
SeaCatfiih
North
Hog tucker
Thaw
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Number
temple*
5
2
1
2
2
1
1
1
1
1
3
3
1
1
1
Number
positive
samples
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Concentration
range
ND- 0.70
NEK 1.50-
3.31)
NEK 1.96)
NEK 0.65-
0.72)
ND( 0.89-
1.04)
NEK 1.45)
NEK 1-10)
NEK 2.46)
NEK 2.56)
NEK 1-13)
NEK 0.60-
2.47)
NEK 0.22-
1.04)
NEK 0.22)
ND( 2.47)
NEK 2.47)
Cone.
mean
1.08
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
wt,
wUI8
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location1'
Varioua, US
Varioua, US
Varioua, US
Varioui, US
Varioua, US
Varioua, US
Varioua, US
Varioua, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R#f.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Cwament*
samplea composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samplea composite 3-5 fiih
samplea composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fiah
samples composite 3-5 fish
samplea composite 3-5 fish
samples composite 3-5 fiah
B-47
-------
Table B-8. Environmental Lev* of Woxms in Rsh (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDD
(continued)
1,2,3,6,7,8-HxCDD
Rib
species*
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefiah
White Catfish
Crayfish
Various'
Pike
Pike
Herring
Herring
Herring
Sucker
LmBaai
Rock Bam
Rock Bau
Tissue
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
Muscle
Muscle
Whole
Whole
Whole
Whole
Fillet
Whole
Fillet
Number
sample*
1
2
1
2
1
1
1
314
8
1
1
2
2
15
4
2
1
Number
positive
samples
0
0
0
0
0
0
0
100
8
1
0
1
2
4
0
0
0
Concentration
range
NEK 2.47)
NEK 2.46)
NEK 2.47)
NEK 2.47)
ND( 2.47)
ND( 2.47)
ND( 2.47)
NR
30-100
22
NEK0.2)
ND-2.4
2.2-8.1
ND-0.46
NEK 0.90-
2.40)
NEK 2.87-
3.71)
NEK 3. 49)
Cone.
mean
NA
NA
NA
NA
NA
NA
NA
1.67
50.5
22
NA
1.25
5.15
0.97
NA
NA
NA
Wt,
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fresh
Fresh
Fresh
Wet
Wet
Wet
Wet
Location'
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Oulf of Bothnia, Sweden
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Various
Industrial
Industrial
Pristine
Urban
Industrial
Background
Background
Background
Background
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
88
88
NR
NR
NR
86-89
86-89
86-89
86-89
Ret
no.
20
20
20
20
20
20
20
20
19
19
5
5
5
20
20
20
20
Comments
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 5-10 fish
composite 5-10 fish
composite 5-10 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-48
-------
Table B-*. Environmental Lereb of Dkmns in Fish (ppt) (continued)
: Cheaafc*!
1,2,3,6,7,8-HxCDD
(continued)
Ftfh
species*
Sm Ban
Redeye Ban
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Walleye
Chain Pickerel
Black Crappie
Tiwue
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Number
(•mplet
2
1
5
2
1
2
2
1
1
1
1
1
3
3
1
Number
positive
samples
0
0
3
0
0
0
0
0
0
0
1
0
0
0
0
Concentration
range
NEK 1-84-
1.85)
NEK 1.85)
ND-3.57
NEK 2.25-
5.00)
NEK 1.96)
NEK 0.65-
0.72)
NEK 1.74-
1.78)
NEK l-*5)
ND( 1-10)
NEK l-M)
1.36
NEK 1.13)
NEK 0.60-
1.85)
NEK 0.87-
1.04)
NEK 0.22)
Cone.
tnran
NA
NA
1.63
NA
NA
NA
NA
NA
NA
NA
1.36
NA
NA
NA
NA
wt
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location*
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Swop.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ref.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-49
-------
Table B-8. Environment^ Levcb of Diorins in Fhh (ppt) (continued)
Chemical
1,2,3,6,7,8-HxCDD
(continued)
1,2,3,7,8,9-HxCDD
Fisfc
species*
Sea Catfish
North
Hogsucker
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefish
White Catfiih
Crayfish
Various"
Pike
Pike
Herring
Herring
Herring
Sucker
Lm Bas§
Tissue
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
Muscle
Muscle
Whole
Whole
Whole
Whole
Fillet
Number
sample*
1
1
1
2
1
2
1
1
1
314
8
1
1
2
2
15
4
Number
positive
sample!
0
o
1
0
0
1
0
1
0
217
0
0
0
0
0
0
0
Concentration
range
ND( 1-85)
ND( 1 85)
0.67
NEK l->4)
NEK 1-85)
ND-0.40
NEK 1-84)
0.68
NEK 1.85)
MR
NEK3-11)
ND(6)
NEK0.2)
NEK0.2)
NEK0.2)
NEK 0.60-
3.37)
NEK 0.90-
2.40)
Cone.
mean
NA
NA
0.67
NA
NA
0.67
NA
0.68
NA
4.29
NA
NA
NA
NA
NA
NA
NA
VK,
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fresh
Fresh
Fresh
Wet
Wet
Location'
Various, US
Various US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Lake Vanem, Sweden
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Various
Industrial
Industrial
Pristine
Urban
Industrial
Background
Background
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
88
88
NR
NR
NR
86-89
86-89
Ref.
no.
20
20
20
20
20
20
20
20
20
20
19
19
5
5
5
20
20
CoottQtnt?
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 5-10 fish
composite 5-10 fish
composite 5-10 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-50
-------
Table B-8. EnriromnenUl Leveb of Dioxms in Rsh (ppt) (continued)
Chemical
1,2,3,7,8,9-HxCDD
(continued)
KA
speciei"
Rock Ban
Rock Ban
SmBau
Redeye Ban
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Walleye
Hwue
Whole
Fillet
Fillet
FiUet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Number
umpkt
2
1
2
1
5
2
1
2
2
1
1
1
1
1
3
Number
positive
umples
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Concentration
range
NEK 2.47-
2.87)
ND(1.25)
NEK 1.38)
NEK 1.38)
NEK 1.15-
2,69)
NEK 1.50-
2.48)
ND( 1.96)
NEK 0.65-
0.72)
NEK 0.89-
1.04)
NEK 1.45)
NEK 1.10)
ND(1.37)
ND(1.38)
ND( 1-13)
NEK 0.60-
1.38)
Cone.
BI6AB
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Wt,
baiis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Ixwwfew*
Varioui, US
Varioui, US
Varioui, US
Varioua, US
Varioua, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
tocatjon
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R«f.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
COtWQMflfo
umplei composite 3-5 fi«h
lamplei composite 3-5 fiih
•ample! composite 3-5 fiah
umplei composite 3-5 firfi
umplei compoaite 3-5 fish
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fish
umplei composite 3-5 fiah
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fiih
umplei compoiite 3-5 fiih
B-51
-------
Table B-8. Environmental Levels of Dioxmg in Fish (ppt) (continued)
ChemicaJ
1,2,3,7,8,9-HxCDD
(continued)
HxCDDs
Fi*
species*
Chain Pickerel
Black Crappie
Sea Catfish
North
Hogtucker
Summer
Flounder
Dolly Varden
Comporite
Bottom
Winter
Flounder
Bluefiah
White Catfish
Crayfish
Various'
Bream
Perch
Carp
Carp
Ttoue
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
Whole
Whole
Number
sample*
3
1
1
1
1
2
1
2
1
1
1
314
13
2
3
3
Number
positive
samplet
0
0
0
0
1
0
0
0
0
0
0
119
13
2
3
1
Concentration
range
ND( 0.22-
1.04)
ND( 0.22)
ND( 1.38)
ND(1.38)
0.34
ND( 1.37-
1.38)
NEK 1-38)
ND( l-3>)
NEK 1.38)
NEK 1-38)
NEK 1-38)
NR
4.3-46.4
18.6-21.5
2.3-11
ND-3.0
Cone.
mean
NA
NA
NA
NA
0.34
NA
NA
NA
NA
NA
NA
1.15
17.8
20.0
6.9
1.0
Wt.
fcaaic
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Freah
Fresh
NR
NR
Location'
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Hamburg, Germany
Hamburg, Germany
Mississippi River, MN
Lake Orono, MN
Location
deacription
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Various
Urban
Urban
Industrial
Industrial
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
84
84
NR
NR
Rtf,
DO.
20
20
20
20
20
20
20
20
20
20
20
20
4
4
8
8
Comments
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
Elk River power station
Elk River power station
B-52
-------
Table B-S. Environmental Levels of Diorins in Fish (ppt) (continued)
Chemical
HxCDDi
(continued)
Frth
specie**
Blue Crab
Lobster
Sir. Ban
Br. Trout
Br. Trout
Rb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Tiwue
Meat
Meat
Fillets
Whole
Fillets
Whole
Fillets
Whole
Fillets
Whole
Fillets
Number
sampiei
2
2
2
1
1
1
1
1
1
1
1
Nttnibef
positive
samples
2
2
2
1
1
1
1
1
1
1
1
Concentration
range
0.3-1.5
3.0-3.4
0.6-0.7
20
25
67
37
114
27
16
22
Cone.
mean
0.9
3.2
0.65
20
25
67
37
114
27
16
22
Wt
bails
Wet
Wet
Wet
NR
NR
NR
NR
NR
NR
NR
NR
Location*
Pasaaic River, NJ
New York Bight
Newark Bay, NJ
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Location
description
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
NR
NR
Samp.
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
10
10
10
12
12
12
12
12
12
12
12
Comment*
former sewage sludge
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
Hepuchlorodibenzo^-JioxiMOrfW- 425 ,3 1)
1,2,3,4,6,7,8-HpCDD
Carp
Herring
Herring
Herring
Sucker
Lm Bass
Rock Bass
Whole
Whole
Whole
Whole
Whole
Fillet
Whole
2
1
2
2
15
4
2
2
0
1
0
8
1
0
3-4
ND(0.2)
ND-0.6
ND(0.2)
ND-8.16
ND- 0.75
ND02.94-
19.27)
3.5
NA
0.35
NA
2.59
1.54
NA
NR
Fresh
Fresh
Fresh
Wet
Wet
Wet
Lake Huron
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Various, US
Various, US
Various, US
NR
Pristine
Urban
Industrial
Background
Background
Background
NR
NR
NR
NR
86-89
86-89
86-89
18
5
5
5
20
20
20
samples composite 3-5 fish
composite 5-10 fish
composite 5-10 fish
composite 5-10 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-53
-------
Tabte B-«. Environmental Lereb of DMrins in Fish (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDD
(continued)
Fish
species*
Rock Baal
SmBais
Redeye Ban
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Walleye
Chain Pickerel
Black Crappie
Tfeaue
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Number
samplei
1
2
1
5
1
1
2
2
1
1
1
1
1
2
3
1
Number
positive
sampfet
0
1
0
3
0
0
0
2
1
0
0
1
0
0
0
0
Concentration
range
ND(10.70)
ND-0.23
ND(1.26)
ND-7.14
ND(6.96)
ND(4.91)
ND( 1.31-
4.45)
1.67-2.21
1.80
ND<3.10)
ND( 4.43)
3.23
ND( 7.36)
ND(0.75-
0.86)
ND( 3.08-
5.09)
ND(2.29)
Cone.
mean
NA
0.11
NA
7.18
NA
NA
NA
1.94
1.80
NA
NA
3.23
NA
NA
NA
NA
Wt,
tail*
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Various, US
Varioui, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Simp.
ye*r
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R#f.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-54
-------
Table B-8. Environmental Levels of Dioxms in Fish (ppt) (continued)
Chcttie*!
1,2,3,4,6,7,8-HpCDD
(continued)
HpCDDi
Fish
species*
Sea Catfish
North
Hog sucker
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefiih
White Catfish
Crayfish
Various'
Bream
Perch
Carp
Carp
Blue Crab
Lobster
Str. Bau
Br. Trout
Itwue
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed*
Whole
Whole
Meat
Meat
Fillets
Whole
Number
sample*
1
1
1
2
1
2
1
1
1
314
13
2
3
3
2
2
2
1
Number
positive
samples
1
1
1
2
1
2
0
1
1
279
13
2
3
2
0
1
2
1
Concentration
range
0.51
0.74
3.06
0.77- 0.79
2.18
0.61- 0.80
NEK 4. 10)
0.89
0.49
NR
1.5-14.4
3.5-7.1
15-22
ND-11
ND(1.1)
ND-8.5
4.0-11.4
7
Cone.
mean
0.51
0.74
3.06
0.78
2.18
0.71
NA
0.89
0.49
10.5
6.7
5.3
19.3
7.0
NA
4.25
7.7
7
Wt,
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fresh
Fresh
NR
NR
Wet
Wet
Wet
NR
Location*
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Hamburg, Germany
Hamburg, Germany
Mississippi River, MN
Lake Orono, MN
Passaic River, NJ
New York Bight
Newark Bay, NI
Lake Ontario
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Various
Urban
Urban
Industrial
Industrial
Urban
Dump Site
Urban
NR
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
84
84
NR
NR
NR
NR
NR
NR
Ref.
00.
20
20
20
20
20
20
20
20
20
20
4
4
8
8
10
10
10
12
Comments
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
Elk River power station
Elk River power station
former sewage sludge
composite 3 samples
B-55
-------
Table B-8. Environmental Lev* of Dioxma in Fish (ppt) (continued)
Chemical
HpCDDs (continued)
1,2,3,4,6,7,8,9-OCDD
Fish
speciei1
Br. Trout
Rb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Tiasue
FilleU
Whole
FilleU
Whole
Filled
Whole
Filleti
Eel
Trout
Grayling
Barbel
Carp
Chub
Eel
Bream
Perch
Herring
Herring
Herring
Fillet
Fillet
FiUet
Fillet
FiUet
Fillet
Fillet
Whole
Whole
Whole
Number
samples
1
1
1
1
1
1
1
5
1
1
1
1
1
5
14
3
1
2
2
Number
positive
tamplei
1
1
0
1
0
1
1
Concentration
range
9
12
ND(7)
16
ND(7)
30
50
Cone.
mean
9
12
NA
16
NA
30
50
wt,
basis
MR
NR
NR
NR
NR
NR
NR
Location*
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Location
description
NR
NR
NR
NR
NR
NR
NR
Octachlorodibenzo-p-dioxin(MW«460.76)
5
0
1
1
1
1
5
14
3
1
1
1
28-60
ND(5.0)
47
9.0
23
15
25-40
1.4-5.1
2.3-10.5
1.1
ND-0.7
ND-0.3
44.4
NA
47
9
23
15
30
2.5
5.2
1.1
0.4
0.2
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Freah
Fresh
Fresh
Fresh
Freah
Rhine River, Germany
Nectar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Hamburg, Germany
Hamburg, Germany
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
NR
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Pristine
Urban
Industrial
Samp.
year
NR
NR
NR
NR
NR
NR
NR
tut
no.
12
12
12
12
12
12
12
Continent*
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
88
88
88
88
88
88
87-88
84
84
NR
NR
NR
2
2
2
2
2
2
2
4
4
5
5
5
up & downstream Basal
composite sample
composite sample
composite 5-10 fish
composite 5-10 fish
composite 5-10 fish
B-56
-------
Table B-8. Environmental Levels of Dioxins in Fish (ppt) (continued)
Chemical
1,2,3,4,6,7,8,9-OCDD
(continued)
K«h
species"
Salmon
Salmon
Perch
Pike
Pike
Cup
Carp
Carp
Blue Crab
Lobster
Sir. Ban
Lake Trout
Lake Trout
Lake Trout
Walleye
Walleye
Lake Trout
Lake Trout
Br. Trout
Br. Trout
Tittue
Muicle
Muacle
MR
Muscle
Muscle
Whole
Whole
Whole
Meat
Meat
Fillets
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Fillets
Number
samples
2
2
3
8
1
3
3
2
2
2
2
1
1
3
1
1
1
10
1
1
Number
positive
samples
1
2
3
8
1
3
3
2
2
2
2
1
1
3
1
1
1
10
0
1
Concentration
range
ND-1.5
0.8-1.9
0.6-0.8
10-17
22
56-62
35-43
3-5
34.3-78.8
6.3-10.9
5.1-49.5
1.0
0.7
1.1-2.5
2.8
1.8
1.2
0.8-3.7
NDfT)
11
Cone.
mean
0.75
1.35
0.73
14.75
22
59
39
4
56.6
8.6
27.3
1.0
0.7
1.8
2.8
1.8
1.2
1.6
NA
11
Wt.
basis
Fresh
Fresh
Fresh
Fat
Fat
NR
MR
NR
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
NR
NR
Location'
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Mississippi River, MN
Lake Orono, MN
Lake Huron
Passaic River, NI
New York Bight
Newark Bay, NJ
Lake Superior
Lake Huron
Lake Michigan
Lake Erie
Lake St. Clair
Lake Ontario
Lake Michigan
Lake Ontario
Lake Ontario
Location
description
NR
NR
NR
Industrial
Industrial
Industrial
Industrial
NR
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
NR
NR
NR
Samp.
year
NR
NR
NR
88
88
NR
NR
NR
NR
NR
NR
84
84
84
84
84
84
84
NR
NR
Rtf,
no.
5
5
5
19
19
8
8
18
10
10
10
11
11
11
11
11
11
11
12
12
Comments
wild salmon
hatched salmon
caught near pulp mill
simples composite 2-5 fish
composite 5 fish
Elk River power station
Elk River power station
samples composite 3-5 fish
former sewage sludge
mean 5 samples
mean 5 samples
range 3 sample sites
mean 5 samples
mean 5 samples
mean 5 samples
composite 3 samples
composite 3 samples
B-57
-------
Table W. EnTiitmmenUl Levels of Diorins in Fish (ppt) (continued)
Chemical
1,2,3,4,6,7,8-OCDD
(continued)
Fish
specie**
Rb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Cod
Haddock
P. Flounder
Plaice
Flounder
Eel
Mussel
Shrimp
Cod
Tissue
Whole
FilleU
Whole
Filleti
Whole
FilleU
Fillets
FilleU
FilleU
Fdleti
FilleU
Fillet*
Muscle
Muscle
FilleU
Nuttlbef
samples
1
1
1
1
1
1
4
1
1
1
1
4
3
2
6
Number
positive
simples
0
0
1
1
1
1
3
0
1
1
1
3
3
1
MR
Concentration
range
ND(7)
ND(7)
89
28
160
280
ND-11
ND(3.6)
3.4
424
2.4
ND-770
12-140
ND-18
0.63-2.2
Co«.
NA
NA
89
28
160
280
4.95
NA
3.4
424
2.4
204
62.0
9.0
NR
Wt.
buil
NR
NR
NR
NR
NR
NR
Freih
Fresh
Fresh
Freah
Fresh
Fresh
Fresh
Fresh
Fresh
Location'
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Qrenlandsfjord.Sweden
Qrenlandsfjord.Sweden
Frierfjord, Sweden
Location
description
NR
NR
NR
NR
NR
NR
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Sttap.
year
NR
NR
NR
NR
NR
NR
88
88
88
88
88
87-88
87
88
87
Ref,
no.
12
12
12
12
12
12
17
17
17
17
17
17
17
17
17
Continents
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 10 samples
composite 10 samples
composite 10 samples
composite 10 samples
only cone, range given
B-58
-------
Table B-8. EBTirwmtcntal Lenfc of Dioxms in Fish (ppt) (continued)
Footnote Refereaces
• Ch. - Channel; Y. - Yellow; Sm. M. - Small Mouth; Sir. - Striped; Br. - Brown; Kb. - Rainbow; P. - Pole.
» Varioui, NetherUndi - samples taken from six location* around Ijsselmeer Lake; Varioua, Michigan - wnplea taken from Tittabawasaee River, Grand River, Saginaw River, Saginaw Bay, and Lake Michigan; Varioui, Sweden
• nmplei taken from Grenlandifjord and Frierfjord; Varioua US -> lamplea taken from 314 aitea acroaa the US, including industrial and background ahea.
' Speciea were taken from both bottom feeders and open water feeder*, and then compoaited.
' Whole fiah aamplea and fillet tamplei were combined during analyrii.
NOTES: Summary atatiatka provided in or derived from referencea; when reference did not compute mean, it waa computed using one-half the detection limit for non-detecta;
NA - not applicable;
ND = non-detected (limit of detection);
NR - not reported;
Descriptions provided were thoae given by reference or surmised from study deacription when not given;
One half me detection Umit waa uaed in calculating mean*. Therefore, it ia pouible to have mean concentratk»a greater than the range (e.g., reported detection limit for nondetectt greater than the positive sample).
Sources: 1. Van den Berg, et al. (1987) 11. Vault, et al. (1989)
2. Frommberger(1991) 12. Niimi and Oliver (1989a)
4. Ootz, et al. (1990) 17. Oehme, et al. (1989)
5. Rappe, et al. (1989) 18. Stalling, et al. (1983)
7. Harfeaa and Lewis (1982) 19. Kjeller, et al. (1990)
8. Reed, et al. (1990) 20. USEPA(1992)
10. Rappe, et al. (1991)
B-59
-------
Table B-9. EnTironmeatal Levels of Dibenzofurans in Fish (ppt)
Chemical
Fish
specie**
Time
Number
sample*
Number
positive
simple*
Coooentntkra
range
Cone.
mean
Wt.
bttit
Location*
Location
description
Samp.
year
Ref.
00,
Comments
Tetrachk>rodibenzoft>rani(MW=305.98)
2,3,7,8-TCDF
Eel
Eel
Br. Trout
Grayling
Barbel
Cnp
Chub
Eel
Herring
Herring
Herring
Herring
Salmon
Salmon
Perch
Artie Char
Pike
Pike
Carp
Carp
Liver
Fillet*
Filteu
Fillets
Filleti
Fillets
Fillets
Fillets
Adipose
Whole
Whole
Whole
Muscle
Muscle
NR
NR
Muscle
Muscle
Whole
Whole
6
5
1
1
1
1
1
5
2
1
2
2
2
2
3
5
8
1
2
3
0
5
1
1
1
1
1
5
2
1
2
2
2
2
3
5
8
1
2
3
ND
2.1-12
45
108
57
58
128
0.9-2.0
3^»
1.7
5.3-5.5
3.0-6.2
28-35
7.8-9.0
2.1-8.7
21-75
330-3000
430
11
1.8-3.0
NA
6.98
45
108
57
58
128
1.35
3.5
1.7
5.4
4.6
31.5
8.4
5.4
55
774
430
NA
2.6
NR
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fat
Fat
NR
NR
Various, Netherlands
Rhine River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
South Baltic Sea
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Lake Vattern, Sweden
Lake Vanem, Sweden
Hedesunda Bay, Sweden
Lake Huron
Mississippi River, MN
NR
NR
Urban
Urban
Urban
Urban
Urban
Urban
NR
Pristine
Urban
Industrial
NR
NR
NR
NR
Industrial
Industrial
NR
Industrial
NR
88
88
88
88
88
88
87-88
NR
NR
NR
NR
NR
NR
NR
NR
88
88
NR
NR
1
2
2
2
2
2
2
2
3
5
5
5
5
5
5
5
19
19
18
8
one sample near dump site
up A downstream Basal
composite sample
composite sample
composite 2-5 fish
composite 2-5 fish
composite 2-5 fish
wild salmon
hatched salmon
caught near pulp mill
samples composite 2-5 fish
composite 5 fish
samples composite 3-5 fish
Elk river power station
B-60
-------
Table B-9. Emiroamcntal L*r«b of DibeuofyrMH • fish (fft) (conthmed)
Chemie*!
2,3,7,8-TCDF
(continued)
lulu
specie*
Carp
Carp
Catfith
Smk. Chub
Str. Ban
Lg. M. Bau
Lake Trout
Blue Crab
Lobtter
Str. Bau
Lake Trout
Lake Trout
Lake Trout
Walleye
Walleye
Lake Trout
Lake Trout
Br. Trout
Br. Trout
Rb. Trout
Rb. Trout
Tt*a»
Whole
FilleU
Filleta
FiUeti
Fdleta
FiUeta
Fillet*
Meat
Meat
Fdleti
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Fillets
Whole
FiUeu
Number
Mtmpioc
3
1
1
1
5
1
3
2
2
2
1
1
3
1
1
1
10
1
1
1
1
Number
potitiv*
samples
3
1
1
1
5
1
3
2
2
2
1
1
3
1
1
1
10
1
1
1
1
Cooeenttttion
fUlgO
1.0-1.3
49
6
3
7-93
10
11-56
11.0-15.5
3.5-4.1
51.9-85.5
14.8
22.8
34.8-42.3
11.3
24.8
18.5
27.0-56.0
11
8
19
6
Cone.
mean
1.1
49
6
3
28.0
10
31.7
13.2
3.8
68.7
14.8
22.8
39.5
11.3
24.8
18.5
38.4
11
8
19
6
Wt,
bMur
NR
NR
NR
NR
NR
NR
NR
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
NR
NR
NR
NR
LOWtfotf
LakeOrono, MN
NR
Saginaw River
NR
Hudson River
Hudaon River
Lake Superior
Faaaaic River, NJ
New York Bight
Newark Bay, NJ
Lake Superior
Lake Huron
Lake Michigan
Lake Erie
Lake St. Clair
Lake Ontario
Lake Michigan
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
: Location
description
IndMtfrifl
NR
NR
NR
NR
NR
NR
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
SftfBfP*
year
NR
78
84
85
85
85
85
NR
NR
NR
84
84
84
84
84
84
84
NR
NR
NR
NR
Rrf,
no.
8
9
9
9
9
9
9
10
10
10
11
11
11
11
11
11
11
12
12
12
12
Cottttttftfftft
Elk river power station
contamimated site
contaminated site
contaminated site
contaminated site
contaminated site
contaminted site
former sewage sludge
mean 5 samples
mean 5 samples
range 3 sample sites
mean 5 samples
mean 5 samples
mean 5 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
B-61
-------
Table B-9. Environmental terete of Dibenxofarami • fish (ppt) (continued)
Chemical
2,3,7,8-TCDF
(continued)
Fi«h
species*
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Cod
Haddock
P. Flounder
Plaice
Flounder
Eel
Musael
Shrimp
Cod
Variou^
Sucker
LmBau
Rock Ban
Rock Ban
Sm Bass
Redeye Bass
TlWue
Whole
Fillets
•Whole
Fillets
FilleU
Fillets
Fillets
Fillets
FilleU
Fillets
Muscle
Muscle
Fillets
Mixed1
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Number
•ample*
1
1
1
1
4
1
1
1
1
4
3
2
6
314
15
4
2
1
2
1
Number
positive
sample*
1
1
1
1
4
1
1
1
1
3
3
2
NR
279
12
0
1
0
2
0
Concentration
HfigC
15
6
20
6
0.2-1.4
0.75
0.28
1.4
1.2
ND-68
16.1-61
6.1-37
0.49-14.3
NR
ND- 6.21
ND( 0.23-
0.59)
ND-0.86
ND(1.95)
0.19-0.30
ND( 0.49)
Cone,
. mean
15
6
20
, 6
0.62
0.75
0.28
1.4
1.2
17.1
32.4
21.6
NR
13.6
1.96
NA
1.24
NA
0.25
NA
wt
bum
NR
NR
NR
NR
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Various, Sweden
Grenlandsfiord,Sweden
GrenUndsfiprd,Sweden
Frierfiord, Sweden
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
NR
NR
NR
NR
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
Industrial
i Various
Background
Background
Background
Background
Background
Background
8*09.
y«ar
NR
NR
NR
NR
88
88
88
88
88
88
87
88
87
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R*f,
no.
12
12
12
12
17
17
17
17
17
17
17
17
17
20
20
20
20
20
20
20
Codw>eflfs
composite 3 samples
composites umples
composite 3 samples
composite 3 samples
composite 10 samples
composite 10 samples
composite 10 samples
composite 10 samples
only cone, range given
•ample* composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-62
-------
Table B-9. Eimramentai Letch of D&euofsran m Fish (ppt) (continued)
Chemtail
2,3,7,8-TCDF
(continued)
RA
specie**
Cup
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redbone
Longear
Sunfiih
Walleye
Chain Pickerel
Black Crappie
Sea Catfish
North
Hog sucker
Summer
Flounder
*~
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Numbet
tttmpiM
5
2
1
2
2
1
1
1
1
1
3
3
1
1
1
1
Number
positive
Munpfec
4
1
0
0
2
0
0
1
1
0
1
0
0
0
0
0
CotKwwn&Qtt
XVfljgB :
ND- 1.36
ND-0.29
ND(0.20)
ND(0.20)
0.75- 0.90
ND( 0.48)
NEK 0.42)
2.30
1.77
ND( 0.41)
ND-0.86
ND(0.20-
0.24)
NEK 0.20)
ND( 0.49)
NEK 0.84)
ND( 0.71)
Cool.
mean
0.96
0.37
NA
NA
0.83
NA
NA
2.30
1.77
NA
0.41
NA
NA
NA
NA
NA
-•"*!::'
•:b«aj*s:::
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
'f. ! Location' "
Various, US
Various, US
Various, US
Varioui, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
' Location
deacriptkm
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
9mop'
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ret
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
CoubttMw
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-63
-------
TaWe B-9. Environmental Lev* of DibauofurttH ii Rsfc (pp«) (cootinoed)
Chemical
2,3,7,8-TCDF
(continued)
TCDFs
Ft*
specie*
Dolly Varden
Compolite
Bottom
Winter
Flounder
Bluefiih
White Catfish
Crayfish
Bream
Perch
Y. Perch
Carp
Carp
Blue Crab
Lobster
Sit. Bats
Br. Trout
Br. Trout
Rb. Trout
Rb. Trout
Lake Trout
Tiwue
Whole
Whole
Whole
Whole
Whole
Whole
NR
NR
Whole
Whole
Whole
Meat
Meat
Fillets
Whole
Fillets
Whole
Fillets
Whole
Number
•unptM ,
2
1
2
1
1
1
13
2
1
3
3
2
2
2
1
1
1
1
1
Number
positive
sample*
2
1
2
1
1
0
13
2
1
3
3
2
2
2
1
1
1
1
1
CoowmraJioa
XlfigC
0.37
0.86
13.30-13.73
1.93
1.14
ND(0.57)
7.8-86.5
10.7-41.1
1060
2.4-4.0
1.0-1.3
133-164
23.0-31.2
77.2-108
11
8
19
6
18
Coot.
mean
0.37
0.86
13.52
1.93
1.14
NA
44.3
25.9
1060
3.1
1.2
149
27.1
92.4
11
8
19
6
18
Wfc
basis
Wet
Wet
Wet
Wet
Wet
Wet
Fresh
Fresh
NR
NR
NR
Wet
Wet
Wet
NR
NR
NR
NR
NR
Location'
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Hamburg, Germany
Hamburg, Germany
Housatonic River, MA
Mississippi River, MN
Lake Orono, MN
Passaic River, NJ
New York Bight
Newark Bay, NJ
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Location
description
Background
Background
Background
Background
Background
Background
Urban
Urban
NR
Industrial
Industrial
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
Sllfflp'
year
86-89
86-89
86-89
86-89
86-89
86-89
84
84
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ret
no.
20
20
20
20
20
20
4
4
6
8
8
10
10
10
12
12
12
12
12
CpflWliftfttl
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
Elk river power station
Elk river power station
former sewage sludge
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
B-64
-------
TaWe B-9. Environmental Uweb of Dibeuofurans in Fish (opt) (continued)
f*tV.* stAJVi *t
vncwidi*
TCDFs
(continued)
TCDF»
other than
2,3,7,8-TCDF
R«h
species*
Lake Trout
Coho Salmon
Coho Salmon
Eel
Grayling
Barbel
Carp
Chub
Eel
Tiwu*
Filleu
Whole
FilleU
FilleU
Fillets
FilleU
FilleU
FilleU
FilleU
Number
sample*
1
1
1
5
1
1
1
1
1
Number
positive
samples
1
1
1
5
1
1
1
1
1
Concentration
range
6
20
6
4.6-13
142
77
14
17
1.5
Cone.
mean
6
20
6
8.8
142
77
14
17
1.5
Wt,
basis
NR
NR
NR
Fat
Fat
Fat
Fat
Fat
Fat
Location"
Lake Ontario
Lake Ontario
Lake Ontario
Rhine River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Location
description
NR
NR
NR
NR
Urban
Urban
Urban
Urban
Urban
Samp.
year
NR
NR
NR
88
88
88
88
88
88
Ref.
no.
12
12
12
2
2
2
2
2
2
Comment*
composite 3 samples
composite 3 samples
composite 3 samples
up A downstream Basal
sample composite 5 chubs
sample composite 2 eels
rVntachlorodibeazoftiraM(MW-340.42)
1,2,3,7,8-PeCDF
Carp
Pike
Pike
Herring
Herring
Herring
Various'
Sucker
Lm Ban
Whole
Muacle
Muscle
Whole
Whole
Whole
Mixed1
Whole
Fillet
2
8
1
1
2
2
314
15
4
2
8
1
1
2
2
151
1
0
1-5
43-140
39
0.4
1.4-2.5
0.8-0.9
NR
ND- 0.62
ND( 0.33-
0.78)
3
73.2
39
0.4
1.95
0.85
1.71
0.33
NA
NR
Fat
Fat
Fresh
Fresh
Fresh
Wet
Wet
Wet
Lake Huron
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Various, US
Various, US
Various, US
NR
Industrial
Industrial
Pristine
Urban
Industrial
Various
Background
Background
NR
88
88
NR
NR
NR
86-89
86-89
86-89
18
19
19
5
5
5
20
20
20
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 2-5 fish
composite 2-5 fish
composite 2-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-65
-------
Table B-9. Environmental Levels of Dibemoraraiis in Fish (ppt) (continued)
Chemical
1,2,3,7,8-PeCDF
(continued)
KUk
A'Mt
•perie**
Rock Bail
Rock Ban
Sm Ban
Redeye Bass
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Walleye
Tiwu*
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Fillet
Number
samples
2
1
2
1
5
2
1
2
2
1
1
1
1
1
3
Number
poaittv*
ttunplei
0
0
1
0
0
1
0
0
1
0
0
0
0
0
0
Coneentflitioa
IVflgB ••
ND( 0.76-
0.82)
ND( 0.59)
ND- 0.33
ND( 0.78)
ND( 0.56-
0.80)
ND-0.92
ND( 0.36)
ND(0.20-
0.35)
ND- 0.47
ND( 0.90)
ND( 0.25)
ND(0.77)
ND( 0.78)
ND( 0.52)
ND(0.20-
0.78)
Cone,
mean
NA
NA
0.16
NA
NA
0.69
NA
NA
0.51
NA
NA
NA
NA
NA
NA
Wt
0M19 •
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Varioui, US
Various, US
Varioui, US
Varioui, US
Various, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Various, US
Varioui, US
Varioui, US
Varioui, US
fcX)Cw0ll
deicriptkra
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Stop.
yew
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ref,
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
umplei composite 3-5 fish
samples composite 3-5 fish
sample* composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-66
-------
Table B-9. EnTironmcnUl Lords of Dibauofarans in Fish (ppt) (continued)
Chemicaj
1,2,3,7,8-PeCDF
(continued
2,3,4,7,8-PeCDF
.. Run
species?
Chain Pickerel
Black Cnppie
Sea Catfish
North
Hogiucker
Summer
Flounder
Dolly Varden
Compotite
Bottom
Winter
Flounder
Bhiefiah
White Catfiah
Crayfish
Various
Carp
Pike
Pike
Herring
Herring
Herring
t1»*»
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
Whole
Muicle
Muacle
Whole
Whole
Whole
Number
samples
3
1
1
1
1
2
1
2
1
1
1
34
2
8
1
1
2
2
Number
pottttv*
•ample*
0
0
0
0
0
0
0
2
1
1
0
34
2
8
1
1
2
2
Coaewjtrttioa
range
ND(O.I9-
0.28)
ND(0.20)
ND( 0.78)
ND( 0.78)
ND(0.77)
ND(0.77)
ND(0.78)
1.74- 1.90
1.06
0.73
ND( 0.78)
0.1-1.90
4-11
120-290
110
3.0
6.8-19.0
8.8-8.9
Cone.
mean
NA
NA
NA
NA
NA
NA
NA
1.82
1.06
0.73
NA
0.43
7.5
189
NA
NA
12.9
8.85
wt,
baric
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
NR
Fat
Fat
Freah
Freah
Freah
Location'
Various, US
Various, US
Various, US
Various, US
Varioui, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Lake Huron
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background'
NR
Industrial
Industrial
Pristine
Urban
Industrial
Ssjnpr
yea*
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
NR
88
88
NR
NR
NR
R«f,
no.
