TOXICOLOGICAL REVIEW

OF

HEXAVALENT CHROMIUM

(CAS No. 18540-29-9) 

In Support of Summary Information on the 

Integrated Risk Information System (IRIS) 

August 1998 

U.S. Environmental Protection Agency 

Washington, DC 
DISCLAIMER 

This document has been reviewed in accordance with U.S. Environmental Protection 

Agency policy and approved for publication. Mention of trade names or commercial products 

does not constitute endorsement or recommendation for use. This document may undergo 

revisions in the future. The most up-to-date version will be available electronically via the IRIS 

Home Page at http://www.epa.gov/iris. 

ii 
CONTENTS—TOXICOLOGICAL REVIEW FOR HEXAVALENT CHROMIUM 

(CAS No. 18540-29-9) 

FOREWORD .................................................................v

AUTHORS, CONTRIBUTORS, AND REVIEWERS ................................ vi

LIST OF ABBREVIATIONS .................................................. vii

1. INTRODUCTION ...........................................................1

2. CHEMICAL AND PHYSICAL INFORMATION RELEVANT TO ASSESSMENTS .....2

3. TOXICOKINETICS RELEVANT TO ASSESSMENTS ............................4

3.1. ABSORPTION FACTORS IN HUMANS AND EXPERIMENTAL ANIMALS . . 4

3.1.1. Oral .......................................................4

3.1.2. Inhalation ..................................................4

3.1.3. Metabolism .................................................5

3.1.4. The Essentiality of Chromium ..................................6

4. HAZARD IDENTIFICATION .................................................7

4.1. STUDIES IN HUMANS ..............................................7

4.1.1. Oral .......................................................7

4.1.2. Inhalation ..................................................7

4.2. SUBCHRONIC, CHRONIC STUDIES AND CANCER BIOASSAYS IN 

ANIMALS ............................................................17

4.2.1. Chronic Oral Studies .........................................17

4.2.2. Subchronic Oral Studies ......................................17

4.2.3. Chronic Inhalation Studies ....................................18

4.2.4. Subchronic Inhalation Studies .................................20

4.3. REPRODUCTIVE/DEVELOPMENTAL STUDIES .......................23

4.3.1. Oral Studies ................................................23

4.3.2. Inhalation Studies ...........................................26

4.4. OTHER STUDIES ..................................................26

4.4.1. Contact Dermatitis ..........................................26

4.4.2. Toxicant Interactions.........................................27

4.4.3. Genotoxicity ...............................................27

4.5. SYNTHESIS AND EVALUATION OF MAJOR NONCANCER EFFECTS ....28

4.5.1. Oral Studies ................................................28

4.5.1.1. Human Studies ......................................28

4.5.1.2. Animal Studies ......................................28

4.5.2. Inhalation Studies ............................................29

4.5.2.1. Human Studies ......................................29

iii 
CONTENTS (continued) 

4.5.2.2. Animal Studies ......................................30

4.6. WEIGHT-OF-EVIDENCE EVALUATION AND CANCER

CHARACTERIZATION ...........................................31

4.7. OTHER HAZARD IDENTIFICATION ISSUES ..........................32

4.7.1. Possible Childhood Susceptibility ..............................32

4.7.2. Possible Sex Differences ......................................32

5. DOSE-RESPONSE ASSESSMENTS ..........................................32

5.1. ORAL REFERENCE DOSE (RfD) .....................................32

5.1.1. Choice of Principal Study and Critical Effect ......................32

5.1.2. Method of Analysis ..........................................34

5.1.3. RfD Derivation .............................................35

5.2. INHALATION REFERENCE CONCENTRATION (RfC) ..................35

5.2.1. Choice of Principal Study and Critical Effect ......................35

5.2.2. RfC Derivation .............................................38

5.2.2.1. Chromic Acid Mists and Dissolved Hexavalent Chromium

Aerosols ............................................38

5.2.2.2. Hexavalent Chromium Dusts ...........................39

5.3. CANCER ASSESSMENT ............................................41

5.3.1. Summary ..................................................41

5.3.2. Dose-Response Data .........................................41

5.3.3. Dose Conversion ............................................42

5.3.4. Extrapolation Method ........................................43

6. MAJOR CONCLUSIONS IN THE CHARACTERIZATION OF 

HAZARD AND DOSE RESPONSE ........................................46

6.1. HUMAN HAZARD POTENTIAL .....................................46

6.2. DOSE RESPONSE .................................................49

7. REFERENCES ............................................................51

APPENDIX A. EXTERNAL PEER REVIEW—

SUMMARY OF COMMENTS AND DISPOSITION ..........................65

iv 
FOREWORD 

The purpose of this Toxological Review is to provide scientific support and rationale for 

the hazard identification and dose-response assessment in IRIS pertaining to chronic exposure to 

Cr(VI). It is not intended to be a comprehensive treatise on the chemical or toxicological nature 

of Cr(VI). 

In Section 6, EPA has characterized its overall confidence in the quantitative and 

qualitative aspects of hazard and dose response. Matters considered in this characterization 

include knowledge gaps, uncertainties, quality of data, and scientific controversies. This 

characterization is presented in an effort to make apparent the limitations of the assessment and 

to aid and guide the risk assessor in the ensuing steps of the risk assessment process. 

For other general information about this assessment or other questions relating to IRIS, 

the reader is referred to EPA’s Risk Information Hotline at 513-569-7254. 

v 
AUTHORS, CONTRIBUTORS, AND REVIEWERS 

Chemical Manager/Author 

Peter C. Grevatt, Ph.D., EPA Region 2 

Reviewers 

This document and summary information on IRIS have received peer review both by EPA 

scientists and by independent scientists external to EPA. Subsequent to external review and 

incorporation of comments, this assessment has undergone an Agencywide review process 

whereby the IRIS Program Director has achieved a consensus approval among the Office of 

Research and Development; Office of Air and Radiation; Office of Prevention, Pesticides, and 

Toxic Substances; Office of Solid Waste and Emergency Response; Office of Water; Office of 

Planning and Evaluation; and Regional Offices. 

Internal EPA Reviewers 

Robert Benson, Ph.D., D.A.B.T., EPA Region 8

Herman Gibb, Ph.D., EPA NCEA, Washington, DC

Annie Jarabek, EPA NCEA, RTP, NC

Charles Hiremath, Ph.D., EPA NCEA, Washington, DC

Winona Victery, Ph.D., EPA Region 9

External Peer Reviewers 

Richard Anderson, Ph.D.

USDA

Robert Chapin, Ph.D.

NIEHS

Robert Drew, Ph.D.

Consultant in Toxicology

Gunter Obersorster, D.V.M., Ph.D.

University of Rochester

Elizabeth T. Snow, Ph.D.

New York University Medical Center

Summaries of the external peer reviewers’ comments and the disposition of their 

recommendations are in Appendix A. 

vi 
LIST OF ABBREVIATIONS

BAL Bronchoalveolar lavage

BALF Bronchoalveolar lavage fluid

BCF Bioconcentration factor

BMC Benchmark concentration

BMD Benchmark dose

CASRN Chemical Abstracts Service Registry Number

CS Composite score

ESADDI Estimated safe and adequate dietary intake

IRIS Integrated Risk Information System

LDH Lactate dehydrogenase

LOAEL Lowest-observed-adverse-effect level

LOEL Lowest-observed-effect level

MCH Mean corpuscular hemoglobin

MCV Mean corpuscular volume

MED Minimum effective dose

NOAEL No-observed-adverse-effect level

NOEL No-observed-effect level

PCMR Proportionate cancer mortality ratio

ppm Parts per million

RfC Inhalation reference concentration

RfD Oral reference dose

Rvd Dose-rating value

Rve Effect-rating value

SIR Standard incidence ratio

SMR Standard mortality ratio

TWA Time-weighted average

vii 
1. INTRODUCTION 

This document presents background and justification for the hazard and dose-response 

assessment summaries in EPA’s Integrated Risk Information System (IRIS). IRIS Summaries 

may include an oral reference dose (RfD), inhalation reference concentration (RfC) and a 

carcinogenicity assessment. 

The RfD and RfC provide quantitative information for noncancer dose-response assessments. 

The RfD is based on the assumption that thresholds exist for certain toxic effects such as cellular 

necrosis but may not exist for other toxic effects such as some carcinogenic responses. It is 

expressed in units of mg/kg-day. In general, the RfD is an estimate (with uncertainty spanning 

perhaps an order of magnitude) of a daily exposure to the human population (including sensitive 

subgroups) that is likely to be without an appreciable risk of deleterious effects during a lifetime. 

The inhalation RfC is analogous to the oral RfD. The inhalation RfC considers toxic effects for 

both the respiratory system (portal-of-entry) and for effects peripheral to the respiratory system 

(extrarespiratory or systemic effects). It is generally expressed in units of mg/m3

. 

The carcinogenicity assessment provides information on the carcinogenic hazard potential of 

the substance in question and quantitative estimates of risk from oral exposure and inhalation 

exposure. The information includes a weight-of-evidence judgment of the likelihood that the 

agent is a human carcinogen and the conditions under which the carcinogenic effects may be 

expressed. Quantitative risk estimates are presented in three ways. The slope factor is the result 

of application of a low-dose extrapolation procedure and is presented as the risk per mg/kg-day. 

The unit risk is the quantitative estimate in terms of either risk per μg/L drinking water or risk 

per μg/m3

 air breathed. Another form in which risk is presented is a drinking water or air 

concentration providing cancer risks of 1 in 10,000; 1 in 100,000; or 1 in 1,000,000. 

Development of these hazard identifications and dose-response assessments for hexavalent 

chromium has followed the general guidelines for risk assessment as set forth by the National 

Research Council (1983). EPA guidelines that were used in the development of this assessment 

may include the following: the Guidelines for Carcinogen Risk Assessment (U.S. EPA, 1986a), 

Guidelines for the Health Risk Assessment of Chemical Mixtures (U.S. EPA, 1986b), Guidelines 

for Mutagenicity Risk Assessment (U.S. EPA, 1986c), Guidelines for Developmental Toxicity 

Risk Assessment (U.S. EPA, 1991), Proposed Guidelines for Neurotoxicity Risk Assessment (U.S. 

EPA, 1995a), Proposed Guidelines for Carcinogen Risk Assessment (U.S. EPA, 1996a), 

Guidelines for Reproductive Toxicity Risk Assessment (U.S. EPA, 1996b), and Guidelines for 

Neurotoxicity Risk Assessment (U.S. EPA, 1998a); Recommendations for and Documentation of 

Biological Values for Use in Risk Assessment (U.S. EPA, 1988); (proposed) Interim Policy for 

Particle Size and Limit Concentration Issues in Inhalation Toxicity (U.S. EPA, 1994a); Methods 

for Derivation of Inhalation Reference Concentrations and Application of Inhalation Dosimetry 

(U.S. EPA, 1994b); Peer Review and Peer Involvement at the U.S. Environmental Protection 

Agency (U.S. EPA, 1994c); Use of the Benchmark Dose Approach in Health Risk Assessment 

(U.S. EPA, 1995b); Science Policy Council Handbook: Peer Review (U.S. EPA, 1998b); and 

memorandum from EPA Administrator, Carol Browner, dated March 21, 1995, Subject: 

Guidance on Risk Characterization. 

1
Literature search strategies employed for this compound were based on the CASRN and at 

least one common name. At a minimum, the following databases were searched: RTECS, 

HSDB, TSCATS, CCRIS, GENETOX, EMIC, EMICBACK, DART, ETICBACK, TOXLINE, 

CANCERLINE, MEDLINE AND MEDLINE backfiles. Any pertinent scientific information 

submitted by the public to the IRIS Submission Desk was also considered in the development of 

this document. 

2. CHEMICAL AND PHYSICAL INFORMATION RELEVANT TO ASSESSMENTS 

In the hexavalent state, chromium exists as oxo species such as CrO3 and CrO4

2-) that are 

strongly oxidizing (Cotton and Wilkinson, 1980). The CAS Registry numbers and the 

solubilities of a few important hexavalent chromium compounds are given in Table 1. 

In solution, hexavalent chromium exists as hydrochromate (HCrO4

-

), chromate (CrO4

2-), 

and dichromate (Cr2O7

2-) ionic species. The proportion of each ion in solution is pH dependent. 

In basic and neutral pH, the chromate form predominates. As the pH is lowered (6.0 to 6.2), the 

hydrochromate concentration increases. At very low pH, the dichromate species predominate 

(U.S. EPA, 1984). 

The primary sources of hexavalent chromium in the atmosphere are chromate chemicals 

used as rust inhibitors in cooling towers and emitted as mists, particulate matter emitted during 

manufacture and use of metal chromates, and chromic acid mist from the plating industry 

(ATSDR, 1993). Hexavalent chromium in air eventually reacts with dust particles or other 

pollutants to form trivalent chromium (NAS, 1974); however, the exact nature of such 

atmospheric reactions has not been studied extensively. Both hexavalent and trivalent chromium 

are removed from air by atmospheric fallout and precipitation (Fishbein, 1981). The atmospheric 

half-life for the physical removal mechanism is dependent on the particle size and particle 

density. Chromium particles of small aerodynamic diameter (< 10 μm) will remain airborne for 

a long period (U.S. EPA, 1984). 

Hexavalent chromium may exist in aquatic media as water-soluble complex anions and 

may persist in water. Hexavalent chromium is a strong oxidizing agent and may react with 

organic matter or other reducing agents to form trivalent chromium. The trivalent chromium will 

eventually be precipitated as Cr2O3·xH2O. Therefore, in surface water rich in organic content, 

hexavalent chromium will exhibit a much shorter lifetime (Callahan et al., 1979). 

Any hexavalent chromium in soil is expected to be reduced to trivalent chromium by 

organic matter. The primary processes by which the converted trivalent chromium is lost from 

soil are aerial transport through aerosol formation and surface water transport through runoff 

(U.S. EPA, 1984). Very little chromium is leached from soil because it is present as insoluble 

Cr2O3·xH2O (Fishbein, 1981). 

2
The bioconcentration factor (BCF) for hexavalent chromium in fish muscle appears to be 

< 1.0 (U.S. EPA, 1980), but values of 125 and 192 were obtained for oyster and blue mussel, 

respectively (U.S. EPA, 1980). 

Table 1. CAS numbers and aqueous solubilities of selected hexavalent chromium 

compounds 

Compound CAS No. Water solubility 

Ammonium chromate 7788-98-9 40.5 g/100 mL at 30�C 

(NH4)2CrO4 

Calcium chromate 13765-19-0 2.23 g/100 mL at 20�C 

CaCrO4 

Chromic acid 1333-82-0 61.7 g/100 mL at 0�C 

CrO3 

Potassium chromate 7789-50-6 62.9 g/100 mL at 20�C 

K2CrO4 

Potassium dichromate 7789-50-9 4.9 g/100 mL at 0�C 

K2Cr2O7 

Sodium chromate 7775-11-3 87.3 g/100 mL at 30�C 

Na2CrO4 

Sodium dichromate dihydrate 7789-12-0 230 g/100 mL at 0�C 

Sources: Weast, 1980; Hartford, 1979. 

3
3. TOXICOKINETICS RELEVANT TO ASSESSMENTS 

3.1. ABSORPTION FACTORS IN HUMANS AND EXPERIMENTAL ANIMALS 

3.1.1. Oral 

Gastrointestinal absorption of Cr(VI) occurs with greater efficiency than absorption of 

Cr(III), though absorption of ingested hexavalent chromium is estimated to be less than 5%. 

Donaldson and Barreras (1966) fed Na51CrO4 to rats and humans. Based on mean urinary 

excretion, 51Cr,

 absorption was estimated to be 2.1% in humans. In rats, approximately 2% of the 

administered dose was absorbed based on fecal excretion of 51Cr when Na51CrO4 was 

administered intragastrically. Intestinal absorption of hexavalent chromium appears to be 

significantly affected by contact with gastric juices. When Na51CrO4 was introduced to humans 

intraduodenally (avoiding contact with gastric juices), approximately half of the chromium was 

absorbed based on fecal excretion. Similar results were observed following intrajejunal 

administration in rats. Incubation of hexavalent chromium with gastric juices prior to 

intraduodenal or intrajejunal administration in humans and rats, respectively, virtually eliminated 

absorption of chromium. Absorption of trivalent chromium (51CrCl3) was not increased by 

intraduodenal or intrajejunal administration. The authors demonstrated that hexavalent 

chromium is reduced to the trivalent form by incubation with gastric juices and concluded that 

reduction of hexavalent chromium to the trivalent form in the stomach significantly reduces 

absorption by the oral route of exposure. Gastric juices have peak reductive capacity 2 to 4 hours 

after a meal and are at a minimum between meals and at night (DeFlora et al., 1987). Anderson 

et al. (1983) confirmed the low absorption of trivalent chromium in humans following oral 

administration of 200 μg of CrCl3. 

MacKenzie et al. (1959) administered Na51CrO4 to rats by gavage. Based on urinary 

excretion, absorption was estimated to be 6% in fasted rats and 3% in nonfasted rats. The rate of 

absorption was twofold greater than that observed following administration of 51CrCl3 by gavage. 

Absorption of hexavalent chromium was found to be increased by three- to fivefold following 

intestinal administration of Na51CrO4, consistent with reduction of hexavalent chromium during 

passage through the stomach. Absorption of hexavalent and trivalent chromium was found to be 

less than 1.4% in the hamster (Henderson et al., 1979), while Visek (1953) estimated that less 

than 0.5% of ingested CrCl3 was absorbed through the gastrointestinal tract of the rat. 

3.1.2. Inhalation 

A number of factors can influence the absorption of chromium following inhalation, 

including the size, oxidation state, and solubility of the chromium particles; the activity of 

alveolar macrophages; and the interaction of chromium with biomolecules following deposition 

in the lung (ATSDR, 1993). Absorption of inhaled chromium following occupational exposure 

has been demonstrated by measurement of chromium in the serum, urine, and hair of workers in 

the chromium industry (Minoia and Cavalleri, 1988; Randall and Gibson, 1987; Tossavainen et 

al., 1980). 

4
Langard et al. (1978) demonstrated that water-soluble hexavalent chromium, such as 

chromic acid, is absorbed rapidly following inhalation by rats. However, insoluble hexavalent 

chromium, such as zinc chromate, is less well absorbed. Animals were exposed to zinc chromate 

dust at a level of 7.35 mg/m3

. After 0, 100, 250, and 350 min of exposure, the concentrations of 

chromium in the blood (μg/ml) were 0.007, 0.024, 0.22, and 0.31, respectively. In the second 

part of this study, rats were exposed to the same level for 6 hours on 4 consecutive days. Blood 

concentrations appeared to peak at the end of the second exposure and then began to decline 

slowly. Mean blood chromium values measured at the end of each exposure period averaged 

0.03, 0.56, 0.46, and 0.34 μg/ml for exposures l-4, respectively. No significant differences in 

absorption as reflected by blood chromium levels were noted between the sexes or between day 

and night exposures. 

Suzuki et al. (1984) exposed rats to potassium dichromate (VI) or Cr(III) trichloride by 

inhalation and determined that while lung clearance of both valence states was dependent on 

particle size, Cr(VI) was absorbed with threefold greater efficiency than Cr(III). 

3.1.3. Metabolism 

In vivo reduction of Cr(VI) to Cr(III) has been widely studied, and some characterizations 

can be made. Ingested hexavalent chromium is efficiently reduced to the trivalent form by the 

gastric juices (DeFlora et al., 1987). Hexavalent chromium can also be reduced to the trivalent 

form in the epithelial lining fluid of the lungs by ascorbate and glutathione. The reduction by 

ascorbate is more rapid than by glutathione, and results in a shorter residence time for chromium 

in the lungs (Suzuki and Fukuda, 1990). 

Once absorbed into the bloodstream, hexavalent chromium readily enters red blood cells 

through the phosphate and sulfate anion-exchange carrier pathway, though a portion may remain 

in plasma for an extended period (Wiegand et al., 1985). While Cr(III) compounds are unable to 

cross the red cell membrane by this pathway (Gray and Sterling, 1950), they may enter red blood 

cells, but only with very low efficiency (Mertz, 1969; O’Flaherty, 1996). Hexavalent chromium 

is reduced to the trivalent form in the red blood cell by the action of glutathione (Debetto and 

Luciani, 1988; Petrilli and De Flora, 1978a). During reduction to the trivalent form, chromium 

may interact with cellular macromolecules, including DNA (Wiegand et al., 1985), or may be 

slowly released from the cell (Bishop and Surgenor, 1964). 

Visek et al. (1953) reported that an insignificant amount of 51Cr crossed the placenta of 

rats in the 24 hours following intravenous injection regardless of the chemical form injected, the 

valence state, the gestational stage, or the size of the litter. In no instance was the radioactivity 

measured in the fetuses greater than 0.13% of the dose. Danielsson et al. (1982) reported that 

sodium dichromate crossed the placenta more readily than Cr(III) trichloride following 

intravenous injection of mouse dams. Casey and Hembridge (1984) demonstrated that chromium 

can be transferred to infants through breast milk. The breast milk of 45 lactating women was 

found to have a chromium content averaging 0.3 μg/L. These concentrations were taken to 

represent background levels in women whose chromium exposure occurs primarily through the 

diet. 

