ECAO-CIN-P229 fmi DRAFT
ECAO-CIN-P229
AQ«nev August, 1987
4>EPA Research and
Development
HEALTH AND ENVIRONMENTAL EFFECTS PROFILE
FOR BENZO(K)FLUORANTHENE
Prepared for
OFFICE OF SOLID HASTE AND
EMERGENCY RESPONSE
Prepared by
Environmental Criteria and Assessment Office
Office of Health and Environmental Assessment
U.S. Environmental Protection Agency
Cincinnati, OH 45268
DRAFT: D0 NOT CITE OR °UOTE
m«n*
*eg/on v UH tal Protect/on A
230 South nary 8enc*
Chi«*o, /^reet
This document Is a preliminary draft. It has not been formally released
by the U.S. Environmental Protection Agency and should not at this stage be
construed to represent Agency policy. It 1s being circulated for comments
on Us technical accuracy and policy Implications.
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* UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL CRITERIA AND ASSESSMENT OFFICE
CINCINNATI, OHIO 45268
August 20, 1987
SUBJECT: Health and Environmental Effects Profiles
FROM: Chris DeRosa
Chief _
Chemical Mixtures Assessment Branch, ECAO-C1n
TO: Matthew Straus
Chief, Waste Characterization Branch
Office of Solid Waste (WH-562B)
THRU: Steven D. Lutkenhoff
Acting Director
Environmental Criteria and Assessment Office-CIn
A \ //« QPD 8 IQRT
Preuss /^AiltU&A bt
Office of Health and Environmental Assessment (RD-689)
Attached please find two unbound copies of the Health and Environmental
Effects Profiles (HEEPs) for:
Benzo(k)F1uoranthene (ECAO-C1n-P229)
Benzo(gh1)Perylene (ECAO-Cin-P276)
Phenanthrene (ECAO-Cin-P226)
Pyrene (ECAO-C1n-P277)
These documents represent scientific summaries of the pertinent
available data on the environmental fate and mammalian and aquatic toxldty
of each chemical at an extramural effort of about 5.2K. These documents
received Internal OHEA, OPP and OTS reviews as well as review by two
external scientists. Any part of these document's files (e.g., drafts,
references, reviews) 1s available to you upon request.
Attachments
cc: M. Callahan (RD-689)
P. Durkln, Syracuse Research Corporation (w/enclosures)
W. Farland (RD-689)
R. Hardesty (RD-689)
0. Kooyoomjlan (WH-548B) (w/enclosures)
E. McNamara (PM-211A) (w/enclosures)
D. McK1e (WH-562) (w/enclosures)
J. Moore (RD-689)
M. Lee (WH-562) (w/enclosures)
M. Pfaff (RD-689) (w/enclosures)
R. Rubenstein (WH-562B)
R. Scarberry (WH-562B)
D. V1llar1 (WH-562B) (w/enclosures)
C. Zamuda (WH-548D)
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DISCLAIMER
This report 1s an external draft for review purposes only and does not
constitute Agency policy. Mention of trade names or commercial products
does not constitute endorsement or recommendation for use.
&?,--
11
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PREFACE
Health and Environmental Effects Profiles (HEEPs) are prepared for the
Office of Solid Waste and Emergency Response by the Office of Health and
Environmental Assessment. The HEEPs are Intended to support listings of
hazardous constituents of a wide range of waste streams under Section 3001
of the Resource Conservation and Recovery Act (RCRA), as well as to provide
health-related limits for emergency actions under Section 101 of the Compre-
hensive Environmental Response, Compensation and Liability Act (CERCLA).
Both published literature and Information obtained from Agency program
office files are evaluated as they pertain to potential human health,
aquatic life and environmental effects of hazardous waste constituents. The
literature searched and the dates of the searches are Included In the
section titled "Appendix: Literature Searched." The literature search
material 1s current through November, 1985.
Quantitative estimates are presented provided sufficient data are
available. For systemic toxicants, these Include Reference doses (RfDs) for
chronic exposures. An RfD Is defined as the amount of a chemical to which
humans can be exposed on a dally basis over an extended period of time
(usually a lifetime) without suffering a deleterious effect. In the case of
suspected carcinogens, RfDs are not estimated 1n this document series.
Instead, a carcinogenic potency factor of q-j* Is provided. These potency
estimates are derived for both oral and Inhalation exposures where possible.
In addition, unit risk estimates for air and drinking water are presented
based on Inhalation and oral data, respectively.
Reportable quantities (RQs) based on both chronic toxldty and carclno-
genldty are derived. The RQ 1s used to determine the quantity of a hazard-
ous substance for which notification 1s required In the event of a release
as specified under CERCLA. These two RQs (chronic toxldty and cardnogen-
IcHy) represent two of six scores developed (the remaining four reflect
1gn1tab1l1ty, reactivity, aquatic toxldty and acute mammalian toxldty).
The first draft of this document was prepared by Syracuse Research
Corporation under EPA Contract No. 68-03-3228. The document was subse-
quently revised after reviews by staff within the Office of Health and
Environmental Assessment: Carcinogen Assessment Group, Reproductive Effects
Assessment Group, Exposure Assessment Group, and the Environmental Criteria
and Assessment Office In Cincinnati.
The HEEPs will become part of the EPA RCRA and CERCLA dockets.
111
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EXECUTIVE SUMMARY
^
»
Benzo[k]fluoranthene 1s a pale yellow solid at ambient temperatures. It
1s soluble In ethanol, benzene and acetic acid, but Is practically Insoluble
In water (Weast, 1980; Pearlman et al., 1984). This compound 1s susceptible
to oxidation by ozone, peroxides and other oxldants. Frequently, dlone 1s
the product of such oxidation, although dlmerlzatlon may occur 1n some cases
(NAS, 1972). Benzo[k]fluoranthene Is neither commercially produced nor used
1n the United States (IARC, 1983).
If released to the aquatic environment, benzo[k]fluoranthene 1s not
expected to hydrolyze, oxidize (by R02 radical or ^p) or volatilize
significantly (Mabey et al., 1981; Lyman et al., 1982). A static culture
flask-screening blodegradatlon study with domestic wastewater seed has shown
that benzo[k]fluoranthene can be significantly blodegraded (Fochtman, 1981);
however, mlcroblal oxidation of PAH requires oxygen and will not proceed 1n
anoxlc sediments or water (U.S. EPA, 1986a). In natural water, blodegrada-
^
tlon 1s expected to be slow. In the dissolved state, direct photolysis may
be significant In the water column; however, photolysis will be Insignifi-
cant 1n deep, turbid waters. Adsorption to suspended participate matters
and sediments 1n water Is an Important environmental fate process (U.S. EPA,
1986a). The very low water solubility and high log K of benzo[k]fluor-
anthene suggest a significant potential for bloaccumulatlon; however, PAH
may not appreciably bloconcentrate In organisms such as fish that have
mlcrosomal oxldase because this metabolizes PAH (Santodonato et al., 1981).
Therefore, bloaccumulatlon potential may be dependent on the organism being
considered. The nonvarlabHUy of benzo[k]fluoranthene concentrations 1n
bottom sediment cores In remote lakes (Tan and Helt, 1981) Indicate that
benzo[k]fluoranthene 1s very persistent under anaerobic and dark conditions.
1v
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If released to the atmosphere, benzo[k]fluoranthene will exist primarily In
the partlculate (adsorbed) phase, although vapor phase benzo[k]fluoranthene
may also be present. Vapor phase benzo[k]fluoranthene appears susceptible
to significant transformation by direct photolysis and reaction with ozone
and HO radical (Lane and Katz, 1977; U.S. EPA, 1986b). Partlculate phase
benzo[k]fluoranthene may be more resistant to reactions as Indicated by long
distance transport of the atmospheric aerosol (Tan and He1t, 1981; Lunde and
Bjoerseth, 1977). This compound 1s expected to be physically removed from
the atmosphere by wet and dry deposition (Llgockl et al., 1985a; Tan and
HeVt, 1981). If released to soil, benzo[k]fluoranthene may be susceptible
to slow blodegradatlon under aerobic conditions. Under most conditions, 1t
Is not expected to leach or volatilize and may persist 1n soils.
