lewisite and phenarsazine-chloride

Sea dumping of chemical warfare (CW) took place worldwide during the 20th century. Submerged CW included metal bombs and casings that have been exposed for 50-100 years of corrosion and are now known to be leaking. Therefore, the arsenic-based chemical warfare agents (CWAs), pose a potential threat to the marine ecosystems. The aim of this research was to support a need for real-data measurements for accurate risk assessments and categorization of threats originating from submerged CWAs. This has been achieved by providing a broad insight into arsenic-based CWAs acute toxicity in aquatic ecosystems. Standard tests were performed to provide a solid foundation for acute aquatic toxicity threshold estimations of CWA: Lewisite, Adamsite, Clark I, phenyldichloroarsine (PDCA), CWA-related compounds: TPA, arsenic trichloride and four arsenic-based CWA degradation products. Despite their low solubility, during the 48 h exposure, all CWA caused highly negative effects on Daphnia magna. PDCA was very toxic with 48 h D. magna LC50 at 0.36 μg × L

Topics: Animals; Arsenic; Arsenicals; Chemical Warfare Agents; Chlorides; Daphnia; Ecosystem; Lethal Dose 50; Limit of Detection; Seawater; Toxicity Tests, Acute; Water Pollutants, Chemical

The four arsenic-containing chemical warfare agents (CWA) Adamsite (technical, 10-chloro-9-10-dihydrophenarsazine), Clark 1 (Diphenyl arsine chloride), Clark 2 (Diphenyl arsine cyanide), and Lewisite (2-chloro-ethenyl dichloro arsine) were evaluated toxicologically using an in vitro and an in vivo model. The CWA were tested in vitro, using human leucocytes, in order to evaluate their effects on cell proliferation and cell cycle kinetics assayed by flow cytometry. The concentration for total inhibition of cell proliferation for the CWAs ranged from 0.3 micrograms/mL (Lewisite) to 15 micrograms/mL (Clark 1). The results showed no differences in cell proliferation between the different stages of the S-phase either at no-effect or at effect concentrations when samples treated with the CWAs were compared with untreated controls. As2O5 was used as a reference, and the arsenic concentration required for total inhibition of the cell proliferation was 1.7 mg/mL. A lower arsenic concentration, 0.83 micrograms/mL, showed a decreasing proliferation ration in the different parts of the S-phase with Searly and Slate having the highest and lowest ratios, respectively. In addition, there was a positive correlation between the unlabeled S-phase cell ratio and the arsenic concentration, indicating cessation of DNA-synthesis. Conclusively, the examined CWAs exerts a toxicity more potent than arsenic, with respect to cell proliferation. This might indicate that the toxicity of these arsenic-containing CWAs only to a minor extent can be explained by their arsenic content. Because of their relatively good water solubility and ability to easily degrade to arsenic acid, organo-arsenics, e.g., Lewisite, pose less of an environmental threat than organo-arsenics that are sparingly soluble and chemically persistent, like Adamsite. The four CWAs were also tested in vivo in a dietary exposure study, using juvenile three-spined stickleback (Gasterosteus aculeatus L.) as test organism, with measurement of EROD-activity and studies of liver morphology. The results from the in vivo study indicated small effects, suggesting that a 10-week period of dietary exposure at tested dose levels (1 and 100 ng/ml) affects juvenile three-spined stickleback only to a minor extent.

Topics: Animals; Arsenic Poisoning; Arsenicals; Cell Cycle; Cell Division; Chemical Warfare Agents; Cytochrome P-450 CYP1A1; Cytochrome P-450 Enzyme System; DNA; Female; Fishes; Flow Cytometry; Food Contamination; Humans; Leukocytes; Liver; Molecular Weight; Oxidoreductases