5
A physiologically based model for chromium has recently been developed, which 

incorporates absorption and disposition schemes for Cr(VI) and Cr(III) throughout the body 

(O’Flaherty, 1996). The model was calibrated on the basis of published oral and intratracheal 

kinetic studies using soluble Cr(III) and Cr(VI) in the rat, and accounts for most of the major 

features of chromium kinetics, including reduction of Cr(VI) to Cr(III). The model suggests the 

following in vivo disposition for chromium. Both Cr(III) and Cr(VI) are poorly absorbed from 

the lung and the gastrointestinal tract. Following inhalation exposure, chromium may be 

absorbed into the systemic circulation, transferred to the gastrointestinal tract by mucociliary 

action, or remain in the lung. Cr(VI) is reduced to Cr(III) in all tissues, including the lung and 

the gastrointestinal tract. Both Cr(III) and Cr(VI) are better absorbed from the gastrointestinal 

tract in the fasted than in the fed state, and the absorption efficiency of Cr(III) salts is largely 

dependent on the nutritional status of the animal as well as the nature of the anion making up the 

Cr(III) salt. The model assumes that reduction of Cr(VI) does not occur in the plasma. Cr(VI) 

enters cells by the phosphate and sulfate anion-exchange carrier pathway. Cr(III) travels in the 

bloodstream largely bound to amino acids, other organic acids, and plasma proteins such as 

globulins. The complexes of Cr(III) that are bound to lower molecular weight ligands are most 

likely to be able to traverse cell membranes (Mertz, 1969). A significant amount of absorbed 

chromium is taken up in the bone (Witmer and Harris, 1991; Weber, 1983), Chromium is also 

concentrated in tissues of the liver, kidney, and spleen. Once in the cell, Cr(VI) may be reduced 

to Cr(III), which may subsequently interact with cellular macromolecules including DNA 

(Wiegand et al., 1985), or may be slowly released from the cell (Bishop and Surgenor, 1964). 

The model suggests that the bioaccessibility of chromium to absorption processes may be the 

single most important factor determining the toxicity of a specific chromium source (O’Flaherty, 

1996). 

Given the rapid reduction of Cr(VI) to Cr(III) in vivo, it is relevant to consider whether 

environmental exposures to Cr(VI) or administration of Cr(VI) in controlled animal experiments 

is essentially identical to environmental exposures to Cr(III) or administration of Cr(III) in 

controlled experiments. Although considerably more data are available for Cr(VI) than for 

Cr(III), it appears at present that exposures to Cr(VI) have considerably different outcomes than 

exposures to Cr(III). The Agency has prepared the toxicological summaries and IRIS files for 

Cr(VI) and Cr(III) from this perspective. 

3.1.4. The Essentiality of Chromium 

Cr(III) in its biologically active form (glucose tolerance factor, or GTF, a dinicotinatochromium[III] glutathione-like complex), facilitates interaction of insulin with its receptor site, 

influencing glucose, protein, and lipid metabolism. Thus, Cr(III) is essential for animals and 

human beings. Inorganic chromium compounds do not appear to have insulin-potentiating 

activity. Chromium deficiency may cause changes in the metabolism of glucose and lipids. In 

some studies, dietary supplementation with chromium reversed changes in glucose tolerance and 

serum lipids. The National Research Council has identified an estimated safe and adequate daily 

dietary intake (ESADDI) for chromium of 50-200 μg/d (NRC, 1989), corresponding to 0.71-2.9 

μg/kg/day for a 70-kg adult. FDA has selected a Reference Daily Intake for chromium of 120 

μg/d (DHHS, 1995). 

6
4. HAZARD IDENTIFICATION 

4.1. STUDIES IN HUMANS 

4.1.1. Oral 

Cr(VI) is considerably more toxic than Cr(III). A cross-sectional study of 155 villagers 

reported the effects of environmental contamination of well water adjacent to a chromium alloy 

plant. Cr(VI) concentrations were reported as 20 mg/L, with an estimated dose rate of 0.57 

mg/kg-day (Zhang and Li, 1987). Reported effects at this dose included oral ulcers, diarrhea, 

abdominal pain, indigestion, vomiting, leukocytosis, and presence of immature neutrophils. 

Effects data for lower exposure doses were not available. 

Other reports of toxic effects in humans are limited to case reports from accidental 

poisonings. Some Cr(VI) compounds (such as potassium tetrachromate and chromic acid) are 

potent oxidizing agents, and are thus strong irritants of mucosal tissue. Effects included 

metabolic acidosis, acute tubular necrosis, kidney failure, and death (Saryan and Reedy, 1988). 

4.1.2. Inhalation 

Occupational exposure to chromium compounds has been studied in the chromateproduction, chrome-plating and chrome pigment, ferrochromium production, gold mining, 

leather tanning, and chrome alloy production industries. 

Workers in the chromate industry are exposed to both trivalent and hexavalent 

compounds of chromium. Epidemiological studies of chromate production plants in Japan, Great 

Britain, West Germany, and the United States have revealed a correlation between occupational 

exposure to chromium and lung cancer, but the specific form of chromium responsible for the 

induction of cancer was not identified (Machle and Gregorius, 1948; Baejter, 1950a,b; Bidstrup, 

1951; Mancuso and Hueper, 1951; Brinton et al., 1952; Bidstrup and Case, 1956; Todd, 1962; 

Taylor, 1966; Enterline, 1974; Mancuso, 1975; Ohsaki et al., 1978; Sano and Mitohara, 1978; 

Hayes et al., 1979; Hill and Ferguson, 1979; Alderson et al., 1981; Haguenor et al., 1981; Satoh 

et al., 1981; Korallus et al., 1982; Frentzel-Beyme, 1983; Langard and Vigander, 1983; Watanabe 

and Fukuchi, 1984; Davies, 1984; Mancuso, 1997). 

Mancuso and Hueper (1951) conducted a proportional mortality study of a cohort of 

chromate workers (employed for > l year from 1931 to 1949 in a Painesville, OH, chromate 

plant) in order to investigate lung cancer associated with chromate production. Of the 2,931 

deaths of males in the county where the plant is located, 34 (1.2%) were due to respiratory 

cancer. Of the 33 deaths among the chromate workers, however, 6 (18.2%) were due to 

respiratory cancer. Within the limitations of the study design, this report strongly suggested an 

increased incidence of respiratory cancer in the chromate-production plant. 

In an update of the Mancuso and Hueper (1951) study, Mancuso (1975) followed 332 of 

the workers employed from 1931-1951 until 1974. By 1974, > 50% of this cohort had died. Of 

7
these men, 63.6%, 62.5%, and 58.3% of the cancer deaths for men employed in 1931-1932, 

1933-1934 and 1935-1937, respectively, were due to lung cancer. Lung cancer death rates 

increased with increases in exposure to total chromium, and significant deposition of chromium 

was found in the lungs of workers long after the exposure ceased. The age-specific lung cancer 

rates from and gradient exposures to total chromium from this study are presented in Table 2. 

Mancuso (1975) reported that these lung cancer deaths were related to insoluble (trivalent), 

soluble (hexavalent), and total chromium exposure, but the small numbers involved make 

identification of the specific form of chromium responsible for the lung cancer uncertain. 

Mancuso (1997) recently updated this study, following the combined cohort of 332 

workers until 1993. Of 283 deaths (85% of the cohort identified), 66 lung cancers were found 

(23.3% of all deaths and 64.7% of all cancers). Lung cancer rates clearly increased by gradient 

level of exposure to total chromium. The relationship between gradient level of exposure and 

lung cancer rates is less clear for trivalent and hexavalent chromium. The rates of lung cancer 

within the cohort are consistent with those reported in Mancuso (1975) and provide further 

support for the cancer risk assessment based on those data. 

Hayes et al. (1979) conducted a study of 2,101 male workers in a chromium chemicals 

production plant in Baltimore, MD, to determine whether employment in a modernized facility 

resulted in a reduction in the risk of lung cancer in comparison with that seen in workers 

employed in older production facilities. Mortality data for the workers were compared with 

cause-specific mortality rates for Baltimore city males, and correlations were made between a 

history of having worked in specific job positions and cancer of the lung. Workers with lung 

cancer as an underlying or contributory cause of death were individually matched to controls 

selected from plant workers who died of causes other than cancer. Many of the specific causes of 

death, including several sites of malignancy, showed results well below the expected number. 

While the newer facility had been constructed to reduce exposure to carcinogens, workers in the 

new facility were still found to have an increased risk of lung cancer. Both short-term and longterm workers were found to have excess risk for lung cancer, but the effect was more pronounced 

in the long-term workers. A dose-response relationship with respect to length of employment 

was observed, and long-term laborers were found to have a maximum risk (standard mortality 

ratio [SMR] = 3.9) between 15 and 19 years after the initial exposure. A history of having 

worked with highly soluble hexavalent chromium compounds in the “wet end” of the production 

process was particularly associated with an increased risk of lung cancer. Among the workers in 

the low- exposure group (n = 699), no excess risk was demonstrated. The authors were unable to 

obtain suitable data to account for cigarette smoking in the study population, and assumed that 

the smoking habits of workers were similar to those of the in the general population. 

Pastides et al. (1994) conducted a retrospective cohort study in the United States’ largest 

chromate chemicals manufacturing facility in Castle Hayne, NC. This plant was designed to 

reduce the high level of chromium exposure found at most of the older chromate production 

facilities. The study utilized more than 5,000 personal breathing zone samples collected over a 

15-year period. Occupational, medical, and smoking data from current and former employees 

were collected using a questionnaire. A healthy-worker effect was observed in the population. 

There was no increased risk of mortality or cancer among employees who worked only at this 

8
Table 2. Age-specific lung cancer death rates and gradient exposures to total chromium 

Mg/m3 - Yrs. total insoluble chromium 

Age < 1.00 1.0-1.99 2.0-3.99 4.0-5.99 6.0-6.99 7.0-7.99 

45-54 55-64 65-74 

Deaths 

Person-years 

Deaths 

Person-years 

Deaths 

Person-years 

1 

886 

1 

707 

1 

235 

2 

459 

3 

356 

1 

166 

2 

583 

1 

462 

2 

182 

4 

348 

4 

250 

1 

80 

3 

159 

2 

113 

1 

42 

3 

140 

3 

98 

0 

41 

aData in the last column are not used in EPA’s risk assessment because the range of exposure in this class 

and it does not appear reasonable to assume that all three age groups had an identical exposure distributio

9

Source: Mancuso, 1975. 
facility, though a subgroup of workers who transferred from older facilities was found to have 

higher risks of mortality and cancer. 

Rosenman and Stanbury (1996) recently reported on a study of lung cancer risk in a 

population of former workers from four facilities that produced chromium compounds from 

chromite ore. Workers at these facilities between 1937 and 1971 were found to have 

proportionate cancer mortality ratios (PCMR) of 1.51 for white men and 1.34 for black men. The 

PCMRs were found to increase with duration of employment and time since first employment. 

The authors also reported a PCMR for nasal/sinus cancer of 5.18. The lung cancer risk remained 

elevated for more than 20 years following the cessation of exposure. While the study was unable 

to account for smoking habits of the workers, the lack of increase in other smoking-related 

diseases suggested that the lung cancer was not related to smoking. The authors were unable to 

distinguish risk from trivalent and hexavalent chromium, and were also unable to examine risk 

by exposure estimates. 

Alexander et al. (1996) reported on a study of lung cancer in chromate-exposed aerospace 

workers with a minimum of 6 mo exposure to hexavalent chromium. Standard incidence ratios 

(SIRs) for lung cancer were determined on the basis of the duration of employment in chromateexposure jobs and cumulative exposure. The authors reported an inverse relationship between 

lung cancer risk and estimates of cumulative chromate exposure in spray painters. Elevated lung 

cancer risks were found for subjects who worked as chrome platers or surface processor tank 

tenders, sanders/maskers, and polishers, but the numbers are too low to establish a clear 

association between chromate exposure and lung cancer risk in these workers. The authors 

suggested that the lack of increased lung cancer risk among spray painters may reflect the 

exposure to chromate in paint mists, which they suggested may render the hexavalent chromium 

less biologically active. 

Studies of workers in chromate pigment production plants have demonstrated an 

association with increased risk of lung cancer. Hayes et al. (1989) studied workers employed 

between 1940 and 1969 in a lead and zinc chromate pigment production plant in New Jersey. 

The SMR for lung cancer was 160, based on comparison with U.S. lung cancer rates for white 

males. Workers in the high-exposure group were continuously exposed to greater than 2 mg/m3 

chromate dust; workers in the moderate-exposure group were occasionally exposed to 

concentrations between 0.5 and 2 mg/m3

 ; and workers in the low-exposure group were 

infrequently exposed at concentrations below 0.1 mg/m3

. Significant SMRs were also found for 

lung cancer in nonwhite males and stomach cancer in white males. Air monitoring revealed that 

exposures were lead chromate. 

Davies (1978, 1979) studied three chromate pigment plants in England, two of which 

produced both zinc and lead chromate, and one which produced only lead chromate. The cohort 

of exposed workers consisted of employees with �1 year of service and for whom vital statistics 

were available as of 1977. Using these guidelines, 396 and 136 subjects were obtained from the 

plants producing both zinc and lead chromate, and 114 subjects were obtained from the plant that 

produced only lead chromate. The observed mortality from lung cancer in the different plants 

was compared to the expected mortality based on national lung cancer mortality rates for all 

10
males in England and Wales. An elevated risk of lung cancer was present only in the plants 

producing both zinc and lead chromate. The authors suggested that these data indicated that zinc 

chromate was associated with the etiology of lung cancer, whereas lead chromate was not. 

Davies (1984) conducted a follow-up study on workers in the same three chromate 

pigment production plants. Workroom chromium concentrations and smoking statistics for the 

workers were not available in any of the factories. Elevated SMRs for lung cancer were 

observed, particularly for workers employed prior to improvements in industrial hygiene. 

Workers in the high- and medium-exposure groups in a plant producing lead and zinc chromates 

had an SMR for lung cancer of 232. Workers in high- and medium-exposure groups in a second 

lead and zinc chromate production plant had a SMR for lung cancer of 373. The SMR for 

workers in high and medium groups exposed to lead, zinc, and strontium chromate was 562. In 

the third plant, only lead chromate pigments were produced, and no excess lung cancer deaths 

were reported. 

Langard and Norseth (1975) reported on three pigment plants in Norway that were in 

operation between 1948 and 1972 (one of the plants was brought on line in the year the study 

ended). A total of 133 workers were identified as employees at the three plants during this time 

period. Of the 133, 24 had been employed > 3 years, and of this cohort, 3 cases of lung cancer 

were identified through the Cancer Registry of Norway. All of the lung cancer cases had been 

employed for 5 years or longer. Data from the cancer registry indicated an expected number of 

lung cancer cases among those employed of 0.079; thus, the observed number of cases was 38 

times greater than expected, based on the general population. Exposure levels determined by 

personal monitoring were reported for the plants for the year 1972, with chromium levels in the 

two older plants ranging between 0.04 and 1.35 mg/m3

 and levels in the new plant between 0.01 

and 0.08 mg/m3

. Although an increased risk of lung cancer was indicated, two of the individuals 

with lung cancer were moderate to heavy smokers. Nevertheless, a relative risk of lung cancer of 

38 could not be explained by differences in smoking between the study cohort and the Norwegian 

population. Langard and Vigander (1983) conducted a follow-up study on workers employed for 

at least 3 years in the same chromate pigment producing factories. Workroom monitoring 

revealed significantly elevated concentrations of hexavalent chromium (0.01 - 1.35 mg/m3), and 

an SMR for lung cancer of 4,444 was reported. Workers in this group were exposed over a 

period of 6-9 years. 

Frentzel-Beyme (1983) reported that the observed number of lung cancer deaths exceeded 

those expected among workers in five chromate pigment plants in the Netherlands and West 

Germany. In only one factory, however, was this excess statistically significant. The authors did 

not find a lung cancer mortality dose-response by intensity or duration of exposure. The analysis 

was limited by the numbers of deaths in each category. 

Several studies of the chrome-plating industry have demonstrated a positive relationship 

between cancer and exposure to chromium compounds (Royle, 1975; Franchini et al., 1983; 

Sorahan et al., 1987). Royle (1975) studied mortality in the chromium plating industry in 

England in a retrospective study between 1969 and 1972. Workers in this industry are exposed 

to hexavalent chromium in the form of chromic acid mist and some sodium dichromate dust. 

11
The study traced 1,238 chrome plating workers employed for > 3 months along with 1,284 

manual laborers used as controls. There was little difference in smoking habits between the 

groups. There was a significant (p < 0.05) difference in the death rate for cancer at all sites, 

3.15% in chrome platers as compared to 1.63% in controls. Deaths from malignancy of the lung 

and gastrointestinal tract were each increased, though not significantly. 

Franchini et al. (1983) conducted a retrospective cohort study of 178 workers in nine 

Italian chromeplating plants to determine the mortality of workers employed for at least 1 year 

between January 1951 and December 1981. The mortality experience of workers was compared 

to that for the Italian male population of the same age during the follow-up period. Direct 

exposure measures from the plants were not available, but the exposures were related to airborne 

chromium concentrations taken from Italian electroplating plants in 1980, after industrial hygiene 

practices had improved considerably. A significant excess of all malignancies and lung cancer 

specifically was found for the workers in “hard” chromeplating plants, who were expected to 

have the greatest chromium exposures. While the small size of the cohort limited the statistical 

power of the study and confounding factors were not assessed, this study is taken to provide 

suggestive evidence of a causal relationship between exposure to chromic acid and cancer. 

Sorahan et al. (1987) conducted a mortality study of nickel/chromium platers in England 

who were employed between 1946 and 1983. Exposure in these the plants was to soluble 

hexavalent chromic acid mist (CrO3). The cohort in the study included a population of 2,689 

workers (1,288 men, 1,401 women). Workers’ exposure to chromium was estimated based on 

participation in any of eight chromeplating job categories and on cumulative duration of 

employment in chrome bath jobs. The mortality experience of the cohort was evaluated through 

comparison with that expected for the general population of England and Wales, as well as 

through comparison of the estimated chrome exposures of workers who died in a given year with 

those of matching survivors in the same follow-up year, controlling for sex, year of starting 

chrome employment, and age starting in chrome employment. Overall, compared with the 

general population, significant differences were found for all cancers, cancers of the lung and 

bronchus, cancer of the nose and nasal cavities, cancer of the stomach, and primary cancer of the 

liver. The results were particularly striking for chrome bath workers, who were likely the most 

heavily exposed to chromium. Significant positive associations were found between cancers of 

the lung and bronchus and duration of chrome bath work. 

Some studies of the chromeplating industry have reported inconclusive results 

(Silverstein et al., 1981; Okubo and Tsuchiya, 1979; Takahashi and Okubo, 1990; Itoh et al., 

1996). Okubo and Tsuchiya (1979) conducted a cohort study of 889 Tokyo chrome platers, with 

an unspecified number of controls selected from the same factories. The study included a 6-year 

follow-up period. The investigation was conducted by a questionnaire sent to the manager of 

each factory, and vital statistics were ascertained using the records of the Tokyo Health Insurance 

Society of the Plating Industry. The recovery rate of the questionnaire was 70.5%. Among the 

889 male chromium platers, 19 deaths were observed, or about 50% of those expected (healthyworker effect). In contrast, the authors reported a slightly higher percentage of deaths in the 

control group. The authors reported negative results for the relationship between chromeplating 

12
and lung cancer; however, the results were not related to well-defined exposure data and the 

study utilized a very short follow-up period. 

Takahashi and Okubo (1990) reported on an epidemiological study of metal platers in 415 

small chromeplating plants in Japan. Members of the cohort were all male workers employed as 

platers for at least 6 mo between April 1970 and September 1976. The follow-up period 

extended until 1987 and no members of the cohort were lost to follow-up. The members of the 

cohort were classified into two subgroups based on their work histories: 52% of the cohort had 

more than 6 mo experience in chrome plating and 48% of the cohort had more than 6 mo plating 

experience using metals other than chromium. The mean duration of exposure before the followup period was 12.3 years. The study lacked direct exposure measures, and smoking histories for 

the workers were not available. All-cause mortality in the cohort was slightly below the expected 

number (healthy-worker effect). The study demonstrated that exposure to metal plating is 

associated with a statistically significant increase in lung cancer, though the elevated SMR was 

not statistically significant in either of the two plater subgroups. While chromium platers with 

initial exposure prior to 1960 had a 2.5-fold (though statistically insignificant) excess incidence 

of lung cancer, there was no increase in numbers of deaths due to lung cancer relative to the 

length of time exposed to chromeplating. The results of this study are considered equivocal 

regarding the relationship between chromeplating and lung cancer. Itoh et al. (1996) 

subsequently reported on a prospective cohort study of the same cohort of 1,193 workers at small 

Japanese plating facilities. While a trend toward statistical significance for risk of lung cancer 

was seen in the chromium plating subgroup, the study lacked sufficient statistical power to form 

a clear conclusion. 

