Toxicity Profiles
Toxicity Summary for BENZENE
NOTE:
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- EXECUTIVE SUMMARY
- 1. INTRODUCTION
- 2. METABOLISM AND DISPOSITION
- 2.1 ABSORPTION
2.2 DISTRIBUTION
2.3 METABOLISM
2.4 EXCRETION
- 3. NONCARCINOGENIC HEALTH EFFECTS
- 3.1 ORAL EXPOSURES
3.2 INHALATION EXPOSURES
3.3 OTHER ROUTES OF EXPOSURE
3.4 TARGET ORGANS/CRITICAL EFFECTS
- 4. CARCINOGENICITY
- 4.1 ORAL EXPOSURES
4.2 INHALATION EXPOSURES
4.3 OTHER ROUTES OF EXPOSURE
4.4 EPA WEIGHT-OF-EVIDENCE
4.5 CARCINOGENICITY SLOPE FACTORS
- 5. REFERENCES
September 1992
Prepared by: Mary Lou Daugherty, M.S., Chemical Hazard Evaluation and Communication Group, Biomedical and Environmental Information Analysis Section, Health and Safety Research Division*, , Oak Ridge, Tennessee.
Prepared for OAK RIDGE RESERVATION ENVIRONMENTAL RESTORATION PROGRAM.
*Managed by Martin Marietta Energy Systems, Inc., for the U.S. Department of Energy under
Contract No. DE-AC05-84OR21400.
EXECUTIVE SUMMARY
Benzene is absorbed via ingestion, inhalation, and skin application. Experimental data indicate
that animals can absorb up to 95% of oral doses and that humans can absorb up to 80% of inhaled
benzene (after 5 minutes of exposure) (Sabourin et al., 1987; Srobova et al., 1950). Humans may absorb
benzene vapors through the skin as well as the lungs; of the total dose absorbed by the two routes, an
estimated 22-36% enters the body through the skin (Susten, 1985).
Autopsy of a youth who died while sniffing benzene revealed that the chemical was distributed
to the urine, stomach, bile, liver, kidney, abdominal fat, and brain (Winek and Collum, 1971). The depots
for benzene and its metabolites in animals are similar to those in humans, and in addition, include the
fetus and placenta, bone marrow, Zymbal gland, and oral and nasal cavities (Ghantous and Danielsson,
1986; Rickert et al., 1979; Low et al., 1989).
Numerous studies indicate that the metabolism of benzene is required for its toxicity (Kalf et
al., 1987). The liver is the main site for the metabolism of benzene; the bone marrow, a minor site
(ATSDR, 1992). Phenol, hydroquinone, catechol, and benzene oxide are the major metabolites (Kalf et
al, 1987; Snyder, 1987). The metabolite(s) of benzene that are responsible for its toxicity have not been
positively identified, but likely candidates include muconaldehyde, quinones, and free radicals generated
by oxidizing enzymes (Henderson et al., 1989; Snyder, 1987).
Benzene is eliminated either unchanged in expired air or as metabolites in the urine (ATSDR,
1992). The proportions of the administered dose excreted by each route and the half-times for
excretion are dependent on route, dose, and duration of exposure.
Lethal oral doses of benzene are estimated to be 10 mL in humans; oral LD50 values for benzene
in rats range from 0.93 to 5.96 g/kg (Cornish and Ryan, 1965; Withey and Hall, 1975). These data
indicate that benzene is of low acute toxicity (O'Bryan and Ross, 1986).
Limited data show that nonlethal oral doses of benzene can impact the nervous, hematological,
and immunological systems. Ingested benzene produces symptoms of neurotoxicity at acute doses of
2 mL for humans and 325 mg/kg for rats (Thienes and Haley, 1972; Clayton and Clayton, 1981; Cornish
and Ryan, 1965). A four week exposure of mice to >=8 mg of benzene/kg/day in the drinking water
induced the synthesis and catabolism of monoamine neurotransmitters and produced dose-related
decreases in red-blood cell parameters and lymphocyte numbers (Hsieh et al., 1988b). Rats and mice
that were treated with benzene by gavage for 103 weeks developed a dose-related lymphocytopenia
(LOAEL, 25 mg/kg/day) and mice had hyperplasia of the bone marrow and lymphoid depletion of the
splenic follicles and thymus (100 mg/kg/day) (Huff et al., 1989).
Inhalation of benzene vapor concentrations of 20,000 ppm for 5-10 minutes can be fatal to
humans; death results from central nervous system depression (Clayton and Clayton, 1981). The
estimated LC50 value for the rat is 13,700 ppm (Drew and Fouts, 1974).
As with orally administered benzene, the targets for nonlethal concentrations of inhaled benzene
include the nervous, hematological, and immunological systems. Neurological symptoms in humans may
appear at exposure concentrations of 700 ppm (Clayton and Clayton, 1981). In animals, 1 week of
exposure to 300 ppm induced behavioral effects (Drew and Fouts, 1974), and one to four weeks of
exposure to benzene concentrations ranging from 21-50 ppm suppressed the bone marrow (NOAEL, 10
ppm) (Cronkite et al., 1985; Toft et al., 1982), the cellular immune response (NOAEL, 10 ppm) (Rosenthal
and Snyder, 1985), and the humoral immune response (LOAEL, 50 ppm) (Aoyama, 1986).
