Document Lprwr0Lmxpx9v5JzO68pk7z77

/e 1///1 >jJ(L GA/os, c/i REGULATORY TOXICOLOGY and pharmacology 13, 3-17 (1941) Effect of Exposure Route on Potency of Carcinogens William E. Pepelko Human Health Asxessmept Group, Other uj Health and Environmental Awevunent L' S Environmental Froteetum Auencv, JO! M Siren. Slf, W ashington. DC 20460 Retetved February I". 1990 To compare tl.tr cffecttvencis of different exposure routes for the induction of cancer in exper imental animals, the estimated dose associaicd with a 35% additional nsk of cancer (RRD;,I was calculated using a group of carcinogenic agents tor which both inhalation and oral ingestion cancer bioassays were available. Companions were made of 14 agents in rats and 9 in mice. Seven of the nine compared in mice were also compared in rats Among rats, 8 of 14 agents were more effective via the oral route, while 7 of 9 were more effective via the oral route in mice. The sanation in RRD;S values with route, however, was less than 10-fold for all the agents tested in mice and for 11 of 14 tested in rats. An overall difference in potency with route could not he detected statistically. In rats, differences in potency greater than 10-fold were found for asbestos, vinyl chlonde. and hydrazine. In the case of asbestos, the agent was in the form of relativclv insoluble particulate matter The greater potency via inhalation is likely due to longer residence time of the panicles in the deep lung than in the gut, allowing for a greater degree of panicle dissolution with an accompanying increase in bioavailability. Vinyl chlonde was generally tested by inhalation at doses high enough to saturate activation pathways, resulting m underestimates of low-dose potency Many of me smjller poicno differences with route, as well as those Ior hydrazine, were considered likely to be the result of variability in the design and/or qualitv of studies. It was concluded that, if the design and conduct of the expenmems were adequate, if agents in the form of relatively insoluble particuu . matter are eliminated, and if corrections are made to account for incomplete activation, then large errors during route extrapolation are unlikely to occur, tc 1991 Amfcnnc fan, Inc. INTRODUCTION It is sometimes necessary to assess carcinogenic risk quantitatively using data for which the exposure route is different than the normal route of human exposure. This occurs most frequently with experimental animal studies that use the oral route, while the primary route of human exposure for the agent in question is inhalation. While extrapolation of cancer risk from the oral to the inhalation route has been carried out quite often, t systematic comparison of route-related potency along with an evaluation of the factors responsible for route-related differences in potency has not been per formed. The assumption most often made during route extrapolation is that carcinogenic potency as a function of applied dose is equivalent across both dose routes, i.e.. that Or3-2300/41 S3.00 Copvn0u { |Wj by Academic Pink Inc, AU nghti of rvpftjductKvrt <r jny form rtstnvd. OLI 3152 I 4 WILLIAM E PEPELKO the dose received from inhalation exposure expressed in terms of mg/kg body wt per day is equivalent to the same dose orally. This approach, however, ignores important pharmacokinetic and toxicokmetic considerations that may be responsible for differ ences in both carcinogenic and noncarcinogenic potency (Pepelko and Wiihey. 1985). Some of these are absorption efficiency , first-pass effects, ponal-of-entry effects, and effect of route on degree of blood level fluctuation. It is often possible to adjust for some ofthese uncertainties. Data regarding absorption efficiency are quite often available and can be taken into account quite simply. In formation regarding first-pass effects (the degree of inactivation during first pass through the liver) can also be used to adjust the estimated target organ dose, assuming that the liver is not the primary target organ. Other factors, however, are more difficult to adjust for. One example is a potential difference in target organ sensitivity when cancer occurs at a portal of entry. Another involves chemicals that are easily absorbed but have limited solubility in the blood or short active half-lives. In such cases the areas under the blood time-concentration curves are likely to be the same for equivalent doses administered by the oral or inhalation route (Trouwborst. 