Draft screening assessment certain Organic Flame Retardants Substance Grouping 1,3,5-Triazine-2,4,6-triamine (Melamine)

Chemical Abstracts Service Registry Number 108-78-1

Environment and Climate Change Canada

Health Canada

October 2016

Synopsis

Pursuant to section 74 of the Canadian Environmental Protection Act, 1999 (CEPA), the Ministers of the Environment and Climate Change and of Health have conducted a screening assessment of 1,3,5-triazine-2,4,6-triamine (CAS RN 108-78-1), commonly known as melamine, a substance included in the Certain Organic Flame Retardants (OFR) Substance Grouping under Canada's Chemicals Management Plan, which includes ten organic substances having a similar function: application to materials to slow the ignition and spread of fire. Melamine was identified in the categorization of the Domestic Substances List (DSL) under subsection 73(1) of CEPA as meeting criteria for greatest potential for exposure of individuals in Canada. The substance also met categorization criteria for persistence, but not for bioaccumulation or inherent toxicity to non-human organisms.

Melamine does not occur naturally in the environment. It is not manufactured in Canada; however, imports of melamine, as a pure substance or blended into products, in the range of 10 to 100 million kg were reported for the year 2011. In Canada, melamine has numerous industrial applications; its predominant use is in the manufacture of polyurethane foams and melamine-based resins for application in laminates, plastics, paints and coatings. Globally, melamine is used primarily in the synthesis of melamine–formaldehyde resins for similar applications, and in adhesives and moulding compounds. Due to its high nitrogen content, melamine has also been used globally as a fertilizer. In Canada, sources of exposure to melamine are primarily from waste streams or effluents of manufacturing of melamine-based resins, and to a lesser degree from processing plants using melamine to manufacture products with flame retardant properties. Discharges to the environment can be direct or via municipal waste water treatment systems.

Melamine is a compact and stable molecule characterized by high water solubility, negligible vapour pressure, and low to negligible organic carbon-water and octanol-water partition coefficients. Monitoring of melamine in environmental media has not been conducted in Canada. When released to the environment, melamine is expected to predominantly reside in water and, to a lesser degree, in soil, depending on the compartment of release.

Melamine does not degrade rapidly in the environment; it has a long half-life in air, and has relatively slow biodegradation rates in water and soil. Melamine has a limited potential to bioaccumulate in tissues of organisms. It has very low bioconcentration factors in fish, and residue clearance rates from numerous organisms including mammals, fish and birds are known to be fast.

Based on empirical evidence from short- and long-term studies, melamine has a low toxicity to aquatic and soildwelling organisms. As the toxic effects of melamine exposure were more pronounced in long-term studies and those encompassing sensitive life stages, results from these types of studies were generally more informative. In contrast, in the multiple short-term studies, the toxicity limit for melamine could not be defined since the highest concentration tested showed no effects.

It is expected that melamine may be released to the Canadian environment as a result of industrial processing activities. Although melamine can be found in consumer or commercial products, it is expected that release to the environment via this route is minimal. Industrial scenarios, where melamine is released to water, were developed to provide estimates of exposure. Risk quotient analyses, integrating conservative estimates of exposure with toxicity information, were performed for the aquatic compartment. These analyses showed that melamine risk to organisms and the broader integrity of environment in Canada is unlikely.

Considering all available lines of evidence presented in this screening assessment, there is low risk of harm to organisms or to the broader integrity of the environment from melamine. It is proposed to conclude that melamine does not meet the criteria under paragraphs 64(a) or (b) of CEPA as it is not entering 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 and that constitute or may constitute a danger to the environment on which life depends.

The main sources of exposure to melamine for the general population in Canada are expected to be from environmental media (water, soil), food and from the use of consumer products. Biomonitoring data were also available from relevant populations (U.S.).

Based principally on the weight of evidence assessments of international agencies and available information, critical effects associated with exposure to melamine are carcinogenicity and effects on the urinary system. Available information indicates that melamine is not genotoxic. Comparison of levels between critical effects in animal studies and estimates of exposure from environmental media or consumer products were considered adequate to address uncertainties in the health effects and exposure databases.

On the basis of the adequacy of the margins between estimates of exposure and critical effect levels in experimental animals, it is proposed to conclude that melamine does not meet the criteria under paragraph 64(c) of CEPA as 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.

Overall proposed conclusion

It is proposed to conclude that melamine does not meet any of the criteria set out in section 64 of CEPA.

1. Introduction

Pursuant to sections 68 and 74 of the Canadian Environmental Protection Act, 1999(CEPA) (Canada 1999), the Minister of the Environment and Climate Change and the Minister of Health conduct screening assessments of substances to determine whether these substances present or may present a risk to the environment or to human health.

The Substance Groupings Initiative is a key element of the Government of Canada's Chemicals Management Plan (CMP). The Certain Organic Flame Retardants (OFR) Substance Grouping consists of ten substances identified as priorities for assessment as they meet the categorization criteria under section 73 CEPA, and/or were considered as a priority based on ecological and/or human health concerns (Environment and Climate Change Canada and Health Canada 2007). All of these substances have a similar function: the application to materials to slow the ignition and spread of fire. Also, these substances are potential alternatives for substances currently subject to controls or considered for controls in Canada and internationally.