Subchronic and chronic exposures to benzene vapors induce a progressive depletion of the bone
marrow and dysfunction of the hematopoietic system. Early symptoms of bone marrow depression
include leukopenia, anemia or thrombocytopenia, or a combination of the three (Snyder, 1984). A group
of workers exposed to benzene concentrations of 30 and 150 ppm for 4 months to 1 year had increased
incidences of pancytopenia (Aksoy et al., 1971; Aksoy et al., 1972; Aksoy and Erdem, 1978). A group of
patients who had been exposed to benzene concentrations of 150 to 650 ppm for 4 months to 15 years
exhibited severe blood dyscrasias and eight of the 32 patients died with thrombocytopenic hemorrhage
and infection (Aksoy et al., 1972). The human data are supported by animal data showing bone marrow
suppression in mice and rats exposed to benzene concentrations ranging from 10 ppm for 24 weeks to
300 ppm for 13 weeks (Baarson et al., 1984; Ward et al., 1985).
Benzene may also have long-term effects on the central nervous system. Workers exposed to
benzene for 0.5 to 4 years exhibited EEG changes and atypical sleep activity consistent with
neurotoxicity (Kellerova, 1985). Others exposed to benzene concentrations of 210 ppm for 6-8 years
had peripheral nerve damage (Baslo and Aksoy, 1982).
In humans, benzene crosses the placenta and is present in the cord blood in amounts equal to
those in maternal blood (Dowty et al., 1976); however, studies of the effects of benzene on human
reproduction and development have been confounded by the presence of other chemicals in the
environment (USAF, 1989). Benzene does produce developmental effects (fetal toxicity, but not
malformations) in the offspring of treated animals, mostly at maternally toxic doses (Nawrot and
Staples, 1979; Seidenberg et al., 1986; Keller and Snyder, 1988).
Reference doses/concentrations for benzene have not been established. An oral risk assessment
for benzene will be reviewed by an EPA work group and an inhalation risk assessment is currently under
review (U.S. EPA, 1992a).
Benzene is carcinogenic in humans and animals by inhalation and in animals by the oral route
of exposure. Occupational exposure to benzene has been associated mainly with increased incidences
of acute myeloblastic or erythroblastic leukemias and chronic myeloid and lymphoid leukemias among
workers (Aksoy, 1989). Workers at risk were exposed in one study to 8-hour TWA concentrations ranging
from 10 to 100 ppm (Rinsky et al., 1981) and in another to 8-hour TWA concentrations ranging from
<2 to >25 ppm (Ott et al., 1978). In a historical prospective mortality study of chemical workers, Yin
et al. (1987) described a dose-response relationship between exposure to benzene and lymphatic and
hematopoietic cancers, which adds strength to the association between exposure in the workplace and
cancer development. Studies in animals have demonstrated an association between oral and inhalation
exposure to benzene and the development of a variety of tumors, including lymphoma and carcinomas
of the Zymbal gland, oral cavity, mammary gland, ovaries, lung, and skin (Huff et al., 1989; Maltoni et
al., 1989). In one study C57Bl/BNL mice had increased incidences of leukemia, lymphoma, and solid
tumors after exposure to 300 ppm for only 16 weeks (Cronkite et al., 1985; Cronkite, 1983).
Based on "several studies of increased incidence of nonlymphocytic leukemia from occupational
exposure, increased incidence of neoplasia in rats and mice exposed by inhalation and gavage, and some
supporting data", benzene has been placed in the EPA weight-of-evidence classification A, human
carcinogen (U.S. EPA, 1991a). The oral and inhalation slope factors for benzene are 2.9E-2
(mg/kg/day)-1 and the oral and inhalation unit risk values are 8.3E-7 and 8.3E-6, respectively, based
on the studies of Ott et al. (1978), Rinsky et al. (1981), and Wong et al. (1983) (U.S. EPA, 1992a,b).
1. INTRODUCTION
Benzene (C6H6, CAS No. 71-43-2) is a volatile, colorless liquid with a characteristic "aromatic"
odor (Snyder, 1987). Benzene has a molecular weight of 78.12, a vapor pressure (at 26C) of 100 mm
Hg, a vapor density of 2.77, and a density (at 20C) of 0.87865 g/mL (Snyder, 1987).
Benzene is used primarily in the production of other chemicals such as ethylbenzene, cumene,
and cyclohexane (ATSDR, 1989). Benzene has also been used as a solvent, but this use is declining,
coincidental with the replacement of benzene with other organic solvents (ATSDR, 1989). Benzene is
emitted into the workplace and the environment (aquatic, terrestrial, and atmospheric) from industrial
and other manmade sources, including gasoline from filling stations, smoking tobacco products, and auto
exhaust (ATSDR, 1989).
Workers employed in industries that produce or use benzene are at risk for exposure to high
levels of the chemical. According to OSHA (1985), an estimated 17,336 workers are potentially exposed
to 8-hour time-weighted-average (TWA) concentrations of benzene ranging from 5.1 to 10 ppm. More
recent data were not available. Exposure of the general population to benzene may occur in residential
areas near chemical manufacturing sites; exposure has also been associated with the ingestion of
contaminated food and drinking water, cigarette smoking, and pumping gas. Estimated daily intake
values for 70-kg adults average 2.86 g/kg/day for drinking water, 7.8 g/kg/day for smoking 20
cigarettes/day, and 2.76 g/kg/day for exposure to emissions from nearby chemical manufacturing
plants (ATSDR, 1989).