1982). out the shapes of these curves can be considerably different. During inhalation exposure, blood concentrations tend to reach an asymptote and remain stable with continuing exposure. With bolus dosing, common during oral exposure, blood levels can fluctuate greatly (Pepelko and Wiihey, 1985). This can result in difierent degrees of activation, varying toxic effects at the target organ, etc., all of which can affect carcinogenic potency. The present study compares the carcinogenic potency of a variety of chemicals for which adequate long-term bioassays by both the inhalation and oral route of exposure are available, identifies factors responsible for large differences in potency with route, and attempts to adjust for them should they occur. METHODS The cancer potency data base of Gold et al. (1984) was surveyed to identify chemicals having long-term cancer bioassay data for both the oral and inhalation routes. The literature was searched to find potentially useful studies published since 1984, Certain unpublished studies listed in EPA documents were also used (Tables 1 and 2). Adequate oral and inhalation data were found for 14 chemicals tested in rats and for 9 chemicals tested in mice. In some of the oral studies the animals were dosed via gavage. Since we were unable to detect consistent differences in potency for chemicals tested by gavage or by administration in the food or water, they were not differentiated. All except asbestos arc organic compounds. Unfortunately, no adequate comparisons were available for any of the metals or other agents ir the form of relatively insoluble particulate matter. While positive inhalation data were available for some metals such as cadmium (Takenaka et al.. 1983) and beryllium (Schepers. 1961). oral studies were either of marginal significance or negative. Seven of the chemicals were adequately tested by both routes in mice and rats. For each data set. the applied dose was expressed in terms of milligrams administered per day. Unless body weights were listed, mice were assumed to have a body weight of 0.03* kg and rats. 0.35 kg. Respiratory volumes over a 24-hr period were estimated using the following allometric equations as described by Anderson et al. (1983) and *t i i OLI 3153 EXPOSURE ROUTE AND CANCER POTENCY 5 inhalation data reported b> Guyton (1950); 0.105 (body wt/0.113 kg)* for rats, and 0.0345 (body wt/0.025 kg)u6: ;or mice. After using body weight and respiratory volume to convert the exposure concentration to units of mg/dav, the daily dose was adjusted to reflect the equivalent daily dose administered over a lifetime. For less-than-lifetime rodent studies, the daily dose was multiplied by the fraction of lifetime exposed. No adjustment was made for potential differences in absorption, since it was desired to initially test all the agents without making any corrections. The adjusted daily applied doses and reported tumor incidences for each data set were used as inputs for the Global 86 multistage model computer program. The pro gram was requested to provide both the maximum likelihood estimate (MLE) of dose and the 95% Iow-.t confidence limit on the dose associated with an additional risk of 0.25. The risk reference dose (RRD;J) is the MLE of the dose required to increase the probability of cancer to 25% + probability at dose zero. The use of additional risk in this study should not substantially affect the comparison of carcinogenic potency by dose route because very few of the data sets used reflected high background response rates. For those data sets having unusually high background rates, or decreasing rates of response at high concentration, due to acute toxicity or saturation of activating biochemical pathways, an additional risk of 0.25 did not yield a numerically stable estimate of RRD:5. The criterion for numerical instability was an observed percentage of cancer at the highest dose level less than 90^ of the highest percentage observed at any dose. In these cases. Global 86 provided a warning and the RRD-, value was excluded from further