This draft screening assessment concerns substance 1,3,5-triazine-2,4,6-triamine, commonly known as melamine. Melamine was identified in the categorization of the Domestic Substances List (DSL) under subsection 73(1) of CEPA as meeting criteria for greatest potential for exposure of individuals in Canada. The substance also met categorization criteria for persistence, but not for bioaccumulation or inherent toxicity to non-human organisms. In addition to its use as a flame retardant, melamine has numerous other (non-flame retardant) applications.

Screening assessments focus on information critical to determining whether substances within a grouping meet the criteria as set out in section 64 of CEPA, by examining scientific information to develop conclusions by incorporating a weight of evidence approach and precaution^{Footnote 1}.

This draft screening assessment includes consideration of information on chemical properties, environmental fate, hazards, uses and exposure, including additional information submitted by stakeholders. Relevant data were identified up to March 2014 for both ecological and human health components. However, a cursory search was conducted to include any salient literature up to June 2015. Empirical data from key studies, as well as some results from models were used to reach proposed conclusions. When available and relevant, information presented in assessments from other jurisdictions was considered.

The draft screening assessment does not represent an exhaustive or critical review of all available data. Rather, it presents the most critical studies and lines of evidence pertinent to the proposed conclusion.

This draft screening assessment was prepared by staff in the Existing Substances Programs at Health Canada and Environment and Climate Change Canada and incorporates input from other programs within these departments. The ecological and human health portions of this assessment have undergone external written peer review and/or consultation. Comments on the technical portions relevant to the environment were received from Dr. John Arnot of Arnot Research and Consulting, Dr. Laurence Deydier of the European Chemicals Agency (ECHA), and Dr. Miriam Diamond of the University of Toronto. Comments on the technical portions relevant to human health were received from Dr. Lynne Haber of Toxicology Excellence for Risk Assessment, Dr. Paul Rumsby of the U.S. National Centre for Environmental Toxicology and Dr. Pam Williams of E Risk Sciences.

The critical information and considerations upon which the draft screening assessment is based are given below.

2. Substance identity

The substance 1,3,5-triazine-2,4,6-triamine (CAS RN 108-78-1), hereinafter referred to by its common name, melamine, is a discrete organic chemical characterized by a high nitrogen content. It belongs to the chemical subgroup of substances known as triazines. It is noted that the name melamine for the chemical is also commonly used for the plastic made from it (WHO c2014).

Information regarding substance identity of melamine is summarized in Table 2-1.

^aSimplified Molecular Input Line Entry System.

3. Physical and chemical properties

A summary of experimental and modelled physical and chemical properties of melamine that are relevant to its toxicity and environmental fate are presented in Table 3-1.

Empirical physical chemical property data were gathered from published literature (Hirt et al. 1960), chemistry handbooks (Crews et al. c2012; Lide 2005) and other sources including database summaries of unpublished studies compiled by other jurisdictions (ECHA c2007-2013). Models based on quantitative structureactivity relationships (QSARs) were also used to generate data for some of the physical and chemical properties of the substance. Most of these models rely on the neutral form of a chemical as input (in SMILES form: c1(nc(nc(n1)N)N)N). Consequently, except where noted, the modelled values shown in Table 3-1 are for the neutral form of substance. Generally, a very good correlation was found between the available empirical physical chemical property values and the modelled values.

Melamine is an odourless, white, fine crystalline powder at room temperature (BASF 2012; ECHA c2007-2013). It is highly soluble in water (Yalkowsky and He 2003; Crews et al. c2012; ECHA c2007-2013) and in ethanol (Lide 2005). Melamine has very low vapour pressure (~10^-9 to 10^-7 Pa at room temperature) (Hirt et al 1960; ECHA c2007-2013), and calculated Henry's Law Constant (HLC) of ~10-9 Pa·m³/mol (EPI Suite 2012). The empirical and modelled log K_ow values for melamine are low at -1.37 to -0.38, respectively (Hansch et al. 1995; ECHA c2007-2013; KOWWIN 2010; ECHA c2007-2013). The modelled log K_oc values were low at 1.5 (based on the MCI estimation method) and 0.0 (based on the K_ow estimation method), respectively (EPI Suite 2012). Melamine is an organic base. Two studies characterizing ionization potential of melamine were identified (Weber 1970; SWISSI 2009). pKa of 7.3 presented in the SWISSI (2009) report indicates that melamine could ionize to some degree at environmentally relevant pH levels greater than 7, whereas according to Weber (1970), with a pK_a of 5, melamine is not expected to appreciably ionize at typically environmentally relevant pH levels (pH 6 to 9). Given limited experimental details, an evaluation of reliability was not feasible for these pK_a studies. However, model results, indicating a pK_a of 5 for melamine, support the finding that the substance exists predominantly as a neutral chemical at pH 6 to 9 (ACD/Percepta 2005). The modelled log D values did not vary with pH, and were approximately -1.2 at pH levels ranging from 6.5 to 8 (ACD/Percepta 2005). In addition, mammalian toxicity data suggest that melamine is in a neutral form at physiological pH levels (see Human Health section). Although the empirical and modelling data indicate that melamine exists in both the neutral and ionized forms at environmentally relevant pH, the available weight of evidence suggests that melamine will predominantly exist (greater than ~90%) in the neutral form under typical environmental pH.