20
20
20
20
20
20
20
20
20
20
20
20
18
19
19
5
5
5
Comments
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 2-5 fish
composite 2-5 fish
composite 2-5 fish
B-67
-------
Table B-9. Environmental L«reb of Dibcnzofurans in Fbh (ppt) (continued)
cttemieai
2,3,4,7,8-PeCDF
(continued)
R«h
species*
Sucker
LmB«u
Rock Ban
Rock Bui
SmBaii
Redeye Bail
Caip
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Tiraue
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Numbw
sample*
15
4
2
1
2
1
5
2
1
2
2
1
1
1
1
1
Number
positive
sample!
6
0
0
0
0
0
2
1
0
0
2
0
0
0
0
0
Concentration
mi£8
ND- 1.36
ND( 0.33-
O.S5)
ND( 0.76-
0.82)
ND( 0.59)
ND( 0.85)
ND( 0.85)
ND- 0.34
ND- 1.33
ND( 0.36)
ND( 0.20-
0.35)
0.70
ND( 0.90)
ND( 0.25)
ND( 0.95)
ND( 0.92)
ND( 0.52)
Cone,
mean
0.46
NA
NA
NA
NA
NA
0.35
0.82
NA
NA
0.70
NA
NA
NA
NA
NA
Wt,
vMUft
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp*
yew
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R*f.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
CbtiUtteotA
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-68
-------
Table B-9. Environmental Letch of D&enmfarsns • Ft* (ppt) (continued)
Chemie*!
2,3,4,7,8-PeCDF
(continued)
PeCDFs
Fl*
species*
Walleye
Chain Pickerel
Black Crappie
SeaCatfiih
North
Hogsucker
Summer
Flounder
Dolly Vaiden
Composite
Bottom
Winter
Flounder
Bluefiih
White Catfish
Crayfish
Various*
Bream
Perch
Y. Perch
Carp
• Tissue
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
NR
NR
Whole
Whole
Numbe*
samples
3
3
1
1
1
1
2
1
2
1
1
1
314
13
2
1
3
Number
potjttve
samples
0
0
0
0
0
0
0
0
2
1
1
0
201
13
2
1
3
Coocentrttioa
TMflfiC
NEK 0.20-
0.85)
NEK 0.19-
0.28)
ND(0.20)
NEK 0.85)
ND( 0.85)
NEK 0.85)
NEK 0.85)
ND( 0.85)
0.64- 0.70
0.93
1.39
ND(0.85)
NR
13.9-114
62.3-153
640
15-45
Cone.
mean
NA
NA
NA
NA
NA
NA
NA
NA
0.67
0.93
1.39
NA
3.06
65.4
108
640
26.3
Wt
baiis
Wet
W«t
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Freah
Fresh
NR
NR
twstttott*
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Hamburg, Germany
Hamburg, Germany
Housatonic River, MA
Mississippi River, MN
toetfioa
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Various
Urban
Urban
NR
Industrial
Sump.
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
84
84
NR
NR
*et.
20
20
20
20
20
20
20
20
20
20
20
20
20
4
4
6
8
Cotntteotn
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-69
-------
TabfeB-9. Environmental Lords of
• Rah (nit) (continued)
Chemical
PeCDFi
(continued)
PeCDFi
other thin
1,2,3,7,8-PeCDF
and
2,3,4,7,8-PeCDF
F!»h
specie?
Carp
Blue Crab
Lobster
Str. Bau
Br. Trout
Br. Trout
Kb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Grayling
Barbel
Carp
- Time
Whole
Meat
Meat
Filleu
Whole
FilleU
Whole
FilleU
Whole
Fillet*
Whole
Filleu
Filleu
Filleu
Fillets
Number
sample*
3
2
2
2
1
1
1
1
1
1
1
1
1
1
1
Number
positive
•ample*
2
2
2
2
0
1
1
1
1
1
1
0
1
1
1
imgjB
ND-13
89.7-94.1
29.8-37.3
34.3-82.6
ND(7)
3
8
7
39
8
13
ND(7)
22
21
17
Cone.
me«n
9.0
91.9
33.6
S8.4
NA
3
8
7
39
8
13
NA
22
21
17
Wt
bub
NR
Wet
Wet
Wet
NR
NR
NR
NR
NR
NR
NR
NR
Fat
Fat
Fat
Location'
UkeOrono.MN
Pauaic River, NI
New York Bight
Newark Bay, NI
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Neckar River, Germany
Neckar River, Germany
Neckar River, Germany
Location
description
Industrial
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
NR
NR
Urban
Urban
Urban
»**!.+.
0afnp.
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
88
88
88
Ret
no.
8
10
10
10
12
12
12
12
12
12
12
12
2
2
2
Commetfa
Elk river power station
former sewage sludge
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
HexacMorodibedZoftirana(MW»374.87)
1,2,3,4,7,8-HxCDF
Carp
Pike
Pike
Herring
Whole
Muscle
Muscle
Whole
2
8
1
1
2
8
1
1
2-5
10-33
11
0.2
3.5
14.4
11
0.2
NR
Fat
Fat
Freah
Lake Huron
Lake Vanern, Sweden
Hedetunda Bay, Sweden
Atlantic Coast, Sweden
NR
Industrial
Industrial
Pristine
NR
88
88
NR
18
19
19
5
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 2-5 fish
B-70
-------
Table B-9. Environmental Levels of Dibenxofenan • RA (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDF
(continued)
Rih
species*
Herring
Herring
Sucker
Lm Ban
Rock Bass
Rock Ban
Sm Bass
Redeye Bau
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Gray
Redhone
Black
Redhone
Ti«ue
Whole
Whole
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Whole
Whole
Number
•ample*
2
2
15
4
2
1
2
1
5
2
1
2
2
1
1
1
Number
positive
•ample*
2
2
0
0
0
0
0
0
1
1
0
0
0
0
0
0
CoocefltrKioo
fau£B
0.4-0.7
0.3
ND( 0.33-
2.84)
NEK 0.41-
2.84)
NEK 1.13-
1.30)
NEK 0.72)
NEK 2.83-
2.84)
NEK 2.84)
ND-0.40
ND-1.24
NEK 0.96)
NEK 0.23-
0.42)
NEK 0.45-
0.58)
ND( 1.46)
NEK 0.52)
NEK 2.82)
Cone,
mean
0.55
NA
NA
NA
NA
NA
NA
NA
0.98
0.81
NA
NA
NA
NA
NA
NA
W*.
baait
Fresh
Freah
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location*
Baltic Sea, Sweden
Oulf of Bothnia, Sweden
Varioui, US
Various, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Location
description
Urban
Industrial
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
MR
NR
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
tut
DO.
5
5
20
20
20
20
20
20
20
20
20
20
20
20
20
20
COfflffKtfl^l
composite 2-5 fish
composite 2-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-71
-------
Table B-9. EnTinmmcntal Le*«b of DibeaMfanas • FSA fart) (continued)
Chemical
1,2,3,4,7,8-HxCDF
(continued)
1,2,3,6,7,8-HxCDF
Fish
species*
Golden
Redhone
Longear
Sunfiih
Walleye
Chain Pickerel
Black Crappie
SeaCatfiih
North
Hogsucker
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefish
White Catfish
Crayfish
Various'
Pike
Tissue
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed1
Muscle
Number
(ample*
1
1
3
3
1
1
1
1
2
1
2
1
1
1
314
8
Number
po»1tSv«
sample*
1
0
0
0
0
0
0
0
0
0
0
0
0
0
132
8
Codceatratioit
range
1.18
ND( 0.78)
ND( 0.21-
2.84)
ND(0.20-
0.42)
ND{ 0.20)
ND( 2.84)
ND( 2.84)
ND( 2.83)
ND( 2.83)
ND(2.84)
ND( 2.83-
2.84)
ND( 2.83)
ND{ 2.84)
NEK 2.84)
NR
5.6-22
Cone.
mean
1.18
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
2.35
11.9
wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Locattonk
Various, US
Virious, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Lake Vanern, Sweden
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Various
Industrial
Samp.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
88
R«f.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
19
COtttfflefrfl
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 2-5 fish
B-72
-------
TabteB-9. Environmental Lew eb of Dibeuofurans in Ffah (ppt) (continued)
Ctumfe*t
1,2,3,6,7,8-HxCDF
(continued)
Fish
•pecies*
Pike
Herring
Herring
Herring
Sucker
Lm Ban
Rock Bail
Rock Ban
Sm Ban
Redeye Ban
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
Ti«*l«
Muicle
Whole
Whole
Whole
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Number
samples
1
1
2
2
15
4
2
1
2
1
5
2
1
2
2
1
Number
poiittv*
sample*
1
1
2
2
0
0
0
0
0
0
0
1
0
0
0
0
Concentration
range
5.6
0.1
0.4-0.8
0.2
ND( 0.26-
2.85)
ND( 0.41-
2.85)
ND( 1.13-
1.30)
NEK 0.72)
NEK 2.84-
2.85)
NEK 2.85)
NEK 0.52-
2.85)
ND- 1.35
ND( 0-96)
NEK 0.23-
0.42)
ND( 0.45-
0.58)
ND( 1-46)
Cone,
mean
5.6
0.1
0.6
NA
NA
NA
NA
NA
NA
NA
NA
0.87
NA
NA
NA
NA
Wt,
bsiis
Fat
Freih
Fresh
Freih
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Hedesunda Bay, Sweden
Atlantic Coast, Sweden
Baltic Sea, Sweden
Oulf of Bothnia, Sweden
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Locution
description
Industrial
Pristine
Urban
Industrial
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
88
NR
NR
NR
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
fcef.
no.
19
5
5
5
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
compoiite5 fiih
composite 2-5 fish
compoiite 2-5 fish
composite 2-5 fish
samplei compoiite 3-5 fish
ssmplei compoiite 3-5 fish
samplei compoiite 3-5 fiih
samplei composite 3-5 fish
samplei compoiite 3-5 fish
samplei composite 3-5 fish
samplei compoiite 3-5 fish
samplei composite 3-5 fish
samplei compoiite 3-5 fish
samplei compoiite 3-5 fish
samplei compoiite 3-5 fiih
simplei compoiite 3-5 fiih
B-73
-------
Table B-9. Environmental Levch of Dibenxofurans in Fbh (opt) (contmned)
Ch*mie«l
1,2,3,6,7,8-HxCDF
(continued)
RA -
•• jpeeie?"
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiah
Walleye
Chain Pickerel
Black Cnppie
SeaCatfiah
North
Hogsucker
Summer
Flounder
Dolly Vanfen
Composite
Bottom
Winter
Flounder
Bhiefiah
White Catfiah
Tiswe
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Nwnbw
•araptM •
1
1
1
1
3
3
1
1
1
1
2
1
2
1
1
Number
powttv^
uunpler
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Concentration
migo :
ND( 0.52)
ND( 2.83)
ND( 2.85)
ND(0.52)
NEK 0.21-
2.85)
NEK 0.20-
0.42)
ND( 0.20)
NEK 2.S5)
NEK 2.85)
NEK 2.84)
ND( 2.84)
NEK 2.85)
ND( 2.85)
NEK 2.84)
ND( 2.85)
Cone,
mean
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Wt.
twit
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Various, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Locution
uMCitptiQn
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
5atb£«
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
*ef,
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comment*
lamplei composite 3-5 filh
umplei composite 3-5 filh
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
umplei composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-74
-------
TabkB-9. Environmental Ler* rf Diben«oftir«ns in Fish (ppt) (continued)
chtfffljftflf
1,2,3,7,8,9-HxCDF
(continued)
R*
specie**
Cnyfiih
Various"
Pike
Pike
Sucker
Lm Bail
Rock Ban
RockBau
Sm Bau
Redeye Ban
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Brook Trout
: tlMKW
Whole
Mixed1
Muacle
Mutcle
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
Fillet
Number
tttfnploc
i
314
S
1
15
4
2
1
2
1
5
2
1
2
2
1
Number
jKWttve
MfllfHM
0
66
0
0
0
0
0
0
0
0
b
0
0
0
0
0
C0tV&JttlWti0tJ;
migo
NEK 2.85)
NR
ND<3-6)
ND<6)
ND<0.26-
2.78)
ND( 0.41-
2.78)
NEK 1.13-
1.30)
ND( 0.72)
ND( 2.77-
2.78)
NEK 2.78)
NEK 0.52-
2.78)
NEK 0.77-
0.78)
ND( 0.96)
ND( 0.23-
0.42)
ND( 0.39-
0.45)
ND( 1.46)
Cone.
mean
NA
1.74
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Wt,
tail
Wet
Wet
Fat
Fat
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
• Location*
Varioui, US
Varioui, US
Lake Vanern, Sweden
Hedeunda Bay, Sweden
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Location
description
Background
Varioui
Industrial
Industrial
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Satnp.
year
86-89
86-89
88
88
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R*f,
no.
20
20
19
19
20
20
20
20
20
20
20
20
20
20
20
20
OxmwflM
iamplei composite 3-5 fish
aamplei composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
samples composite 3-5 fish
simples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples componte 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-75
-------
Table B-9. Environmental Leveb of Dibcnzofarang in Fish (ppt) (continued)
Chemical
1,2,3,7,8,9-HxCDF
(continued)
Fitb,
species*
Gray
Redhone
lack Redhone
Golden
Redhone
Longear
Sunfiah
Walleye
Chain Pickerel
Black Grapple
Sea Catfiih
North
Hogsucker
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefish
White Catfish
Crayfish
Tinue
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Number
Mmpief
1
1
1
1
3
3
1
1
1
1
2
1
2
1
1
1
Number
positive
MinguM
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Concentration
range
ND( 0.52)
ND( 2.76)
ND( 2.78)
ND( 0.52)
ND( 0.21-
2.78)
ND(0.20-
0.42)
ND(0.20)
ND( 2.78)
ND( 2.78)
ND(2.77)
ND( 2.77)
ND( 2.78)
ND( 2.77-
2.78)
ND(2.77)
ND( 2.78)
ND( 2.78)
Cone.
mean
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
wt,
*.--!-.
vMlv
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location"
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
yew
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Rrf.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
CommenU
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-76
-------
Table B-9. Environmental Lenfe of Dibenzofurans in Fish (ppt) (continued)
2,3,4,6,7,8-HxCDF
tKtlt
specie**
Vinous1
Pike
Pike
Herring
Herring
Herring
Sucker
Lm Ban
Rock Ban
Rock Biu
SmBau
Redeye Bail
Carp
not available
Brown Trout
Brown Trout
Rainbow
Trout
Mixed1
Mutcle
Mutcle
Whole
Whole
Whole
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Whole
Fillet
Fillet
•unplM
314
8
1
1
2
2
15
4
2
1
2
1
5
2
1
2
2
Number
juun&l&c
3
7
0
0
2
2
0
0
0
0
0
0
1
0
0
0
0
llOgC
NR
ND(3-17)
ND(6)
NEK0.2)
0.4-0.8
0.3
ND( 0.26-
1.96)
ND( 0.41-
1.96)
ND( 1.13-
1.30)
ND( 0.72)
NEK 1.96)
ND( 1.96)
ND- 0.92
ND( 0.78-
2.72)
ND( 0.96)
ND( 0.23-
0.42)
NEK 0.45-
0.58)
mean
1.22
7.96
NA
NA
0.6
NA
NA
NA
NA
NA
NA
NA
0.76
NA
NA
NA
NA
ttSMM
•MM*
Wet
Fat
Fat
Freih
Freih
Freih
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Varioui, US
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Atlantic CoaM, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
description
Varioui
Industrial
Industrial
Pristine
Urban
Industrial
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
ft*flVlA
year
86-89
88
88
NR
NR
NR
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
tiff
no.
20
19
19
5
5
5
20
20
20
20
20
20
20
20
20
20
20
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
composite 2-5 fish
composite 2-5 fish
composite 2-5 fish
samples composite 3-5 fish
samplei composite 3-5 fish
samples composite 3-5 fish
samplei compotite 3-5 fish
simples composite 3-5 fish
samples composite 3-5 fish
simples composite 3-5 fish
simples composite 3-5 fish
simplei composite 3-5 fish
samples composite 3-5 fish
samplei composite 3-5 fish
B-77
-------
TaNeB-9. Environmental Le»«b of Dibeniofanuis in Rsfc (pet) (continued)
Chemical
2,3,4,6,7,8-HxCDF
(continued)
FiA
specie**
Brook Trout
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfith
Walleye
Chain Pickerel
Black Crappie
Sea Catfish
North
Hogsucker
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefiah
Tissue
Fillet
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Number
lampta
1
1
1
1
1
3
3
1
1
1
1
2
1
2
1
Number
potitSvt
HinjHM
0
0
0
1
0
0
0
0
0
0
0
0
0
0
0
Cooeentwtioa
range :
ND(1.46)
ND(0.52)
ND(1.95)
1.25
ND( 0.52)
ND( 0.21-
1.96)
NEK 0.20-
0.42)
ND(0.20)
ND(1.96)
ND( 1.97)
ND( 1.96)
ND(1.95-
1.96)
ND(1.96)
ND( 1.96)
ND( 1.96)
Cone.
mean
NA
NA
NA
1.25
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Wt
ttuil
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location"
Various , US
Variout, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Location
tfefcnpfkm
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
46-S9
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
R*f,
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
COttUttetfte
•amplei composite 3-5 fiah
•ample* composite 3-5 fish
tamplei composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fiah
samples composite 3-5 fish
samples composite 3-5 fiah
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
simples composite 3-5 fish
samples composite 3-5 fish
B-78
-------
Table B-9. EnTinmm«nUd Levels of Dibauofnraas in fish (opt) (continued)
VPsxiroCHf
2,3,4,6,7,8-HxCDF
(continued)
HxCDFi
non-2,3,7,8-HxCDFi
Fi*
specie*
White Catfish
Crayfish
Various8
Bream
Perch
Y. Pereh
Cup
Cup
Blue Crab
Lobster
Str. Ban
Br. Trout
Br. Trout
Rb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Barbel
TtOatt
Whole
Whole
Mixed1
NR
NR
Whole
Whole
Whole
Meat
Meat
Fillets
Whole
Fillets
Whole
Fillets
Whole
Fillets
Whole
Fillet*
Fillets
Number
MinplM
1
1
314
13
2
1
3
3
2
2
2
1
1
1
1
1
1
1
1
1
Number
positive
sample*
0
0
100
13
2
1
2
3
2
2
2
1
0
1
1
1
0
0
0
1
Concentration
range
ND( 1-96)
ND( 1.96)
NR
5.7-47.4
21.9-53.8
440
ND-24
2.7-5.1
9.3-9.4
7.7-7.9
2.0-4.4
2
ND(7)
8
2
16
ND(7)
ND(7)
ND(7)
2.1
Cone.
mean
NA
NA
1.24
25.2
37.8
440
10.0
3.5
9.35
7.8
3.2
2
NA
8
2
16
NA
NA
NA
2.1
Wfc
bMM
Wet
Wet
Wet
Fresh
Fresh
NR
NR
NR
Wet
Wet
Wet
NR
NR
NR
NR
NR
NR
NR
NR
Fat
Location'
Various, US
Various, US
Various, US
Hamburg, Germany
Hamburg, Germany
Housatonic River, MA
Mississippi River, MN
Lake Orono, MN
Passaic River, NI
New York Bight
Newark Bay, NI
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Neckar River, Germany
: Location
description
Background
Background
Various
Urban
Urban
NR
lndimri«l
Industrial
Urban
Dump She
Urban
NR
NR
NR
NR
NR
NR
NR
NR
Urban
Sttnp.
year
86-89
86-89
86-89
84
84
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
88
Ret
no.
20
20
20
4
4
6
8
8
10
10
10
12
12
12
12
12
12
12
12
2
Comment*
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
Elk river power station
Elk river power station
former sewage sludge
composite3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
B-79
-------
Table B-9. Environmental Levels of Dibtmxofunms in Fish (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDF
(continued)
FI&
specie**
Cup
Pike
Pike
Herring
Herring
Herring
Sucker
Lai Bui
Rock Ban
Rock Ban
Sm Ban
Redeye Bast
Carp
not available
Brown Trout
Rainbow
Trout
Brook Trout
Tissue
Whole
Muscle
Muscle
Whole
Whole
Whole
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Fillet
Fillet
Fillet
Number
•atopies
2
16
2
1
2
2
15
2
2
1
2
1
5
2
2
2
I
Number
positive
wmplei
2
1
0
0
2
1
3
0
0
0
0
0
3
1
0
1
0
Concentration
range
Heptacidoroditx
3-4
ND(3-7)-17
ND(6-11)
ND(0.2)
0.8-1.2
ND-0.9
ND-1.88
NEK 1.44-
1.45)
NEK 6.61-
8.89)
NEK 1.40)
ND(1.45)
ND( 1.45)
ND-1.31
ND-1.13
ND( 0-77-
0.80)
ND- 0.48
NEK 4. 13)
Cone,
mean
inzofunuu
3.5
3.41
NA
NA
1.0
0.5
0.96
NA
NA
NA
NA
NA
0.71
2.21
NA
0.56
NA
Wt,
basis
i
-------
Table B-9. Environmental Lereb of DibeMofurans in Rsh (ppt) (continued)
Cbemfc*}
1,2,3,4,6,7,8-HpCDF
(continued)
,RStt
specie*
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfiih
Walleye
Chain Pickerel
Black Cnppie
SeaCatfiih
North
Hogsucker
Summer
Flounder
Dolly Varden
Compofite
Bottom
Winter
Flounder
Bluefish
White Catfiah
Tissue
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Number
sample*
1
1
1
1
3
3
1
1
1
1
2
1
2
1
1
Number
positive
lampfai •
0
0
1
0
0
0
0
0
1
0
0
1
0
0
0
Conceatratiott
range
ND( 2.75)
ND( 2.25)
1.25
ND( 3. 11)
ND( 0.71-
1.45)
ND( 0.27-
1.28)
NEK 0.35)
NEK 1.45)
0.27
NEK 1.45)
NEK 1.44-
1.45)
0.23
NEK 1-45)
NEK 1-78)
NEK 1-45)
Cone.
mean
NA
NA
1.25
NA
NA
NA
NA
NA
0.27
NA
NA
0.23
NA
NA
NA
Wt,
baiig
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location*
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
: description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Stoop
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ref.
no.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Comments
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-81
-------
Table B-9. Environmental Levels of DibensofaraiB in Fish (ppt) (continued)
ChemicaJ
1,2,3,4,6,7,8-HpCDF
(continued)
1,2,3,4,7,8,9-HpCDF
FJ*
species*
Crayfish
Various
Pike
Pike
Sucker
Lm BaH
Rock Ban
Rock Bats
Sm Bait
Redeye Bail
Carp
nf. available
Brown Trout
Rainbow
Trout
Brook Trout
Tiwue
Whole
Mixed*
Muscle
Mutcle
Whole
Fillet
Whole
Fillet
Fillet
Fillet
Whole
Whole
Fillet
Fillet
Fillet
Number
samples
1
314
8
1
15
2
2
1
2
1
3
2
2
2
1
Number
positive
•ample*
0
170
0
0
0
0
0
0
0
0
0
0
0
0
0
Cottoetitnttoii
range
NEK 1 45)
MR
ND(3-11)
ND(6)
ND( 0.71-
4.23)
ND( 2.61-
2.26)
NEK 2.64-
5.92)
ND(1.40)
ND( 2.61-
2.62)
ND( 2.62)
NEK 2.61-
2.62)
ND( 1.12-
1.64)
NEK 0.77-
0.80)
ND( 0.63-
0.91)
ND( 4-13)
Cone.
mean
NA
1.91
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Wt,
bait
Wet
Wet
Fat
Fat
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location*
Varioui US
Various, US
Lake Vanem, Sweden
Hedesunda Bay, Sweden
Various, US
Varioui, US
Various, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Varioui, US
Various, US
Various, US
Varioui, US
Location
description
Various
Industrial
Industrial
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Samp.
year
86-89
86-89
88
88
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ret.
no.
20
20
19
19
20
20
20
20
20
20
20
20
20
20
20
OWttOJWW
samples composite 3-5 fish
samples composite 2-5 fish
composite 5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-82
-------
Table B-9. EnTiromneatal Lereb of Dibenxofuraiu in Fish (ppt) (continued)
VllCQUCIU
1,2,3,4,7,8,9-HpCDF
(continued)
Rsh
specie*
Gray
Redhone
Black
Redhone
Golden
Redhone
Longear
Sunfish
Walleye
Chain Pickerel
Black Crappie
Sea Catfiah
North
Hognicker
Summer
Flounder
Dolly Varden
Composite
Bottom
Winter
Flounder
Bluefiih
White Catfish
TlMIM
Whole
Whole
Whole
Whole
Fillet
Fillet
Fillet
Fillet
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Number
sunptei
1
1
1
1
3
3
1
1
1
1
2
1
2
1
1
Number
positive
samples
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Concentration
nut£c
ND( 2.75)
NEK 3.82)
NEK 2.62)
ND( 3. 11)
NEK 0.71-
2.62)
NEK 0.27-
1.28)
NEK 0.23)
NEK 2.62)
NEK 2.62)
NEK 2.61)
NEK 2.61)
NEK 2.62)
NEK 2.62)
NEK 3. 12)
NEK 2.62)
Cone.
mean
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
wt,
basi*
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location*
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Various, US
Location
description
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Background
Sarop.
year
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
86-89
Ret
DO.
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Cotttracdtji
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
samples composite 3-5 fish
B-83
-------
Table B-9. Environmental Levels of DibenxofanuH m Fish (ppt) (continued)
Chemtca!
1,2,3,4,7,8,9-HpCDF
(continued)
HpCDFi
Fisfe
species*
Crayfish
Various
Bream
Perch
Y. Perch
Carp
Carp
Blue Crab
Lobster
Str. Ban
Br. Trout
Br. Trout
Rb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Tiwue
Whole
Mixed1
NR
NR
Whole
Whole
Whole
Meat
Meat
Filleti
Whole
Filleti
Whole
Filleti
Whole
Filleti
Whole
Filleti
Number
«ampte«
1
314
13
2
1
3
3
2
2
2
1
1
1
1
1
1
1
1
Number
poaitjv*
•ample*
0
13
13
2
0
1
0
2
0
2
0
0
1
0
1
0
0
0
Coacenttttiott
fango
ND( 2.62)
NR
1.8-6.0
5.0-10.1
ND(5.0)
ND-14
ND(6.6)
2.8-3.5
NEK0.9)
1.3-2.4
ND(7)
ND(7)
1
ND(7)
1
NEK7)
ND(7)
ND(7)
Coac.
mean
NA
1.24
3.6
7.6
NA
4.7
NA
3.15
NA
1.8
NA
NA
1
NA
1
NA
NA
NA
wt
bant
Wet
Wet
Freah
Freah
NR
NR
NR
Wet
Wet
Wet
NR
NR
NR
NR
NR
NR
NR
NR
Location'
Various, US
Varioui, US
Hamburg, Germany
Hamburg, Germany
Houutonic River, MA
Miuiuippi River, MN
Lake Orono, MN
Paaiaic River, NJ
New York Bight
Newark Bay, NJ
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Location
: description
Background
Various
Urban
Urban
NR
Industrial
Industrial
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
NR
NR
Stop.
JWM
86-89
86-89
84
84
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
20
20
4
4
6
8
8
10
10
10
12
12
12
12
12
12
12
12
OotnrrtftflN
samples composite 3-5 fish
samples composite 3-5 fish
Elk river power station
Elk river power station
former sewage sludge
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
Oct»chk)rodibenzofti™ni(MW-444.76)
1,2,3,4,6,7,8,9-OCDF
Bream
Perch
NR
NR
14
3
10
3
ND-3.1
1.1-8.3
1.2
3.7
Freah
Freah
Hamburg, Germany
Hamburg, Germany
Urban
Urban
84
84
4
4
B-84
-------
Table B-9. Environmental Leveb of Dibcnwfurans in Rsh (ppt) (coatinaed)
Ch*rete«!
1,2,3,4,6,7,8,9-OCDF
(continued)
F»«fc
species*
Herring
Herring
Herring
Salmon
Salmon
Perch
Pike
Pike
Carp
Y. Perch
Carp
Carp
Blue Crab
Lob Her
Str. Bat*
Lake Trout
Lake Trout
Lake Trout
Walleye
Walleye
Lake Trout
TitKM
Whole
Whole
Whole
Muscle
Muicle
MR
MuKle
Muicle
Whole
Whole
Whole
Whole
Meat
Meat
Filleti
Whole
Whole
Whole
Whole
Whole
Whole
Number
•ample*
1
2
2
2
2
3
8
1
2
1
3
3
2
2
2
1
1
3
1
1
1
riutnbef
positive
uifliptefl
0
1
0
0
0
1
0
0
2
0
0
3
0
0
0
1
1
3
1
1
1
Concentration
faBgG
ND(0.2)
ND-0.3
ND<0.2)
ND(2.0)
ND(0.5)
ND-1.7
ND(3-11)
ND(11)
4-8
ND(5.0)
ND(6.6)
ND(6.6)
ND(8.3)
ND(8.4)
ND(3.1)
0.4
0.1
0.3-1.0
0.9
0.4
0.4
Cone.
mean
NA
0.2
NA
NA
NA
0.57
NA
NA
6
NA
NA
NA
NA
NA
NA
0.4
0.1
0.85
0.9
0.4
0.4
Wt.
twri*
Fresh
Fresh
Fresh
Fresh
Fresh
Fresh
Fat
Fat
NR
NR
NR
NR
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location'
Atlantic Coast, Sweden
Baltic Sea, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Gulf of Bothnia, Sweden
Lake Vanern, Sweden
Hedesunda Bay, Sweden
Lake Huron
Housatonic River, MA
Mississippi River, MN
Lake Orono, MN
Passaic River, NJ
New York Bight
Newark Bay, NJ
Lake Superior
Lake Huron
Lake Michigan
Lake Erie
Lake St. Clair
Lake Ontario
Location
description
Pristine
Urban
Industrial
NR
NR
NR
Industrial
Industrial
NR
NR
Industrial
Industrial
Urban
Dump Site
Urban
NR
NR
NR
NR
NR
NR
Samp.
year
NR
NR
NR
NR
NR
NR
88
88
NR
NR
NR
NR
NR
NR
NR
84
84
84
84
84
84
R*f,
no.
5
5
5
5
5
5
19
19
18
6
8
8
10
10
10
11
11
11
11
11
11
CiMninetfts-
composite 2-5 fish
composite 2-5 fish
composite 2-5 fish
wild salmon
hatched salmon
caught near pulp mill
samples composite 2-5 fish
composite 5 fish
samples composite 3-5 fish
Elk river power station
Elk river power station
former sewage sludge
mean 5 samples
mean 5 samples
range 3 sample sites
mean 5 samples
mean 5 samples
mean 5 samples
B-85
-------
Table B-9. Environmental Lereb of Dibeniofuraii!! in Fish (ppt) (continued)
vll6ltttC4tt
1,2,3,4,6,7,8,9-OCDF
(continued)
Fi«h
species*
Br. Trout
Rb. Trout
Rb. Trout
Lake Trout
Lake Trout
Coho Salmon
Coho Salmon
Cod
Haddock
P. Flounder
Plaice
Flounder
Eel
Mussel
Shrimp
Cod
Tissue
Filleti
Whole
Filleu
Whole
FilleU
Whole
FilleU
FilleU
FilleU
FilleU
FilleU
FilleU
FilleU
Miucle
Muicle
FilleU
Number
•unoiM
i
i
i
i
i
i
i
4
1
1
1
1
4
3
2
6
Number
poaitivt
•ample*;
0
0
0
1
0
0
0
4
1
1
1
1
4
3
2
NR
Concentration
range
ND{7)
NDfT)
ND(7)
2
ND{7)
ND{7)
ND(7)
3.4-9.6
4.3
4.7
41
5.6
31-581
13.4-933
2.3-41
ND-21
Co**,
mean
NA
NA
NA
2
NA
NA
NA
6.3
4.3
4.7
41
5.6
205
339
21.6
NR
wt
buir
NR
NR
NR
NR
NR
NR
NR
Freih
Freih
Freih
Freih
Freih
Freih
Freih
Freih
Freih
Location'
Lake Ontario
Lake OnUrio
LakeOnUrio
Lake OnUrio
LakeOnUrio
LakeOnUrio
LakeOnUrio
Various, Sweden
Varioui, Sweden
Varioui, Sweden
Varioui, Sweden
Varioui, Sweden
Varioui, Sweden
Grenlandifjord.Sweden
Grenlandsfjord,Sweden
Frierfjord, Sweden
Location
oMdipfXCffl
NR
NR
NR
NR
NR
NR
NR
Industrial
Industrial
Induftrial
fpHll«»ri«l
Industrial
Industrial
loduitrial
Industrial
Industrial
sMWip*
ye«
NR
NR
NR
NR
NR
NR
NR
88
88
88
88
88
88
87
88
87
Kef.
DO.
12
12
12
12
12
12
12
17
17
17
17
17
17
17
17
17
CommeaU
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 3 samples
composite 10 samples
composite 10 samples
composite 10 samples
composite 10 samples
only cone, range given
B-86
-------
Table B-9. Environmental Lwb of Dibenw>rnnms in FJsh (ppt) (continued)
Footnote Reference*
• Br. - Brown; Smk. = Smoked; Sir. - Striped; Lg. M. = Large Mouth; Rb. » Rainbow; P. = Pole; Y. - Yellow.
* Varioui, Netherlands - lamplei taken from rix locations around Ilstelmeer Lake; Various, Sweden - samples taken from Orenlandsfjord and Frierfjord; Various US - samples taken from 314 sites across the US, including
industrial and background sites.
c Species were taken from bom bottom feeders and open water feeden, and then composited.
* Whole fish samples and fillet samples were combined during analysti.
NOTES: Summary statistics provided in or derived from references; when reference did not compute mean, it was computed using one-half the detection limit for non-detects;
NA - not applicable;
ND - non-detected (limit of detection);
NR " not reported;
Descriptions provided were those given by reference or surmised from study description when not given;
One half the detection limit was used in calculating means. Therefore, h ii possible to have mean concentrations greater man the range (e.g., reported detection limit for non detects greater than the positive sample).
Sources: 1. Van den Berg, et al. (1987)
2. Frommberger (1991)
3. Rappe, et al. (1984)
4. Gotz, et al. (1990)
5. Rappe, et al. (1989)
8. Reed, et al. (1990)
9. Gardner and White (1990)
10. Rappe, et al. (1991)
11. Vault, etal. (1989)
12. Niimi and Oliver (1989a)
17. Oehme, et al. (1989)
18. Stalling, et al. (1983)
19. Kjeller, et al. (1990)
20. USEPA(1992)
B-87
-------
Table B-10. Environmental Levels of PCBs in Fish (ppt)
Chemical
(1UPAC number)
F««h
*peei«l*
Tissue
Number
sample*
Number
positive
•ample*
Concentration
tttog$
Cone.
mean
Wt.
bttSfe
Location*
Location
description
Samp.
year
Ref.
00.
Coiamenti
Tetrachloro-PCB
-------
Table B-10. Environmental Lereb of PCBs in Fish (ppt) (continued)
Chemical
(IUPAC number)
3,4,4',5-TCB
(continued)
TCBs
Fish
species*
Rb. Trout
Rb. Trout
Coho Salmon
Coho Salmon
Carp
Various
Tittue
Whole
Fillet*
Whole
Fillets
Whole
Mixed1
Number
•unpLei
2
2
2
2
1
362
Number
po*hive
sample*
2
1
2
2
1
263
Concentration
range
13,000-30,000
ND-9,000
2,000-26,000
8,000-14,000
17,000
NR
Cow.
21,500
4,500
14,000
11,000
NA
696,240
Wt.
basil
NR
NR
NR
NR
NR
Wet
Location*
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Saginaw Bay
Various, US
location
description
NR
NR
NR
NR
NR
Various
Samp.
year
NR
NR
NR
NR
NR
86-89
Kef.
no.