Because of benzene's high vapor pressure, inhalation is the most likely route of exposure to the
chemical, particularly in the workplace. OSHA (1987) has set air exposure limits for benzene of 1 ppm
(8-hour TWA) and 5 ppm (15-minute STEL).
2. METABOLISM AND DISPOSITION
2.1. ABSORPTION
No data were found for the oral absorption of benzene in humans. Rabbits given 340-500 mg/kg
benzene orally absorbed at least 90% of the dose and rats and mice given 0.5-150 mg/kg absorbed >97%
of the dose (Sabourin et al., 1987).
Human and animal studies indicate that inhaled benzene is absorbed rapidly. Srbova et al.
(1950) studied respiratory uptake in humans inhaling benzene concentrations of 47-110 ppm for 2-3
hours. Uptake (the difference between the amount of benzene in inhaled and exhaled air expressed
as a percent of the concentration in inhaled air) was 70-80% during the first 5 minutes of exposure and
approximately 50% by 1 hour (Srbova et al., 1950). For another group of volunteers, exposed to 52-62
ppm benzene for 4 hours, respiratory uptake was approximately 47% and retention (benzene that was
absorbed and not excreted through the lungs) was approximately 30% (Nomiyama and Nomiyama, 1974a).
Animal data also confirm that benzene is absorbed rapidly through the lungs. In dogs exposed to
benzene concentrations of 200-1300 ppm, blood levels of the chemical reached a steady state in about
1 hour (Schrenk et al., 1941).
Recent studies have indicated that absorption of benzene through the skin my be a significant
route of exposure, particularly for workers. Susten et al. (1985) estimated that employees in tire-building operations could absorb 4-8 mg of benzene/day through intact skin; this is approximately 22-40% of the total dose absorbed via skin and inhalation. These data are supported by the work of Blank
and McAuliffe (1985), who calculated that 17% of the total absorbed dose of ambient benzene (skin plus
inhalation) could be absorbed by the skin.
2.2. DISTRIBUTION
No data were found for the distribution of orally administered benzene in humans. In
rats, the pattern of distribution for ingested benzene is similar to that of inhaled benzene. Low et al.
(1989) observed that the bone marrow and adipose tissue were depots for doses of benzene >=15 mg/kg.
With regard to the unconjugated metabolites, hydroquinone appeared in the liver, kidney, and blood, and
phenol appeared in the oral cavity, nasal cavity and kidney. The conjugated metabolites, phenyl sulfate,
hydroquinone glucuronide, and trans, trans-muconic acid, appeared in the blood, bone marrow, oral
cavity, kidney and liver, whereas phenyl glucuronide was present in the Zymbal gland and nasal cavity.
Case studies have provided most of the information regarding the distribution of inhaled benzene
in humans. Benzene was present in tissue samples taken at autopsy from a youth who died while
sniffing the reagent grade chemical. The specimens contained the following amounts of benzene: 2.0
mg% in blood, 3.9 mg% in brain, 1.6 mg% in liver, 1.9 mg% in kidney, 1 mg% in stomach, 1.1 mg% in bile,
2.23 mg% in abdominal fat, and 0.06 mg% in urine (Winek and Collom, 1971).
In pregnant mice exposed to benzene concentrations of 2,000 ppm for 10 minutes, the parent
compound and its metabolites were found in lipid-rich tissues, such as brain and fat, and in well-perfused tissues such as liver and kidney, as well as in the fetuses and placenta (Ghantous and
Danielsson, 1986). In rats exposed to 500 ppm benzene, levels of the chemical reached a steady-state
concentration in the blood (11.5 g/mL) within 4 hours, in the fat (164.4 g/g) within 6 hours, and in
the bone marrow (37 g/g) within 2 hours (Rickert et al., 1979). The kidney, lung, liver, brain, and
spleen also contained benzene. After 6 hours of exposure, metabolites of benzene (phenol, catechol, and
hydroquinone) were detected in the blood and in the bone marrow, where levels of the metabolites
exceeded those in the blood. The levels of phenol in the blood and bone marrow declined more rapidly
than did those of catechol or hydroquinone. This suggests that catechol and hydroquinone may
accumulate.
For 14C-benzene applied to the skin of male rats, the kidney, liver, and treated skin were the
target sites for radioactivity (Skowronski et al., 1988).
2.3. METABOLISM
Numerous studies indicate that the metabolism of benzene is required for its toxicity (reviewed
by Kalf et al., 1987). The liver is the major site for the transformation of benzene, the bone marrow
a minor site. It appears that benzene metabolism (qualitative at least) is similar for different routes
of administration and for different species, including humans (ATSDR, 1992). Benzene can stimulate its
own metabolism, and can therefore increase the rate of the formation of toxic metabolites (ATSDR,
1992).
Phenol, hydroquinone, catechol, and benzene oxide are the major metabolites of benzene (Kalf
et al., 1987). Snyder (1987) summarized the complex scheme for the metabolism of benzene: "The
metabolism of benzene initially involves the formation of hydroxylated benzenes. Only small amounts
of ring-opened metabolites are formed due to the stability of the aromatic ring. The enzymes
catalyzing these hydroxylations are the mixed function cytochrome monooxygenase enzymes, which are
found predominantly in the liver, but also in the bone marrow, which is the putative target organ of
benzene toxicity. The oxidizing moieties produced by the enzymes probably involve a cascade of reactive
oxygen species, including free radicals. These reactive oxygen species may contribute to benzene-induced cell damage. The substitution of hydroxyl groups onto the benzene ring proceeds by at least
two pathways: an indirect pathway through an epoxide intermediate and a direct pathway involving
direct insertion of hydroxyl groups. Both pathways appear to proceed through an enone intermediate.