Human exposure to benzo[k]fluoranthene occurs primarily through the
Inhalation of tobacco smoke and polluted air and by the Ingestlon of contam-
inated food and water (IARC, 1983). The U.S. EPA (1982) reported that -96%
(2700 kkg) PAH are emitted to the atmosphere; of these the total release of
benzo[k]fluoranthene comprises -210 kkg/year. The compound occurs
ubiquitously as a product of Incomplete combustion and naturally In fossil
fuels (IARC, 1983). It has been widely detected 1n drinking water, surface
water, groundwater, rainwater and aquatic sediments (see Tables 3-1 and
3-2), In many foods (Dennis et al., 1983), and 1n the ambient atmosphere
(see Table 3-3). The presence of benzo[k]fluoranthene In food Is a result
of contamination from a polluted environment and formation during the
cooking process (Santodonato et al., 1981; Fazio and Howard, 1983). The
average dietary Intake of benzo[k]fluoranthene In England has been estimated
to be 0.06 yg/day (Dennis et al, 1983). The average Intake of this
compound from drinking water 1n the United States has been estimated to
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be 0.2 ng/day, while the Inhalation Intake 1n the United States has been
estimated to be 0.6-20 ng/day. Its concentration 1n the ambient atmosphere
has apparently been decreasing over the past 25 years (Santodonato et al.,
1981; Gordon and Bryan, 1973). The higher atmospheric levels of this
compound In wintertime compared with summertime may be due to Increased use
of fossil fuel combustion for heating purposes (Greenberg et al., 1985).
Data concerning the toxldty of benzo[k]fluoranthene to aquatic
organisms could not be located 1n the available literature as cited In the
Appendix. The only Information consisted of monitoring data for various
species and locations. Residues 1n species that are commonly eaten by
humans were mussels 1n Norway, 6-69 ng/g (Knutzen and Sortland, 1982), clams
1n Japan, 0.12-0.92 ng/g (Tsujl et al., 1985), and lobster from Eastern
Canada, 0.35 ng/g before Impoundment and 169 ng/g after Impoundment (Dunn
and Fee, 1979).
Information regarding the absorption, distribution or excretion of
benzo[k]fluoranthene could not be located 1n the available literature as
cited 1n the Appendix.
IH vitro studies with rat liver preparations have shown that 8,9-dl-
hydro-8,9-d1hydroxybenzo[k]fluoranthene 1s the major metabolite of benzofk]-
fluoranthene (LaVole et al., 1980; Hecht et al., 1980).
Single Intrapulmonary Injections of 0.16, 0.83 or 4.15 mg benzo[k]fluor-
anthene (99.5% pure) In beeswax trloctanoln mixture Into groups of 27-35
rats produced dose-related squamous cell carcinomas of the lung after life-
time observation (Deutsch-Wenzel et al., 1983). Tumors were not observed 1n
groups of 35 vehicle or untreated controls, and Incidences In the low-,
middle- and high-dose treated groups were 0/35, 3/31 and 12/27, respectively.
v1
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The cardnogenlcHy of benzo[k]fluoranthene has also been evaluated 1n
dermal studies with mice Involving 2 or 3 times weekly applications for life
or 13 months (Wynder and Hoffman, 1959; Habls et al., 1980), 1n mouse-skin
Initiation-promotion assays using TPA as a promoter (LaVole et al., 1982;
Amln et al., 1985), and In a subcutaneous Injection study In which mice were
given three Injections at monthly Intervals (Lacassagne et al., 1963).
Benzo[k]fluoranthene was active as an Initiator 1n the Initiation-promotion
assays and produced Injection site sarcomas In the subcutaneous study.
Interpretation of the subcutaneous Injection study Is complicated, however,
by the lack of vehicle or untreated controls and by an unspecified observa-
tion period.
Benzo[k]fluoranthene Induced mutations In Salmonella typhlmurlum strains
TA100 and TA98 In the presence of exogenous metabolic activation prepara-
tions (LaVole et al., 1980; Hermann et al., 1980; Am1n et al., 1985).
Information regarding chronic or subchronlc toxic effects, teratogenlc-
Hy or other reproductive effects of benzo[k]fluoranthene could not be
located In the available literature as cited In the Appendix.
There was sufficient evidence that benzo[k]fluoranthene 1s carcinogenic
to animals, but the lack of studies by a relevant route precluded derivation
of a q,* based on data specific for benzo[k]fluoranthene. According to
IARC (1983), benzo[k]fluoranthene 1s a Group 2B chemical, meaning that H Is
probably carcinogenic to humans. The corresponding EPA classification 1s
B2. Data were Insufficient to derive an RQ based on chronic toxlclty.
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TABLE OF CONTENTS
Page
1. INTRODUCTION 1
1.1. STRUCTURE AND CAS NUMBER 1
1.2. PHYSICAL AND CHEMICAL PROPERTIES 1
1.3. PRODUCTION DATA 2
1.4. USE DATA 2
1.5. SUMMARY 2
2. ENVIRONMENTAL FATE AND TRANSPORT PROCESSES 3
2.1. WATER 3
2.1.1. Hydrolysis 3
2.1.2. Oxidation 3
2.1.3. Photolysis 3
2.1.4. M1crob1al Degradation 3
2.1.5. Volatilization 4
2.1.6. Adsorption 4
2.1.7. B1oconcentrat1on 4
2.1.8. Persistence 5
2.2. AIR 5
2.2.1. Degradation 6
2.2.2. Physical Removal 7
2.3. SOIL 7
2.3.1. M1crob1al Degradation 7
2.3.2. Chemical Degradation 7
2.3.3. Adsorption 7
2.3.4. Volatilization 8
2.3.5. Persistence 8
2.4. SUMMARY 8
3. EXPOSURE 10
3.1. WATER 10
3.2. FOOD 14
3.3. INHALATION 15
3.4. DERMAL 17
3.5. SUMMARY 17
4. PHARMACOKINETCS 18
4.1. ABSORPTION 18
4.2. DISTRIBUTION 18
4.3. METABOLISM .v . . . . 18
4.4. EXCRETION 18
4.5. SUMMARY 18
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TABLE OF CONTENTS (cont.)
Page
5. EFFECTS ..... 20
5.1. CARCINOGENICITY 20
5.2. MUTAGENICITY 21
5.3. TERATOGENICITY 21
5.4. OTHER REPRODUCTIVE EFFECTS 21
5.5. CHRONIC AND SUBCHRONIC TOXICITY 21
5.6. OTHER RELEVANT INFORMATION 24
5.7. SUMMARY 24
6. AQUATIC TOXICITY 25
6.1. ACUTE 25
6.2. CHRONIC 25
6.3. PLANTS 25
6.4. RESIDUES 25
6.5. SUMMARY 27
7. EXISTING GUIDELINES AND STANDARDS 28
7.1. HUMAN 28
7.2. AQUATIC 29
8. RISK ASSESSMENT 30
9. REPORTABLE QUANTITIES 31
9.1. REPORTABLE QUANTITY (RQ) RANKING BASED ON CHRONIC
TOXICITY 31
9.2. WEIGHT OF EVIDENCE AND POTENCY FACTOR (F=1/ED10)
FOR CARCINOGENICITY 31
10. REFERENCES 34
APPENDIX: LITERATURE SEARCHED. . . 45
1x
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LIST OF TABLES
No.
3-1
3-2
3-3
Title
Benzo[k]fluoranthene Monitoring Data for Various Types
of Water
U.S. Sediment Monitoring Data for Benzo[k]fluoranthene. . . .
U.S. A1r Monitoring Data for Benzo[k]f1uoranthene During
1979-1983
Pag
11
13
16
5-1 Dermal Injection Carc1nogen1c1ty Studies of
Benzo[k]f1uoranthene 22
5-2 MutagenlcHy Testing of Benzo[k]fluoranthene 23
6-1 Monitoring Data for Benzo[k]f1uoranthene In Marine
Species from Norwegian Waters 26
9-1 Benzo[k]fluoranthene: Minimum Effective Dose (MED) and
Reportable Quantity (RQ) 32
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LIST OF ABBREVIATIONS
BCF Bloconcentratlon factor
CAS Chemical Abstracts Service
Koc Soil sorptlon coefficient
Kow Octanol/water partition coefficient
PAH Polycycllc aromatic hydrocarbons
ppb Parts per billion
ppm Parts per million
ppt Parts per trillion
TLV Threshold limit value
TPA Terephthallc acid
TWA Time-weighted average
UV Ultraviolet
x1
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1. INTRODUCTION
1.1. STRUCTURE AND CAS NUMBER
The chemical commonly called benzo[k]fluoranthene 1s also known as
11,12-benzofluoranthene; 8,9-benzfluoranthene; B[k]F; and 11,12-benzo[k]-
fluoranthene (U.S. EPA, 1986a; Santodonato et al.f 1981). The structure,
empirical formula, molecular weight and CAS Registry number for this
chemical are as follows:
Empirical formula: C?0H12
Molecular weight: 252.32
CAS Registry number: 207-08-9
1.2. PHYSICAL AND CHEMICAL PROPERTIES
Benzo[k]fluoranthene Is a pale yellow crystalline solid at ambient
temperatures. It Is soluble In ethanol, benzene and acetic add, but prac-
tically Insoluble In water (Weast, 1980). Some of the physical properties
of this compound are listed below:
Melting point: 217°C
Boiling point: 480°C
Water solubility at 25°C: 0.76
Log K
ow
Vapor pressure at 25°C:
6.04-6.44
(estimated)
9.59X10""11 mm Hg
Weast, 1980
Weast. 1980
Pearlman et a!.,
1984
Readman et al., 1982;
Ruepert et al., 1985
Santodonato et al.,
1981
0865p
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03/23/87
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Henry's Law constant: 4.19xlO~8 atmos-mVmol
(estimated)
Since this compound 1s a PAH, H Is expected to be reasonably chemically
reactive. It can undergo substitution and addition reaction, and 1s suscep-
tible to oxidation by ozone, peroxides and other oxldants (NAS, 1972).