15
15
15
15
16
20
Comment*
samples composite 3-5 fish
PentocUoro-PCBtMW'- 326.44)
3,3',4,4',5-PeCB
(126)
2,3,3',4,4'-PeCB
(105)
Carp
BIk. Bullhead
Lg. M. Bass
Blk. Crappie
Wh. Sucker
Coho Salmon
Wh. Crappie
Y. Perch
Small Smelt
Large Smelt
Salmonids
Br. Trout
Br. Trout
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Filleu
1
1
1
1
1
1
1
1
1
1
1
1
1
0
1
1
1
1
1
1
1
1
1
1
1
1
ND(5,000)
352,000
290,000
114,000
483,000
45,000
242,000
80,000
15,000
38,000
110,000
55,000
24,000
NA
352,000
290,000
114,000
483,000
45,000
242,000
80,000
15,000
38,000
110,000
55,000
24,000
NR
NR
NR
NR
NR
NR
NR
NR
Wet
Wet
Wet
NR
NR
Saginaw Bay
Waukegan Harbor, IL
Waukegan Harbor, IL
Waukegan Harbor, IL
Waukegan Harbor, IL
Waukegan Harbor, IL
Waukegan Harbor, IL
Waukegan Harbor, IL
Port Credit, Lake Ontario
VineUnd, Lake Ontario
Lake Ontario
VineUnd, Lake Ontario
Vineland, Lake Ontario
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
78
78
78
78
78
78
78
86
82
81-82
NR
NR
16
13
13
13
13
13
13
13
14
14
14
15
15
composite 6 samples
composite 3 samples
composite 6 samples
composite 5 samples
composite 48 samples
composite 20 samples
composite 60 samples
composite 10 samples
composite 10 samples
B-89
-------
Table B-10. Environmental Levels of PCBs in Fish (ppt) (continued)
Chemical
(IUPAC number)
2,3,y,*,4'-¥cCB
(continued)
2,3,4,4',5-PeCB
(114)
2,3',4,4',5-PeCB
(118)
RA
species*
Lake Trout
Lake Trout
Rb. Trout
Rb. Trout
Coho Salmon
Coho Salmon
Carp
Carp
Small Smelt
Large Smelt
Salmonidi
Br. Trout
Br. Trout
Lake Trout
Lake Trout
Rb. Trout
Rb. Trout
Coho Salmon
Coho Salmon
Carp
Tfcwe
Whole
Fillets
Whole
Fillets
Whole
Fillets
Whole
Whole
Whole
Whole
Whole
Whole
Fillets
Whole
Fillets
Whole
Fillets
Whole
Fillets
Whole
Number
samples
1
1
2
2
2
2
1
1
1
1
1
1
1
1
1
2
2
2
2
1
Number
positive
samples
1
1
2
2
2
2
1
1
1
1
1
1
1
1
1
2
2
2
2
1
Concentration
n&£6
253,000
101,000
34,000-138,000
6,000-50,000
48,000-121,000
19,000-56,000
427,000
57,000
37,000
87,000
250,000
133,000
60,000
634,000
242,000
80,000-310,000
16,000-115,000
100,000-271,000
39,000-136,000
1.35x10"
Cone.
mean
253,000
101,000
86,000
28,000
84,500
37,500
427,000
57,000
37,000
87,000
250,000
133,000
60,000
634,000
242,000
195,000
65,500
185,500
87,500
1.35x
Iff
Wt.
basis
NR
NR
NR
NR
NR
NR
NR
NR
Wet
Wet
Wet
NR
NR
NR
NR
NR
NR
NR
NR
NR
Location*
Port Credit, Lake Ontario
Port Credit, Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Saginaw Bay
Saginaw Bay
Port Credit, Lake Ontario
Vineland, Lake Ontario
Lake Ontario
Vineland, Lake Ontario
Vineland, Lake Ontario
Port Credit, Lake Ontario
Port Credit, Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Lake Ontario
Saginaw Bay
Location
description
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
S*mp<
year
NR
NR
NR
NR
NR
NR
NR
NR
86
82
81-82
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
15
15
15
15
15
15
16
16
14
14
14
15
15
15
15
15
15
15
15
16
Comment*
composite 10 samples
composite 10 samples
composite 48 samples
composite 20 samples
composite 60 ssmples
composite 10 samples
composite 10 samples
composite 10 ssmples
composite 10 samples
B-90
-------
Table B-10. Environmental Lewfc of PCBs in fish (ppt) (continued)
Chemical
(IUPAC number)
PeCBi
8*
species*
Various
Htwe
Mixed*
Nurtber
sample!
362
Number
positive
samples
314
ConcentrUioa
range
NR
Cone,
mean
564,700
MCt
basis
Wet
U««i«»%
Various, US
Location
description
Various
Swop.
year
86-89
Kef.
00.
20
COdMrieflW
composite 3-5 fish
HexadUofo-PCB(MW-360,88)
3,3',4,4'.5,5'-HxCB
(169)
2,3,3',4,4',5-HxCB
(156)
2,3,3',4,4',5'-HxCB
(157)
2,3',4,4',5,5'-HxCB
(167)
HxCBi
Carp
Small Smelt
Large Smelt
Salmonidi
Carp
Carp
Carp
Various
Whole
Whole
Whole
Whole
Whole
Whole
Whole
Mixed'
1
1
1
1
1
1
1
362
0
1
1
1
1
1
1
321
ND(5,000)
2,700
6,100
34,000
79,000
76,000
77,000
NR
NA
2,700
6,100
34,000
79,000
76,000
77,000
355,930
NR
Wet
Wet
Wet
NR
NR
NR
Wet
Saginaw Bay
Port Credit, Lake Ontario
Vineland, Lake Ontario
Lake Ontario
Saginaw Bay
Saginaw Bay
Saginaw Bay
Various, US
NR
NR
NR
NR
NR
NR
NR
Various
NR
86
82
81-82
NR
NR
NR
86-89
16
14
14
14
16
16
16
20
composite 48 samples
composite 20 samples
composite 60 samples
composite 3-5 fish
Heplachloro-PCB (MW- 396.33)
2,3,3',4,4',5,5'-HpCB
(189)
HpCBs
Carp
Various
Whole
Mixed1
1
362
1
250
29,000
NR
29,000
96,700
NR
Wet
Saginaw Bay
Various, US
NR
Various
NR
86-89
16
20
composite 3-5 fish
Footnote Reference*
Blk. = Black; Lg. M. - Large Mouth; Wh. - White; Y. - Yellow; Br. = Brown; Rb. = Rainbow
* US = samples taken from 362 sites across the US, including industrial and background sites.
' Species were Uken from both bottom feeders and open water feeders, and men composited.
' Whole fish samples and fillet samples were combined for analysis.
B-91
-------
Table B-ll. Leveb of Diorins in Food Products (ppt)
Chemical
Sample
type8
Number
•amplei
Number
positive
samples
Concentration
range
Cone,
Meanb
W.
bans
Location
Location
description
Sample
year
Kef.
no.
CommenU
Tetnchlorodibenzo-p-droxina (MW«321 .98)
2,3,7,8-TCDD
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Egg«
Herring
Cod
Redfiih
Milk
Beef
Pork
Milk
Cheese
3
1
2
4
1
1
1
1
1
1
1
I
1
1
1
3
3
10
10
0
1
0
3
1
1
1
1
1
1
1
1
1
1
1
3
0
NR
0
ND(0. 1-0.4)
1.4
ND(.012-.013)
ND-0.049
0.2
0.08
0.6
0.03
0.01
0.3
0.2
4.7
23
2.8
0.0018
0.017-0.062
ND(0.006)
ND-1.9
ND(0.5)
NA
1.4
NA
0.027
0.2
0.08
0.6
0.03
0.01
0.3
0.2
4.7
23
2.8
0.0018
0.032
NA
0.4
NA
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Whole
Fat
Fat
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
U.S.
U.S.
U.S.
W. Germany
W. Germany
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
1
1
2
2
3
3
3
3
3
3
3
3
3
3
4
4
4
5
5
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
front slaughterhouse
from slaughterhouse
samples not randomly selected
B-92
-------
Table B-ll. Lereb of Diorins in Food Products (ppt) (continued)
Chemical
2,3,7,8-TCDD
(continued)
Sample
type*
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Number
samples
5
3
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
0
0
0
0
0
0
0
0
MR
3
1
1
1
0
1
0
0
0
0
0
Concentration
range
ND(0.5)
ND(0.5)
ND(0.5)
ND(0.5)
ND(0.5)
ND(0.5)
ND(0.5)
ND(0.5)
ND-0.013
0.13-0.18
0.07
0.19
0.05
ND(0.16)
0.06
ND(0.15)
ND(0.03)
ND(0.36)
ND(0.34)
ND(0.72)
Cone,:
Mean*
NA
NA
NA
NA
NA
NA
NA
NA
0.009°
0.16
0.07
0.19
0.05
NA
0.06
NA
NA
NA
NA
NA
• VKi ;
bajrii
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
": '•'" -" Location
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
Location
description
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
ReL
no.
5
5
5
5
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
8
Comment*
B-93
-------
Table B-ll. Levels of Dioxms in Food Prodncta (ppt) (continued)
Chemical
2,3,7,8-TCDD
(continued)
Sample
type*
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Milk
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Egg"
Egg"
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
Number
positive
samples
0
0
0
0
0
0
1
0
0
0
1
1
0
0
0
0
2
1
0
0
Concentration
range
ND(0.53)
ND(0.03)
ND(0.57)
ND(0.34)
ND(0.99)
ND(0.95)
0.1Z"1
ND(0.003)
ND(0.05)
ND(0.04)
0.04
0.07
ND(0.12-0.41)
ND(0. 16-0.40)
ND(0.07-0.52)
ND(0.39-0.49)
ND-0.43
ND-1.67
ND(0.01-0.03)
ND(0.01-0.03)
Cone.
Mean1*
NA
NA
NA
NA
NA
NA
0.12"1
NA
NA
NA
0.04
0.07
NA
NA
NA
NA
0.23
0.70
NA
NA
Wf.
bam
Wet
Wet
Wet
Wet
Wet
Wet
Whole
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Location
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
Vermont, U.S.
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Location
description
Background
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
88-89
88-89
88-89
NR
NR
NR
87-88
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
Ret
no.
8
8
8
8
8
8
9
10
10
10
10
10
11
11
11
11
11
11
11
11
Comment*
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
B-94
-------
Table B-ll. Leveb of Dioxms in Food Products (ppt) (continued)
: Chemical
2,3,7,8-TCDD
(continued)
1,2,3,7,8-PeCDD
Sample
type*
Beef
Pork
Chicken
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
Red fish
Milk
Cheese
Number
samples
3
1
1
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
Number
pOIIUVG
sample*
3
1
1
Concentration
0.005-0.028
0.013
0.011
PentadU
0
1
0
2
1
1
1
1
1
1
1
1
1
1
NR
NR
ND(0.2-0.8)
3.5
ND(0.04-0.06)
ND-0.25
0.7
0.41
0.8
0.12
0.5
0.7
0.4
12
1.3
6.5
ND-2.5
ND-0.8
Conc*i
0.017
0.013
0.011
(WwibeUSK^
NA
3.5
NA
0.12
0.7
0.41
0.8
0.12
0.5
0.7
0.4
12
1.3
6.5
1.2
0.6
bait*
Wet
Wet
Wet
J>-d*oxJmi{t
Fieab.
Fren
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
location
New York, NY
New York, NY
New York, NY
Location
description
Sample
year
1990
1990
1990
& 432«.44>
Stockholm, Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ret
no.
12
12
12
1
1
2
2
3
3
3
3
3
3
3
3
3
3
5
5
Comments
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-95
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,7,8-PeCDD
(continued)
Sample
type*
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Laid
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Number
•ample*
5
3
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
0
3
4
0
0
2
1
0
7
3
1
1
0
1
0
0
0
0
0
0
Concentration
range
ND(0.5)
0.5-4.6
2.5-3.4
ND(0.5)
ND(0.5)
0.9-1.2
ND-0.9
ND(0.5)
0.012-0.023
0.10-0.38
0.10
0.60
ND(0.06)
0.07
ND(0.04)
ND(0.07)
ND(0.02)
ND(0.18)
ND(0.17)
ND(0.36)
Cone,
Meanb
NA
1.7
3.1
NA
NA
1.0
0.6
NA
0.016C
0.24
0.10
0.60
NA
0.07
NA
NA
NA
NA
NA
NA
Wl.
but*
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
Location
description
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
Ref.
no.
5
5
5
5
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
8
Comments
B-96
-------
Table B-ll. Levels of Dioxms in Food Products (ppt) (continued)
Chemical
1,2,3,7,8-PeCDD
(continued)
Sample
type'
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Egg*
Egg*
Beef
Number
samples
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
3
Number
positive
samples
0
0
0
1
1
1
1
1
1
1
1
0
0
0
0
0
0
0
0
3
Concentration
range
ND(0.26)
ND(0.02)
ND(0.29)
0.17
0.50
0.95
0.01
0.2
0.11
0.11
0.12
ND(0.40-17.50)
ND(0.49-1.09)
ND<1. 00-4.36)
ND(1. 94-2.70)
ND(0.19-2.19)
ND(0.44-7.40)
ND(0.06-0.40)
ND(0.04-0.06)
0.01 - 0.208
Cone.
Mean*
NA
NA
NA
0.17
0.50
0.95
0.01
0.2
0.11
0.11
0.12
NA
NA
NA
NA
NA
NA
NA
NA
0.093
m.
basts
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Location
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
88-89
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
Kef.
no.
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
Comments
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
B-97
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,7,8-PeCDD
(continued)
PeCDDs
1,2,3,4,7,8-HxCDD
Staple
type*
Pork
Chicken
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Egg»
Herring
Number
sample!
1
1
1
1
1
1
1
3
1
2
4
1
1
1
1
1
1
1
1
Number
positive
samples
1
0
1
1
1
1
1
Concentration
range
0.041
ND(0.011)
0.6
14
5
4
4
Cone.
Mean*
0.041
NA
0.6
14
5
4
4
Wl.
bans
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Location
description
Sample
year
1990
1990
1990
1990
1990
1990
1990
Ref.
no.
12
12
10
10
10
10
10
Comment*
Hexachlorodibenzo-p-dioxin8(MW = 390.87)
0
1
1
3
1
1
1
1
1
1
1
1
ND(0.4-1.6)
0.47
ND-0.068
ND-0.23
0.3
0.15
0.6
0.21
0.3
0.5
1.3
1.2
NA
0.47
0.049
0.14
0.3
0.15
0.6
0.21
0.3
0.5
1.3
1.2
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Stockholm, Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
1
1
2
2
3
3
3
3
3
3
3
3
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
B-98
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDD
(continued)
Sample
type*
Cod
Red fish
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Number
samples
1
1
10
10
5
3
4
3
2
2
2
4
1
1
1
1
1
1
1
1
Number
positive
samples
1
1
NR
10
0
3
4
0
2
1
1
0
0
0
0
0
0
0
1
0
Concentration
range
0.01
0.5
ND-2.0
0.2-0.4
ND(0.5)
0.5-4.6
1.1-3.0
ND(0.5)
0.7-1.0
ND-0.8
ND-2.1
ND(0.5)
ND(0.07)
ND(0.02)
ND(0.18)
ND(0.17)
ND(0.36)
ND(0.26)
0.012
ND(0.29)
Cone,
Meanb
0.01
0.5
0.8
0.3
NA
1.9
1.9
NA
0.8
0.6
1.0
NA
NA
NA
NA
NA
NA
NA
0.012
NA
W«.
bans
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
Location
description
Urban
Urban
Simple
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
Ref.
no.
3
3
5
5
5
5
5
5
5
5
5
5
8
8
8
8
8
8
8
8
Comment*
samples not randomly selected
B-99
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDD
(continued)
1,2,3,6,7,8-HxCDD
Sample
type*
Pork Micks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Eggs
Eggs
Chicken
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Number
sample*
1
1
1
1
1
1
1
1
5
3
1
3
1
2
4
1
1
1
1
1
Number
positive
samples
1
1
1
1
1
1
1
1
0
0
0
0
1
1
3
1
1
1
1
1
Concentration
range
0.24
0.60
0.48
0.02
0.29
0.07
0.14
0.017
ND(0. 12-0.67)
ND(0.08-0.25)
ND(0.017)
ND(0.4-1.6)
1.8
ND-0.068
ND-0.29
1.1
0.95
1.9
0.29
1.5
Cone,
Mean1*
NA
NA
NA
0.02
0.29
0.07
0.14
0.017
NA
NA
NA
NA
1.8
0.049
0.18
1.1
0.95
1.9
0.29
1.5
Vft.
bans
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Whole
Whole
Wet
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Location
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Fransisco
New York, NY
Stockholm, Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Location
description
Urban
Urban
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Sample
year
NR
MR
NR
1990
1990
1990
1990
1990
NR
NR
1990
NR
88
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
8
8
8
10
10
10
10
10
11
11
12
1
1
2
2
3
3
3
3
3
Comments
Composite 6 samples
Composite 6 samples
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
B-100
-------
Table B-ll. Levels of Dioxms in Food Products (ppt) (continned)
Chemical
1,2,3,6,7,8-HxCDD
(continued)
Sample
type*
Chicken
Eg«»
Herring
Cod
Redfiih
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Number
sample!
1
1
1
1
1
10
10
5
3
4
3
2
2
2
4
1
1
1
1
1
Number
positive
samples
1
1
1
1
1
10
10
MR
3
4
0
2
2
2
NR
1
1
1
1
0
Concentration
range
2.8
1.4
5.8
17
8.4
0.5-10.0
0.4-1.2
ND-1.0
1.3-6.0
3.3-8.0
ND(0.5)
2.3-3.7
1.7-1.8
0.9-7.4
ND-0.6
0.135
0.018
0.288
0.340
ND(0.36)
Cone,
Meanb
2.8
1.4
5.8
17
8.4
4.0
0.8
0.7
3.2
5.3
NA
3.0
1.8
3.2
0.3
0.135
0.018
0.288
0.340
NA
Wt.
tana
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Wet
Wet
Wet
Wet
Wet
Location
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Vr . Germany
W. Germany
vf , Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
USSR
USSR
USSR
USSR
USSR
Location
description
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
Rof.
no.
3
3
3
3
3
5
5
5
5
5
5
5
5
5
5
8
8
8
8
8
Comments
samples not randomly (elected
B-101
-------
Table B-ll. Levels of Dxndns in Food Products fart) (continued)
Chemical
1,2,3,6,7,8-HxCDD
(continued)
Sample
type"
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Eggs
Eggs
Beef
Number
samples
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
3
Number
positive
samples
1
1
0
1
1
1
1
1
1
1
1
0
0
0
0
1
1
0
0
3
Concentration
range
0.318
0.048
ND(0.29)
0.47
1.69
3.8
0.07
1.72
0.7
0.58
0.38
ND(0.74-2.72)
ND(1. 64-4.08)
ND(0.64-3.60)
ND(1. 06-2.92)
ND-2.14
ND-4.30
ND(0.10-0.56)
ND(0.07-0.21)
0.03-1.981
Cone..
Mean*
0.318
0.048
NA
0.47
1.69
3.8
0.07
1.72
0.7
0.58
0.38
NA
NA
NA
NA
0.98
1.84
NA
NA
0.84
- . Wfiy "
baata
Wet
Wet
Wet
Wet
wa
Wet
Wet
Wet
Wet
wa
wa
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
-.:./:'• :* iooitioB
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
88-89
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
Ref.
no.
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
Comment*
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
B-102
-------
Table B-ll. Levels of Dioxms in Food Products (ppt) (contnmed)
Chemical
1,2,3,6,7,8-HxCDD
(continued)
1,2,3,7,8,9-HxCDD
Single
type8
Pork
Chicken
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Number
samples
1
1
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
Number
positive
samples
1
1
0
1
1
3
j
1
1
1
1
1
1
1
1
1
NR
10
0
3
Concentration
range
0.282
0.04
ND(0.5-1.6)
0.25
ND-0.068
NEMU7
0.4
0.26
0.6
0.06
0.4
0.6
0.5
1.0
5.2
1.3
ND-3.0
0.3-0.9
ND(0.5)
0.7-4.5
Cone.
Mean1*:
0.282
0.04
NA
0.25
0.049
0.10
0.4
0.26
0.6
0.06
0.4
0.6
0.5
1.0
5.2
1.3
0.8
0.5
NA
2.0
m.
tout*
Wet
Wet
Fresh
Ficdi
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Location
New York, NY
New York, NY
Stockholm, Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
Location
description
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
1990
1990
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ret
no.
12
12
1
1
2
2
3
3
3
3
3
3
3
3
3
3
5
5
5
5
Comment*
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-103
-------
Table B-ll. Levels of Dioxms in Food Products (ppt) (continned)
Chemical
1,2,3,7,8,9-HxCDD
(continued)
Sample
type*
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Number
samples
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
4
0
NR
2
NR
0
NR
3
1
1
0
1
0
0
0
0
0
0
0
1
Concentration
range
1 2-3 0
ND(0.5)
ND-1.1
0.5-0.6
ND-2.7
ND(0.5)
ND-0.018
0.02-0.05
0.02
0.07
ND(0.02)
0.04
ND(0.04)
ND(0.07)
ND(0.02)
ND(0.18)
ND(0.17)
ND(0.36)
ND(0.26)
0.012
Cone.
Meanb
1 8
NA
0.7
0.6
1.2
NA
0.010°
0.04
0.02
0.07
NA
0.04
NA
NA
NA
NA
NA
NA
NA
0.012
Wt.
bans
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England St. Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Location
description
Rural
Sample
y«ar
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
Ref.
no.
5
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
8
8
8
Comments
B-104
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,7,8,9-HxCDD
(continued)
HxCDDs
Sample
type*
Sausage
Pork nicks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Beef
Pork
Chicken
Chicken fat
Number
sample*
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
3
1
1
26
Number
positive
samples
0
1
1
1
1
1
1
1
1
0
0
0
0
1
1
3
1
0
13
Concentration
range
NEK0.29)
0.10
0.40
0.67
0.02
0.29
0.14
0.14
0.19
ND(0.74-2.72)
ND(1. 64-4.08)
ND(0.64-3.6)
ND(1. 06-2.92)
ND-2.14
ND-4.30
0.011-0.616
0.044
ND(0.014)
ND-67
Cone.
Mean*
NA
0.10
0.40
0.67
0.02
0.29
0.14
0.14
0.19
NA
NA
NA
NA
NA
NA
0.238
0.044
NA
27
Wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Wet
Wet
Wet
Fat
Location
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles, CA
San Francisco, CA
Los Angeles,
San Francisco, CA
Los Angeles, CA
San Francisco, CA
New York
New York, NY
New York, NY
Canada
Location
description
Sample
year
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
1990
1990
1990
80
"tot
no.
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
12
12
12
6
Comment!
Hept«chtorodibenzo-p-
-------
Table B-11. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDD
<»
Sample
type"
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Pork
Number
samples
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
3
Number
positive
samples
0
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
NR
Concentration
range
ND(0.4-1.7)
0.45
0.064
0.066-0.42
2
1.5
18
2.1
15
6.0
0.4
3.6
10
3.0
1.0-29.0
1.2-4.0
0.5-5.0
1.8-6.7
2.6-43.7
ND-1.6
Cone.
Meanb
NA
0.45
0.064
0.21
2
1.5
18
2.1
15
6.0
0.4
3.6
10
3.0
6.2
2.3
1.7
3.9
14.4
0.7
Wt.
basil
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Location
Stockholm, Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
Location
description
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
R*f.
no.
1
1
2
2
3
3
3
3
3
3
3
3
3
3
5
5
5
5
5
5
Comment!
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-106
-------
Table B-ll. Levels of Dionns in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDD
(continued)
Sample
type*
Sheep
Chicken
Canned meat
Lard
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Number
samples
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
2
2
2
4
NR
3
1
1
0
1
1
1
1
1
0
1
1
1
1
1
Concentration
nu^ge
10.9-11.8
4.5-5.0
2.5-33.0
2.0-3.0
ND-0.066
0.13-0.34
0.48
0.47
ND(0.44)
0.26
0.21
0.450
0.156
0.720
ND(0.17)
1.44
0.530
0.240
0.57
2.84
Cone,
Meanb
11.4
4.5
13.2
2.8
0.046C
0.22
0.48
0.47
NA
0.26
0.21
0.450
0.156
0.720
NA
1.44
0.530
0.240
0.57
2.84
Wf.
bans
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
England A Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
Location
description
Rural
Sample
year
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
Ret
no.
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
8
8
8
8
8
Comments ,
B-107
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDD
(continued)
HpCDDs
Sample
typ«*
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Egg*
Eggs
Beef
Pork
Chicken
Chicken fat
Number
samples
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
3
1
1
26
Number
positive
samples
1
1
1
1
1
1
1
4
3
5
3
4
3
0
0
3
1
1
16
Concentration
range
7.44
13.3
0.18
S.88
2.11
1.51
1.13
ND-6.71
4.56-8.95
3.32-45.50
3.04-15.30
ND-35.20
1.10-11.40
ND(0. 10-0.42)
ND(0.08-0.24)
0.117-12.065
8.197
0.133
ND-142
Cone.
Mean1*
7.44
13.3
0.18
5.88
2.11
1.51
1.13
4.48
6.28
14.74
10.15
9.64
4.62
NA
NA
4.45
8.2
0.13
52
Wt.
basil
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Fat
Location
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
Canada
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
1990
1990
1980
Ref.
no.
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
12
12
6
Comment*
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Octachlorodibenzo-p-dioxin(MW=460.76)
B-108
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
1,2,3,4,6,7,8,9-OCDD
type*
Food baiket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Egg«
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Pork
•ample*
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
3
Number
samples
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
3
range
1.0-2.1
0.34
0.12-0.16
0.16-0.59
10
3.4
25
19
68
52
12
19
83
11
4.3-25.0
5.0-17.0
2.0-35.0
4.7-«.0
3.1-69.0
5.4-12.3
Meanb
1.47
0.34
0.14
0.32
10
3.4
25
19
68
52
12
19
83
11
11.0
10.5
11.6
5.4
22.3
8.2
. . Vft . ...
bMM
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Stockholm, Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
I /vrAfwm
description
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
yew
NR
1988
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref
no.
1
1
2
2
3
3
3
3
3
3
3
3
3
3
5
5
5
5
5
5
sample composite 12 fillets
Near Incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-109
-------
Table B-ll. Lereb of Diorins in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8,9-OCDD
(continued)
Sample
type*
Sheep
Chicken
Canned meat
Laid
Chicken fat
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coif y, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Number
sample*
2
2
2
4
26
7
3
1
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
2
2
2
4
12
7
3
1
1
1
1
1
1
1
1
1
1
1
1
1
Concentration
inige
14.4-24.4
14.0-19.0
17.0-122
10.0-23.0
ND-238
0.215-0.323
1.40-3.20
4.81
3.4
2.79
1.36
2.25
3.15
0.63
5.40
3.40
11.5
9.01
0.660
5.70
Cone.
Mean*
19.3
16.5
53.0
16.0
90
0.230°
2.12
4.81
3.4
2.79
1.36
2.25
3.15
0.63
5.40
3.40
11.5
9.01
0.660
5.70
Wt.
ban*
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
Canada
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
Location
descrqrtion
Rural
•
»
Sample
year
NR
NR
NR
NR
80
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
..Hot.
no.
5
5
5
5
6
7
7
7
7
7
7
7
8
8
8
8
8
8
8
8
..... wO0XQ)6fZt8 , < ....
B-110
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (contmaed)
Chemical
1,2,3,4,6,7,8,9-OCDD
(continued)
Sample
type*
Pork sticks
Pork fat
Chicken fat
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Eggs
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
Number
positive
samples
1
1
1
1
1
1
1
1
1
1
1
1
1
4
3
5
3
4
3
0
Concentration
range
9.46
29.8
22.8
0.66
5.7
9.46
29.8
22.8
0.34
5.93
1.54
1.5
1.6
ND-11.40
8.03-11.90
13.70-254.00
24.90-125.00
ND-64.00
2.61-96.20
ND(0.80-1.60)
Cone.
Meanb
9.46
29.8
22.8
0.66
5.7
9.46
29.8
22.8
0.34
5.93
1.54
1.5
1.6
8.5S
9.43
77.20
72.43
28.97
35.01
NA
Wt.
ban*
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Location
South Vietnam
South Vietnam
South Vietnam
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
NR
NR
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
Kef.
no.
8
8
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
.. Comments
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
Composite 6 samples
B-111
-------
Table B-ll. Levels of Dioxins in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8,9-OCDD
(continued)
Sample
type*
Eggs
Beef
Pork
Chicken
Number
samples
3
3
1
1
Number
positive
samples
1
3
1
1
Concentration
range
ND-1.30
0.414-15.825
50.742
0.74
Cone.
Meanb
0.63
6.167
50.7
0.74
Wt.
bans
Whole
Wet
Wet
Wet
Location
San Francisco
New York, NY
New York, NY
New York, NY
Location
description
Urban
Simple
year
NR
1990
1990
1990
Ref.
no.
11
12
12
12
Comments
Composite 6 samples
Footnote references
8 Samples were obtained from grocery stores unless stated otherwise. Milk samples were obtained from dairies or transport trucks. No cooked samples from the references were used.
For ND values 1/2 LOD was used in calculating the mean. Therefore, it is possible to have mean concentrations greater than the range (e.g., reported detection limit for nondetects
greater than the positive sample).
0 For ND values the detection limit was used in calculating the mean.
d Value in reference was reported as total 2,3,7,8-TCDD toxic equivalents.
NR = not reported
NA = not applicable
Sources: 1. de Wit et al. (1990)
2. Rappe et al. (1987)
3. Becketal. (1989)
4. LaFleur et al. (1990)
5. Furstetal. (1990)
6. Ryan et al. (1985)
7. Startin et al. (1990)
8. Schecter et al. (1990)
9. U.S. EPA (1991)
10. Schecter et al. (1992)
11. Stanley and Bauer (1989)
12. Schecter etal. (1993)
B-112
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt)
Chemical
Sample
type"
Number
samples
Number
positive
samples
Concentration
rang*
Cone,
mean*
wt.
basis
Location
Location
description
Sample
year
Ref.
no.
Comment*
Tetrachlorodibenzoftiratw(MW-30S.98)
2,3,7,8-TCDF
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fit
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
Red fish
Milk
Beef
Pork
Milk
Cheese
Butter
3
1
2
4
1
1
1
1
1
1
1
1
1
1
1
3
3
10
10
5
3
1
2
4
1
1
1
1
1
1
1
1
1
1
0
1
3
NR
NR
0
0.1-0.4
7.6
0.021-0.028
0.022-0.035
0.7
0.15
0.3
0.11
0.6
2.1
1.1
57
98
78
ND(0.001)
ND-0.005
0.013-0.020
ND-10.0
ND-2.6
ND(0.3)
2.3
7.6
0.024
0.029
0.7
0.15
0.3
0.11
0.6
2.1
1.1
57
98
78
NA
0.0032
0.015
4.1
1.1
NA
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Whole
Fat
Fit
Fat
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
U.S.
U.S.
U.S.
W. Germany
W. Germany
W. Germany
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
1
1
2
2
3
3
3
3
3
3
3
3
3
3
4
4
4
5
5
5
sample composite 12 fillets
near incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-113
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,7,8-TCDF
(continued)
Sample
type-
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Number
samples
3
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
0
NR
0
0
2
0
NR
NR
3
1
1
1
1
1
1
1
1
0
1
1
1
0
Concentration
range
ND(0.3)
ND-0.5
ND(0.3)
ND(0.3)
1.2-4.0
ND(0.3)
ND-1.0
ND-0.011
0.90-1.86
2.61
2.47
0.22
0.31
0.14
0.285
0.027
0.108
ND(0.17)
0.288
0.212
0.021
ND(0.17)
Cone.
mean*
NA
0.2
NA
NA
2.6
NA
0.5
0.008C
1.32
2.61
2.47
0.22
0.31
0.14
0.285
0.027
0.108
NA
0.288
0.212
0.021
NA
Wt.
basis
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
Location
description
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
Ref.
no.
5
5
5
5
5
5 •
5
7
7
7
7
7
7
7
8
8
8
8
8
8
8
8
Comments
B-114
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,7,8-TCDF
(continued)
Sample
type-
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Eggs
Eggs
Beef
Pork
Chicken
Number
samples
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
3
1
1
Number
positive
samples
1
1
1
1
1
1
1
1
1
2
0
0
0
1
0
1
3
1
1
Concentration
range
0.34
0.50
1.9
0.02
0.15
0.07
0.07
0.1
ND-0.84
ND-1.56
ND(0.22-0.49)
ND(0.35-0.54)
ND(0. 19-0.58)
ND-0.67
ND(0.01-0.03)
ND-0.01
0.01-0.051
0.065
0.032
Cone.
tneanb
0.34
0.50
1.9
0.02
0.15
0.07
0.07
0.1
0.28
0.78
NA
NA
NA
0.33
NA
0.01
0.029
0.065
0.032
Wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
WEt
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Location
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
1990
1990
Ref.
no.
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
12
12
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
Pentachlorodibenzofurans (MW-340,42)
1,2,3,7,8-PeCDF
Food basket
Herring, fillet
3
1
0
1
ND(0. 1-0.4)
4.2
NA
4.2
Fresh
Fresh
Sweden
Baltic Sea, Sweden
Urban
NR
88
1
1
sample composite 12 fillets
B-115
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
1,2,3,7,8-PeCDF
(continued)
Sample
type-
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Number
samples
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
3
2
2
2
4
Number
positive
samples
2
4
1
1
1
1
1
1
1
1
1
1
NR
MR
0
0
0
0
0
1
0
NR
Concentration
range
0.020-0.021
0.020-0.036
0.2
0.09
0.01
0.01
0.01
0.01
0.6
16
48
31
ND-1.3
ND-0.3
ND(0.3)
ND(0.3)
ND(0.3)
ND(0.3)
ND(0.3)
ND-1.2
ND(0.3)
ND-0.3
Cone.
mean*
0.020
0.028
0.2
0.09
0.01
0.01
0.01
0.01
0.6
16
48
31
0.3
0.2
NA
NA
NA
NA
NA
0.7
NA
0.2
Wt.
basis
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Location
•
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
Location
description
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
2
2
3
3
3
3
3
3
3
3
3
3
5
5
5
5
5
5
5
5
5
5
Comments
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-116
-------
Table B-12. Levels of Dibenzofiirans in Food PioducU (ppt) (continued)
Chemical
1,2,3,7,8-PeCDF
(continued)
Sample
type-
Milk
Plaice, whole
Mackeral, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
Number
samples
7
3
1
1
1
1
1
I
1
1
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
0
3
1
1
1
1
1
1
1
0
0
1
1
1
0
1
1
1
0
0
0
1
Concentration
range
ND(.002-.017)
0.14-0.23
0.08
0.47
0.05
0.07
0.07
0.165
0.006
ND(0.07)
ND(0.17)
0.144
0.212
0.006
ND(0.17)
0.14
0.20
0.48
ND(0.003)
ND(0.05)
ND(0.04)
0.04
Cone.
mean1'
0.005'
0.18
0.08
0.47
0.05
0.07
0.07
0.165
0.006
NA
NA
0.144
0.212
0.006
NA
0.14
0.20
0.48
NA
NA
NA
0.04
Wt.
fasi*
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
Location
description
Rural
Sample
ytu
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
Ref.
no.
7
7
7
7
7
7
7
8
8
8
8
8
8
8
8
8
8
8
10
10
10
10
Comments
B-117
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
1,2,3,7,8-PeCDF
(continued)
2,3,4,7,8-PeCDF
Sample
type-
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Egg«
Eg««
Beef
Pork
Chicken
Beef
Pork
Chicken
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Number
samples
1
5
3
5
3
5
3
5
3
3
1
1
3
1
1
3
1
2
4
1
1
1
Number
positive
samples
0
0
0
0
0
0
0
0
0
1
1
0
1
1
0
0
1
2
4
1
1
1
Concentration
range
ND(0.05)
ND(0.25-0.86)
ND(0.10-1.44)
ND(0.37-1.40)
ND(0.28-0.58)
ND(0. 16-0.67)
ND(0.12-0.15)
ND(0.03-0.10)
ND(0.01-0.02)
ND-0.01
0.009
ND(0.006)
ND-0.01
0.009
ND(0.006)
ND(0. 1-0.5)
17.0
0.069-0.084
0.066-0.43
1.4
0.4S
1.5
Cone.
mean*
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
0.009
NA
NA
0.009
NA
NA
17.0
0.076
0.24
1.4
0.45
1.5
Wt.
basis
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Location
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Background
Industrial
Urban
Urban
Sample
year
1990
MR
NR
NR
NR
NR
NR
NR
NR
1990
1990
1990
1990
1990
1990
NR
88
NR
NR
NR
NR
NR
Ref.
DO.
10
11
11
11
11
11
11
11
11
12
12
12
12
12
12
1
1
2
2
3
3
3
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
sample composite 12 fillets
near incinerators
composite from 8 trucks
from slaughterhouse
B-118
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,4,7,8-PeCDF
(continued)
Sample
type?
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Number
samples
1
1
1
1
1
1
1
10
10
5
3
4
3
2
2
2
4
7
3
1
1
1
Number
positive
samples
1
1
1
1
1
1
1
10
10
MR
3
4
0
2
2
2
MR
7
3
1
1
1
Concentration
range
0.08
0.9
1.5
0.8
29
3.1
25
1.7-4.6
0.9-2.5
ND-2.0
1.7-3.9
6.5-8.2
ND(0.3)
0.7-2.8
0.7-2.0
0.3-1.3
ND-0.4
0.028-0.038
0.39-1.58
0.37
1.96
0.03
Cone.
mean*
0.08
0.9
1.5
0.8
29
3.1
25
2.7
1.7
1.1
2.7
7.4
NA
1.7
1.3
0.8
0.3
0.032*
0.95
0.37
1.96
0.03
Wt.
basi*
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Location
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England A Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
Kef.
no.
