Canadian Environmental Protection Act, 1999 federal environmental quality guidelines Triclosan
Environment and Climate Change Canada
Federal Environmental Quality Guidelines (FEQGs) provide benchmarks for the quality of the ambient environment. They are based solely on the toxicological effects or hazard of specific substances or groups of substances. FEQGs serve three functions: first they can be an aid to prevent pollution by providing targets for acceptable environmental quality; second they can assist in evaluating the significance of concentrations of chemical substances currently found in the environment (monitoring of water, sediment and biological tissue); and third, they can serve as performance measures of the success of risk management activities. The use of FEQGs is voluntary unless prescribed in permits or other regulatory tools. Thus FEQGs, which apply to the ambient environment are not effluent limits or “never-to-be-exceeded” values but may be used to derive effluent limits. The development of FEQGs is the responsibility of the Federal Minister of Environment under the Canadian Environmental Protection Act, 1999 (CEPA) (Government of Canada (GC) 1999). The intent is to develop FEQGs as an adjunct to risk assessment/risk management of priority chemicals identified in the Chemicals Management Plan (CMP) or other federal initiatives. This factsheet describes the Federal Water Quality Guideline (FWQG) for the protection of aquatic life from adverse effects of triclosan (Table 1). This fact sheet is based largely on the assessment report published under Canada’s Chemicals Management Plan, and was revised following public comment. The toxicity data are current to April 2017 (Environment and Climate Change Canada, Health Canada (ECCC, HC) 2016). No FEQGs have been developed for the sediment and biological tissue compartments at this time.
FEQGs are similar to Canadian Council of Ministers of the Environment (CCME) guidelines in that they are benchmarks for the quality of the ambient environment and are based solely on toxicological effects data. Where data permit, FEQGs are derived following CCME methods. FEQGs are developed where there is a federal need for a guideline (e.g. to support federal risk management or monitoring activities) but where the CCME guidelines for the substance have not yet been developed or are not reasonably expected to be updated in the near future.
|Guideline value (µg/L)||Lower 95th percent confidence interval (µg/L)||Upper 95th percent confidence interval (µg/L)|
2. Substance identity
Triclosan (C12H7Cl3O2; CAS Registry Number 3380-34-5) is a chlorinated aromatic compound with phenol and ether functional groups. There are no known natural sources of triclosan and its presence in the environment is exclusively due to anthropogenic activity. Triclosan can be released to the environment as a result of its use in many products used by consumers, or as a result of the industrial manufacture or formulation of products containing triclosan. Triclosan released into municipal wastewater reaches wastewater treatment plants (WWTPs) where it is partly removed from the wastewater, depending on the type of treatment, and then released into surface water as part of WWTP effluents (ECCC, HC 2016).
Government of Canada (ECCC, HC 2016) concluded that triclosan meets the criteria under section 64(a) of CEPA as it is entering or may enter the environment in a quantity or concentration or under conditions that have or may have an immediate or long-term harmful effect on the environment or its biological diversity. Triclosan did not meet the criteria under sections 64(b) and 64(c), as it is not entering the environment in a quantity or concentration or under conditions that constitute or may constitute a danger to the environment on which life depends, and it is not entering the environment in a quantity or concentration or under conditions that constitute or may constitute a danger in Canada to human life or health.
Triclosan is used in cosmetics, drugs and natural health products (ECCC, HC 2016). There were 482 cosmetic products containing triclosan notified to Health Canada, including skin cleansers (body, face and hands), moisturizers, face and eye makeup, deodorant sticks/sprays, fragrances, tanning products, shaving preparations, bath products, exfoliants, massage products, styling products and shampoos (ECCC, HC 2016). Approximately 130 drug products containing triclosan with an assigned drug identification number were listed on Health Canada’s Drug Product Database (DPD 2015). There are 14 licensed natural health products (e.g., toothpaste, foot gel, acne treatment, body spray, skin cleanser and lotion) that contain triclosan as a non-medicinal ingredient (NHPID 2015).
