DOCSLIB.ORG

Toward Improved Models for Predicting Bioconcentration of Well-Metabolized Compounds by Rainbow Trout Using Measured Rates of in Vitro Intrinsic Clearance

Total Page：16

File Type：pdf, Size：1020Kb

Download full-text PDF Read full-text
Toward Improved Models for Predicting Bioconcentration of Well-Metabolized Compounds by Rainbow Trout Using Measured Rates of in Vitro Intrinsic Clearance Environmental Toxicology and Chemistry, Vol. 32, No. 7, pp. 1611–1622, 2013 # 2013 SETAC Printed in the USA TOWARD IMPROVED MODELS FOR PREDICTING BIOCONCENTRATION OF WELL-METABOLIZED COMPOUNDS BY RAINBOW TROUT USING MEASURED RATES OF IN VITRO INTRINSIC CLEARANCE JOHN W. NICHOLS,*y DUANE B. HUGGETT,z JON A. ARNOT,xk PATRICK N. FITZSIMMONS,y and CHRISTINA E. COWAN-ELLSBERRY# yUS Environmental Protection Agency, Office of Research and Development, National Health and Environmental Effects Research Laboratory, Mid-Continent Ecology Division, Duluth, Minnesota, USA zDepartment of Biological Sciences, University of North Texas, Denton, Texas, USA xDepartment of Physical & Environmental Sciences, University of Toronto Scarborough, Toronto, Ontario, Canada kArnot Research and Consulting, Toronto, Ontario, Canada #CE2Consulting, Cincinnati, Ohio, USA (Submitted 28 November 2012; Returned for Revision 24 January 2013; Accepted 8 March 2013) Abstract: Models were developed to predict the bioconcentration of well-metabolized chemicals by rainbow trout. The models employ intrinsic clearance data from in vitro studies with liver S9 fractions or isolated hepatocytes to estimate a liver clearance rate, which is extrapolated to a whole-body biotransformation rate constant (kMET). Estimated kMET values are then used as inputs to a mass-balance bioconcentration prediction model. An updated algorithm based on measured binding values in trout is used to predict unbound chemical fractions in blood, while other model parameters are designed to be representative of small fish typically used in whole-animal bioconcentration testing efforts. Overall model behavior was shown to be strongly dependent on the relative hydrophobicity of the test compound and assumed rate of in vitro activity. The results of a restricted sensitivity analysis highlight critical research needs and provide guidance on the use of in vitro biotransformation data in a tiered approach to bioaccumulation assessment. Environ Toxicol Chem 2013;32:1611–1622. # 2013 SETAC Keywords: Bioaccumulation Bioconcentration Biotransformation In vitro–in vivo extrapolation Fish INTRODUCTION methods that do not involve additional whole-animal testing. Biotransformation can strongly impact the extent to which One approach that may satisfy this need involves the use of in hydrophobic organic chemicals accumulate in fish [1–4]. Until vitro metabolizing systems derived from liver tissue. Using recently, however, methods that could be used to predict this procedures developed initially by the pharmaceutical industry, activity were unavailable. Fortunately, this situation is changing. several groups have extrapolated in vitro biotransformation data fi Using a mass-balance modeling approach, Arnot et al. [5,6] for sh to the intact animal and used this information to predict – evaluated measured bioconcentration factors (BCFs) and dietary impacts on chemical accumulation [11 15]. In each case, bioaccumulation data for fish to estimate whole-body rates of incorporating in vitro information into established models of biotransformation for over 600 compounds. This information chemical accumulation substantially improved model perfor- was then used to develop a screening-level quantitative mance, resulting in predicted BCFs that were in better agreement structure–activity relationship (QSAR) model that predicts with measured values than predictions obtained assuming no biotransformation rates based on chemical structure [7]. The biotransformation. “ biotransformation rate QSAR has been integrated with a Collectively, these studies have provided a proof of ” screening-level BCF and bioaccumulation factor (BAF) predic- concept for the use of in vitro biotransformation data in fi tion model [8] and incorporated into the BCFBAF module of