Frequently, dlone 1s the product of such oxidation, although dlmerlzatlon
may occur In some cases (NAS, 1972).
1.3. PRODUCTION DATA
Benzo[k]fluoranthene 1s neither commercially produced nor Imported Into
the United States (IARC, 1983; USITC. 1984).
1.4. USE DATA
There 1s no known commercial use of benzo[k]fluoranthene (IARC, 1983).
Small amounts of this compound are used for scientific research.
1.5. SUMMARY
Benzo[k]fluoranthene 1s a pale yellow solid at ambient temperatures. It
1s soluble in ethancl, benzene and acetic add, but 1s practically Insoluble
1n water (Weast, 1980; Pearlman et al., 1984). This compound Is susceptible
to oxidation by ozone, peroxides and other oxldants. Frequently, dlone 1s
the product of such oxidation, although dlmerlzatlon may occur 1n some cases
(NAS, 1972). Benzo[k]fluoranthene Is neither commercially produced nor used
In the United States (IARC, 1983).
0865p -2- 10/31/86
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2. ENVIRONMENTAL FATE AND TRANSPORT PROCESSES
2.1. HATER
2.1.1. Hydrolysis. Benzo[k]fluoranthene contains no hydrolyzable
functional groups; therefore, hydrolysis 1s not expected to be significant
(Mabey et al., 1981).
2.1.2. Oxidation. The rate constants for the oxidation of benzo[k]fluor-
anthene with photochemlcally produced R02 radical and 10_ have been
estimated to be 5xlOa and 4xl07 M""1 hour'1, respectively, at 25°C
(Mabey et al., 1981). Assuming the RO- radical and 10p concentrations
of natural waters are 10~» and 10~12 M {Mabey et al., .1981), respec-
tively, the respective half-lives are estimated to be 15.8 and 2.0 years.
Therefore, these reactions are not environmentally significant.
2.1.3. Photolysis. In a cyclohexane solvent, benzo[k]fluoranthene
exhibits UV absorption maxima at 295, 306, 358, 370, 378 and 400 nm (IARC,
1983); therefore, direct photolysis 1n sunlight Is a possibility. Muel and
Saguem (1985) exposed a 28.6 yg/SL n-heptane solution of benzo[k]fluor-
anthene to 1 month of November sunlight and found that 72% had degraded
after the exposure period. This would suggest that direct photolysis In the
dissolved state 1n the water column 1s possible.
The majority of benzo[k]fluoranthene will be present, however, 1n the
partlcle-sorbed state 1n water (Section 2.1.6.) and may not readily
photolyze. Therefore, photolysis may be relatively more significant 1n
shallow, clear water than 1n deep, turbid water. Overall, photodegradatlon
may not be as Important as other processes 1n water.
2.1.4. M1crob1al Degradation. Fochtman (1981) examined the blodegrad-
abllHy of benzo[k]fluoranthene 1n a static culture flask-screening proce-
dure 1n which 1% of the compound was dissolved 1n an emulslfler and added to
0865p -3- 10/31/86
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the bacterial suspension (domestic wastewater seed) at a concentration of
1-2 ppm. The suspension was Incubated for 7 days. A fresh bacterial
suspension was prepared weekly using the seed from the previous week and the
procedure was continued for 28 days. Approximately 54% of the benzo[k]-
fluoranthene was typically degraded during a 7-day Incubation.
In natural waters, PAH with four or more aromatic rings are degraded
slowly by microbes, and blodegradatlon 1s considered to be the ultimate fate
process (U.S. EPA, 1986a); however, the concentrations of microorganisms
capable of oxidizing the hydrocarbons are extremely low 1n all but heavily
polluted fresh and marine waters, and most species of microorganisms cannot
use PAH as a sole carbon source. M1crob1al oxidation of PAH requires oxygen
and will not proceed 1n anoxlc sediments or water (U.S. EPA, 1986a).
2.1.5. Volatilization. Based on a water solubility of 0.00076 ppm at
25°C (Pearlman et al., 1984} and a vapor pressure of 9.59X10"11 mm Hg at
25°C (Santodonato et al., 1981), Henry's Law constant for benzo[k]fluor-
anthene can be estimated to be 4.2xlO~8 atm-mVmol. This value of
Henry's Law constant Indicates that benzo[k]fluoranthene 1s not expected to
volatilize significantly from the aquatic environment (Lyman et al., 1982).
2.1.6. Adsorption. The estimated K value of benzo[k]fluoranthene 1s
nearly 1 million (Section 2.3.3.) and the widespread detection of benzo[k]-
fluoranthene 1n various sediments (Section 3.1.) Indicates that adsorption
to suspended partlculate matters and sediments 1s an Important environmental
fate process. Movement by sediments 1s considered to be an Important
transport process for PAH (U.S. EPA, 1986a).
2.1.7. B1oconcentrat1on. Estimation of BCF can be made from the follow-
ing equations (Lyman et al., 1982):
log BCF = 0.76 log KQW - 0.23 (2-1)
log BCF = 2.791-0.564 log water solubility (1n ppm) (2-2)
0865p -4- 10/31/86
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Based on a water solubility of 0.00076 ppm at 25°C (Pearlman et al., 1984)
and a log KQW of 6.12 (U.S. EPA, 1986b), the BCF values estimated from
Equations 2-1 and 2-2 for benz-o[k]fluoranthene are 35,500 and 26,400,
respectively, which suggest significant bloaccumulatlon potential. PAH,
however, may not appreciably bloconcentrate 1n organisms such as fish that
have mlcrosomal oxldase because this enzyme metabolizes PAH (Santodonato et
al., 1981). Therefore, the bloaccumulatlon potential may be dependent on
the organism being considered.
2.1.8. Persistence. Tan and He1t (1981) monitored sediment cores taken
from Woods Lake In the remote Adirondack Forest of upstate New York for
various PAH. The following benzo[k]fluoranthene concentrations (ng/g dry
sediment) were found at various depths: 560 (0-4 cm), 180 (4-8 cm), 11
(8-11 cm), 4 (12-17 cm), 7 (24-26 cm), 5 (42-44 cm) and 8 (80-84 cm). The
constancy 1n the concentration of benzo[k]fluoranthene In the deeper sedi-
ment 'cores Indicates that the compound 1s very persistent under anaerobic
and dark conditions present 1n the deep sediment cores.
2.2. AIR
Benzo[k]fluoranthene exists 1n the ambient atmosphere predominantly 1n
partlculate-assodated form. From their ambient air monitoring data
collected 1n Portland, OR, Llgockl et al. (1985a,b) found the combined mean
benzo[b,j,k]fluoranthene concentration 1n the vapor phase was 0.11 ng/m3,
while the combined mean concentration of the same three compounds In the
partlculate phase was 3.4 ng/m3. Yamasakl et al. (1985) conducted a
laboratory experiment 1n which ambient airborne partlculates were exposed to
PAH-free air for 48 hours at 9.1°C and found that -95% of the benzo[k]-
fluoranthene remained adsorbed to the partlculates. Cautreels and Van
Cauwenberghe (1978) found that the concentration of benzo[k]fluroanthene 1n
0865p -5- 10/31/86
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the participate phase was -12 times higher than Us concentration 1n the gas
phase. In a monitoring study of the air over the tropical and equatorial
eastern Atlantic Ocean, Marty et al. (1984) detected benzo[k]fluoranthene 1n
the partlculates but not 1n the vapor phase. The form In which benzo[k]-
fluoranthene exists In the atmosphere has a significant bearing on Its
environmental fate. In general, the compound will be less reactive In the
participate phase than 1n the gas phase.
2.2.1. Degradation. Lane and Katz (1977) used simulated atmospheric
conditions to expose pure benzo[k]fluoranthene to ozone, a Quartzllne lamp
with spectral distribution very close to solar distribution between 295 and
400 nm, or a combination of both light and ozone. The half-life using UV
light only was 14.1 hours, while the half-life with ozone (0.19 ppm) 1n the
dark was 34.9 hours; a combination of both light and ozone resulted In a
half-life of 3.9 hours. These results suggest that a combination of photol-
ysis 1n the presence of ozone may Induce faster transformation of benzo[k]-
fluoranthene than either of the processes alone. It 1s, however, difficult
to assess the significance of this reaction In the ambient atmosphere
because the concentrations of 0., used In these experiments were higher
than normally found In the atmosphere.