A survey conducted in 2013 on the manufacture, import, use and release of triclosan for the year 2011 indicated that triclosan was not manufactured in Canada and that between 10 000 and 100 000 kg of triclosan was imported by twenty-nine companies in Canada in 2011 as either the pure substance or in product and five companies exported 100 to 1000 kg of triclosan in manufactured products (EC 2013). Twenty companies reported using triclosan to manufacture formulated products. The formulated products containing triclosan included over-the-counter drugs, cosmetic and cleaning products such as antibacterial soap, skin cleansers, toothpastes, make-up, deodorants, skin creams, fragrances, general all-purpose cleaners and general purpose detergents. Of the total quantity of triclosan used in Canada, 88% was used in antibacterial soaps, skin cleansers and toothpaste (registered as drugs, cosmetics or natural health products); 6% used for other reported product types; and for the remaining 6% the end uses were not identified (EC 2013).
Triclosan was also registered in Canada as an active ingredient in pest control products, for use as material preservative in textiles, plastic, paper, leather and rubber materials. However, as of December 31, 2014, triclosan is no longer registered as a pest control product due to its voluntary withdrawal from the market by the Canadian registrants.
4. Fate, behaviour and partitioning
Triclosan can be released to the environment as a result of consumer use and down-the-drain disposal of products containing triclosan, or as a result of the industrial manufacture of products containing triclosan. The continual nature of triclosan releases results in its ubiquitous presence in the environment. Triclosan is released to aquatic ecosystems as part of waste water treatment plant (WWTP) effluents; however, some triclosan partitions to biosolids during the wastewater treatment process. As a result, triclosan can also reach terrestrial ecosystems by way of biosolids amendment to agricultural land. Triclosan can reach surface water from soil from runoff if there is an immediate rainfall following the application of either liquid or dewatered wastewater biosolids on soil (Topp et al. 2008; Sabourin et al. 2009).
Triclosan is a hydrophobic compound with a high log Kow of 4.8 at pH 6.7 (ECHA 2007-2014) and moderate log Koc (3.34 to 4.67). Triclosan has a pKa of 8.1; consequently, it will ionize to some extent in most natural water bodies. A low Henry’s law constant (5.05 x 10-4 Pa∙m3/mol) indicates that triclosan does not volatilize from the water surface. Triclosan is susceptible to phototransformation in surface waters (ECCC, HC 2016). Tixier et al. (2002) observed that pH has an impact on its ability to absorb sunlight and that the direct phototransformation rate increases with pH. In aerobic sediments, triclosan is susceptible to rapid oxidation (half-life <21 hr) by manganese oxides (Zhang and Huang 2003). Triclosan is not persistent in soil (half-life 2.9 to 58 days in aerobic soil). Its log Koc value suggests that it is not mobile in soil, especially if the organic carbon content is high, and it is not expected to volatilize from soil (ECCC, HC 2016).
Triclosan is available for uptake by organisms and can also be readily metabolized by organisms. Triclosan is unlikely to biomagnify in aquatic and terrestrial food webs, primarily because it can be metabolised by organisms. Bioconcentration factors (BCFs) for triclosan range from low to high in two fish species (16–19 L/kg for common carp (NITE 2006) and 2018–8700 L/kg for zebrafish (Böttcher 1991; Schettgen et al. 1999; Schettgen 2000; Gonzalo-Lumbreras et al. 2012)), whereas a moderate BCF (1700 L/kg) was reported for mussels (Gatidou et al. 2010). Triclosan bioaccumulation factors (BAFs) reported for snail (500 L/kg) and algae (900-2100 L/kg) were low to moderate (Coogan et al. 2007; Coogan and La Point 2008). It was determined that triclosan has a sufficient bioconcentration potential to result in internal body burdens that exceed narcotic or polar narcotic thresholds of toxicity (ECCC, HC 2016), that is, even low to moderate levels of bioconcentration of triclosan may cause adverse effects in aquatic organisms.
