Investigating the Incidence of Type I Errors for Chronic Whole Effluent Toxicity Testing Using Ceriodaphnia Dubia

Moore, Timothy F.; Canton, Steven P.; Grimes, Max

doi:10.1897/1551-5028(2000)019<0118:itioti>2.3.co;2

Cited by 5 publications

(6 citation statements)

References 4 publications

(4 reference statements)

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“…Although very few investigations have been conducted to evaluate the accuracy in predicting the absence of toxicants, some analyses using results from control organisms suggest that biological variability is one possible cause of high false positive rates (Dhaliwall et al, 1995). A previous study on chronic toxicity with the microcrustacean Ceriodaphnia dubia indicated a high proportion (6 out of 17 labs) of toxic blank samples (Moore et al, 2000). Robidoux et al (2001), in an intercalibration study to validate an ecotoxicological procedure to monitor septic sludge using…”

Section: Resultsmentioning

confidence: 99%

Overview of results from the WaterTox intercalibration and environmental testing phase II program: Part 1, statistical analysis of blind sample testing

Ronco

Gagnon

Diaz-Baez

et al. 2002

Environmental Toxicology

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There is an urgent need to evaluate the presence of toxicants in waters used for human consumption and to develop strategies to reduce and prevent their contamination. The International Development Research Centre undertook an intercalibration project to develop and validate a battery of bioassays for toxicity testing of water samples. The project was carried out in two phases by research institutions from eight countries that formed the WaterTox network. Results for the first phase were reported in the special September 2000 issue of Environmental Toxicology. Phase II involved toxicity screening tests of environmental and blind samples (chemical solutions of unknown composition to participating laboratories) using the following battery: Daphnia magna, Hydra attenuata, seed root inhibition with Lactuca sativa, and Selenastrum capricornutum. This battery was also used to assess potential toxicity in concentrated (10x) water samples. Results are presented for a set of six blind samples sent to the participating laboratories over a 1-year period. Analyses were performed for each bioassay to evaluate variations among laboratories of responses to negative controls, violations of test quality control criteria, false positive responses induced by sample concentration, and variability within and between labs of responses to toxic samples. Analyses of the data from all bioassays and labs provided comparisons of false positive rates (based on blind negative samples), test sensitivities to a metal or organic toxicant, and interlaboratory test variability. Results indicate that the battery was reliable in detecting toxicity when present. However, some false positives were identified with a concentrated soft-water sample and with the Lactuca and Hydra (sublethal end-point) tests. Probabilities of detecting false positives for individual and combined toxic responses of the four bioassays are presented. Overall, interlaboratory comparisons indicate a good reliability of the battery.

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Section: Resultsmentioning

confidence: 99%

Overview of results from the WaterTox intercalibration and environmental testing phase II program: Part 1, statistical analysis of blind sample testing

Ronco

Gagnon

Diaz-Baez

et al. 2002

Environmental Toxicology

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“…The power parameter "p" was chosen using cross-validation, that is, by minimizing the associated predicted residual sum of squares (PRESS) over a grid of powers (SAS Institute, 1990).…”

Section: Statistical Analysis Of the Lc 50 Datamentioning

confidence: 99%

“…However, the interpretation of results are often complicated by variability associated with WET tests. In particular, the problems associated with false positive results (Type I errors) and "unacceptable results" due to both inter-and intra-laboratory variability are possible and have not been sufficiently addressed (Dhaliwal et al, 1995;Warren-Hicks et al, 1999;Moore et al, 2000).…”

Section: Introductionmentioning

confidence: 99%

The Effects of Age on Pimephales Promelas Survival in Acute Whole Effluent Toxicity Tests