analysis. This occurred with tetrachloroethylene (in rats) and cadmium. An RRD;< was calculated for each target organ showing a statistically sig nificant increase in tumor incidence, as well as for total tumor incidence. The approach described above generated a range of MLE and lower limit RRDm values for each of the two dose routes. To facilitate a comparison of carcinogenic potency by dose route, the geometric mean RRD;} for each range of RRDs was com puted by dose route and species using tumor incidences at all sites where a significant increase was detected. If high dose levels are used for chemicals requiring metabolic activation, saturation of the activation pathway may occur. The tumor response then tends to reach a plateau and the RRD- value may be driven to an artificially high level. To attempt to account for this possibility, an MLE and lower bound RRD representing a 1% additional risk (designated as RRDU,) were also calculated for each data set. RESULTS The chemicals compared and the number of data sets examined for each species along with references arc listed in Tables 1 and 2. The geometric mean RRD;J values for the 14 agents having adequate cancer response data by both the oral and the inhalation routes in rats are summarized in Table 3. Nine comparisons for mice are listed in Table 4. Except for vinyl chloride, asbestos, and hydrazine, the geometric mean RRDi< values determined from oral bioassays are within an order of magnitude of the ones obtained from inhalation studies in rats. Two other compounds, tetrachlo roethylene and cadmium, administered to rats by both dose routes could not be analyzed. In the case of cadmium, oral bioassays led to tumor responses that were OLI 3154 . ---- szm WILLIAM E. PEPELKO TABLE I Summary of Information Examined for Each agent in Rats Oral Inhalation Agem Number of data sets Reference Number of data sets Referenci Aery lonunlc Asbesios (chrysoule) :k Quasi ci at, 1980b: Bio/ dynamics Inc.. I980a-c. Bellies riel, )98o i Donham c: al. 1979 12 Quasi ci at. 1980a, Malioni ci at. 1977 4 Reeves ci al.. 1974. Wagner a at.. 1974. Benzene Cadmium compounds 7 Malloni ci at.. I98.t 1 Loser. 1980 Davis ci at.. 1978 5 Malioni a at.. 1983 *> Takenaka ci at. 1983 Dibromochloropropanc i: NCI. 1977a; Hazleion, 1977 7 NTP. 1982c J.2-Dihromocthanc 4 NCI. 1978a 39 Won^ cl al. 1982. NTP 1.2-Dichlorocihanc Dichloromcihane 6 NCI, 1978b R Scrota etal. 1986a: 1982a i Malioni ci at. 1980 20 Doxx Chemical Co.. 1980 National Coflcc Assn., 1982a NTP. 1985: KJrschman ci al 1986. Burek ci at 1984 Epichlorohydrir 7 Komshi rial. 1980: van 3 Laskin ci al. 1980 Esch. 1982 Eihylcne oxide 4 Dunkelbcrg. 1982 23 Snelling: <; at, 1981. Lynch and Moorman. 1982 Hydrazine 3 Seven and Bianeifiori. 1968 4 MacEwen and ' ernoi Propylene oxide Tciraehlorocthylenc Tnchloroeihyiene ] Dunkclhcrg. 1982 3 NCI. 1977b 6 NTP. 1986b, 1987 1980 -> Rexzel and Kuper. 1983 29 Rampy a at.. 1978. NTP. 1986a 4 Henschler ei al.. 1980 Fukada el at. 1983. Malioni ei a!. 1986 Vinyl chloride 10 Feron cl al, 1981 IS Drew ci at. 1983: Hong ei at.. 1981: Lee e/ ai 1978: Malioni. 1977 Malioni and Lefemine 197;: Malioni c: al Vinylidene ehlonde 16 NTP. 1982b 1981: Viola ci al 19'i 7 Malioni ei at, 1985. Lee ei at.. 1978. Quasi a at. !98n too limited to yield a stable RRDy. estimate. At least two other metals, nickel and beryllium, yielded positive results via the inhalation route of exposure but not b> ingestion (U.S. EPA. 1986. 1987). For letrachioroethylene, theonix available oral bioassay in rats failed to yield stable potency estimates because of excessive mor tality. OLI 3155 EXPOSURE ROUTE AND CANCER POTENCY TABLE 2 Summary of Information Examined for Each agent in Mice Oral Inhalation Agent Number of data sets Reference Number of data sets Reference Di bromoch loropropane 1.2-Dibromocthane 1.2-Dichloroethane Dichloromethane 1 I-Dimeifulhydrazine H'drazine Tcirachloroethylcnc Trichloroethylene Vinylidene chloride NCI. 1977a NCI. 1978a 15 NCI. 1978b 4 Nat. Cotfce Assn.. 1982b: Kirschman d ul. 1986; Scrota i7 ul. 1986b 7 Toth. 1973 12 Bianciliort. 1970. Toth. 1969. 1972; Se^cri and Buneifion. 1968 2 NCI, 1977b 8 Hcrren-Freund d ul. 1987: Van Duuren d ul.. 1979; NTP. 1986b; NCI. 1976 12 NTP, 1982c 8 NTP. 1982c 17 NTP. 1982a: Stinson d ul. 1981 1 Mjitom ct ul, 1980 20 NTP, 1985 8 Haun ct ul, I9N-1 1 MacEvicn and Vernot. 