The assessment of triclosan (ECCC, HC 2016) determined that it does not meet the persistence criteria as set out in the Persistence and Bioaccumulation Regulations of CEPA (Government of Canada (GC) 2000), however, it is continuously present in the environment. Similarly, triclosan accumulates in organisms to levels that can cause adverse effects (ECCC, HC 2016), it does not meet the bioaccumulation criteria as set out in the Persistence and Bioaccumulation Regulations of CEPA (GC 2000).
5. Measured concentrations
The main source of release of triclosan to aquatic ecosystems is via effluents from WWTPs. In Canada, concentrations of triclosan measured in effluents ranged from 12 to 4,160 ng/L between 2002 and 2013 (ECCC, HC 2016). Triclosan concentrations were measured in surface waters of Canada for all provinces and territories, except Prince Edward Island, from 2002 to 2013 and also for certain locations for 2014. Reported concentrations ranged from below the method detection limit of 4-42 ng/L to 874 ng/L and the highest median concentration was 139 ng/L. The available surface sediment monitoring data (2012-2013) from the Pacific and Atlantic regions, Lake Erie and St. Lawrence River ranged from <1 to 47 ng/g (ECCC unpublished data). No triclosan monitoring data are available for soils in Canada (ECCC, HC 2016). No air monitoring data are available for triclosan and given its short half-life in air (0.66 day), triclosan is not likely to be subject to long-range transport.
6. Mode of action
Triclosan inhibits the enzyme enoyl-acyl carrier protein (ACP) reductase involved in type II bacterial fatty acid synthesis (McMurry et al. 1998; Heath et al. 1999; Hoang and Schweizer 1999; Levy et al. 1999). Enoyl-ACP reductase is also shown to be a possible target for triclosan with the brassicacea Arabidopsis (rockcress) (Serrano et al. 2007). Activation of peroxisome proliferators-activated receptor alpha (PPARα) is the primary mode of action for triclosan-induced hepatocarcinogenesis in mouse (ECCC, HC 2016). In addition, the molecular structure of triclosan resembles that of several non-steroidal estrogens, such as diethylstilbestrol and bisphenol A, in that it contains two phenol functional groups. Triclosan has been shown to have endocrine disruption effects in amphibians at environmentally-realistic concentrations (Veldhoen et al. 2006). Endocrine disruption effects were also noted in fish and mammals, however these effects occurred at very high concentrations that may not be environmentally relevant.
7. Federal water quality guideline derivation
Federal Water Quality Guidelines (FWQGs) are preferably developed using CCME (2007) protocols. In the case of triclosan sufficient chronic toxicity data were available to meet the minimum data requirements for a CCME Type A guideline Footnote 1 . No CCME water quality guideline for triclosan exists for the protection of aquatic life. The FWQG developed here identifies a benchmark for aquatic ecosystems that is intended to protect all forms of freshwater aquatic life for indefinite exposure periods.
The aquatic toxicity dataset compiled by ECCC (ECCC, HC 2016) was further updated and evaluated for developing the FWQG. In summary, the long-term freshwater toxicity endpoints for four fish, three amphibian, five invertebrate and eight plant species met the CCME protocol (2007) requirements and were used to deriving the FWQG for triclosan (Table 2). In general, plants tended to be more sensitive to triclosan than invertebrates or fish, although both the most sensitive and the least sensitive species in the dataset were algae (Table 2). The Pacific tree frog (Pseudacris regilla) was the second most sensitive species in the data set. Among invertebrates, snail (Physa acuta) was most sensitive and the least sensitive species was a crustacean, Ceriodaphnia dubia. Of the four reported values for fish, oriental weatherfish (Misgurnus anguillicaudatus) was the most sensitive whereas the Japanese medaka (Oryzias latipes) was the least sensitive fish.
|Table 2. Chronic freshwater aquatic toxicity data considered for developing FWQG for triclosan.|
Each species for which appropriate toxicity data were available (Table 2) was ranked according to sensitivity and its position on the species sensitivity distribution (SSD) was determined (Figure 1). Several cumulative distribution functions (normal, logistic, extreme value and Gumbel) were fit to the data using regression methods and the model fit was assessed using statistical and graphical techniques. The best model based on goodness of fit was the log-normal model; the 5th percentile of the SSD plot is 0.47 µg/L, with lower and upper confidence limits of 0.34 and 0.65 µg/L, respectively.