Silverstein et al. (1981) found a statistically significant increase (p < 0.001) in the lung 

cancer proportionate mortality ratios for both male and female white employees in a die-casting 

and electroplating plant. In this plant, workers were exposed to chromium during electroplating, 

but nickel and copper were also used in electroplating. Other operations of the plant included 

zinc alloy die-casting, buffing and polishing, and cleaning of zinc and steel parts. No conclusion 

can be made from this study regarding the association of chromium electroplating and lung 

cancer mortality, because of the employees’ exposure to other potential carcinogens. 

A number of epidemiological studies have considered the association between inhalation 

of Cr(VI) and noncarcinogenic endpoints, including upper respiratory irritation and atrophy, 

lower respiratory effects, and systemic effects. 

Bloomfield and Blum (1928) examined 23 men from 6 chromium plating plants in the 

United States. Fourteen of these workers typically spent 2-7 hours/day over vats of chromic acid, 

which generated airborne hexavalent chromium ranging from 0.12 to 5.6 mg/m3

. These men 

experienced nasal tissue damage, including perforated septum (2), ulcerated septum (3), chrome 

holes (6), nosebleed (9), and inflamed mucosa (9). In general, the nine remaining workers 

examined, not directly exposed to chromium vapors, had only inflamed mucosae. The authors 

concluded that chromic acid at concentrations greater than 0.1 mg/m3 is likely to cause nasal 

tissue injury. However, no concentrations lower than 0.12 mg/m3

 were observed, and injury to 

nasal tissue caused by lower concentrations could not be ruled out. 

13
Machle and Gregorius (1948) reported an incidence of nasal septal perforation of 43.5% 

in 354 employees who worked in a chromate-producing plant that manufactured sodium 

chromate and bichromate. At the time of the study, airborne chromate concentrations ranged 

from 10 to 2,800 μg/m3

. The plant had been in operation for at least 17 years, and some 

employees probably worked in the plant when reverberatory furnaces, a prominent source of high 

chromate exposure, were used. 

Mancuso and Hueper (1951) reported on physical examinations of a random sample of 97 

workers from a chromate-chemical plant. The results indicated that 61 of the 97 workers (63%) 

had septal perforation. The data suggested to the author that Cr(III) may be partly responsible for 

the perforations; however, there are insufficient data to make an unequivocal conclusion. 

The U.S. Public Health Service conducted a study of workers in seven 

chromate-producing plants in the early 1950s. Of 897 chromate industry workers in the study, 

57% were found to have a nasal septum perforation. Perforated septum was observed even in 

workers employed less than 6 mo The study indicated that exposure to chromate results in severe 

nasal tissue destruction, but exposure levels were not measured; hence, the data are of limited 

usefulness for risk assessment purposes (Federal Security Agency, 1953). 

Vigliani and Zurlo (1955) reported nasal septal perforation in workers exposed to 

chromic acid and chromates in concentrations of 0.11-0.15 mg/m3

. The lengths of exposure were 

not known. Hanslian et al., (1967) reported on otolaryngologic examinations of 77 persons 

exposed to chromic acid aerosol during chrome plating. Among this group, 19% were observed 

to have septal perforation and 48% to have nasal mucosal irritation. The workers averaged 6.6 

years of exposure to an airborne chromium concentration of 0.4 mg/m3. In 14 persons, 

papillomas of the oral cavity and larynx were found. The diagnosis of papilloma was confirmed 

by histologic examination. There were no signs of atypical growth or malignant degeneration. 

Kleinfeld and Russo (1965) reported some degree of nasal septal ulceration in 7 of 9 

workers in a chromeplating plant, with 4 of 7 demonstrating frank perforations. Analyses of air 

samples showed chromium concentrations of 0.18-1.4 mg/m3

. Data regarding the length of 

exposure and exposure concentration for individual workers were not available. 

Gomes (1972) examined 303 employees who worked in 81 electroplating operations in 

Sao Paulo, Brazil. More than two-thirds of the workers had mucous membrane or cutaneous 

lesions, with many of them having ulcerated or perforated nasal septa. The duration of exposure 

was not stated, but the author mentioned that the harmful effects were noted in < l year. A direct 

correlation between workers exposed to a given airborne concentration of Cr(VI) and the 

development of harmful effects could not be made. 

Cohen and Kramkowski (1973) and Cohen et al. (1974) examined 37 workers (7 male 

and 30 female) employed in the nickel-chrome department of an electroplating plant in 

comparison with 21 workers (15 male and 6 female) in other areas of the plant not significantly 

exposed to chromic acid. Smoking demographic data were not provided. Environmental air 

samples were collected from breathing zones of several workers in the exposed and control 

14
groups to determine concentrations of total chrome and Cr(VI). Brief medical histories were 

confined to the ear, nose, throat, and cutaneous structures. Within l year of employment, 12 

workers experienced nasal ulceration or perforation. Nasal ulcers and perforations were 

associated with total chromium concentrations of 1.4 to 49.3 μg/m3

, averaging 7.1 μg/m3, and 

Cr(VI) concentrations of 0.09 to 9.1 μg/m3, averaging 2.9 μg/m3. Ninety-five percent of the 37 

workers studied exhibited pathologic changes in nasal mucosa in a concentration-duration 

response. More than half of the workers employed less than 1 year had nasal pathology that was 

more severe than simple redness of the nasal mucosa. Almost all the workers (35 of 37) 

employed longer than 1 year had nasal tissue damage. The authors noted the lack of good 

industrial hygiene practices, implicating direct contact, such as touching of the nose with 

chromium-contaminated hands, as a potentially important route of exposure. 

Lucas and Kramkowski (1975) conducted a health hazard evaluation of 11 employees in 

the “hard” chrome area of an industrial plating facility. The average age of the employees was 39 

years and the average duration of employment in the hard chrome area was 7.5 years. Medical 

examinations were conducted to evaluate the presence of dermatitis, chrome holes, old chrome 

hole scars, ulcerated nasal septum, infection of the mucosa, nasal redness, perforated nasal 

septum, reddened throat, conjunctivitis, and wheezing. Environmental air samples were 

collected from the breathing zone on all workers in the hard chrome area to determine the 

concentrations of hexavalent chromium. Cr(VI) concentrations ranged from 1 to 20 μg/m3

, 

averaging 4 μg/m3. However, the authors attributed the nasal pathology primarily to direct 

contact. Clinical observations included injection of the nasal mucosa in five workers, ulcerated 

nasal septum in two workers, atrophic scarring indicative of the presence of past ulceration in 

two workers, and complete perforation of the nasal septum in four workers. Poor hygiene 

practices including touching the nose with the hand were noted at the plant and represented a 

confounding factor in the etiology of the nasal lesions. 

Markel and Lucas (1973) conducted a health hazard evaluation of 32 workers at a “cold 

dip” chromeplating plant who were employed in the chrome department or who regularly spent a 

portion of their workday in that area. Twenty of the employees worked in the chrome area of the 

plant for more than 5 years. A total of 16 personal and 7 general air samples were taken to 

determine the concentrations of Cr(VI). Maximum airborne Cr(VI) concentration was 3 μg/m3

. 

No workers were found to have ulcerated nasal mucosa or perforated nasal septa. Half of the 32 

employees had varying degrees of mucosal irritation. The authors did not consider this to be 

significant, because the survey was carried out at the peak of the 1972-1973 influenza epidemic. 

Lindberg and Hedenstierna (1983) compared lung function, the condition of the nasal 

septum, and subjective symptoms related to respiratory health (data obtained by questionnaire) in 

unexposed controls (119) and workers (43) exposed to chromic acid in chromeplating operations. 

Exposed workers were divided into low- (< 2) and high- (> 2 μg Cr[VI]/m3

) exposure groups 

based on the exposures they were likely to have experienced in the workplace. Complaints of 

diffuse nasal symptoms (“constantly running nose,” “stuffy nose,” or “a lot to blow out”) were 

registered by 4/19 workers in the low-exposure group and half of the 24 workers in the high 

exposure group. The authors reported reddening of the nasal mucosa at 1 to 2 μg/m3

 and nasal 

irritation (chronic and nasal septal ulceration and perforation) in two-thirds of the subjects at 

15
concentrations from 2 to 20 μg/m3

. All workers with nasal ulceration had been exposed to 

chrome acid mist, which contained Cr(VI) at 20 μg/m3

, or greater than 20 μg/m3 near the baths. 

Changes in pulmonary function measurements, as determined by changes in vital capacity and 

forced expiatory volume at 1 sec (FEVl), were seen in workers who experienced Cr(VI) 

exposures greater than 2 μg/m3. Examination of the nasal septum revealed that damage was 

significantly greater in exposed workers than in unexposed controls and appeared to be 

somewhat more severe in the high-exposure group than the low-exposure group. There was a 

tendency for lung function parameters to return to normal over a 2-day weekend. 

In the United States, 97 workers in chromate-producing plants had a higher incidence of 

severely red throats and pneumonia, but did not show any increase in the incidence of other 

respiratory diseases when compared with control groups. Although bilateral hilar enlargement 

was observed, there was no evidence of excessive pulmonary fibrosis in these workers (Federal 

Security Agency, 1953). The various lung changes described in these workers may represent a 

nonspecific reaction to irritating material or a specific reaction to chromium compounds. Many 

of the conditions mentioned occur widely in the general population (NAS, 1974). 

Lindberg and Vesterberg (1983a) studied urinary excretion of proteins in 24 currently 

employed chrome platers and 27 former chrome platers. Results were compared with those for a 

group of 37 referents. Exposures for current workers were determined using personal samplers 

and were found to range from 2 to 20 μg/m3

, with an average level of 6 μg/m3. Exposure levels 

of former platers were thought to be higher than those for the current workers. The duration of 

exposure ranged from < 1 to 26 years. Cr(VI) exposure was found to result in renal effects in a 

dose-dependent fashion (based on elevated excretion of �-2-microglobulin as an indicator of 

nephrotoxicity) in current workers exposed to 4 to 20 μg/m3 Cr(VI) over 8-hour shifts. The 

effect may be reversible because former chromeplaters did not have an elevated concentration of 

either �-2-microglobulin or albumin in their urine. Most of the currently exposed workers were 

also observed to have irritation symptoms of the airways, including ulcerated nasal septum and 

complete perforations. Severe objective and subjective levels for the airway effects occurred at 

NOAEL levels for renal toxicity. 

In another study, Saner et al. (1984) did not find increased urinary �-2-microglobulin 

levels in tannery workers in comparison to referent control workers. However, comparison of 

urinary chromium concentrations of the tannery workers in this study versus the chromeplaters in 

the Lindberg and Vesterberg (1983a,b) study suggests that the latter had distinctly higher 

chromium exposures. 

Various other disease states have been attributed to chromium, but in most cases, the 

etiologic relation to chromium is doubtful because of the presence of other chemicals (NAS, 

1974). These studies, reviewed by EPA (1984) and ATSDR (1993), will not be reviewed here. 

16
4.2. SUBCHRONIC, CHRONIC STUDIES AND CANCER BIOASSAYS IN ANIMALS 

4.2.1. Chronic Oral Studies 

Only one chronic study pertaining to the oral toxicity of hexavalent chromium was 

located in the available literature. Anwar et al. (1961) exposed dogs orally to potassium 

chromate in drinking water for 4 years. Treatment levels were 0, 0.45, 2.25, 4.5, 6.75, and 11.2 

ppm potassium chromate; there were two dogs/group. No effects were observed with regard to 

gross and microscopic analysis of all major organs, urinalysis, and weights of spleen, liver, and 

kidney. 

4.2.2. Subchronic Oral Studies 

The National Toxicology Program recently conducted a three-part reproductive toxicity 

study to investigate oral ingestion of hexavalent chromium in experimental animals (NTP, 

1996a,b, 1997). Rats and mice were exposed to 0 - 400 ppm potassium dichromate daily in the 

diet for 9 weeks. Animals were examined for body weights; feed and water consumption; organ 

weights; microscopic evaluation of the liver, kidney, and ovaries; hematology; histology of the 

testis and epididymus for Sertoli nuclei and preleptotene spermatocyte counts in Stage X or XI 

tubules; and chromatin analysis. No treatment-related hematology findings were reported except 

for slight decreases in mean corpuscular volume (MCV) and mean corpuscular hemoglobin 

(MCH) values in the male and female treatment groups receiving 400 ppm potassium dichromate 

(24 mg/kg-day). The findings were characterized by the authors as suggestive of a potential bone 

marrow/erythroid response. The authors considered the 100 ppm (6 mg/kg-day) dose group to be 

representative of the NOAEL for the study. The studies are described in greater detail in the 

reproductive/developmental section of this document. 

MacKenzie et al. (1958) exposed groups of eight male and eight female Sprague-Dawley 

rats to 0-11 ppm (0-11 mg/L) hexavalent chromium (as K2CrO4) for 1 year in drinking water. 

The control group (10/sex) received distilled water. A second experiment involved three groups 

of 12 male and 9 female rats. One group was given 25 ppm (25 mg/L) chromium (as K2CrO4), a 

second group received 25 ppm chromium in the form of chromic chloride, and the controls again 

received distilled water. The results of the MacKenzie et al. study are presented in Table 3. No 

significant adverse effects were seen on appearance, weight gain, or food consumption, and there 

were no pathologic changes in the blood or other tissues in any treatment group. The rats 

receiving 25 ppm of chromium (as K2CrO4) showed an approximate 20% reduction in water 

consumption. This dose corresponds to 2.5 mg Cr(VI)/kg/day based on actual body weight and 

water consumption data. Blood was examined monthly, and tissues (livers, kidneys, and femurs) 

were examined at 6 mo and 1 year. Spleens were also examined at 1 year. The 25 ppm groups 

(and corresponding controls) were examined similarly, except that no animals were killed at 6 

mo. An abrupt rise in tissue chromium concentrations was noted in rats treated with greater than 

5 ppm. The authors stated that “apparently, tissues can accumulate considerable quantities of 

chromium before pathological changes result.” In the 25 ppm treatment groups, tissue 

concentrations of chromium were approximately nine times higher for those treated with 

hexavalent chromium than for the animals exposed to trivalent chromium. 

17
Table 3. Subchronic oral toxicity of hexavalent chromium in rats 

Number of 

animals 

Dose and 

compound 

Period of 

exposure 

Endpoints monitored 

and effect 

9 females, 12 males at 25 

ppm 

10 males, 19 females at 9 

ppm 

8 males, 8 females at 

other treatment levels 

0, 0.45, 2.2, 4.5, 7.7, 11, 

25 ppm as potassium 

dichromate in drinking 

water 

1 year No effect based on body 

weight, gross external 

condition, 

histopathological 

analysis, and blood 

chemistry. 

Source: MacKenzie et al., 1958. 

Gross and Heller (1946) reported that 0.125% K2CrO4 in the feed of rats was tolerated 

without observable effects. A dose of 0.25% in the diet resulted in “subnormal condition,” 

including rough coat and “subnormal” young born to treated animals. Doses of 0.5% and 1% in 

feed resulted in diarrhea, rough dirty coats, and sterility. ZnCrO4 administered in the feed at 

levels of 0.125%, 0.25%, 0.5%, and 1.0% resulted in subnormal appearance, rough and dirty 

coats, and sterility at all dose levels. Group sizes, duration of treatment, and criteria for 

determining sterility were not reported. 

4.2.3. Chronic Inhalation Studies 

Two studies have provided suggestive evidence of carcinogenicity in mice and rats 

following inhalation of hexavalent chromium (Nettesheim et al., 1971; Glaser et al., 1986). 

Nettesheim et al. (1971) exposed C57B1 mice to 13 mg calcium chromate/m3

 (4.33 mg 

Cr[VI]/m3 as calcium chromate dust), 5 hours/day, 5 days/week for life. Chromium exposure 

resulted in a cessation of body weight gain at 6 mo followed by a decrease in body weight 

thereafter. Bronchial epithelial effects ranged from marked hyperplasia and atrophy to necrosis, 

suggesting that the maximum tolerated dose may have been exceeded in this study. 

Inflammatory infiltration into the subepithelium including proliferation of bronchial epithelial 

cells was noted. Distension of terminal bronchioli and alveoli resembling emphysema was 

associated with alveolar proteinosis. A 2.8% increase in the number of lung tumors was reported 

with respect to controls. However, statistical analysis was not performed, and the significance of 

these results is unclear. In a review of this study, IARC (1990) concluded that a significant 

excess of treatment-related tumors was not observed. Nettesheim identified 4.33 mg of calcium 

chromate dust/m3

 as a LOAEL for the occurrence of epithelial necrosis, marked hyperplasia and 

atrophy of the pulmonary bronchi, emphysema-like changes, and atrophy of the spleen and liver. 

The single dose used in this study raises the question whether 4.33 mg Cr(VI)/m3

 actually 

represents a LOAEL. 

18
Glaser et al. (1986) exposed male Wistar rats (20/group) to aerosols of sodium chromate 

at measured concentrations of 0.025, 0.05, and 0.1 mg Cr(VI)/m3

, 22 hr/day, 7 days/week for 18 

mo. An additional group was exposed to a pyrolized Cr(VI)/Cr(III) (3:2) oxide mixture at 0.063 

Cr(VI)/m3. The animals were held under conventional conditions for 12 mo following the 

exposure. Body weights and mortality were similar among all exposure groups and controls. 

Primary lung tumors (1 adenocarcinoma and 2 adenomas) and 1 squamous cell carcinoma of the 

pharynx were evident in the high-chromate exposure group. It is not clear whether the 

adenocarcinoma and adenomas occurred in the same animal or in different animals. One primary 

lung adenoma was observed in the oxide-exposed group. Primary lung tumors were not observed 

in the controls or low-chromate exposure groups. Dose-dependent retention of chromium was 

seen in the chromate- and oxide-exposed groups relative to the controls. At the conclusion of the 

study, lung chromium retention was 10-fold greater in the oxide-exposed group than in the highchromate-exposed group. Significantly increased lung weights were determined for the oxideexposed group and greater liver weights in the high-exposure group of the chromate. Pigmentloaded macrophages were found in a dose-dependent manner in rats exposed to chromate and to 

the oxide. Oxide-exposed rats developed focal thickened septa, partially combined with 

interstitial fibrosis and accumulation of eosinophilic substance in the alveolar lumens. Oxideexposed groups also demonstrated elevated white- and red-blood cell counts, elevated serum 

cholesterol, and decreased total serum immunoglobulin levels. The results of this study may 

provide evidence of a weak carcinogenic potency of aerosols of both sodium dichromate and 

Cr(VI/III) oxide (Glaser et al., 1986; Glaser et al., 1988). 

Steinhoff et al. (1983) investigated the carcinogenicity of soluble sodium dichromate and 

calcium chromate in Sprague-Dawley rats via intratracheal administration and reported positive 

carcinogenic effects. The study consisted of 10 treatment groups, one negative control group, 

and two positive control groups. Each test group contained 40 male and 40 female rats (10 

weeks old at the outset). The design of the dose levels selected was such as to assess the impacts 

of the chemicals delivered in single high doses or in the same dose distributed over a 5-day 

period. The duration of the study was 2 years and 8 months. Doses ranged from 0.5 to 1.25 

mg/kg. Rats administered sodium dichromate or calcium chromate one or five times per week 

had no significant reduction in survival periods as compared to controls, except in the case of 

females treated with calcium chromate 5 × 0.25 mg/kg/week. An increased incidence of lung 

tumors as compared to controls was observed in the treated group in which sodium dichromate 

was administered in a single dose of 1.25 mg. No lung tumors were observed in the other 

sodium dichromate treatment groups. In rats administered calcium chromate, statistically 

significant increases in lung tumors were found in groups treated with a single dose of 1.25 

mg/kg as well as in the group treated with 5 × 0.25 mg/kg/week distributed over a period of 5 

days. 

There is some evidence that hexavalent chromium may be carcinogenic following 

intrapleural implantation of calcium chromate (Hueper and Payne, 1962) or intrabronchial 

implantation of strontium chromate, calcium chromate, or zinc chromate (Levy and Martin, 

1983). These tumors, however, were observed only at the site of implantation. Steffee and 

Baetjer (1965) observed statistically significant increases in lung tumors following intratracheal 

19
instillation of 0.01 to 0.03 mg zinc chromate in strain A mice. The instillations were performed 

at 2-week intervals and the animals were observed until death. 