1980 18 NTP. 1986a 14 Hcnschler cl ul. 1980; Bell ci ul.. 1978: Fukada d ul.. 1983; MallOni d ul.. 1986 11 Maliom d ul.. 1985; Lee d al. 1978 The RRD;i values obtained for each route in mice are generally in closer agreement than those for rats. The only oral/inhalation RRD;S ratio approaching an order of magnitude was that for dibromoethane. The other ratios varied only from 0.6 to 2. Although oral/inhalation RRDij ratios were less than one in the majority of com parisons. the small route-related differences in most cases and the variability in the data do not allow any generalizations regarding the likelihood that one route is more effective in mice. Non-portal-of-entry. site-specific RRD;S comparisons were available for several of the agents evaluated. These are shown in Table 5. Differences in site-specific RRD;; values derived from oral versus inhalation studies paralleled the differences in mean RRD;; values for all tumor sites combined with some exceptions. Somewhat greater differences were seen for mammary gland tumors in rats exposed to acrylonitrile, while in mice exposed to vinylidene chloride, the inhalation route was slightly more effective for induction of mammary tumors, the opposite of that for all tumors com bined. The relative potency for kidney and liver tumor induction differed less with route in rats exposed to vinyl chloride, but the oral route was still apparently muci more potent for both sites. The apparent route-related difference in sensitivity to mammary tumor induction by acrylonitrile was probably due to large reported dif ferences in background tumor incidence among studies. Overall, restricting the com parisons by tumor site did not substantially alter the observed relationship between potency by the oral and the inhalation routes. Several of these agents arc site-of-contact carcinogens fi.e.. they induce stomach tumors by the oral route and nasal cavity or lung tumors by the inhalation route). OLI 3156 s WILLIAM E PEPELKO TABLE 3 Geometric Mean Rise Reeerence Doses foi Substances administered to Rats* RRD.i <mg/da> 1 RRD,,. i mg/da') Agent Oral Inhalation Oral/inhalation Oral Inhalation Oral'inhalation Acrylonitrile Asbestos Benzene Dibromochloropropa nc l.2-Dihromoetli;mc 1.2-Dichloroethane Dtchloromcthane Epichlorohvdnn Ethylene oxide Hydrazine Propylene oxide Trichloroethylene Vmvl chlonde Vinylidene chloride 5} 047 IOU8 1.7 *> 1 20 .774 <2 5.0 7.4 48 Hoe 5.: 3.7 8.5 389 08 14 67 1416 34 6.4 01 34 200 219 II 06 04 0 73 109 64 0.21 2.6 *17 14 ^ 0 12 0 065 0.2 0.O8 0.56 0.7 1 4 4 4 0 7 24 109 1.5 0.14 0.12 09 0 75 0.92 17 0.087 0.017 0 1 0.77 1.2 ft.7 no 21 0.02 0.27 8.9 0.7 0.32 2.1 05 305 4.2 19 0.1 0.3 0.2 1.2 0.8 49 0.6 <, 2 0 03 0.2 * Geometric mean of range in RRDs across all tumor sues. These include dibromochloropropane in rats and mice and dibromoethanc and epi* chlorohydrin tn rats. Ethylene oxide is a contact-site carcinogen by the orai route but is widely distributer tn the tissues following inhalation exposure and induce-, leukemia as well as brain tumors when exposure occurs by this route. Despite the dissimilanties in site of action following exposure by the two routes, all of these substances showed similar carcinogenic potencies for cither route of administration. Vinyl chloride vas the only agent evaluated that induced tumors at the same porta1-of-entry site, the lung, by both routes of exposure. Interestingly, the oral route was more potent, although the difference was less than for all tissues combined. The effects of route on potency were examined statistically using a regression tech nique that considers that RRD:? values for both dose routes are subject to statistical error (i.e.. both are independent observations) (Kendall and Stuart. 