Abbreviations: HLC, Henry's Law constant; log K_ow, octanol-water partition coefficient; log K_oc, organic carbon-water partition coefficient; log K_aw, air-water partition coefficient; log K_oa, octanolair partition coefficient; Log D, distribution coefficient (usually for octanol-water); pK_a, acid dissociation constant; NA, not available; MCI, Molecular Connectivity Index

^a Values in parentheses represent the original ones as reported by the authors or as estimated by the models.

^b Indicates selected value for modelling.

4. Sources

Melamine does not occur naturally in the environment. Melamine can be produced from urea, dicyandiamide or hydrogen cyanide. Commercially produced melamine is manufactured using urea as a starting material (WHO 2009).

A survey conducted under section 71 of CEPA (Canada 2013a) and information obtained from voluntary stakeholder engagement indicated that between 10 and 100 million kg of melamine were imported into Canada in 2011 (ECCC 2013-2014). Melamine was not manufactured in Canada in quantities above the reporting threshold of 100 kg (ECCC 2013-2014).

Canadian import quantities of melamine, of approximately 15 million kg for the year 2011, were reported by the Canadian International Merchandise Trade Database (Statistics Canada 2014).

In 2007, world production of melamine was approximately 1.2 billion kg (1.2 million tonnes), and the dominant producers were located in China and Western Europe (WHO 2009). In the U.S., 80 million kg/year (80,000 tonnes/year) are produced, and in 2011-2012, about 1.5-1.6 million kg/year (1500-1600 tonnes/year) were imported (ICIS c2014). However, the substance is not found in the US EPA High Production Volume Information System (HPVIS) database (US EPA 2007). In the Nordic countries, 12.5 million kg of melamine were used in 2011, whereas use quantities reported for 1999 to 2010 were lower, and ranged between 4.7 million and 10.6 million kg (SPIN c2014).

5. Uses

Uses of melamine are diverse and span numerous industrial sectors, globally and domestically in Canada. The known melamine uses and applications, including instances of adulteration of food products and feed, are summarized below.

In Canada, according to the results of the section 71 survey for the year 2011 and information obtained from voluntary stakeholder engagement (ECCC 2013-2014), melamine was used in paints and coatings available in both consumer and commercial products; in foam seating and bedding (seats and backs which are used for metal frame furniture at concentrations of 28-29%); and in melamine-formaldehyde resin that is used for decorative laminates (ECCC 2013-2014). The substance was also used as a flame retardant in Canada (ECCC 2013-2014). Also, melamine has application as a plasticizer in concrete and in automobile brake tubes and hoses (ECCC 2013-2014). An internet search of current Canadian products also showed use in thermally-fused melamine paper and shelves, whiteboards and flakeboards, paints, sealants for mechanical, electrical and plumbing applications, and in inkjet ink (The Home Depot Canada 2014; Home Hardware 2014: Formica Corporation 2014: Grand and Toy 2014; Flakeboard Company Ltd. 2014; CSL Silicones Inc. 2014; BASF 2014). Globally, melamine is used primarily in the synthesis of melamine-formaldehyde resins for the manufacture of laminates (e.g., for kitchen countertops, tabletops), plastics, coatings, commercial filters, consumer products such as glues or adhesives, and moulding compounds (dishware and kitchenware) (WHO 2009; Scorecard c2011).

According to the results of the section 71 survey of CEPA, approximately 4% of all melamine imported into Canada in 2011 was used as a flame retardant (ECCC 2013-2014) which is consistent with what is observed worldwide. Melamine is used as a flame retardant mainly in polyurethane foams (EFRA 2007). Melamine is often used in combination with numerous other flame retardants such as bicyclic phosphate, decabromodiphenyl ether (decaBDE), antimony oxide, Dechlorane Plus (DP), and others, and in polyolefin formulations for use in plastics and elastomers, to improve the overall flame retardant capability of the final product (Weil and Choudhary 1995). Melamine is also used in the production of other flame-retardants, such as melamine cyanurate (CAS RN 37640-57-6), melamine phosphate (CAS RN 20208-95-1), melamine polyphosphate (CAS RN 218768-84-4), and melamine pyrophosphate (CAS RN 15541-60-3) (EFRA 2007).

Other global uses of melamine include its application as an impregnating or adhesive resin in woodbased panels for furniture and flooring, and in paper money, glossy magazines, and textiles (DSM 2010).

Melamine has applications in agriculture. Due to its high nitrogen content, melamine has been tested and used as a slow-release fertilizer (Wehner and Martin 1989; WHO 2009). In addition, melamine is also a metabolic by-product of the insecticide, cyromazine, which is an insect growth inhibitor that can be applied as spray or in feed (Roberts and Hudson 1999; Zhu et al. 2009). In Canada, cyromazine is registered for use in products to control the Colorado beetle in potato crops, and insects in greenhouse crops (Health Canada 2012).

Melamine is not listed as an approved food additive in the List of Permitted Food Additives, as regulated under the Food and Drugs Act (Canada 2013b). Respondents to the section 71 survey under CEPA did not report any uses of melamine in materials that come in contact with food (ECCC 2013-2014), but melamine may be found in various food packaging products in Canada (e.g. interior coating of cans, excluding infant formula, coating of metallic closures of glass jars, bottles or plastic bottles of baby food and infant formula, paper bags to package bread or margarine, films for milk packaging) (pers. comm. from Food Directorate to Risk Management Bureau (RMB), Health Canada; August 2013; unreferenced)). Based on notifications submitted to Health Canada under the Cosmetic Regulations, melamine is not anticipated to be used in cosmetics in Canada (June 2013 email from the Consumer Product Safety Directorate, Health Canada to the Risk Management Bureau, Health Canada; unreferenced).