bioaccumulation modeling efforts with sh. However, a closer the US Environmental Protection Agency’s (USEPA’s) Estima- examination of these efforts indicates a number of differences in tion Programs Interface Suite software program [9]. Additional assumed extrapolation factors and physiological inputs. Some of fi QSAR approaches based on documented chemical trans- these differences can be attributed to the use of different sh fi fl formations in rats have been developed to estimate the species (trout, carp, and cat sh), while others re ect differences probability that a chemical will undergo biotransformation in in reported values for a particular species (see Table 1 in Cowan- fish and predict likely products of this activity [10]. Ellsberry et al. [13]). In addition, all of these studies have fi – Despite this progress, however, a need remains for methods provided BCF predictions for relatively large sh (trout: 200 fi to directly assess biotransformation of chemicals not adequately 1000 g; carp: 375 g; cat sh: 160 g) containing a substantial covered by existing databases or for which greater certainty in amount of whole-body lipid (10%). While this is understand- the prediction is required. Ideally, this need would be met using able, given that these animals were used as the source of in vitro material (S9 fractions, microsomes, or hepatocytes), most of the BCF testing with fish has been performed using much smaller All Supplemental Data may be found in the online version of this article. animals. Failure to account for differences in fish mass and lipid * Address correspondence to [email protected] content may result in a mismatch between predicted BCFs Published online 15 March 2013 in Wiley Online Library (wileyonlinelibrary.com). and the measured BCFs used to evaluate model accuracy and DOI: 10.1002/etc.2219 performance. 1611 1612 Environ Toxicol Chem 32, 2013 J.W. Nichols et al. Table 1. Independent variable inputs to the S9-bioconcentration (S9-BCF) model Parameter (symbol) Value Units Reference Octanol–water partition coefficient (KOW) Measured or estimated Unitless of test compound Log KOW of test compound From KOW Unitless Body weight of modeled fish (BwgM) Set by investigator; here, assumed to be 10 g Body weight of fish used as source of S9 Measured g protein (BwgS9) S9 protein concentration (CS9) Set by investigator; typically 0.5 to 2.0 mg/mL Reaction rate (Rate) Measured; from substrate depletion assay 1/h Fish holding temperature (T, for BCF testing) Set by investigator; here, assumed to be 15 Celsius Liver S9 protein content (LS9) 163 mg/g liver The present study Liver weight as fraction of whole-body 0.015 Unitless [38] weight (LFBW) Liver blood flow as fraction of cardiac 0.259; includes both arterial and portal blood flows Unitless [29] output (QHFRAC) Fractional water content of blood (nWBL) 0.84 Unitless [57] a Fractional whole-body lipid content (nLWB) Set by investigator; here, assumed to be 0.05 Unitless À6 Particulate organic carbon content (CPOC) 4.6 Â 10 kg/L [39] POC binding constant (aPOC) 0.35 Unitless [41] À6 Dissolved organic carbon content (CDOC) 1.0 Â 10 kg/L [39] DOC affinity constant (aDOC) 0.08 Unitless [40] Total aqueous chemical concentration (CW,TOT) Set by investigator; does not impact BCF calculation mg/L aAlthough fixed by the investigator, this parameter was varied in the sensitivity analysis. POC ¼ particulate organic carbon; DOC ¼ dissolved organic carbon The purpose of this report is to provide updated models for depletion experiments are performed under first-order reaction predicting the bioconcentration of well-metabolized chemicals conditions to characterize the rate of chemical disappearance by rainbow trout. The models incorporate recent advances in our from the system. Measured concentrations of the parent chemical knowledge of key extrapolation factors and chemical partition- are log10-transformed, and a linear regression is performed on the ing relationships and are designed to predict steady-state BCFs transformed values to calculate a first-order elimination rate for a reference fish, defined as a 10-g rainbow trout held at 15 8C constant (1/h), which is related to the regression slope by the that contains 