1979). For rati, the regression describing the relationship is ln(RRD,,,,.) = l.Mdn RRDora)) - 0.302. The 95% confiaence interval on slope is the range 0.33 u 3.3*. The variability of the slope term is influenced by the large oral/inhalation differences obtained for vinyl chloride and asbestos. Omitting the results for these two substances changes the re lationship to ln(RRD,,,h 1.28(ln RRDm,' - 0.866. The 95% confidence inten'al on slope then decreased to a range of 0.35 to 1.7C. Regardless of whether the data for vinyl chloride and asbestos are included, both analyses show that a siope of 1 cannot be ruled out: that is. there is nc statistical busts for discarding the hypothesis that carcinogenic potency, expressed as u function of applied dose, is the same regardless of whether the dose is administered by the oral or inhalation route. OLI 3157 EXPOSURE ROUTE AND CANCER POTENCY Table 4 Geometric Mean Risk Reference Doses for Se bstances administered to Mice" RRD:. RRD0| (mg/da>) Agent Oral Inhalation Oral/inhalation Oral Inhalation Oral/mhalauon Dibromochloropropane 1.2-Dibromoeihane 1.2-Dichloroethane Diuhli'romeihunc 1 !-Dimeihylhydra2ine Ihdraiinc Teirachloroeihylene Tnchloroeihvlenc Vunlidcne chloride 0 3S 0.19 46 49 0 3b 004 44 :i 10 0.26 1.3 78 0.P 0 O'4.8 23 1b 1.3 0.0 lb 0.015 0.1 0 007 0.17 0.6 0.69 3 6 (19 I.J 6.2 2.0 0,018 y 009 07 0.001 0,002 0.9 0.23 0.69 09 0 84 1 9 0 6 0 08 0 09 l.l 0,04 0.2 0.2 2.1 O.b 0.3 0.5 04 " Geometric mean of range of RRDs across all tumor sues. For mice, the regression analysis resulted in the relationship ln(RRD,,,h! = 1.03 ln(RRDorjl) + 0.25. The 95T confidence interval on slope is 0.16 to 4.81. Thus, the relationship between carcinogenic potency of these substances in mice treated orally compared with those treated b> inhalation is very' similar to the relationship derived from rat studies. As was the case for rat studies, the RRD;., values obtained from the mouse studies cannot be used to rule out the hypothesis that exposure route does not influence carcinogenic potency. In addition to RRD;.< \alues. all data sets for each chemical were used with Global 86 to compute the MLE and lower-bound RRD representing a 1% additional risk (designated as RRD(,,). This risk level is below the observable range in bioassays. This calculation was made because some chemicals may be activated through a rate-limiting mechanism causing the cancer response to level out at higher concentrations. This could drive the RRD value to an artificially high level, because of the apparently decreased potency at the high doses. Since the RRD,M is likely to be below metabolically saturating levels, a more accurate estimate of potency may be obtained for such agents. Examination of Tables 2 and 3 shows that, in the majority of cases, the ratio of oral to inhalation RRD values was altered only modestly by calculating a i% additional nsk as compared with 259c. The difference was equal or less than twofold for 15 of the 23 comparisons in mice and rats and equal or less than threefold for 20 of the 23 comparisons. The maximum change ranged from about four- to sixfold for hydrazine and propylene oxide in rats and dichloromethane in mice. Unexpectedly, vinyl chloride, a chemical known to require activation and administered in the inhalation studies at saturating doses, showed little change m the oral/inhalation ratios at 1% compared with 25%. As can be seen in Tables 3 and 4. oral and inhalation RRD values for both mice and rats are listed for seven chemicals, dibromochloropropane. 1.2-dibromoethane. 1.2-dichloroethane. dichloromethane. hydrazine, trichloroethylere. and vinylidene chloride. The geometric mean of oral RRDyc values for these seven chemicals equaled OLI 3158 10 WILLIAM E. PEPELKO TABLE 5 Comparison, op RRDjj, at Identical, Nonportal of Entry Sites* Agent T umor site Oral Inhalation Oral/inhalation Rats Acrylonitnlc Benzene 1.2-Dichlormethane Dichloromclhane Trichloroethylene Vinyl chloride Vinvlidene chlonde Mice 1.2-Dichloroethane Dichloromclhane Tetrachloroethvlene Trichloroethylene Vmylidcnc chloride Zymhal gland Mammarv gland Bnnn. spinal cord Zymhal gland Mammary gland Liver kidney Liver kidney Pancreas Thvrotd Mammary gland Liver Liver Liver Mammary gland 10 0 06 3.3 1008 12 245 1096 49 5.1 2.8 3.9 2.8 37 4.4 21 0 44 2ft 83 V.5 283 67 922 262 89 2334 25 30 7.8 6-3 4.5 32 0.20 04 0.1 0,4 3.6 0.2 03 4.2 0.05 0.002 0.1 01 04 06 1.0 07 * Non-portal-of-cntry sues. i.e.. cicluding the respirators and gastrointestinal tracts. 