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Issues in Risk Assessment (1993)
Commission on Life Sciences (CLS)

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. "ANNEX E: CORRELATION BETWEEN TD50S FOR RATS AND MICE." Issues in Risk Assessment. Washington, DC: The National Academies Press, 1993.

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Issues in Risk Assessment

the sample size n are shown in Table 1. (Note that the values of h1 and h2 are implicit functions of n.) These results are based on a one-stage model (k = 1) with a spontaneous response rate p0 = 0.10, and a nominal significance level of γ = 0.05 with r = 10 in the case n = 50. The value of σ2 = V(logeMTD) = 8.196 is based on the variance of the MTD of the 191 experiments considered previously by Krewski et al. (1990b). Using common logarithms, V(log10MTD) = 1.546.

The dependency of the correlations between log10TD50 and logeMTD on the Weilbull shape parameter k is illustrated in Table 2 for a sample size of n = 50. These results, including the limiting cases as k → 0 or ∞, are also based on (D.13). Note that the correlation remains high regardless of the value of k.

Annex E: Correlation Between TD50s For Rats and Mice

In this annex, we derive analytical expressions for the correlation between TD50 values for rats and mice. Letting Yrats and Ymice denote the logarithms (basee) of the estimated TD50s for rats and mice, we seek an expression for ρ = Corr(Yrats, Ymice). Following Bernstein et al. (1985) we assume initially that the MTD for rats is directly proportional to that for mice, with

Using the notation of annex D, we will denote the logarithms of the MTDs for rats and mice by Xrats and Xmice, so that

Note that (E.2) implies that V(Xrats) = V(Xmice) = σ2

As in annex D, we assume that the TD50s for rats and mice are uniformly distributed about their respective MTDs. From (D.10), we may then write