The hydroxylated benzenes can undergo conjugation reactions to form glucuronides and sulfate esters,
or can be further oxidized to benzoquinones. The benzoquinones are probably the electrophilic species
which covalently bind to macromolecules including DNA, and therefore may be the ultimate carcinogenic
forms of benzene."
Figure 1 illustrates the pathways related to the biotransformation of benzene. One pathway of
detoxification is via the formation of glutathione conjugates of benzene oxide and its subsequent
metabolism to phenyl mercapturic acid, which is excreted via the bile (Henderson et al., 1989; Sabourin
et al., 1988); another pathway of detoxification is via the formation of water-soluble urinary metabolites,
which are the glucuronide or sulfate conjugates of phenol (Henderson et al., 1989). Phenol can also
undergo metabolism to catechol and trihydroxy benzene that are excreted as sulfate or glucuronide
conjugates (ATSDR, 1992). The formation of two proposed toxic metabolites, benzoquinone and
muconaldehyde, proceeds through the further oxidation of hyroquinone, and the opening of the ring of
benzene oxide followed by aromatization, respectively (Henderson et al., 1989).
Recent metabolic studies on benzene have focused on identifying both the moiety that initially
oxidizes benzene and the electrophilic benzene metabolite(s) that react with cellular macromolecules
to initiate damage (Snyder, 1987). Previously, a benzene epoxide was the suspect cytotoxic species,
but the results of recent studies indicate that the benzoquinones and possibly free radicals generated
by the oxidizing enzymes are the more likely candidates (Snyder, 1987).
2.4. EXCRETION
Benzene is eliminated either unchanged in expired air or as metabolites in the urine (ATSDR,
1992). The combined results of two studies show that human volunteers exposed to 47-110 ppm of the
chemical for 2-4 hours excreted 16-41.6% of absorbed benzene through the lungs within 5-7 hours
(Nomiyama and Nomiyama, 1974a; Srbova et al., 1950). In one of the studies, the subjects excreted only
0.07-0.2% of the retained benzene in the urine (Srbova et al., 1950).
Porteus and Williams (1949) and Parke and Williams (1953, 1954) quantified the excretion of
benzene and its metabolites by rabbits given oral doses of 14C-labeled benzene. The animals eliminated
approximately 43% of the dose as unchanged benzene in exhaled air and about 35% of the radioactivity
in the urine. The isolated urinary metabolites consisted of phenol (68% of radioactivity), hydroquinone
(14%), catechol (6%), trans,trans-muconic acid (4%), phenylmercapturic acid (1%) and 1,2,4-trihydroxybenzene (1%). Similar patterns of excretion have been observed for humans (Teisinger et al.,
1952), cats and dogs (Oehme, 1969), rats (Cornish and Ryan, 1965), and mice (Longacre et al., 1981).
In humans and rats, the excretion of benzene in expired air appears to biphasic. The half-times for
benzene eliminated by rats in expired air were 0.7 hours for the rapid phase and 13.1 hours for the slow
phase (Rickert et al., 1979). The half-times increase with duration of exposure.
During a 32-hour period following application of 0.0024 mg/cm2 14C-benzene to the skin, human
volunteers excreted approximately 0.0023% of the dose in the urine (Franz, 1984). Excretion of the label
was greatest in the first 2 hours following application, and more than 80% of the label had been
eliminated in 8 hours.
3. NONCARCINOGENIC HEALTH EFFECTS
3.1. ORAL EXPOSURES
3.1.1. Acute Toxicity
3.1.1.1. Human
The central nervous system and cardiovascular system are the targets of acute benzene toxicity
in humans. The ingestion of benzene produces staggering gait, vomiting, loss of consciousness, delirium
and death (Clayton and Clayton, 1981); 2 mL may produce symptoms, whereas 10 mL may be fatal
(Thienes and Haley, 1972). Death results from cardiac failure or respiratory arrest. A man who
swallowed an unspecified quantity of benzene survived, but developed severe gastritis and eventual
pyloric stenosis (Greenburg, 1926).
3.1.1.2. Animal
Animal lethality data indicate that the oral acute toxicity of benzene is low (O'Bryan and Ross,
1986). Oral LD50 values for benzene in rats range from 0.93 to 5.96 g/kg (Cornish and Ryan, 1965; Withey and Hall, 1975). The oral LD50 for benzene in mice is 4.7 g/kg (Sandmeyer, 1978).
Sublethal acute oral doses of benzene affect the nervous system and liver. Single oral doses
of benzene to Sprague-Dawley rats produced slight nervous system depression at 352 mg/kg and tonic
clonic convulsions at 1,870 mg/kg (Cornish and Ryan, 1965). Benzene induced synthesis and catabolism
of monoamine neurotransmitters, but no behavioral effects in CD-1 mice given 8, 40, or 180 mg/kg/day
of the chemical in drinking water for 4 weeks (Hsieh et al., 1988a). In rats, benzene (1400 mg/kg/day
for 1-3 days) altered drug metabolism and lipid peroxidation in the liver, decreased the protein content
in the postmitochondrial supernatant, and increased liver weight (Pawar and Mungikar, 1975).
3.1.2. Subchronic Toxicity
3.1.2.1. Human
No data were found.