In Europe, melamine is approved for use as a monomer, and as an additive in plastics intended to come into contact with food, with a migration limit set at 2.5 mg/kg food (EU 2011). In the U.S., melamine and melamine-formaldehyde copolymer may be used in the formulation of adhesives used as components of articles for use in packaging, transporting, or holding food (indirect food additive) provided that the adhesive is separated from the food by a functional barrier (US eCFR 2014a). Moreover, melamine-formaldehyde resin or polymer may be used as the food contact surface coating (indirect food additive) of articles intended for use in producing, manufacturing, packing, processing, preparing, treating, packaging, transporting, or holding food (US eCFR 2014b).

Melamine is not listed in the Drug Products Database nor the Therapeutic Products Directorate's internal Non-Medicinal Ingredient Database as a medicinal or non-medicinal ingredient present in final pharmaceutical products or veterinary drugs in Canada (DPD 2014; July 2013 email from the Therapeutic Products Directorate, Health Canada, to Risk Management Bureau, Health Canada; unreferenced). Melamine is listed in the Natural Health Products Ingredients Database with a Non-Natural Health Product role as it is not a naturally occurring substance included in Schedule 1 to the Natural Health Products Regulations; as such, it is not listed in the Licensed Natural Health Products Database as being present in currently licensed natural health products in Canada (NHPID 2014; LNHPD 2014).

Following identification of a melamineadulterated pet food in the U.S. in 2007, and melamineadulterated baby formula in China in 2008, global standards were developed to ensure the safety of consumers, and to differentiate between the presence of background levels of melamine in food and intentional adulteration (Health Canada 2009). In Canada, interim standards for melamine were set at 0.5 ppm (or mg/kg) for infant formula and sole source nutrition products, including meal replacement products, and at 2.5 ppm (mg/kg) in products containing milk and milk derived ingredients (Health Canada 2009). These interim standards apply to the presence of both melamine and cyanuric acid, often found together, in order to ensure that foods available for sale in Canada have not been contaminated or adulterated with either compound (Health Canada 2009). Similar standards were also adopted by other jurisdictions including Europe, the U.S., Australia, New Zealand, and China (Health Canada 2009).

6. Releases to the environment

Melamine has many industrial uses and is used in large quantities, both in Canada and worldwide (Du et al. 2010).

Anthropogenic releases to the environment depend upon various losses occurring during the manufacture, industrial use, consumer/commercial use, service life and disposal of a substance. Potential releases are expected to mainly  occur during handling of melamine when it is added, as a pure substance, and during industrial processes to make desired products such as melamine resins. These releases are expected to be primarily caused by the diffuse (fugitive) emissions within the industrial facilities during loading/unloading operations, handling or cleaning of processing equipment, and cleaning of transport and storage containers. It is assumed that 0.6% of the total quantity of melamine used could be released into wastewater (OECD 2002).

Melamine release to the environment is most likely to occur during the manufacturing, formulation and/or industrial use stages, rather than when the substance is contained in products. Releases of melamine to the Canadian environment from use and disposal of (commercial or consumer) products or manufactured items containing melamine are expected to be diffuse.

Releases to the environment are expected to occur primarily to wastewater. Although release to the soil could also occur through the application of sewage sludge as biosolids to agricultural and pasture lands, it is expected that these would be minimal given melamine's limited propensity for partitioning to solids (see Section 7).

Melamine may also be released into the environment from agricultural applications of the pesticide cyromazine, approved for use in Canada. Cyromazine transforms to melamine in soil (major metabolite), plants (minor metabolite) and animals (minor metabolite) (FAO 2007a, b). An environmental and human health re-evaluation of cyromazine itself, is scheduled by the Pest Management Regulatory Agency (PMRA) of Health Canada. This re-evaluation will include revisions to toxicological reference doses and residue definitions, if applicable (Health Canada 2013b).

This information is used to further develop exposure characterization scenarios to estimate resulting environmental concentrations.

7. Environmental fate and behaviour

7.1 Environmental distribution

Based on the known industrial applications in Canada (ECCC 2013-2014), melamine is expected to be released primarily to wastewaters. Due to its low K_oc and high water solubility melamine is not likely to be efficiently removed by adsorption to sludge in wastewater treatment. Level III fugacity modelling using the New EQC model (2011) was applied to describe the fate of melamine.

The overall results of Level III fugacity modelling suggest that when melamine is released into the environment it is expected to predominantly reside in water and soil, depending on the compartment of release (Table 7-1).

When melamine is released to air, it is expected to quickly partition to the particulate phase in air due to its very high estimated K_oa, and as a result, melamine is not expected to reside air. The particulate phase is deposited to land and water as wet and dry deposition. For the amount transferred from air to soil, the majority (more than 70%) will remain in soil, and nearly 30% will be found in water.

When released to surface water from wastewater treatment systems, most of the melamine is expected to remain in water due to its high water solubility. Melamine could also potentially be found in sediment pore water due to its high water solubility.