The 5th percentile calculated from the SSD (0.47 µg/L) is selected as the FWQG. The guideline represents the concentration below which one would expect either no, or only a low likelihood of adverse effects on aquatic life. In addition to this guideline, two other concentration ranges are provided for use in risk management (Figure 1). At concentrations between >5th and 50th percentile of the SSD (>0.47-13 µg/L), there is a moderate likelihood of adverse effects to aquatic life. Concentrations greater than the 50th percentile (>13 µg/L) have a higher likelihood of causing adverse effects. Risk managers may find these additional concentration ranges useful in defining short-term or interim risk management objectives for a phased risk management plans. The moderate to higher concentration ranges may also be used in setting less protective interim targets for waters that are already highly degraded or where there are socio-economic considerations that preclude the ability to meet the FWQG.
Böttcher, J. 1991. Report on the bioaccumulation test of FAT-80’023/Q. Test No. G 069 09: Ciba-Geigy Ltd., D&C Product Ecology, FC 6.13. 26 p.
Brown, J., M.J. Bernot and R. Bernot. 2012. The influence of TCS on the growth and behavior of the freshwater snail, Physa acuta. J. Environ. Sci. Health 47: 1626-1630.
[CCME] Canadian Council of Ministers of the Environment. 2007. A Protocol for the Derivation of Water Quality Guidelines for the Protection of Aquatic Life. In: Canadian Environmental Quality Guidelines, 1999, Canadian Council of Ministers of the Environment, Winnipeg.
Ciniglia, C., C. Cascone, R. Giudice, G. Pinto and A. Pollio A. 2005. Application of methods for assessing the geno- and cytotoxicity of triclosan to C. ehrenbergii. J. Hazard Mater 122: 227-232.
Coogan, M.A. and T.W. La Point. 2008. Snail bioaccumulation of triclocarban, triclosan, and methyl-triclosan in a North Texas, USA, stream affected by wastewater treatment plant runoff. Environ. Toxicol. Chem. 27: 1788–1793.
Coogan, M.A., R.E. Edziyie, T.W. La Point and B.J. Venables. 2007. Algal bioaccumulation of triclocarban, triclosan, and methyl-triclosan in a North Texas wastewater treatment plant receiving stream. Chemosphere 67: 1911–1918.
[DPD] Drug Product Database. 2014. Ottawa (ON): Health Canada.
Dussault, E.B., V.K. Balakrishnan, E. Sverko, K.R. Solomon and P.K. Sibley. 2008. Toxicity of human pharmaceuticals and personal care products to benthic invertebrates. Environ. Toxicol. Chem. 27: 425-432.
[EC] Environment Canada. 2013. Data for triclosan collected under Canadian Environmental Protection Act, 1999, Section 71: Notice with respect to triclosan (5-chloro-2-(2,4-dichlorophenoxy)phenol). Data prepared by: Environment Canada, Existing Substances Program.
[ECCC, HC] Environment and Climate Change Canada, Health Canada. 2016. Assessment report: triclosan. Gatineau (QC).
[ECHA] European Chemicals Agency. c2007-2014. Registered Substances database. Search results for CAS RN [3380-34-5]. Helsinki (FI): ECHA.
Franz, S., R. Altenburger, H. Heilmeier and M. Schmitt-Jansen M. 2008. What contributes to the sensitivity of microalgae to triclosan? Aquatic Toxicol. 90: 102–108.
Fort, D. J., Mathis, M. B., Pawlowski, S., Wolf, J. C., Peter, R., and Champ, S. 2017. Effect of triclosan on anuran development and growth in a larval amphibian growth and development assay. J. Appl. Toxicol.