3
3
3
3
3
3
3
5
5
5
5
5
5
5
5
5
5
7
7
7
7
7
Comments
from slaughterhouse
samples not randomly selected
B-119
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,4,7,8-PeCDF
(continued)
Sample
type-
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w /butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
Number
positive
samples
0
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
0
0
0
0
Concentration
range
ND(0.04)
0.04
1.10
0.177
0.108
0.204
0.504
1.43
0.015
0.171
0.27
0.99
0.02
0.25
0.14
0.18
0.07
ND(0.22-0.78)
ND(0.28-1.31)
ND(0.33-1.28)
ND(0.26-0.53)
Cone.
mean*
NA
0.04
1.10
0.177
0.108
0.204
0.504
1.43
0.015
0.171
0.27
0.99
0.02
0.25
0.14
0.18
0.07
NA
NA
NA
NA
Wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Location
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Location
description
Urban
Urban
Urban
Urban
Sample
year
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
Ref,
no.
7
7
8
8
8
8
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
Cbmmefita
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
B-120
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,4,7,8-PeCDF
(continued)
PeCDFs
Sample
type*
Chicken
Chicken
Egg'
Eggs
Beef
Pork
Chicken
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Number
simples
5
3
5
3
3
1
1
1
1
1
1
1
Number
positive
samples
0
0
0
0
3
1
1
1
1
1
1
1
Concentration
range
ND(0. 15-0.60)
ND(0.11-0.14)
ND(0.01-0.07)
ND(0.02-0.02)
0.03-1.783
0.039
0.01
0.3
5
2
2
2
Cone.
me»nb
NA
NA
NA
NA
0.626
0.039
0.01
0.03
5
2
2
2
Wt.
basis
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Location
description
Urban
Urban
Urban
Urban
Sample
y^
NR
NR
NR
NR
1990
1990
1990
1990
1990
1990
1990
1990
Ref.
no.
11
11
11
11
12
12
12
10
10
10
10
10
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
HexachIorOdibenzofurans(MW=374.87)
1,2,3,4,7,8-HxCDF
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Eggs
2
4
1
1
1
1
1
1
1
2
4
1
1
1
1
1
1
1
0.017-0.020
0.026-0.13
0.9
0.43
0.8
0.15
0.9
0.6
0.4
0.018
0.075
0.9
0.43
0.8
0.15
0.9
0.6
0.4
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
NR
NR
NR
NR
NR
NR
NR
NR
NR
2
2
3
3
3
3
3
3
3
near incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
B-121
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDF
(continued)
Sample
type-
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Lard
Milk
Plaice, whole
Mackeral, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Number
samples
1
1
1
10
10
5
3
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
Number
positive
samples
1
1
1
10
MR
MR
NR
4
0
1
1
2
0
7
3
0
1
0
1
1
1
1
Concentration
nogt
3.0
6.9
3.5
0.7-3.0
ND-2.6
ND-1.0
ND-1.1
1.8-6.0
ND(0.3)
ND-1.4
ND-1.9
0.6-0.9
ND(0.3)
0.013-0.026
0.05-0.16
ND(0.02)
0.12
ND(0.1)
0.04
0.03
1.05
0.141
Cone.
mean*
3 0
6.9
3.5
1.7
0.8
0.7
0.7
2.9
NA
0.8
1.0
0.8
NA
o.oir
0.11
NA
0.12
NA
0.04
0.03
1.05
0.141
Wt.
basis
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
Berlin W Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
Location
description
Urban
Urban
Urban
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
Ref.
no.
3
3
3
5
5
5
5
5
5
5
5
5
5
7
7
7
7
7
7
7
8
8
Comments
samples not randomly selected
/
B-122
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDF
(continued)
Sample
type-
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
E««»
Eggs
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
Number
positive
samples
1
0
1
1
1
1
1
1
1
1
1
1
1
1
0
0
0
0
0
0
0
0
Concentration
range
0.108
ND<0.17)
0.432
2.01
0.009
0.171
0.27
0.79
0.48
0.06
0.93
0.47
0.43
0.36
ND(0.38-1.19)
ND(0.35-0.79)
ND(0.49-3.40)
ND(0.40-3.33)
ND(0.35-0.59)
ND(0.5 1-0.71)
ND(0. 14-0.25)
ND(0.04-0.09)
Cone.
mean*
0.108
NA
0.432
2.01
0.009
0.171
0.27
0.79
0.48
0.06
0.93
0.47
0.43
0.36
NA
NA
NA
NA
NA
NA
NA
NA
Wt,
basil
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Location
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Location
uesctipuvti
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
88-89
88-89
88-89
88-89
88-89
88-89
NR
MR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
8
8
8
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
B-123
-------
Table B-12. Levels of Dibenzoftirans in Food Products (ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDF
(continued)
1,2,3,6,7,8-HxCDF
Sample
type-
Beef
Pork
Chicken
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Egg»
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Number
samples
3
1
1
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
Number
positive
samples
3
1
1
0
1
2
4
1
1
1
1
1
1
1
1
1
1
10
NR
MR
NR
4
Concentration
range
0.066-4.846
0.108
0.009
ND(0. 1-0.8)
1.7
0.021-0.028
0.018-0.19
0.8
0.44
0.6
0.07
1.2
0.4
0.3
4.2
13
6.0
0.5-2.0
ND-0.9
ND-1.0
ND-0.9
1.3-5.0
Cone.
mean1'
1.69
0.108
0.009
NA
1.7
0.024
0.090
0.8
0.44
0.6
0.07
1.2
0.4
0.3
4.2
13
6.0
1.1
0.5
0.7
0.5
2.4
Wt.
basil
Wet
Wet
Wet
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Location
New York, NY
New York, NY
New York, NY
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
Location
description
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
1990
1990
1990
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
12
12
12
1
1
2
2
3
3
3
3
3
3
3
3
3
3
5
5
5
5
5
Comments
sample composite 12 fillets
near incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-124
-------
Table B-12. Levels of Dibenzofiirans in Food Product* (ppt) (continued)
Chemical
1,2,3,6,7,8-HxCDF
(continued
Sample
type*
Pork
Sheep
Chicken
Canned meat
Lan!
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Number
samples
3
2
2
2
4
7
3
1
1
I
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
0
1
2
1
0
7
3
1
1
0
1
1
1
1
1
0
1
1
1
1
1
1
Concentration
range
ND(0.3)
ND-1.0
0.3-0.8
ND-0.7
ND(0.3)
0.009-0.017
0.02-0.06
0.06
0.16
ND(0.1)
0.05
0.06
0.240
0.030
0.108
ND(0.17)
0.144
0.424
0.009
0.171
0.14
0.40
Cone.
mean*
NA
0.6
0.5
0.5
NA
0.01 2«
0.04
0.06
0.16
NA
0.05
0.06
0.240
0.030
0.108
NA
0.144
0.424
0.009
0.171
0.14
0.40
Wt
fasi*
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
Location
description
Rural
Sample
year
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
NR
Ref.
no.
5
5
5
5
5
7
7
7
7
7
' 7
7
8
8
8
8
8
8
8
8
8
8
Comments
B-125
-------
Table B-12. Levels of Dibenzofiuans in Food Product* (ppt) (continued)
Chemical
1,2,3,6,7,8-HxCDF
(continued)
Sample
type-
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Eggs
Eggs
Beef
Pork
Chicken
Food basket
Herring, fillet
Milk
Plaice, whole
Mackerel, whole
Number
samples
1
1
1
1
1
1
5
3
5
3
5
3
5
3
3
1
1
3
1
7
3
1
Number
positive
samples
1
1
1
1
1
1
0
0
0
0
0
0
0
0
3
1
1
0
0
0
1
0
Concentration
range
0.38
0.02
0.34
0.14
0.18
0.1
ND(0.37-1.17)
ND(0.35-0.77)
ND(0.48-0.81)
ND(0.39-0.84)
ND(0.35-0.56)
ND(0.14-0.70)
ND(0. 14-0.31)
ND(0.04-0.05)
ND-0.199
0.031
0.008
ND(0.1-0.3)
ND(0.04)
ND(.002-.012)
NEM).02
ND(0.04)
Cone.
me«nv
0.38
0.02
0.34
0.14
0.18
0.1
NA
NA
NA
NA
NA
NA
NA
NA
NA
0.031
0.008
NA
NA
o.oor
0.015
NA
wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Fit
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Fresh
Fresh
Whole
Wet
Wet
-_._..- Location
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York
New York
New York
Sweden
Baltic Sea, Sweden
England & Wales
Norwich, UK
Norwich, UK
Location
deACtlpuon.
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
1990
Urban
Rural
Sample
year
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
1990
1990
NR
88
89
NR
NR
Ref.
no.
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
12
12
1
1
7
7
7
Comment*
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
sample composite 12 fillets
B-126
-------
Table B-12. Levels of Dibenzofunuu in Food Products (ppt) (cominued)
Chemical
1,2,3,7,8,9-HxCDF
(continued)
Sample
type-
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
5
3
Numbet
positive
samples
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Concentration
range
ND(0 OS)
ND(O.I)
ND(0.05)
ND(0.04)
ND(0.04)
ND(0.01)
ND(0.11)
ND(0.17)
ND(0.14)
ND(0.16)
ND(0.01)
ND(0.11)
NDCO.l)
ND(0.2)
ND(0.19)
ND(0.006)
ND(0.1)
ND(0.04)
NEK0.04)
ND(0.05)
ND(0.48-1.51)
ND(0.45-1.01)
Cone.
mean*
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
•wt
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fit
Location
N*«nr>lt I IV
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Location
description
Urban
Urban
Sample
year
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
Ref.
no.
7
7
7
8
8
8
8
8
8
8
8
8
8
8
10
10
10
10
10
11
11
Comments
composite 6 samples
composite 6 samples
B-127
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
1,2,3,7,8,9-HxCDF
(continued)
2,3,4,6,7,8-HxCDF
Sample
type-
Pork
Pork
Chicken
Chicken
Eggs
Eggs
Beef
Pork
Chicken
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Egg"
Herring
Cod
Number
sample*
5
3
5
3
5
3
3
1
1
3
1
2
4
1
1
1
1
1
1
1
1
1
Number
positive
samples
0
0
0
0
0
0
0
0
0
0
1
1
4
1
1
1
1
1
1
1
1
1
Concentration
range
ND(0.62-1.06)
ND(0.51-1.09)
ND(0.45-0.75)
ND(0. 18-0.91)
ND(0. 18-0.58)
ND(0.05-0.06)
ND(0.002-0.01)
ND(0.007)
ND(0.012)
ND(0.1-0.5)
3.9
ND-0.020
0.018-0.28
0.7
0.31
1.3
0.05
1.5
0.3
1.7
3.6
8.2
Cone.
mem*
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
3.9
0.015
0.12
0.7
0.31
1.3
0.05
1.5
0.3
1.7
3.6
8.2
Wit.
basis
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Location
Lot Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
MR
NR
NR
NR
NR
NR
1990
1990
1990
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Ref.
no.
11
11
11
11
11
11
12
12
12
1
1
2
2
3
3
3
3
3
3
3
3
3
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
sample composite 12 fillets
near incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
B-128
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,4,6,7,8-HxCDF
(continued)
2,3,4,6,7,8-HxCDF
Sample
type-
Redfish
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Laid
Milk
Plaice, whole
Mackeral, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Number
samples
1
10
10
5
3
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
Number
positive
samples
1
10
NR
NR
NR
4
0
1
1
1
0
7
3
1
1
0
1
1
1
1
1
0
Concentration
range
7.2
0.7-2.2
ND-1.1
ND-1.0
ND-1.5
1.7-5.0
ND(0.3)
ND-0.9
ND-1.2
ND-0.6
ND(0.3)
0.007-0.017
0.04-0.13
0.03
0.15
ND(0.1)
0.04
0.03
0.060
0.009
0.072
ND(0.17)
Cone.
mean*
7.2
1.3
0.7
0.7
0.9
2.8
NA
0.5
0.7
0.4
NA
o.oir
0.08
0.03
0.15
NA
0.04
0.03
0.060
0.009
0.072
NA
Wt.
basis
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
Location
description
Urban
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
Ref.
no.
3
5
5
5
5
5
5
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
Comments
samples not nndomly selected
B-129
-------
Table B-12. Levels of Dibenzofiirans in Food Products (ppt) (continued)
Chemical
(continued)
Sample
typtf
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
E«8»
E«g»
Beef
Pork
Number
samples
1
1
1
1
1
1
1
1
1
1
,
1
5
3
5
3
5
3
5
3
3
1
Number
positive
samples
1
1
1
1
1
1
1
1
1
1
1
1
0
0
0
0
0
0
0
0
3
1
Concentration
range
0.144
0.159
0.006
0.114
0.10
0.20
0.19
0.01
0.15
0.11
0.14
0.07
ND(0.44-1.39)
ND(0.4 1-0.92)
ND(0.57-0.97)
ND(0.47-1.00)
ND(0.41-0.69)
ND(0.17-0.84)
ND(0. 16-0.52)
NEKO.04-0.05)
0.01-0.177
0.019
Cone.
mean*
0.144
0.159
0.006
0.114
0.10
0.20
0.19
0.01
0.15
0.11
0.14
0.07
NA
NA
NA
NA
NA
NA
NA
NA
0.075
0.019
Wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Location
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
88-89
88-89
88-89
88-89
NR
MR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
1990
Ref.
no.
8
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
12
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
B-130
-------
Table B-12. Levels of Dibenzofiiraiu in Food Products (ppt) (continued)
Chemical
Sample
type«
Chicken
Number
samples
1
Number
positive
samples
0
Concentration
range
ND(0.01)
Cone.
mean*
NA
Wt.
basis
Wet
Location
New Yoik, Ny
Location
description
Sample
year
1990
Ref,
no.
12
Comments
Heptachlorodibenzofuran(MW== 409.3 1)
1,2,3,4,6,7,8-HpCDF
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
E«g«
Herring
Cod
Redfish
Milk
Cheese
Butter
Beef
Veal
Poik
3
1
2
4
1
1
1
1
1
1
1
1
1
1
10
10
5
3
4
3
0
1
1
3
1
1
1
1
1
1
1
1
1
1
10
NR
NR
NR
4
0
ND(0.2-0.9)
0.38
ND-0.12
ND-0.49
0.5
0.34
2.2
1.1
8.1
0.8
0.6
1.6
10
1.5
0.2-6.0
ND-1.1
ND-1.0
ND-5.1
0.7-4.0
ND(0.3)
NA
0.38
0.08
0.25
0.5
0.34
2.2
1.1
8.1
0.8
0.6
1.6
10
1.5
1.5
0.5
0.3
2.0
1.7
NA
Fresh
Fresh
Whole
Whole
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
1
1
2
2
3
3
3
3
3
3
3
3
3
3
5
5
5
-5
5
5
sample composite 12 fillets
near incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
samples not randomly selected
B-131
-------
Table B-12. Levels of Dibenzofiirans in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDF
(continued)
Sample
type-
Sheep
Chicken
Canned meat
Laid
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Number
simples
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
Number
positive
samples
2
2
2
NR
0
3
1
1
0
1
1
0
0
0
0
0
0
0
0
1
1
1
Concentration
range
0.6-1.4
0.5-0.5
0.9-1.9
ND-0.5
ND(.007-.067)
0.04-0.10
0.07
0.14
ND(0.2)
0.06
0.05
ND(O.OT)
ND(0.02)
ND(0.18)
ND(0.17)
ND(0.36)
ND(0.26)
ND(0.02)
ND(0.29)
0.10
0.40
0.38
Cone.
tnein*
1.0
0.5
1.2
0.2
0.020s
0.07
0.07
0.14
NA
0.06
0.05
NA
NA
NA
NA
NA
NA
NA
NA
0.10
0.40
0.38
Wt.
basis
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
W. Germany
W. Germany
W. Germany
W. Germany
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
Location
description
Rural
Sample
y«*f
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
NR
NR
Ref.
no.
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
8
8
8
8
8
8
8
Comtficots
B-132
-------
Table B-12. Levels of Dibenzofurans in Pood Productt (ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDF
(continued)
1,2,3,4,7,8,9-HpCDF
Sample
type-
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Pork
Chicken
Chicken
Egg»
Egg»
Beef
Pork
Chicken
Food basket
Herring, fillet
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Number
samples
1
1
1
1
1
5
3
5
3
5
3
5
3
3
1
1
3
1
7
3
1
1
Number
positive
samples
1
1
1
1
1
3
1
4
3
5
1
0
I
3
1
1
0
0
0
1
0
0
Concentration
range
0.1
1.76
0.6
0.58
0.52
ND-1.15
ND-0.67
ND-10.60
2.09-5.68
1.57-24.60
ND-1.01
ND(0.06-0.77)
ND-0.07
0.018-2.702
1.251
0.024
ND(0.3-1.6)
ND(0.04)
ND(0.01-.067)
ND-0.02
ND(0.08)
ND(0.06)
Cone.
mean*
0.1
1.76
0.6
0.58
0.52
0.96
0.74
4.05
3.55
7.00
0.51
NA
0.05
1
1.251
0.024
NA
NA
0.026e
0.03
NA
NA
wt.
basis
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Wet
Fresh
Fresh
Whole
Wet
Wet
Wet
Location
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
Sweden
Baltic Sea, Sweden
England & Wales
Norwich, UK
Norwich, UK
Norwich, UK
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Rural
Sample
year
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
1990
1990
NR
88
89
NR
NR
NR
Ref.
no.
10
10
10
10
10
11
11
11
11
11
11
U
11
12
12
12
1
1
7
7
7
7
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
sample composite 12 diets
B-133
-------
Table B-12. Levels of Dibenzofunns in Food Product* (ppt) (continued)
Chemical
1,2,3,4,7,8,9-HpCDF
(continued)
Sample
type-
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
American cheese
Beef
Beef
Pork
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
5
3
5
Number
positive
samples
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
1
0
0
0
0
0
Concentration
range
ND(0.2)
ND(0.13)
ND(0.10)
ND(0.07)
ND(0.02)
ND(0.18)
ND(0.17)
ND(0-36)
ND(0.26)
ND(0.02)
ND(0.29)
ND(0.07)
ND(0.3)
ND(0.19)
ND(0.03)
ND(0.34)
0.14
ND(0.18)
ND(0.12)
ND(0.37-3.28)
ND(0.78-2.37)
ND(2.22-5.40)
Cone.
mean*
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
0.14
NA
NA
NA
NA
NA
wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Location
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Lot Angeles
Location
description
Urban
Urban
Urban
Sample
year
NR
NR
NR
88-89
88-89
88-89
88-89
88-89
88-89
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
Ref.
no.
7
7
7
8
8
8
8
8
8
8
8
8
8
8
10
10
10
10
10
11
11
11
Comments
composite 6 samples
composite 6 samples
composite 6 samples
B-134
-------
Table B-12. Levels of Dibenzofurana in Food Products (jppt) (continued)
Chemical
Sample
type1
Pork
Chicken
Chicken
E««»
E«8»
Beef
Pork
Chicken
Number
samples
3
5
3
5
3
3
1
1
Number
positive
samples
0
0
0
0
0
2
1
0
Concentration
range
ND(1.63-3.12)
ND(0.47-4.10)
ND(0.45-0.75)
ND(0.09-1.10)
ND(0.04-0.18)
ND-0.118
0.097
ND(0.01)
Cone.
mean*
NA
NA
NA
NA
NA
NA
0.097
NA
m
bans
Fat
Fat
Fit
Whole
Whole
Wet
Wet
Wet
: Location
San Francisco
Loa Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
New York, NY
Location
description
Urban
Urban
Urban
Urban
Urban
Sample
year
NR
NR
NR
NR
NR
1990
1990
1990
Ref.
no.
11
11
11
11
11
12
12
12
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
Octachlorodibenzomrans(MW=444.76)
1,2,3,4,6,7,8,9-OCDF
Food basket
Herring, fillet
Milk
Milk
Milk
Butter
Beef fat
Pork
Sheep fat
Chicken
Eggs
Herring
Cod
3
1
2
4
1
1
1
1
1
1
1
1
1
0
0
1
1
1
1
1
1
1
1
1
1
1
ND(0.4-2.1)
ND(0.07)
ND-0.20
ND-0.52
I
0.25
0.2
0.41
0.3
0.6
0.2
1.4
2.1
NA
NA
0.12
0.19
1
0.25
0.2
0.41
0.3
0.6
0.2
1.4
2.1
Fresh
Fresh
Whole
Whole
Fat
Fat
Fit
Fat
Fat
Fat
Fat
Fat
Fat
Sweden
Baltic Sea, Sweden
Switzerland
Switzerland
W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Berlin, W. Germany
Urban
Background
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
NR
88
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
1
1
2
2
3
3
3
3
3
3
3
3
3
sample composite 12 fillets
near incinerators
composite from 8 trucks
from slaughterhouse
from slaughterhouse
B-135
-------
Table B-12. Levels of Dibenzofiinni in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8,9-OCDF
(continued)
Sample
type-
Redfiah
Milk
Cheese
Butter
Beef
Veal
Pork
Sheep
Chicken
Canned meat
Laid
Milk
Plaice, whole
Mackerel, whole
Herring, whole
Cod, whole
Skate, whole
Coley, whole
Cow cream
Beef
Cheese w/butter
Beef fat
Number
samples
1
10
10
5
3
4
3
2
2
2
4
7
3
1
1
1
1
1
1
1
1
1
Number
positive
samples
1
NR
10
0
0
NR
0
0
2
2
0
7
3
1
1
1
1
0
0
0
0
0
Concentration
range
0.3
ND-4.3
0.4-4.2
ND(0.3)
ND(0.3)
ND-5.0
ND(0.3)
ND(0.3)
0.6-1.5
0.3-2.7
ND(0.3)
0.023-0.071
0.08-0.23
0.20
0.19
0.26
0.14
ND(0.30)
ND(0.07)
ND(0.02)
ND(0.18)
ND(0.17)
Cone.
mean*
0.3
1.2
1.2
NA
NA
1.4
NA
NA
1.0
1.3
NA
0.041'
0.16
0.20
0.19
0.26
0.14
NA
NA
NA
NA
NA
Wt.
basis
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Location
Berlin, W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
W. Germany
England &. Wales
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
Norwich, UK
USSR
USSR
USSR
USSR
Location
description
Urban
Rural
Sample
year
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
89
NR
NR
NR
NR
NR
NR
88-89
88-89
88-89
88-89
Ref.
no.
3
5
5
5
5
5
5
5
5
5
5
7
7
7
7
7
7
7
8
8
8
8
Comments
samples not randomly selected
B-136
-------
Table B-12. Levels of Dibenzoftirans in Food Products (ppt) (continued)
Chemical
1,2,3,4,6,7,8,9-OCDF
(continued)
Sample
type*
Pork
Butter
Swiss cheese
Sausage
Pork sticks
Pork fat
Chicken fat
Cottage cheese
Soft blue cheese
Heavy Cream cheese
Soft cream cheese
Beef
Beef
Pork
Pork
Eggs
Egg»
Beef
Pork
Number
samples
1
1
1
1
1
1
1
1
1
1
1
1
5
3
5
3
5
3
5
3
3
1
Number
positive
samples
0
0
0
0
1
0
1
1
1
1
1
1
0
0
4
1
2
0
0
0
3
1
Concentration
rang*
ND(0.36)
ND(0.26)
ND(0.02)
ND(0.29)
0.10
ND(0.3)
0.57
0.06
1.08
0.29
0.29
0.3
ND(0.48-5.31)
ND(0.45-2.15)
ND-9.36
ND-1.89
ND-26.00
ND(0.64-0.77)
ND(0.10-1.30)
ND(0.05-0.21)
0.018-1.073
0.821
Cone.
mem*
NA
NA
NA
NA
0.10
NA
0.57
0.06
1.08
0.29
0.29
0.03
NA
NA
2.90
1.20
6.64
NA
NA
NA
0.381
0.821
Wt.
basis
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Wet
Fat
Fat
Fat
Fat
Fat
Fat
Whole
Whole
Wet
Wet
Location
USSR
USSR
USSR
Moscow, USSR
South Vietnam
South Vietnam
South Vietnam
New York, NY
New York, NY
New York, NY
New York, NY
New York, NY
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
Los Angeles
San Francisco
New York, NY
New York, NY
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
year
88-89
88-89
88-89
88-89
NR
NR
NR
1990
1990
1990
1990
1990
NR
NR
NR
NR
NR
NR
NR
NR
1990
1990
Ref.
DO.
8
8
8
8
8
8
8
10
10
10
10
10
11
11
11
11
11
11
11
11
12
12
Comments
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
composite 6 samples
B-137
-------
Table B-12. Levels of Dibenzofurans in Food Products (ppt) (continued)
Chemical
Sample
typ*
Chicken
Number
samples
1
Number
positive
samples
1
Concentration
range
0.034
Cone.
mean*
0.034
Wt.
basis
Wet
Location
New York, NY
Location
description
Sample
year
1990
Kef.
no.
12
Comments
Footnote references
* Samples were obtained from grocery stores unless stated otherwise. Milk samples were obtained from dairies or transport trucks. No cooked samples from the references were used.
* For ND values 1/2 LOD was used in calculating the mean. Therefore, it is possible to have mean concentrations greater than the range (e.g., reported detection limit for nondetects
greater than the positive sample).
* For ND values the detection limit was used in calculating the mean.
NR = not reported.
NA = not applicable.
Sources: 1. de Wit et al. (1990)
2. Rappe et al. (1987)
3. Beck et al. (1989)
4. LaFleur et al. (1990)
5. Furstetal. (1990)
6. Ryan et al. (1985)
7. Startin et al. (1990)
8. Schecteretal. (1990)
9. U.S. EPA (1990)
10. Schecteretal. (1992)
11. Stanley and Bauer (1989)
12. Schecteretal. (1993)
B-138
-------
CD
«A
CO
(O
I
I
r
2
s
r
I
-------
Table B-13 Environmental Levels of PCB» fa Food Products (ppt) (continued)
1UPAC
number Chemical
118 2,3',4,4',5-PeCB
(continued)
Sttnpfe
Type
Pork
Poultry
Eggs
Margarine
Cream
Icecream
Yogurt
Cheese
Cottage
cheese
Processed
cheese
Butter
Number
samples
4
4
5
1
5
5
5
5
5
5
5
Number
potttive
sample*
4
4
5
1
5
5
5
5
5
5
5
Conc«nt«tioB
range
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
NR
Cone.
mean*
55
81
99
19
72
53
24
251
33
184
487
Location
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Location oeMfiptiOQ
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sample
rear
86-88
86-88
86-88
86-88
86-88
86-88
86-88
86-88
86-88
86-88
86-88
R*f.
no*
1
1
1
1
1
1
1
1
1
1
1
e—
Heacachloro-PCB (MW«f 360.88)
156 2,3,3',4,4',5-HxCB
Steak
Ground
Beef
Pork
Poultry
Egg*
Cream
Ice cream
2
4
2
3
3
2
2
2
4
2
3
3
2
2
NR
NR
NR
NR
NR
NR
NR
8
14
9
16
24
9
9
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Urban
Urban
Urban
Urban
Urban
Urban
Urban
86-88
86-88
86-88
86-88
86-88
86-88
86-88
1
1
1
1
1
1
1
B-140
-------
Table B-13 EaTiramncntal Levels of PCBs in Food Products (pot) (continued)
IUPAC
number Chemical
156 2,3,3',4,4',5-HxCB
(continued)
Sample
Type
Yogurt
Cheeie
Cottage
cheese
Proceued
cheese
Butter
Number
aunplei
1
5
1
5
5
Number
potitiv*
sample*
1
5
1
5
5
Concent**tion
range
NR
NR
NR
NR
NR
Cone.
mean*
7
28
13
22
63
Location
Canada
Canada
Canada
Canada
Canada
Urban
Urban
Urban
Urban
Urban
Sample
year
86-88
86-88
86-88
86-88
86-88
fcrf.
no.
1
1
1
1
1
CommBttte
HeptacUoro-PCB (MW«396.3J)
189 2,3,3',4,4',5,5'-HpCB
Roast
beef
Cream
Butter
1
1
1
1
1
1
NR
NR
NR
10
10
7
Canada
Canada
Canada
Urban
Urban
Urban
86-88
86-88
86-88
1
1
1
Footnote References
* The mean is the geometric mean.
NR= Not Reported
Sources: 1. Mei, et al. (1991).
B-141
-------
Table B-14. EimronnenUl Let«h rf Dioxms fa
Chemical
2,3,7,8-TCDD
aHutnitef
•ample*
3
3
NR
I
7
28
NR
NR
1
2
2
3
2
1
1
3
1
2
2
1
1
1
1
7
Nombw
poihive
!«tttp|et
0
0
NR
0
NR
2
NR
NR
1
2
2
0
0
0
0
0
0
0
0
1
1
1
1
0
CoocdditthoA
ttagt
ND(.01-.02)
ND(.01-.02)
ND(0.01)
ND(0.0095)
ND-0.05
ND-0.004
ND(0.02)
ND(0.03)
0.0004
0.02-0.06
0.02-0.08
ND(.01 2-0.2)
ND(0.24-0.82)
ND(0.15)
ND<0.058)
ND(0.04-0.15)
ND(0.06)
ND(0.05-0.18)
ND(0.04-0.21)
0.0004
0.0007
0.0002
0.0001
ND(0.004-
0.023)
Cone.
mow
Location
NA
NA
NA
NA
0.01
0.002
NA
NA
0.0004
0.04
0.05
NA
NA
NA
NA
NA
NA
NA
NA
0.0004
0.0007
0.0002
0.0001
NA
NUgra F«U«, NY
Niagra F«Ui, NY
Greenbay, WI
Lot Angeles, CA
Bridgeport, CT
Wallingford, CT
Rutland, VT
Durham, NC
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Cohunbui, OH
Columbui, OH
Waldo, OH
Albany, NY
Binghamton, NY
Utica, NY
Niagara Falli , NY
Stockholm
Stockholm
Stockholm
Stockholm
Reseda, CA
Location
-------
Table B-14. Environmental Lerefc a* Dtariw m Air (pg/m5) (coatimed)
dkdsit4w
2,3,7,8-TCDD
(continued)
TCDDs
Number
umpte*
1
6
5
7
4
2
2
16
16
7
27
1
2
2
3
2
1
1
3
1
2
2
1
Number
pontive
sample*
0
0
0
0
1
0
1
3
12
NR
20
1
2
2
1
0
0
0
0
0
0
0
1
Codccntrttioit
nuige
ND{0.030)
ND<0.0026-
0.048)
ND(0.0106-
0.045)
ND<0.0070-
0.051)
NIM).034
NDC0.022-
0.039)
ND-0.0086
ND-0.18
ND-10.12
ND-0.54
ND-0.07
0.05
0.10-0.22
0.21-1.5
ND-0.18
ND(0.24-0.82)
ND(0.15)
ND(0.058)
ND(0.04-0.15)
ND(0.06)
ND(0.05-0.18)
ND(P.04-0.21)
0.05
Corte.
mttn
NA
NA
NA
NA
.017
NA
0.0079
0.04
0.99
0.20
0.03
0.05
0.16
0.86
0.12
NA
NA
NA
NA
NA
NA
NA
0.05
Location
Commerce, CA
North Long Beach,
CA
San Betnadino, CA
El Tore, CA
Cal Tranrit, CA
Canon, CA
WeM Long Beach,
CA
Niagra Falls, NY
Niagra Falls, NY
Bridgeport, CT
Wallingford, CT
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbus, OH
Columbus, OH
Waldo, OH
Albany, NY
Binghamton, NY
Utica, NY
Niagara Falls, NY
Stockholm
Location
description
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Urban
Industrial
Industrial
Urban
Rural
Urban
Urban
Urban
Industrial
Urban
Sample
year
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
87-88
88
89
NR
NR
87
87
87
87
87-88
88
88
87
89
Rrf.
W>.
14
14
14
14
14
14
14
1
1
4
5
7
8
8
9
9
9
9
11
11
11
11
12
OottuMotii
mostly residential
mostly residential
mostly residential
near highway
on she at gas cooking equipment manufacturer
mostly residential area
downwind industrial eomplex
composite of 2-7 samples
urban air & inride traffic tunnel
downwind incinerator ft industrial complex
near incinerators
near incinerators
next to interstate highway
background Site
B-143
-------
Table B-14. EnrironinmUl Ler* of Dwxms fa Air (pg/m1) (continued)
Chemical
TCDDi (continued)
1,2,3,7,8-PeCDD
Number
wmpte*
1
1
1
7
1
6
5
7
4
2
2
3
3
MR
1
7
28
NR
NR
1
2
2
Number
potitive
Mrapfei
1
1
1
0
0
0
0
0
1
1
1
0
1
NR
0
NR
9
NR
NR
1
1
2
Concentration
range
0.026
0.031
0.0057
ND(0.0050-
0.046)
ND(0.030)
ND(0.0026-
0.075)
ND(0.0106-
0.093)
ND
-------
Table B-14. En?inmmcntal Lertfc of Dioxmc fa Air (pg/m5) (continued)
Chemical
1,2,3,7,8-PeCDD
(continued)
PeCDDt
Number
samples
3
2
1
1
1
1
1
1
1
7
1
6
5
7
4
2
2
16
16
7
28
1
Number
positive
samples
0
0
0
0
1
1
1
1
1
1
1
0
0
0
0
0
0
1
11
MR
21
1
Concentration
range
ND(.034-0.27)
ND(.047-.06)
ND(0.082)
ND(0.033)
0.006
0.0038
0.0014
0.0007
0.0004
ND-0.14
0.120
ND
-------
Table B-14. Environmental Lerds of DimdM b Air (pg/m1) (continued)
Chemical
PeCDD« (continued)
Nuoilxr
•tffipfet
2
2
3
2
1
1
3
1
2
2
1
1
1
1
7
1
6
5
7
4
2
2
Number
potato
ample*
2
2
1
0
0
0
0
0
0
0
1
1
1
1
2
1
2
0
0
1
1
0
Concentration
mnge
0.07-1.3
2.4-5.0
ND-0.10
ND(0.47-.06)
ND(0.082)
ND(0.033)
ND<0.04-0.21)
ND(0.11)
ND(0.07-fl.34)
ND(0.07-0.34)
0.110
0.079
0.04
0.019
ND-O.89
0.57
ND-0.81
N 0(0.063-
0.93)
ND(0.0062-
0.047)
ND-0.1S
NEM).042
ND(0.045-
0.088)
Cone,
tnettt
0.68
3.70
0.097
NA
NA
NA
NA
NA
NA
NA
0.110
0.079
0.04
0.019
0.143
0.57
0.150
NA
NA
0.0618
0.0345
NA
Location
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbui, OH
Columbui, OH
Waldo, OH
Albany, NY
Binghtmton, NY
Utica, NY
Niagara, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reaeda, CA
Commerce, CA
North Long Beach,
CA
San Bemadino, CA
El Toro, CA
Cal Tranait, CA
Carton, CA
Weat Long Beach,
CA
Location
4wacnptioft
Urban
Urban
Induitrial
Industrial
Urban
Rural
Urban
Urban
Urban
Induitrial
Urban
Suburban
Rural
Coaatal
Urban
Urban
Urban
Urban
Urban
Urban
Induitrial
Urban
Sample
y*v
NR
NR
87
87
87
87
87-88
88
88
87
89
89
89
89
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
Ret
w».
8
8
9
9
9
9
11
11
11
11
12
12
12
12
14
14
14
14
14
14
14
14
Comment*
urban air A inside traffic tunnel
downwind incinerator & industrial complex
near incinerators
near incinerators
next to interstate highway
background site
mostly residential
near freeway
mostly residential
mostly residential
mostly residential
near highway
on lite at gas cooking equipment manufacturer
mostly residential
B-146
-------
Table B-14. Environmental Lereh «f Dimda* m Air (pg/m3) (continued)
1,2,3,4,7,8-HxCDD
samples
3
3
NR
1
7
28
NR
NR
1
2
2
3
2
1
1
1
1
1
1
1
7
1
6
5
Number
positive
samples
0
3
NR
0
NR
8
NR
NR
1
0
2
3
0
0
1
1
1
1
1
1
3
1
1
1
Concentration
range
ND(.01-.02)
.04- .64
NR
ND(0.076)
ND-0.08
ND-0.03
NR
NR
0.004
ND(0.08-0.17)
0.19-1.0
.032-.055
ND(.028-.039)
ND(0.032)
0.031
0.004
0.0028
0.0012
0.0006
0.0023
ND-0.20
0.12
NDO.14
ND-0.043
Cone.