In contrast, intratracheal and intrapleural implantation studies of other chromium 

compounds have not demonstrated increases in tumor incidences. Mixed hexavalent and 

trivalent chromium-containing dust was not carcinogenic in strain A Swiss and C57BL mice and 

mixed-breed rats following intratracheal implantation (Baetjer et al., 1959). Steffee and Baetjer 

(1965) did not observe increases in lung adenomas following instillation of chromium dust, zinc 

chromate, and lead chromate into the tracheas of guinea pigs and rabbits. Hueper and Payne 

(1962) reported similar negative results after instillation of strontium chromate or calcium 

chromate suspended in gelatin; however, the experimental detail in the report was insufficient for 

adequate evaluation. Hueper and Payne (Hueper, 1955, 1958; Payne, 1960; Hueper and Payne, 

1962) described a series of studies in rats treated by intrapleural injection of a number of 

hexavalent or trivalent compounds. Hueper (1955) injected powdered metallic chromium into 

the pleural cavity of rats, guinea pigs, and mice and observed no significant increase in tumor 

incidence, either at the injection site or in other organs. Payne (1960) implanted chromite roast, 

from which the soluble sodium chromate was extracted, into the pleural cavity of 35 rats. None 

of the 35 control animals developed tumors, and three of the treated animals developed tumors at 

the implantation site. In an earlier study, Hueper (1958) using chromite roast not leached of 

sodium chromate, none of the 25 treated male Bethesda rats developed implantation site tumors 

during 24 mo; however, the early deaths of nine of the treated animals decreased the number of 

animals at risk. Hueper and Payne (1962) noted that no implantation site tumors were observed 

in 42 rats during a 24-mo period following eight implantations of 25 mg of trivalent chromium 

acetate in gelatin over a 13-mo period. 

Baetjer et al. (1959) chronically exposed three strains of mice (Strain A, Swiss, and 

C57Bl) and mixed-breed rats to approximately l mg chromium dust/m3

, 4 hours/day, 5 days/week 

over a range of 16-58 weeks, and reported no increase in the incidence of lung tumors with 

respect to untreated controls. Similar results were obtained by Steffee and Baetjer (1965) for 

Wistar rats, rabbits, and guinea pigs exposed to chromium dust. 

Laskin (1972) exposed rats and hamsters to calcium chromate aerosol at a level of 2 

mg/m3

 (0.67 mg Cr(VI)/m3) for 589 days out of an 891-day study. Although some laryngeal 

hyperplasias and metaplasias were observed in both species tested, details pertaining to controls 

were not given in the available review. 

4.2.4. Subchronic Inhalation Studies

Data from animal studies identify the respiratory tract as the primary target of chromium 

toxicity following inhalation. Glaser et al. (1985) exposed 5-week-old male Wistar rats to 

aerosols of sodium dichromate at concentrations ranging from 0.025 to 0.2 mg Cr(VI)/m3

, 22 

hr/day in subacute (28 day) or subchronic (90 day) protocols. Subacute and subchronic 

exposures to Cr(VI) aerosol concentrations resulted in a positive correlation between exposure 

dose and significant effects on alveolar macrophages and immunological function. Inhalation of 

Cr(VI) aerosols stimulated the humoral immune system. Differences in the mean total serum 

20
immunoglobulin were significant at exposures above 0.025 mg/m3

, while exposures to aerosol 

concentrations greater than 0.1 mg/m3

 resulted in depression of the immune system stimulation. 

The primary antibody response to the �-cell-dependent antigen sheep red blood cell was elevated 

in a chromium time- and dose-dependent manner. The immune stimulating effect of subchronic 

exposure to an aerosol with 0.05 mg/m3 chromium was not reversed after 2 months of fresh air 

regeneration. Subchronic exposure to 0.2 mg/m3 chromium resulted in depression of the 

immune-stimulating effect relative to the response at 0.05 mg/m3

. The spleen T-lymphocyte 

subpopulation was also stimulated by subchronic exposure to 0.2 mg/m3

 chromium. 

Bronchoalveolar lavage (BAL) cell counts were significantly decreased following subchronic 

exposure to levels above 0.025 mg/m3

 chromium, though it was not clear whether the 

effectiveness of the lavagability of the cells was altered at the higher dose levels. The number of 

lymphocytes and granulocytes showed a slight but significant increase in the lavage fluids of the 

of the subacute and subchronically exposed groups. At subacute exposure concentrations up to 

0.05 mg/m3

 the phagocytic activity of the alveolar macrophages increased; however, subchronic 

exposure at 0.2 mg/m3

 decreased this function significantly, complicating the interpretation of 

this result. Following subacute exposure to 0.2 mg/m3 chromium, reductions in macrophage cell 

counts and phagocytic activities correlate with an observed lower clearance of inhaled iron oxide. 

Inhaled chromium was found to preferentially accumulate in the lung following exposure to 

chromate aerosols. Lung and spleen weights were significantly increased (p < 0.005) after both 

subacute and subchronic inhalation of chromate aerosols at concentrations greater than 0.025 

mg/m3

. Serum contents of triglycerides and phospholipids differed significantly from controls (p 

< 0.05) in rats exposed subchronically to 0.2 mg/m3 chromate. 

Glaser et al. (1990) presented a paper at the Second European Meeting of Environmental 

Hygiene that reported exposure of 8-week-old male Wistar rats to sodium dichromate at 0.05, 

0.1, 0.2, and 0.4 mg Cr(VI)/m3 22 hr/day, 7 days/week for 30-90 days. Chromium-induced 

effects occurred in a strong dose-dependent manner. The authors observed obstructive 

respiratory dyspnea and reduced body weight following subacute exposure at the higher dose 

levels. The mean white blood cell count was increased at all doses (p < 0.05) and was related to 

significant dose-dependent leukocytosis following subacute exposures. Mean lung weights were 

significantly increased at exposure levels of 0.1 mg/m3 following both the subacute and 

subchronic exposures. Accumulation of macrophages was seen in all of the exposure groups and 

was postulated to be a chromium-specific irritation effect that accounted for the observed 

increases in lung weights. 

Focal inflammation was observed in the upper airways following the subchronic 

exposure. BAL analyses provided more detailed information on the nature of the dichromateinduced irritation effect. BAL albumin was increased following the subacute exposure, and was 

taken to indicate exudation into the alveolar region as an early irritation effect. The mean protein 

content of the cell-free lavage fluid was significantly increased in a dose-dependent fashion after 

the subacute and subchronic exposures. However, protein levels returned to control levels 

following a recovery period. Cytosolic lactate dehydrogenase and the number of mononuclear 

macrophages were also elevated following the subacute and subchronic exposures, particularly at 

the highest dose levels. The enzyme activity and number of macrophages returned to the control 

level following the recovery period. The authors concluded that chromium inhalation induced 

21
pneumocyte toxicity and suggested that inflammation is essential for the induction of most 

chromium inhalation effects and may influence the carcinogenicity of Cr(VI) compounds (Glaser 

et al., 1990). 

Johansson et al. (1980) exposed groups of four rabbits to chromium dust at 

concentrations of 3.1 mg/m3

 and 0.6 mg/m3 for 5 days/week, 6 hours/day for 4 weeks. 

Macrophages collected from rabbits exposed to the higher concentration of chromium 

phagocytized significantly more chromium particles than the controls, though the number of 

nonviable macrophages was less than 3%. 

Johansson et al. (1986) exposed groups of rabbits to aerosols of hexavalent (0.9 mg 

Cr[VI]/m3

 as Na2CrO4) or trivalent (0.6 mg Cr[III]/m3 as Cr[NO3]3) chromium 5 days/week, 6 

hours/day for four to six weeks. The number of macrophages obtained from the lungs of the 

rabbits exposed to Cr(VI) was significantly increased. While the numbers of macrophages from 

rabbits exposed to Cr(III) were not increased, striking morphological changes were observed, 

including round dark chromium-rich inclusions in the cytoplasm, an increased number of cells 

with a smooth, inactive cell surface, enlarged Golgi apparatus, and a tendency toward elongated 

cell shape. The macrophages from rabbits exposed to Cr(VI) showed less marked morphological 

changes than those exposed to Cr(III). 

Lee et al. (1988) exposed groups of 30 male and 30 female rats to 0.5 mg/m3

 or 25 mg/m3 

CrO2 (IV) 6 hr/day, 5 days/week for 2 years. There were no compound-related differences in 

weight gain between exposed and control groups and no exposure-related mortality in any 

exposed group. There were no compound-related lesions in the vital organs and tissues other 

than in the lungs of exposed rats. Dust-laden alveolar macrophages with slight Type II 

pneumocyte hyperplasia were noted following exposure at 0.5 mg/m3

. Inhaled particles were 

deposited mainly in the alveoli adjacent to the alveolar ducts and the dust particles appeared as 

dense particles and were phagocytized by intraalveolar macrophages. Exposure at 25 mg/m3 was 

suggested to have overwhelmed the lung clearance mechanisms and resulted in significant 

increases in dust-laden macrophages, bronchoalveolar cell hyperplasia with foamy macrophage 

response, and cholesterol granuloma. The mechanism of action was not confirmed in the study, 

and the observation of dust particles in the alveolar macrophages is not necessarily indicative of 

overloading of the lung clearance mechanism. At 24 mo, the dust deposition and effects were 

increased significantly, with severe dust-laden macrophages, dust deposition in peribronchial 

lymphoid tissue, hyperplasia of Type II pneumocytes, and collagenized fibrosis occurring in 

100% of all lung tissues examined in either gender. Two female rats developed welldifferentiated cystic keratinizing squamous cell carcinomas with no tumor metastasis. The 

tumors were not characterized as neoplastic lesions. 

Mice exposed to 1.81 or 3.63 mg/m3

 Cr(VI) as CrO3 for 1 year developed nasal septal 

perforation, loss of cilia, and metaplasia of the lung, trachea, and bronchus (Adachi, 1987; 

Adachi et al., 1986) 

22
4.3. REPRODUCTIVE/DEVELOPMENTAL STUDIES 

4.3.1. Oral Studies 

High doses of Cr(VI) compounds have been reported to cause developmental toxicity in 

mice. Trivedi et al. (1989) exposed mice to 250, 500, and 1,000 ppm potassium dichromate daily 

through drinking water during the entire gestational period. The authors reported decreased fetal 

weight, increased resorptions, and increased abnormalities (tail kinking, delayed ossification of 

the cranium) in exposed mice. The medium- and high-dose groups registered significant 

reductions in body weight gain when compared to controls. The most significant finding of the 

study was the complete absence of uterine implantation in the high-dose group. The 250 and 500 

ppm dose groups also showed significant incidences of resorption as compared to controls. The 

authors observed significant increases in preimplantation and postimplantation losses and dosedependent reductions in total weight and crown-rump length in the lower dose groups. 

Additional effects included treatment-related increases in abnormalities in the tail, wrist 

forelimbs and subdermal hemorrhagic patches in the offspring. 

Zahid et al. (1990) fed BALB/C albino Swiss mice trivalent (chromium disulfate) and 

hexavalent (potassium dichromate) chromium at concentrations of 100, 200, and 400 ppm for 35 

days in the diet. The authors stated that the exposure groups included seven animals per group, 

and an additional seven animals were used as controls, though conflicting summaries of the 

actual group sizes are presented throughout the report. Following the treatment, the authors 

examined the testes and epididymis of the animals. The epididymis was weighed and minced 

suspended in buffered formalin. Sperm counts were then subsequently determined and sperms 

were examined for morphological abnormalities. Testes were fixed with Bouin’s fluid for 1 

week and were subsequently sectioned to 0.6 micron thickness and stained with haematoxylin 

and eosin for histological examination. Ten sections were chosen randomly from the anterior, 

middle, and posterior parts of each testis and studied. One seminiferous tubule was chosen and 

examined to determine the cellular stages of spermatogenesis and the number of degenerated 

tubules. Statistical analyses of the data were conducted using the t-test between means and the 

2 × 2 contingency chi-square test between percentages. The authors reported deleterious effects 

on the male mouse testes, including ambiguous levels of degeneration in the outermost cellular 

layers of the seminiferous tubules, reduced (or absent) spermatogonia per tubule, accumulation of 

germ cells in the resting spermatocytes stage, reduced sperm count in the epididymis, and 

increased percentage of morphologically abnormal sperms at all dose levels. The authors 

concluded that the small but significant increase of hexavalent chromium in the testes of fed 

animals induced significant degeneration. 

Serious questions have been raised regarding the design and conduct of this study (Finley 

et al., 1993; NTP 1996a,b, 1997). The methods utilized in the Zahid et al. study are considered 

to be insufficient to identify spermatogonia, likely generated nonreproducible counts of 

epididymal sperm, and resulted in the biologically implausible conclusion of reduction in 

spermatogonia numbers concurrent with unchanged spermatocyte and spermatid numbers. 

Additional questions have been raised with regard to uncertainties regarding the actual groupings 

of animals used and the statistical analysis of the data. 

23
The National Toxicology Program recently conducted a three-part study to investigate 

oral ingestion of hexavalent chromium in experimental animals (NTP, 1996a,b, 1997). 

The study included a determination of the potential reproductive toxicity of potassium 

dichromate in Sprague-Dawley rats, a repeat of the study of Zahid et al. (1990) using BALB/C 

mice, and a Reproductive Assessment by Continuous Breeding study in BALB/C mice. 

The study in the Sprague-Dawley rat (NTP, 1996a) was conducted in order to generate 

data in a species commonly used for regulatory studies. Groups of 24 males and 48 females were 

exposed to 0, 15, 50, 100, or 400 ppm potassium dichromate daily in the diet for 9 weeks 

followed by a recovery period of 8 weeks. Six male and 12 female rats were sacrificed after 3, 6, 

or 9 full weeks of treatment or after the full recovery period. Animals were examined for body 

weights; feed and water consumption; organ weights; microscopic evaluation of the liver, kidney, 

and ovaries; hematology; histology of the testis and epididymus for Sertoli nuclei and 

preleptotene spermatocyte counts in Stage X or XI tubules; and chromatin analysis. No 

treatment-related hematology findings were reported except for slight decreases in MCV and 

MCH values in the male and female treatment groups receiving 400 ppm potassium dichromate 

(24 mg/kg-day). While the trends in MCV and MCH were not large and were within the 

reference ranges (Charles River Laboratories, 1993), they are consistent with the findings of the 

companion studies in BALB/C mice (see below) and were characterized by the authors as 

suggestive of a potential bone marrow/erythroid response. The authors considered the 100 ppm 

(6 mg/kg-day) dose group to be representative of the NOAEL for the study. 

The reproductive study in BALB/C mice (NTP, 1996b) was conducted to reproduce the 

conditions utilized by Zahid et al. (1990) in their examination of comparative effects of trivalent 

and hexavalent chromium on spermatogenesis of the mouse. Groups of 24 male and 48 female 

BALB/C mice were exposed to 0, 15, 50, 100, or 400 ppm potassium dichromate in the diet for 9 

weeks followed by a recovery period of 8 weeks. Six male and 12 female mice were sacrificed 

after 3, 6, or 9 full weeks of treatment or after the full recovery period. Animals were examined 

for body weights; feed and water consumption; organ weights; microscopic evaluation of the 

liver, kidney, and ovaries; hematology; histology of the testis and epididymus for Sertoli nuclei 

and preleptotene spermatocyte counts in Stage X or XI tubules; and chromatin analysis. 

Treatment-related effects included a slight reduction in the mean body weights in the 400 ppm 

males and the 100 ppm females, a slight increase in food consumption at all dose levels, a slight 

decrease in MCV and MCH at 400 ppm, and cytoplasmic vacuolization of the hepatocyte at 50, 

100 and 400 ppm. None of the effects on spermatogenesis reported by Zahid et al. (1990) were 

observed in this study. On the basis of the cytoplasmic vacuolization of the hepatocyte in the 50, 

100, and 400 ppm dose groups, the authors selected 15 ppm (4 mg/kg-day) as the NOAEL. 

The potential reproductive toxicity of potassium dichromate was further evaluated in 

BALB/C mice using the Reproductive Assessment by Continuous Breeding protocol (NTP, 

1997). In the continuous breeding phase of the study, groups of 20 male and female pairs of 

animals (F0) were exposed to dose levels of 0, 100, 200, and 400 ppm potassium dichromate, 

based on the previous study of reproductive effects in BALB/C mice. Litters born after the 

continuous breeding phase (F1) received the same concentrations of potassium dichromate as 

their F0 parents. F1 animals were used for assessment of second-generation reproductive toxicity. 

24
At sexual maturity, 20 control animals of each sex and 20 treated animals of each sex in each 

dose group were selected as breeding pairs (avoiding sibling matings), cohabitated for 7 days, 

and then separated. Offspring were counted and examined for terminal body and organ weights 

and received sperm and tissue analysis. The NTP studies were designed to repeat the findings of 

Zahid using methods of greater rigor and definition, but were unable to do so. The reproductive 

assessment indicated that potassium dichromate administered at 100, 200, or 400 ppm in the diet 

to male and female BALB/C mice is not a reproductive toxicant in either sex. Fertility and the 

pregnancy index (number delivering/number cohabitated) were not affected by continued 

exposure to potassium dichromate. No treatment-related differences were observed in the mean 

average litters per pair, number of live pups per litter, proportion of pups born alive, sex ratio, 

absolute live pup weight, or adjusted live pup weight. Mean body weights of the high-dose F0 

and F1 animals were slightly decreased relative to controls, and mean food consumption in the F1 

animals was increased relative to controls. Mean absolute liver weights in the high-dose group 

F0 animals were decreased relative to controls. Treatment-related changes were observed in the 

hematology data for the F1 animals. The MCV was slightly decreased in the high-dose males, 

and the MCH was slightly decreased in the female animals in all dose groups. The authors 

suggested that the NOAEL was not established in this study because of the slight decrease in 

MCH in the females of the 100 ppm (22.4 mg/kg-day) dose group. 

Junaid et al. (1996) exposed female Swiss albino mice to 250, 500, or 750 ppm potassium 

dichromate in drinking water to determine the potential embryotoxicity of hexavalent chromium 

during days 6-14 of gestation. No notable changes in behavior or clinical signs were observed in 

the control or treated dams. Chromium levels in blood, placenta, and fetus increased in a dosedependent fashion over the course of the study. The authors reported retarded fetal development 

and embryo- and fetotoxic effects including reduced fetal weight, reduced number of fetuses (live 

and dead) per dam, and higher incidences of stillbirths and postimplantation loss in the 500 and 

750 ppm dosed mothers. Significantly reduced ossification in nasal, frontal, parietal, 

interparietal, caudal, and tarsal bones was observed in the high-dose group, while reduced 

ossification in only the caudal bones was observed in the 500 ppm dose group. Based on the 

body weight of the animals (30 +/- 5 g) and the drinking water ingested by the animals in the 250 

ppm dose group (8.0 ml/mouse/day), the dose level in the 250 ppm group can be identified as 67 

mg/kg-day. 

Kanojia et al. (1996) exposed female Swiss albino rats to 250, 500, or 750 ppm potassium 

dichromate in drinking water to determine the potential teratogenicity of hexavalent chromium 

pregestationally for 20 days. No notable changes in behavior or clinical signs were observed in 

the control or treated dams. Chromium levels in blood, placenta, and fetus were significantly 

increased in the dams of the 500 and 750 ppm dose groups. The authors reported a reduced 

number of corpora lutea and implantations, retarded fetal development, and embryo- and 

fetotoxic effects including reduced number of fetuses (live and dead) per dam and higher 

incidences of stillbirths and postimplantation loss in the 500 and 750 ppm dosed mothers. 

Significantly reduced parietal and interparietal ossification was observed in the high-dose group. 

Based on the body weight of the animals (175 +/- 25 g) and the drinking water ingested by the 

animals in the 250 ppm dose group (26 ml/mouse/day) the dose level in the 250 ppm group can 

be identified as 37 mg/kg-day. 

25
Elbetieha and Al-Hamood (1997) examined fertility following potassium dichromate 

exposures in mice at concentrations considerably greater than those used by NTP. Sexually 

mature male and female mice were exposed to 1,000, 2,000, 4,000, or 5,000 mg/L potassium 

dichromate in drinking water for 12 weeks. The effects of the exposures on fertility was 

examined at 140 days. No mortality or clinical signs of toxicity were reported in any group of 

male or female mice exposed at any concentration in the experiment. Exposure of male mice to 

hexavalent chromium compounds for 12 weeks had adverse impacts on the male reproductive 

system and fertility, though the mating capability of the mice was not affected. Fertility was 

significantly reduced in males exposed to 5,000 mg/L potassium dichromate. Testes weights 

were significantly increased in the males exposed in the 2,000 and 5,000 mg/L dose groups, 

while seminal vesicle and preputial gland weights were significantly reduced in the 5,000 mg/L 

exposed males. The numbers of implantation sites and viable fetuses were significantly reduced 

in females impregnated by males exposed to 2,000 and 4,000 mg/L. The numbers of 

implantations and viable fetuses were significantly reduced in pregnant females exposed to 

2,000, 4,000, and 5,000 mg/L of the hexavalent chromium compound. 

The findings of Junaid et al. (1996) and Kanojia et al. (1996) are consistent with those of 

Trivedi et al. (1989), and studies suggest the presence of embryotoxic and fetotoxic effects of 

potassium dichromate following oral exposures in mice and rats. The studies utilized similar 

dose levels provided in the drinking water of female mice and rats. The dose levels are similar to 

those used by the NTP study, which demonstrated no reproductive effects following 

administration of potassium dichromate in the diet. It cannot be determined whether the lack of 

reproductive toxicity demonstrated in the NTP studies are reflective of the reduced 

bioavailability of hexavalent chromium provided in the diet in comparison to that provided in 

drinking water, or whether the NTP studies identified a NOAEL for reproductive effects. 