Page
169
Front Matter (R1-R18)
Executive Summary (1-2)
USE OF THE MAXIMUM TOLERATED DOSE IN ANIMAL BIOASSAYS FOR CARCINOGENICITY (3-8)
THE TWO-STAGE MODEL OF CARCINOGENESIS (9-9)
A PARADIGM FOR ECOLOGIC RISK ASSESSMENT (10-12)
Issues In Risk Assessment Use Of Maximum Tolerated Dose in Animal Bioassays for Carcinogenicity (13-14)
BACKGROUND (15-17)
SCOPE OF REPORT (18-20)
DEFINITIONS AND BACKGROUND (21-23)
CORRELATIONS (24-32)
RELATIONSHIP BETWEEN TOXICITY AND CARCINOGENICITY OBSERVED AT MTD (33-42)
QUALITATIVE INFORMATION (43-48)
QUANTITATIVE INFORMATION (49-52)
OPTION 1 (53-53)
OPTION 2 (54-54)
OPTION 3 (55-56)
Option 4A (57-58)
Option 4B (59-60)
5 Conclusions and Recommendations (61-66)
REFERENCES (67-78)
BACKGROUND (79-79)
DEFINING AND DETERMINING THE MTD (80-90)
Appendix B Organizing Subcommittee (91-92)
Appendix C Federal Liaison Group (93-94)
Appendix D Workshop Program (95-96)
Appendix E Workshop Attendees (97-110)
1. INTRODUCTION (111-112)
2.1 Measures of Carcinogenic Potency (113-115)
2.2 Carcinogenic Potency Database (CPDB) (116-116)
2.3 Variation in Carcinogen Potency (117-118)
2.4 Classification of Carcinogens (119-120)
3.1 Empirical Correlations (121-124)
3.2 Range of Possible TD50 Values (125-125)
3.3 Analytical Correlations (126-127)
3.4 Model Dependency (128-129)
3.5 Genotoxic vs. Nongenotoxic Carcinogens (130-130)
4.1 Predictions Based on the MDT (131-131)
4.2 Predictions Based on Mutagenicity and Acute Toxicity (132-134)
5.1 Correlation Between Upper Bounds On the Low Dose Slope and MTD (135-135)
5.2 Correlation Between q1* and the TD50 (136-138)
5.3. Preliminary Estimate of Risk (139-139)
6. INTERSPECIES EXTRAPOLATION (140-140)
6.1 Extrapolation from Rats to Mice (141-143)
6.2 Extrapolation from Rodents to Humans (144-145)
7. CONCLUSIONS (146-148)
8. ACKNOWLEDGEMENTS (149-149)
9. REFERENCES (150-159)
ANNEX A: MAXIMUM LIKELIHOOD METHODS FOR FITTING THE WEIBULL MODEL (160-161)
ANNEX B. SHRINKAGE ESTIMATORS OF THE DISTRIBUTION OF CARCINOGENIC POTENCY (162-163)
ANNEX C: ADJUSTMENT OF POTENCY VALUES FOR LESS THAN LIFETIME EXPOSURE (164-165)
ANNEX D: CORRELATION BETWEEN TD50 AND MTD (166-168)
ANNEX E: CORRELATION BETWEEN TD50S FOR RATS AND MICE (169-172)
Appendix G Informal Search for ''Supercarcinogens" (173-174)
CRITERIA AND CANDIDATE CHEMICALS (175-176)
DATA (177-180)
RESULTS (181-181)
DISCUSSION (182-184)
Issues in Risk Assessment The Two-Stage Model Of Carcinogenesis (185-186)
INTRODUCTION (187-187)
BIOLOGIC CONSIDERATIONS (188-189)
THE TWO-STAGE MODEL (190-195)
APPLICATIONS OF THE TWO-STAGE MODEL TO ANIMAL DATA (196-211)
Data Needs (212-212)
Criteria for Adoption (213-213)
Prospects (214-214)
CONCLUSIONS AND RECOMMENDATIONS (215-216)
REFERENCES (217-222)
BIOLOGICAL FACTORS IN TWO-STAGE MODELS (223-225)
TWO-STAGE MODEL OF CLONAL EXPANSION (226-227)
APPLICATION OF THE TWO-STAGE MODEL TO ANIMAL DATA (228-232)
Appendix B Workshop Program (233-234)
Appendix C Workshop Federal Liaison Group (235-236)
TOPIC GROUP MEMBERS (237-238)
Appendix E Workshop Organizing Task Group (239-240)
Isuees In Risk Assessment A Paradigm for Ecological Risk Assessment (241-242)
1 Introduction (243-246)
2 Scope of Ecological Risk Assessment (247-248)
COMPONENTS OF THE 1983 FRAMEWORK (249-250)
CONSISTENCY OF CASE STUDIES WITH THE 1983 FRAMEWORK (251-253)
INTEGRATION OF ECOLOGICAL RISK INTO THE 1983 FRAMEWORK (254-254)
DEFINITION OF FRAMEWORK COMPONENTS FOR ECOLOGICAL RISK ASSESSMENT (255-258)
EXTRAPOLATION ACROSS SCALES (259-260)
QUANTIFICATION OF UNCERTAINTY (261-261)
VALIDATION OF PREDICTIVE TOOLS (262-262)
VALUATION (263-264)
5 Conclusions (265-266)
6 Recommendations (267-268)
REFERENCES (269-272)
Appendix A Workshop Participants (273-278)
Appendix B Workshop Organizing Subcommittee and Federal Liaison Group (279-280)
Appendix C Workshop Introduction (281-282)
TERRY F. YOSIE BUILDING ECOLOGICAL RISK ASSESSMENT AS A POLICY TOOL (283-285)
D. WARNER NORTH: RELATIONSHIP OF WORKSHOP TO NRC'S 1983 RED BOOK REPORT (286-288)
MICHAEL SLIMAK: U.S. ENVIRONMENTAL PROTECTION AGENCY ACTIVITIES IN ECOLOGICAL RISK ASSESSMENT (289-292)
CASE STUDY 1: TRIBUTYLTIN RISK MANAGEMENT IN THE UNITED STATES (293-293)
Discussion (294-294)
CASE STUDY 2: ECOLOGICAL RISK ASSESSMENT FOR TERRESTRIAL WILDLIFE EXPOSED TO AGRICULTURAL CHEMICALS (295-296)
CASE STUDY 3A: MODELS OF TOXIC CHEMICALS IN THE GREAT LAKES: STRUCTURE, APPLICATIONS, AND UNCERTAINTY ANALYSIS (297-298)
CASE STUDY 3B: ECOLOGICAL RISK ASSESSMENT OF TCDD AND TCDF (299-299)
Discussion (300-300)
CASE STUDY 4: RISK ASSESSMENT METHODS IN ANIMAL POPULATIONS: THE NORTHERN SPOTTED OWL AS AN EXAMPLE (301-301)
Discussion (302-302)
CASE STUDY 5: ECOLOGICAL BENEFITS AND RISKS ASSOCIATED WITH THE INTRODUCTION OF EXOTIC SPECIES FOR BIOLOGICAL CONTROL OF A... (303-303)
Discussion (304-304)
CASE STUDY 1: UNCERTAINTY AND RISK IN AN EXPLOITED ECOSYSTEM: A CASE STUDY OF GEORGES BANK (305-306)
Discussion (307-308)
Generic Issues (309-309)
Analysis of Case Studies (310-310)
DOSE-RESPONSE ASSESSMENT (311-311)
Selection of End Points (312-312)
Consideration of Nonlinearities And Discontinuities (313-313)
Understanding the Stressor (314-314)
Additions to the 1983 Paradigm Needed for Ecological Risk Assessment (315-315)
Modeling Needs for Stress-Response Relationships (316-316)
Methods of Measuring Stressors for Ecological Exposure Assessment (317-317)
Definition of Risk Characterization (318-318)
Components of Risk Characterization (319-319)
Organization and Presentation (320-320)
Differences from and Similarities To the 1983 Report (321-321)
Application to the Case Studies (322-323)
Agricultural Chemicals (324-324)
Northern Spotted Owl (325-325)
General Discussion: Models and Risk Assessment (326-326)
Uncertainties Identified In the Case Studies (327-327)
Implications of Uncertainty for Ecological Risk Assessment (328-328)
VALUATION (329-330)
Risk Assessment Has Many Uses (331-332)
Different Risk Assessment Methods Are Suited to Different Risk Assessment Needs (333-333)
Risk Assessors and Risk Managers Need to Communicate (334-334)
Credibility is Crucial (335-336)
Appendix G Contemplations on Ecological Risk Assessment (337-342)
Appendix H Workshop Summary (343-346)
Appendix I References for Appendixes (347-350)
Appendix J Workshop Program (351-356)