Hexschlot
NA
0.24
0.01
NA
0.03
0.01
0.05
0.01
0.004
NA
0.60
0.041
NA
NA
0.031
0.004
0.0028
0.0012
0.0006
0.0023
0.0588
0.12
0.0402
0.0406
Location
odlbeoa»^
-------
Table B-14. Environmental Levels of Dioxms fa Air (pg/nr1) (continued)
Chemical
1,2,3,4,7,8-HxCDD
(continued)
1,2,3,6,7,8-HxCDD
Number
samples
7
4
2
2
3
3
MR
1
7
28
MR
NR
1
2
2
3
2
1
1
1
1
1
1
Numb*
positive
sample*
0
0
0
0
1
3
NR
0
NR
22
NR
NR
1
2
2
3
1
0
1
1
1
1
1
Concentration
range
ND(0.012-
0.10)
ND<0.0078-
0.074)
ND(0.015-
0.025)
ND(0.038-
0.043)
ND-.03
.05-1.06
NR
ND
-------
Table B-14. EnTironmental Letch *f DioriM fa Air (pg/m*) (cantimsMl)
Chemical
1,2,3,6,7,8-HxCDD
(continued)
1,2,3,7,8,9-HxCDD
Number
samples
1
7
1
6
5
7
4
2
2
3
3
NR
1
7
28
NR
NR
1
2
2
3
2
1
JNttittbef
positive
samples
1
3
1
1
1
0
1
0
0
1
2
NR
0
NR
18
NR
NR
0
0
2
3
!
0
Concentration
«nge
0.0029
ND-0.35
0.25
ND-0.39
ND-0.15
ND(0.0070-
0.097)
ND-0.065
ND(0.015-
0.025)
ND(0.019-
0.032)
ND-.03
ND-0.11
NR
N D(0.086)
ND-0.25
ND-0.07
NR
ND(0.01)
NEK0.001)
ND(0.08-0.17)
0.36-5.2
.017-.050
ND-.064
ND(0.032)
Cone,
mem
0.0029
0.0801
0.25
0.0833
0.0586
NA
0.0383
NA
NA
0.02
0.06
0.02
NA
0.08
0.03
0.05
NA
NA
NA
2.78
0.031
0.039
NA
Location
Bloomington, IN
Reseda, CA
Commerce, CA
North Long Beach,
CA
San Bemadino, CA
El Toro, CA
Cal Transit, CA
Carson, CA
West Loaf Beach,
CA
Niagra Falls, NY
Niagra Falls, NY
Oreenbay, WI
Los Angeles, CA
Bridgeport, CT
Wallingford, CT
Rutland, VT
Durham, NC
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbus, OH
Columbus, OH
Location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Industrial
Urban
Sample
year
86
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
NR
87
87-88
88
NR
NR
89
NR
NR
87
87
87
Kef.
no.
13
14
14
14
14
14
14
14
14
1
1
2
3
4
5
6
6
7
8
8
9
9
9
CondRtoetiUl
mostly residential
near freeway
mostly residential
mostly residential
mostly residential
near highway
on she at gas cooking equipment manufacturer
mostly residential
downwind industrial complex
composite of 2-7 samples
urban air A inside traffic tunnel
downwind incinerator & industrial complex
near incinerators
near incinerators
next to interstate highway
B-149
-------
Table B-14. EaTiranm«ntalL«T«lsefDMndiHinAir(I«/m>)(coiitiinM4)
Chemical
1,2,3,7,8,9-HxCDD
(continued)
HxCDDs
Number
aarnptei
1
1
1
1
1
1
7
1
6
5
7
4
2
2
16
16
7
28
1
2
2
3
2
Number
positive
samples
1
1
1
1
1
1
3
1
1
1
0
0
0
0
11
12
MR
27
1
2
2
3
2
Concentration
range
0.025
0.0065
0.0052
0.0018
0.0013
0.0013
ND-0.35
0.27
ND-0.35
ND-0.10
ND(0.009-
0.12)
NDC0.023-
0.074)
ND(0.015-
0.019)
ND(0.019-
0.040)
ND-0.23
ND-12.16
ND-2.17
ND-0.68
0.10
0.74-2.7
5.3-24
0.6-0.63
0.43-0.78
Cone.
mean
0.025
0.0065
0.0052
0.0018
0.0013
0.0013
0.1198
0.27
0.0758
0.0499
NA
NA
NA
NA
0.08
1.69
0.72
0.26
0.10
1.72
14.6
0.62
0.60
Location
Waldo, OH
Stockholm
Stockholm
Stockholm
Stockholm
Bloomington, IN
Reaeda.CA
Commerce, CA
North Long Beach,
CA
San Bemadino, CA
El Tore, CA
Cal TnnaH, CA
Canon, CA
West Long Beach,
CA
Niagra Falli , NY
Niagia Falls, NY
Bridgeport, CT
Wallingfoid, CT
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbui, OH
Location
description
Rural
Urban
Suburban
Rural
Coastal
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Urban
Industrial
Industrial
Sample
year
87
89
89
89
89
86
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
87-88
88
89
NR
MR
87
87
Rof.
n»-
9
12
12
12
12
13
14
14
14
14
14
14
14
14
1
1
4
5
7
8
8
9
9
Comments
background site
mostly residential
near freeway
mostly residential
mostly residential
mostly residential
near highway
on she at gas cooking equipment manufacturer
mostly residential
downwind industrial complex
composite of 2-7 samples
urban air & inside traffic tunnel
downwind incinerator & industrial complex
near incinerator*
near incinerator*
B-150
-------
Table B-14. Environmental Lercb of Dfoxfas fa Air (pg/m1) (continued)
Chemical
HxCDDs (continued)
Number
1
1
3
1
2
2
1
1
1
1
7
1
6
5
7
4
2
2
1,2,3,4,6,7,8-HpCDD
3
3
NR
1
7
28
Number
positive
•amplei
1
1
1
0
1
1
1
1
1
1
7
1
4
2
4
2
1
2
3
2
NR
1
NR
23
Concentration
range
0.15
0.33
ND(0.34)-0.13
ND(0.16)
ND(0.55)-0.1
ND(0.1 1)-0.17
0.096
0.082
0.03
0.014
0.062-3.0
2.00
ND-3.2
ND-0.77
ND-0.11
NIX0.27
ND-0.14
0.16-0.32
0.34-0.51
ND-5.43
NR
0.25
0.02-1.07
NDO.73
Cone.
mean
0.15
0.33
0.125
NA
0.188
0.112
0.096
0.082
0.03
0.014
0.988
2.00
0.640
0.197
0.0424
0.153
0.10
0.241
Location
Columbus, OH
Waldo, OH
Albany, NY
Binghamton, NY
Utica, NY
Niagara Falls, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reseda, CA
Commerce, CA
North Long Beach,
CA
San Bemadino, CA
El Torn, CA
Cal Transit, CA
Canon, CA
West Long Beach,
CA
HeptMhlor«lJbem»iM«orim(MW.
0.41
2.0
0.11
0.25
0.48
0.29
Niagn Falls, NY
Niagra Falls , NY
Qreenbay, WI
Lot Angeles, CA
Bridgeport, CT
Wallingford, CT
Location
A*.+A*&*ritf---
Urban
Rural
Urban
Urban
Urban
Induitrijtl
Urban
Suburban
Rural
Coastal
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Sampfc
year
87
87
NR
NR
NR
NR
89
89
89
89
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
•425.31)
Urban
Industrial
Urban
Urban
Urban
Urban
86-87
86-87
NR
87
87-88
88
Ref.
9
9
11
11
11
11
12
12
12
12
14
14
14
14
14
14
14
14
1
1
2
3
4
5
Cotantents
next to interstate highway
background site
mostly residential
near freeway
mostly residential
mostly residential
moitly residential
near highway
on she at gaa cooking equipment manufacturer
moitly residential
downwind industrial complex
composite of 2-7 samples
B-151
-------
Table B-14. EarinMHi«nUl Levels »f Dioxins m Air (pg/m1) (continaed)
Chemic*!
1,2,3,4,6,7,8-HpCDD
(continued)
HpCDDt
Number
samples
NR
NR
1
3
2
1
1
1
1
1
1
1
7
1
6
5
7
4
2
2
16
15
7
28
1
Number
positive
sample*
NR
NR
1
3
2
1
1
1
1
1
1
1
7
1
6
5
4
4
2
2
14
15
NR
26
1
Concentration
tinge
NR
NR
0.10
0.52-0.57
0.26-0.52
0.32
0.24
0.1
0.091
0.027
0.012
0.0051
0.11-8.40
2.70
0.21-3.50
0.21-1.20
ND-0.26
0.41-0.87
0.19-0.22
0.30-0.40
ND-0.86
0.24-9.78
0.02-2.19
ND-1.48
0.20
Cone,
mean
0.41
0.04
NA
0.54
0.39
0.32
0.24
0.1
0.091
0.027
0.012
0.0051
2.44
2.70
0.795
0.582
0.138
0.540
0.205
0.351
0.44
2.60
1.02
0.61
0.20
Location
Rutland, VT
Durham, NC
Stockholm, Sweden
Akron, OH
Columbui, OH
Columbus, OH
W.ldo, OH
Stockholm
Stockholm
Stockholm
Stockholm
Bloomington, IN
Reseda, CA
Commerce, CA
North Long Beach,
CA
San Bernadino, CA
B Toro, CA
Cat. Transit, CA
Canon, CA
We* Long Beach,
CA
Niagra Falli, NY
Niagra Falls, NY
Bridgeport, CT
Wallingford, CT
Stockholm, Sweden
Location
description
Urban
Urban
Urban
Industrial
Industrial
Urban
Rural
Urban
Suburban
Rural
Coastal
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Sample
year
NR
NR
89
87
87
87
87
89
89
89
89
86
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
87-88
88
89
Ret.
BO,
6
6
7
9
9
9
9
12
12
12
12
13
14
14
14
14
14
14
14
14
1
1
4
5
7
Comments
near incinerators
near incinerators
next to interstate highway
background site
mostly residential
near freeway
mostly residential
mostly residential
mostly residential
near highway
on site at gas cooking equipment manufacturer
mostly residential
downwind industrial complex
composite of 2-7 samples
B-152
-------
Table B-14. EaTironmeoUd Ler A of Dioxma in Air (pg/m1) .78
ND-5.79
0.39-8.88
Code.
2.0
10.2
1.07
0.70
0.56
0.48
0.44
0.48
0.342
0.525
0.2
0.19
0.062
0.03
4.94
5.30
1.61
1.06
0.246
1.07
0.467
0.739
Octtchtoi
1.14
2.94
Location
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbui, OH
Columbui, OH
Waldo, OH
Albany, NY
Binghamton, NY
Utica, NY
Niagara Falli, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reaeda.CA
Commerce, CA
North Long Beach,
CA
San Bemadino, CA
H Toro, CA
Cal. Transit, CA
Canon, CA
West Long Beach,
CA
txHbenzo^ioxinCMW-
Niagra Falli, NY
Niagra Falli, NY
deicription
Urban
Urban
Induitrial
Industrial
Urban
Rural
Urban
Urban
Urban
Induitrial
Urban
Suburban
Rural
Coastal
Urban
Urban
Urban
Urban
Urban
Urban
Induitrial
Urban
A/Lf\ ^f\
^vV« *O/
Urban
Industrial
Sample
je*t
NR
NR
87
87
87
87
NR
NR
NR
NR
89
89
89
89
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
Ret.
no.
8
8
9
9
9
9
11
11
11
11
12
12
12
12
14
14
14
14
14
14
14
14
1
1
Cointnents.
urban air ft inaide traffic tunnel
downwind incinerator ft induitrial complex
near incinerators
near incinerator!
next to interstate highway
background lite
moitly residential
near freeway
mostly reiidential
moidy residential
mostly residential
near highway
on the at gas cooking equipment manufacturer
mostly residential
downwind induitrial complex
B-153
-------
Table B-14. Environmental Lereh of Dwxim at Air (pg/m*) (continued)
Chemical
1,2,3,4,6,7,8,9-OCDD
(continued)
Number
Mamie*
NR
1
7
16
NR
NR
1
2
2
3
2
1
1
1
3
1
2
2
1
1
1
1
6
5
5
Number
positive
samples
NR
I
NR
IS
NR
NR
1
2
2
3
2
1
1
1
2
1
2
2
1
1
1
1
6
5
5
Coocentntwo
note
NR
1.9
0.17-5.55
ND-29.5
NR
NR
0.23
0.37-4.4
7.4-40
1.00-1.20
0.51-1.10
0.96
0.50
0.053
0.6-3.16
1.35
0.84-1 .58
1.4-1.6
0.23
0.23
0.068
0.041
0.43-17.0
0.68-1.90
0.93-8.60
Cone.
mean
0.30
1.9
2.10
5.53
1.10
0.13
0.23
3.38
23.7
1.13
0.80
0.96
0.50
0.053
1.53
1.35
1.21
1.5
0.23
0.23
0.068
0.041
5.36
1.42
3.08
Location
Greenbay, WI
Lot Angeles, CA
Bridgeport, CT
Wtllingford, CT
Rutland, VT
Durham, NC
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbia, OH
Cohunbui, OH
Waldo, OH
Trout Lake, WI
Albany, NY
Binghamton, NY
Utka, NY
Niagara FaUi, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reseda, CA
North Long Beach,
CA
San Bemadino, CA
Location
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
industrial
Industrial
Urban
Rural
Rural
Urban
Urban
Urban
Imduftri*!
Urban
Suburban
Rural
Coaital
Urban
Urban
Urban
Sample
year
NR
87
87-88
88
NR
NR
89
NR
NR
87
87
87
87
NR
NR
NR
NR
NR
89
89
89
89
87-89
87-89
87-89
Rrf.
• no.
2
3
4
5
6
6
7
8
8
9
9
9
9
10
11
11
11
11
12
12
12
12
14
14
14
Comment*
composite of 2-7 atmple*
urban air A inride traffic tunnel
downwind incinerator & industrial complex
near incinerator*
near incinerator!
next to intentale highway
background site
background rite
mostly residential
near freeway
mostly residential
B-154
-------
Table B-14. EoTiremeoUd Ler* «f Diodn fa Air (M/B*) (cantimed)
r*l>Jimi»*1
V>IWUwrvN. . .
1,2,3,4,6,7,8,9-OCDD
(continued)
Kfi««Amm
X^QUMWf
7
4
2
2
Ntw*et
poJiitiVft
6
4
2
2
CoAttntranW
ND-2.16
1.80-3.73
0.48-1.60
2.05-3.83
Cone.
1.05
2.37
1.04
2.94
: Lttatioa
EJ Toro, CA
Cal. Tranrit, CA
Canon, CA
Wen Long Beach,
CA
Lteation
"HnfiOiiAtM
Urban
Urban
Induftrial
Urban
Staple
... .J** ...
87-88
88-89
88-89
88-89
forf.
14
14
14
14
Contmenu
moctly reiidentUl
near hiffaway
on iite at f ai cookinf equipmeot manufacturer
ntoMly reiidentUl
Fe«tnote RcfenncM
NOTES: Summary rtatiftici provided in or derived from reference*; when reference did not compute mean, h wai computed uring one-half the detection limit for non-detecti;
NA - Not applicable;
ND - Non-detect;
NR » Not reported.
Source*:
1. Smith, et al. (1989).
2. HarkM, et al. (1990).
3. Maiael and Hunt (1990).
4. Hunt and Maiwl (1990).
5. CDEP(1988).
6. Harle** and Lewit (1991).
7. Naf, et al. (1990).
8. Rappe and Kjelkr (1987).
9. Bdferlon, et al. (1989).
10. Ehzer and Kite* (1989).
11. Smith, etal. (1990).
12. fireman, et al. (1991).
13. Ehzer and Kite* (1989).
14. Hunt, et al. (1990).
B-155
-------
TaWeB-15. Environmental Lerds «jf Dibouofanns fat Air
CbwnteaJ
NwnbM
•ttnpt**:
pitttnDef
poattive;
•ample*
Conctntfttioa
ttn£0
Cone.
two..
Ucttfott
t*ng«
Locatkm
description
Sampte
• ytu-'-
ft*f.
no.
CMOttKtt*
T«U*chlorod»*nzQ
-------
Table B-15. EnTironmenUI U»«b of Dibcnmfnran in Air (pg/ar1) (continued)
Chemical
2,3,7,8,-TCDF
(continued)
TCDFi
Number
sample*
2
2
16
16
7
28
1
2
2
3
2
1
1
3
1
2
2
1
1
1
1
7
1
6
Nt»n*tf
positive
sample*
1
2
10
16
NR
26
1
2
2
3
2
0
1
3
1
2
2
1
1
1
1
5
1
4
Concentration
2Vtt£0
ND-0.024
0.019-0.48
ND4.66
0.18-17.4
ND-2.29
ND-0.86
0.33
0.36-6.2
3.3-4.9
0.99-1.50
1.90-3.80
ND(0.13)
0.89
2.08-5.46
0.94
5.87*8.81
1.10-1.20
0.33
0.20
0.08
0.048
ND-1.10
1.40
ND-1.00
Code,
mean
0.0137
0.250
0.23
3.25
0.86
0.38
0.33
3.28
4.1
1.23
2.85
NA
0.89
3.64
0.94
7.34
1.15
0.33
0.20
0.08
0.048
0.275
1.40
0.432
: Location '
• aage
Canon, CA
We* Long Beach,
CA
Niagra Falls, NY
Niagra Falls, NY
Bridgeport, CT
Wallingford, CT
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbus, OH
Columbus, OH
Waldo, OH
Albany, NY
Bingfaamton, NY
Utfc«,NY
Niagra Falli, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reseda, CA
Commerce, CA
North Long Beach,
CA
Location
dMcriptfott
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Industrial
Industrial
Industrial
Urban
Rural
Urban
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sampte
jwwr
88-89
88-89
86-87
86-87
87-88
88
89
NR
NR
87
87
87
87
87-88
88
88
87
89
89
89
89
87-89
87
87-89
Rtf.
no.
14
14
1
1
4
5
7
8
8
9
9
9
9
11
11
11
11
12
12
12
12
14
14
14
Comtaeatt
on rite at gas cooking equipment
manufacturer
mostly residential
downwind industrial complex
composite of 2-7 samples
urban air & inside traffic tunnel
downwind incinerator A industrial complex
near incinerators
near incinerators
next to interstate highway
background site
mostly residential
near freeway
mostly residential
B-157
-------
Table B-15. Environmental Levels of Dibenzofurans in Air (pg/m5) (continued)
Chemical
TCDFs (continued)
Number
samples
5
7
4
2
2
Number
positive
sample*
5
4
2
2
2
Concentration
range
0.024-0.98
ND-0.32
ND-0.87
0.089-0.32
0.15-0.48
Cone,
mean
0.430
0.147
0.418
0.206
0.316
Location
range
Sin Bemadino, CA
El Toro, CA
Cal. Transit, CA
Canon, CA
West Long Beach,
CA
Location
description
Urban
Urban
Urban
Industrial
Urban
Sample
year
87-89
87-88
88-89
88-89
88-89
Ref,
no.
14
14
14
14
14
Comment!
mostly residential
mostly residential
near freeway
on site at gas cooking equipment
manufacturer
mostly residential
1,2,3,7, 8-PeCDF(MW=340.42) :
1,2,3,7,8-PeCDF
3
3
NR
1
7
28
NR
NR
3
2
1
1
7
1
6
5
7
4
0
3
NR
1
NR
9
NR
NR
3
2
0
1
1
1
1
1
2
1
ND(0.01)
0.03-0.61
NR
0.08
ND-0.10
ND-0.02
NR
NR
.026-.033
.032-.057
ND(0.036)
0.021
ND-0.14
0.092
ND-0.13
ND-1.90
ND-0.077
ND-0.053
NA
0.25
0.05
0.08
0.03
0.01
0.03
0.01
0.029
0.044
NA
0.021
0.0327
0.0920
0.0383
0.399
0.0349
0.0346
Niagra Falla, NY
Niagra Falls, NY
Greenbay, WI
Los Angeles, CA
Bridgeport, CT
Wallingford, CT
Rutland, VT
Durham, NC
Akron, OH
Columbus, OH
Columbus, OH
Waldo, OH
Reseda, CA
Commerce, CA
North Long Beach,
CA
San Bemadino, CA
El Toro, CA
Cal Transit, CA
Urban
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Industrial
Urban
Rural
Urban
Urban
Urban
Urban
Urban
Urban
86-87
86-87
NR
87
87-88
88
NR
NR
87
87
87
87
87-89
87
87-89
87-89
87-89
88-89
1
1
2
3
4
5
6
6
9
9
9
9
14
14
14
14
14
14
downwind industrial complex
composite of 2-7 samples
near incinerators
near incinerators
next to interstate highway
background site
mostly residential
near freeway
mostly residential
mostly residential
mostly residential
near highway
B-158
-------
i
i
i
s
i
1
i
g
1
1
I
I
I
I
8
i
1
I
1
i
O)
to
-------
I
A
&
S
I
2 8
I
s
s
n
I
I
1
i
:§
8
I
8
I
s
O
to
I
m
-------
Table B-15. Environmental Lereb of DibtuofanHM in Air (pg/m3) (continued)
f^hA^.jJ.^t
VDOfDJCW •
PeCDFs (continued)
l,2,3,4(7fS-HxeDF
HttfnDtf • •
Samples
7
1
6
5
7
4
2
2
3
3
NR
I
7
28
NR
NR
3
2
1
1
7
1
Nttn&ef
pttftivft
samples
5
1
4
2
4
2
2
2
1
2
NR
1
NR
21
NR
NR
3
2
0
1
1
1
CotK«Mt*ti
-------
Table B-15. Environmental Levels of Dibauofuraaa fai Air (pg/nr1) (continned)
Cheffilcai
1,2,3,4,7,8-HxCDF
(continued)
1,2,3,6,7,8-HxCDF
WWwlNNt-
samples
6
5
7
4
2
2
3
3
NR
1
7
28
NR
NR
1
2
2
3
2
1
1
1
1
Nttttbet
postft*
rtnpte
1
2
2
0
0
0
1
3
NR
1
NR
17
NR
NR
1
2
2
3
2
0
1
1
1
COflttBtrttioa
rang*
ND-0.25
ND-0.18
ND-0.15
ND<0.039-
0.15)
NEX0.038-
0.054)
NDfO.029-
0.085)
ND-0.02
0.05-1.17
NR
0.25
ND-0.15
ND-0.07
NR
NR
0.008
0.03-0.15
0.24-1.4
.048- .092
.092-0.19
ND(0.034)
0.014
0.0078
0.0059
CMC*
mean
0.0574
0.0821
0.0499
NA
NA
NA
0.01
0.45
0.03
NA
0.04
0.03
0.03
0.02
0.008
0.09
0.82
0.065
0.14
NA
0.014
0.0078
0.0059
Location
ttfig6
North Lonf Beach,
CA
San Bemadino, CA
El Tore, CA
Cal. Transit, CA
Canon, CA
Weil Loaf Beach,
CA
Niagra Fall*, NY
Niagra Fall*, NY
Greenbay.WI
Lot Angeles, CA
Bridgeport, CT
Wallingford, CT
Rutland, VT
Durham, NC
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbia, OH
Columbus, OH
Waldo, OH
Stockholm
Stockholm
Loc.ticw
djoscnpfioti
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Industrial
Industrial
Urban
Rural
Urban
Urban
Sampte
J«ar
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
NR
87
87-88
88
NR
NR
89
NR
NR
87
87
87
87
89
89
R*f.
no,
14
14
14
14
14
14
1
1
2
3
4
5
6
6
7
8
8
9
9
9
9
12
12
CoffifflOOU
mostly residential
mostly residential
mostly residential
near highway
on site at gas cooking equipment
manufacturer
mostly residential
downwind industrial complex
composite of 2-7 samples
urban air A inside traffic tunnel
downwind incinerator & industrial complex
near incinerators
near incinerators
next to interstate highway
background site
B-162
-------
Table B-15. EaTironmenUl Levcb of Dibenmfnram in Air (pg/m1) (contained)
CheinJcal
1,2,3,6,7,8-HxCDF
(continued)
1,2,3,7,8,9-HxCDF
Nwnbw
tunptei ••:
1
1
7
1
6
5
7
4
2
2
3
3
NR
1
7
28
NR
NR
1
2
2
3
2
tii.tmhij
jrHnnocf
positive
Ample*
1
1
1
1
1
1
2
0
0
0
0
1
NR
0
NR
1
NR
NR
1
0
1
3
2
C<*tt*M**tioa
iAfl£ft "•• •
0.0024
0.0014
ND-0.80
0.41
ND-0.48
NEM>.37
NEXO.25
ND<0.031-
0.092)
ND(0.030-
0.036)
ND(0.060-
0.070)
ND(.01-.02)
N£M).l
NR
ND(0.08)
NM.02
ND-0.003
ND(0.03)
ND(0.01)
0.0008
ND(.01-.05)
NM.33
.020- .039
.038-0.12
Cone,
town
0.0024
0.0014
0.130
0.410
0.0931
0.0977
0.0689
NA
NA
NA
NA
0.04
0.01
NA
0.01
0.003
NA
NA
0.0008
NA
0.17
0.032
0.079
Ucrtfem
•; . - «»** -
Stockholm
Stockholm
ReKda,CA
Commerce, CA
North Long Beach,
CA
San Bernadino, CA
El Toro, CA
Cal. Transit, CA
Canon, CA
We* Loot Beach,
CA
Niagra Falla, NY
Niagra Falli , NY
Greenbay, WI
Lot Angeles, CA
Bridgeport, CT
Wallingford, CT
Rutland, VT
Durham, NC
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbui, OH
location
description
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Induitrial
Urban
Urban
Induitrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Inductrial
Induitrial
InduMrial
tkuatfo
,.|Wt..
89
89
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
NR
87
87-88
88
NR
NR
89
NR
NR
87
87
ft*£
no.
12
12
14
14
14
14
14
14
14
14
1
1
2
3
4
5
6
6
7
8
8
9
9
Comma**
mostly reiidential
near freeway
moatly residential
moitly residential
mostly residential
near highway
on rite at gai cooking equipment
manufacturer
moitly reiidential
downwind induitrial complex
composite of 2-7 wmplei
urban air A iniide traffic tunnel
downwind incinerator A industrial complex
near incinerators
near incinerators
B-163
-------
Table B-15. Environmental Lerefe of Dibouofaram fa Air (pg/m*) (continued)
Chemical
1,2,3,7,8,9-HxCDF
(continued)
2,3,4,6,7,8-HxCDF
Nutnbtr
samptes
1
1
1
1
1
1
1
7
1
6
5
7
4
2
2
3
3
NR
1
7
28
Namber
positive
... simple*
0
1
1
1
1
1
1
0
0
0
0
0
0
0
0
1
2
NR
0
NR
19
vOttQttittslSott
mnj* . . ..
ND(0.034)
0.097
0.0008
0.0006
0.0003
0.0004
0.0001
ND(0.0040-
0.075)
ND(0.11)
ND(0.010-
0.043)
ND(0.033-
0.21)
ND(0.015-
0.083)
ND(0.0032-
0.068)
ND(0.0054-
0.014)
ND(0.040-
0.086)
ND-0.04
ND-2.17
NR
ND(0.08)
ND-0.30
ND-0.10
Cone,
mean
NA
0.097
0.0008
0.0006
0.0003
0.0004
0.0001
NA
NA
NA
NA
NA
NA
NA
NA
0.02
0.76
ND(.01)
NA
0.09
0.04
Location
Ak0£6
Columbui, OH
Waldo, OH
Stockholm
Stockholm
Stockholm
Stockholm
Bloomington, IN
Reseda, CA
Commerce, CA
North Long Beech,
CA
S«n Bernadino, CA
El Toro, CA
C«l. Transit, CA
Canon, CA
Wert Loot Beach,
CA
Niagra Falli, NY
Niagra Falla, NY
Oreenbay, WI
Lot Angelei, CA
Bridgeport, CT
Wallingford, CT
Loeatkw
deKriptioa
Urban
Rural
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Swnpte
fete •:
87
87
89
89
89
89
86
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
NR
87
87-88
88
«*t
no,
9
9
12
12
12
12
13
14
14
14
14
14
14
14
14
1
1
2
3
4
5
Coountat*
next to interstate highway
background the
mostly residential
near freeway
mostly residential
mostly residential
mostly residential
near highway
on site at gas cooking equipment
manufacturer
mostly residential
downwind industrial complex
composite of 2-7 ssmplei
B-164
-------
Table B-15. EaTiroomentel Lercfc of Dibenaoftiram fa Air (pg/m1) (continued)
Chemical
2,3,4,6,7,8-HxCDF
(continued)
Nwabw
aampfaM
NR
NR
1
2
2
3
2
1
1
1
1
1
1
1
7
1
6
5
7
4
2
2
Ntwrtbef
NR
NR
1
1
2
0
0
0
0
1
1
1
1
1
1
1
1
1
0
0
0
0
1*4*
ND(P.03)
ND(0.01
0.005
ND-0.05
0.21-0.8
ND(.005-.036)
ND(.012-.028)
ND(0.034)
ND(.008)
0.0054
0.0063
0.002
0.0009
0.0016
ND-0.28
0.180
NM.19
NIV0.16
NEK0.018-
0.078)
ND(0.039-
0.103)
ND<0.014-
0.021)
ND(0.035-
0.086)
Cone,
meatt
NA
NA
0.005
0.03
0.50
NA
NA
NA
NA
0.0054
0.0063
0.002
0.009
0.0016
0.0551
0.180
0.0474
0.0584
NA
NA
NA
NA
Location
rang* ..
Rutland, VT
Durham, NC
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Cohimbui, OH
Columbui, OH
Waldo, OH
Stockholm
Stockholm
Stockholm
Stockholm
Bloomingtoa, IN
Reseda, CA _
Commerce, CA
North Long Beach,
CA
San Bernadino, CA
H Toro, CA
Cat. Transit, CA
Canon, CA
West Long Beach,
CA
location
description
Urban
Urban
Urban
Urban
Induitrial
Induitrial
Induitrial
Urban
Rural
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Induitrial
Urban
Sarnpte
NR
NR
89
NR
NR
87
87
87
87
89
89
89
89
86
87-89
87
87-89
87-89
87-88
88-89
88-89
88-89
Ret
no.
6
6
7
8
8
9
9
9
9
12
12
12
12
13
14
14
14
14
14
14
14
14
Comment*
urban air & inside traffic tunnel
downwind incinerator ft induitrial complex
near incinerators
near incinerator!
next to interstate highway
background site
mostly residential
near freeway
moitly residential
moitly residential
mostly residential
near highway
on lite at gai cooking equipment
manufacturer
moitly residential
B-165
-------
Table B-15. Environmental Levels *f
hi Air (pg/B1) (contmoed)
Chemical
HxCDFi
Number
.. ItillpMl..:,,
16
16
7
28
1
2
2
3
2
1
1
3
1
2
2
1
1
1
1
7
1
6
5
7
4
Number
positive
Mmpkf
11
15
NR
28
1
2
2
3
2
1
1
3
0
1
2
1
1
1
1
5
1
4
4
4
3
QQtitt4ilit1|rt$Qft
Ma**....'.
ND-0.58
ND-10.2
ND-2.15
0.03-1.57
0.08
0.18-1.1
2.2-9.5
0.56-0.70
0.37-1.20
0.10
0.51
0.19-0.37
NCHP.09)
ND(0.26)-0.46
0.12-0. IS
0.078
0.062
0.029
0.015
ND-2.00
1.1
ND-1.70
NIW).90
NIW).40
ND-0.84
COOC,
...... mean .
0.14
1.96
0.58
0.49
0.08
0.64
5.85
0.62
0.78
0.10
0.51
0.31
NA
0.295
0.15
0.078
0.062
0.029
0.015
0.415
1.10
0.452
0.606
0.162
.0341
Ixwatto*
ante
Niagn Fans, NY
Niagra Falh, NY
Bridgeport, CT
Waffingford, CT
Stockholm, Sweden
Hamburg , Germany
Hamburg, Oennany
Akron, (HI
Columbus, OH
Cohunbua,OH
Waldo, OH
Albany, NY
Binghamton, NY
Utka,NY
Niagra Falls, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reseda, CA
Commerce, CA
North Long Beach.
CA
San Bemadino, CA
El Tore, CA
Cat. Transit, CA
-------
Table B-15.
it Air (•«/*•*) (c«itiimed)
.,—
HxCDFt (continued)
1,2,3,4,6,7,8-HpCDF
Nutnlwr
wunptoa
2
2
3
3
NR
1
7
28
NR
NR
1
3
2
1
1
1
1
1
1
1
7
1
6
Number
potittv*
•ample*
2
1
1
3
NR
0
NR
22
NR
NR
1
3
2
1
1
1
1
1
1
1
3
1
4
.1*0** '.
0.19-0.27
NIXO.35
ND-0.15
0.26-5.43
NR
ND(0.2)
ND-0.54
ND-0.80
NR
NR
0.09
0.22-0.25
0.20-0.47
0.087
0.22
0.087
0.055
0.028
0.011
0.0035
ND-1.20
0.820
ND-1.10
mwa
.0230
0.200
t f A „ | A. .'it. In^uW
nopncojonx
0.05
2.08
0.08
NA
0.21
0.26
0.12
0.02
0.09
0.24
0.34
0.087
0.22
0.087
0.055
0.028
0.011
0.0035
0.211
0.820
0.276
. U«*jfea
Canon, CA
Wett Long Beach,
CA
Niagra Fall., NY
Niagra Fall., NY
Greenbay, WI
Lot Angeka, CA
Bridgeport, CT
Wallingford, CT
Rutland, VT
Durham, NC
Stockholm, Sweden
Akron, OH
Cohimbua,OH
Columbus, OH
Waldo, OH
Stockholm
Stockholm
Stockholm
Stockholm
Bloonrington
Reseda, CA
Commerce, CA
North Long Beach,
CA
jtm&, ,-i— »a, ,i*t
mduatrial
Urban
Urban
mduatrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
mduatrial
mduatrial
Urban
Rural
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Sarnpfe
88-89
88-89
86-87
86-87
NR
87
87-88
88
NR
NR
89
87
87
87
87
89
89
89
89
86
87-89
87
87-89
Rtf,
: no,
14
14
1
1
2
3
4
5
6
6
7
9
9
9
9
12
12
12
12
13
14
14
14
«_
on rite at gaa cooking equipment
manufacturer
mottly reiidential
downwind induatrial complex
compoaite of 2-7 (ample*
near incinerator*
near incinerator*
next to interstate highway
background aite
mottly reiidential
near freeway
mottly residential
B-167
-------
Table MS. Environment*! Levch of Dibeuofbnwi fa Air (pgW) (coBtnmd)
ChemJeid
1,2,3,4,6,7,8-HpCDF
(continued)
1,2,3,4,7,8,9-HpCDF
NttroW
AunpiM : :
5
7
4
2
2
NR
1
7
28
NR
NR
1
3
2
1
1
1
1
1
1
1
7
1
Kvnft*
' nnAftpm
povPivv
: *amE>Ici
3
1
3
1
1
NR
0
NR
12
NR
NR
0
1
0
0
1
1
1
1
1
1
0
1
Cooe»«fi>lioo
-- M0£ft
NW).47
ND-0.13
ND-1.58
NM.20
ND-0.13
NR
ND(0.02)
NF>0.07
ND-0.30
ND(0.01)
ND(0.01)
ND(0.001)
ND-O.Q31
ND(.015-.028)
ND(P.013)
0.019
0.004
0.0033
0.0014
0.0003
0.0001
ND(0.0062-
0.11)
0.0920
... Coac'
mean
0.254
0.0746
0.497
0.110
0.0733
0.01
NA
0.03
0.03
NA
NA
NA
0.020
NA
NA
0.019
0.004
0.0033
0.0014
0.0003
0.0001
NA
0.0920
j • • IX****
: :-.-. ttOftt'\ . .
San Beraadino, CA
El Tore, CA
Cal. Tranut, CA
Canon, CA
Wert Long Beach,
CA
Oreenbay, WI
Loi Angelei, CA
Bridgeport, CT
Wallingfiml, CT
Rutland, VT
Duiham, NC
Stockholm, Sweden
Akron, OH
Cohunbut, OH
Columbut, OH
Waldo, OH
Stockholm
Stockholm
Stockholm
Stockholm
Bloomington, IN
Reieda, CA
Commerce, CA
Lowrtten
Jt^ ^, fc ^riai it
. IMMBIttjflOn
Urban
Urban
Urban
Induitrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Indiutrial
Induitrial
Urban
Rural
Urban
Urban
Urban
Urban
Urban
Urban
Urban
J*ar
87-89
87-88
88-89
88-89
88-89
NR
87
87-88
88
NR
NR
89
87
87
87
87
89
89
89
89
86
87-89
87
ft*e
no.