4.3.2. Inhalation Studies 

No developmental effects were reported in rats exposed to 0.2 mg/m3

 Cr(VI) as sodium 

dichromate for three generations (Glaser et al., 1984). No histopathological effects of the testes 

were reported following exposure of rats to 0.2 mg/m3

 Cr(VI) as sodium dichromate for 28 or 90 

days (Glaser et al., 1985) or 0.1 mg/m3

 Cr(VI) as sodium dichromate for 18 mo (Glaser et al., 

1986, 1988). 

4.4. OTHER STUDIES 

4.4.1. Contact Dermatitis 

Chromium is one of the most common contact sensitizers in males in industrialized 

countries (Fowler, 1990; Cronin, 1980) and is associated with occupational exposures to 

numerous materials and processes, including chromeplating baths, chrome colors and dyes, 

cement, tanning agents, wood preservatives, anticorrosive agents, welding fumes, lubricating oils 

and greases, cleaning materials, and textiles and furs (Burrows and Adams, 1990; Polak et al., 

1973). Solubility and pH appear to be the primary determinants of the capacity of individual 

26
chromium compounds to elicit an allergic response (Fregert, 1981; Polak et al., 1973). The low 

solubility Cr(III) compounds are much less efficient contact allergens than Cr(VI) (Spruit and van 

Neer, 1966). 

Dermal exposure to chromium has been demonstrated to produce irritant and allergic 

contact dermatitis (Bruynzeel et al., 1988; Polak, 1983; Cronin, 1980; Hunter, 1974). Primary 

irritant dermatitis is related to the direct cytotoxic properties of chromium, while allergic contact 

dermatitis is an inflammatory response mediated by the immune system. Allergic contact 

dermatitis is a cell-mediated immune response that occurs in a two-step process. In the first step 

(induction), chromium is absorbed into the skin and triggers an immune response (sensitization). 

Sensitized individuals will exhibit an allergic dermatitis response when exposed to chromium 

above a threshold level (Polak, 1983). Induction is generally considered to be irreversible. 

Chromium allergic dermatitis is characterized by symptoms of erythema, swelling, papules, small 

vesicles, dryness, scaling, and fissuring (Adams, 1990; MacKie, 1981). 

4.4.2. Toxicant Interactions 

Potassium dichromate has been reported to potentiate the effects of the nephrotoxins, 

mercuric chloride, citrinin, hexachlorobutadiene, and maleic acid (ATSDR, 1993). The 

genotoxicity of hexavalent chromium has also been shown to be altered in the presence of other 

compounds, including ascorbic acid and vitamin E and thiol compounds (Susa et al., 1994). 

Vitamin B2 has been reported to enhance the cytotoxicity of sodium chromate (ATSDR, 1993). 

4.4.3. Genotoxicity 

Hexavalent chromium is rapidly taken up by cells through the sulfate transport system 

(Sugiyama, 1992). Once inside the cell, Cr(VI) is quickly reduced to the trivalent form by 

cellular reductants, including ascorbic acid, glutathione, and flavoenzymes, such as cytochrome 

P-450 glutathione reductase, and riboflavin. The intracellular reduction of Cr(VI) generates 

reactive chromium V and chromium IV intermediates as well as hydroxyl free radicals (�OH) and 

singlet oxygen (1O2). A variety of DNA lesions are generated during the reduction of Cr(VI) to 

Cr(III), including DNA strand breaks, alkali-labile sites, DNA-protein and DNA-DNA 

crosslinks, and oxidative DNA damage, such as 8-oxo-deoxyguanosine. The relative importance 

of the different chromium complexes and oxidative DNA damage in the toxicity of Cr(VI) is 

unknown. 

Hexavalent chromium has been shown to be genotoxic only in the presence of appropriate 

reducing agents in vitro or in viable cell systems in vitro or in vivo. Hexavalent chromium has 

been shown to be mutagenic in bacterial systems in the absence of a mammalian activating 

system (Venitt and Levy, 1974; Nishioka, 1975; Nakamuro et al., 1978; Green et al., 1976; 

Kanematsu et al., 1980; Lofroth and Ames, 1978; Newbold et al., 1979; Bonatti et al., 1976; 

Fukanaga et al., 1982), and not mutagenic when a mammalian activating system is present 

(Lofroth, 1978; Petrilli and DeFlora, 1977, 1978a,b). Hexavalent chromium is also mutagenic in 

eukaryotic test systems (Bonatti et al., 1976; Newbold et al., 1979; Fukanaga et al., 1982) and 

clastogenic in cultured mammalian cells (Raffetto, 1977; Levis and Majone, 1979; Umeda and 

27
Nishimura, 1979; Tsuda and Kato, 1977; Newbold et al., 1979; Nakamuro et al., 1978; Stella et 

al., 1982; Ohno et al., 1982; Gomez-Arroyo et al., 1981; Wild, 1978; Sarto et al., 1982). 

Hexavalent chromium in the presence of glutathione has been demonstrated to produce genotoxic 

DNA adducts that inhibit DNA replication and are mutagenic (Snow, 1994). 

4.5. SYNTHESIS AND EVALUATION OF MAJOR NONCANCER EFFECTS 

4.5.1. Oral Studies 

4.5.1.1. Human Studies 

Cr(VI) is considerably more toxic than Cr(III). A cross-sectional study reported the 

effects of environmental contamination of well water adjacent to a chromium alloy plant. Cr(VI) 

concentrations were reported as 20 mg/L, with an estimated exposure dose of 0.57 mg/kg-day 

(Zhang and Li, 1987) No lower dose levels were reported in this study. Reported effects 

included oral ulcers, diarrhea, abdominal pain, indigestion, vomiting, leukocytosis, and presence 

of immature neutrophils. The single high dose level reported in the study limits its usefulness for 

quantitative risk assessment purposes. 

Other reports of toxic effects in humans are limited to case reports from accidental 

poisonings. Some Cr(VI) compounds are potent oxidizing agents (such as potassium 

tetrachromate and chromium trioxide) and are thus strong irritants of mucosal tissue. Effects 

included metabolic acidosis, acute tubular necrosis, kidney failure, and death (Saryan and Reedy, 

1988). 

4.5.1.2. Animal Studies 

Only one chronic study pertaining to the oral toxicity of hexavalent chromium was 

located in the available literature. Anwar et al. (1961) exposed dogs orally (2 dogs/group) to 

potassium chromate in drinking water for 4 years. No effects were observed with regard to gross 

and microscopic analysis of all major organs, urinalysis, and weights of spleen, liver, and kidney. 

A NOEL of 0.31 mg potassium chromate/kg/day can be established from this study. The small 

group size in this study limits its usefulness for quantitative risk assessment purposes. 

Mackenzie et al. (1958) exposed groups of male and female rats to potassium dichromate 

(0-25 ppm of hexavalent chromium) in drinking water for 1 year. No effects were observed at 

any level of treatment, and a NOEL of 2.5 mg/kg-day can be established based on body weight, 

gross external condition, histopathological analysis, and blood chemistry. 

Junaid et al. (1996) exposed female Swiss albino mice to 250, 500, or 750 ppm potassium 

dichromate in drinking water to determine the potential embryotoxicity of hexavalent chromium 

during days 6-14 of gestation. The authors reported retarded fetal development and embryo- and 

fetotoxic effects including reduced fetal weight, reduced number of fetuses (live and dead) per 

dam, and higher incidences of stillbirths and postimplantation loss in the 500 and 750 ppm dosed 

28
mothers. Significantly reduced ossification in bones was also observed in the medium- and highdose groups. Based on the body weight of the animals (30 +/- 5 g) and the drinking water 

ingested by the animals in the 250 ppm dose group (8.0 ml/mouse/day), the dose level in the 250 

ppm group can be identified as 67 mg/kg-day. 

Kanojia et al. (1996) exposed female Swiss albino rats to 250, 500, or 750 ppm potassium 

dichromate in drinking water to determine the potential teratogenicity of hexavalent chromium 

pregestationally for 20 days. The authors reported a reduced number of corpora lutea and 

implantations, retarded fetal development, and embryo- and fetotoxic effects including reduced 

number of fetuses (live and dead) per dam and higher incidences of stillbirths and 

postimplantation loss in the 500 and 750 ppm dosed mothers. Significantly reduced parietal and 

interparietal ossification was observed in the high-dose group. Based on the body weight of the 

animals (175 +/- 25 g) and the drinking water ingested by the animals in the 250 ppm dose group 

(26 ml/mouse/day), the dose level in the 250 ppm group can be identified as 37 mg/kg-day. 

Elbetieha and Al-Hamood (1997) exposed sexually mature male and female mice to 

1,000, 2,000, 4,000, or 5,000 mg/L potassium dichromate in drinking water for 12 weeks. The 

effects of the exposures on fertility was examined at 140 days. The authors reported adverse 

impacts on the male reproductive system and fertility, though the mating capability of the mice 

was not affected. Testes weights were significantly increased in the males exposed in the 2,000 

and 5,000 mg/L dose groups, while seminal vesicle and preputial gland weights were 

significantly reduced in the 5,000 mg/L exposed males. The number of implantation sites and 

viable fetuses was significantly reduced in females impregnated by males exposed to 2,000 and 

4,000 mg/L, and the numbers of implantations and viable fetuses was significantly reduced in 

pregnant females exposed to 2,000, 4,000, and 5,000 mg/L of the hexavalent chromium 

compound. Information regarding the amount of water consumed by the animals was not 

provided in this study. 

4.5.2. Inhalation Studies 

4.5.2.1. Human Studies 

4.5.2.1.1. Respiratory tract effects. Three studies on chromeplaters provide some quantitative 

information on upper respiratory irritation after exposure to Cr(VI) as chromic acid. In the study 

of Cohen et al. (1974), nasal ulcers and perforations were associated with total chromium 

concentrations of 1.4 to 43.9 μg/m3

, averaging 7.1 μg/m3, and Cr(VI) concentrations of 0.09 to 

9.1 μg/m3, averaging 2.9 μg/m3. Ninety-five percent of the 37 workers studied exhibited 

pathologic changes in nasal mucosa in a concentration-duration response. More than half of the 

workers employed less than 1 year had nasal pathology that was more severe than simple redness 

of the nasal mucosa. Almost all the workers (35 of 37) employed longer than 1 year had nasal 

tissue damage. The authors noted the lack of good industrial hygiene practices, implicating 

direct contact, such as touching of the nose with chromium-contaminated hands, as a potentially 

important route of exposure. A subsequent study by Lucas and Kramkowski (1975) revealed 

similar results. Cr(VI) concentrations ranged from 1 to 20 μg/m3

, averaging 4 μg/m3. The 

authors attributed the nasal pathology primarily to direct contact. Lindberg and Hedenstierna 

29
(1983) also found similar effects on nasal pathology and subjective symptoms. They reported 

reddening of the nasal mucosa at 1 to 2 μg/m3

, and nasal irritation (chronic and nasal septal 

ulceration and perforation) in two-thirds of the subjects exposed to concentrations of 2 to 20 

μg/m3. All workers with nasal ulceration had been exposed to chrome acid mist, which 

contained Cr(VI) at 20 μg/m3, or greater than 20 μg/m3 near the baths. Changes in pulmonary 

function (vital capacity and forced expiatory volume) were seen at Cr(VI) exposures greater than 

2 μg/m3. 

4.5.2.1.2. Renal effects. Exposure to Cr(VI) at concentrations as low as 4 to 6 μg/m3

 has been 

reported to result in elevated excretion of ß-2-microglobulin (Lindberg and Vesterberg, 1983b). 

The effect may be reversible because former chromeplaters did not have an elevated 

concentration of either ß-2-microglobulin or albumin in their urine. Saner et al. (1984) did not 

find increased urinary ß-2-microglobulin levels in tannery workers in comparison to referent 

control workers. However, urinary chromium concentrations in the Saner et al. study were likely 

distinctly lower than those in the study of Lindberg and Vesterberg. 

In summary, effects on the airways and kidney have been observed in chromeplaters 

exposed subchronically to chromic acid mist containing Cr(VI) in air at concentrations greater 

than 1 μg/m3

. Such effects include reddening of nasal mucosa, nasal irritation (ulceration, 

perforation), changes in pulmonary function, and renal proteinuria. Many of the available studies 

lack quantitative concentration-response data on chromium health effects suitable for quantitative 

risk assessment. 

4.5.2.2. Animal Studies 

Data from studies in rats, mice, and rabbits identify the respiratory tract as the primary 

target of chromium toxicity following inhalation. Glaser et al. (1985) exposed rats to 0-0.2 mg 

Cr(VI)/m3

 22 hr/day, 7 days/week for 90 days. The authors reported increased lung and spleen 

weight, and increased macrophage activity and percent lymphocytes in BAL fluid. Glaser et al. 

(1990) exposed rats to 0-0.4 mg Cr(VI)/m3, 22 hr/day, 7 days/week for 30-90 days and reported 

hyperplasia, increased lung weight, macrophage infiltration, and LDH in bronchoalveolar lavage 

fluid (BALF). The authors suggested that inflammation is essential for the induction of most 

chromium inhalation effects and may influence the carcinogenicity of Cr(VI) compounds. 

Rats exposed to 0.5 mg/m3

 CrO2 (IV) 6 hr/day, 5 days/week for 2 years produced dustladen alveolar macrophages with slight Type II pneumocyte hyperplasia. Exposure at 25 mg/m3 

overwhelmed the lung clearance mechanisms and resulted in significant increases in dust-laden 

macrophages, bronchoalveolar cell hyperplasia with foamy macrophage response, and cholesterol 

granuloma (Lee et al., 1988). 

Mice exposed to 1.81 or 3.63 mg/m3

 Cr(VI) as CrO3 for 1 year developed nasal septal 

perforation, loss of cilia, and metaplasia of the lung, trachea, and bronchus (Adachi, 1987; 

Adachi et al., 1986). Epithelial changes of the bronchial tree ranging from necrosis and atrophy 

to hyperplasia were observed in mice exposed to 4.3 Cr/m3 as CaCrO4 dust for 18 months 

(Nettesheim et al., 1971). 

30
Rabbits exposed to chromium dust at 3.1 mg/m3

 and 0.6 mg/m3 for 5 days/week, 6 

hours/day for 4 weeks phagocytized significantly more chromium particles than the controls, 

though the number of nonviable macrophages was less than 3% (Johansson et al., 1980). In a 

subsequent study, rabbits were exposed to aerosols of hexavalent (0.9 mg/m3

 Na2CrO4) or 

trivalent (0.6 mg/m3 Cr[NO3]3) chromium for 5 days/week, 6 hours/day for 4 to 6 weeks. The 

number of macrophages obtained from the lungs of the rabbits exposed to Cr(VI) was 

significantly increased, while striking morphological changes were observed in macrophages of 

rabbits exposed to Cr(III) (Johansson et al., 1986). 

4.6. WEIGHT-OF-EVIDENCE EVALUATION AND CANCER CHARACTERIZATION 

Applying the criteria outlined in the Guidelines for Carcinogen Risk Assessment (U.S. 

EPA, 1986) for evaluating the overall weight of evidence for carcinogenicity to humans, 

hexavalent chromium is most appropriately designated a Group A - Known Human Carcinogen. 

Using the proposed Guidelines for Carcinogen Risk Assessment (U.S. EPA, 1996), hexavalent 

chromium is most appropriately designated a known human carcinogen by the inhalation route of 

exposure on the following basis. The potential carcinogenicity of chromium by the oral route of 

exposure cannot be determined at this time. 

Results of occupational epidemiologic studies of chromium-exposed workers are 

consistent across investigators and study populations. Dose-response relationships have been 

established for chromium exposure and lung cancer. Workers in the chromium industry are 

exposed to both Cr(III) and Cr(VI) compounds. Because only Cr(VI) has been found to be 

carcinogenic in animal studies, however, data support only the classification of Cr(VI) as a 

human carcinogen. 

Animal data provide suggestive evidence of the carcinogenicity of hexavalent chromium. 

Hexavalent chromium compounds have produced the following tumor types in animal assays: 

lung tumors following inhalation of aerosols of sodium chromate and pyrolized Cr(VI)/Cr(III) 

oxide mixtures in rats, lung tumors following intratracheal administration of sodium dichromate 

in rats, intrapleural implant site tumors for various Cr(VI) compounds in rats, intrabronchial 

implantation site tumors for various Cr(VI) compounds in rats, intramuscular injection site 

tumors in rats and mice, and subcutaneous injection site sarcomas in rats. Inflammation is 

considered to be essential for the induction of most chromium inhalation effects and may 

influence the carcinogenicity of Cr(VI) compounds (Glaser et al., 1985). 

In vitro data are suggestive of a potential mode of action for hexavalent chromium 

carcinogenesis. Cr(VI) readily passes through cell membranes and is rapidly reduced 

intracellularly to generate reactive Cr(V) and Cr(IV) intermediates and reactive oxygen species. 

The reactive oxygen species may interact with DNA to form premutagenic lesions. Hexavalent 

chromium has been shown to be mutagenic in bacterial assays, yeasts, and V79 cells, and Cr(VI) 

compounds decrease the fidelity of DNA synthesis in vitro and produce unscheduled DNA 

synthesis as a consequence of DNA damage. Chromate has been shown to transform both 

primary cells and cell lines. 

31
IARC (1990) concluded that there is sufficient evidence of respiratory carcinogenicity in 

humans occupationally exposed during chromate production. Animal data were considered 

supportive of the epidemiological data; however, the relative contributions to carcinogenic risk of 

metallic chromium, trivalent chromium, hexavalent chromium, or soluble versus insoluble 

chromium compounds could not be elucidated. IARC (1982) classified chromium and chromium 

compounds as Group I chemicals. 

At present, the carcinogenicity of hexavalent chromium by the oral route of exposure 

cannot be determined. One study of miners in Ontario suggested that exposure to chromium may 

have been associated with stomach cancer, but other human and animal studies have not reported 

similar effects. 

4.7. OTHER HAZARD IDENTIFICATION ISSUES 

4.7.1. Possible Childhood Susceptibility 

A number of factors may differentially affect the response of children to toxicants such as 

Cr(VI). These factors include diet and physical environment as well as maturation of 

physiological and biochemical processes. At present, there is too little information to make any 

statements about how these factors may specifically affect the toxicological responses of Cr(VI) 

in children, be they cancer or noncancer. 

4.7.2. Possible Sex Differences 

The extent to which men differ from women in susceptibility to chromium toxicity has 

not been reported. The most significant health effects associated with exposure to Cr(VI) involve 

the respiratory system and kidney. While effects on the respiratory system are unlikely to differ 

significantly with gender, the effect of gender on kidney toxicity is unknown. 

5. DOSE-RESPONSE ASSESSMENTS 

5.1. ORAL REFERENCE DOSE (RfD) 

5.1.1. Choice of Principal Study and Critical Effect 

Relatively few studies were located that addressed the oral toxicity of Cr(VI). One 

human study located in the literature, Zhang and Li (1987), reported on health effects in Chinese 

villagers who consumed drinking water from a well contaminated with hexavalent chromium 

from an alloy plant in Jinzhou. The Jinzhou area is heavily industrialized. In 1965, the well 

water in a nearby suburban area was found to be stained yellow, presumably because of 

chromium contamination from a mining operation which had begun operating in 1959. The 

mining operation was initially conducted in pilot scale, with a poor recovery rate for chromium 

(24.5%). Full-scale operation began in 1965. At this time, waste water was generated at a rate of 

32
125 pounds/hour and contained concentrations of up to 105 mg/L hexavalent chromium. Waste 

water was deposited directly into a surface channel. Following sedimentation, the surface water 

concentration was still in excess of 20 mg/L. In addition to the surface water discharge, the 

mining operation generated hexavalent chromium-containing steam and a considerable amount 

of chromium-containing mine tailings. The tailings were stored in an open waste pile, containing 

approximately 300,000 pounds of waste, covering an area of 50 hectares. The waste pile 

constituted an additional source of ground water contamination through leaching and surface 

water runoff. In 1965, more than 28% of the area ground water samples were observed to be 

contaminated with chromium, with 54% of the samples contaminated at a concentration of 20 

mg/L or greater. Ground water samples were found to be contaminated over an area of 10 square 

kilometers. In 1965, the material in the waste pile was found to contain an average of 1.55% 

hexavalent chromium. The soil in the vicinity of the waste pile was found to contain an average 

concentration of hexavalent chromium of 4,700 mg/kg, and 0.3 pounds/day of hexavalent 

chromium was estimated to leach into the ground water from the waste pile. In addition, 

irrigation water for the considerable agricultural operation in the vicinity of Jinzhou was 

contaminated with chromium at concentrations of 0.006-0.739 mg/L. However, concentrations 

in soil and produce in the agricultural areas were only slightly elevated above the controls. 