16 for rais versus 1.4 for mice. The means for ihe inhalation \alues equaled 15.5 for rats versus 2.3 for mice. Thus, the mice are apparently more sensitive to this group ofchemicals than rats. The reason for these results is uncertain. Since mice are smaller, with a greater metabolic rate, it could be predicted that they would respond to a lesser degree to the same dose per milligram body weight than rats. Possible explanations include greater sensitivity of the target organs in mice, more efficient activation for those chemicals requiring activation, and more efficient absorption. In several of the studies with mice, the liver was the primary target organ. Since mice respond to many chemicals by the induction of liver tumors, the liver may well be a sensitive target organ and thus be responsible for the low RRD values. In any case, for this set of chemicals, the use of mouse data will result in greater potency estimates for humans, extrapolating on a mg/kg body wt basis, than if rat data are used. If a body surface area correction is used, the differences in human potency estimates for mouse and rat data will become even greater. DISCUSSION There is probably no way to compare cancer potencies in a simple straightforward manner with a high degree of precision and accuracy. The 25% response rate was selected because it was expected to be in the observable range for most studies, thus not requiring extrapolation. Unfortunately this was not always true. Moreover, the dose-response curve does not always continue in a straight line to 100%. but ma> flatten out at much lower response levels due to saturation of activation pathways, or may even decrease at high dose levels due to acute toxicity. Global 86 produced a OLI 3159 EXPOSURE ROUTE AND CANCER POTENCY 11 warning when the data fit poorly and these data sets were eliminated. Nevertheless, some data sets produced at concentrations known to result in saturation of activation pathways were not eliminated by this warning. Thus it is important to have as much knowledge of metabolism and acute toxicity as possible when attempting potency comparisons. This analy sis of the relationship between carcinogenic potency and route of ad ministration generally demonstrated that the carcinogenic potencies of most of the substances examined were not substantially influenced by dose route. While differences were somewhat greater in rats than mice, data were not available in mice for the two agents showing the greatest differences in rats. Several factors may affect the carcinogenic potency of an agent with route. If the effects occur at a portal of entry, then the target organ will In: different for the gas trointestinal and inhalation routes. Lacking further information, the potential differing sensitivities of these organs can result in an unquantifiable amount of uncertainty if route extrapolation is attempted. As mentioned previously, among those three or four agents inducing respiratory tract tumors via inhalation and stomach tumors orally, little difference in potency was seen. Another important factor is absorption efficiency. Among the organic chemicals compared, vinyl chloride showed the largest route-related difference in RRD;. Al though the literature was not searched for information relating to absorption for most of the agents evaluated, based upon the lack of large differences in potency, it is unlikely that this is a major factor in many instances. In the case of vinyl chloride, there is some evidence that absorption efficiency via the oral route is about twice that by inhalation (Feron el ul,, 1981: Krajewski et ai. 1980) and could thus account for some of the difference in potency for this chemical. Mar.y pollutants, however, are in the form of solid paniculate matter. These include asbestos, manmade mineral fibers, combustion products, and various metal com pounds. When inhaled, a ponion is deposited in the alveolar regions where it can remain lor relatively long periods, allowing for dissolution of relatively insoluble par ticles. and thus rendering them bioavailable. On the other hand, little or no solubili zation may occur during the relatively rapid passage through the gastrointestinal tract. This was seen quite clearly in the case for asbestos. Similarly, a stable estimate of RRD;s could not be obtained for cadmium via the oral route because of the low response. Two other metals, beryllium and nickel, also induced cancer via the inhalation route, but not orally (U.S. EPA, 1986. 