Fulton, B.A., R.A. Brain, S. Usenko, J.A. Back, R.S. King and B.W. Brooks. 2009. Influence of nitrogen and phosophorous concentrations and ratios on Lemna gibba growth responses to triclosan in laboratory and field experiments. Environ. Toxicol. Chem. 28: 2610-2621.
Gatidou, G., E. Vassalou and N.S. Thomaidis. 2010. Bioconcentration of selected endocrine disrupting compounds in the Mediterranean mussel, Mytilus galloprovincialis. Mar. Pollut. Bull. 60: 2111-2116.
Gonzalo-Lumbreras, R., J. Sanz-Landaluze, J. Guinea and C. Cámara. 2012. Miniaturized extraction methods of triclosan from aqueous and fish roe samples. Bioconcentration studies in zebrafish larvae (Danio rerio). 2012. Anal. Bioanal. Chem. 403: 927-937.
[GC] Government of Canada. 1999. Canadian Environmental Protection Act, 1999. S.C., 1999, c. 33, Canada Gazette. Part III, vol. 22, no. 3.
[GC] Government of Canada. 2000. Canadian Environmental Protection Act, 1999: Persistence and Bioaccumulation Regulations, P.C. 2000-348, 29 March, 2000, SOR/2000-107.
Heath R.J., J.R. Rubin, D.R. Holland, E. Zhang, M.E. Snow and C.O. Rock. 1999. Mechanism of triclosan inhibition of bacterial fatty acid synthesis. Journal of Biological Chemistry 16: 11110-11114.
Hoang T.T. and H.P. Schweizer. 1999. Characterization of Pseudomonas aeruginosa enoyl-acyl carrier protein reductase (Fab I): a target for the antimicrobial triclosan and its role in acylated homoserine lactone synthesis. Journal of Bacteriology 181: 5489-5497.
Ishibashi, H., N. Matsumura, M. Hirano, M. Matsuoka, H. Shiratsuchi, Y. Ishibashi, Y. Takao and K. Arizono. 2004. Effects of triclosan on the early life stages and reproduction of medaka Oryzias latipes and induction of hepatic vitellogenin. Aquat. Toxicol. 67: 167–179.
Levy, C.W., A. Roujeinikova, S. Sedelnikova, P.J. Baker, A.R. Stuitje, A.R. Slabas, D.W. Rice and J.B. Rafferty. 1999. Molecular basis of triclosan activity. Nature 398: 383-384.
Marlatt, V.L., N. Veldhoen, B.P. Lo, D. Bakker, V. Rehaume, K. Vallee, M. Haberl, D. Shang, G.C. van Aggelen, R.C. Skirrow, J.R. Elphick and C.C. Helbing. 2013. Triclosan exposure alters postembryonic development in a Pacific tree frog (Pseudacris regilla) amphibian metamorphosis assay (TREEMA). Aquat. Toxicol. 126: 85–94.
McMurry, L.M., M. Oethinger and S.B. Levy. 1998. Triclosan targets lipid synthesis. Nature 394: 531.
[NHPID] Natural Health Products Ingredients Database. 2015. Ottawa (ON): Health Canada.
[NITE] National Institute of Technology and Evaluation. 2006. Japan chemicals collaborative knowledge database (J-CHECK) [Internet]. Tokyo (JP): Ministry of Health, Labour and Welfare, Ministry of the Environment and National Institute of Technology and Evaluation.
Orvos, D.R., D.J. Versteeg, J. Inauen, M. Capdevielle, A. Rothenstein and V. Cunningham. 2002. Aquatic toxicity of triclosan. Environ. Toxicol. Chem. 21: 1338-1349.
Raut, S.A. and R.A. Angus. 2010. Triclosan has endocrine-disrupting effects in male western mosquitofish, Gambusia affinis. Environ. Toxicol. Chem. 29: 1287-1291.