In 1965, a study of 155 subjects exposed to drinking water at concentrations of 

approximately 20 mg/L of hexavalent chromium was conducted outside Jinzhou. Subjects were 

observed to have sores in the mouth, diarrhea, stomach ache, indigestion, and vomiting. Subjects 

were observed to have elevated white blood cell counts with respect to controls, as well as a 

higher per capita rate of cancers, including lung cancer and stomach cancer. Precise exposure 

concentrations, exposure durations, and confounding factors were not discussed, and this study 

does not provide a NOAEL for the observed effects. However, the study suggests that 

gastrointestinal effects may occur in humans following exposures to hexavalent chromium at 

levels of 20 ppm in drinking water (Zhang and Li, 1987). 

Several animal studies addressing oral toxicity of hexavalent chromium were located in 

the literature. Anwar et al. (1961) exposed groups of female dogs (2/group) to up to 11.2 ppm 

Cr(VI) in drinking water for 4 years with no effect. MacKenzie et al. (1958) exposed groups of 

Sprague-Dawley rats (16-21/group) to up to 25 ppm Cr(VI) in drinking water for 1 year. No 

significant adverse effects were seen in any treatment group. Both the Mackenzie et al. (1958) 

and Anwar et al. (1961) studies are limited by the small number of animals/group and the lack of 

an observed effect at any dose level. While the MacKenzie et al. study has the additional 

limitation of being conducted for only 1 year, this study is considered to be more useful for risk 

assessment because of the identification of a NOAEL value and the larger number of animals per 

dose group that those available from Anwar et al. (1961). 

Elbetieha and Al-Hamood (1997) reported adverse impacts on the male reproductive 

system and fertility, and reduced numbers of implantations and viable fetuses in pregnant females 

following exposures to hexavalent chromium. Information regarding the amount of water 

consumed by the animals was not provided, and this study is not considered useful for this risk 

assessment. 

33
The National Toxicology Program (NTP 1996a,b, 1997) did not observe reproductive 

effects in either sex of BALB/C mice or Sprague-Dawley rats following oral exposures to 15 -

400 ppm Cr(VI) in the diet. 

Junaid et al. (1996) and Kanojia et al. (1996) exposed female Swiss albino mice and 

female Swiss albino rats, respectively, to 250, 500, or 750 ppm potassium dichromate in drinking 

water to determine the potential embryotoxicity of hexavalent chromium during days 6-14 of 

gestation. The authors reported retarded fetal development and embryo- and fetotoxic effects 

including reduced fetal weight, reduced number of fetuses (live and dead) per dam, and higher 

incidences of stillbirths and postimplantation loss in the 500 and 750 ppm dosed mothers. 

Significantly reduced ossification in bones was also observed in the medium- and high-dose 

groups. Based on the body weight and the drinking water ingested by the animals in the 250 ppm 

dose group, the exposure levels in the 250 ppm groups can be identified as 67 mg/kg-day and 37 

mg/kg-day in mice and rats, respectively. 

The Junaid et al. (1996) and Kanojia et al. (1996) studies utilized doses approximately 

10-fold higher than those used in Mackenzie et al (1958), but neither of the reproductive studies 

identified a clear NOAEL for the embryotoxic effects of hexavalent chromium. Based on the 

body weight and the drinking water ingested by the animals in the low-dose groups (250 ppm), 

the LOAELs of 67 mg/kg-day and 37 mg/kg-day can be identified from Junaid et al. (1996) and 

Kanojia et al. (1996) in mice and rats, respectively. Application of 10-fold uncertainty factor to 

extrapolate from LOAELs to NOAELs in these studies would generate NOAELs of 6.7 mg/kgday and 3.7 mg/kg-day, respectively. These extrapolated NOAEL values are similar to, and 

support the use of, the NOAEL of 2.5 mg/kg-day identified from the study of MacKenzie et al. 

(1958) for development of the reference dose. 

5.1.2. Method of Analysis 

MacKenzie et al. exposed groups of eight male and eight female Sprague-Dawley rats to 

0.45-11.2 ppm (0.45-11.2 mg/L) hexavalent chromium (as K2CrO4) for 1 year in drinking water. 

The control group (10/sex) received distilled water. A second experiment involved three groups 

of 12 male and 9 female rats. One group was given 25 ppm (25 mg/L) chromium (as K2CrO4), a 

second received 25 ppm chromium in the form of chromic chloride, and the controls again 

received distilled water. No significant adverse effects were seen in appearance, weight gain, or 

food consumption, and there were no pathologic changes in the blood or other tissues in any 

treatment group. The rats receiving 25 ppm of chromium (as K2CrO4) showed an approximate 

20% reduction in water consumption. This dose corresponds to 2.5 mg Cr(VI)/kg/day based on 

actual body weight and water consumption data. 

For rats treated with 0-11 ppm (in the diet), blood was examined monthly and tissues 

(livers, kidneys and femurs) were examined at 6 mo and 1 year. Spleens were also examined at 1 

year. The 25 ppm groups (and corresponding controls) were examined similarly, except that no 

animals were killed at 6 mo. An abrupt rise in tissue chromium concentrations was noted in rats 

treated with greater than 5 ppm. The authors stated that “apparently, tissues can accumulate 

considerable quantities of chromium before pathological changes result.” In the 25 ppm 

34
treatment groups, tissue concentrations of chromium were approximately 9 times higher for those 

treated with hexavalent chromium than for the trivalent group. Similar no-effect levels have 

been observed in dogs. Anwar et al. (1961) observed no significant effects in female dogs 

(2/dose group) given up to 11.2 ppm Cr(VI) (as K2CrO4) in drinking water for 4 years. The 

calculated doses were 0.012-0.31 mg/kg of Cr(VI). 

5.1.3. RfD Derivation 

No effects were reported at any dose level in the MacKenzie et al. study. The highest 

dose group (25 mg/L) was selected for derivation of the reference dose. Based on the body 

weight of the rat (0.35 kg) and the average daily drinking water consumption for the rat (0.035 

l/day), this dose can be converted to give an adjusted NOAEL of 2.5 mg/kg-day. 

The adjusted NOAEL is further modified by two 10-fold uncertainty factors to account 

for the expected interspecies and interhuman variability in lieu of specific data. An additional 

threefold uncertainty factor is applied to the adjusted NOAEL to compensate for the less-thanlifetime exposure duration in the MacKenzie et al. study. A threefold modifying factor is applied 

to address concerns raised by the study of Zhang and Li (1987). The total uncertainty factor 

applied to the adjusted NOAEL is 900. Application of the uncertainty factor to the adjusted 

NOAEL of 2.5 mg/kg-day gives the reference dose of 3 × 10-3 mg/kg-day. 

5.2. INHALATION REFERENCE CONCENTRATION (RfC) 

The inhalation reference concentration (RfC) is based on the assumption that thresholds 

exist for certain toxic effects such as cellular necrosis, but may not exist for other toxic effects 

such as carcinogenicity. In general, the RfC is an estimate (with uncertainty spanning perhaps an 

order of magnitude) of a daily exposure to the human population (including sensitive subgroups) 

that is likely to be without an appreciable risk of deleterious effects during a lifetime. 

5.2.1. Choice of Principal Study and Critical Effect 

Numerous studies have reported upper respiratory, lower respiratory, and kidney effects 

in humans and animals following exposures to hexavalent chromium. Of these endpoints, upper 

and lower respiratory effects appear to be the most sensitive and are discussed in greater detail 

below. 

Three studies have focussed on nasal mucosal irritation, atrophy, and perforation 

following occupational exposures to chromic acid mists (Cohen et al., 1974; Lucas and 

Kramkowski, 1975; Lindberg and Hedenstierna, 1983). Of these, the study of Lindberg and 

Hedenstierna provides the most information on exposure levels and symptoms reported by 

exposed workers. Respiratory symptoms, lung function, and changes in nasal septum were 

studied in 104 workers (85 males, 19 females) exposed in chromeplating plants. Workers were 

interviewed using a standard questionnaire for the assessment of nose, throat, and chest 

35
symptoms. Nasal inspections and pulmonary function testing were performed as part of the 

study. 

The median exposure time for the entire group of exposed subjects (104) in the study was 

4.5 years (0.1-36 years). Forty-three subjects exposed almost exclusively to chromic acid 

experienced a mean exposure time of 2.5 years (0.2-23.6 years). The subjects exposed almost 

exclusively to chromic acid were divided into a low-exposure group (8 hr TWA below 0.002 

mg/m3

, N = 19) and high exposure group (8 hr TWA above 0.002 mg/m3, N = 24). Exposure 

measurements using personal air samplers were performed for 84 subjects in the study on 13 

different days. Exposure for the remaining 20 workers was assumed to be similar to that 

measured for workers in the same area. Nineteen office employees were used as controls for 

nose and throat symptoms. A group of 119 auto mechanics whose lung function had been 

evaluated by similar techniques was selected as controls for lung function measurements. 

Smoking habits of workers were evaluated as part of the study. 

At mean exposures below 0.002 mg/m3

, 4/19 workers from the low-exposure group 

complained of subjective nasal symptoms. Atrophied nasal mucosa were reported in 4/19 

subjects from this group and 11/19 had smeary and crusty septal mucosa, which was statistically 

higher than controls. No one exposed to levels below 0.001 mg/m3

 complained of subjective 

symptoms. At mean concentrations of 0.002 mg/m3 or above, approximately one-third of the 

subjects had reddened, smeary, or crusty nasal mucosa. Atrophy was seen in 8/24 workers, 

which was significantly different from controls. Eight subjects had ulcerations in the nasal 

mucosa and five had perforations of the nasal septum. Atrophied nasal mucosa was not observed 

in any of the 19 controls, but smeary and crusty septal mucosa occurred in 5/19 controls. 

Short-term effects on pulmonary function were evaluated by comparing results of tests 

taken on Monday and Thursday among exposed groups and controls. No significant changes 

were seen in the low-exposure group or control group. Nonsmokers in the high-exposure group 

experienced significant differences in pulmonary function measurements from the controls, but 

the results were within normal limits. 

The authors concluded that 8-hour mean exposures to chromic acid above 0.002 mg/m3 

may cause a transient decrease in lung function, and that short-term exposures to greater than 

0.02 mg/m3

 may cause septal ulceration and perforation. Based on the results of this study, a 

LOAEL of 0.002 mg/m3

 can be identified for incidence of nasal septum atrophy following 

exposure to chromic acid mists in chromeplating facilities. It should be noted that there are 

significant uncertainties related to the use of this LOAEL for development of an RfC for 

hexavalent chromium in the environment. There is considerable uncertainty with regard to the 

relevance of the nasal septum atrophy endpoint observed in the chromeplating industry to 

exposure to hexavalent chromium in the environment. The effects were observed in 

chromeplaters exposed to chromic acid mists near the plating baths. Environmental exposures 

would most likely occur through contact with hexavalent chromium dusts. An additional 

uncertainty is related to the determination of dose in the Lindberg and Hedenstierna study. Nasal 

septum atrophy in this study was related to time-weighted average (TWA) exposures to chromic 

acid. The most significant effects (nasal septum perforation) were observed in workers who 

36
experienced peak excursions to levels considerably greater than the TWA. It is uncertain 

whether the peak excursion data or the TWA are more appropriate for the determination of dose 

in this study. 

An alternative approach to development of the RfC is to focus on respiratory effects 

following inhalation of hexavalent chromium particulates. Two studies provide high quality data 

on lower respiratory effects following exposures to chromium particulates (Glaser et al., 1990; 

Glaser et al., 1985). Glaser et al. (1990) exposed 8-week-old male Wistar rats to sodium 

dichromate at 0.05 - 0.4 mg Cr(VI)/m3

 22 hr/day, 7days/week for 30-90 days. Chromiuminduced effects occurred in a strong dose-dependent manner. The authors observed obstructive 

respiratory dyspnea and reduced body weight following subacute exposure at the higher dose 

levels. The mean white blood cell count was increased at all doses (p < 0.05) and was related to 

significant dose-dependent leukocytosis following subacute exposures. Mean lung weights were 

significantly increased at exposure levels of 0.1 mg/m3

 following both the subacute and 

subchronic exposures. Accumulation of macrophages was seen in all of the exposure groups and 

was postulated to be a chromium-specific irritation effect that accounted for the observed 

increases in lung weights. Focal inflammation was observed in the upper airways following the 

subchronic exposure, and albumin and LDH in BALF were increased following the exposure. 

The authors concluded that chromium inhalation induced pneumocyte toxicity and suggested that 

inflammation is essential for the induction of most chromium inhalation effects, and may 

influence the carcinogenicity of Cr(VI) compounds. 

Glaser et al. (1985) exposed 5-week-old male Wistar rats to aerosols of sodium 

dichromate at concentrations ranging from 0.025 to 0.2 mg Cr(VI)/m3

, 22 hr/day in subacute (28 

day) or subchronic (90 day) protocols. Chromium-induced effects occurred in a dose-dependent 

manner. Lung and spleen weights were significantly increased (p < 0.005) after both subacute 

and subchronic exposures at concentrations greater than 0.025 mg/m3. Differences in the mean 

total serum immunoglobulin were also significant at exposures above 0.025 mg/m3, while 

exposures to aerosol concentrations greater than 0.1 mg/m3

 resulted in depression of the immune 

system stimulation. The immune-stimulating effect of subchronic exposure was not reversed 

after 2 mo of fresh air regeneration. BAL cell counts were significantly decreased following 

subchronic exposure to levels above 0.025 mg/m3 chromium. The number of lymphocytes and 

granulocytes showed a slight but significant increase in the lavage fluids of the subacute and 

subchronically exposed groups. At subacute exposure concentrations up to 0.05 mg/m3

, the 

phagocytic activity of the alveolar macrophages increased; however, subchronic exposure at 0.2 

mg/m3

 decreased this function significantly. The spleen T-lymphocyte subpopulation was 

stimulated by subchronic exposure to 0.2 mg/m3

 chromium, and serum contents of triglycerides 

and phospholipids differed significantly from controls (p < 0.05) at this concentration. 

Together, these studies provide useful information on chromium exposure-related impacts 

including lung and spleen weight, lactate dehydrogenase (LDH) in BALF, protein in BALF, and 

albumin in BALF. The cellular content of BALF is considered representative of initial 

pulmonary injury and chronic lung inflammation, which may lead to the onset of pulmonary 

fibrosis (Henderson, 1988). While these studies present dose-dependent results on sensitive 

indicators of lower respiratory toxicity, potential upper respiratory impacts resulting from the 

37
exposures were not addressed. Glaser et al. (1990) states that the upper respiratory tract was 

examined, but these data are not reported. In light of the numerous reports of severe upper 

respiratory impacts following exposure to chromic acid in the occupational setting, the studies of 

Glaser et al. alone are not considered sufficient to support derivation of an RfC for chromium. 

While the studies of Lindberg and Hedenstierna (1983) and Glaser et al. (1985, 1990) are 

independently considered insufficient for development of an RfC for hexavalent chromium, 

taken together these offer an approach for development of an RfC. 

5.2.2. RfC Derivation 

Lindberg and Hedenstierna (1983) will be used to support development of an RfC for 

upper respiratory effects of chromic acid mists and dissolved hexavalent chromium aerosols, and 

Glaser et al. (1985, 1990) will be used to support development of an RfC for lower respiratory 

effects from chromium particulates. 

5.2.2.1. Chromic Acid Mists and Dissolved Hexavalent Chromium Aerosols 

A LOAEL for nasal septum atrophy of 2 μg/m3

 chromic acid can be identified based on 

the results of Lindberg and Hedenstierna (1983). At TWA exposures greater than 2 μg/m3, nasal 

septum ulceration and perforations occurred in addition to the atrophy reported at lower 

concentrations. The LOAEL is based on an 8-hour TWA occupational exposure. The LOAEL is 

adjusted to account for continuous exposure according to the following equation: 

LOAELc = 2 μg/m3

 × (MVho/MVh) × 5 days/7 days 

where: 

LOAELc is the LOAEL for continuous exposure 

MVho is the breathing volume for an 8-hour occupational exposure (10 m3

) 

MVh is the breathing volume for a 24-hour continuous exposure (20 m3) 

The LOAEL of 2 μg/m3 based on a TWA exposure to chromic acid is converted to a 

LOAEL for continuous exposure of 0.714 μg/m3

. An uncertainty factor of 3 is applied to the 

LOAEL to extrapolate from a subchronic to a chronic exposure, an uncertainty factor of 3 is 

applied to account for extrapolation from a LOAEL to a NOAEL, and an uncertainty factor of 10 

is applied to the LOAEL to account for interhuman variation. The total uncertainty factor 

applied to the LOAEL is 90. Application of the uncertainty factor of 90 to the LOAEL of 0.714 

μg/m3

 generates an RfC for upper respiratory effect of chromic acid mists and dissolved 

hexavalent chromium aerosols of 0.008 μg/m3. 

38
5.2.2.2. Hexavalent Chromium Dusts 

Glaser et al. (1990) exposed male Wistar rats to 0.05-0.4 mg/m3

 sodium dichromate 22 

hr/day, 7 days/week for 30 or 60 days, or 90 days with a 30-day recovery period. In Glaser et al. 

(1985), male Wistar rats were exposed to 0.025 - 0.2 mg/m3 sodium dichromate 22 hr/day, 7 

days/week for 28 or 90 days. Data were reported on numerous endpoints indicative of lung 

toxicity. One approach for development of an RfC using these data was offered by Malsch et al. 

(1994), who generated an inhalation RfC for chromium dusts using a benchmark concentration 

(BMC) approach. The Agency based its RfC derivation on this approach. After excluding 

exposures for periods of less than 90 days from the BMC analysis, Malsch et al. (1994) 

developed BMCs for lung weight, lactate dehydrogenase (LDH) in BALF, protein in BALF, 

albumin in BALF, and spleen weight. The Malsch et al. (1994) analysis defined the benchmark 

concentration as the 95% lower confidence limit on the dose corresponding to a 10% relative 

change in the endpoint compared to the control. Dose-effect data were adjusted to account for 

discontinuous exposure (22 hr/day) and the maximum likelihood model was used to fit 

continuous data to a polynomial mean response regression, yielding maximum likelihood 

estimates of 36 -78 μg/m3

 and BMCs of 16 - 67 μg/m3. Malsch et al. (1994) applied dosimetric 

adjustments and uncertainty factors to the BMCs to determine a RfC based on the following 

equation: 

RfC = BMC × RDDR 

UFA × UFF × UFH 

where: 

RfC is the inhalation reference concentration 

BMC is the benchmark concentration (lower 95% confidence limit on the dose 

corresponding to a 10% relative change in the endpoint compared to the control) 

RDDR is the regional deposited dose ratio to account for pharmacokinetic differences between 

species 

UFA is a threefold uncertainty factor to account for pharmacodynamic differences not 

addressed by the RDDR 

UFF is a threefold uncertainty factor to account for extrapolating from subchronic to 

chronic exposures; and 

UFH is a 10-fold uncertainty factor to account for the variation in sensitivity among 

members of the human population 

The RDDR factor is incorporated to account for differences in the deposition pattern of 

inhaled hexavalent chromium dusts in the respiratory tract of humans and the Wistar rat test 

animals (Jarabek et al., 1990). The RDDR of 2.1355 was taken from U.S. EPA (1990), based on 

the mass median aerodynamic diameter (0.28 μm for dose levels of 50-100 μg/m3

 and 0.39 for 

dose levels of 100-400 μg/m3) and the geometric standard deviation (1.63 for dose levels of 50-

100 μg/m3

 and 1.72 for dose levels of 100-400 μg/m3) of the particulates reported in Glaser et al. 

(1990). A 3.16-fold uncertainty factor (midpoint between 1 and 10 on a log scale) was 

incorporated to account for the pharmacodynamic differences not accounted for by the RDDR. 

An additional 3.16-fold uncertainty factor was incorporated to account for the less-than-lifetime 

39
exposure in Glaser et al. (1990), and a 10-fold uncertainty factor was applied to account for 

variation in the human population. A total uncertainty factor of 100 was applied to the BMC in 

addition to the RDDR. 

Glaser et al. (1990) reported that LDH in BALF increased in a dose-dependent fashion 

from 50 to 400 μg/m3

 sodium dichromate, and this endpoint generated the lowest BMC (16 

μg/m3

) and RfC (0.34 μg/m3). LDH in BALF is considered the among the most sensitive 

indicators of potential lung toxicity (Henderson, 1984, 1985, 1988; Beck et al., 1982; Venet et 

al., 1985), as LDH is found extracellularly after cell damage and BALF is the closest site to the 

original lung injury. LDH in BALF may also reflect chronic lung inflammation, which may lead 

to pulmonary fibrosis through prevention of the normal repair of lung tissue (Henderson, 1988). 

Several uncertainties must be addressed with regard to the BMC and RfC developed by 

Malsch et al. (1994). Potentially important endpoints including upper airway effects and 

potential renal or immunological toxicity were not addressed in the Glaser et al. (1985, 1990) 

studies and could not be included in the BMC analysis. While LDH in BALF resulted in the 

lowest BMC and RfC, several of the effects noted in Glaser et al. (1985, 1990) can be considered 

indicative of an inflammatory response, and might be equally suited to development of the RfC. 