The half-life for the vapor phase reaction of benzo[k]fluoranthene with
photochemlcally produced HO radical has been estimated to be ~1 day at 25°C
assuming an average atmospheric HO radical concentration of 8xl05
molecules/cm3 (U.S. EPA, 1986b).
Data specific to the degradation of partlculate adsorbed benzo[k]fluor-
anthene could not be located In the available literature as cited 1n the
Appendix. Behymer and HHes (1985) examined the atmospheric photodegrada-
tlon of 15 other PAHs that were adsorbed to various substrates (silica gel,
0865p -6- 03/23/87
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alumina, fly ash and carbon black) by using a laboratory photoreactor to
simulate atmospheric conditions. In general, significant photolysis was
observed when the adsorbing substrate was either silica gel, alumina or fly
ash; however, carbon black adsorption clearly stabilized the phototransfor-
matlon of the PAH. In the atmosphere, adsorption to stabilizing substrates
will allow PAH to be transported over long- distances 1n the atmospheric
aerosol because of Increased persistence. Lunde and BJoerseth (1977)
reported that benzo[k]fluoranthene was transported In " the atmospheric
aerosol from England to Norway.
2.2.2. Physical Removal. Removal of adsorbed benzo[k)fluoranthene from
the atmosphere may occur by wet and dry deposition. Partlculate-assoclated
benzo[k]fluoranthene has been detected In rainwater {L1gock1 et al., 1985b).
The presence of benzo[k]flouranthene 1n lake sediments In the Adirondack
Forest In New York has been attributed to physical Deposition (Tan and He1t,
1981). Dissolved benzo[k]fluoranthene has also been detected 1n rainwater
(Llgockl et al., 1985a), suggesting that physical removal by washout or
dissolution Into clouds with subsequent rainfall may be possible.
2.3. SOIL
2.3.1. H1crob1al Degradation. Benzo[k]fluoranthene may possibly undergo
slow blodegradatlon 1n soil under aerobic conditions (see Section 2.1.4.);
however, additional experimental data are required to predict the rate at
which blodegradatlon may occur.
2.3.2. Chemical Degradation. No data are available to Indicate that
benzo[k]fluoranthene Is transformed chemically In natural soils.
2.3.3. Adsorption. Estimation of K can be made from the following
regression equations (Lyman et al., 1982):
log K =0.44-0.54 log water solubility (1n mol fraction) (2-3)
log KQC=1.00 log KQW-0.21 (2-4)
0865p -7- 03/23/87
-------
Based on a water solubility of 0.76 yg/8. (Pearlman et al., 1984) at 25°C
and a log KQW of 6.12 (U.S. EPA, 19865), the KQC values estimated from
Equations 2-3 and 2-4 for benzo[k]fluoranthene are 0.96 and 0.81 million,
respectively, which suggest soil Immobility. The detection of benzo[k]-
fluoranthene 1n several groundwaters (Section 3.1.), however, Indicates that
leaching can occur. This leaching may occur under certain conditions, such
as from soils with low organic content (e.g., sand) or high porosity, or
from sites that have been exposed to spills or chemical wastes containing
benzo[k]fluoranthene. Benzo[k]fluoranthene Is not expected to leach In soil
under most other conditions.
2.3.4. Volatilization. Volatilization of benzo[k]fluoranthene from soils
1s not .expected to be an Important process (S1ms and Overcash, 1983).
2.3.5. Persistence. When seven applications of PAH-contalnlng oil sludge
was amended to a sandy loam soil over a 2-year period, and then monitored
for an additional 1.5 years, 30% of the total benzo[k]fluoranthene applica-
tion remained after the total 3.5 years (Bossert et al., 1984). Therefore,
this compound Is expected to persist 1n most soils.
2.4. SUMMARY
If released to the aquatic environment, benzo[k]fluoranthene 1s not
expected to hydrolyze, oxidize (by ROp radical or ^O^) or volatilize
significantly (Mabey et al., 1981; Lyman et al., 1982). A static culture
flask-screening blodegradatlon study with domestic wastewater seed has shown
that benzo[k]fluoranthene can be significantly blodegraded (Fochtman, 1981);
however, microblal oxidation of PAH requires oxygen and will not proceed 1n
anoxlc sediments or water (U.S. EPA, 1986a). In natural water, blodegrada-
tlon Is expected to be slow. In the dissolved state, direct photolysis may
0865p -8- 03/23/87
-------
be significant 1n the water column; however, photolysis will be Insignifi-
cant 1n deep, turbid waters. Adsorption to suspended partlculate matters
and sediments In water 1s an Important environmental fate process (U.S. EPA,
1986a). The very low water solubility and high log K of benzo[k]fluor-
anthene suggest a significant potential for bloaccumulatlon; however, PAH
may not appreciably bloconcentrate 1n organisms such as fish that have
mlcrosomal oxldase because this metabolizes PAH (Santodonato et al., 1981).
Therefore, bloaccumulatlon potential may be dependent on the organism being
considered. The nonvar1abH1ty of benzo[k]fluoranthene concentrations In
bottom sediment cores 1n remote lakes (Tan and Belt, 1981) Indicate that
benzo[k]fluoranthene 1s very persistent under anaerobic and dark conditions.
If released to the atmosphere, benzo[k]fluoranthene will exist primarily In
the partlculate (adsorbed) phase, although vapor phase benzo[k]fluoranthene
may also be present. Vapor phase benzo[k]fluoranthene appears susceptible
to significant transformation by direct photolysis and reaction with ozone
and HO radical {Lane and Katz, 1977; U.S. EPA, 1986b). Partlculate phase
benzo[k]fluoranthene may be more resistant to reactions as Indicated by long
distance transport of the atmospheric aerosol (Tan and Helt, 1981; Lunde and
Bjoerseth, 1977). This compound 1s expected to be physically removed from
the atmosphere by wet and dry deposition (Llgockl et al., 1985a; Tan and
He1t, 1981). If released to soil, benzo[k]fluoranthene may be susceptible
to slow blodegradatlon under aerobic conditions. Under most conditions, It
1s not expected to leach or volatilize and may persist 1n soils.
0865p -9- 03/23/87
-------
3. EXPOSURE
Human exposure to benzo[k]fluoranthene occurs primarily through the
Inhalation of tobacco smoke and polluted air and by the Ingestlon of
contaminated food and water (IARC, 1983). The compound occurs ubiquitously
as a product of Incomplete combustion and occurs naturally 1n fossil fuels
(IARC, 1983).
3.1. HATER
Table 3-1 lists various benzo[k]fluoranthene monitoring data for drink-
Ing water, groundwater, surface water and rainwater; Table 3-2 lists
sediment monitoring data for various U.S. locations. In an analysis of the
U.S. EPA STORET database, benzo[k]fluoranthene was detected In 1.8% of 1248
effluents and 3.0% of 873 surface waters (Staples et al., 1985). Grlest
(1980) detected benzo[b,j and k]fluoranthene at a concentration of 23.0
yg/g (dry sediment) 1n the sediment of an effluent channel from a coking
plant. Benzo[k]fluoranthene was also Identified 1n the effluent from a
sewage treatment plant at levels <12 ppt (Kveseth et al., 1982).
Shackelford and Keith (1976) detected benzo[k]fluoranthene 1n effluents from
chemical plants, sewage treatment plants and In raw sewage. In the prelimi-
nary findings of the U.S. EPA Nationwide Urban Runoff Program, benzo[k]-
fluoranthene was detected In the stormwater runoff from Bellevue, WA, and
Lake Qulnslgamond, MA, at levels of 4-10 ppb (Cole et al., 1984).
In general, PAH can be released to water from Industrial and municipal
treatment plant effluents, atmospheric fallout and precipitation, road
runoff (tire wear, bitumen and asphalt surfaces, cracked lubricating oils)
and marine shipping and harbor oil (Santodonato et al, 1981). Sorrell et
0865p -10- 10/31/86
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0865p
-12-
10/31/86
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TABLE 3-2
U.S. Sediment Monitoring Data for Benzo[k]fluoranthene
Concentration
(ng/g)
12-26a
8-UOa
88-250b
16-550b
2.9-86 (mean)c
560 (0-4 cm depth)
180 (4-8 cm depth)
8 (80-84 cm depth)
120 (0-4 cm depth)
110 (4-8 cm depth)
2 (71-75 cm depth)
14-696
Location
Washington State
(river bottom sediment)
Columbia River
(suspended sediment)
Cayuga Lake, NY
(deepwater sediment)
Cayuga Lake, NY
(littoral sediment)
Lake Pontchartraln, LA
Woods Lake, NY
Woods Lake, NY
Woods Lake, NY
Sagamore Lake, NY
Sagamore Lake, NY
Sagamore Lake, NY
Penobscot Bay,
Gulf of Maine
Sampling
Date
1979-1980
1979-1980
1978
1978
1980
NR
NR
NR
NR
NR
NR
1982
Reference
Prahl
et al., 1984
He1t, 1985
McFall
et al., 1985
Tan and
He1t, 1981
Johnson
et al., 1985
aBenzo[j+k]fluoranthene
bBenzo[b+k]fluoranthene
GUnspec1f1ed Isomers
NR = Not reported
0865p
-13-
10/31/86
-------
al. (1980) suggested that benzo[k]fluoranthene and other PAHs may contami-
nate drinking water supplies as a result of coal tar or asphalt-based
materials used to line transmission pipes and storage tanks.