5% whole-body lipid. This definition recognizes expression Rate ¼ –2.3 Slope. that most of the in vivo testing with fish has been performed Rate is divided by the measured concentration of S9 protein 6 using small animals or juveniles of larger species [16] and is (CS9; mg/mL) or hepatocytes (CHEP;10 cells/mL) to calculate consistent with recommendations for testing trout given in in vitro intrinsic clearance (CLIN VITRO,INT; mL/h/mg protein or current guidance [17,18]. The models are flexible, however, and 106 hepatocytes). For reactions that exhibit classical Michaelis- contain algorithms that adjust for user-specified changes in Menten kinetics, CLIN VITRO,INT is equal to the maximum rate of temperature, lipid content, fish mass, and several extrapolation reaction (VMAX; mmole/h/mg protein) divided by the affinity factors. A limited sensitivity analysis was conducted to evaluate constant (KM; mmole/mL), where KM is the substrate concentra- model sensitivity to changes in selected input parameters. The tion resulting in half-maximal activity. Multiplying CLIN VITRO, results of this analysis highlight critical research needs and INT by the S9 content of liver tissue (LS9; mg/g liver) or 6 provide guidance for using these models in a tiered approach to hepatocellularity (LHEP;10 cells/g liver) and liver weight as a bioaccumulation assessment. fraction of total body weight (LFBW; g liver/g fish) yields the in vivo intrinsic clearance (CLIN VIVO,INT; mL/h/g fish), while fi MODEL DESCRIPTION further multiplication by 24 (h/d) provides units of mL/d/g sh (equivalent to L/d/kg fish). Two computational models were developed to predict the A well-stirred liver submodel [20,21] is used to calculate bioconcentration of well-metabolized chemicals by rainbow hepatic clearance (CLH; L/d/kg fish) trout. Both employ a 1-compartment description of the animal ÀÁ and use data obtained from an in vitro test system to estimate ¼ = þ ð Þ CLH QH f U CLIN VIVO; INT QH f U CLIN VIVO; INT 1 a whole-body biotransformation rate constant (kMET). The S9-BCF model uses data derived from liver S9 fractions, while This description accounts for possible rate limitations the HEP-BCF model relies on data from isolated hepatocytes.
Load more

Recommended publications
  • Activated Carbon in Sediment Remediation
    ACTIVATED CARBON IN SEDIMENT REMEDIATION. BENEFITS, RISKS AND PERSPECTIVES Darya KUPRYIANCHYK Thesis committee Promoter Prof. dr. A.A. Koelmans Professor Water and Sediment Quality Co-promoter Dr. ir. J.T.C. Grotenhuis Assistant professor Environmental Technology Other members Prof. dr. R.N.J. Comans, Wageningen University Prof. dr. ir. W.J.G.M. Peijnenburg, RIVM, Leiden University Prof. dr. ir. A.J. Hendriks, Radboud University Nijmegen Dr. ir. M.T.O. Jonker, Utrecht University This research was conducted under the auspices of the Graduate School for Socio-Economic and Natural Sciences of the Environment (SENSE). ACTIVATED CARBON IN SEDIMENT REMEDIATION. BENEFITS, RISKS AND PERSPECTIVES Darya KUPRYIANCHYK Thesis submitted in fulfilment of the requirements for the degree of doctor at Wageningen University by the authority of the Rector Magnificus Prof. dr. M.J. Kropff, in the presence of the Thesis Committee appointed by the Academic Board to be defended in public on Friday 1 February 2013 at 4.00 p.m. in the Aula Darya Kupryianchyk Activated carbon in sediment remediation. Benefits, risks and perspectives 264 pages. Thesis, Wageningen University, Wageningen, The Netherlands (2013) With references and summaries in English and Dutch ISBN 978-94-6173-431-0 To my mother “who told me songs were for the birds, then taught me all the tunes I know and a good deal of the words.” Ken Kesey Contents Chapter 1. General introduction....................................................................................... 9 Chapter 2. In situ remediation of contaminated sediments using carbonaceous materials. A review......................................................................................... 17 Chapter 3. In situ sorption of hydrophobic organic compounds to sediment amended with activated carbon.....................................................................................