3.1.2.2. Animal
The main targets for the oral subchronic toxicity of benzene are the hematopoietic and immune
systems. Dose-related decreases in red-blood cell parameters and lymphocyte numbers were observed
in mice fed >=8 mg of benzene/kg/day in the drinking water for 4 weeks (Hsieh et al., 1988b). In a
17-week gavage study, Fischer-344 rats developed leukopenia and lymphoid depletion of the spleen at
200 mg of benzene/kg/day (NOAEL, 100 mg/kg/day), and B6C3F1 mice exhibited leukopenia at 400
mg/kg/day (NOAEL, 200 mg/kg/day) (Huff et al., 1989). Rats treated by gavage with benzene for 6
months exhibited leukopenia at 10 mg/kg/day and decreased erythrocyte counts at 50 mg/kg/day
(NOAEL for both effects, 1 mg/kg/day) (Wolf et al., 1956).
Impairment of the immune system can result from effects on the blood-forming organs, thus
decreased lymphocyte numbers, such as those observed above, can indicate immunosuppression. In
addition, immunological responses of CD-1 mice to orally administered benzene for four weeks were
either biphasic or suppressed in studies conducted by Hsieh et al. (1988b). For example, the splenic
lymphocyte proliferative response to B- and T-cells was enhanced at 8 mg/kg/day and depressed at
40 and 180 mg/kg/day; cell-mediated immunity showed a similar biphasic response. The humoral
immune response was suppressed at 40 and 180 mg/kg/day.
3.1.3. Chronic Toxicity
3.1.3.1. Human
No data were found.
3.1.3.2. Animal
In a chronic toxicity study conducted by the NTP (Huff et al., 1989), male rats were given
benzene doses of 0, 50, 100, or 200 mg/kg/day in corn oil by gavage 5 days/week for 103 weeks; female
rats and male and female mice were given doses of 0, 25, 50, or 100 mg/kg. Males and females of both
species had decreased body weights and reduced survival at the highest doses and a dose-related
lymphocytopenia (LOAEL, 25 mg/kg/day). Mice given the highest dose also had hyperplasia of the bone
marrow and lymphoid depletion of the splenic follicles and thymus.
3.1.4. Developmental and Reproductive Toxicity
3.1.4.1. Human
No data were found.
3.1.4.2. Animal
Oral doses of 0.5 and 1.0 mL/kg of benzene, given to pregnant mice on days 6-15 of gestation,
produced resorptions and maternal deaths, but did not induce malformations (Nawrot and Staples, 1979).
A dose of 1.3 g/kg/day of benzene given to pregnant mice on gestation days 8-12 caused significant
reductions in fetal body weights (Seidenberg et al., 1986).
3.1.5. Reference Dose
A risk assessment for benzene is currently under development and will be reviewed by an EPA work
group (U.S. EPA, 1992a).
3.2. INHALATION EXPOSURES
3.2.1. Acute Toxicity
3.2.1.1. Human
The central nervous system (CNS) is the target of acute inhalation exposure to benzene.
Depending on the concentration of benzene and duration of exposure, symptoms may range from mild
manifestations such as headache and lightheadedness (50-250 ppm) to more severe effects that include
convulsions, respiratory paralysis, and death (20,000 ppm, 5-10 minutes) (Finkel, 1983; Clayton and
Clayton, 1981). Concentrations up to 25 ppm have not produced effects (Clayton and Clayton, 1981).
3.2.1.2. Animal
The estimated LC50 value for benzene in the rat is 13,700 ppm (Drew and Fouts, 1974). Nonlethal
concentrations of benzene can affect the hematological, immunological, and neurological systems.
The hematological effects of benzene are evident in both the peripheral blood and the bone
marrow. These may occur at low concentrations and include lymphocytopenia in mice exposed to 25
ppm of benzene 5 days/week for 2 weeks (NOAEL, 10 ppm) (Cronkite et al., 1985) and increased
micronuclei and decreased numbers of cells per tibia and colony-forming units (granulocytic stem cells)
per tibia in mice exposed to 21 ppm, continuously, for 4-10 days (LOAEL) (Toft et al., 1982).
Impairment of the immune response can result from effects on the blood-forming organs; thus
the finding of leukopenia in rats exposed to 100 ppm benzene for 1 week and lymphopenia in mice
exposed to 25 ppm for 2 weeks (Li et al., 1986; Cronkite et al., 1989), suggest potential suppression of
the cellular immune response by benzene. Immunological studies have demonstrated that benzene can
affect both the cellular and humoral immune response. Mice inhaling 30 ppm benzene 6 hours/day for
12 days exhibited decreased resistance to infection by Listeria monocytogenes (cellular response; NOAEL,
10 ppm) (Rosenthal and CA Snyder, 1985). Mice inhaling 50 ppm had depressed T-lymphocytes (cellular
response) and B-lymphocytes (humoral response) (Aoyama, 1986).
The neurotoxicity of benzene in animals is characterized by narcosis in rabbits exposed to
45,000 ppm (Carpenter et al., 1944); increased licking of sweetened milk by mice exposed for 1 week
to 300 ppm; a 90% decrease in hind limb grip strength after one exposure to 1,000 or 3,000 ppm; and
tremors after one exposure to 3,000 ppm (Dempster et al., 1984).
3.2.2. Subchronic Toxicity
3.2.2.1. Human
Workers exposed to benzene concentrations of 30 and 150 ppm for 4 months-1 year had
increased incidences of pancytopenia; 25% of the workers died (Aksoy et al., 1972).