In addition, the threefold uncertainty factor accounting for the use of a subchronic study may not 

be sufficiently protective for long-term effects. While the analysis acknowledged the importance 

of particle size and airway deposition in the development of the RDDR, the potential impact of 

different particle sizes in respiratory toxicity by hexavalent chromium particulates was not 

addressed. 

Several of these uncertainties have been conservatively addressed in the analysis of 

Malsch et al. (1994). LDH in BALF generated the lowest estimate of the BMC from the effects 

noted by Glaser et al. (1985, 1990). This effect can be considered to be indicative of cell damage 

that occurs prior to fibrosis, as LDH appears in BALF following cell lysis. While other 

endpoints considered in the Malsch et al. (1994) analysis demonstrated a relatively better curve 

fit than LDH in BALF, the model generated a conservative fit in the data that is unlikely to 

overestimate the BMC, and the curve fit for LDH in BALF is considered to be acceptable. LDH 

in BALF as reported in Glaser et al. (1990) is considered to be an acceptable endpoint for 

development of an RfC for inhalation of hexavalent chromium particulates, and Malsch et al. 

(1994) used a reasonable approach for development of a BMC based on this endpoint. 

The threefold uncertainty factor used to account for the subchronic study is insufficient 

for development of the RfC for inhalation of chromium particulates. Glaser et al. (1985) 

demonstrated that at the end of the 90-day exposure period, chromium was still accumulating in 

the lung tissue of the test animals, suggesting that lower long-term exposures might lead to 

accumulation of a critical concentration in the lung. Subchronic studies also may not adequately 

predict the presence of inflammatory effects from lower long-term exposures. The Agency has 

therefore determined that a 10-fold uncertainty factor accounting for the use of a subchronic 

study is more appropriate in this case for the development of the RfC for inhalation of chromium 

particulates. 

40
Selection of a threefold uncertainty factor to account for the pharmacodynamic 

differences not accounted for by the RDDR, an additional 10-fold uncertainty factor to account 

for the less-than lifetime exposure in Glaser et al. (1990), and a 10-fold uncertainty factor to 

account for variation in the human population generates a total uncertainty factor of 300. 

Application of the total uncertainty factor of 300 and the RDDR of 2.1576 to the BMC generated 

by Malsch et al. (1994) based on LDH in BALF (Glaser et al., 1990) results in an RfC of 0.1 

μg/m3

 for inhalation of hexavalent chromium particulates. The selected RfCs are 0.008 μg/m3 

for chromic acid mists and dissolved hexavalent chromium aerosols and 0.1 μg/m3 for hexavalent 

chromium particulates. 

5.3. CANCER ASSESSMENT 

5.3.1. Summary 

There are many epidemiologic studies demonstrating that hexavalent chromium (CrVI) is 

a potential human carcinogen, but few provide adequate exposure data for use in risk estimation. 

Mancuso (1975) provides limited but adequate information for this purpose, and Mancuso's data 

are used as the main database for estimating the carcinogenic potency of hexavalent chromium. 

Three foreign studies on ferrochromium plants were also considered for use in the potency 

calculations. From the quantitative risk assessment viewpoint, these studies are less adequate 

than the Mancuso study. For the Norwegian study (Langard et al., 1980), the exposure 

measurements were taken in 1975, while some workers could have been exposed to chromium as 

early as 1928, when the ambient dust levels were much higher than in later years. For the 

Swedish study (Axelsson et al., 1980), the chromium-exposed workers did not show a 

significant increase of lung cancer, and thus only the statistical upper bound of the response can 

be used in potency estimation. It is expected that the use of data from the Norwegian and 

Swedish studies would result in an overestimation of the true carcinogenic potency of hexavalent 

chromium. While a Russian study (Pokrovskaya and Shabynina, 1973) does not have the 

deficiencies of the other two foreign studies, the cohort in this study is not well defined and is not 

suitable for use in risk assessment. 

Animal data from intratracheal studies were not used to estimate the carcinogenic potency 

of chromium by inhalation because there is limited pharmacokinetic information relating the 

distribution of chromium to lung tissues by inhalation and by intratracheal administration. This 

information is needed to reconcile the differences in dose distribution between these two 

exposure patterns. Furthermore, the physiological mechanism of dose distribution by 

intratracheal administration may depend (in a nonlinear fashion) on the dose levels used in the 

experiment, as evidenced by the observation that a single administration of sodium dichromate 

induced a carcinogenic response in Sprague-Dawley rats but failed to induce a response when the 

same weekly dose was given over 5 days (Steinhoff et al., 1983). 

5.3.2. Dose-Response Data 

41
The Mancuso (1975) study was based on a cohort of 332 white male workers who were 

employed in a chromate plant between 1931 (when the plant began to operate) and 1937, and 

who were followed to 1974. Mancuso reported lung cancer death rates by levels of exposure to 

soluble, insoluble, and total chromium concentrations. Because only lung cancer mortality for 

total chromium exposure was reported by age group, only the dose-response data for total 

chromium were used to estimate the carcinogenic potency of hexavalent chromium. The use of 

dose-response data for total chromium would result in an underestimation of the potency of 

hexavalent chromium. An additional uncertainty of the study was the assumption that the 

smoking habits of chromate workers were similar to those of the general white male population. 

This assumption may lead to an overestimation of the role of hexavalent chromium in lung 

cancer seen in the cohort. 

Exposure information in the Mancuso study was derived from an industrial hygiene study 

of the plant conducted in 1949 (Bourne and Yee, 1950). In this study, TWAs of exposure to 

insoluble, soluble, and total chromium per cubic meter were calculated for each occupation and 

for each worker in every department. Using these data and company personnel records, Mancuso 

was able to calculate an estimate of exposure to soluble, insoluble, and total chromium by 

duration of exposure (in mg/m3

/years) for each member of the 1931-37 cohort. In 1949, after the 

industrial hygiene study had been conducted, the company initiated a comprehensive program 

designed to reduce employees' exposures and improve manufacturing efficiency. Until that time, 

however, the company had not undertaken any programs for the purpose of reducing employee 

exposure. It should be noted that Bourne and Yee (1950), who conducted the industrial hygiene 

survey in 1949, reported that “in order to meet price and quality competition, improvements in 

equipment and processes have been made periodically during the past 18 years, and it is the 

universal experience of industrial hygiene personnel that greater process efficiency is almost 

invariably associated with a more healthful working environment. Therefore, there seems little 

doubt that atmospheric contamination in the past was greater than in 1949.” Nonetheless, no 

concerted effort was made to reduce employee exposure until late in 1949, and because this 

particular plant was a relatively modern one at the time of the survey, it is unlikely that 

improvements in efficiency over the period 1931 to 1949 would have reduced employee 

exposure to a great extent. Thus, Mancuso is considered to have utilized a reasonable 

approximation of what workers in the study cohort were exposed to during their entire working 

history. Exposure in the cohort may be slightly underestimated because of the likelihood that a 

greater proportion of the “total exposure” was contributed prior to 1949 than after 1949. The 

effects of underestimating the exposure concentration, as well as the effects of other uncertainties 

on the estimation of potency, are addressed in Section 6. 

5.3.3. Dose Conversion 

Table 3, which is taken from Mancuso (1975), presents age-specific lung cancer deaths, 

corresponding person-years, and range of exposures to total chromium. To estimate the lifetime 

cancer risk due to exposure to chromium, it is assumed that an exposure, D (mg/m3

/years), as 

presented in Table 3, is equivalent to the continuous exposure d (μg/m3) calculated by 

42
d = D × 8 × 240 × 103

 μg/m3 

fLe 24 365 

where Le is the midrange in each age category, f is the fraction of time in age exposed, and 8/24 

and 240/365 are the fractions of a day and year, respectively, that a worker spent at the plant. For 

instance, if D = 8 mg/m3

/years, Le = 60, and f = 0.65, then d = 44.96 μg/m3. The assumption of f 

= 0.65 implies that the cohort exposure to chromium began at approximately age 20. The 

assumption is that the particular exposure pattern (unknown) leading to the cancer mortality rates 

as observed is equivalent to the continuous constant exposure starting from the age when 

exposure began. This assumption may or may not be realistic. However, it would be less 

realistic to make a different assumption concerning the exposure pattern when the exposure 

estimates provided in Mancuso (1975) were determined using the weighted average of the 

duration of exposure for each respective job the worker had. 

Since the person-year in each category presented in Table 2 is very small, the exposure 

categories are combined as shown in Table 4 to increase statistical stability. The last column of 

Table 4 is given for the purpose of identifying which exposure categories in Table 2 are 

combined. The midrange of age and exposure concentration is used in Table 4. Data in this 

table are used to estimate the lifetime cancer risk due to chromium exposure. 

5.3.4. Extrapolation Method 

It has been widely recognized (e.g., Doll, 1971) that the age-specific incidence curve 

tends to be linear on doubly logarithmic graphs, or equivalently, the age-specific incidence 

follows the mathematical form: 

I(T) = bTk-l 

where b and k are parameters that may be related to other factors such as dose, and T may be one 

of the following three cases: 

1. T is age when cancer is observed, 

2. T is the time from the first exposure to observed cancer, or 

3. T is the time from exposure to cancer minus the minimum time for a cancer to be clinically 

recognized. 

43
Table 4. Combined age-specific lung cancer death rates and total chromium 

exposure (in μg/m3

) 

Age Concentration 

(μg/m3

) 

Deaths Person-years Background 

rateb 

Exposure 

range 

50 

50 

50 

60 

60 

60 

70 

70 

5.66 

25.27 

46.83 

4.68 

20.79 

39.08 

4.41 

21.29 

3 

6 

6 

4 

5 

5 

2 

4 

1,345 

931 

299 

1,063 

712 

211 

401 

345 

6.05 × 10-4 

6.05 × 10-4 

6.05 × 10-4 

1.44 × 10-3 

1.44 × 10-3 

1.44 × 10-3 

1.57 × 10-3 

1.57 × 10-3 

�1.99 

2.0-5.99 

6.0-7.99 

�1.99 

2.0-5.99 

6.0-7.99 

�1.99 

2.0-7.99 a

The midrange of each exposure category in Table 2 is first converted to μg/m3 by using f = 0.65 in the formula 

described in the section “data available for potency calculations.” The concentrations presented in this table are the 

averages of several exposure categories weighted by corresponding person-years. 

b

Background rate is estimated from 1964 U.S. Vital Statistics. The year 1964 is selected because it is estimated that 

a large proportion of lung cancer deaths occurred during that year. 

This model has been shown to arise from the somatic mutation hypothesis of 

carcinogenesis (Armitage and Doll, 1954; Whittemore, 1978; Whittemore and Keller, 1978). It 

has also been shown to arise from the epigenetic hypothesis when the reversible cellular change 

is programmed to occur randomly (Watson, 1977). These authors and many others have used 

this model to interpret and/or estimate potency from human data. 

Since the data that could be used for risk estimation are limited, a simple model that fits 

the data should be used. Therefore, the observed age-specific incidence is assumed to follow the 

model 

I(t,d) = B(t) + h(t,d) 

where B(t) is the background rate at age t and h(t,d) = Q(d) tk-l

 with Q(d) = q

of dose d. 

l

d + q2d2, a function 

Once the parameters ql

, q2, and k are estimated, the lifetime cancer risk associated with an 

exposure d by age t, taking into account the competing risk, can be calculated by 

t s 

44
P(t,d) = o� h(s,d)exp {-[o� h(y,d)dy + A(s)]}ds 

where exp[-A(s)] is the probability of surviving to age s and h(t,d) = I(t,d) - B(t) is the 

age-specific incidence after adjusting the background rate. 

To estimate the parameters in h(t,d) we assume, as is usually done, that the number of 

lung cancer deaths, X, at age t, follows the Poisson distribution with the expected value 

E(X) = N × [B + Q(d) tk-1

] 

where N is the person-year associated with X, B is the background rate at age t, and Q(d) = q ld + 

q2d2. 

Using the BMDP computer program P3R and the theory relating the maximum likelihood 

and nonlinear least square estimation by Jennrich and Moore (1975), the parameters ql

, q2, and k 

are estimated by the method of maximum likelihood as ql = 1.11 × 10-7, q2 = 1.84 × 10-9, and k = 

2.915; the corresponding standard deviations are respectively 7.8 × 10-7, 1.2 × 10-8, and 1.7. 

Thus, the age-specific cancer death incidence at age t due to chromium exposure d μg/m3 

is given by 

h(t,d) = Q(d) tl.915 

where 

Q(d) = 1.11 × 10-7d + 1.84 × 10-9d2 

The model fits the data well, as can be seen from the goodness-of-fit statistic 

x2 = � (0-E)2/E = 1.60 

which has, asymptotically, a chi-square distribution with 5 degrees of freedom under the model 

specified. The observed and predicted values used in calculating x2 are (3, 2.5), (6, 7.2), (6, 5.1), 

(4, 3.1), (5, 6.7), (5, 4.1), (2, 1.4), and (4, 4.3). 

Taking into account the competing risk, the lifetime probability of lung cancer death due 

to exposure to chromium d μg/m3

 is given by 

L 

P(L,d) = o� h(t,d)exp {-[(Q(d)/2.915) t2.915 + A(t)]}dt 

where L is the maximum human lifetime and is mathematically equivalent to infinity, since the 

probability of surviving beyond L is 0. At low doses approximately, 

P(L,d) = d × P(L,l) 

45
where P(L,l) is the lifetime cancer risk due to exposure to 1 μg/m3

 of chromium. The unit risk, 

P(L,l), has been adopted by the EPA as an indicator of the carcinogenic potency of a chemical 

compound. 

5.3.5. Inhalation Unit Risk 

To calculate the unit risk, P(L,1) it is necessary to know exp[-A(t)], the probability of 

surviving to age t. Since this probability can only be estimated, it is assumed that the survival 

probability is constant over a 5-year interval, as provided in the U.S. Vital Statistics. 

Using this approximation and by integrating the formula P(L,1) we have 

P(L,1) = �[exp(-3.87 × 10-8 ti-1

2.9l5) - exp(-3.87 × 10-8 ti2.9l5)] × Pi 

= 1.16 × 10-2/μg/m3 

where (ti-l, ti) is a 5-year interval and Pi is the probability of survival up to the age ti-l. Pi is 

assumed to be a constant over the interval and is estimated from the 1975 U.S. Vital Statistics. 

As a crude approximation, the carcinogenic potency of chromium can be also be 

calculated by B = (R-1) × Po/d, where Po = 0.036 is the estimated lung cancer mortality rate for 

the U.S. population, R is the relative risk of the lung cancer deaths in the cohort, and d is the 

“standardized” lifetime dose concentration to which the workers were assumed to be exposed. 

This approach is used by EPA to calculate carcinogenic potency when the only data available are 

the relative risk estimate and an average exposure concentration. 

For the Mancuso (1975) data, the relative risk R and the “standardized” dose d are 

estimated respectively to be R = 7.2 and d = 15.5 μg/m3

. They are calculated by combining the 

relative risks and dose concentrations in each of the age-exposure categories, weighted by the 

relative magnitude of person-years, as shown in Table 4. 

Therefore, the carcinogenic potency of hexavalent chromium (CrVI) is estimated to be 

B = (7.2-1) × 0.036/15.5 = 1.4 × 10-2/μg/m3 

This crude estimate is only slightly higher than the previous estimate, 1.2 × 10-2/μg/m3. 

6. MAJOR CONCLUSIONS IN THE CHARACTERIZATION OF 

HAZARD AND DOSE RESPONSE 

6.1. HUMAN HAZARD POTENTIAL 

Chromium is a naturally occurring element present in rocks, soils, plants, animals, and 

volcanic emissions. Chromium may exist in several chemical forms and valence states in the 

46
environment. The most commonly occurring valence states are chromium metal (0), trivalent 

Cr(III), and hexavalent Cr(VI). The primary sources of hexavalent chromium in the environment 

are most likely chromate chemicals used as rust inhibitors in cooling towers and emitted as mists, 

particulate matter emitted during manufacture and use of metal chromates, and chromic acid mist 

from the chromeplating industry. Hexavalent chromium in the atmosphere may react with dust 

particles or other pollutants to form trivalent chromium, or may be removed from air by 

atmospheric fallout and precipitation. Hexavalent chromium may exist in aquatic media as 

watersoluble complex anions and may persist in water. Hexavalent chromium may also may 

react with organic matter or other reducing agents to form trivalent chromium. Hexavalent 

chromium in soil tends to be reduced to trivalent chromium by organic matter. 

Cr(III) potentiates the action of insulin in peripheral tissue and is essential for animals and 

human beings. Adults in the United States are estimated to ingest approximately 60 μg/day of 

chromium from food (ATSDR, 1993). The national Research Council has identified an 

estimated safe and adequate daily dietary intake (ESADDI) for chromium of 50-200 μg/d (NRC, 

1989), corresponding to 0.71-2.9 μg/kg/day for a 70 kg adult. FDA has selected a Reference 

Daily Intake for chromium of 120 μg/d (DHHS, 1995). 

The bioavailability of chromium may be the single most important factor determining the 

toxicity of a specific chromium source (O’Flaherty, 1996). Ingested hexavalent chromium is 

efficiently reduced to the trivalent form in the gastrointestinal tract. Gastrointestinal absorption 

of Cr(VI) occurs with greater efficiency than absorption of Cr(III), though absorption of ingested 

hexavalent chromium is estimated to be less than 5%. Following inhalation exposure, chromium 

may be absorbed into the systemic circulation, transferred to the gastrointestinal tract by 

mucociliary action, or remain in the lung. A number of factors can influence the absorption of 

chromium following inhalation, including the size, oxidation state, and solubility of the 

chromium particles; the activity of alveolar macrophages; and the interaction of chromium with 

biomolecules following deposition in the lung. Inhaled hexavalent chromium can be reduced to 

the trivalent form by ascorbate and glutathione. Absorption of inhaled chromium following 

occupational exposure has been demonstrated by the measurement of chromium in the serum and 

urine and hair of workers in the chromium industry. Water-soluble hexavalent chromium has 

been shown to be absorbed rapidly by inhalation in rats. 

A significant amount of absorbed chromium is taken up in the bone, liver, kidney, and 

spleen. Hexavalent chromium readily crosses cell membranes through the phosphate and sulfate 

anion-exchange carrier pathway. Cr(III) compounds may cross cell membranes, but only with 

very low efficiency. Cr(VI) readily passes through cell membranes and produces a number of 

potentially mutagenic DNA lesions upon intracellular reduction to Cr(III). Hexavalent chromium 

is mutagenic in bacterial assays, yeasts, and V79 cells, and transforms both primary cells and cell 

lines. 

Results of occupational epidemiologic studies of chromium-exposed workers across 

investigators and study populations consistently demonstrate that chromium is carcinogenic by 

the inhalation route of exposure. While data from these studies could be used to suggest that 

total chromium is carcinogenic by inhalation, animal data support the human carcinogenicity data 

47
only on hexavalent chromium. Hexavalent chromium compounds have been shown to produce 

the following tumor types in animal assays: intramuscular injection site tumors in rats and mice, 

intrapleural implant site tumors in rats, intrabronchial implantation site tumors in rats, and 

subcutaneous injection site sarcomas in rats. Workers are exposed to both Cr(III) and Cr(VI) 

compounds. Because only Cr(VI) has been found to be carcinogenic in animal studies, however, 

it was concluded that only Cr(VI) should be classified as a human carcinogen. 

At present, the carcinogenicity of hexavalent chromium by the oral route of exposure 

cannot be determined because of a lack of sufficient epidemiological or toxicological data. One 

study of miners in Ontario suggested that exposure to chromium may have been associated with 

stomach cancer, but other human and animal studies have not reported similar effects. 

A number of epidemiological studies of workers in chromium production facilities have 

demonstrated an association between inhalation of Cr(VI) and upper respiratory irritation and 

atrophy, lower respiratory effects, and renal effects. There is significant uncertainty regarding the 

relevance of occupational exposures to chromic acid mists to environmental exposures to 

hexavalent chromium particulates, as well as the role of direct contact between chromiumcontaminated hands and nasal passages in the studies reporting nasal irritation, atrophy, and nasal 

septum perforation in the occupational setting. Animal studies have reported a variety of effects 

including perforation of the nasal septum, necrosis, atrophy and hyperplasia of the bronchial 

epithelium, bronchiolization of the alveoli, alveolar proteinosis, changes in lung weight, lactate 

dehydrogenase in BALF, albumin in BALF, changes in tracheal and submandibular lymph nodes, 

atrophy of the spleen and liver, and ulcerations in the stomach and intestinal mucosa following 

exposures to Cr(VI) compounds by inhalation (Steffee and Baetjer, 1965; Nettesheim et al., 

1971; Glaser et al., 1985; Glaser et al., 1990). 

Little data exist regarding health effects resulting from ingestion of hexavalent chromium. 

A single cross-sectional study was located that reported effects in humans resulting from 

ingestion of chromium-contaminated well water. Residents of a village in China were reported 

to have experienced oral ulcers, diarrhea, abdominal pain, indigestion, vomiting, leukocytosis, 

and presence of immature neutrophils. Other reports of toxic effects of Cr(VI) in humans are 

limited to case reports from accidental poisonings. With the exception of increased body burden 

of chromium, no significant adverse effects have been observed in animal studies following 

ingestion of chromium. 