Roberts, J., O. Price, N. Bettles, C. Rendal and R. van Egmond. 2014. Accounting for dissociation and photolysis: a review of the algal toxicity of triclosan. Environ. Toxicol. Chem. 33: 2551–2559
Sabourin, L., A. Beck, P.W. Duenk, S. Kleywegt, D.R. Lapen, H. Li, C.D. Metcalfe, M. Payne and E. Topp. 2009. Runoff of pharmaceuticals and personal care products following application of dewatered municipal biosolids to an agricultural field. Sci. Total Environ. 407: 4596–4604.
Schettgen, C. 2000. Bioakkumulation von Triclosan bei verschiedenen pH-Werten des Wassers und der Pyrethroide Cyfluthrin, Cypermethrin, Deltamethrin und Permethrin. Dissertation Universität Oldenburg.
Schettgen, C., A. Schmidt and W. Butte. 1999. Variation of accumulation and clearance of the predioxin 5-chloro-2-(2,4-dichlorophenoxy)-phenol (Iragsan DP 300, triclosan) with the pH of water. Organohalogen Compounds 43: 49-52.
Serrano, M., S. Robatzek, M. Torres, E. Kombrink, I.E. Somssich, M. Robinson and P. Schulze-Lefert. 2007. Chemical interference of pathogen-associated molecular pattern-triggered immune responses in Arabidopsis reveals a potential role for fatty-acid synthase type II complex-derived lipid signals. Journal of Biological Chemistry 282: 6803-6811.
Study Submission 2013. Unpublished confidential studies submitted to Environment Canada under the Chemicals Management Plan initiative. Gatineau (QC): Environment Canada, Program Development and Engagement Division
Tatarazako, N., H. Ishibashi, K. Teshima, K. Kishi and K. Arizono. 2004. Effects of triclosan on various organisms. Environmental Sciences 11: 133-140.
Tixier, C., H.P. Singer, S. Canonica and S.R. Muller. 2002. Phototransformation of triclosan in surface waters: a relevant elimination process for this widely used biocide-laboratory studies, field measurements, and modeling. Environ. Sci. & Tech. 36: 3482-3489.
Topp, E., S.C. Monteiro, A. Beck, B.B. Coelho, A.B.A. Boxall, P.W. Duenk, S. leywegt, D.R. Lapen, M. Payne, L. Sabourin, H. Lee and C.D. Metcalfe. 2008. Runoff of pharmaceuticals and personal care products following application of biosolids to an agricultural field. Sci. Total. Environ. 396: 52–59.
Veldhoen, N., R.C. Skirrow, H. Osachoff, H. Wigmore, D.J. Clapson, M.P. Gunderson, G. van Aggelen and C.C. Helbing. 2006. The bactericidal agent triclosan modulates thyroid hormone–associated gene expression and disrupts postembryonic anuran development. Aquat. Toxicol. 80: 217–227.
Wang, X.; Liu, Z.; Yan, Z.; Zhang, C.; Wang, W.; Zhou, J.; Pei, S. Development of aquatic life criteria for triclosan and comparison of the sensitivity between native and non-native species. Journal of Hazardous Materials 2013, 260, 1017-1022.
Zhang, H. and C.H. Huang. 2003. Oxidative transformation of triclosan and chlorophene by manganese oxides. Environ. Sci. Technol. 37: 2421–2430.
List of acronyms and abbreviations
Bioaccumulation Factor: the ratio of the concentration of a chemical compound in an organism relative to the concentration in the exposure medium, based on uptake from the surrounding medium and food
Bioconcentration Factor: the ratio of the concentration of a chemical compound in an organism relative to the concentration of the compound in the exposure medium (e.g. soil or water)
Canadian Council of Ministers of the Environment
Canadian Environmental Protection Act
Chemicals Management Plan
Drug Product Database
European Chemical Agency
Federal Environmental Quality Guidelines
Federal Water Quality Guideline
Maximum Acceptable Toxicant Concentration
National Institute of Technology and Evaluation
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No Observed Effect Concentration
Predicted No Effect Concentration
Species Sensitivity Distribution
Waste Water Treatment Plant
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