Based on the monitoring data from Table 3-1, the concentration of benzo-
[k]fluoranthene In drinking water may be on the order of 0.1 ppt (ng/i).
Assuming an average dally water Intake of 2.0 i for an adult, the Intake
of benzo[k]fluoranthene from drinking water 1s estimated to be 0.2 ng/day.
3.2. FOOD
In general, PAHs found 1n food are present as a result of contamination
from a polluted environment or are formed during the cooking process
(Santodonato et al., 1981; Fazio and Howard, 1983); minute amounts of the
chemical may originate from geochemlcal or blosynthetlc sources (Fazio and
Howard, 1983).
Fazio and Howard (1983) reported the detection of benzo[k]fluorathene 1n
oysters, very dark coffee (0-0.8 jig/kg) and cooked Japanese horse mackerel
(0.2 yg/kg).
Dennis et al. (1983) examined total diet samples of food groups In
England and found the following mean benzo[k]fluoranthene concentrations (1n
vg/kg) In the various food groups: cereals (0.08), meat (0.01), fish
(0.04), oils and fats (0.32), fruit and sugar (0.02), vegetables
(0.02-0.07), beverages (0.003) and milk (0.003). The total benzo[k]fluor-
anthene dietary load was estimated to be 0.06 ug/person/day (Dennis et
al., 1983). Based on the monitoring of total diet market basket samples
collected 1n the Netherlands, Vaessen et al. (1984) estimated the median
Intake of benzo[b+j+k]fluoranthene to be 0.1 yg/day.
0865p -14- 03/23/87
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3.3. INHALATION
Table 3-3 lists recent (1979^-1983) U.S. ambient air monitoring data for
benzo[k]fluoranthene; In general, the mean average concentration detected 1s
<1.0 ng/m3. Ambient air monitoring data for benzo[k]fluoranthene from
1958 to the mid-1970s (Santodonato et a!., 1981; Gordon and Bryan, 1973)
suggest that the ambient atmospheric load of benzo[k]fluoranthene has been
generally decreasing over the past 25 years, possibly because of decreases
In coal consumption for residential heating and Industrial uses. Improved
disposal methods of solid wastes, restrictions on open burning and Improved
efficiencies for stationary Incineration and combustion operations and
Improvement of pollution control. The higher atmospheric levels of benzo-
[k]fluoranthene In wintertime verus summertime air In New Jersey (see Table
3-3) may be a reflection of the Increased use of fossil fuel combustion for
heating purposes.
Assuming the approximate average ambient air concentrations of benzo[k]-
fluoranthene In the United States range from 0.03-1.0 ng/m3 (see Table
3-3) and an Individual air Intake of 20 ma/day, the average Intake Is
estimated to be 0.6-20 ng/day. Matsumoto and Kashlmoto (1985) used Japanese
monitoring data to estimate an average dally Intake of 15 ng.
In general, -96% (27000 kkg) PAH are emitted to the atmosphere. Of the
atmospheric emissions combustion of fossil fuels (oil, coal), gasoline and
dlesel exhaust, open burning (agricultural burning, forest fires, structural
fires, refuse burning), the burning of wood especially for residential
heating (NRC, 1983) and municipal/Industrial Incineration comprise -99% of
the benzo[a]pyrene group PAHs. U.S. EPA (1982) reported an estimate of 210
kkg/year benzo[k]fluoranthene released to the environment.
0865p -15- 08/11/87
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TABLE 3-3
U.S. A1r Monitoring Data for Benzo[k]f"luoranthene During 1979-1983
Concentration
(ng/m3)
0.18 (average)*
0.19 (average)*
0.41 (average)*
0.11
(mean gas-phase)
3.4 (average
participate phase)*
0.03-0.3
(participate phase)
0.03-0.20 (mean)
0.28-0.97 (mean)
0.04-0.11 (mean)
0.08-0.63 (mean)
Location
Qulllayute, WA
Sequlm, WA
Seattle, WA
Portland, OR
Portland, OR
Columbia, SC
4 cities - New Jersey
4 cities - New Jersey
4 cities - New Jersey
4 cities - New Jersey
Sampling
Date
1979
1979
1979
1984
1984
1982
Summer 1981
Winter 1982
Summer 1982
Winter 1983
Reference
Prahl et al.,
1984
L1gock1
et al., 1985a
Llgockl
et al., 1985b
Keller and
Bldleman, 1984
Harkov et al.,
1984
Greenberg
et al., 1985
*Benzo[b+j *k]fluoranthenes
0865p
-16-
10/31/86
-------
Benzo[k]fluoranthene was Identified In mainstream cigarette smoke (0.7-12
ng/dgarette) and mainstream marijuana smoke (11 ng/c1garette) (IARC,
1983). The concentration of benzo[k]fluoranthene detected In various fly
ash samples ranged from not detected to 23 ng/g (Elceman et a!., 1981).
3.4. DERMAL
Pertinent dermal monitoring data could not be located In the available
literature as cited 1n the Appendix.
3.5. SUMMARY
Human exposure to benzo[k]fluoranthene occurs primarily through the
Inhalation of tobacco smoke and polluted air and by the Ingestlon of contam-
inated food and water (IARC, 1983). The compound occurs ubiquitously as a
product of Incomplete combustion and naturally In fossil fuels (IARC, 1983).
It has been widely detected In drinking water, surface water, groundwater,
rainwater and aquatic sediments (see Tables 3-1 and 3-2), 1n many foods
(Dennis et a!., 1983), and 1n the ambient atmosphere (see Table 3-3). The
presence of benzo[k]fluoranthene 1n food 1s a result of contamination from a
polluted environment and formation during the cooking process (Santodonato
et al., 1981; Fazio and Howard, 1983). The average dietary Intake of benzo-
[kjfluoranthene 1n England has been estimated to be 0.06 tig/day (Dennis et
al., 1983). The average Intake of this compound from drinking water In the
United States has been estimated to be 0.2 ng/day, while the Inhalation
Intake 1n the United States has been estimated to be 0.6-20 ng/day. Its
concentration In the ambient atmosphere has apparently been decreasing over
the past 25 years {Santodonato et al., 1981; Gordon and Bryan, 1973). The
higher atmospheric levels of this compound 1n wintertime compared with
summertime may be due to Increased use of fossil fuel combustion for heating
purposes (Greenberg et al., 1985).
0865p -17- 08/11/87
-------
4. PHARHACOKINETICS
4.1. ABSORPTION
Specific data regarding the gastrointestinal or pulmonary absorption of
benzo[k]fluoranthene could not be located In the available literature as
cited In the Appendix. Data' from other structurally related PAH suggest,
however, that benzo[k]fluoranthene 1s absorbed readily from the gastrointes-
tinal tract (Rees et a!., 1971) and lungs" (Kotln et al., 1969; Valnlo et
al., 1976). In general, PAH are highly Upld soluble and can pass across
epithelial membranes (U.S. EPA, 1980a).
4.2. DISTRIBUTION
Pertinent data regarding the distribution of benzo[k]fluoranthene could
not be located 1n the available literature as dted 1n the Appendix.
4.3. METABOLISM
8,9-D1hydro-8,9-d1hydroxy benzo[k]fluoranthene has been Identified as
the major metabolite of benzo[k]fluoranthene In j£ vitro metabolism studies
with rat liver S-9 preparations (LaVole et al., 1980; Hecht et al., 1980).
Benzo[k]fluoranthene-8,9-epox1de was not Isolated but considered to be the
Hkely precursor of the 8,9-d1hydrod1ol. Indirect evidence (mutagenldty)
suggests that the 8,9-dlhydrodlol may form a dlhydrodlol-epoxlde.
4.4. EXCRETION
Pertinent data regarding the excretion of benzo[k]fluoranthene could not
be located 1n the available literature as cited 1n the Appendix.
4.5. SUMMARY
Information regarding the absorption, distribution or excretion of
benzo[k]fluoranthene could not be located 1n the available literature as
cited 1n the Appendix.
0865p -18- 08/11/87
-------
In vitro studies with rat liver preparations have shown that 8,9-dl-
hydro-8,9-d1hydroxybenzo[k]fluoranthene Is the major metabolite of benzo[k]-
fluoranthene (LaVole et al., 1980; Hecht et al., 1980).
0865p -19- 08/11/87
-------
5. EFFECTS
5.1. CARCINOGENICITY
Studies evaluating the tumorlgenic potential of orally-administered
benzo[k]fluoranthene could not be located 1n the available literature as
cited 1n the Appendix.