14
14
14
14
14
2
3
4
5
6
6
7
9
9
9
9
12
12
12
12
13
14
14
ComtJMait
meetly residential
moMly residential
near highway
on site at gai cooking equipment
manufacturer
moatly residential
composite of 2-7 samples
near incinerators
near incinerators
next to interstate highway
background site
mostly residential
near freeway
B-168
-------
Table B-15. Environmental Levels of Dibenaofnnm m Air (pt/m*) (contined)
Cheated
1,2,3,4,7,8.9-HpCDF
(continued)
HpCDFt
fctkkAMlLhk*
I*WIWR
tamplet
6
5
7
4
2
2
16
16
7
28
1
2
2
3
2
1
1
3
1
2
2
1
Number
» fi dttta
posmve.
staples
1
0
0
2
0
0
12
12
NR
26
1
2
2
3
2
1
1
1
0
1
2
1
Coacentwtiott
rang*
HIM). 11
ND(0.030-
0.12)
ND(0.017-
0.10)
NEMU4
ND(0.024-
0.040)
ND(0.015-
0.043)
NIMK43
ND-8.76
ND-1.0
ND-1.58
0.11
0.1-1.2
2-5
0.37-0.39
0.26-0.64
0.15
0.29
ND-0.65
ND<0.14)
ND(0.41)-0.07
0.13-0.26
0.11
Cone,
mean
0.0397
NA
NA
0.0606
NA
NA
0.13
1.67
0.37
0.47
0.11
0.65
3.5
0.38
0.45
0.15
0.29
0.312
NA
0.138
0.195
0.11
location
'.:•." .'i'lMge.- • :..
North Long Beach,
CA
San Bernadino, CA
El Tore, CA
Cal. Transit, CA
Carson, CA
West Long Beach,
CA
Niagra Falls, NY
Niagra Palls, NY
Bridgeport, CT
Wallingford, CT
Stockholm, Sweden
Hamburg, Germany
Hamburg, Germany
Akron, OH
Columbus, OH
Columbus, OH
Waldo, OH
Albany, NY
Binghamton, NY
Utica, NY
Niagra Falls, NY
Stockholm
Ueatfem
if- -n .Vt .if Jn-rfc
wvtrnpwm
Urban
Urban
Urban
Urban
Industrial
Urban
Urban
Industrial
Urban
Urban
Urban
Urban
Industrial
Industrial
Industrial
Urban
Rural
Urban
Urban
Urban
Industrial
Urban
Sompfe
'"ji*ar"-
87-89
87-89
87-88
88-89
88-89
88-89
86-87
86-87
87-88
88
89
NR
NR
87
87
87
87
87-88
88
88
87
89
ft**.
no,
14
14
14
14
14
14
1
1
4
5
7
8
8
9
9
9
9
11
11
11
11
12
Coinnwau
mostly residential
mostly residential
mostly residential
near highway
on site at gas cooking equipment
manufacturer
mostly residential
downwind industrial complex
composite of 2-7 samples
urban air ft inside traffic tunnel
downwind incinerator A industrial complex
near incinerators
near incinerators
next to interstate highway
background site
B-169
-------
Table B-15. EBvinmmcntal Lenfe of Dibeuofnram ia Air (pg/m1) (coatmaed)
Chemical
HpCDFs (continued)
1,2,3,4,6,7,8,9-OCDF
-." sample* .
1
1
1
7
1
6
5
7
4
2
2
16
15
NR
1
7
28
NR
NR
1
2
2
3
«*rapk»
1
1
1
5
1
4
3
1
3
1
1
11
8
NR
1
NR
18
NR
NR
1
0
2
3
.'. .. ring* ,
0.081
0.036
0.015
ND-1.40
1.80
ND-1.20
ND-0.66
ND-0.13
ND-2.25
ND4.33
ND-0.30
ND-0.22
ND-3.38
NR
0.06
ND-0.56
ND-0.70
NR
NR
0.02
ND<0.11-1.0)
0.78-7.0
0.17-0.19
Cone,
mean
0.081
0.036
0.015
0.288
1.80
0.327
0.822
0.0860
0.724
0.174
0.161
jt*fcntM ntiti i mtitfl
UCcBOulOIW
0.09
0.62
0.07
0.06
0.21
0.21
0.14
0.03
0.02
NA
3.89
0.18
Location
range
Stockholm
Stockholm
Stockholm
Reseda, CA
Commerce, CA
North Long Beach,
CA
San Bernadino, CA
El Tore, CA
Cal. Transit, CA
Canon, CA
West Long Beach,
CA
bettB>farmm
-------
Table B-15. Eanronmcntal L«reti of DibauoraraiH fa Air (pf/m3) (continued)
Chemfcfti
1,2,3,4,6,7,8,9-OCDF
(continued)
Nunjbw
samples
2
1
1
3
1
2
2
1
1
1
1
6
5
5
7
4
2
2
Number
pftrift*
samples
1
0
1
1
0
0
2
1
1
1
1
3
2
3
4
2
1
2
Concentration
xAflfft
ND-0.21
ND(0.16)
0.077
ND(0.93)-0.3
ND(0.3)
ND(0.12-I.10)
0.12-0.18
0.016
0.0072
0.003
0.0009
ND-0.13
ND-0.43
ND-0.29
ND-0.13
ND-2.17
ND-0.12
0.32-0.43
Cone,
: mean .
0.18
NA
0.077
0.312
NA
NA
0.15
0.016
0.0072
0.003
0.0009
0.116
0.152
0.162
0.0756
0.662
0.164
0.374
location
: .. ' tin**- .-.
Columbui, OH
Columbus, OH
Waldo, OH
Albany, NY
Binghamtoa, NY
Utica, NY
Niagra Falls, NY
Stockholm
Stockholm
Stockholm
Stockholm
Reseda, CA
North Long Beach,
CA
San Bemadino, CA
H Toro, CA
Cal. Transit, CA
Carton, CA
We* Long Beach,
CA
Location
Industrial
Urban
Rural
Urban
Urban
Urban
Induatrial
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Urban
Industrial
Urban
Sample
.-•. juiti ':-:
87
87
87
87-88
88
88
87
89
89
89
89
87-89
87-89
87-89
87-88
88-89
88-89
88-89
**£.
m"
9
9
9
11
11
11
11
12
12
12
12
14
14
14
14
14
14
14
Comment*
near incinerator!
next to interstate highway
background site
mostly residential
mostly residential
mostly residential
mostly residential
near highway
on site at gas cooking equipment
manufacturer
mostly residential
Footnote Rcvcrcsictt
NOTES: Summary statistics provided in or derived from references; when reference did not compute mean, ft was computed using one-half the detection limit for non-detecU;
NA - Not available;
NR •* Not reported;
ND = Non-detect.
B-171
-------
Table B-15. Environmental Lev* of DibcnMferaBS fa Air (ng/m>) (continued)
Sources:
1. Smith, etal. (1989). 6. Harleu and Lewii (1991). 11. Smith, etal. (1990).
2. Harien, et al. (1990). 7. Naf, et al. (1990). 12. Broman, et al. (1991).
3. Maiiel and Hunt (1990). 8. Rappe and Kjeller (1987). 13. Eitzer and Hhei (1989).
4. Hunt and Maiiel (1990). 9. Edgerton, et al. (1989). 14. Hunt, et al. (1990).
5. CDEP(1988). 10. Eitzer and Hitei (1989).
B-172
-------
Table B-16. EnTiromnentol Lereb of PCBs in Air (pg/m3)
IUPAC Chemical
Number
118 2,3',4,4',5-PeCB
114 2,3,4,4' ,5-PeCB
105 2,3,3',4,4'-PeCB
Number
samples
143
143
143
Number
positive
•ample*
143
143
143
Concentration
range
NR
NR
NR
Cone.
mean
Penuchlc
2.3
1.2
0.16
Location
>ro-PCB^W«326.44)
Egbert, ON
Egbert, ON
Egbert, ON
Location
description
Rural
Rural
Rural
Sample
year
88-89
88-89
88-89
Ref.
no.
14
14
14
CoukmeiM
He*achloro-PCBCMW-360.88)
156 2,3,3',4,4',5-HxCB
143
143
NR
0.07
Egbert, ON
Rural
88-89
14
Heptachloro-PCB (MW-396.33)
189 2,3,3',4,4',5,5'-HpCB
143
143
NR
0.01
Egbert, ON
Rural
88-89
14
Footnote References
NOTES: Summery lUtinki provided in or derived from reference!; when reference did not compute mean, it wai computed using one-half the detection limit for non-detecU;
NA - not available;
NR = not reported;
ND •= Non-detect.
Sources:
14. Hoff, et al. (1992).
B-173
-------
Chemical
2,3,7,8-TCDD
TCDDs
1,2,3,7,8-PeCDD
PeCDDs
Table B-17. Mean Background Environmental Levels of Dioxins in Soil (ppt)
Number
•ample*
135
43
92
155
65
90
Number
positive
sample*
Concentration
range
Arithmetic
mean*
Geometric
mean*
: Location*
Tetrachlo«Klibenzo-p-dfoxin*(MW«321.98)
19
7
12
13
0
13
ND-7
ND-5
ND-7
ND-120
ND(1.0-55)
ND-120
0.71
0.88
0.62
17.4
22.6
13.6
0.46
0.81
0.36
12.4
14.2
11.3
World Wide
North America
Europe
World Wide
North America
Europe
Ref, no.
1,6,7,10,11
1,6
7.10,11
1,4,6,7,10,11
1,4.6
7,10,11
PcnUchJorodibenzo-p-dioxin» (MW=356.42) =
81
4
77
161
65
96
0,NR
0
NR
20
1
19
ND-2.4
ND(3.75)
ND-2.4
ND-49.9
ND-27.5
ND-49.9
0.33
1.88
0.25
15.86
23.10
10.96
0.28
1.88
0.25
10.97
15.78
8.57
World Wide
North America
Europe
World Wide
North America
Europe
6,11
6
11
1,4,6,7,10,11,14
1.4,6
7,10,11,14
Hexachtorodibenzo-p-dioxjns(MW= 390.87)
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
HxCDDs
4
4
NA
4
4
NA
4
4
NA
155
65
90
0
0
NA
1
1
NA
2
2
NA
18
5
13
ND(3.75)
ND(3.75)
NA
ND-14
ND-14
NA
ND-9.9
ND-9.9
NA
ND-165
ND-99
ND-165
1.88
1.88
NA
4
4
NA
9
9
NA
31.8
26.5
35.6
1.88
1.88
NA
4
4
NA
9
9
NA
28.9
22.5
34.7
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
6
6
NA
6
6
NA
6
6
NA
1,4,6.7.10,11
1.4,6
7,10,11
B-174
-------
Table B-17. Mean Background Environmental Leveb of Dioxins in Soil (ppt) (continued)
Chemical
1,2,3.4,6,7,8-HpCDD
HpCDDs
OCDD
TEQs
for
Number
samples
4
4
NA
187
95
92
185
95
90
Number
positive
samples
4
4
NA
28
15
13
42
29
13
Concentration
range
Heptaehlorodibenz*
37-360
37-360
NA
ND-640
ND-640
ND-234
Octachtorodlbetun
ND-10,600
ND-10,600
ND-832
Arithmetic
mean*
>-p-dio3um (MW=4
194
194
NA
51.4
39.2
63.9
t-p-dioxin (MW*4<
205
237
171
4.51
5.49
0.92
Geometric
mean*
25.31)
194
194
NA
34.9
20.1
61.6
0.76)
96.1
59.9
158
Location*
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Worldwide
North America
Europe
Ref.no. j
6
6
NA
1.4,6,7.10,11.13
1,4,6,13
7,10,11
1,4,6,7,10,11,13
1,4.6.13
7.10,11
B-175
-------
Table B-17. Mean Background EnTironmental Lereb of Dioxins in Soil (ppt) (continued)
Footnote References
" Means were taken from pristine, reference, residential, rural, and agricultural sites.
Industrial, urban, and dump sites were not used because they were assumed to be contaminated.
k Worldwide includes Europe and North America only.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
NA = not applicable, no data found
Sources:
1. EPA (1985)
4. Pearson, et al. (1990).
6. Reed, et al. (1990).
7. Stenhouse and Badsha (1990).
10. Rappe and Kjeller (1987).
11. Greaser, et al. (1989).
13. Birmingham (1990).
B-176
-------
Table B-18. Mean Background Environmental Levels of Dibenzofurans in Soil (ppt)
Chemical
Number
•ample*
Number
positive
Sample*
Cone, rtnge
Arithmetic
BicftnT
Geometric
Location*
Ref. no(»).
Tetnujhlorodibenzofunua(MW=30S.98)
2,3,7,8-TCDF
TCDF.
24
12
12
150
58
92
14
2
12
17
2
15
ND-50
ND-6
3-50
ND-300
ND-280
ND-300
9.29
1.59
17
42.2
54.2
34.5
4.85
1.39
17
33.8
43.0
29.1
Worldwide
North America
Europe
World Wide
North America
Europe
1,6,7
1,6
7
1,4,6.7,10,11
1,4,6
7,10,11
IV»tacMo»dib«tu»fii^
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
PeCDFs
16
4
12
16
4
12
160
62
98
12
0
12
12
0
12
24
3
21
ND-10
ND(3.75)
1-10
ND-5
ND(3.75)
1-5
ND-46.5
ND-27.5
ND-46.5
3.47
1.88
4
1.97
1.88
2
25.35
25.81
25.06
3.31
1.88
4
1.97
1.88
2
22.67
20.22
24.37
World Wide
North America
Europe
WoridWide
North America
Europe
World Wide
North America
Europe
6.7
6
7
6,7
6
7
1,4.6,7,10.11
1,4,6
7.10,11
Hexachtorodibenzofiinuw (MW-374.87)
1,2,3,4,7,8-HxCDF
1,2,3,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6,7,8-HxCDF
HxCDF
4
4
4
4
NA
4
4
NA
4
4
157
0
0
0
0
NA
0
0
NA
1
1
19
ND(3.75)
ND(3.75)
ND(3.75)
ND(3.75)
NA
ND(3.75)
ND(3.75)
NA
ND-7.1
ND-7.1
ND-212
1.88
1.88
1.88
1.88
NA
1.88
1.88
NA
2
2
33.2
1.88
1.88
1.88
1.88
NA
1.88
1.88
NA
2
2
27.2
World Wide
North America
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
World Wide
6
6
6
6
NA
6
6
NA
6
6
1,4,6,7,10,11
B-177
-------
Table B-18. Mean Background Environmental Leveb of Dibenzofurans in Soil (ppt) (continued)
Chemical
HxCDF (cent.)
Number
samples
65
92
Number
positive
sample*
4
15
Cone, range
ND-150
ND-212
Arithmetic
mean*
26.5
37.9
Geometric
mean*
17.7
36.8
Location*
North America
Europe
Ref. no(i).
1,4.6
7,10,11
HepUchlorodibenZofurani (MW»409.3 1)
1,2,3,4,6,7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
HpCDFi
4
4
NA
4
4
NA
157
65
92
4
4
NA
0
0
NA
20
5
15
11-80
11-80
NA
ND(3.75)
ND(3.75)
NA
ND-260
ND-260
ND-138
47
47
NA
1.88
1.88
NA
110
231
25.0
47
47
NA
1.88
1.88
NA
52.1
148.5
24.8
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
6
6
NA
6
6
NA
1,4,6,7,10,11
1,4,6
7,10,11
Oct»chk>itxlib<«2»furafl*(MW««444.76)
OCDFs
TEQs
for
Dibenzofurans
155
65
90
17
4
13
ND-270
ND-270
ND-144
28.4
30.2
27.2
3.37
2.48
2.93
25.2
23.1
26.9
World Wide
North America
Europe
Worldwide
North America
Europe
1,4,6.7,10,11
1.4,6
7.10.11
B-178
-------
Table B-18. Mean Background Environmental Lereb of Dibenzofurans in Soil (ppt) (continued)
Footnote References
* Means were taken from pristine, reference, residential, rural, and agricultural sites.
Industrial, urban, and dump sites were not used because they were assumed to be contaminated.
b Worldwide includes Europe and North America only.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
NA = non-applicable, no data found
Sources:
1. EPA (1985)
4. Pearson, et al. (1990).
6. Reed, et al. (1990).
7. Stenhouse and Badsha (1990).
10. Rappe and Kjeller (1987)
11. Greaser, et al. (1989).
B-179
-------
Table B-19. Mean Background Levels of Dioxins and Dibenzofurans in Water (ppq)
Chemical
Number
samples
Number
positive
samples
Cone, range
Arithmetic
mean*
Geometric
mean*
Location
Rcf.
IKK.).
OctacMorodibenzo-p-dioxin (MW=460.76)
1,2,3,4,6,7 ,8,9-OCDD
1,2,3,4,6,7,8,9-OCDF
TEQs for
Dibenzodioxins
TEQs for
Dibenzofurans
214
214
4
4
22
22
2
2
ND-46
ND-46
achlonxUbenzofurans (
ND-0.8
ND-0.8
3.16
3.16
MW*=444J6)
2.45
2.45
0.0032
0.0032
0.0025
0.0025
2.70
2.70
World Wide
North America
2.24
2.24
World Wide
North America
World Wide
North America
World Wide
North America
1
1
2
2
Footnote References
* Means were taken from treated surface drinking water sample sites.
NOTES: One-half the limit of detection was used in calculating the meani where applicable. Therefore, it is possible to have mean concentrations greater than the range (e.g., reported detection
limit for nondetects greater than the positive sample).
ND = non-detected (limit of detection)
Sources: 1. Jobb, et al. (1990)
2. Meyer, et al. (1989)
B-180
-------
Table B-20. Mean Background Environmental Levels of Dioxuu in Sediments (ppt)
Cbemkat
2,3,7,8-TCDD
TCDDs
Number
(Ample*
25
5
20
27
7
20
Number
positive
Sample!
Concentration
range
Tetnushlotodibenzo-p-
2
0
2
18
2
16
ND-35
ND(4.7-12.7)
ND-35
ND-1400
ND-26
ND-1400
Arithmetic
mean*
Geometric
mean*
(PPt)
Location
Ref. ao(l>
dioxin.(MW=321.98)
25.9
3.16
31.6
252
6.81
338
16.2
2.88
25.0
87.4
2.95
286
World Wide
North America
Europe
World Wide
North America
Europe
1.4,5,13
4.5
1,13
1.3,5,13
3,5
1.13
PenUuMmxfibenzo-p-dioxins (MW«356.42)
PteCDDs
9
7
2
4
2
2
ND-100
ND-12
52-100
20.5
4.66
76
5.52
2.61
76
World Wide
North America
Europe
3.5,13
3.5
13
Hexachtorodibenzo-p-diounf (MW-390.87)
HxCDD»
9
7
2
HpCDDs
6
4
2
6
4
2
*
6
4
2
ND-170
ND-14
120-170
36.6
5.57
145
8.56
3.81
145
Ieptachlorodibeo2o-p-dioMra (MW=425.31)
7.3-210
7.3-110
79-210
95.7
71
145
90.1
71
145
World Wide
North America
Europe
3,5.13
3.5
13
World Wide
North America
Europe
5,13
5
13
B-181
-------
Table B-20. Mean Background Environmental Levels of Dioxins in Sediments (ppt) (continued)
Chemical
Number
samples
Number
positive
samples
Concentration
tutg/t
Arithmetic
mean*
(Ppt)
Geometric
mem*
(Ppt)
Location
Ref, nofr)'
Octachbrodib«t7x>-p-dio)un(MW===460.76) : .
OCDD
TEQs
for
Dibenzodioxins
27
7
20
12
7
5
ND-600
54-600
ND-250
131
439
22.5
26.0
3.60
31.6
22.5
364
8.51
World Wide
North America
Europe
World Wide
North America
Europe
1,3,5.13
3,5
1,13
Footnote References
* Means were taken from pristine, reference, residential, rural, and various location sites.
Industrial, urban, and dump sites were not used because they were assumed to be contaminated.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
ppt = Parts per trillion
Sources:
1. Koistinen et at. (1990)
3. Czuczwa et al. (1984)
4. Norwood et al. (1989)
5. Reed et al. (1990)
13. Rappeetal. (1989a)
B-182
-------
Table B-2I. Mean Background EnTironmental Lerds of Dibenzofurans in Sediments (ppt)
Chcoucn!
Number
Munpfai
Number
positive
wtnplcv
Cone.
range :
AnUnnetio
. mestf
GA>«*Mfr
nwtn*
: ." . 1 Locat«>B:':.
R«f.BO(»>- ..
i Tetnw)hlon)dibcnzofiiran»(MW=305,98) , : •
2,3.7,8-TCDF
TCDFs
25
5
20
9
7
2
4
2
2
6
4
2
ND-35
ND-15
ND-35
ND-130
ND-18
87-130
26.7
3.06
32.6
28.0
4.86
109
11.7
0.23
31.2
2.16
0.7
109
Worldwide
North America
Europe
World Wide
North America
Europe
1,4,5,13
4,5
1,13
3,5,13
3,5
13
Pcntachlorodlb«nzofijirwu(MW*340.42)
PfcCDF*
9
7
2
6
4
2
ND-125
ND-25
66-125
25.4
5.26
96
7.25
3.26
96
World Wide
North America
Europe
3,5.13
3.5
13
He»chlorodibenzofuran»{MW«374.87)
HxCDFs
9
7
2
5
3
2
ND-150
ND-12
78-150
27.1
2.31
114
4.55
1.81
114
World Wide
North America
Europe
3.5,13
3.5
13
: H«ptachlorodiben7Mfurww(MW=409.31)
HpCDFs
6
4
2
5
3
2
ND-180
ND-30
79-180
54.0
16
130
32.2
16
130
World Wide
North America
Europe
5,13
5
13
B-183
-------
Table B-21. Mean Background Enrironmental Lereb of Dibenzofurans in Sediments (ppt) (continued)
Chemical
OCDF
TEQs
for
Dibenzofurans
Number
samples
27
7
20
Number
positive
•ample*
8
4
4
Cone.
rang*
Arithmetic
mean*
Geometric
mean*
OcUchlorodfoenzofuran* (MW=444,76)
ND-160
ND-23
ND-160
10.6
4.50
12.8
2.68
0.31
3.27
8.72
3.98
11.5
Location
World Wide
North America
Europe
World Wide
North America
Europe
Ref. RO(*}>
1,3.5,13
3,5
1,13
Footnote References
* Means were taken from pristine, reference, residential, rural, and various location sites.
Industrial, urban, and dump sites were not used because they were assumed to be contaminated.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
ppt = Parts per trillion
Sources:
1. Koistinen et al. (1990)
3. Czuczwa et al. (1984)
4. Norwood et al. (1989)
5. Reed et al. (1990)
13. Rappe et al. (1989a)
B-184
-------
Table B-22. Mean Background EnTironmental Levels of PCBs in Sediment (ppt)
ItfPAC
number Chemical
Number
samples
Number
poiitive
sample*
Concentration
range
Arithmetic
mean*
Geometric
mean*
Tetan?hloriH»CB(MW«»1.99)
77 3,3>4,4t-TeCB
81 3,4,4'5-TeCB
19
NR
18
NR
NR
13
NR
13
NR
NR
ND-550
ND(500)
ND-550
ND(500)
ND(500)
143.61
250
137.7
250
250
pentachloro-PCB (MW»326.44)
126 3,3',4,4',5-PeCB
105 2,3,3',4,4>-PeCB
114 2,3,4,4',5-PeCB
118 2,3,4,4',5-PeCB
19
NR
18
49
39
10
NR
NR
38
1
1
NR
1
10
NR
10
NR
NR
NR
0
ND-110
ND(500)
ND-110
ND-10,000
NR
52-120
NR
NR
0.01-15.000
11,000-15,000
0.01
13.26
250
6.1
7893.14
9892.31
96.4
1000
1000
14,1897.44
14,897.44
0.01
142
250
137.7
250
250
7.42
250
6.1
3834.95
9861.3
96.4
1000
1000
14,881.18
14,881.18
0.01
Location
Work! Wide
North America
Europe
World Wide
North America
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
World Wide
North America
Europe
Ref. n«X«).
1.16
16
1
16
16
1.16
16
1
1,7,16
7,16
1
16
16
7.16,17
7,16
7,16.17
HewwbtonHPCB (MW=360,88)
156 2,3,3',4,4',5-HxCB
38
NR
1700-2100
1700-2100
2089.7
2089.7
2088.7
2088.7
World Wide
North America
7,16
7,16
B-185
-------
Table B-22. Mean Background Environmental Levels of PCBs in Sediments (ppt) (continued)
IUPAC
number Chemical
167 2,3',4,4I,5I5'-HxCB
169 3.3',4,4>,5.5'-HxCB
Number
samples
NR
NR
18
NR
18
Number
positive
samples
NR
NR
0
NR
0
Concentration
range
ND(500)
ND(500)
ND(36-500)
ND(500)
ND(36)
Arithmetic
mean*
250
250
30.21
250
18
Geometric
mean*
250
250
20.67
250
18
Location
World Wide
North America
World Wide
North America
Europe
Ref, no(s).
16
16
1.16
16
1
: = HepUchtero-PCB(MW«396.33)
189 2,3,3',4,4'.5,5>-HpCB
NR
NR
NR
NR
ND(500)
ND(500)
250
250
250
250
World Wide
Europe
16
16
Footnote References
* Means were taken from various location sites. Industrial and urban sites were not used because they were assumed to be contaminated.
NOTES: One-half the limit of detection was used in calcukting the means where applicable.
NR = Not Reported
ND = Not Detected (detection limit)
ppt = Parts per trillion
Sources:
1. Koistinen et al. (1990)
7. Oliver and Nilmi (1988)
9. Huckins et al. (1988)
16. Smith et al. (1990)
B-186
-------
Table B-23. Mean Background EnTironmental Levels of Dioxins in Finfbh (ppt)
..-V*>/,-Jf ^^;^:':
;VO:^;<^SS^
Number
:x- *ample»
Number
powtive
wmpka
Cone, range
Arithmetic
meuf
Geometric
mean*
H Loeatfoflf
Ref. no(i).
" "^ ; : • ?ff Eft :^^v * nl- = •• • -: . ; ! . t«nWhtenxfibetao^MJ^ (MW-32U98)
2,3,7,8-TCDD
61
60
1
14
14
0
ND-2.26
ND-2.26
ND(O.OS)
0.343
0.348
0.025
0.263
0.273
0.025
World Wide
North America
Europe
5,20
20
5
;:A ^?; ;%gf;-HK'Vr.: . ../ . .<= . IVnudiJorodibemo^MlioxiMCMW-SSe^) . .= -
1,2,3.7,8-FteCDD
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
61
60
1
59
60
1
61
60
1
61
60
1
5
4
1
Hex*
3
3
0
11
11
0
1
1
0
ND-0.3
ND-0.29
0.3
chkwodibenzo-p-di
ND-0.35
ND-0.35
ND(0.1)
ND-1.79
ND-1.79
ND(0.1)
ND-0.17
ND-0.17
ND(O.l)
0.411
0.413
0.3
MUM (MW*B390*S<
0.566
0.575
0.05
0.597
0.606
0.05
0.478
0.485
0.05
0.369
0.370
0.3
r>
0.509
0.529
0.05
0.536
0.558
0.05
0.441
0.457
0.05
World Wide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
5,20
20
5
5,20
20
5
5,20
20
5
5,20
20
5
B-187
-------
Table B-23. Mean Background Environmental terete of Dioxins in Finfish (ppt) (continued)
Chemical
Number
samples
Number
positive
samples
Cone, range
Arithmetic
mean*
Geometric
mean*
Location*
Ref. m>(«)<
Hej)tachlorodibciizo-|KlioMns(MW»425.31)
1,2,3,4,6,7,8-HpCDD
59
58
1
27
27
0
ND-4.08
ND-4.08
ND(0.1)
1.547
1.573
0.05
1.122
1.184
0.05
World Wide
North America
Europe
5.20
20
5
Octachlorodibenzo-|Maoxin(MW=460J6)
1,2,3,4,6,7,8,9-OCDD
TEQs
for
Dibenzodioxins
1
1
1
1
0.55
0.55
0.55
0.55
0.729
0.737
0.191
0.55
0.55
World Wide
Europe
World Wide
North America
Europe
5
5
Footnote Reft
* Whole fish concentrations were divided in half to obtain the mean concentrations (USEPA, 1990; Branson et al., 1985).
k Worldwide includes North America and Europe only.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (Emit of detection);
Sources: 5. Rappe, et al. (1989)
20. USEPA (1992)
B-188
-------
Table B-24. Mean Background Environmental Lereb of Dibenzofurans in Finfish (ppt)
— <
2,3,7,8-TCDF
twrapka
61
60
1
Number
positive
«wnpk»
Tfl
33
22
1
c^
0.1-13.73
ND-6.87
0.85
Arithmetic
u»(MW=305,98)
0.734
0.732
0.85
OoDitictn6
mean*
0.425
0.420
0.85
Location*
World Wide
North America
Europe
R«t no(»).
5,20
20
5
P*ntachtorodiben»ftlr*nl(MWw340,42)
1,2,3,7,8-PeCDF
2,3.4,7,8-PeCDF
61
60
1
61
60
1
9
8
1
16
15
1
ND-0.95
ND-0.95
0.2
ND-1.5
ND-0.7
1.5
0.253
0.254
0.2
0.286
0.266
1.5
0.219
0.220
0.2
0.245
0.237
1.5
World Wide
North America
Europe
World Wide
North America
Europe
5,20
20
5
5,20
20
5
Hexachtortxtlb««»furam{MW**374.87) .
1,2,3,4,7,8-HxCDF
1,2,3,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
61
60
1
61
60
1
60
60
4
3
1
2
1
1
0
0
ND-0.62
ND-0.62
0.1
ND-0.068
ND-0.68
0.05
ND(0. 13-2.78)
ND(0. 13-2.78)
0.534
0.541
0.1
0.528
0.536
0.05
0.534
0.534
0.446
0.458
0.1
0.434
0.450
0.05
0.443
0.443
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
5,20
20
5
5,20
20
5
20
20
B-189
-------
Table B-24. Mean Background Environmental Leveb of Dibouofnnuu in FinfBh (ppt) (continued)
Chemical
2,3,4,6,7,8-HxCDF
Number
sample*
61
60
1
1,2.3,4,6,7,8-HpCDF
59
58
1
Number
positive
samples
2
2
0
Cone, range
ND-0.63
ND-0.63
ND(0.2)
Arithmetie
mean*
0.402
0.408
0.05
Geometric
mean"
0.347
0.359
0.05
HcptAchlorodibcnzoftJnuB(MW-409Jl)
8
8
0
1,2,3,4,6,7,8,9-OCDF
TEQs
for
Dibenzorunns
1
1
0
0
ND-0.94
ND-0.94
ND(0.2)
iachlorodibenzorura
ND(0.2)
ND(0.2)
0.568
0.577
0.05
' -
0.05
0.435
0.427
0.866
0.481
0.500
0.05
u—
World Wide
North America
Europe
Ref, 00(1),
5,20
20
5
World Wide
North America
Europe
5,20
20
5
0.05
0.05
World Wide
Europe
World Wide
North America
Europe
5
5
Footnote References
• Whole fish concentrations were divided in half to obtain the mean concentrations (USEPA, 1990; Branson et •!., 1985).
* Worldwide includes North America and Europe only.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
Sources: 5. Rappe, et al. (1989)
20. USEPA (1992)
B-190
-------
Table B-25. Mean Background Level* of Mums fa Food Prodncts (wet wt. ppt)
Chemkal
2,3,7,8-TCDD
: Staple .
lyp®
Milk
Milk
Milk
Dairy products
Dairy products
Dairy products
Eggs
Eggs
Egg*
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Number
samples
21
1
20
25
5
20
9
8
1
22
14
8
16
12
4
12
9
3
Number
positive
samples
TdjrBCD«0w?
2
1
1
3
2
1
1
0
1
6
6
0
2
1
1
5
4
1
COHC.
«*.*
[fibeiizo-p-diaxii»(MV
ND-0.063
0.0018
ND-0.063
ND-0.26
ND-0.07
ND-0.26
ND-0.02
NDCO.01-0.03)
0.02
ND-0.062
ND-0.062
NDCO.015-0.05)
ND-0.03
ND-0.013
ND-0.03
ND-0.25
NM.25
ND-0.045
Ariftmetic
metoF
r-321.9«)
0.010
0.0018
0.011
0.103
0.031
0.121
0.011
0.01
0.02
0.027
0.026
0.029
0.048
0.018
0.195
0.05
0.055
0.040
mean5
0.009
0.0018
0.010
0.072
0.018
0.102
0.011
0.01
0.02
0.022
0.021
0.025
0.017
0.010
0.147
0.032
0.030
0.040
Location •
•; ..... . •;; . _. :;
Worldwide
North America
Europe
WoridWide
North America
Europe
Worldwide
North America
Europe
WoridWide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
':=w,"
• • ItefL
«*.<•>
••"••i •'••:.:. .-.•• ' •"
2,3,4,5,7
4
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
4,5,8,11,12
4,11,12
5,8
4,3,5,11,12
4,11,12
3,5
3,5,11,12
11,12
3,5
B-191
-------
Table B-25. Mean Background Levels of Dwxms fat Food Prodncts (wet wt ppt) (continued)
Chemical
Sample:
1,2,3,7,8-PeCDD
1,2,3,4,7,8-HxCDD
Milk
Milk
Dairy product!
Dairy product!
Dairy product!
Egg,
Egg.
Eggi
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Milk
Number
•ample*
Number
positive
Penttchlonx
20
20
25
5
20
9
8
1
19
11
8
13
9
4
12
9
3
13
8
8
6
5
1
1
0
1
10
3
7
2
1
1
3
0
3
Hexaehlorod
2
Cone. „:-..
b
ft>«nzo^>-dio»rui(MW
ND-0.082
ND-0.082
ND-0.33
0.01-0.2
ND-0.33
ND-0.04
MXO.04-0.4)
0.04
ND-0.87
ND-0.208
ND-0.87
ND-0.018
ND-0.041
ND(0.075)-0.018
ND-0.18
ND(0.011-1.11)
0.105-0.18
. Arithmetic
aearf
' ~ 326.44)
0.029
0.029
0.166
0.11
0.18
0.077
0.081
0.04
0.224
0.221
0.23
0.119
0.158
0.033
0.117
0.111
0.14
ib.nz^Jioxin^MW - 390.87)
ND-0.66
0.028
Geometric
me*nc
0.027
0.027
0.133
0.078
0.15
0.061
0.065
0.04
0.111
0.082
0.17
0.087
0.138
0.032
0.062
0.048
0.13
0.027
Location
World Wide
Europe
Worldwide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
World Wide
Kef.
2,3,5,7
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11,12
11,12
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3,5
2,3,5
B-192
-------
Table B-25. Mean Background Leveb of Dioxins in Food Products (wet wt. ppt) (continued)
Chemical
1,2,3,4,7,8-HxCDD
(continued)
1,2,3,6,7,8-HxCDD
Sample
; iw**
Milk
Dairy producU
Daiiy producti
Dairy product*
Egg*
Egg*
Egg*
Beef and veal
Beef
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Milk
Milk
Dairy producU
Dairy producti
Number
•ample*
13
25
5
20
9
8
1
8
3
8
4
1
4
3
1
3
13
13
25
5
Number
positive
tample*
2
17
5
12
1
0
1
7
3
7
1
1
1
2
0
2
12
12
20
5
Cone. ••
rangeb
ND-0.66
ND-0.29
0.017-0.29
ND-0.20
ND-0.13
NDCO.08-0.67)
0.13
ND-1.981
0.03-1.981
ND-0.87
0.032-0.282
0.282
0.032-0.038
ND-0.12
ND(0.04)
ND-0.12
ND-O.33
ND-0.33
ND-1.72
0.07-1.72
Arithmetic
mean'
0.028
0.117
0.107
0.119
0.15
0.16
0.13
0.374
0.836
0.20
0.086
0.282
0.037
0.044
0.04
0.085
0.11
0.11
0.418
0.690
GootMinc-
mean*
0.027
0.093
0.063
0.103
0.14
0.14
0.13
0.172
0.309
0.14
0.0282
0.282
0.036
0.070
0.040
0.085
0.10
0.10
0.327
0.451
Location
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
Europe
World Wide
North America
JterV
*>.<«>
2,3,5
3,5,8,10
10
3,5,8
3,11
11
3
5,8,12
12
5,8
3,5,12
12
3,5
3,5,12
12
3,5
2,3,5
2,3,5
3,5,8,10
10
B-193
-------
Table B-25. Mean Background Levels of Dknrins fat Food Products (wet wt. fpt) (contnmed)
. v-j m,tW
•"'. /.;..V-.: ;.?!:•- K;*i -:R :;:'
; "" "H"-:-. "-V;:k:l;:::->
1,2,3,6,7,8-HxCDD
(continued)
1,2,3,7,8,9-HxCDD
::::-:":'-!'J'3*BO|»Ift...-.