    [Show full text]
  • Fish Bioconcentration Data Requirement: Guidance for Selection of Number of Treatment Concentrations
    Document ID No.: EPA 705-G-2020-3708 Fish Bioconcentration Data Requirement: Guidance for Selection of Number of Treatment Concentrations [Supplement to OCSPP Test Guideline 850.1730] July 15, 2020 Disclaimer: The contents of this document do not have the force and effect of law and are not meant to bind the public in any way. This document is intended only to provide clarity to the public regarding existing requirements under the law or agency policies. Office of Pesticide Programs Office of Chemical Safety and Pollution Prevention U.S. Environmental Protection Agency I. Purpose The purpose of this document is to clarify EPA recommendations for the number of treatment concentrations needed to result in acceptable fish bioconcentration factor (BCF) studies for pesticide registration. EPA routinely requires BCF studies to determine whether pesticide active ingredients have the potential to accumulate in fish, enter the food chain, and cause adverse effects in fish-eating predators such as aquatic mammals and birds of prey. In April 2017, EPA was approached by an outside party, the National Centre for the Replacement, Refinement and Reduction of Animals in Research (NC3R), with a suggestion to modify the test guideline for the BCF study to reduce the number of animals used in BCF testing, by reducing the number of concentration levels used from three (two positive doses and one control) to two (one positive level and one control). NC3R stated that this would be “[i]n the interest of international harmonization and reducing unnecessary animal testing” because “[a]t the moment the Japanese and US EPA guideline require that two concentrations are always tested, which is in contrast to the OECD Test Guideline[1]; therefore, many companies are understandably continuing to test two concentrations to ensure acceptance within these regions.” This modification has the potential to reduce the number of fish used by one-third.
    [Show full text]
  • Perfluorooctane Sulfonate (PFOS) and Perfluorooctanoic Acid (PFOA) November 2017 TECHNICAL FACT SHEET – PFOS and PFOA
    Technical Fact Sheet – Perfluorooctane Sulfonate (PFOS) and Perfluorooctanoic Acid (PFOA) November 2017 TECHNICAL FACT SHEET – PFOS and PFOA Introduction At a Glance This fact sheet, developed by the U.S. Environmental Protection Agency Manmade chemicals not (EPA) Federal Facilities Restoration and Reuse Office (FFRRO), provides a naturally found in the summary of two contaminants of emerging concern, perfluorooctane environment. sulfonate (PFOS) and perfluorooctanoic acid (PFOA), including physical and Fluorinated compounds that chemical properties; environmental and health impacts; existing federal and repel oil and water. state guidelines; detection and treatment methods; and additional sources of information. This fact sheet is intended for use by site managers who may Used in a variety of industrial address these chemicals at cleanup sites or in drinking water supplies and and consumer products, such for those in a position to consider whether these chemicals should be added as carpet and clothing to the analytical suite for site investigations. treatments and firefighting foams. PFOS and PFOA are part of a larger group of chemicals called per- and Extremely persistent in the polyfluoroalkyl substances (PFASs). PFASs, which are highly fluorinated environment. aliphatic molecules, have been released to the environment through Known to bioaccumulate in industrial manufacturing and through use and disposal of PFAS-containing humans and wildlife. products (Liu and Mejia Avendano 2013). PFOS and PFOA are the most Readily absorbed after oral widely studied of the PFAS chemicals. PFOS and PFOA are persistent in the exposure. Accumulate environment and resistant to typical environmental degradation processes. primarily in the blood serum, As a result, they are widely distributed across all trophic levels and are found kidney and liver.