Mixtures of heated beeswax and trloctanoln (1:1) containing 0.16, 0.83'
or 4.15 mg benzo[k]fluoranthene (99.5% pure) were Injected Into the left
lung lobes of 35, 31 and 27 female Osborne-Mendel rats, respectively, after
thoracotomy (Deutsch-Wenzel et a!., 1983). Additional groups of 35 rats
served as vehicle, untreated and positive (0.1, 0.3 or 1.0 mg benzo[a]pyrene
controls. Necropsies were performed on all rats at the time of natural
death or when moribund, but hlstologlcal examinations were limited to the
lungs and organs showing gross abnormalities. Median survival times were
114, 95, 98, 104 and 118 weeks In the low-dose, middle-dose, high-dose,
vehicle and untreated control groups, respectively. Median survival times
for positive controls were 111, 77 and 54 weeks at Us low, medium and high
dose benzo[a]pyrene respectively. Squamous cell carcinomas of the lung
occurred 1n the benzo[k]fluoranthene-treated mice at Incidences of 0/35 (low
dose), 3/31 (middle dose) and 12/27 (high dose). Lung tumors were not
observed In either the vehicle or untreated control groups but did occur
(carcinomas) at dose-related Incidences 1n the positive controls (4/35,
21/35, 33/35). The dose-related pulmonary tumor response In the
benzo[k]fluoranthene-treated mice was considered to be a treatment-related
effect.
The carclnogenldty of benzo[k]fluoranthene was also evaluated In dermal
studies with mice Involving 2 or 3 times weekly applications for life or 13
months (Wynder and Hoffman, 1959; Habls et al., 1980), 1n mouse-skin Initia-
tion-promotion assays using TPA as a promoter (LaVole et al., 1982; Am1n et
0865p -20- 08/11/87
-------
al., 1985) and 1n a subcutaneous Injection study In which mice were given
three Injections at monthly Intervals (Lacassagne et al., 1963). As
detailed In Table 5-1, benzo[k]fluoranthene was active as an Initiator 1n
the Initiation-promotion assays and produced Injection site sarcomas In the
subcutaneous study. Interpretation of the subcutaneous Injection study 1s
complicated, however, by the lack of vehicle or untreated controls and by an
unspecified observation period.
5.2. MUTAGENICITY
Benzo[k]fluoranthene was reported to Induce mutations 1n Salmonella
typh1mur1um strains TA100 (LaVole et al., 1980; Am1n et al., 1985) and TA98
(Hermann et al., 1980) when assayed In the presence of rat liver S-9
metabolic activation preparations (Table 5-2). The chemical was not tested
In the absence of S-9.
Additional genotoxlclty data for benzo[k]fluoranthene could not be
located 1n the available literature as cited In the Appendix.
5.3. TERATOGENICITY
Pertinent data regarding the teratogenldty of benzo[k]fluoranthene
could not be located In the available literature as cited In the Appendix.
5.4. OTHER REPRODUCTIVE EFFECTS
Pertinent data regarding other reproductive effects of benzo[k]fluor-
anthene could not be located 1n the available literature as cited 1n the
Appendix.
5.5. CHRONIC AND SUBCHRONIC TOXICITY
Pertinent data regarding the of benzo[k]fluoranthene could not be
located In the available literature as cited 1n the Appendix.
0865p -21- 08/11/87
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-------
5.6. OTHER RELEVANT INFORMATION
Dally IntrapeMtoneal Injections of 0.05-40 mg/kg benzo[k]fluoranthene
In arachls oil for 3 days produced dose-related Increases In liver aryl
hydrocarbon monooxygenase activity 1n rats (Schmoldt et al., 1981).
5.7. SUMMARY
Single Intrapulmonary Injections of 0.16, 0.83 or 4.15 mg benzo[k]fluor-
anthene {99.5% pure) 1n beeswax trloctanoln mixture Into groups of 27-35
rats produced dose-related squamous cell carcinomas of the lung after life-
time observation (Deutsch-Henzel et al., 1983). Tumors were not observed In
groups of 35 vehicle or untreated controls, and Incidences 1n the low-,
middle- and high-dose treated groups were 0/35, 3/31 and 12/27, respectively.
The cardnogenlclty of benzo[k]fluoranthene has also been evaluated In
dermal studies with mice Involving 2 or 3 times weekly applications for life
or 13 months (Wynder and Hoffman, 1959; Habls et al., 1980), In mouse-skin
Initiation-promotion assays using TPA as a promoter (LaVole et al., 1982;
Am1n et al., 1985), and 1n a subcutaneous Injection study In which mice were
given three Injections at monthly Intervals (Lacassagne et al., 1963).
Benzo[k]fluoranthene was active as an Initiator In the Initiation-promotion
assays and produced Injection site sarcomas In the subcutaneous study.
Interpretation of the subcutaneous Injection study Is complicated, however,
by the lack of vehicle or untreated controls and by an unspecified observa-
tion period.
Benzo[k]fluoranthene Induced mutations In Salmonella typhlmurlum strains
TA100 and TA98 In the presence of exogenous metabolic activation prepara-
tions {LaVole et al., 1980; Hermann et al., 1980; Amln et al., 1985).
Information regarding chronic or subchronlc toxic effects, teratogenlc-
1ty or other reproductive effects of benzo[k]fluoranthene could not be
located 1n the available literature as cited 1n the Appendix.
0865p -24- 08/11/87
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6. AQUATIC TOXICITY
6.1. ACUTE
Pertinent data regarding the acute toxldty of benzo[k]fluoranthene to
aquatic organisms could not be located In the available literature as cited
1n the Appendix.
6.2. CHRONIC
Pertinent data regarding the chronic toxldty of benzo[k]fluoranthene to
aquatic organisms could not be located In the available literature as dted
1n the Appendix.
6.3. PLANTS
Pertinent data regarding the effects of benzo[k]fluoranthene on aquatic
plants could not be located 1n the available literature as dted 1n the
Appendix.
6.4. RESIDUES
The only Information about benzo[k]fluoranthene and aquatic organisms
consisted of residue monitoring data for various species and locations.
Table 6-1 contains data from the study by Knutzen and Sortland (1982), who
examined marine species from polluted areas In Norway; the highest concen-
trations were reported 1n mussels, HytHus edulls (6-69 ng/kg). Tsujl et
al. (1985) reported that clams (unspecified species) collected In Japanese
waters contained 0.12-0.92 ng/g (presumably wet weight)
benzo[k]fluoranthene. Haccubbln et al. (1985) found that the stomach
contents of white suckers, Catostomus commersonl. from eastern Lake Erie
contained benzo[k]fluoranthene at concentrations of 2-11 ng/g (wet weight).
Dunn and Fee (1979) found that lobsters, Homarus amerlcanus. caught In
eastern Canada had an average concentration of 0.35 ng/g wet weight;
however, after Impoundment, the body burden was 169 ng/g.
0865p -25- 08/11/87
-------
TABLE 6-1
Monitoring Data for Benzo[k]fluoranthene 1n Marine Species
from Norwegian Waters*
Species
Tissue Concentration
dry weight)
INVERTEBRATE
Mussel, Mytllus edulls
Periwinkle, LUtorlna llttorea
Limpet, Patella vulgata
Sponge, Hallchondrla panlcea
PLANTS
Bladder wrack, Fucus veslculosus
Knotted wrack, Ascophyllum nodosum
Toothed wrack, Fucus serratus
Lam1nar1a saccharlna
Ceramlum rubrum
6-69
3-20
trace-39
40
trace-66
trace
4-15
4
6
*Source: Knutzen and Sortland, 1982
0865p
-26-
10/31/86
-------
It 1s a common practice to store lobsters for some time before sending them
to market, and frequently the enclosures are made wHh creosote-treated
wood, a possible source of benzo[k]fluoranthene and other PAH. The 500-fold
difference In benzo[k]fluoranthene levels between freshly caught and
Impounded lobsters Indicate that the Impoundment procedure may result 1n a
significant Increase In human exposure to benzo[k]fluoranthene.
6.5. SUMMARY
Data concerning the toxlclty of benzo[k]fluoranthene to aquatic
organisms could not be located 1n the available literature as cited In the
Appendix. The only Information consisted of monitoring data for various
species and locations. Residues In species that are commonly eaten by
humans were mussels In Norway, 6-69 ng/g (Knutzen and Sortland, 1982), clams
In Japan, 0.12-0.92 ng/g (Tsujl et a!., 1985), and lobster from Eastern
Canada, 0.35 ng/g before Impoundment and 169 ng/g after Impoundment (Dunn
and Fee, 1979).