Volatilization from surface water to air is expected to be a very slow process as melamine has a negligible vapour pressure and a very low Henry's Law Constant. Overall, there are limited rates of advective loss of melamine from aqueous systems.

Melamine has a very low K_oc indicating a low soil and sediment sorption potential. However, since melamine is denser than water, it could, to some degree, settle to sediments. When released to soil (e.g., as a function of biosolid application to agricultural lands), melamine is expected to be adsorbed, and also to run off to aqueous systems. Evaporation from soil is not expected as melamine is relatively non-volatile.

In summary, based on the results of fugacity modeling, and its physical and chemical properties, melamine will predominantly reside in water and soil compartments, and in pore water associated with sediments. Therefore, aquatic, benthic and soil organisms could potentially be exposed to this substance. High exposure to terrestrial organisms through inhalation is not expected, given the expected low melamine concentrations in air.

7.1.1 Long-range transport potential

Monitoring data for melamine in remote areas (e.g. polar regions) are not available.

It was determined that melamine has long half-lives in air and in water. However, melamine is expected to have very low concentrations in air and releases of it into air are not expected based on the known uses of the substance (see Uses section). With its high water solubility, negligible vapour pressure and Henry's Law constant, rates of volatilization to air from surface waters are expected to be very low. Modelled results from the OECD POV and LRTP Screening Tool (OECD 2009) confirmed that melamine will not be found in air as a result of emissions to surface waters. Long range transport in water systems is plausible based on the substance's characteristics and emission patterns. Results of theTaPL3 model (2003) and the OECD POV and LRTP Screening Tool (OECD 2009) indicated that the characteristic travel distance (CTD) in water for melamine was 120 000 km, and 2 300 km, respectively. It is noted that these CTD results should not be interpreted as the absolute distance that the substance can travel, but rather as an indication that the substance has the potential to move over relatively long distances in water.

7.2 Environmental persistence

Empirical and modelled data were considered to determine the degradation potential of melamine in the environment.

Melamine is produced using a condensation process of urea. Melamine can be reacted with a considerable number of organic and inorganic derivatives, such as formaldehyde, forming highly stable products with wide consumer and industrial applications (Ramusino and Vailati 1982). However, based on melamine industrial uses identified from the section 71 survey of CEPA (ECCC 2013-2014), water is thought to be the main receiving compartment of melamine from effluents.

Catabolic biodegradation pathway of melamine has been elucidated, using bacterial strains of Pseudomonas species, Klebissiela pneumonia, and Rhodococcus corallines, isolated from soil. Metabolism of melamine provides a source of nitrogen for bacterial growth; however, melamine metabolism is generally slow (Shelton et al. 1997). A novel strain of bacteria CY1, closely related to β-proteobacteria Alicycliphilus denitrificans, isolated from melamine-manufacturing factory sludge, was observed to be capable of relatively fast and complete biodegradation of melamine in an in vitro study (Wang et al. 2014).

Melamine is known to be metabolized through three consecutive hydrolytic deamination reactions; first to form ammeline, then ammelide, and then yielding cyanuric acid (Wackett et al. 2002; Shelton et al. 1997). This has been attributed to the presence of specific plasmid-encoded genes encoding melaminedegrading enzymes (Karns and Eaton 1997; Wackett et al. 2002; Takagi et al. 2012; Hatakeyama et al. 2015). In cell free extracts, cyanuric acid was shown to undergo further metabolism to biuret, urea, and ammonia (Cook et al. 1985). A complete mineralization of melamine, through intermediates ammeline, ammelide, cyanuric acid, biulet and allophanate, by a mixed bacterial culture containing a novel Nocardioides species was described in Takagi et al (2012). Formation of melaminecyanurate complex precipitate, in addition to melamine degradation intermediates ammeline, amelide, cyanuric acid, biuret, allophanate and urea, was detected in biodegradation assays with the CYI bacterial strain (Wang et al. 2014).

Available information regarding degradation and persistence potential of melamine is organized and presented based on the environmental compartment (i.e., air, water, soil and sediment). Empirical biodegradation data are summarized in Table 7-2, and modelled degradation data are presented in Appendix A.

7.2.1 Air

Empirical data for the degradation potential of melamine in air were not available. Modelled results, based on the available QSAR model (AOPWIN 2010), indicated a long half-life of 16.2 days in air. Therefore, it is expected that the substance will not be rapidly degraded by reaction with hydroxyl radicals in the atmosphere. The ozone reaction half-life could not be modelled since the model AOPWIN (2010) does not provide estimates for this class of chemicals. Overall, melamine is considered not readily degradable in air. It is noted that melamine is unlikely to reside in air in high concentrations. Modelled data in air are summarized in Appendix A.

7.2.2 Water

For the water compartment, degradation by hydrolysis, biodegradation by microorganisms found in the sludge, and modelled biodegradation are discussed below.

7.2.2.1 Hydrolysis

Melamine does not undergo hydrolysis under environmentally relevant conditions (ECHA c2007-2013). However, melamine hydrolyzes under conditions catalyzed by strong alkaline and acidic solutions such as mineral acid and inorganic alkali (Crews et al. 2005). This process proceeds stepwise, with the loss of first, second, and then all three amino groups, to produce ammeline, ammelide and cyanuric acid, respectively. The proportion of reaction products can vary with temperature, concentration, and pH (Crews et al. 2005). Melamine hydrolysis rate constants were measured at 100°C, and reported as 3.80 x 10^-5 (OH-) and 1.25 x10^-4 (H+) (ECHA c2007-2013).