1987). Based upon these findings, route ex trapolation for agents in the form of inhaled particulate matter does not appear to be feasible unless data regarding bioavailability by both routes are known. Many organic chemicals require activation before induction of mutational changes leading to cancer. If the rate-limiting step occurs during activation rather than break down. then the carcinogenic response will not be expected to increase linearly with dose at high concentrations. The large oral/inhalation RRD differences for vinyl chlo ride are likely the result of this factor. While the doses used in the oral studies were well below those necessary to saturate activation pathways, many of the inhalation studies used much higher concentrations, some as high as 10.000 ppm or more. To determine if metabolic saturation is a major factor in the large oral/inhalation RRD differences for vinyl chloride, the inhalation data set of Drew et al. (1983) was examined. These researchers exposed female Fischer 344 rats to 100 ppm vinyl chloride 6 hr/day for 24 months. Since the km. or concentration at half-saturation, was reported OLI 3160 I f 12 WILLIAM E. PEPELKO to be 860 ppm for a 6-hr exposure (Gehring et a!.. 1978). the percentage activation should be near 100`S. The geometric mean RRD;f value for all tumor sites reported in this study was only 16.? mg/day. less than one-tenth the value derived as the mean of all inhalation studies, and not much greater than the mean for the oral studies. If a further adjustment is made lor an approximately twofold greater absorption efficiency by the oral route, the inhalation RRD^ value would be little different from the oral value of 5.2. Thus, at exposure levels below saturation of activation pathways, there does not appear to be a true route-related difference in carcinogenic potency for vinyl chloride. Dibromo- and dichloroethane are two other chemicals requiring activation whose pharmacokinetics have been studied (U.S. EPA. 1985). While oral/inhalation RRD^ * differences are much less than those for vinyl chloride, it is likely that if k,,, values were known, adjusting for the degree of activation would result in even better agreement. Hydrazine is the only other chemical with oral/inhalation RRDs differing hv more than 10-fold in rats. There is no apparent pharmacokinetic explanation for this dif ference. especially since route had little effect on potency in mice. Moreover, potency via the inhalation rouie differed to only a small degree in mice and rats. While a large number of oral studies were available for mice, only one was reported using rats (Severi and Biancifiori. 1968). In this study only one exposure level was used and the number of animals assayed was small. 1 ? to 18 per sex. The potential variability w hen only one such experiment is available may well have accounted for much of the apparent difference in potency with route in rats. For the remaining organic compounds, the observed dose-routc-related differences in carcinogenic potency are not substantial. In fact, the potency values derived from different studies involving the same substance and the same dose route generally varied to a greater extent than values for the same substance administered by different routes. As was likely the case for hydrazine, the small differences seen may often be the result of differences in study design or quality. The underlying data for one compound. 1.2dichloroethane. were examined more closely to evaluate the likelihood of such an explanation. This compound was chosen because there appeared to be little variation in the potency estimates derived from studies involving the same route. For 1.2-dichloroethane. there is a threefold difference in the mean potency values for oral and inhalation dose routes: the oral route is more potent. The potency value for the inhalation route derives from a single study in Sprague-Dawlcy rats (Maltom et al.. 1980): in this study there was a high background rate of mammary tumors and a marginal tumorigenic response. Different strains of rats were used in oral bioassays of this compound (NCI. 1978b). and in these studies, the background rates were low . and the tumor response was