High oral doses of hexavalent chromium compounds have been reported to cause 

reproductive and developmental toxicity in mice, including decreased fetal weight, increased 

resorptions, and increased abnormalities. A recent study in mice and rats determined that 

hexavalent chromium is not a reproductive toxicant in either sex. 

Chromium is one of the most common contact sensitizers in industrialized countries, and 

allergic contact dermatitis is associated with occupational exposures to numerous materials and 

processes, including chromeplating baths, chrome colors and dyes, cement, tanning agents, and 

wood preservatives. 

48
6.2. DOSE RESPONSE 

The data of Mancuso (1975) were used to generate the unit risk for inhalation of 

hexavalent chromium of 1.2 × 10-2/μg/m3

. A recent follow-up study (Mancuso, 1997) is 

supportive of the conclusions of Mancuso (1975); however, several important uncertainties in the 

potency estimate result from the use of the Mancuso data for the dose-response estimation. 

The risk of hexavalent chromium is estimated on the basis of the total chromium obtained 

from all the soluble and insoluble chromium to which workers were exposed. Since there are 

likely differences between the chromium compounds to which workers were exposed, the 

potency of hexavalent chromium compounds may be underestimated. Bourne and Yee (1950) 

reported that the ratios of Cr(III) to Cr(VI) concentrations in the airborne dust in nine major 

departments in the plant in which the Mancuso cohort worked ranged from 1 to 3, except for two 

departments where the ratios were 6 for the lime and ash operation and 52 for the ore 

preparation. Excluding the ore operation, the maximum ratio of trivalent chromium to 

hexavalent chromium is 6, and thus the underestimation of the risk for hexavalent chromium is 

unlikely to be greater than sevenfold. 

Use of the hygiene data collected in 1949 may result in a slight underestimation of the 

levels of exposure workers experienced between 1931 and 1937. However, because the plant 

was relatively modern in the 1930s, the underestimation is unlikely to be large. If an 

underestimation of 2 times were assumed, then the unit risk would be reduced from 

1.2 × 10-2/μg/m3 to 6 × 10-3/μg/m3

. 

The risk presented in this report may be somewhat overestimated as a result of the 

assumption that smoking habits of chromate workers were similar to those of the general white 

male population. It is generally accepted that the proportion of smokers is higher for industrial 

workers (thus the higher background incidence rates) than for the general population. For 

example, the background age-specific rate of lung cancer at ages 50, 60, and 70 could be 40% 

greater than that presented in Table 4 should it be assumed that 80% of the chromate workers in 

the Mancuso study were ever-smokers (individuals who smoke at least 100 cigarettes during their 

lifetimes) and only 50% of the general white male population were ever-smokers. For example, 

if the background rate of lung cancer mortality (due to smoking) for the cohort in Table 4 is 

increased by 40%, then the corresponding unit risk would be reduced by about 25%, or from 1.2 

× 10-2/μg/m3 to 8.7 × 10-3/μg/m3

. 

Relatively few studies in the literature address the oral toxicity of Cr(VI). The Zhang and 

Li (1987) human study reported on health effects in 155 Chinese villagers who consumed 

drinking water contaminated with hexavalent chromium at 20 ppm. Only one exposure level was 

included and the study did not indicate whether the drinking water was contaminated with other 

materials in addition to hexavalent chromium. The study also did not address whether potential 

airborne exposures to hexavalent chromium from the plant or other confounding factors may 

have contributed to observed effects. The exposure period was unknown, and the study could not 

provide a NOAEL for the observed effects. However, the study of Zhang and Li suggests that 

49
gastrointestinal effects in humans may occur at an exposure level of 20 ppm of hexavalent 

chromium in drinking water. 

Two studies have reported fetotoxic and developmental effects of Cr(VI) in mice and rats 

at exposure levels of 250 - 700 ppm in drinking water (Junaid et al., 1996; Kanojia et al., 1996). 

While neither of these studies provide clear NOAEL values, LOAELs for fetotoxicity can be 

used to extrapolate to NOAELs of 6.7 mg/kg-day and 3.7 mg/kg-day in mice and rats, 

respectively. 

Both the MacKenzie et al. (1958) and Anwar et al. (1961) animal studies are limited by a 

small number of animals/group and a lack of an observed effect at any dose level. The 

MacKenzie et al. study has the additional limitation of being conducted for less than a lifetime. 

However, the MacKenzie study was considered to be most suitable for the dose-response 

assessment for ingested chromium and generated an adjusted NOAEL of 2.5 mg/kg-day. 

The adjusted NOAEL from the MacKenzie study was modified by two 10-fold 

uncertainty factors to account for the expected interspecies and interhuman variability in lieu of 

specific data. An additional threefold uncertainty factor is applied to the adjusted NOAEL to 

compensate for the less-than-lifetime exposure duration in the Mackenzie study. A modifying 

factor of 3 is applied to account for uncertainties resulting from study of Zhang and Li. The total 

uncertainty factor applied to the adjusted NOAEL is 900, yielding an RfD of 3 × 10-3 mg/kg-day. 

Confidence in the oral reference dose is low. Confidence in the chosen study is low because of 

the small number of animals tested, the small number of parameters measured, and the lack of 

toxic effect at the highest dose tested. Confidence in the database is low because the supporting 

studies are of equally low quality, because of concerns raised by the study of Zhang and Li, and 

because of the lack of information on teratogenic endpoints. Low confidence in the RfD follows. 

Two RfCs have been generated for hexavalent chromium. The RfC for chromic acid 

mists and dissolved hexavalent chromium aerosols is based on a study of workers in a chromium 

plating facility (Lindberg and Hedenstierna, 1983). The occurrence of nasal mucosal atrophy in 

the Lindberg and Hedenstierna study is consistent with previous reports that exposure to 

chromium acid mists is associated with ulceration of the mucous membranes and perforation of 

the cartilaginous portions of the nasal septum (Hamilton and Hardy, 1974). 

Several uncertainties result from the exposure characterization in the Lindberg and 

Hedenstierna (1983) study. While nasal mucosal atrophy has been consistently reported 

following occupational exposure to chromic acid mists, it is uncertain whether these exposures 

are relevant to exposures to hexavalent chromium particulates in the environment. The LOAEL 

for this study is based on an 8-hour TWA concentration. However, it is possible that the 

exposure response may be better explained by the peak exposure rather than the TWA dose. The 

authors acknowledge that nasal septum ulcerations and perforations did not correlate with mean 

exposure concentrations in the 2-20 μg/m3

 group and observed that damage to the nasal septum 

correlated better with short-term peak exposure than with 8-hour mean exposures. The report 

does not provide sufficient detail on peak exposures to resolve this issue unequivocally, and in 

the absence of additional data, the RfC was generated based on the TWA exposure. The RfC 

50
based on Lindberg and Hedenstierna (1983) is applicable only to chromic acid mists and 

dissolved hexavalent chromium aerosols. 

Confidence in the RfC for chromic acid mists and dissolved hexavalent chromium 

aerosols is low. Confidence in the chosen study is low because uncertainties regarding the 

exposure characterization and the role of direct contact for the critical effect. Confidence in the 

database is low because the supporting studies are equally uncertain with regard to the exposure 

characterization. Low confidence in the RfC follows. 

The RfC for hexavalent chromium particulates was developed based on Glaser et al. 

(1985, 1990). Several uncertainties are associated with the use of these studies for development 

of the RfC. Glaser et al. (1985, 1990) did not provide details of upper respiratory, reproductive, 

or renal effects resulting from the exposures, and did not include chromic acid mists or dissolved 

hexavalent chromium aerosols in their study. This uncertainty has been addressed by limiting the 

RfC developed on the basis of Glaser et al. (1985, 1990) to lower respiratory effects from 

inhalation of hexavalent chromium dusts. Uncertainty results from the use of a subchronic study 

for development of the chronic RfC. This uncertainty was addressed by the use of a 10-fold 

uncertainty factor to account for potential chronic effects. It is uncertain which of the endpoints 

reported in Glaser et al. (1985, 1990) is most appropriate for development of the BMC. LDH in 

BALF was used for development of the RfC, as this endpoint is considered to be a sensitive 

indicator of toxicity and provides the most conservative estimate of the BMC based on the Glaser 

et al. (1985, 1990) data. Uncertainty in the dose-response curve for LDH in BALF was 

addressed through the use of a conservative model fit of the data. 

Confidence in the RfC for hexavalent chromium particulates is medium. Confidence in 

the chosen study is medium because of uncertainties regarding upper respiratory, reproductive, 

and renal effects resulting from the exposures. Medium confidence in the RfC follows. 

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APPENDIX A. EXTERNAL PEER REVIEW— 

SUMMARY OF COMMENTS AND DISPOSITION 

The support document and IRIS summary for hexavalent chromium have undergone both 

internal peer review performed by scientists within EPA and a more formal external peer review 

performed by scientists performed accordance with EPA guidance on peer review (U.S. EPA, 

1992). Comments made by the internal reviewers were addressed prior to submitting the 

documents for external peer review and are not part of this appendix. The external peer 

reviewers were tasked with providing written answers to general questions on the overall 

assessment and on chemical-specific questions in areas of scientific controversy or uncertainty. 

A summary of significant comments made by the external reviewers and EPA’s response to these 

comments follows. 

Comments on General Questions for IRIS Peer Reviewers

1. Are you aware of any other data/studies that are relevant (i.e., useful for the hazard 

identification or dose-response assessment) for the assessment of the adverse health effects, 

both cancer and noncancer, of this chemical? 

A. Comment: Since Mancuso has recently updated his cohort and since the information is 

already referenced in the IRIS and the Toxicological Review document, I believe the cancer slope 

factors should be recalculated from the total chromium data and the Cr(VI) data. 

Response to Comment: The Agency agrees that the cancer slope factor should be 

recalculated from the updated cohort. The Agency is unable to do so in a time frame consistent 

with the IRIS Pilot process, and will take up revision of the slope factor when possible. 

B. Comment: In calculating the oral reference dose the authors used data from a rodent study 

by MacKenzie et al. (1958) and discounted data from a human study by Zhang et al. I am 

concerned that the NOAEL in the animal study exceeded the level reported in the Chinese study 

(20 ppm) that caused serious illness in humans. 

Response to Comment: The study of Zhang and Li (1987) raises concerns for human 

gastrointestinal effects at high dose levels in drinking water; however, the exposure data in this 

study are limited, the duration of exposure is unknown, the presence of confounding factors is 

not addressed, and a NOAEL could not be identified from the study. While these uncertainties 

preclude the use of this study for risk assessment, a threefold modifying factor has been applied 

to the NOAEL derived from the study of MacKenzie et al. (1958) to address the concerns raised 

by the study of Zhang and Li (1987). 

C. Comment: Several new reports have been found showing significant embryotoxic and 

fetotoxic damage due to exposure of rats and mice to high doses of Cr(VI) or Cr(III) in drinking 

water. I don’t feel confident rederiving an RfD based on this data, and the doses are clearly very 

high. However, derivation of an RfD based on an observed toxicological effect appears to be 

preferable to an RfD based on a NOAEL. 

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Response to Comment: The reports have been added to the reproductive/developmental 

studies section of the toxicological review document and have been considered in the 

development of the RfD for Cr(VI). The new reports do not provide a clear NOAEL for the 

fetotoxic and embryotoxic effects. Extrapolated LOAELs derived from the studies of Junaid et 

al. (1996) and Kanojia et al. (1996) are similar to and support the use of the NOAEL identified in 

the study of MacKenzie et al. (1958) for development of the RfD. 

D. Comment: The documents correctly state that Cr(VI) gets transformed to Cr(III) in vivo, but 

they skirt the issue of whether or not a Cr(VI) study is really a study of in vivo exposure to 

Cr(III). 

Response to Comment: Given the rapid reduction of Cr(VI) to Cr(III) in vivo, it is 

relevant to consider whether environmental exposures to Cr(VI) or administration of Cr(VI) in 

controlled animal experiments is essentially identical to environmental exposures to Cr(III) or 

administration of Cr(III) in controlled experiments. While considerably more data are available 

for Cr(VI) than for Cr(III), it appears at present that exposures to Cr(VI) have considerably 

different outcomes than exposures to Cr(III). The Agency has prepared the toxicological 

summaries and IRIS files for Cr(VI) and Cr(III) from this perspective. 

2. For the RfD and RfC, has the most appropriate critical effect been chosen (i.e., that adverse 

effect appearing first in a dose-response continuum)? For the cancer assessment, are the 

tumors observed biologically significant? Relevant to human health? Points relevant to this 

determination include whether or not the choice follows from the dose-response assessment, 

whether the effect is considered adverse, and if the effect (including tumors observed in the 

cancer assessment) and the species in which it is observed is a valid model for humans. 

A. Comment: The descriptions of the study used to develop the RfC for chromic acid mist were 

confusing. While I agree that the LOAEL is 0.002 mg/m3

, I question the uncertainty factor of 3 

to extrapolate from subchronic to chronic exposure. Virtually all the workers in the high dose 

level in the Lindberg cohort had significant effects even though the duration of exposure for 

workers with nasal ulcerations ranged from 5 mo to more than 10 years. 

Response to Comment: The descriptions of the study of Lindberg and Hedenstierna 

(1983) have been improved. The experience of workers at the high dose level with significant 

effects over a subchronic exposure period does not eliminate the possibility that similar effects 

could occur at considerably lower doses over a chronic exposure period. In order to account for 

this uncertainty, the Agency favors use of a threefold factor to extrapolate from the subchronic to 

chronic exposures. 

B. Comment: The authors argue that the threefold uncertainty factor used by Malsch et al. is 

insufficient. I disagree. In the Glasser paper the concentration in the lung appears to be 

approaching a maximum at 90 days. The authors also suggest that inflammatory effects from 

lower long-term exposures may occur. In my experience inflammation is an early symptom and 

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in some cases even regresses in the presence of continuing exposure. Thus, I would use Malsch’s 

calculations as published yielding a RfC of 0.34 mg/m3

. 

Response to Comment: Information from Glaser (1985) shows that chromium is still 

accumulating in the lung and kidney at the end of the 90-day exposure period and there is 

insufficient information to determine how well subchronic studies predict chronic inflammation. 

The Agency supports the use of a 10-fold uncertainty factor to extrapolate from a subchronic to a 

chronic study. 

C. Comment: The additional uncertainty factor of 3 (for the RfD) to compensate for less than 

lifetime exposure duration in the MacKenzie et al. study can be questioned. Why not apply a 10-

fold uncertainty factor for this purpose, based also on the relatively low number of animals used 

in the study? 

Response to Comment: The use of the MacKenzie et al. study for development of the 

RfD is considered to be conservative, given the lack of an observed effect in the animals. Even 

in light of the relatively low number of animals in the study, the threefold uncertainty factor is 

considered by the Agency to be sufficient for development of the RfD. 

3. Have the noncancer and cancer assessments been based on the most appropriate studies? 

These studies should present the critical effect/cancer (tumors or appropriate precursor) in 

the clearest dose-response relationship. If not, what other study (or studies) should be 

chosen and why? 

A. Comment: A level of 0.002 mg/m3 in the Lindberg and Hedenstierna study was chosen as 

the LOAEL for the RfC. This level caused significant symptoms, including atrophied nasal 

mucosa, in workers exposed, whereas no symptoms were seen at a level of 0.001 mg/m3

. 

Therefore, why not use this lower level as a NOAEL? 

Response to Comment: Although no subjective irritation occurred in the subgroup 

exposed at 0.001 mg/m3

, the distribution of the four cases of atrophy in this group was not 

provided, which precluded designation of a NOAEL at 0.001 mg/m3

. 

B. Comment: The RDDR is based on aerodynamic diameters of particles used in the animal 

studies; however, it would be helpful to also know something about ambient particle sizes 

containing chromium such that a more appropriate dosimetric adjustment across species using 

differences in particle deposition between rodents and humans can be applied. 

Response to Comment: Data on ambient particle sizes containing chromium are 

necessarily site specific, and will vary depending on the nature of the contaminated media and 

exposure setting. While it might be of interest to determine the ambient particle size distribution 

in order to develop a site-specific RDDR, these data cannot be practically incorporated into the 

RDDR in order to account for all of the possible ambient exposures. The assessment has utilized 

the data in the Agency’s guidance for development of RfCs for this purpose. 

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C. Comment: It appears that the endpoint albumin in bronchoalveolar lavage fluid showed 

even greater effects than LDH, and I wonder why this endpoint was not selected for the 

benchmark approach. 

Response to Comment: LDH in BALF provided a BMD approximately one-half that of 

albumin in BALF (Malsch et al., 1994). In order to be conservative and focus on the critical 

effect, LDH in BALF was chosen as the endpoint for development of the RfC. 

D. Comment: The fact that chromium was still accumulating in lung tissue at the end of a 90-

day exposure does not suggest that lower long-term exposures will lead to accumulation of a 

critical concentration in the lung. This depends very much on the clearance kinetics, and at low 

concentrations lung levels will reach an equilibrium that is lower than that achieved at higher 

concentrations. 

Response to Comment: The Agency acknowledges the possibility that at low 

concentrations lung levels will reach an equilibrium which is lower than that achieved at higher 

concentrations. However, in the absence of data, it cannot be demonstrated that chronic 

exposures will not lead to accumulation of a critical concentration in the lung. In order to 

conservatively reflect the uncertainty on this issue, the Agency has utilized a 10-fold uncertainty 

factor to account for less-than lifetime exposure. 

4. Studies included in the RfD and RfC under the heading “Supporting/Additional studies” are 

meant to lend scientific justification for the designation of critical effect by including any 

relevant pathogenesis in humans, any applicable mechanistic information, any evidence 

corroborative of the critical effect, or to establish the comprehensiveness of the database 

with respect to various endpoints (such as reproductive/developmental toxicity studies). 

Should other studies be included under the “Supporting/Additional” category? Should some 

studies be removed? 

A. Comment: The new data on reproductive toxicity of chromium in the drinking water needs 

to be carefully compared to the NTP study in which rats and mice were fed potassium chromate 

in the diet. The form of chromium and route of exposure are clearly of paramount importance. 

Response to Comment: A discussion comparing and contrasting the results of the NTP 

studies and the new reports has been added to the reproductive/developmental studies section of 

the toxicological review document. 

B. Comment: Some of the statements related to the genotoxic effects of hexavalent chromium 

are either inaccurate or misleading. 

Response to Comment: The recommended modifications to this section have been made. 

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5. For the noncancer assessments, are there other data that should be considered in developing 

the uncertainty factors of the modifying factor? Do you consider that the data support the 

use of different (default) values than those proposed? 

A. Comment: No comment received. 

6. Do the confidence statements and weight-of-evidence statements present a clear rationale 

and accurately reflect the utility of the studies chosen, the relevancy of the effects (cancer 

and non-cancer) to humans, and the comprehensiveness of the database? Do these 

statements make sufficiently apparent all the underlying assumptions and limitations of these 

assessments? If not, what needs to be added? 

A. Comment: Yes. 

Comments on Chemical-Specific Questions

1. Are the conclusions of Zahid et al. regarding potential reproductive toxicity of Cr(III) in any 

way countered by the results of the NTP study? 

A. Comment: The Cr(VI) document does a superficial job of communicating the deficiencies 

of the Zahid study. 

Response to Comment: Additional information has been provided in the 

reproductive/developmental effects section to address this concern. 

2. Should separate RfCs be generated for chromic acid mists and particulates of hexavalent 

chromium? 

A. Comment: Yes. 

B. Comment: Yes, the bioavailability and physiological effects of these two forms of 

chromium appear to differ substantially. 

Response to Comments: Separate RfCs have been generated for chromic acid mists and 

particulates of hexavalent chromium. 

3. Should the RfCs apply to both Cr(VI) and Cr(III) or only to Cr(VI)? 

A. Comment: The RfCs based on data from Lindberg and Hedenstierna and Glaser are 

appropriate only for Cr(VI). 

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4. Are there any studies available that could be used to develop an RfC for trivalent chromium? 

A. Comment: The Agency has determined that an RfC for Cr(III) cannot be developed and I 

agree. 

5. The principal study (Mancuso, 1975) and the follow-up study (Mancuso, 1997) show the best 

dose-response relationship for total chromium, but animal data support a conclusion of 

carcinogenicity only for hexavalent chromium. Should the potency estimate address total 

chromium or hexavalent chromium? 

A. Comment: The potency estimate should be based on total chromium, but should note that 

the exposure is mixed. 

Response to Comments: EPA will reevaluate the potency estimate for chromium based 

on the recent Mancuso update in the future. 

B. Comment: The potency estimates should be based on hexavalent chromium. 

Response to Comment: EPA will re-evaluate the potency estimate for chromium based 

on the recent Mancuso update in the future. 

6. There is a Canadian study that relates stomach cancer to gold mining following exposures 

to chromium. Does this study justify/support determination of an oral factor for chromium? 

A. Comment: I believe the Canadian study should not be used to determine an oral slope factor. 

Response to Comment: The Canadian study has not been used to determine an oral slope 

factor. 

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