    [Show full text]
  • Toxicity and Assessment of Chemical Mixtures
    Toxicity and Assessment of Chemical Mixtures Scientific Committee on Health and Environmental Risks SCHER Scientific Committee on Emerging and Newly Identified Health Risks SCENIHR Scientific Committee on Consumer Safety SCCS Toxicity and Assessment of Chemical Mixtures The SCHER approved this opinion at its 15th plenary of 22 November 2011 The SCENIHR approved this opinion at its 16th plenary of 30 November 2011 The SCCS approved this opinion at its 14th plenary of 14 December 2011 1 Toxicity and Assessment of Chemical Mixtures About the Scientific Committees Three independent non-food Scientific Committees provide the Commission with the scientific advice it needs when preparing policy and proposals relating to consumer safety, public health and the environment. The Committees also draw the Commission's attention to the new or emerging problems which may pose an actual or potential threat. They are: the Scientific Committee on Consumer Safety (SCCS), the Scientific Committee on Health and Environmental Risks (SCHER) and the Scientific Committee on Emerging and Newly Identified Health Risks (SCENIHR) and are made up of external experts. In addition, the Commission relies upon the work of the European Food Safety Authority (EFSA), the European Medicines Agency (EMA), the European Centre for Disease prevention and Control (ECDC) and the European Chemicals Agency (ECHA). SCCS The Committee shall provide opinions on questions concerning all types of health and safety risks (notably chemical, biological, mechanical and other physical risks) of non- food consumer products (for example: cosmetic products and their ingredients, toys, textiles, clothing, personal care and household products such as detergents, etc.) and services (for example: tattooing, artificial sun tanning, etc.).
    [Show full text]
  • Toxicological Profile for Zinc
    TOXICOLOGICAL PROFILE FOR ZINC U.S. DEPARTMENT OF HEALTH AND HUMAN SERVICES Public Health Service Agency for Toxic Substances and Disease Registry August 2005 ZINC ii DISCLAIMER The use of company or product name(s) is for identification only and does not imply endorsement by the Agency for Toxic Substances and Disease Registry. ZINC iii UPDATE STATEMENT A Toxicological Profile for Zinc, Draft for Public Comment was released in September 2003. This edition supersedes any previously released draft or final profile. Toxicological profiles are revised and republished as necessary. For information regarding the update status of previously released profiles, contact ATSDR at: Agency for Toxic Substances and Disease Registry Division of Toxicology/Toxicology Information Branch 1600 Clifton Road NE Mailstop F-32 Atlanta, Georgia 30333 ZINC vi *Legislative Background The toxicological profiles are developed in response to the Superfund Amendments and Reauthorization Act (SARA) of 1986 (Public law 99-499) which amended the Comprehensive Environmental Response, Compensation, and Liability Act of 1980 (CERCLA or Superfund). This public law directed ATSDR to prepare toxicological profiles for hazardous substances most commonly found at facilities on the CERCLA National Priorities List and that pose the most significant potential threat to human health, as determined by ATSDR and the EPA. The availability of the revised priority list of 275 hazardous substances was announced in the Federal Register on November 17, 1997 (62 FR 61332). For prior versions of the list of substances, see Federal Register notices dated April 29, 1996 (61 FR 18744); April 17, 1987 (52 FR 12866); October 20, 1988 (53 FR 41280); October 26, 1989 (54 FR 43619); October 17, 1990 (55 FR 42067); October 17, 1991 (56 FR 52166); October 28, 1992 (57 FR 48801); and February 28, 1994 (59 FR 9486).