statistically significant. The difference in response may therefore be a reflection of both differences in background rates and responsiveness with strains. The smaller difference in RRD; with route in mice also suggests the lack of a true route-related difference in potency . It should be recognized, however, that route-related differences in carcinogenic po tency are minimized if only agents testing positively by both routes are considered. An attempt was therefore made to estimate the prevalence of chemicals testing positive by only one route. Two sources of information were reviewed, the EPA's Integrated Risk Information System (IRIS) and the Office of Solid Waste and Emergency Re sponse's reportable quantities documents. Both sources provided short reviews and OLI 3161 EXPOSURE ROUTE AND CANCER POTENCY 13 cancer assessments for a large v ariety of chemicals. For purposes of this review, chem icals that were shown to induce cancer following intratracheal instillation as well as inhalation were considered to be positive by the respirators- route. Positive cancer responses by the oral or respiratory route, not including the ones used for calculation of RRDs. were reported for 120 agents. Unfortunately, adequate bit assay data by both routes were reported for only 13 of the 120. Of these. 10 were positive both routes. These 10 were not used for RRD calculation because either the species differed, intratracheal instillation was used, or the data set was inadequate for quantitation. Another three, nickel subsulfide. cadmium, and beryllium, were pos itive by inhalation, but negative via the oral route. None of those adequately tested by both routes were positive by only the oral route. Thus, including chemicals used for RRD calculation. 26 of 29 adequately tested were positive for cancer by both routes. The only definite exceptions were agents in the form of relatively insoluble paniculate matter. Among pooriv soluble aerosols, even those testing positively by both routes, such as asbestos and cenain cadmium compounds, were more effective via inhalation, as mentioned previously, their greater effectiveness via the inhalation route is probably due to a longer residence time, allowing for greater solubilization. If poorly soluble paniculate matter is excluded, then the likelihood of carrying out a route extrapolation on an agent having widely diffenng cancer potency with route will be decreased. CONCLUSIONS In the absence of cancer bioassav data for either the oral or inhalation route, it was found that extrapolation is less likely to result in large errors in potency estimates if (a) the agent is in vapor, liquid, or relatively soluble solid form: (b) the design and quality of the available studies are good: or (c) the doses used are not great enough to saturate either activation or deactivation pathways. It is also important to determine if (d) absorption efficiency differs greatly with route, (el whether the agent acts systemically or at a por.al of entry, and (f) if there are major tirsi-pass effects. If the above factors can be adjusted for. then large differences in potency with route are much less likeiy to occur. It should be noted, however, that the findings are based upon a limited number of comparisons. Until cancer bioassays by both routes, along with pharma cokinetic studies, have been carried out on a much larger number of chemicals, con siderable uncertainty will continue to exist when extrapolating potency from one route to another. REFERENCES j Anderson. E. L. and the Carcinogen Assessment Group. U'.S Em ironroental Protection Agency (19831 j Quantitative approaches in use to assess cancer nsk. Risk Ana! 3. 27*-29J. ` Beliles. R P.. Paulin, H. J.. Maoris. N G.. and Weir, R. J, |!980i. Three-generation reproductive ! vtudv of rats receiving acrylonitrile in dnnking water, (n Health .iswtmeni Document for .icnlonunle U.S, EPA EPA-600/8-83-007F. Bell. Z. G.. Olson. K.. H.. and Benya, T J, < t7g|, Final report of audit findings of the Manufacturing i Chemists Association Administered trichloroethylene chrome inhalation stud' at Industrial Biotest Labs In Addendum to the Heullh H.i.ve'vmen/ Document lor Tntl.lnroelhvlene: lpouted Curanogenictly . 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