.:;;:.• type* ;
Dairy products
Eggs
Egg!
Egg!
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Milk
Milk
Dairy products
Dairy products
Dairy products
Eggi
Eggs
Number
sample*
20
9
8
1
16
8
8
12
8
4
11
9
3
20
20
25
5
20
1
1
Number
positive
samples
15
1
0
1
8
0
8
1
0
1
5
2
3
2
2
17
5
12
1
1
; Cone.
: range"
ND-0.81
ND-0.14
ND(0.07-0.56)
0.14
ND-1.14
ND(0. 14-0.78)
0.018-1.14
ND-0.044
ND.<«>
3,5,8
3,11
11
3
5,8,11
11
5,8
3,5,11
11
3,5
3,5,11,12
11,12
3,5
2,3,5,7
2,3,5,7
3,5,8,10
10
3,5,8
3
3
B-194
-------
Table B-25. Mean Background Lercfc «f Dknrins fa Food Products (wet wt. ppt) (continued)
.:" Chemical !£."
1,2,3,7,8,9-HxCDD
(continued)
Sample
: :.'! ***«
Beef and veal
Beef and veal
Beef and veal
Pott
Pork
Pork
Chicken
Chicken
Chicken
Number
•ample*
19
11
8
13
9
4
12
9
3
Number
positive
•ample*
10
3
7
2
1
1
5
2
3
: Cone.
i i»ngeb
ND-0.86
ND-0.616
ND-0.86
0.009-0.282
ND-0.282
0.009-0.038
ND-4.3
ND-4.3
0.075-0.090
Arithmetic
meanc
0.205
0.206
0.20
0.093
0.121
0.031
0.153
0.174
0.090
Geometric *
mea&c
0.135
0.134
0.14
0.067
0.102
0.027
0.098
0.101
0.090
Location
World Wide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
Ref.
*>-{«>
5,8,11,12
11,12
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3,5
: HepUchlorodibenzo-p-dioxin»(MW » 425.31) !
1,2,3,4,6,7,8-HpCDD
Milk
Milk
Dairy products
Dairy product*
Dairy product*
Egga
Egg*
Egg»
Beef and veal
Beef and veal
20
20
25
5
20
9
8
1
19
11
13
13
25
5
20
1
0
1
18
10
ND-0.96
ND-0.96
0.24-5.88
0.18-5.88
0.24-1.38
ND-0.04
ND(0.08-0.42)
0.04
ND-12.065
ND-12.065
0.13
0.13
1.139
2.162
0.883
0.10
0.11
0.04
1.446
1.925
0.10
0.10
0.895
1.307
0.814
0.097
0.11
0.04
0.840
0.959
World Wide
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
2,3,5,7
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11,12
11,12
B-195
-------
Table B-25. Mean Background Lereb of Dianas fat Food Products (wet wt. ppt) (continued)
Chemical
1,2,3,4,6,7,8-HpCDD
(continued)
Sample
type*
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Number
•ample*
8
13
9
4
12
9
3
Number
positive
Munplef
8
10
9
1
11
8
3
Coot.
nnge*
0.156-2.97
ND-8.197
0.46-8.197
ND-0.32
ND-5.28
ND-5.28
0.68-0.90
Arithmetic
mean6
0.79
1.881
2.647
0.16
0.975
1.049
0.75
O0OQMSfriC
«W:'."
0.70
0.758
1.611
0.14
0.522
0.463
0.75
Location
Europe
Worldwide
North America
Europe
Worldwide
North America
Europe
Ret
«»-{«)
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3,5
OctacWoitxlibaizo-p-
-------
Table B-25. Mean Backgnmnd Levels of Dioxms in Food Products (wet wt. ppt) (contimwd)
: Chemka!
1,2,3,4,6,7,8,9-OCDD
(continued)
TEQ»
for
Dibenzodioxini
- Sample
type*
Pork
Chicken
Chicken
Chicken
Milk
Milk
Milk
Dairy products
Dairy products
Dairy products
Egg§
Eggi
E««»
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Number
•ample*
4
12
9
3
Number
positive
•aifi|M£ff
4
11
8
3
""'':" Coiaii>.';" -'::'.
; nageb
0.81-2.85
ND-14.4
ND-14.4
2.1-7.8
ArManetic
: me*?
1.64
4.248
4.246
4.25
0.0421
0.0018,0.12d
0.0431
0.2714
0.2029
0.2873
0.0842
0.0812
0.0736
0.2473
0.2892
0.2341
0.1692
0.1979
0.2255
0.2298
uoomotno
mean*
1.52
2.223
1.887
3.63
0.12"1
Location
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
Ref.
*».<«>
3,5
3,5,11,12
11,12
3,5
B-197
-------
Table B-25. Mean Background Levels of Dioxnu in Food Products (wet wt. ppt) (continued)
Chemical
TEQs
for Dibenzodioxini
Sample
type'
Chicken
Chicken
Number
samples
Number
positive
•ample*
Cone.
-»*»
Arithmetic
mean?
0.1587
0.1713
Geometric
mean6
Location
North America
Europe
Ret
«>.{«)
Footnote References
* Dairy product* include butter, chee*ea, and cow cream.
Samples analyzed on a fat weight basil were adjusted to a wet weight basis by multiplying the value by the percentage of fat contained in the sample: beef, 19.0; butter, 11.0;
cheese, 33.0; chicken, 15.0; cow cream, 37.0; egga, 10.0; milk, 3.3; pork, 15.0; Swiss cheese, 27.0; and veal, 6.7 (USDA, 1979-1984).
0 Means were taken from all sites except near incinerators, South Vietnam, and pork samples from the USSR because, the sites were possibly contaminated.
d Value was reported as total 2,3,7,8-TCDD toxic equivalents (U.S., EPA 1991b).
NOTES: One-half the limit of detection was used in calculating the means where applicabk. Therefore, it is possible to nave mean concentrations greater than the range (e.g., reported detection limit for nondetects greater than
the positive sample).
ND «= not detected (limit of detection)
Sources: 2. Rappe et al. (1987)
3. Beck et al. (1989)
4. LaReuretal. (1990)
5. Furatetal. (1990)
7. Startin et al. (1990)
S. Schecter et al. (1990)
10. Schecter et al. (1992)
11. Stanley and Bauer (1989)
B-198
-------
Table B-26. Mean Background Leveb of Dibeniofann m Food Products (wet wt. apt)
Chemical
2,3,7,8-TCDF
Sample
Milk
Milk
Milk
Dairy product*
Dairy product*
Dairy product*
Egg*
Egg*
Egg*
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Number
sample*
21
1
20
25
5
20
9
8
1
22
14
8
16
11
4
12
9
3
rvutxtbcc
JMMtttVB
•ample* '•
Tetrachloroc
3
0
3
10
5
5
2
1
1
9
7
1
5
4
1
5
2
3
COM*
libeozoiunn*•:.;
2,3,4,5,7
4
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
4,5,8,11,12
4,11,12
5,8
3,4,5,11,12
4,11,12
3,5
3,5,11,12
11,12
3,5
B-199
-------
Table B-26. Mean Background Lereb of Dibenzofuran* ia Food Frodncts (ppt) (continued)
Chemical
Sampfe
'\*n* ' .
Number
•ample*
Number
pOMttVG
tamp leg
Cone*
Range*
•Aflnunelio
mean*
Geometric ..
mean*
location4
Rrfl :.
«»<•>• ;
: := PenUchlorodibenzoniran*(MW » 340.42) .
1,2,3,7,8-PeCDF
Milk
Milk
Dairy product!
Dairy product*
Daiiy product*
Eggs
Egg«
Egg«
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
20
20
25
5
20
9
8
1
19
11
8
13
9
4
12
9
3
3
3
5
1
4
1
0
1
2
1
1
2
1
1
2
0
2
ND-0.043
ND-0.043
ND-0.212
ND-0.04
ND-0.212
ND-0.06
ND(0.01-0.1)
0.06
ND-0.028
ND-0.01
ND-0.028
ND-0.009
ND-0.009
ND-0.002
ND^.18
ND(0.018-0.1)
ND-0.18
0.009
0.009
0.077
0.022
0.088
0.027
0.023
0.06
0.032
0.043
0.016
0.037
0.046
0.017
0.032
0.019
0.071
0.008
0.008
0.057
0.016
0.073
0.021
0.021
0.06
0.017
0.019
0.014
0.027
0.038
0.012
0.017
0.015
0.028
World Wide
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Worid Wide
North America
Europe
Worid Wide
North America
Europe
2,3,5,7
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11,12
11,12
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3,5
B-200
-------
Table B-26. Mean Background Levels of Dibenzofurans in Food Prodncts (pat) (continned)
Chemical
2,3,4,7,8-PeCDF
Sample
ty^8
Milk
Milk
Dairy product!
Dairy product*
Dairy products
Eggs
Eggs
Egg*
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Number
•ample*
1O
20
25
5
20
9
8
1
19
11
8
13
9
4
12
9
3
Number
• . positive
staples
20
20
20
5
IS
1
0
1
11
3
8
2
1
1
4
1
3
Cone*
R*ngeb
0.028-0.15
0.028-0.15
ND-1.431
0.02-0.25
ND-1.431
ND-0.08
ND(0.01-0.07)
0.08
ND-1.783
ND-1.783
0.18-0.74
ND-0.039
ND-0.039
ND(0.045)-0.012
ND-0.30
ND-0.01
0.105-0.30
Anthtncfic,
mean6
0.066
0.066
0.549
0.132
0.653
0.023
0.016
0.08
0.317
0.211
0.46
0.037
0.045
0.020
0.066
0.018
0.21
Geometric
meanc
0.059
0.059
0.368
0.098
0.512
0.019
0.015
0.08
0.145
0.064
0.44
0.032
0.041
0.019
0.030
0.015
0.21
. Location*1
World Wide
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Itef.
*><•>• :
2,3,5,7
2,3.5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11,12
11,12
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3,5
: Hex»cWorodibenzofuram(MWw374.87) :' :
1,2,3,4,7,8-HxCDF
Milk
20
20
0.013-0.099
0.037
0.032
World Wide
2,3,5,7
B-201
-------
Table B-26. Mean Background Lereb of Dibenzofnnms in Food Products (ppt) (continued)
r -•";v''4^MSk^--
l,2,3,4,7,S-HxCDF
(continued)
l,2,3,6,7,S-HxCDF
:.:|:;.:...:.lSampk.. '
i^i type*
Milk
Dairy product*
Dairy product!
Dairy producti
Egg§
Egg*
Egg*
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Milk
Milk
Dairy product*
Number
•ainpiM
20
25
5
20
9
(
1
19
11
8
13
9
4
12
9
3
20
20
25
Number
<•• pOHQVB
Maple*
20
10
5
5
1
0
1
8
3
5
2
1
1
3
1
2
20
20
10
"-Cooo*
; R«ngeb
0.013-0.099
ND-2.014
0.06-0.93
ND-2.014
ND-0.04
ND(0.04-0.25)
0.04
ND-4.846
ND-4.846
ND-0.41
ND-0.108
ND-0.108
ND-0.022
ND-0.28
NEMK009
ND-0.28
0.009-0.066
0.009-0.066
ND-0.57
Anttuwtic
mean4
0.037
0.449
0.450
0.449
0.069
0.073
0.04
0.365
0.51
0.17
0.086
0.115
0.022
0.058
0.035
0.13
0.026
0.026
0.255
Geometric •
mean*
0.032
0.313
0.332
0.309
0.061
0.065
0.04
0.122
0.099
0.16
0.057
0.088
0.022
0.044
0.031
0.13
0.023
0.023
0.184
Location*1
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
WoridWide
North America
Europe
WoridWide
North America
Europe
WoridWide
North America
Europe
World Wide
Europe
World Wide
Ret r
*X»' ;
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11
11
5,8
3,5,11
11
3,5
3.5,11
11
3,5
2,3,5,7
2,3,5,7
3,5,8,10
B-202
-------
Table B-26. Mean Background Levels of Dibenioforans in Food Products (ppt) (continned)
Chemical
1,2,3,6,7,8-HxCDF
(continued)
1,2,3,7,8,9-HxCDF
: Sample
•
-------
Table B-26. Mean Background Lereb of Dibenzoforans in Food Products (ppt) (continued)
Chemical
1,2,3,7,8,9-HxCDF
(continued)
2,3,4,6,7,8-HxCDF
Sample
«n»*
Eggi
Egg*
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Chicken
Chicken
Milk
Milk
Dairy product*
Dairy producti
Dairy product*
Eggs
Eggs
Egg»
Beef and veal
Beef and veal
Number
aampief
8
8
12
11
1
9
9
9
9
20
20
25
5
20
9
8
1
19
11
Number
poutive
•amplet
0
0
0
0
0
0
0
0
0
19
19
10
5
5
1
0
1
8
3
: Cone*
Ringe*
ND(0.05-0.58)
ND(0.05-0.58)
ND(0.002-0.29)
ND(0.002-0.29)
ND(0.005)
ND(0.076-0.16)
ND(0.076-0.16)
ND(0.012-0.14)
ND(0.012-0.14)
ND-0.073
ND-0.073
ND-0.57
0.01-0.15
ND-0.57
ND-0.17
ND(0.04-0.52)
0.17
ND-0.34
ND-0.177
AnthtDBtto
taetaf
0.13
0.13
0.053
0.058
0.005
0.056
0.056
0.040
0.040
0.028
0.028
0.247
0.096
0.285
0.12
0.12
0.17
0.109
0.072
Geometric
mean*
0.092
0.092
0.024
0.028
0.005
0.032
0.032
0.044
0.044
0.024
0.024
0.168
0.069
0.209
0.087
0.080
0.17
0.080
0.058
Location^
World Wide
North America
WoridWide
North America
Europe
Worldwide
North America
WoridWide
North America
World Wide
Europe
WoridWide
North America
Europe
World Wide
North America
Europe
World Wide
North America
.*?£..
•»<#.
11
11
8,11,12
11,12
8
11,12
11,12
11,12
11,12
2,3,5,7
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11,12
11,12
B-204
-------
Table B-26. Mean Background Lereb of Dibenzofurans in Food Products (ppt) (continued)
Chemical
2,3,4,6,7,8-HxCDF
(continued)
Sample
typ«*
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Number
aanipwa
8
13
9
4
12
9
3
Number
pONtive
sample*
5
2
1
1
2
0
2
.: Cone*
: Range*
ND-0.34
ND-0.029
ND-0.029
ND(0.022)-0.008
ND-0.18
ND(0.01-0.13)
ND-0.18
Arithmetic
mean6
0.16
0.043
0.054
0.019
0.048
0.036
0.085
Geometric
mean*
0.12
0.037
0.052
0.017
0.038
0.029
0.079
Location*
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Ret
«x».
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3,5
; HeptichkKodEbenzofiif«n«(MW « 409 Jl) . ... : ...:
1,2,3,4,6,7,8-HpCDF
Milk
Milk
Dairy products
Dairy product!
Dairy products
Eggi
Egg»
Egg*
Beef and veal
Beef and veal
Beef and veal
20
20
25
5
20
9
8
1
19
11
8
12
12
6
5
1
2
1
1
9
5
4
ND-0.20
ND-0.20
ND-1.76
0.1-1.76
ND-0.28
ND-0.07
ND-0.07
0.06
ND-2.702
ND-2.702
ND-0.97
0.041
0.041
V0.276
0.712
0.167
0.14
0.15
0.06
0.314
0.395
0.20
0.036
0.036
0.182
0.502
0.141
0.11
0.12
0.06
0.163
0.186
0.14
World Wide
Europe
Worldwide
North America
Europe
Worldwide
North America
Europe
World Wide
North America
Europe
2,3,5,7
2,3,5,7
3,5,8,10
10
3,5,8
3,11
11
3
5,8,11,12
11,12
5,8
B-205
-------
Table B-26. Mean Background Levels of Dibenzoftmns m Food Products (pot) (contmned)
Chemical
1,2,3,4,6,7,8-HpCDF
(continued)
1,2,3,4,7,8,9-HpCDF
:,., Sample
:
-------
Table B-26. Mean Background Lereb of Dibauofnrans in Food Products (ppt) (continued)
Chemical
1,2,3,4,7,8,9-HpCDF
(continued)
1,2,3,4,6,7,8,9-OCDF
:• Sample
«*>«'
Chicken
Chicken
Milk
Milk
Dairy products
Dairy product*
Eggs
Eggs
Eggs
Beef and veal
Beef and veal
Beef and veal
Pork
Pork
Pork
Chicken
Chicken
Chicken
Number
sample*
9
9
20
20
20
20
9
8
1
19
11
8
13
9
4
12
9
3
Number
pCMUuVB
samples
0
0
9
9
11
11
1
0
1
NR
3
NR
7
6
1
6
3
3
••! •• Cone*
i Rang**
ND(0.01-0.62)
ND(0.01-0.62)
ibenzofonuM(MW-44.
ND-0.20
ND-0.20
ND-1.39
ND-1.39
ND-0.02
ND(O.OS-1.30)
0.02
ND-1.073
ND-1.073
ND-0.34
ND-1.40
ND-1.40
ND-0.062
ND-3.90
ND-3.90
0.09-0.22
AnthtDBfic. ..... .
mean6
0.088
0.088
Lv6j)
0.048
0.048
0.253
0.253
0.22
0.24
0.02
0.154
0.224
0.059
0.282
0.393
0.032
0.464
0.575
0.13
.... Oeometric.f •••
IPffftil :••'•
0.054
0.054
0.045
0.045
0.185
0.185
0.14
0.14
0.02
0.078
0.115
0.045
0.132
0.261
0.029
0.141
0.146
0.13
£'.•«*!
•••v"E%.'..-
WorUWide
North America
'•".'-"'
Worldwide
Europe
Worldwide
Europe
Worldwide
North America
Europe
WorUWide
North America
Europe
Worldwide
Norm America
Europe
World Wide
Norm America
Europe
..!*iiiJ ..
.%%*.(
11,12
11,12
..-:•'. -
2,3,5,7
2,3,5,7
3,5,8
3,5,8
3,11
11
3
5,8,11,12
11,12
5,8
3,5,11,12
11,12
3,5
3,5,11,12
11,12
3.5
B-207
-------
Table B-26. Mean Background Levels of Dibenzofarans in Food Products (ppt) (continued)
Chemical
TEQ»
for
Dibenzofiiraiu
Sample
I <•)•
B-208
-------
Table B-26. Mean Background Lereb of Dibcnzofarans in Food Products (ppt) (continued)
Footnote References
* Dairy products include butter, cheeses, and cow cream.
" Samples analyzed on a fat weight basis were adjusted to a wet weight basis by multiplying the value by the percentage of fat contained in the sample: beef, 19.0; butter, 81.0;
cheese, 33.0; chicken, 15.0; cow cream, 37.0; eggs, 10.0; milk, 3.3; pork, 15.0; Swiss cheese, 27.0; and veal, 6.7 (USDA, 1979-1984).
c Means were taken from all sites except near incinerators, South Vietnam, and pork samples from the USSR because, the sites were possibly contaminated.
d World Wide includes North American and Europe only.
NOTES: One-half the limit of detection was used in calculating the means where applicable. Therefore, H is possible to have mean concentrations greater than the range (e.g., reported detection limit for nondetecu greater than
the positive sample).
ND «= not detected (limit of detection)
Sources:
2. Rappe et al. (1987)
3. Beck et al. (1989)
4. LaFleuretal. (1990)
5. Furst et al. (1990)
7. Startin et al. (1990)
8. Schecteretal. (1990)
10. Schecteretal. (1992)
11. Stanley and Bauer (1989)
B-209
-------
Table B-27. Mean Background Lereb of PCBs in Food Products (wet wt. ppt)
Chemkai
Simple
typ**
h
Number
•ample*
Number
pxwhto
•ample*
Cooo.
Range*
Antoinette
• i »*^
QMnUr
Geometric
meat
Lowrttoo4
Rrf.
wX(»>.
Pentachloro-PCB (MW - 326.44)
2,3,3',4,4-PeCB
2,3',4,4',5-PeCB
Pork
Pork
Chicken
Chicken
Beef/veal
Bee (/veal
Daily
Daiiy
Eggi
Eggi
Pork
Pork
Chicken
Chicken
Bee&veal
Beef/veal
Dairy
Dairy
1
1
4
4
6
6
25
25
4
4
4
4
4
4
15
IS
36
36
1
1
4
4
6
6
25
25
4
4
4
4
4
4
15
15
36
36
54
54
25
25
10-19
10-19
10-116
10-116
34
34
55
55
81
81
190-595
190-595
19-487
19-487
54
54
25
25
18.83
18.83
47.12
47.12
34
34
55
55
81
81
71
71
153.86
153.86
54
54
25
25
16.4
16.4
34.626
34.626
34
34
55
55
81
81
63.26
63.26
90.5
90.5
World wide
North America
Worldwide
North America
World wide
North America
Worldwide
North America
Worldwide
North America
World wide
North America
World wide
North America
World wide
North America
Worldwide
North America
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
B-210
-------
Table B-27. Mean Background Lercb of PCBs in Food Products (wet wt. ppt) (contfaMd)
Chemical
-f
2,3',4,4',5-PeCB
coot.
2,3,3',4,4',5-HxCB
2,3,3',4,4'.5,5'-HpCB
Sample
type*
Eggs
Eggs
Pork
Pork
Chicken
Chicken
Beef/veal
Beef/veal
Dairy
Dairy
Egg.
Eggs
Beef/Veal
Beef/Veal
Dairy
Dairy
simple*
5
5
2
2
3
3
8
8
21
21
3
3
1
1
2
2
=s^=^=
Number
poMuvft . .
sample*
5
5
Hexachlon
2
2
3
3
8
8
21
21
3
3
Heptaehla
1
1
2
2
Cone.
Range*
99
99
>PCB (MW** 360*81
9
9
16
16
7-14
7-14
7-63
7-63
24
24
ro-PCB (MW*396<3
10
10
7-10
7-10
AntaHMStjO
99
99
9
9
16
16
10.75
10.75
29.57
29.57
24
24
3)
10
10
8.5
8.5
Geometric
mesrf
99
99
9
9
16
16
10.24
10.24
23.32
23.32
24
24
10
10
8.37
8.37
Locatiofl*
Worldwide
North America
Worldwide
North America
Worldwide
North America
Worldwide
North America
World wide
North America
Worldwide
North America
Worldwide
North America
Worldwide
North America
Kef.
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
=fr=^=mast==S3.
B-211
-------
Table B-27. Mean Background Leveb of PCBs in Food Products (wet wl. ppt) (continoed)
Footnote References
* Dairy product! include butter, cheeiei, and cow cream.
b Samplei analyzed on a fat weight baiii were adjusted to a wet weight baiii by multiplying the value by the percentage of fat contained in the sample: beef, 19.0; butter, 81.0;
cheese, 33.0; chicken, 15.0; cow cream, 37.0; egga, 10.0; milk, 3.3; pork, 15.0; Swiss cheese, 27.0; and veal, 6.7 (USDA, 1979-1984).
c Means were taken from all sites except near incinerators, South Vietnam, and pork samples from the USSR because, the sites were possibly contaminated.
World Wide includes North American and Europe only.
Notes: One-half the limit of detection was used in calculating the means where applicable.
ND = not detected (limit of detection)
Sources: 1. Mes, et al. (1991).
B-212
-------
Table B-28. Mean Rural/Urban Background Environmental Levels of Dioxins in Air (pg/m3)
Chemical
Number
tamples*
Number
positive
samples
Concentration
range
Arithmetic
mean1*
Geometric
meanb
Location6
Ref. no.
Tetrachlorodiben;^p-diojdrw(MW=32i.98)
2,3,7,8-TCDD
TCDDs
78
73
5
81
76
5
8
3
5
29
24
5
ND-0.08
ND-0.08
0.0002-0.007
ND-0.18
ND-0.18
0.0057-0.05
0.0100
0.0107
0.0004
0.0429
0.0435
0.0325
0.0052
0.0063
0.0003
0.0318
0.0322
0.0258
World Wide
North America
Europe
World Wide
North America
Europe
1,3,4,5,7.9,11.12,14
1,3,4,5,9,11,14
7,12
1,4,5,7,9,11,12,14
1,4,5,9,11,14
7,12
Pentachlorodibenzo-p-dJoxins (MW =356,42)
1,2,3,7,8-PeCDD
PeCDDs
73
68
5
90
85
5
16
11
5
31
26
5
ND-0.14
ND-0.14
0.0007-0.006
ND-0.89
ND(0.89)
0.019-0.11
0.0297
0.0316
0.0036
0.0836
0.0843
0.0716
0.0125
0.0141
0.0027
0.0559
0.0557
0.0592
World Wide
North America
Europe
World Wide
North America
Europe
1,3,4,5,7,9,12,13,14
1,3,4,5,9,13,14
7,12
1,4,5,7,9,11,12,14
1,4,5,9,11,14
7,12
He»chk>rodibei»2o-p-dio>un*(MW==390,87)
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
73
68
5
73
68
5
73
68
5
20
15
5
35
30
5
30
26
4
ND-0.14
ND-0.14
0.0006-0.004
ND-0.39
ND-0.39
0.0009-0.008
ND-0.35
ND-0.35
ND-0.0052
0.0231
0.0246
0.0025
0.0350
0.0372
0.0050
0.0458
0.0489
0.0031
0.0164
0.0192
0.0020
0.0264
0.0304
0.0038
0.0327
0.0400
0.0021
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
1,3,4,5,7.9,12,13.14
1,3,4,5,9,12,13,14
7,12
1,3,4,5,7,9,12,13,14
1,3,4,5,9,13,14
7,12
1,3,4,5,7,9,12,13,14
1,3,4,5,9,13,14
7,12
B-213
-------
Table B-28. Mean Background Environmental Levels of Dioxins in Air (pg/m3) (continued)
Chemical
HxCDDs
1,2,3,4,6,7,8-HpCDD
HpCDDs
OCDD
TEQs for
Dibenzodioxins
Number
samples*
90
85
5
Number
positive
samples
65
60
5
73
68
5
90
85
5
73
68
5
58
53
5
74
69
5
63
58
5
Concentration
range
ND-3.2
ND-3.2
0.014-0.1
Arithmetic
meanb
0.3067
0.3210
0.0644
Geometric
meanb
0.2010
0.2179
0.0506
Location6
World Wide
North America
Europe
HeptachlonxlibenZo-P^K»uns(MW=425.3l) :
ND-8.4
ND-8.4
0.012-0.1
ND-8.4
ND-8.4
0.03-0.2
Octachlorodibcn
ND-29.5
ND-29.5
0.041-0.23
0.5474
0.5828
0.0660
0.9738
1.0231
0.1364
QQMCMjjQXin (MW3*5^
2.6551
2.8386
0.1598
0.0434
0.0462
0.00408
0.3370
0.3881
0.0494
0.6400
0.7109
0.1072
60.76}
1.7663
2.1426
0.1277
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Ref. no.
1,4,5,7,9,11,12,14
1,4,5,9,11,14
7,12
1,3,4,5,7,9,12,13,14
1,3,4,5,9,13,14
7,12
1,4,5,7,9,11,12,14
1,4,5,9.11,14
7,12
1,3,4,5,7,9,10,11,12.14
1,3,4,5,9,10,11,14
7.12
Footnote References
" The number of positive samples from Hunt and Maisel (1990) were not included because they were not reported.
b Means were taken from rural, urban, and pristine sites.
Industrial, sites were not used because they were assumed to be contaminated.
c Worldwide includes Europe and North America only.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
Sources: 1. Smith, et al. (1989).
3. Maisel and Hunt (1990).
4. Hunt and Maisel (1990).
5. CDEP (1988).
7. Naf, et al. (1990)
9. Edgerton, et al. (1989).
10. Eitzer and Kites (1989).
11. Smith, etal. (1990).
12. Broman, et al. (1991).
13. Eitzer and Kites (1989).
14. Hunt, et al. (1990).
B-214
-------
Table B-29. Mean Rural/Urban Background Environmental Levels of Dibenzofurans in Air (pg/m3)
Chemical
Number
samples
Number
positive
samples*
Cone.
range
Arithmetic
meanb
Geometric
tneanb
Location*
Ref. no(s).
Tetraehlofodibenzoiurans (MW=305.98)
2,3,7.8-TCDF
TCDFs
73
73
90
85
5
50
50
68
63
5
ND-1.24
ND-1.24
ND-8.81
ND-8.81
0.018-0.33
0.1128
0.1128
0.6343
0.6600
0.1976
0.0489
0.0489
0.3787
0.3995
0.1529
World Wide
North America
World Wide
North America
Europe
1,3,4,5,9,11,14
1,3,4,5,9,11,14
1,4,5,7,9,11,12,14
1,4,5,9,11,14
7,12
Pentachlorodibenzofiiran* (MW»340.42)
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
PcCDFs
67
67
72
68
5
90
85
5
17
17
27
22
5
67
62
5
ND-1.90
ND-1.90
ND-0.16
ND-0.16
0.0012-0.02
ND-3.61
ND-3.61
0.026-0. 17
0.0498
0.0498
0.0274
0.0287
0.0098
0.4234
0.4424
0.1012
0.0220
0.0220
0.0230
0.0255
0.0059
0.2963
0.3200
0.0799
World Wide
North America
World Wide
North America
Europe
World Wide
North America
Europe
1,3,4,5,9,14
1,3,4,5,9.14
1,3,4,5,7,9,12,14
1,3,4,5,9,14
7.12
1,4,5,7.9,11,12,14
1.4,5,9,11,14
7,12
Hexachlorodibenzoftirans (MW«374.87)
1,2,3,4,7.8-HxCDF
1,2,3,6,7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6,7,8-HxCDF
67
67
72
67
5
73
68
5
73
68
5
30
30
30
25
5
8
3
5
29
24
5
ND-0.41
ND-0.41
ND-0.8
ND-0.8
0.0014-0.008
ND-0.097
ND-0.097
0.0001-
0.0008
ND-0.3
ND-0.3
0.0009-
0.0063
0.0604
0.0604
0.0548
0.0585
0.0051
0.0147
0.0157
0.0006
0.0420
0.0448
0.0039
0.0562
0.0562
0.0392
0.0463
0.0042
0.0070
0.0085
0.0005
0.0332
0.0395
0.0031
World Wide
North America
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
1,3.4.5,9,14
1.3.4.5,9.14
1,3,4,5,7,9,12,14
1,3,4,5,9,14
7,12
1,3,4,5,7,9,12,13,
14
1,3,4,5,9,13,14
7,12
1,3 4,5,7,9,12,13
14
1.3,4,5,9.13,14
7,12
B-215
-------
Table B-29. Mean Rural/Urban Background Environmental Lereb Dibenzofurans in Air (pg/m1) (continued)
Chemical
HxCDFs
Number
samples
90
85
5
Number
positive
sample**
67
62
5
Cone,
range
ND-2.15
ND-2.15
0.015-0.08
Arithmetic
meank
0.3616
0.3797
0.0528
Heptaohlorodibenzofijran$(MW=
1,2,3,4,6,7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
HpCDFs
73
68
5
70
65
5
90
85
5
42
37
5
19
15
4
60
55
5
ND-1.20
ND-1.20
0.011-0.09
ND-0.3
ND-0.3
ND-0.004
ND-1.58
ND-1.58
0.015-0.11
0.1995
0.2102
0.0542
0.0279
0.0299
0.0019
0.3196
0.3343
0.0704
Geometric
mctn*
0.2947
0.3295
0.0442
409,31)
0.1700
0.1817
0.0686
0.0218
0.0272
0.0012
0.2528
0.2763
0.0556
Location*
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
World Wide
North America
Europe
Ref. no(i).
1,4,5,7,9,11,12,14
1,4,5,9,11,14
7,12
1,3,4,5,7,9.12,13,
14
1,3,4,5,9,13,14
7,12
3,4,5,7,9,12,13,14
3,4,5,9,13,14
7,12
1,4,5,7,9.11,12,14
1,4,5,9,11,14
7,12
OcUchtorodibenzofurans (MW«444.76)
OCDF»
TEQs for
Dibenzofurans
89
84
5
51
46
5
ND-0.70
ND-0.70
0.0009-0.016
0.1597
0.1686
0.0094
0.0471
0.0486
0.0064
0.1271
0.1528
0.0057
World Wide
North America
Europe
World Wide
North America
Europe
1,3,4,5,7,9,11,12,
14
1,3,4,5,9.11.14
7,12
B-216
-------
Table B-29. Mean Rural/Urban Background Environmental Leveb Dibenzofurtns in Air (pg/ms) (continued)
Footnote References
* The number of positive samples from Hunt and Mabel (1990) were not included because they were not reported.
* Means were taken from urban and pristine sites.
Industrial, sites were not used because they were assumed to be contaminated.
' Worldwide includes Europe and North America only.
NOTES: One-half the limit of detection was used in calculating the means where applicable.
ND = non-detected (limit of detection)
Sources:
1. Smith, etal. (1989).
3. Maisel and Hunt (1990).
4. Hunt and Maisel (1990).
5. CDEP (1988)
7. Naf, et al. (1991).
9. Edgerton, et al. (1989).
11. Smith, etal. (1990).
12. Broman, et al. (1990).
13. Eitzer and Hites (1989).
14. Hunt, et al. (1990).
B-217
-------
Table B-30. Mean Background Environmental Leveb of PCBs in Air (pg/m3)
Chemical
Number
wimples
Number
positive
twnpks
range
Arithmetic
mcanr
Geometric
Mwf
Location
Ref. no(»).
Pentachtoro-PCB (MW=326.44)
2,3,4,4'5-PeCB
2,3,4,4',5-PeCB
2,3,3',4,4>-PcCB
2,3,3',4,4',5-HxCB
143
143
143
143
143
143
143
143
143
143
143
143
143
143
143
143
2.3
2.3
1.2
1.2
0.6
0.6
2.3
2.3
1.2
1.2
0.16
0.16
2.3
2.3
1.2
1.2
0.16
0.16
World wide
North America
World wide
North America
World wide
North America
Hexachloro-PCB (MW» 360,88)
0.07
0.07
0.07
0.07
0.07
0.07
World wide
North America
14
14
14
14
14
14
14
14
HepUcbloro-PCB
-------
DRAFT - DO NOT QUOTE OR CITE
APPENDIX C. BIOAVAILABILITY OF DIOXINS
C.1 Bioavailability Data
Umbreit et al. (1985, 1986a,b) conducted experiments in guinea pigs,
administering 2,3,7,8-TCDD in corn oil, 2,3,7,8-TCDD added to chemically
decontaminated soil, or soil from two industrial sites in Newark, New Jersey (a
manufacturing site and a salvage site) contaminated with CDDs. 2,3,7,8-TCDD was the
principal lower chlorinated isomer (dioxin or furan) present in the soil from the
manufacturing site (for which a chemical analysis was presented). Soil from the
manufacturing site was found to have 1,500 to 2,500 ppb 2,3,7,8-TCDD under soxhlet
extraction; release under ambient temperature manual solvent extraction was much lower,
reported as ">2.5 ppb." The soil from the salvage site was reported as approximately
180 ppb 2,3,7,8-TCDD under soxhlet extraction.
In this study, groups of two or four male and two or four female guinea pigs
received single gavage doses of the test materials and were observed until death or
sacrifice at 60 days. 2,3,7,8-TCDD in corn oil or in recontaminated soil (6 g/kg in both)
proved highly toxic, without similar toxicity being observed in animals treated with up to
twice this dose of 2,3,7,8-TCDD in the soil from the manufacturing site. The limited data
on 2,3,7,8-TCDD levels in the liver showed much higher levels following administration of
recontaminated soil versus contaminated soil from the manufacturing site.
Umbreit et al. (1986a) thus demonstrated that gavaged 2,3,7,8-TCDD containing
soil from the manufacturing site was substantially less toxic than equivalent doses of
2,3,7,8-TCDD in corn oil. However, quantitative comparison of the effective doses in this
study is difficult. Approaches to a quantitative comparison are outlined below.
(1) Guinea pigs receiving 12 ug/kg 2,3,7,8-TCDD in contaminated
soil experienced no deaths, while five out of eight guinea pigs
receiving 6 ug/kg 2,3,7,8-TCDD in corn oil died, with no
groups tested having lower doses in corn oil. Other authors
have provided data on the toxic effects of 2,3,7,8-TCDD in
corn oil which could aid in the comparison.