3.2.2.2. Animal
The hematopoietic system is a major target for the subchronic toxicity of benzene in animals.
Ward et al. (1985) observed leukopenia and lymphopenia in both mice and rats exposed to benzene 6
hours/day, 5 days/week for 13 weeks (LOAEL for mice and rats, 300 ppm; NOAEL, 30 ppm).
Histopathological examination revealed that mice exposed to 300 ppm also had depletion of the splenic
periarteriolar lymphoid sheath, depletion of the lymphoid elements in the mesenteric lymph nodes, and
plasma cell infiltration of the mandibular lymph node (NOAEL, 30 ppm). Baarson et al. (1984)
demonstrated that a much lower concentration of benzene (10 ppm) depressed the numbers of
circulating lymphocytes and progenitor red blood cells in the spleen when exposure duration was
increased to 24 weeks (6 hours/day, 5 days/week).
Cronkite et al. (1989) observed stem-cell depression in the bone marrow of C57BL/6 mice
exposed to benzene concentrations of 300 ppm for 4-16 weeks. In animals exposed for 16 weeks, stem
cell numbers had recovered to 92% of normal by 25 weeks after exposure.
3.2.3. Chronic Toxicity
3.2.3.1. Human
The main targets of chronic exposure to benzene are the bone marrow, the immune system, and
the central nervous system.
Early symptoms of bone marrow depression by benzene include leukopenia, anemia or
thrombocytopenia, or a combination of the three (Snyder, 1984). At this stage, the effects may be
reversible (IARC, 1983). Another early symptom of benzene toxicity, occurring in some cases, is bone
marrow hyperplasia (Goldstein, 1977). With continued exposure, bone marrow damage becomes more
severe, progressing to pancytopenia (deficiency of all cellular elements of the blood), and aplastic or
hypoplastic anemia (Proctor and Hughes, 1978). The life-threatening consequences of these conditions
involve increased susceptibility to infection and hemorrhagic conditions (Goldstein, 1977). For example,
a group of 32 patients who had been exposed to benzene concentrations of 150 to 650 ppm for 4 months
to 15 years, exhibited severe blood dyscrasias, and 8 of the 32 patients died with thrombocytopenic
hemorrhage and infection (Aksoy et al., 1972).
Researchers generally agree that the lowest levels of benzene that can produce a decrease in
human circulating blood cells are in the range of 40-50 ppm (Snyder, 1984). However, one investigator
estimated from a study of 119 benzene-exposed workers that hematological changes could occur at 10
ppm (Chang, 1972) and others have reported (infrequently) the presence of chromosomal aberrations
in the bone marrow and peripheral lymphocytes of individuals exposed to <10 ppm (USAF, 1989).
Aberrations induced at levels >100 ppm may persist for many years after exposure has ceased (IARC,
1983); some investigators have linked irreversible chromosome damage and/or injury to the bone
marrow with the development of leukemia (Snyder, 1984).
The chronic effects of benzene also include rare cases of the following: lymphocytosis; pseudo-Pelger Huet anomaly changes in the leukocyte osmotic resistance; decreased phagocytic function of
granulocytes; reduced glycogen content and inhibited peroxidase activity of neutrophils; decreased
alkaline phosphatase, myeloperoxidase, and lipid content of the neutrophils; a decrease in Ea and E18
rosettes (T cells); increased leukoagglutinins; the presence of giant platelets; and increased fibrinolytic
activity (Aksoy, 1988).
There is limited evidence to suggest that benzene has long-term effects on the central nervous
system. Workers exposed to benzene for 0.5 to 4 years have exhibited EEG changes and atypical sleep
activity consistent with neurotoxicity (Kellerova, 1985). Others exposed to benzene concentrations of
210 ppm for 6-8 years had peripheral nerve damage (Baslo and Aksoy, 1982).
3.2.3.2. Animal
Mice exposed to benzene 6 hours/day, 5 days/week for life developed anemia, lymphopenia, and
bone marrow hypoplasia (LOAEL, 100 ppm) (Snyder et al., 1980).
3.2.4. Developmental and Reproductive Toxicity
3.2.4.1. Human
Benzene crosses the placenta and is present in the cord blood in amounts equal to those in
maternal blood (Dowty et al., 1976). Studies of the effects of benzene on human reproduction and
development have been confounded by the presence of other chemicals in the environment (USAF, 1989).
Studies at two Superfund sites where benzene was identified did not reveal clusters of birth defects
(Budnick et al., 1984; Heath, 1983).
3.2.4.2. Animal
Benzene concentrations ranging from 50 to 940 ppm did not induce malformations, but did
produce fetal toxicity in the offspring of pregnant rats, rabbits, and mice (ATSDR, 1989; 1992). The
levels tested induced increased resorptions, reduced fetal weight, and skeletal variations, and were
maternally toxic. In one study, the offspring of mice exposed to 20 ppm 6 hours/day on gestational
days 6-15 had reduced numbers of erythroid precursors (Keller and Snyder, 1988). The available data
indicate that benzene has not induced developmental effects at 1 ppm, the current OSHA standard
(ATSDR, 1989).
Mice exposed subchronically to benzene concentrations of 300 ppm for 13 weeks developed
ovarian cysts and testicular atrophy/degeneration; in addition, the numbers of spermatozoa were
decreased and the incidence of abnormal sperm increased (Ward et al., 1985). Mice exposed to 30 ppm
had no reproductive effects.