Zmuda¹,

Yamanaka²,

Sawyer³

et al. 2001

proc water environ fed

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The effects of age on P. promelas survival in acute whole effluent toxicity (WET) tests were studied. Definitive 48-hour, static, non-renewal WET tests were conducted at a constant temperature of 25°C using hard synthetic fresh water as the dilution and control water with organisms 1 to 2, 3 to 4, 6 to 7, 11 to 12, and 13 to 14-days of age using the reference toxicants potassium chloride (KCl), sodium dodecyl sulfate (SDS), and a mixture of KCl and SDS. Standard analysis of variance (ANOVA) indicated, 1) that the mortality rates of 1 to 2-day old fish exposed to either of the toxicants KCl or SDS are significantly lower than the mortality rates of fish of 3 to 14-days of age exposed to these toxicants (p < 0.05), and 2) that there are no statistically significant differences in the mortality rates of, 1 to 2, 3 to 4, 7 to 8, 11 to 12, or 13 to 14-day age groups of fish exposed to the KCl plus SDS toxicant combination. Mean LC 50 values for 1 to 2-day age groups of fish exposed to the toxicants KCl, SDS, and the KCl plus SDS combination were all numerically higher than the mean LC 50 values for 3 to 4, 7 to 8, 11 to 12, or 13 to 14-day age groups of fish exposed to these toxicants. Standard ANOVA indicated that these differences were not statistically significant. More sophisticated statistical analyses using a cross validation scheme based on a regression model indicated that LC 50 values for 1 to 2-day age groups of fish exposed to either of the toxicants KCl or SDS were statistically higher than the LC 50 values for 3 to 14-day age groups of fish exposed to these toxicants. Power analysis also indicated that the data set may be too small to identify statistically significant differences in the LC 50 values across the different age groups of fish used in this study using only standard ANOVA. Average coefficients of variation (CVs) for tests conducted with 1 to 14-day old fish were numerically greater than CVs for tests conducted with 3 to 14-day old fish for the toxicants KCl, SDS, and the KCl plus SDS combination. These results suggest that LC 50 data generated using the 1 to 2-day old fish are more variable than the LC 50 data generated using 3 to 14-day old fish. The results of this study are consistent with those reported by Markle et al. (2000), who concluded that the age of organisms used for testing needs to be selected and/or specified to the laboratory conducting the bioassay in order to ensure uniform sensitivity and maximize precision. The results of this study indicate that fish age as a cause of inter-and intra-laboratory variability has not been sufficiently addressed by the USEPA in the publication of standard methods for conducting WET tests with P. promelas.

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“…Although numerous publications have discussed sources of laboratory and method variability associated with WET biological endpoints (e.g., Warren‐Hicks and Parkhurst ; Burton et al ; Chapman et al ; Warren‐Hicks et al ), few studies have explored false‐positive and ‐negative rates of WET endpoints used in regulatory compliance. Furthermore, the few that have made the attempt used very small sample sizes (Diamond et al ) or WET tests using methods that have since been refined (Moore et al ); moreover, laboratory performance has improved since these other studies were conducted (Denton et al ).…”

Section: Introductionmentioning

confidence: 99%

Comparison of false‐positive rates of 2 hypothesis‐test approaches in relation to laboratory toxicity test performance

Fox

Denton

Diamond

et al. 2019

Enviro Toxic and Chemistry

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We compared 2 statistical hypothesis‐test approaches (no‐observed‐effect concentration [NOEC] and test of significant toxicity [TST]) to determine the influence of laboratory test performance on the false‐positive error rate using the US Environmental Protection Agency's Ceriodaphnia dubia reproduction whole‐effluent toxicity (WET) test endpoint. Simulation and power calculations were used to determine error rates based on observed control coefficients of variation (CV) for 8 laboratories over a range of effect levels. Average C. dubia control reproduction among laboratories was 20 to 40 offspring per female, and the 75th percentile CV was 0.10 to 0.31, reflecting a range in laboratory performance. The 2 approaches behave similarly for CVs of 0.2 to 0.3. At effects <10%, as CV decreases, TST is less likely to declare toxicity and NOEC is more likely to do so. Laboratory performance affects whether a sample is declared toxic and influences the probability of false‐positive (and −negative) error rates using either approach. At the 75th percentile control CV observed for each laboratory, 4 laboratories would achieve approximately a 5% false‐positive rate using 13 or fewer replicates for this test method. For the remaining 4 laboratories, more replicates would be needed to achieve a 5% false‐positive rate. The present analyses demonstrate how false‐positive rates are influenced by laboratory performance and WET test design. Environ Toxicol Chem 2019;38:511–523. Published 2019 Wiley Periodicals Inc. on behalf of SETAC. This article is a US government work and, as such, is in the public domain in the United States of America.

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Investigating the Incidence of Type I Errors for Chronic Whole Effluent Toxicity Testing Using Ceriodaphnia Dubia

Cited by 5 publications

References 4 publications

Overview of results from the WaterTox intercalibration and environmental testing phase II program: Part 1, statistical analysis of blind sample testing

Overview of results from the WaterTox intercalibration and environmental testing phase II program: Part 1, statistical analysis of blind sample testing

The Effects of Age on Pimephales Promelas Survival in Acute Whole Effluent Toxicity Tests

Comparison of false‐positive rates of 2 hypothesis‐test approaches in relation to laboratory toxicity test performance

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