McConnell et al. (1984) observed one out of six animals dying at
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1 ug/kg and six out of six animals dying at 3 ug/kg. Silkworth et al. (1982)
observed three out of six animals dying at 2.5 ug/kg and no deaths out of
six at 0.5 ug/kg. Comparing these data directly with the Umbreit et al.
results would suggest that the 2,3,7,8-TCDD in the Newark manufacturing
site soil was less effective, by a factor of 10 or greater, in producing toxicity
than 2,3,7,8-TCDD in corn oil.
(2) Umbreit et al. reported a "slightly reduced" weight gain in guinea pigs
receiving 6 ug/kg of 2,3,7,8-TCDD in Newark manufacturing site soil, and a
"greater reduction" at the 12 ug/kg dose. No other signs of toxicity were
noted in these groups. The animals receiving 6 ug/kg 2,3,7,8-TCDD in corn
oil, in contrast, exhibited a marked loss of body weight and showed toxicity
and mortality. Silkworth et al. (1982) also provided data on weights of
guinea pigs receiving 2,3,7,8-TCDD in corn oil. Those receiving 2.5 ug/kg
exhibited a marked reduction in weight gain among three out of six
survivors, while those receiving 0.5 ug/kg showed a weight gain comparable
to vehicle controls. Comparison of this weight data with that of Urnbreit et
al. suggests that the 2,3,7,8-TCDD in corn oil was more than 5 times but
less than 25 times as potent as 2,3,7,8-TCDD in the Newark soil. This
comparison assumes that the effect of the Newark manufacturing site soil
on weight gain was due to 2,3,7,8-TCDD as opposed to other compounds in
the soil. Numerous other dioxin and furan compounds and other chemicals
have been identified in this soil (Umbreit et al., 1987a). It has not been
established that 2,3,7,8-TCDD is the sole or prime source of toxicity in the
soil.
(3) Umbreit et al. presented liver concentrations of 2,3,7,8-TCDD after death or
sacrifice at 60 days following gavage. Much lower concentrations of
2,3,7,8-TCDD were found in the livers of animals receiving soil from the
manufacturing site compared with those receiving the dose in corn oil.
There are, however, two factors that limit the conclusions than can be
drawn from this comparison.
First, the corn oil group experienced major toxicity and weight loss, particularly
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complete loss of body fat. These changes may have affected the partitioning of 2,3,7,8-
TCDD within the body, leading to a higher concentration in the livers of the animals
experiencing toxicity. Second, the animals gavaged with corn oil died early—half were
dead by 26 days, while all of the guinea pigs treated with soil survived to 60 days (with
the exception of one gavage death). The U.S. EPA (1985c) reported a half-life for 2,3,7,8-
TCDD elimination of 30 _+. 6 or 22 to 43 days from two studies in guinea pigs.
Additionally, the U.S. EPA (1985c) stated that elimination in the guinea pig may follow
zero-order kinetics. Differences in elimination due to differences in periods of survival are
likely to have affected the relative quantities of 2,3,7,8-TCDD found in the livers of the
test groups.
Perhaps a more appropriate comparison can be made with the four animals
receiving 0.32 ug/kg of 2,3,7,8-TCDD in contaminated soil from the Newark salvage site.
These animals experienced no reported toxic signs (weight data not presented) and
survived the full 60-day experiment. Approximately 6% of the gavage dose was found in
the liver of these animals, while only about 0.06% of the gavage dose was found in the
livers of guinea pigs in the 12 ug/kg group receiving the Newark manufacturing site soil.
This would suggest that the 2,3,7,8-TCDD in the manufacturing site soil was 100 times
less bioavailable. However, given the different doses used and the fact that only a single
pooled sample was analyzed for 2,3,7,8-TCDD in each group, caution must be used in
interpreting this comparison.
The 2,3,7,8-TCDD in soil from the salvage site was substantially bioavailable,
based on the single liver tissue analysis. Approximately 6% of the administered dose was
recovered from the livers of these animals at 60 days. This can be compared with data on
hamsters given 2,3,7,8-TCDD in corn oil by McConnell et al. (1984), where approximately
8% of the 2,3,7,8-TCDD could be recovered in the 1 ug/kg dose group among survivors at
30 days.
McConnell et al. (1984) treated Hartley guinea pigs (2.5 weeks old) with single
gavage doses of either 2,3,7,8-TCDD or dioxin contaminated soil from two sites in
Missouri. The 2,3,7,8-TCDD concentrations from the two sites were reported at 700 and
880 ppb respectively; total tetrachlorodibenzofurans (TCDF) concentrations in the soil
were 40 to 80 ppb, and polychlorinated biphenyls (PCS) concentrations were 3 to 4 ppm.
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Taking into account the relative toxicities, the authors concluded that toxicity from the
other compounds was likely to be small compared with that from 2,3,7,8-TCDD. Livers
were analyzed for 2,3,7,8-TCDD at death or sacrifice at 30 days following treatment.
Treatment deaths occurred between 5 and 21 days post-gavage.
Guinea pigs that died exhibited severe loss of body fat, markedly reduced thymus
and testicle size, and adrenal hemorrhage. No adverse affects were noted in animals
treated with decontaminated soil. For 2,3,7,8-TCDD in corn oil and for both contaminated
soils, there were clear dose-responses in mortality. The calculated LD50 values for the two
soil types were lower than the LD50 for 2,3,7,8-TCDD in corn oil by a factor of three to
four.
There was a dose-response between the liver concentration of 2,3,7,8-TCDD and
the gavage dose; the details of this relationship are complex. Animals dying during the
experiment had liver concentrations a factor of 1.4 to 3.2 higher than animals in the
same dose groups who survived 30 days. This observation makes quantification of the
dose-response relationships difficult (all or most of the animals in the low-dose groups
survived the experiment, while all of the animals in the high-dose groups died). When the
liver concentrations of 2,3,7,8-TCDD in animals dying early at the middle and high-dose
groups are compared, there appears to be a greater-than-linear increase in liver
concentration with dose for the Times Beach and Minker Stout soil groups, with a 3.3-fold
increase in dose producing a 10- to 13-fold increase in liver concentration.
Liver concentrations of animals in the different dosing groups can best be compared
among groups that experienced similar mortality.
(1) Animals in dose groups in which all animals died within 30 days: 2,3,7,8-
TCDD in corn oil, approximately 20% of the administered dose was in the
liver. For the soil-treated groups, 13% and 11 % of the doses, respectively,
were in the liver. Comparison of these data suggest that 2,3,7,8-TCDD was
approximately twice as available through corn oil as through soil.
(2) Animals surviving the 30-day experiment (in groups where at least 4 out of
6 survived): For 2,3,7,8-TCDD in corn oil, 7.5% of the administered dose
was in the liver. For soil-treated animals < 3.6, 1.3, < 4.2, and 2.0% of
the doses, respectively, were in the liver. Comparison here would suggest
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that 2,3,7,8-TCDD was approximately four times as available through corn
oil as through soil.
The authors note that the differences in liver concentrations observed in the study
may reflect varying partitioning of the 2,3,7,8-TCDD among internal organs, since dying
animals suffered major loss of body weight and fat content. In addition, surviving animals
would have had greater opportunity to metabolize and excrete 2,3,7,8-TCDD due to a
i
longer lifetime.
Umbreit et al. (I986a) reported additional chemical analyses of the Times Beach
soil. Soxhlet extraction of the Times Beach soil yielded a similar quantity of 2,3,7,8-TCDD
to the solvent extraction reported by McConnell et al. (1984). This is in contrast to the
Newark manufacturing site soil used in the Umbreit et al. (1987a) experiments, where only
a small fraction of soxhlet-extractable 2,3,7,8-TCDD was extractable by the solvent
extraction methodology used by McConnell et al. (1984).
McConnell et al. (1984) also reported an experiment in which groups of six
Sprague-Dawley rats were given single gavage doses of 2,3,7,8-TCDD in corn oil or
dioxin-contaminated soil from the Minker site. Induction of aryl hydrocarbon hydroxylase
(AHH) in the rat livers was measured at sacrifice 6 days after dosing. Experimental doses
ranged from 0.4 to 5.0 ug/kg 2,3,7,8-TCDD. Measured AHH induction was similar for
groups receiving 2,3,7,8-TCDD in corn oil or receiving contaminated soil containing nearly
equal doses of 2,3,7,8-TCDD. For example (based on the rate of formation of 3-
hydroxybenzo[a]pyrene), AHH activity was measured at 1,269 pmole min"1 mg"1 for the
group receiving 5 ug/kg 2,3,7,8-TCDD in corn oil and at 1,230 pmole min"1 mg"1 for the
group receiving 5.5 ug/kg 2,3,7,8-TCDD in contaminated soil. For the five dose groups,
the AHH activity for the soil group ranged from 50% to 110% of the activity in the corn
oil group.
The McConnell et al. (1984) rat data indicate that the bioavailability of 2,3,7,8-
TCDD from the Minker site soil was at least 50% of that of equivalent doses of 2,3,7,8-
TCDD in corn oil.
Lucier et al. (1986) provided additional information on the induction of hepatic
enzymes in rats by the 2,3,7,8-TCDD contaminated soil from the Minker site tested by
McConnell et al. (1984). AHH induction was similar for the groups of rats receiving
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2,3,7,8-TCDD in corn oil and contaminated soil (within a factor of two) over a broader
range of doses (0.015 ug/kg to 5 ug/kg) than reported by McConnell et al. (1984). In a
second enzyme assay using the same animals, UDP glucuronyltransferase activity was
found to be slightly higher in groups receiving 2,3,7,8-TCDD in corn oil than groups
receiving equal doses in contaminated soil.
Liver concentrations of 2,3,7,8-TCDD for the rats were also reported. For the corn
oil vehicle the liver concentrations were 40.8 _±_ 6.5 ppb at the 5 ug/kg dose and 7.6 _±_
2.5 ppb at the 1 ug/kg dose. Assuming that the liver comprises 4.0% of body weight, the
retention rates for the 5 and 1 ug/kg doses were 33% and 30%, respectively. In rats
receiving 2,3,7,8-TCDD in contaminated soil, the 5.5 ug/kg group had liver concentrations
of 20.3 +_ 12.9 ppb, and the 1.1 ug/kg group had concentrations of 1.8 _±_ 0.3. Thus,
retention rates for the 5.5 and 1.1 ug/kg groups are estimated at 14% and 7%,
respectively. These data indicate that liver retention in the soil group was 20% to 40% of
that in the corn oil vehicle groups.
Umbreit et al (1986b) report additional studies of mortality in guinea pigs treated
with soil containing 2,3,7,8-TCDD from Newark (manufacturing site) and Missouri (Times
Beach) previously tested by Umbreit et al (1985, 1986a) and McConnell et al. (1984),
respectively. Guinea pigs received a single gavage dose of a soil suspension and were
observed for 60 days. After autopsy, deaths were classified as whether or not they
appeared to be due to TCDD toxicity. Substantial mortality (25% overall) from conditions
not attributed to TCDD was observed across all groups.
The data for both the Newark and Missouri sites are similar in trend for the previous
data on these sites; and clearly indicate the greater toxicity of the Newark soil for given
equal administered doses of 2,3,7,8-TCDD. With larger groups of guinea pig studied, a
toxicity-related death was observed in both the 5 and 10 mg/kg dose groups for Newark
soil while no deaths were observed in corresponding dose groups (6 and 1 2 mg/kg) with
fewer animals in Umbreit et al. (1986a).
Comparing groups within this study, similar mortality (1 or 2 deaths in 10 to 16
animals) was seen in both the 5 and 10 ug/kg Newark groups and the 1 and 3 ug/kg
Missouri groups. These results suggest that the toxicity of these materials differs by an
order of magnitude or less. As noted above, the degree to which toxicity from these soils
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can be attributed to 2,3,7,8-TCDD in the presence of numerous other related toxic
compounds is not known. 2,3,7,8-TCDD tissue concentrations were not reported in this
work.
In another comparative study Umbreit et al. (1987b) compared the Newark
manufacturing site and Times Beach soils in the induction of aryl hydrocarbon hydroxylase
(AHH) in rats. While the use of only single dose levels prevents detailed analysis, the two
soils proved quite similar in their ability to induce AHH. The explanation for the difference
in this finding from those observed in the toxicity studies discussed above is not clear, but
may relate to the presence of other toxic and/or AHH inducing compounds.
Umbreit et al. (1987a) report a reproductive toxicity study with soils from the
Newark manufacturing site and salvage yard previously studied by Umbreit et al. (1986a).
Female mice were treated thrice weekly with soil from these sites, with treatment
continuing through fertilization to weaning of pups. The total doses of 2,3,7,8-TCDD
received by the mice were 720 ug/kg in manufacturing site soil, and 86 ug/kg in salvage
yard soil. A corn oil vehicle group and a recontaminated soil group received a total of 225
ug/kg.
Deaths in animals showing "classic signs" of TCDD toxicity were observed in the
corn oil and recontaminated soil groups, and indicate appreciable bioavailability of 2,3,7,8-
TCDD. Deaths were also observed in animals receiving manufacturing site soil but the
authors did not observe "classic signs" of TCDD toxicity. Fewer live pups born and fewer
pups surviving until weaning were observed in the manufacturing site soil group compared
with those receiving decontaminated soil. TCDD completely blocked reproduction in the
corn oil and recontaminated soil groups. The results of this study demonstrate acute and
reproductive effects occurred in animals receiving manufacturing site soil. However, these
effects were of a lesser magnitude than those seen in animals treated with 2,3,7,8-TCDD
in corn oil at a dose three fold lower. The authors note the presence of substantial
quantities of other toxic substances in the manufacturing site soil (chemical analyses
presented). No toxic effects were noted in animals treated with salvage site soil, who
received a much smaller 2,3,7,8-TCDD dose. The data does not allow a quantitative
evaluation of the bioavailability of 2,3,7,8-TCDD.
Kaminski et al. (1985) and Silkworth et al. (1982) reported the results of a series of
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studies on the toxicity of soot containing dioxin and furan compounds from a fire involving
transformer fluid containing PCBs. Hartley guinea pigs (500 to 600 g) received single oral
doses of soot in an aqueous vehicle, a soxhlet extract of the soot in the same vehicle, or
2,3,7,8-TCDD in either an aqueous vehicle or corn oil.
The soot was reported to contain 2.8 to 2.9 ppm 2,3,7,8-TCDD and 124 to 273
ppm 2,3,7,8-TCDF. The total polychlorinated dibenzofuran content was estimated at
5,000 ppm. Animal weights and mortality were recorded for 42 days, at which point the
survivors were sacrificed and LD50 values were calculated. Blood chemistry and a
pathologic examination were performed at sacrifice.
Silkworth et al. (1982) noted that the LD50s for contaminated soot and soot extract
were similar at 410 and 327 equivalent ug/kg, indicating that the matrix had only a small
effect on toxicity. If expressed in terms of the content of 2,3,7,8-TCDD, the LD50 from
soot is 2.5 ug/kg, which is a factor of seven below the LD50 for 2,3,7,8-TCDD in an
aqueous vehicle, suggesting that other compounds contributed to the toxicity of the soot
and soot extract.
The authors stated that they adopted an aqueous vehicle in these experiments
because it was nontoxic and provided a stable suspension of soot; they regarded this
vehicle as more appropriate for modeling of human exposure conditions than an oil vehicle.
The data from these experiments also demonstrate that use of an oil vehicle leads to
substantially greater 2,3,7,8-TCDD toxicity than does an aqueous vehicle.
Comparison of mortality and weight loss in groups of female guinea pigs receiving
500 ug/kg of soot or the equivalent amount of soot extract suggests that the extract may
be somewhat more toxic; however, all six animals died in the 1,000 ug/kg soot group,
while four out of five died in the 500 ug/kg extract group. Taken together, these data
indicate that the soxhlet extract of soot in an aqueous vehicle was between one and two
times as toxic as the soot itself. It is likely that a larger difference in toxicity would have
been observed if the soot extract was in an oil vehicle.
Van den Berg et al. (1983) fed small groups of male Wistar rats fly ash from a
municipal incinerator (pretreated with HCI) containing dioxins and furans, a soxhlet extract
of the fly ash, or a purified extract of the ash that was obtained using column
chromatography. 2,3,7,8-TCDD was present as 3.3% of the TCDD isomer group in the
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fly ash extract. (The authors did not specify whether this reference was to crude or
purified extract.) 2,3,7,8-TCDF was present as 17.9% of the tetra-CDF isomer group in
the extract. The rats were fed 2 g/d fly ash mixed with diet or the residual from 2 mL/d
extract after the extract was mixed with diet and the solvent was evaporated. The animals
were exposed to the treated diet for 19 days, and then sacrificed, and the liver tissue was
analyzed for the presence of dioxins and furans.
Approximately 1% of the 2,3,7,8-TCDD dose from fly ash was retained in the liver,
and approximately 4% of the dose of this isomer from fly ash extract was so retained.
The corresponding percentages for 2,3,7,8-TCDF are 0.3 and 1.0. Data on the retention of
isomer groups in adipose tissue were presented for the extract-treated groups but not for
the fly ash-treated group. The concentrations of the various isomers in adipose tissue are
comparable to, or less than, the concentrations in liver tissue.
The U.S. EPA (1985b) reported a half-life for elimination of 2,3,7,8-TCDD in the rat
of 20 days at high dose. If a similar half-life is assumed in this experiment, the quantities
of 2,3,7,8-TCDD in the animals at the end of the 19-day feeding experiment would be
significantly less than the absorbed dose, but still of the same order of magnitude.
However, the recovery percentages in this study are low for both the fly ash and fly ash
extract groups in comparison with other studies in which 2,3,7,8-TCDD was administered
to rats. Fries and Marrow (1975) fed rats diets containing 7 or 20 ppb of 2,3,7,8-TCDD
for a period of up to 42 days. After 14 days of feeding, the rat livers contained an
average of 32% of the cumulative administered dose; at 28 days, 21 % of the dose; and at
42 days, 18% of the dose. Thus, in the van den Berg et al. (1983) study, the liver
retention of 2,3,7,8-TCDD for the fly ash extract group is a factor of five to eight below
what could be anticipated for the Fries and Marrow (1975) data, and the liver retention in
the van den Berg et al. (1983) group fed soot is a factor of 20 to 30 lower than that seen
by Fries and Marrow (1975). Data from Kociba et al. (1976), Rose et al. (1976), and
Kociba et al. (1978) lead to similar conclusions to those from the Fries and Marrow (1975)
data regarding the fraction of cumulative 2,3,7,8-TCDD dose retained in the rat liver.
An explanation of the low level of recovery for the animals receiving the soxhlet
extract of soot is not apparent. It is possible that the presence of multiple compounds
affected absorption or metabolism in the rats fed soot and soot extract.
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A second approach to the van den Berg et al. (1983) data is to compare the ratios
of liver concentrations for dioxins in fly-ash-treated animals to the concentrations in
extract-treated animals. These ratios, based on measurements in small numbers of
animals, indicate a substantial bioavailability of dioxin and furan compounds from the
tested fly ash. This availability varied among the different isomers with the value of 0.3
for 2,3,7,8-TCDD, indicating that this isomer was three times as available from fly ash
extract as from fly ash.
Van den Berg et al. (1985) fed fly ash (pre-treated with HCI) to Wistar rats, guinea
pigs, and Syrian golden hamsters. Fly ash was mixed with standard laboratory diet at
2.5% by weight, and animals were allowed to eat ad libitum. The amount of fly ash
consumed by each group of five rodents was determined by the authors. For each species
there were three groups of animals each fed fly ash for approximately 32 days (group I),
60 days (group II), or 94 days (group III). Concentrations of dioxin and furan isomer
groups in the food were presented, and include 1.4 ng/g TCDD compounds and 2.1 ng/g
TCDF compounds.
The authors presented calculated recovery percentages for the cumulative dose of
specific isomers in the rodent liver. For 2,3,7,8-TCDD in guinea pigs, 3.7%, 0.9%, and
1.4% of the administered dose was recovered in the liver in groups I, II, and III,
respectively. The 32-day (group I) recovery percentage is somewhat higher than seen in
the lower dose groups receiving 2,3,7,8-TCDD contaminated soil in McConnell et al.
(1984). The value in hamsters was approximately 2% (only reported for group II), and
analytical problems prevented this determination in rats. No other TCDD compounds were
quantified. Similarly, for 2,3,7,8-TCDF, guinea pigs showed retention of 4.7%, 2.2%,
2.5% of the administered dose in groups I, II, and III, respectively. For both 2,3,7,8-TCDD
and 2,3,7,8-TCDF the recovery percentages in guinea pigs at 32 days were approximately
a factor of 4 to 15 higher than that observed in the van den Berg et al. (1983) study in
rats.
Other TCDD compounds that were present showed comparable or somewhat lower
retention, averaging 1 % to 2% over the animals groups. No TCDD or TCDF compounds
were detected in hamster liver or analyzed for in rat liver. Higher chlorinated congeners
most typically showed retention in the range of 2% to 5% in rat liver and 1 % to 3% in
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guinea pig liver, with the exception of 2,3,4,7,8-PeCDF (9.8%, 8.3%, and 11.3% in the
hamster groups). Few other compounds were found in hamster liver, but 2,3,4,7,8-PeCDF
was found with a recovery of 5% to 8% and 2,3,4,7,8-HxCDD was found at 3% to 7%.
As with other experiments in which the retention of dioxins in the liver has been
determined, these percentages place a lower bound on the bioavailability of the dioxins
but, because not all dioxin is localized in the liver, do not permit bioavailability to be
estimated without knowledge of the elimination of the administered dose over time and
the quantity of dioxins in the remainder of the organism. No positive control group
receiving 2,3,7,8-TCDD was included for comparison.
Poiger and Schlatter (1980) conducted several experiments in Sprague-Dawley rats
(180 to 220 g) in which liver concentrations of tritium label from 2,3,7,8-TCDD were
determined using various doses and vehicles. All experiments consisted of a single gastric
intubation of 2,3,7,8-TCDD-containing material, followed by animal sacrifice at
predetermined times. The doses used were well below the LD50 in the rat (the maximum
dose applied was 5 ug/kg), and no deaths or toxic effects were reported.
In a preliminary experiment, rats were treated with 14.7 ng/rat 2,3,7,8-TCDD in
ethanol. The results indicate substantial localization of 2,3,7,8-TCDD in the rat liver, with
a decrease of a factor of two in the fraction of the dose in the liver between 1 and 4
days. Poiger and Schlatter (1980) conducted all further studies with sacrifice at 24 hours
to maximize the recovery of 2,3,7,8-TCDD from the liver.
In a second experiment, the authors administered 2,3,7,8-TCDD doses in ethanol
ranging from 1 5 to 1,070 ng/rat to groups of six rats. They found a graded increase in
percentage retained in the liver from 37% _+. 1 % at the 1 5 ng dose to 51 % _+_ 4% at 280
ng. At the high-dose point, the percentage may have fallen (42% _+_ 10% at 1,070 ng).
In a further experiment, 2,3,7,8-TCDD was administered at low dose in a series of
vehicles. These data demonstrate that administration of 2,3,7,8-TCDD in soil reduced the
retention of the dose in the liver to 66%, or 44% of the retention seen with 2,3,7,8-TCDD
in ethanol. The lower value, 44%, was obtained for soil that was aged for 8 days at
30-40 °C following addition of 2,3,7,8-TCDD. This observation is consistent with the
findings of other studies reported here that 2,3,7,8-TCDD from environmental soil
(naturally aged) was generally less available than 2,3,7,8-TCDD freshly added to clean
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samples of these soils. The aqueous suspension of 2,3,7,8-TCDD in activated carbon
showed little evidence of bioavailability; this is supported by the authors' measurements
showing that 2,3,7,8-TCDD was only slightly extractable from the activated carbon matrix
by various solvents. In contrast, 58% to 70% of 2,3,7,8-TCDD could be recovered from
soil samples by washing with hexane/acetone (4:1 v/v).
Poiger and Schlatter (1980) also presented results from several skin application
experiments with TCDD-containing materials using rats and rabbits (not reviewed here).
Bonaccorsi et al. (1984) reported the results of a study of gut absorption of
2,3,7,8-TCDD from soil taken from the Seveso, Italy accident site. Soil containing 81 _+. 8
ppb 2,3,7,8-TCDD from the "highly contaminated" area in Seveso was administered to
albino male rabbits (2.6 _+. 0.3 kg) in daily gavage doses for seven days. Additional
samples of clean soil were spiked with 2,3,7,8-TCDD in the laboratory to yield 10 and 40
ppb contamination levels and were administered to rabbits following the same protocol.
For comparison, rabbits were also treated with 2,3,7,8-TCDD in solution in acetone-
vegetable oil (1:6) or alcohol-water (1:1). Rabbits were sacrificed on the day after
treatment stopped and liver concentrations of 2,3,7,8-TCDD were measured. The authors
did not remark on the presence or absence of toxicity in the treated rabbits. EPA (1985a)
reports values for the single dose LD50 of 2,3,7,8-TCDD in rabbits of 11 5 and 275 ug/kg.
The total doses received by the rabbits in this study were approximately 54, 107, and 215
ug/kg over seven days. Based on this comparison, there is a likelihood that toxic effects
occurred in the Bonaccorsi work, and as noted above, toxicity has the potential to affect
the tissue concentrations of 2,3,7,8-TCDD. For this reason, the most appropriate
comparisons among these data are between groups showing similar liver concentrations of
2,3,7,8-TCDD, which may then be inferred to have experienced similar toxic effects.
That this method of comparison is desirable can also be seen from the Bonaccorsi
et al. (1984) data, where both solvent vehicle groups and the spiked soil groups show an
increase of the fraction of the dose in the liver at the higher administered doses.
However, it should be mentioned that use of two different solvent vehicles complicates
interpretation. Similar liver concentrations of 2,3,7,8-TCDD were seen in the 40 ug/d
solvent vehicle and 80 ug/d Seveso soil groups. Comparing the percentage of liver
retention in these two groups indicates absorption from Seveso soil was 40% of that from
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the solvent vehicle. Using the same approach, comparison of the 80 ug/d solvent vehicle
and 160 ug/d Seveso soil groups indicates that absorption from the soil was 41% of that
from the solvent.
The same approach can be used to compare absorption from the solvent vehicle
and from the spiked soil. In this case the 40 ug/d solvent vehicle group had the liver
concentrations closest to either the 40 or 80 ug/d spiked soil groups. Comparison of the
percentage of dose in the liver indicates absorption from spiked soil is 68-73% of that
from the solvent vehicle. Bonaccorsi et al. (1984) conducted work with either aged or non-
aged spiked soil but do not present data to allow a comparison of these groups.
Shu et al. (1987, as cited by Leung and Paustenbach, 1987) studied 2,3,7,8-TCDD
from the Missouri site tested by McConnell et al. (1984). Their paper reports an oral
bioavailability of approximately 43% in the rat dosed with environmentally contaminated
soil from Times Beach, Missouri. This figure did not change significantly over a 500-fold
dose range of 2 to 1450 ng 2,3,7,8-TCDD per kg of body weight for soil contaminated
with approximately 2, 30 or 60 ppb of 2,3,7,8-TCDD. The data from this study is not now
available to the Exposure Assessment Group of EPA for review.
C.2 Summary of Bioavaifability
Table C-1 summarizes data that are pertinent to the bioavailability of 2,3,7,8-TCDD
from environmental matrices. Studies of bioavailability, which examined soil samples,
soot, and fly ash, have utilized three methodologies: measuring acute toxicity, retention of
2,3,7,8-TCDD in the liver, and induction of hepatic enzymes.
Among the five samples of soil from contaminated sites that have been tested,
three have shown substantial bioavailability, e.g., 25% to 50%, when compared with
2,3,7,8-TCDD in corn oil gavage. A fourth soil sample was compared with 2,3,7,8-TCDD
administered in a solvent vehicle, and fell in this range. The fifth soil, tested by Umbreit et
al. (1986a,b; 1987a,b) showed bioavailability substantially less than the other soils tested.
While difficult to gauge quantitatively, dioxin from this fifth soil may be an order of
magnitude less available than from the other soils.
Additionally, three samples of soil spiked with 2,3,7,8-TCDD have been tested for
bioavailability, including one sample in which the 2,3,7,8-TCDD was incubated with soil at
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Table C-1. Summary of Data on the Bioavailability of 2,3,7,b-TCDD
Following Ingestion of Environmental Matrices
Reference
Umbreit et al.
(1986a,b)
Umbreit et al.
(1986a,b)
McConnell et al.
(1984)
Matrix/Source
Soil/Newark
Manuf. Site
Soil/Newark
Salvage Site
Recontaminated
Soil
Soil/Times Beach,
MO
Species
Guinea pig
Guinea pig
Guinea pig
Guinea pig
Dosing
Single gavage
Single gavage
Single gavage
Single gavage
Observation
2,3,7,8-TCDD in
soil <10% as
toxic as in corn oil.
based on lethality
and weight loss.
2,3,7,8-TCDD in
the manuf. site soil
had retention in
liver approx. 1 %
as great as with
salvage site soil.
Liver retention
similar to 2,3,7,8-
TCDD in corn oil
from lower dose
McConnell et al.
(1984) data.
Toxicity similar to
equal dose of
2,3,7,8-TCDD in
corn oil.
LDgQ data indicate
2,3,7,8-TCDD in
soil approx. 25%
as toxic as in corn
oil.
Comparing animals
dying early, liver
retention of
2,3,7,8-TCDD in
soil group approx.
50% of that in
corn oil vehicle
group.
Comparing animals
surviving
experiment, liver
retention of
2,3,7,8-TCDD in
soil group approx.
20% of that in
com oil vehicle
group.
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Table C-1 (continued)
Reference
McConnell et al.
(1984)
McConnell et al.
(1984) and
Lucier et al.
(1986)
Poiger and
Schlatter (1980)
Bonaccorsi
(cited in
McConnell et
al., 1984)
Matrix/Source
Soil/Minker Site,
MO
Soil/Minker Site,
MO
Soil with 2,3,7,8-
TCDD
Soil/Seveso
Accident Site
Species
Guinea pig
Rat
Rabbit
Dosing
Single gavage
Single gavage
Observation
LDgQ data indicate
soil approx. 30%
as toxic as
2,3,7,8-TCDD in
corn oil.
Comparing animals
dying early, liver
retention approx.
50% of that in
corn oil vehicle
group.
Comparing animals
surviving
experiment, liver
retention approx.
25% of that of
com oil vehicle
group.
Introduction of
AHH and UDP
glucuronyltransfer-
ase activity >
50% of that in
groups receiving
2,3,7,8-TCDD in
corn oil.
Liver retention 20-
40% of that in rats
receiving equal
dose of 2,3,7,8-
TCDD in corn oil.
Liver retention
approx. 40-70% of
that in ethanol
vehicle groups.
2,3,7,8-TCDD
30% as
bioavailable from
soil as from
solvent vehicle.
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Table C-1 (continued)
Reference
Kaminski et al.
(1985) and
Silkworth et al.
(1982)
van den Berg et
al. (1983)
van den Berg et
al. (1985)
van den Berg et
al. (1985)
Poiger and
Schlatter (1980)
Matrix/Source
Soot from fire
Incinerator Fly ash
Incinerator fly ash
Incinerator fly ash
2,3,7,8-TCDD on
activated carbon
Species
Guinea pig
Rat
Guinea pig
Hamster
Rat
Dosing
Single gavage
1 9 day feeding
Feeding
60 day feeding
Single gavage
Observation
LDgQ data indicate
soot containing
dioxins and furans
approx. equal in
toxicity to soxhlet
extract of soot in
aqueous vehicle.
Liver retention of
2,3,7,8-TCDD
from ash and ash
extract 1 % and
4% respectively,,
indicating 2,3,7,8-
TCDD approx.
25% as available
from ash as from
extract. Both ash
and extract
retentions are low
compared with
other feeding and
gavage studies.
4%, 1% and 1%
retention of total
dose in liver
following feeding
for 32, 60, and 94
days, respectively.
2% of total dose
retained in liver
following feeding.
<0.1% retention
in liver.
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an elevated temperature. The 2,3,7,8-TCDD added to these soil samples proved to be
highly available (e.g., 40% to 70%).
In one study, soot from a transformer fire containing dioxins and furans proved
similarly toxic to a soxhlet extract of the soot in an aqueous vehicle. However, the soot
extract may have proved more toxic if delivered in corn oil, as was 2,3,7,8-TCDD in the
soil studies. The availability of 2,3,7,8-TCDD and other dioxins and furans from
incinerator fly ash have been addressed by van den Berg et al. (1983, 1985) in extended
feeding studies. In these studies, liver retention of 2,3,7,8-TCDD from either fly ash or fly
ash extract proved low, with availability from fly ash being approximately 25% of that
from the extract.
The individual studies reviewed have a variety of limitations, as discussed in the
preceding text. A notable limitation was that some experiments were conducted using
highly toxic doses of 2,3,7,8-TCDD, so that determination of bioavailability was
complicated by wasting and early death of the test animals. It should also be noted that,
while the relative retention of 2,3,7,8-TCDD in the liver can serve as an appropriate
indication of differences in bioavailability between samples, the percentage of dose found
in the liver only places a lower bound on absorption. This is particularly relevant to
experiments where animals have been maintained for many weeks after dosing and an
undetermined quantity of 2,3,7,8-TCDD has been excreted.
Finally, toxicity data for mixtures for which both toxicity and bioavailability of
individual compounds may vary are difficult to interpret quantitatively in terms of
bioavailability.
As presented in U.S. EPA (1985c), Rose et al. (1976) determined gut absorption of
2,3,7,8-TCDD in a 1:25 mixture of acetone to corn oil (by volume) in the rat. In both
single dose and multiple dose experiments, measured absorption was approximately 85%.
Assuming that absorption from pure corn oil is similar to that from this mixture, and
assuming that absorption in other species for which data are not available is similar, the
85% factor can be applied to the data presented here to obtain an approximate range for
typical 2,3,7,8-TCDD absorption from soil. Using this factor, the estimated relative
bioavailability of 2,3,7,8-TCDD from soil is 25% to 50% and, when compared with corn
oil, provides an estimate of gut absorption of 20% to 40% of ingested 2,3,7,8-TCDD in
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soil. This estimate is comparable with the 20% to 26% absorption from 2,3,7,8-TCDD
treated soil from the work of Poiger and Schlatter (1980).
Recognizing these limitations, the weight of evidence indicates that 2,3,7,8-TCDD
is often highly available from environmental materials. However, in one tested soil sample
the compound was substantially less bioavailable. While the data are too sparse to allow a
prediction as to whether a particular environmental sample will prove more or less
bioavailable, one important suggestion has emerged. In the two samples that have proved
least bioavailable (the Umbreit et al. (1986a) manufacturing site soil sample, and 2,3,7,8-
TCDD on activated carbon tested by Poiger and Schlatter (1980)) the 2,3,7,8-TCDD was
largely resistant to solvent extraction. This was not the case for more bioavailable
materials.
Further research, using short-term experiments in which animals are handled under
identical conditions and are fed dioxins in different media, is needed for an improved
comparison of absorption between different environmental samples. Acutely toxic doses
should be avoided to ensure that tissue concentrations are directly interpretable.
Experiments studying both tissue retention and enzyme induction should prove valuable for
this research. Whole-body levels of 2,3,7,8-TCDD need to be related to liver
concentrations, and the effects of metabolism need to be addressed. The vehicle of
administration has been shown to affect acute 2,3,7,8-TCDD toxicity, and vehicle effects
need to be considered in designing experiments.
C.3 Distribution
Ryan et al. (1985) examined the distribution of 2,3,7,8-TCDD in two humans at
autopsy. On a weight basis, there were 6 ppt of TCDD in fat, 2 ppt in liver and below
levels of detection in kidney and muscle. They reported that on a per lipid basis the levels
were similar between tissues. It is important to note that one of these subjects suffered
from a fatty liver syndrome, possibly resulting in higher levels in the liver than might
normally be found in healthy individuals.
Poiger and Schlatter (1986) estimated that about 90% of the total body burden of
2,3,7,8-TCDD was sequestered in fat. Levels of 2,3,7,8-TCDD averaging 5-10 ppt have
been reported for background populations in St. Louis, MO, by Graham et al. (1986), and
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in Atlanta, GA, and Utah by Patterson et al. (1986). These data are consistent with the
lipid bioconcentrations assumptions made in calculations of daily intakes (vidae supra).
Patterson et al. (1987) developed a high resolution gas chromatographic/high
resolution mass spectrometric analysis for 2,3,7,8-TCDD in human serum. A high
correlation was reported between adipose tissue and serum concentrations when adjusted
for total lipid content. The reader is referred to other documents (U.S/ EPA, 1993;
Schlatter, 1991; Schecter, 1991) for more details on the distribution and elimination.
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