0865p -27- 03/23/87
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7. EXISTING GUIDELINES AND STANDARDS
7.1. HUNAN
Exposure criteria and TLVs have been developed for PAH as a class, as
well as for several Individual PAH. OSHA (1985) set an 8-hour TWA concen-
tration limit of 0.2 mg/ma for the benzene-soluble fraction of coal tar
pitch volatlles (anthracene, benzo[a]pyrene, phenanthrene, acrldlne, chry-
sene, pyrene). NIOSH (1977) recommended a concentration limit for coal tar,
coal tar pitch, creosote and mixtures of these substances of 0.1 mg/ma of
the cyclohexane-extractable fraction of the sample, determined as a 10-hour
TWA. NIOSH (1977) concluded that these specific coal tar products, as well
as coke oven emissions, are carcinogenic and can Increase the risk of lung
and skin cancer 1n workers. NIOSH (1977) also recommended a celling limit
for exposure to asphalt fumes of 5 mg airborne part1culates/m3 of air.
Ambient water quality criteria, which specify concentration limits
Intended to protect humans against adverse health effects, have been recom-
mended for PAH. U.S. EPA (1980a) recommended a concentration limit of 28
ng/l for the sum of all carcinogenic PAH 1n ambient water. This value 1s
based on a mathematical extrapolation of the results from studies with mice
treated orally with benzo[a]pyrene and acknowledges the conservative assump-
tion that all carcinogenic PAH are equal 1n potency to benzo[a]pyrene. On
the basis of the animal bloassay data, dally consumption of water containing
28 ng/l of carglnogenlc PAH over an entire lifetime 1s estimated to keep
the lifetime risk of cancer development <1/100,000 chances.
The EPA has not recommended an ambient water quality criterion for
noncardnogenlc PAH as a class. U.S. EPA (1980a) acknowledged that data
suitable for quantitative risk assessment of noncardnogenlc PAH are essen-
tially nonexistent.
0865p -28- 10/31/86
-------
7.2. AQUATIC
Guidelines and standards for the protection of aquatic biota from the
effects of benzo[k]fluoranthene 1n particular could not be located 1n the
available literature as cited 1n the Appendix. U.S. EPA (1980a) noted, how-
ever, that acute toxldty to saltwater aquatic life occurred at concentra-
tions of 300 vg/l PAH 1n general and would occur at lower concentrations
In species more sensitive than those tested. U.S. EPA (1980a) concluded
that the database was Inadequate to make generalizations or recommend
criteria regarding chronic toxldty or acute toxldty to freshwater biota
of PAH.
0865p -29- 10/31/86
-------
8. RISK ASSESSMENT
Single Intrapulmonary Injections of 0.16, 0.83 or 4.15 mg benzo[k]-
fluoranthene (99.5% pure) In beeswa,x-tr1octano1n mixture Into groups of
27-35 rats produced dose-related squamous cell carcinomas of the lung after
lifetime observation (Deutsch-Wenzel et al., 1983). Tumors were not
observed 1n groups of 35 vehicle or untreated controls, and Incidences 1n
the low-, middle- and high-dose treated groups were 0/35, 3/31 and 12/27,
respectively. Incidences 1n the positive control were 4/35, 21/35 and 33/35
at 0.1, 0.3 and 1.0 mg of benzo(a)pyrene, respectively.
The carclnogenlclty of benzo[k]fluoranthene was also evaluated 1n dermal
studies with mice Involving 2 or 3 times weekly applications for life or 13
months (Hynder and Hoffman, 1959; Habls et al., 1980); 1n mouse-skin Initia-
tion-promotion assays using TPA as a promoter (LaVole et al., 1982; Amln et
al., 1985) and In a subcutaneous Injection study In which mice were given
three Injections at monthly Intervals (Lacassagne et al., 1963). As
detailed In Table 5-1, benzo[k]fluoranthene was active as an Initiator 1n
the Initiation-promotion assays and produced Injection site sarcomas 1n the
subcutaneous study. Interpretation of the subcutaneous Injection study 1s
complicated, however, by the lack of vehicle or untreated controls and by an
unspecified observation period.
Benzo[k]fluoranthene Induced mutations In Salmonella typhlmurlum strains
TA100 and TA98 1n the presence of exogenous metabolic activation prepara-
tions (LaVole et al., 1980; Hermann et al., 1980; Amln et al., 1985).
The results of the above studies provide sufficient evidence to conclude
that benzo[k]fluoranthene 1s carcinogenic to experimental animals. Calcula-
tion of a carcinogenic potency factor (q,*) specifically for benzofk]-
fluoranthene Is precluded, however, by the lack of appropriate oral or
Inhalation studies.
0865p -30- 08/07/87
-------
9. REPORTABLE QUANTITIES
9.1. REPORTABLE QUANTITY (RQ) RANKING BASED ON CHRONIC TOXICITY
Information regarding chronic or subchronlc toxic effects, teratogenclty
or other reproductive effects of benzo[k]fluoranthene could not be located
In the available literature as cited In the Appendix. Calculation of an RQ
ranking for benzo[k]fluoranthene based on chronic toxldty 1s therefore
precluded by the lack of appropriate data (Table 9-1).
9.2. HEIGHT OF EVIDENCE AND POTENCY FACTOR (F=1/ED1Q} FOR CARCINOGENICITY
Single Intrapulmonary Injections of 0.16, 0.83 or 4.15 mg benzo[k]fluor-
anthene (99.5% pure) In beeswax-trloctanoln mixture Into groups of 27-35
rats produced dose-related squamous cell carcinomas of the lung after life-
time observation (Deutsch-Wenzel et al., 1983). Tumors were not observed 1n
groups of 35 vehicle or untreated controls, and Incidences 1n the low-,
middle- and high-dose treated groups were 0/35, 3/31 and 12/27, respectively.
The carclnogenlcHy of benzo[k]fluoranthene has also been evaluated In
dermal studies with mice Involving 2 or 3 times weekly applications for life
or 13 months (Wynder and Hoffman, 1959; Habls et al., 1980), In mouse-skin
Initiation promotion assays using TPA as a promoter (LaVole et al., 1982;
Am1n et al., 1985) and 1n a subcutaneous Injection study 1n which mice were
given three Injections at monthly Intervals (Lacassagne et al., 1963). As
detailed 1n Table 5-1, benzo[k]fluoranthene was active as an Initiator In
the Initiation-promotion assays and produced Injection site sarcomas In the
subcutaneous study. Interpretation of the subcutaneous Injection study Is
complicated, however, by the lack of vehicle or untreated controls and by an
unspecified observation period.
Benzo[k]fluoranthene Induced mutations 1n Salmonella typhlmuMum strains
TA100 and TA98 1n the presence of exogenous metabolic activation prepara-
tions (LaVole et al., 1980; Hermann et al., 1980; Am1n et al., 1985).
0865p -31- 08/06/87
-------
TABLE 9-1
Benzo[k]fluoranthene
Minimum Effective Dose (MED) and Reportable Quantity (RQ)
Route:
Dose:
Effect:
Reference:
RVd:
RVe:
Composite Score:
RQ: Data are not sufficient for deriving an RQ
0865p -32- 08/06/87
-------
The results of the above studies provided sufficient evidence to
conclude that benzo[k]fluoranthene Is carcinogenic to experimental animals.
Calculation of a carcinogenic potency factor (F) specifically for benzo[k]-
fluoranthene Is precluded, however, by the lack of appropriate oral or
Inhalation studies.
IARC (1983) has judged benzo[k]fluoranthene to be probably carcinogenic
to humans (Group 26). The corresponding EPA classification would be Group
B2 (U.S. EPA, 1986c).
0865p -33- 08/07/87
-------
10. REFERENCES
Am1n, S., H. Nalband, G. Balanlka, K. Hu1e and S. Hecht. 1985. Mutagenlc-
Hy and tumor Initiating activity of methylated benzo[k]fluoranthenes.
Cancer Lett. 26: 343-347.
Behymer, T.D. and R.A. HHes. 1985. Photolysis of polyaromatlc hydro-
carbons adsorbed on simulated atmospheric particles. Environ. Scl. Techno!.
19: 1004-1006.
Bossert, I., W.M. Kachel and R. Bartha. 1984. Fate of hydrocarbons during
oily sludge disposal 1n soil. Appl. Environ. M1crob1ol. 47: 763-767.
Cautreels, W. and K. Van Cauwenberghe. 1978. Experiments on the distribu-
tion of organic pollutants between airborne partlculate matter and the
corresponding gas phase. Atmos. Environ. 12: 1133-1141.
Cole, R.H., R.E. Frederick, R.P. Healy and R.G. Rolan. 1984. Preliminary
findings of the priority pollutant monitoring project of the nationwide
urban runoff program. J. Water Pollut. Control Fed. 56: 898-908.
Dennis, M.J., R.C. Massey, D.J. McWeeney, M.E. Knowles and D. Watson. 1983.
Analysis of polycycllc aromatic hydrocarbons 1n UK total diets. Food Chem.
Toxlcol. 21: 569-574.