7.2.2.2 Biodegradation by sludge microorganisms

Several inherent and ready biodegradation studies have been conducted using activated sludge and in some studies, preadapted sludge, to determine the biodegradation potential of melamine in water.

Biodegradation of melamine using activated sludge was investigated by Xu et al. (2013) in two common treatment processes, the modified Ludzack-Ettinger (MLE) process that is characterized by both anoxic and aerobic conditions, and the continuous stirred tank reactor (CSTR) process, under aerobic conditions. Biodegradation of melamine was monitored for 225 days; dosing with melamine at an influent concentration of 3 mg/L was started on day 125 of the study. Melamine showed limited biodegradation potential by sludge microorganisms, even after the prolonged 100day exposure to 3 mg/L of melamine that could lead to adaptation. The average removal efficiencies in the MLE and CSTR systems were similar at 20±15%, and 14±10%, respectively, indicating that mixed anoxic/aerobic and solely aerobic conditions did not impact melamine biodegradation. Therefore, it is likely that the enzymes responsible for the hydrolytic deamination of melamine may not be readily induced in activated sludge processes. At a higher melamine concentration of 75 mg/L, decreases in the nitrifying bacterial activities, by 92%±5% in the MLE system, and 82±8% in the CSTR system, and also a decrease in bacterial populations were also observed. These results suggest that melamine may inhibit activated sludge growth when present at high concentrations.

In earlier studies, biodegradation of melamine based on the biological oxygen demand (BOD) was addressed in publications by Heukelekian and Rand (1955) and Niemi et al. (1987). In these papers, existing published and unpublished data on different classes of chemicals were compiled. Study results were tabulated and descriptions of methodology were limited to general information regarding study protocols or experimental conditions. Heukelekian and Rand (1955) presented two BOD results for melamine, originally published by Swope et al. (1950), which indicated 0 g/g and 0.006 g/g BOD, using sewage and following 5 days of incubation. In Niemi et al. (1987), an existing 1984 study result showing 1% BOD in 5 days of melamine using activated sludge (acclimation was said to not be reported) (Vaishnav 1984) was retested using acclimated activated sludge, also over 5 days. The new results indicated 0% BOD, and verified the previous findings. Test results described in Heukelekian and Rand (1955) and Niemi et al. (1987) point to a slow biodegradation potential of melamine.

Two unpublished industry studies were summarized for the European Union Regulation concerning the Registration Evaluation Authorization and Restriction of Chemical Substances (REACH), and study summaries were available from ECHA (c2007-2013). Summaries of two inherent biodegradation studies, performed in 1991 and 1993 according to the OECD protocol 302B, were available. In the 1991 study, activated sludge and preadapted sludge from an industrial sewage treatment plant were used to test melamine at a concentration of 1000 mg/L (1 g/L). The results from the test using activated sludge indicated 16% dissolved organic carbon (DOC) elimination within 20 days, whereas 10% DOC elimination was observed using adapted inoculum after 14 days. In the 1993 study, melamine was tested twice at a concentration of 100 mg/L using activated sludge. Following 28 days, 0% and less than 10% of DOC were observed in the two trials. In addition, a ready biodegradation study results according to the OECD protocol 301C (ECHA c2007-2013) were summarized in MITI (1992). Results of this study indicated 0% biodegradation, measured as BOD, when 100 mg/L of melamine was tested over two weeks (MITI 1992).

In addition, biodegradation of melamine in water under various conditions according to a Zahn-Wellens like protocol was the subject of a master thesis's from the University of Salzburg, Austria, completed in 1997 (Fimberger 1997). Key findings from this research were summarized in ECHA (c2007-2013) and OECD (2002); the original work was written in German. Melamine was tested at 20 mg/L over 28 days. Results indicated no inherent biodegradation using activated sludge from a municipal waste water treatment plant (WWTP). Modifying study conditions by the addition of glucose supported some biodegradation, and the addition of ammonia inhibited biodegradation facilitated by glucose. Melamine was observed to break down rapidly by sludge from an industrial WWTP where melamine was produced, and was no longer detected after 8 hours (Fimberger 1997). Biodegradation was noted to occur by hydrolytic deamination leading to carbon dioxide, which is the pathway presented in other studies by Wackett et al. (2002), Shelton et al. (1997), Karns and Eaton (1997) that examine microbial degradation of melamine.

A novel species of bacteria CY1, isolated from the sludge of a melamine-manufacturing factory in China, was observed to completely degrade melamine in an in vitro study. Melamine was tested at a concentration of about 500 mg/L. In the initial 24 hours, approximately 64% of melamine was degraded by CY1, and approximately 94% of melamine was observed to be degraded in 10 days (Wang et al. 2014).

Results from the available empirical studies are summarized in Table 7-2.

Abbreviations: BOD, biological oxygen demand; DOC, dissolved organic carbon; WWTP, waste water treatment plant.