3.2.5. Reference Dose/Concentration
A risk assessment for benzene is under review by an EPA work group (U.S. EPA, 1991a).
3.3. OTHER ROUTES OF EXPOSURE
3.3.1. Acute Toxicity
3.3.1.1. Human
Benzene is irritating to the skin and may produce erythema, vesiculation, and dry and scaly
dermatitis by defatting of the keratin layer (Sandmeyer, 1981).
3.3.1.2. Animal
In the rabbit eye, benzene is a moderate irritant, causing conjunctival irritation and transient
corneal injury. Grant (1974) reports that 50% of the rats exposed to vapor concentrations of 50 ppm
developed cataracts after more than 600 hours of exposure. Benzene is slightly to moderately irritating
to the skin of laboratory animals (Wolf et al., 1956).
3.3.2. Subchronic Toxicity
3.3.2.1. Human
No data were found.
3.3.2.2. Animal
No data were found.
3.3.3. Chronic Toxicity
3.3.3.1. Human
No data were found.
3.3.3.2. Animal
No data were found.
3.3.4. Developmental and Reproductive Toxicity
3.3.4.1. Human
No data were found.
3.3.4.2. Animal
Benzene, applied dermally to rats at doses of 64 or 320 mg/kg/day for 4 months, did not affect
the fertility of males, or the ability of females to conceive (Malysheva, 1980). However, the numbers
of spermatogonia in the males was decreased and the mortality of the first generation offspring was
increased.
3.4. TARGET ORGANS/CRITICAL EFFECTS
3.4.1. Oral Exposures
3.4.1.1. Primary Target Organs
- Hematopoietic system: Animals treated with chronic oral doses of benzene developed
lymphocytopenia, hyperplasia of bone marrow and lymphoid depletion of the splenic follicles and
thymus.
- Immune system: Effects on the hematopoietic system, such as lymphocytopenia and
lymphoid depletion of the splenic follicles and thymus, can impact the immune system.
- Nervous system: Symptoms of neurotoxicity are produced in humans and animals, mainly
by high acute doses; however, subacute exposure to low doses affected levels of
neurotransmitters in animals.
3.4.1.2. Other Target Organs
- Reproductive system: Benzene produces fetal toxicity at maternally toxic doses.
3.4.2. Inhalation Exposures
3.4.2.1. Primary Target Organs
- Hematopoietic system: Subchronic and chronic exposure can suppress the bone marrow in
humans and animals. The effects are progressive, and death can result from thrombocytopenic
hemorrhage.
- Immune system: Benzene suppresses the immune response in both humans and animals.
Chronically exposed workers have died from infections.
- Nervous system: Chronically exposed workers exhibited EEG changes and peripheral nerve
damage.
3.4.2.2. Other Target Organs
- Reproductive system: Benzene produces fetal toxicity at maternally toxic doses.
4. CARCINOGENICITY
4.1. ORAL EXPOSURES
4.1.1. Human
No data were found.
4.1.2. Animal
The NTP (1986; Huff et al., 1989) conducted an oral (gavage) carcinogenicity study in F344/N rats
and B6C3F1 mice. Doses of benzene, ranging from 25 to 200 mg/kg, were administered 5 days/week for
103 weeks. Both species developed dose-related lymphocytopenia. Rats exhibited increased incidences
of carcinoma of the Zymbal gland and squamous cell carcinoma of the oral cavity and skin. The mice
had increased incidences of carcinomas of the Zymbal gland, malignant lymphomas and
alveolar/bronchiolar carcinomas, and tumors of the ovaries and mammary glands. The increased
incidences of the different tumor types (in both sexes, both species) were generally dose-related and
statistically significant at p<0.05.
In another study, Maltoni et al. (1989) administered oral doses of 50 to 500 mg of benzene/kg
to Sprague-Dawley and Wistar rats, 4-5 days/week for 52 or 104 weeks. The animals had increased
incidences of carcinomas of the Zymbal gland, oral cavity, nasal cavity, forestomach and liver. Swiss
mice given 500 mg of benzene/kg/day for 52 weeks developed mammary carcinomas (Maltoni et al.,
1989).
4.2. INHALATION EXPOSURES
4.2.1. Human
Occupational exposure to benzene has been associated with increased incidences of acute
myeloblastic or erythroblastic leukemias and chronic myeloid and lymphoid leukemias among workers
(Aksoy, 1989). A few investigations suggest that benzene may also be involved in the development of
malignant lymphoma, multiple myeloma (Aksoy, 1980; Aksoy et al., 1984, Rinsky et al. 1987), and lung
cancer (Aksoy, 1976). The U.S. EPA (1985) used the epidemiologic studies of Rinsky et al. (1981), Ott et
al. (1978), and Wong et al. (1983) to derive quantitative estimates of carcinogenic risk for benzene.
In a retrospective cohort mortality study, Rinsky et al. (1981) observed seven deaths from
leukemia among 748 white workers who were exposed to benzene in rubber manufacturing facilities and
followed for at least 24 years. The increased incidence was statistically significant (standard mortality
ratio [SMR] was 560). Five leukemia deaths occurred among workers with more than 5 years of exposure
(SMR, 2100). Exposures ranged from 10-100 ppm 8-hour TWA.