0865p -34- 08/06/87
-------
Deutsch-Wenzel, R.P., H. Brune, G. Grimmer, G. Dettbarn and J. M1sf1eld.
1983. Experimental studies In rat lungs on the cardnogenldty and dose-
response relationships of eight frequently occurring environmental poly-
cycllc aromatic hydrocarbons. J. Natl. Cancer Inst. 71: 539-544.
Dunn, B.P and J. Fee. 1979. Polycycllc aromatic hydrocarbon carcinogens In
commercial seafoods. 3. Fish Res. Board Can. 36(12): 1469-1476.
Elceman, G.A., R.E. Clement and F.W. Karasek. 1981. Variations 1n concen-
trations of organic compounds Including PCDDS and polynuclear aromatic
hydrocarbons In fly ash from a municipal Incinerator. Anal. Chem. 53:
955-959.
Fazio, T. and J.W. Howard. 1983. Polycycllc aromatic hydrocarbons In
foods. In: Handbook of Polycycllc Aromatic Hydrocarbons, A.' Bjorseth, Ed.
Marcel Dekker Inc., New York, NY. p. 461-505.
Fochtman, E.G. 1981. B1odegradat1on and carbon adsorption of carcinogenic
and hazardous organic compounds. U.S. EPA, Cincinnati, OH. EPA
600/S2-81-032. p. 38.
Gordon, B.J. and R.J. Bryan. 1973. Patterns In airborne polynuclear hydro-
carbon concentrations at four Los Angeles sites. Environ. Scl. Techno!. 7:
1050-1053.
Great Lakes Water Quality Board. 1983. An Inventory of chemical substances
Identified 1n the Great Lakes Ecosystem Volume 1 - Summary. Report to the
Great Lakes Water Quality Board, Windsor, Ontario, Canada, p. 195.
0865p -35- 08/06/87
-------
Greenberg, A., F. Darack, R. Harkov, P. L1oy and J. Dalsey. 1985. Poly-
cycllc aromatic hydrocarbons In New Jersey: A comparison of winter and
summer concentrations over a 2-year period. Atmos. Environ. 19: 1325-1339.
Grlest, W.H. 1980. Multlcomponent polycycllc aromatic hydrocarbon analysis
of Inland water and sediment. ITK Hydrocarbon Halogen. Hydrocarbon Aquatic
Environ., B.K. Afghan and D. Mackay, Ed. Plenum Press, New York, NY.
p. 173-183.
Habls, M., D. Schmaehl and J. Mlsfeld. 1980. Local carclnogenlclty of some
environmentally relevant polycycllc aromatic hydrocarbons after lifelong
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0865p -36- 08/06/87
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Hermann, H., J.P. Ourand, J.H. Charpentler, et al. 1980. Correlations of
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t
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*.
Keller, C.D. and T.F. Bldleman. 1984. Collection of airborne polycycllc
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0865p -37- 08/06/87
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Kveseth, K., B. Sortland and T. Bokn. 1982. Polycycllc aromatic hydro-
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0865p -38- 08/06/87
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Lunde, G. and A. Bjoerseth. 1977. Polycycllc aromatic hydrocarbons In
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15-29, 4-9, 5-4, 5-10.
*
Mabey, W.R., 3.H. Smith, R.T. Podoll, et al. 1981. Aquatic fate process
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0865p -40- 08/07/87
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Readman, J.W., R.F.C. Mantoura, M.M. Rhead and L. Brown. 1982. Aquatic
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0865p -41- 08/07/87
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Schmoldt, A., 0. Jacob and G. Grimmer. 1981. Dose-dependent Induction of
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0865p -42- 08/06/87
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APPENDIX
LITERATURE SEARCHED
This profile Is based on data Identified by computerized literature
searches of the following:
GLOBAL
TSCATS
CASR online (U.S. EPA Chemical Activities Status Report)
CAS online STN International
TOXLINE
TOXBACK 76
TOXBACK 65
RTECS
OHM TADS
STORET
SRC Environmental Fate Data Bases
SANSS
AQUIRE
TSCAPP
NTIS
Federal Register
These searches were conducted In April, 1986. In addition, hand searches
were made of Chemical Abstracts (Collective Indices 6 and 7), and the
following secondary sources were reviewed:
ACGIH (American Conference of Governmental Industrial Hyg1en1sts).
1986. Documentation of the Threshold Limit Values and Biological
Exposure Indices, 5th ed. Cincinnati, OH.
ACGIH (American Conference of Governmental Industrial Hyglenlsts).
1985-1986. TLVs: Threshold Limit Values for Chemical Substances
and Physical Agents In the Workroom Environment with Intended
Changes for 1985-1986. Cincinnati, OH. 114 p.
Clayton, G.D. and F.E. Clayton, Ed. 1981. Patty's Industrial
Hygiene and Toxicology, 3rd rev. ed., Vol. 2A. John Wiley and
Sons, NY. 2878 p.
Clayton, G.D. and F.E. Clayton, Ed. 1981. Patty's Industrial
Hygiene and Toxicology, 3rd rev. ed., Vol. 2B. John WHey and
Sons, NY. p. 2879-3816.
0865p
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08/06/87
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Clayton, 6.D. and F.E. Clayton, Ed. 1982. Patty's Industrial
Hygiene and Toxicology, 3rd rev. ed.. Vol. 2C. John Wiley and
Sons, NY. p. 3817-5112.
Grayson, H. and D. Eckroth, Ed. 1978-1983. K1rk-0thmer Encyclo-
pedia of Chemical Technology, 3rd ed. John Wiley and Sons, NY. 23
Volumes.
Hamilton, A. and H.L. Hardy. 1974. Industrial Toxicology, 3rd ed.
Publishing Sciences Group, Inc., Littleton, MA. 575 p.
IARC (International Agency for Research on Cancer). IARC Mono-
graphs on the Evaluation of Carcinogenic Risk of Chemicals to
Humans. WHO, IARC, Lyons, France.
NTP (National Toxicology Program). 1986. Toxicology Research and
Testing Program. Chemicals on Standard Protocol. Management
Status.
Ouellette, R.P. and J.-A. King. 1977. Chemical Week Pesticide
Register. McGraw-Hill Book Co., NY.
Sax, N.I. 1979. Dangerous Properties of Industrial Materials, 5th
ed. Van Nostrand Relnhold Co., NY.
SRI (Stanford Research Institute). 1984. Directory of Chemical
Producers. Menlo Park, CA.
U.S. EPA. 1985. Status Report on Rebuttable Presumption Against
Registration (RPAR) or Special Review Process. Registration Stan-
dards and the Data Call In Programs. Office of Pesticide Programs,
Washington, DC.
U.S. EPA. 1985. CSB Existing Chemical Assessment Tracking System.
Name and CAS Number Ordered Indexes. Office of Toxic Substances,
Washington, DC.
USITC (U.S. International Trade Commission). 1983. Synthetic
Organic Chemicals. U.S. Production and Sales, 1982, USITC Pub!.
1422, Washington, DC.
Verschueren, K. 1983. Handbook of Environmental Data on Organic
Chemicals, 2nd ed. Van Nostrand Relnhold Co., NY.
Wlndholz, M., Ed. 1983. The Merck Index, 10th ed. Merck and Co.,
Inc., Rahway, NJ.
Worthing, C.R. and S.B. Walker, Ed. 1983. The Pesticide Manual.
British Crop Protection Council. 695 p.
U.S. Environmental Protection Agency
Region V, Library
230 South Dearborn Street
6°604
-46- 08/06/87
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In addition, approximately 30 compendia of aquatic toxlclty data were
reviewed, Including the following:
Battelle's Columbus Laboratories. 1971. Water Quality Criteria
Data Book. Volume 3. Effects of Chemicals on Aquatic Life.
Selected Data from the Literature through 1968. Prepared for the
U.S. EPA under Contract No. 68-01-0007. Washington, DC.
Johnson, W.W. and H.T. Flnley. 1980. Handbook of Acute Toxlclty
of Chemicals to F1sh and Aquatic Invertebrates. Summaries of
Toxlclty Tests Conducted at Columbia National Fisheries Research
Laboratory. 1965-1978. U.S. Dept. Interior, F1sh and Wildlife
Serv". Res. Publ. 137, Washington, DC.
McKee, J.E. and H.W. Wolf. 1963. Water Quality Criteria, 2nd ed.
Prepared for the Resources Agency of California, State Water
Quality Control Board. Publ. No. 3-A.
Plmental, D. 1971. Ecological Effects of Pesticides on Non-Target
Species. Prepared for the U.S. EPA, Washington, DC. PB-269605.
Schneider, B.A. 1979. Toxicology Handbook. Mammalian and Aquatic
Data. Book 1: Toxicology Data. Office of Pesticide Programs, U.S.
EPA, Washington, DC. EPA 540/9-79-003. NTIS PB 80-196876.
0865p -47- 08/06/87
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