In summary, the biodegradation mechanism of melamine proceeds stepwise through hydrolytic deamination, to produce cyanuric acid, and eventually through ring cleavage to yield two final products, ammonia and carbon dioxide. Ready and inherent biodegradation studies indicate that melamine biodegradation in water is slow. Under continuous exposure in industrial waste water treatment conditions, acclimation of microorganisms may occur, and can lead to a more efficient breakdown of melamine to release ammonia that can be used as energy source for the resident microorganism population. However, this does not represent a rapid biodegradation potential, but rather a process of adaption by select microorganisms. There is also contrasting evidence suggesting that melamine may be inhibitory to bacterial growth in activated sludge. Given that melamine is a stable molecule, and that its potential for biodegradation in water is limited, as evidenced by numerous studies (see Table 7-2 above), it is considered that the substance is persistent in this environmental compartment.

7.2.2.3 Modelled biodegradation in water

In addition to the available empirical data for the degradation of melamine in water, a QSARbased weight-of-evidence approach was applied using the degradation models shown in Table 4-3.

The rate of hydrolysis could not be determined for melamine using the model HYDROWIN (2010) since the model cannot provide estimates for triazine structures. BIOWIN sub-models of EPI Suite (2012) were used to evaluate the biodegradation potential of melamine. BIOWIN Sub-model 4 results suggest some potential for primary biodegradation. The results from ultimate biodegradation models, BIOWIN sub-models 3, 5 and 6 (EPI Suite 2012), and CATALOGIC (2012) suggest that melamine biodegrades slowly or not at all. When considered together, the model results indicate a limited potential for ultimate biodegradation, and given the model consensus pointing to slow biodegradation rates, there is insufficient evidence to suggest that melamine undergoes significant primary biodegradation. Model results support findings from empirical biodegradation studies (summarized in Table 7-2), and point to a slow biodegradation of melamine in water. Modelled results for degradation of melamine in water are summarized in Appendix A.

7.2.3 Soil

Biodegradation of melamine in soil proceeds at a very slow rate (Hauck and Stephenson 1964). It may be due in part to the symmetrical resonating structure of the substance; molecular symmetry tends to confer stability (Hauck and Stephenson 1964). Melamine biodegradation mechanism via consecutive hydrolytic deamination reactions was elucidated in vitro in bacteria isolated from soil. This has been attributed to the presence of specific plasmid-encoded genes, known as tri A and trz B, C, D, E genes, that encode enzymes called amidohydrolases which are capable of stepwise conversion of melamine to cyanuric acid to biuret and urea, ultimately leading to degradation to carbon dioxide and ammonia by means of urease (Eaton and Karns 1991 a,b; Karns and Eaton 1997; Wackett et al. 2002).

Nitrification of melamine was studied in two types of soil, silty clay loam at pH 8.2, and fine sandy loam at pH 5.2 (Hauck and Stephenson 1964). Melamine was applied to soil samples at a concentration of 0.2 mg/g soil for up to 24 weeks. Results indicated that melamine was nitrified more readily in the silty clay loam, with nearly 8% nitrate formed after 6 days of incubation, and up to 18% after 24 days. In contrast, in the sandy loam soil, 0% nitrification of melamine occurred in the first 12 days of the study, and after 24 weeks, about 9 % nitrification was observed. These results suggested that in silty clay loam soil at basic pH, nitrification of melamine proceeds at approximately double the rate of that in the slightly acidic sandy loam. In another test in silty clay loam, melamine was applied at a concentration of 2 mg/g soil. Following 10 weeks incubation, about 1% of the nitrogen from melamine was found as nitrate when incubation proceeded for up to 28 weeks, nitrate was no longer found,possibly due to increased nitrate assimilation by the soil microorganism population (Hauck and Stephenson 1964).

In an earlier study (Konishi and Imanishi 1941), melamine was noted to nitrify very slowly in a paddy soil.

Overall, study results demonstrate a slow biodegradation rate of melamine in soil. Therefore, it is considered that melamine is persistent in soil.

7.2.4 Sediment

No experimental studies were found for the biodegradation of melamine in sediments, and limited modelling is available for this compartment. Therefore, an extrapolation ratio of 1:1:4 for water: soil: sediment biodegradation half-life based on Boethling et al. (1995) was applied. Given that the half-life of melamine in water is long and likely greater than 182 days (based on the BOD and DOC results in melamine biodegradation studies), it follows that the half-life in sediments is expected to be greater than 365 days. This indicates that melamine is likely to persist in sediments.

7.3 Potential for bioaccumulation

Physical and chemical properties, as well as relevant empirical and modelled data, were examined to determine the bioaccumulation potential of melamine.

Melamine is highly soluble in water, indicating that the substance can be readily bioavailable in water. Experimental and modelled log K_ow values (in the range of -1.37 - -0.38) for melamine suggest that this chemical is likely to have low potential to bioaccumulate in biota as a function of hydrophobic partitioning. In addition, the combination of two partition coefficient log values, log K_ow of -1.37 and log K_oa of 10.8, indicates that given a terrestrial dietary exposure, melamine is unlikely to biomagnify in terrestrial food webs, as suggested by Gobas et al. (2003) and Kelly et al. (2007).