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OCR for page 169
Issues in Risk Assessment the sample size n are shown in Table 1. (Note that the values of h1 and h2 are implicit functions of n.) These results are based on a one-stage model (k = 1) with a spontaneous response rate p0 = 0.10, and a nominal significance level of γ = 0.05 with r = 10 in the case n = 50. The value of σ2 = V(logeMTD) = 8.196 is based on the variance of the MTD of the 191 experiments considered previously by Krewski et al. (1990b). Using common logarithms, V(log10MTD) = 1.546. The dependency of the correlations between log10TD50 and logeMTD on the Weilbull shape parameter k is illustrated in Table 2 for a sample size of n = 50. These results, including the limiting cases as k → 0 or ∞, are also based on (D.13). Note that the correlation remains high regardless of the value of k. Annex E: Correlation Between TD50s For Rats and Mice In this annex, we derive analytical expressions for the correlation between TD50 values for rats and mice. Letting Yrats and Ymice denote the logarithms (basee) of the estimated TD50s for rats and mice, we seek an expression for ρ = Corr(Yrats, Ymice). Following Bernstein et al. (1985) we assume initially that the MTD for rats is directly proportional to that for mice, with Using the notation of annex D, we will denote the logarithms of the MTDs for rats and mice by Xrats and Xmice, so that Note that (E.2) implies that V(Xrats) = V(Xmice) = σ2 As in annex D, we assume that the TD50s for rats and mice are uniformly distributed about their respective MTDs. From (D.10), we may then write

OCR for page 170
Issues in Risk Assessment where h1 and h2 are the same for rats and mice since g1 and g2 defined in (D.4) and (D.5) respectively are the same for rats and mice. Assuming that Yrats and Ymice are conditionally independent, given MTDmice (and hence MTDrats from (D.1)), we have Hence where ρ = Corr(Yrats, Xrats) is given in (D.13) of annex D. Based on the n = 127 compounds from the CPDB considered in section 6.1, we find σ2rats = 10.065 ≈ σ2mice = 8.873. For σ2 = 10, we have ρ = 0.943. The assumption (D.1) of strict proportionality between MTDrats and MTDmice can be relaxed. Let V(Xrats) = σ2rats and V(Xmice) = σ2mice . As in (D.3), we have and Assuming Yrats and Ymice are conditionally independent, given Xrats and Xmice, we have and hence

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Issues in Risk Assessment For the n = 127 compounds considered in section 6.1, we estimate Cov (Xrats, Xmice) = 7.638, and ρ = 0.763

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