    [Show full text]
  • Acrylamide Mammography Cohort, the Netherlands Study on Diet and Can- Cer, a Cohort of Swedish Men, the U.S
    Report on Carcinogens, Fourteenth Edition For Table of Contents, see home page: http://ntp.niehs.nih.gov/go/roc Acrylamide Mammography Cohort, the Netherlands Study on Diet and Can- cer, a cohort of Swedish men, the U.S. Nurses’ Health Study, and the CAS No. 79-06-1 Danish Diet, Cancer, and Health Study. In addition, several case- control studies (most of which used food-frequency questionnaires) Reasonably anticipated to be a human carcinogen assessed cancer and dietary exposure of Swedish, French, and U.S. First listed in the Sixth Annual Report on Carcinogens (1991) populations to acrylamide. The tissue site studied most frequently Also known as 2-propenamide was the breast. These studies found no overall association between breast cancer and dietary exposure to acrylamide; however, some, H C NH2 but not all, studies reported an association between acrylamide ex- H2C C posure and a specific type of breast cancer (sex-hormone-receptor- O positive cancer in post-menopausal women). The Danish study used Carcinogenicity acrylamide-hemoglobin adducts to assess exposure; however, these adducts are not source-specific, but reflect both dietary exposure Acrylamide is reasonably anticipated to be a human carcinogen based and exposure from other sources, such as smoking. Two of three pro- on sufficient evidence of carcinogenicity from studies in experimen- spective cohort studies reported increased risks of endometrial and tal animals. ovarian cancer, but a case-control study found no increased risk of ovarian cancer. Most of the studies evaluating prostate and colorectal Cancer Studies in Experimental Animals cancer did not find increased risks associated with dietary exposure Acrylamide caused tumors in two rodent species, at several different to acrylamide.
    [Show full text]
  • Bioconcentration, Bioaccumulation, and the Biomagnification in Puget
    Jason E. Hall Bioconcentration, Bioaccumulation, and Biomagnification in Puget Sound Biota: Assessing the Ecological Risk of Chemical Contaminants in Puget Sound The following piece is republished from the UWT Journal on the Environment, an electronic, peer-reviewed journal designed to provide students with a forum in which to publish and read primary and secondary research, reports on conferences and events, and ideas and opinions in the environmental sciences and studies. Tahoma West encourages submissions that deal with scientific and social matters. Note: For the tables referred to in this article please see Journal of the Environment: <http://courses. washington. edu/uwtjoe/>. Introduction: Puget Sound has a large urban and rural human population, which currently exceeds 3 million, and many industrialized ports and shorelines that provide numerous sources of non-point and point source pollution to Puget Sound (Konasewich et al. 1982). Hundreds of poten­ tia lly toxic chemicals are present in Puget Sound sediments (Matins et al. 1982, NOAA and WSDE 2000, Konasewich et al. 1982, and Lefkovitz et al. J 997). As of 1982, J 83 organic compounds had been identified in Puget Sound sediments, biota, and water (Konasewicb et al. 1982). Although chemical contaminants and heavy metals are present in sedi­ ments throughout Puget Sound, these pollutants are generally greatest in number and concentration within the sediments and embayments that are adjacent to the most populated and industrialized areas, such as Elliot Bay, Commencement Bay, and Sinclair Illlet (Malins et al. 1982, Lefkovitz et aJ. 1997, Konasewich et al. 1982, and NOAA and WSDE 2000). However, the distribution and concentrations of chemical contami­ nants and heavy metals in Puget Sound generally reflect their source.