In another retrospective cohort mortality study, Ott et al. (1978) observed three deaths from
leukemia (0.8 expected; SMR, 375) among 594 workers exposed to benzene in three production areas of
a chemical company and followed for at least 23 years. The increase was not statistically significant.
Exposures ranged from <2 to >25 ppm for an 8-hour TWA.
In a historical prospective mortality study, Wong et al. (1983) examined a study population of
4062 workers from seven chemical plants whose jobs were categorized according to peak exposure. The
workers were exposed to benzene for at least 6 months. Dose-dependent increases in leukemia and
lymphatic and hematopoietic cancer were found. For leukemia, 7 deaths were observed, 5.96 were
expected (SMR, 117.4); this is not statistically significant. (However, the unexposed subjects exhibited
a less than expected incidence of neoplasia, complicating the interpretation of the results.)
Other studies, such as that of 28,500 workers in the shoe manufacturing industry (Aksoy et al.,
1974), support the association between exposure to benzene and the development of leukemia. The
workers had been exposed to benzene levels of 210 to 650 ppm for durations ranging from 1 to 15
years. The annual incidence rate for leukemia was 13/100,000 for the shoe manufacturers, compared
with 6/100,000 for the general population. Aksoy (1977) later revised their estimated incidence of
leukemia among the general population in Turkey to 2.5 to 3/100,000, increasing the significance of
leukemia in the exposed workers.
In a historical prospective mortality study of chemical workers, Yin et al. (1987) described a
dose-response relationship between exposure to benzene and lymphatic and hematopoietic cancers,
which adds strength to the association between exposure in the workplace and cancer development. The
cohort consisted of 4602 male workers who were occupationally exposed to benzene for at least six
months. The controls were male chemical workers employed at the plants during the same period, but
never exposed to benzene. Cohort members were divided into three exposure groups: <180 ppm-months, 180-719 ppm-months, and >=720 ppm-months. The dose-response relationships between the
cumulative exposure to benzene and mortality from all lymphopoietic cancers combined and from
leukemia were statistically significant (p=0.02 and p=0.01, respectively), while the dose response
relationship between cumulative exposure and non-Hodgkin's lymphopoietic cancer was of borderline
statistical significance (p=0.06).
Various other epidemiologic and case studies, reporting an increased incidence or a causal
relationship between leukemia and exposure to benzene, have been reviewed by, among others, Goldstein
(1977), IARC (1982), Infante and White (1983), Snyder (1984), Aksoy (1989), (USAF, 1989), (ATSDR, 1989),
and Brett et al. (1989).
4.2.2. Animal
Benzene vapors are carcinogenic to both rats and mice. Sprague-Dawley rats exposed to vapor
concentrations of 200-300 ppm benzene 4-7 hours daily for 104 weeks developed mammary carcinomas
(incidence, 26.6%), hepatomas (2.3%) and leukemia (1.4%) (Maltoni et al., 1983). C57Bl/J6 mice exposed
to vapor concentrations of 300 ppm, 6 hours/day, 5 days/week for life had an increased incidence of
thymic lymphoma (Snyder et al., 1980; C57Bl/BNL mice exposed to 300 ppm, 6 hours/day, 5 days/week
for only 16 weeks developed increased incidences of leukemia, lymphoma, and solid tumors over several
months of observation (Cronkite et al., 1985; Cronkite, 1986).
4.3. OTHER ROUTES OF EXPOSURE
4.3.1. Human
No data were found.
4.3.2. Animal
Papillomas did not develop in mice given topical applications of 800 mg/kg/day of benzene
(initiator) and 1 g of 12-0-tetradecanoylphorbol-13-acetate (promoter) and observed for 52 weeks
(Bull et al., 1986).
4.4. EPA WEIGHT-OF-EVIDENCE
4.4.1. Oral
Classification--A, human carcinogen
Basis--"Several studies of increased incidence of nonlymphocytic leukemia from occupational exposure,
increased incidence of neoplasia in rats and mice exposed by inhalation and gavage, and some
supporting data" (U.S. EPA, 1992a).
4.4.2. Inhalation
Classification--A, human carcinogen
Basis--"Several studies of increased incidence of nonlymphocytic leukemia from occupational exposure,
increased incidence of neoplasia in rats and mice exposed by inhalation and gavage, and some
supporting data" (U.S. EPA, 1992a).
4.5. CARCINOGENICITY SLOPE FACTORS
4.5.1. Oral
- SLOPE FACTOR: 2.9E-2 (mg/kg/day)-1 (U.S. EPA, 1992a)
- ORAL UNIT RISK: 8.3E-7 (g/L)-1 (U.S.EPA, 1992a)
- PRINCIPAL STUDIES: Ott et al. (1978), Rinsky et al. (1981), and Wong et al. (1983).
- VERIFICATION DATE: 10/09/87
- COMMENT: Route-to-route extrapolation is based on increased incidences of leukemia in occupational
inhalation studies (U.S. EPA, 1991a). Pharmacokinetic data that could impact the oral risk assessment
are undergoing evaluation by the EPA (U.S. EPA, 1991a).
4.5.2. Inhalation
- SLOPE FACTOR: 2.9E-2 (mg/kg/day)-1 (U.S. EPA, 1992b)
- INHALATION UNIT RISK: 8.3E-6 (g/m3)-1 (U.S. EPA, 1992a)
- PRINCIPAL STUDIES: Ott et al. (1978), Rinsky et al. (1981), and Wong et al. (1983)
- VERIFICATION DATE: 10/09/87
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