    [Show full text]
  • Toxicological Profile for Phenol
    TOXICOLOGICAL PROFILE FOR PHENOL U.S. DEPARTMENT OF HEALTH AND HUMAN SERVICES Public Health Service Agency for Toxic Substances and Disease Registry September 2008 PHENOL ii DISCLAIMER The use of company or product name(s) is for identification only and does not imply endorsement by the Agency for Toxic Substances and Disease Registry. PHENOL iii UPDATE STATEMENT A Toxicological Profile for Phenol, Draft for Public Comment was released in October 2006. This edition supersedes any previously released draft or final profile. Toxicological profiles are revised and republished as necessary. For information regarding the update status of previously released profiles, contact ATSDR at: Agency for Toxic Substances and Disease Registry Division of Toxicology and Environmental Medicine/Applied Toxicology Branch 1600 Clifton Road NE Mailstop F-32 Atlanta, Georgia 30333 PHENOL iv This page is intentionally blank. PHENOL v FOREWORD This toxicological profile is prepared in accordance with guidelines developed by the Agency for Toxic Substances and Disease Registry (ATSDR) and the Environmental Protection Agency (EPA). The original guidelines were published in the Federal Register on April 17, 1987. Each profile will be revised and republished as necessary. The ATSDR toxicological profile succinctly characterizes the toxicologic and adverse health effects information for the hazardous substance described therein. Each peer-reviewed profile identifies and reviews the key literature that describes a hazardous substance’s toxicologic properties. Other pertinent literature is also presented, but is described in less detail than the key studies. The profile is not intended to be an exhaustive document; however, more comprehensive sources of specialty information are referenced. The focus of the profiles is on health and toxicologic information; therefore, each toxicological profile begins with a public health statement that describes, in nontechnical language, a substance’s relevant toxicological properties.
    [Show full text]
  • Bioaccumulation, Biodistribution, Toxicology and Biomonitoring of Organofluorine Compounds in Aquatic Organisms
    International Journal of Molecular Sciences Review Bioaccumulation, Biodistribution, Toxicology and Biomonitoring of Organofluorine Compounds in Aquatic Organisms Dario Savoca and Andrea Pace * Dipartimento di Scienze e Tecnologie Biologiche, Chimiche e Farmaceutiche (STEBICEF), Università Degli Studi di Palermo, 90100 Palermo, Italy; [email protected] * Correspondence: [email protected]; Tel.: +39-091-23897543 Abstract: This review is a survey of recent advances in studies concerning the impact of poly- and perfluorinated organic compounds in aquatic organisms. After a brief introduction on poly- and perfluorinated compounds (PFCs) features, an overview of recent monitoring studies is reported illustrating ranges of recorded concentrations in water, sediments, and species. Besides presenting general concepts defining bioaccumulative potential and its indicators, the biodistribution of PFCs is described taking in consideration different tissues/organs of the investigated species as well as differences between studies in the wild or under controlled laboratory conditions. The potential use of species as bioindicators for biomonitoring studies are discussed and data are summarized in a table reporting the number of monitored PFCs and their total concentration as a function of investigated species. Moreover, biomolecular effects on taxonomically different species are illustrated. In the final paragraph, main findings have been summarized and possible solutions to environmental threats posed by PFCs in the aquatic environment are discussed.
    [Show full text]
  • The Effect of Ph on the Bioconcentration and Toxicity of Weak Organic Electrolytes
    Downloaded from orbit.dtu.dk on: Sep 23, 2021 The effect of pH on the bioconcentration and toxicity of weak organic electrolytes Rendal, Cecilie Publication date: 2013 Document Version Publisher's PDF, also known as Version of record Link back to DTU Orbit Citation (APA): Rendal, C. (2013). The effect of pH on the bioconcentration and toxicity of weak organic electrolytes. DTU Environment. General rights Copyright and moral rights for the publications made accessible in the public portal are retained by the authors and/or other copyright owners and it is a condition of accessing publications that users recognise and abide by the legal requirements associated with these rights. Users may download and print one copy of any publication from the public portal for the purpose of private study or research. You may not further distribute the material or use it for any profit-making activity or commercial gain You may freely distribute the URL identifying the publication in the public portal If you believe that this document breaches copyright please contact us providing details, and we will remove access to the work immediately and investigate your claim. The effect of pH on the bioconcentration and toxicity of weak organic electrolytes Cecilie Rendal PhD Thesis February 2013 The effect of pH on the bioconcentration and toxicity of weak organic electrolytes Cecilie Rendal PhD Thesis February 2013 DTU Environment Department of Environmental Engineering Technical University of Denmark Cecilie Rendal The effect of pH on the bioconcentration and toxicity of weak organic electrolytes PhD Thesis, February 2013 The synopsis part of this thesis is available as a pdf-file for download from the DTU research database ORBIT: http://www.orbit.dtu.dk Address: DTU Environment Department of Environmental Engineering Technical University of Denmark Miljoevej, building 113 2800 Kgs.
    [Show full text]
  • Toxicological Profile for Wood Creosote, Coal Tar Creosote, Coal Tar, Coal Tar Pitch, and Coal Tar Pitch Volatiles
    TOXICOLOGICAL PROFILE FOR WOOD CREOSOTE, COAL TAR CREOSOTE, COAL TAR, COAL TAR PITCH, AND COAL TAR PITCH VOLATILES U.S. DEPARTMENT OF HEALTH AND HUMAN SERVICES Public Health Service Agency for Toxic Substances and Disease Registry September 2002 CREOSOTE ii DISCLAIMER The use of company or product name(s) is for identification only and does not imply endorsement by the Agency for Toxic Substances and Disease Registry. CREOSOTE iii UPDATE STATEMENT Toxicological profiles are revised and republished as necessary, but no less than once every three years. For information regarding the update status of previously released profiles, contact ATSDR at: Agency for Toxic Substances and Disease Registry Division of Toxicology/Toxicology Information Branch 1600 Clifton Road NE, E-29 Atlanta, Georgia 30333 V FOREWORD This toxicological profile is prepared in accordance with guidelines" developed by the Agency for Toxic Substances and Disease Registry (ATSDR) and the Environmental Protection Agency (EPA). The original guidelines were published in the Federal Register on April 17, 1987. Each profile will be revised and republished as necessary. The ATSDR toxicological profile succinctly characterizes the toxicologic and adverse health effects information for the hazardous substance described therein. Each peer-reviewed profile identifies and reviews the key literature that describes a hazardous substance's toxicologic properties. Other pertinent literature is also presented, but is described in less detail than the key studies. The profile is not intended to be an exhaustive document; however, more comprehensive sources of specialty information are referenced. The focus of the profiles is on health and toxicologic information; therefore, each toxicological profile begins with a public health statement that describes, in nontechnical language, a substance's relevant toxicological properties.
    [Show full text]
  • Aquatic Pesticides Monitoring Program Literature Review
    SAN FRANCISCO ESTUARY INSTITUTE AQUATIC PESTICIDES MONITORING PROGRAM Aquatic Pesticides Monitoring Program Literature Review Geoff Siemering, Nicole David, Jennifer Hayworth and Amy Franz San Francisco Estuary Institute, Oakland, California Karl Malamud-Roam Contra Costa Mosquito Vector Control CONTRIBUTION NO. 71 APRIL 2003 REVISED FEB 2005 Contact Information San Francisco Estuary Institute 7770 Pardee Lane, 2nd Floor Oakland, CA 94621 Phone: 510-746-SFEI Website: www.sfei.org Contra Costa Mosquito Vector Control District 155 Mason Circle Concord, CA 94520 Phone: 925-685-9301 Website: www.ccmvcd.dst.ca.us/index.html This report should be cited as: Siemering, Geoff, N. David, J. Hayworth, A. Franz and K. Malamud-Roam. October 2003. Revised, February 2005. Aquatics Pesticides Monitoring Program Literature Review. SFEI Contribution 71. San Francisco Estuary Institute, Oakland, CA. San Francisco Estuary Institute Contents Executive Summary ......................................................................................................................................................9 Section I. Evaluation of Health and Environmental Risks Associated with Pesticides and other Chemicals in the Environment ..............................................................................................................................................10 A. Chemical Identification and Characterization ....................................................................................................11 I. Chemical Description and Type .............................................................................................................11
    [Show full text]