Bioconcentration factors (BCFs) of melamine were determined empirically in several fish species (MITI 1992; ECHA c2007-2013). These studies exposed fish to melamine under static conditions. Melamine exposure duration and concentrations varied among the studies but it was noted that a steady state concentration of melamine was reached in fish tissues (MITI 1992; ECHA 2007-2013). Overall, these studies were consistent in showing very low BCFs for melamine. In carp (Cyprinus carpio), BCFs were calculated to be less than 3.8, and less than 0.38 L/kg, following exposure to melamine at concentrations of 0.2 mg/L and 2 mg/L, respectively in a 6-week study (MITI 1992). A 96-hour exposure of fathead minnows (Pimephales promelas) to 0.09 mg/L of melamine resulted in BCF values of 0.48, and 0.26 L/kg in viscera and carcass, respectively (ECHA c2007-2013). When a 72-hour depuration period was considered in the calculations, the BCF values were determined to be marginally lower, at 0.32 in viscera, and 0.2 L/kg in the carcass. Similarly, in rainbow trout (Oncorhynchus mykiss), BCFs were determined to be well below 1 L/kg in muscle and viscera following 64-hour exposure at 0.09 mg/L melamine (BCF were 0.11 L/kg in viscera, and 0.05 L/kg in muscle) and melamine was noted to be rapidly eliminated within the 72-hour depuration period (ECHA c2007-2013). Results from the fish bioconcentration studies are summarized in Table 7-3.

^a Values in parentheses represent the test concentrations in mg/L at which the BCFs were derived.

In addition, the modelled fish BCF values, determined using the BCFBAF model of EpiSuite (2012), were in agreement with the empirical BCFs, and ranged from 0.93 to 3.16 L/kg wet weigh for the middle trophic level fish, depending on application of the metabolic rate constant.

In light of the melamine food adulteration episodes that occurred in 2007 and 2008, numerous feeding studies in livestock, fish and shrimp, as well as monkeys were conducted to determine the potential for accumulation of melamine in tissues. These studies typically involved adding both low and high levels of melamine to animal feed, and examining effects of melaminecontaminated feed or effects following a single dose of melamine through diet (Qin et al 2010; Andersen et al. 2008, 2011; Lightner et al. 2009; Reimschuessel et al. 2010a; Liu et al. 2010; Phromkunthong et al. 2013). Generally, the resultant measured residue levels of melamine in tissues were low, and suggested that melamine does not have the potential for significant accumulation in animal tissues following exposure through food. Qin et al. (2010) also noted that melamine residues in animal tissues and milk and eggs were virtually depleted in days and up to two weeks after the melamine-spiked diet was stopped. Similar observations of melamine residue clearance in up to 14 days following a single oral dose were noted in fish (Reimschuessel et al. 2010a); however, adverse effects, including renal failure due to formation of renal crystals were noted when high doses of 20 mg melamine/kg were administered to fish (Reimschuessel et al. 2010b).

In summary, there is strong and consistent evidence indicating that melamine does not bioaccumulate to an appreciable degree in aquatic and terrestrial organisms. Melamine is characterised by a combination of physical and chemical properties that suggest low bioaccumulation potential and very low empirical and modelled BCFs in fish. Empirical studies indicated low potential for melamine to accumulate in animal tissues when administered in feed, and a relatively fast residue clearance. Therefore, based on the available evidence, it is considered that melamine has a low potential for bioaccumulation.

7.4 Summary of environmental fate

Melamine is a compact and stable molecule (see Table 2 for structure). Melamine degradation proceeds stepwise through hydrolytic deamination, and eventually through ring cleavage to yield two final products, ammonia and carbon dioxide. In the environment, melamine does not have the potential to degrade quickly. It has a long half-life in air, and relatively slow biodegradation rates in water and soil. Application of the extrapolation factors recommended by Boethling (1995) indicates that melamine is also expected to have a long half-live in sediments. Hydrolysis of melamine does not occur under environmentally relevant pH (6-9). However, under stringent laboratory conditions, melamine can hydrolyze to form cyanuric acid and a complete degradation of melamine to ammonium proceeds rapidly when catalyzed by strong acids.

Melamine is expected to be released primarily to wastewater from industrial sources. Melamine is essentially non-volatile, and has a limited potential sorb to solid particles. It is not likely to be efficiently removed by waste water treatment plants, therefore high concentrations of melamine are not expected in biosolids slated for application onto soil from biosolids amendment practices. Long-range transport in air is not expected; however, it may undergo long-range transport in water. Given its releases to water and soil, and its tendency to reside in those two media, exposure to aquatic and soildwelling organisms is expected. Melamine does not bioaccumulate appreciably in organisms, and it has relatively fast clearance rates in organisms, including fish and mammals. Therefore, biomagnification in foodwebs is not considered to be a significant process and is not expected to contribute to melamine effects stemming from exposure.

8. Potential to cause ecological harm

8.1 Ecological effects assessment

Ecological effects of melamine were determined through empirical data sourced from both published and unpublished studies. The unpublished industry studies were summarized for the European Union Regulation concerning the Registration Evaluation Authorization and Restriction of Chemical Substances (REACH), and study summaries were available from the European Chemicals Agency website (ECHA c2007-2013). Limited study details were provided in some of the study summaries, therefore multiple studies were used to compare the results. Given that numerous melamine effects studies for aquatic and soil species were available, modelled effects data were not considered.

Based on the known industrial uses of melamine (ECCC 2013-2014) in Canada, it is expected that the majority of melamine releases would be to surface waters.

Information is presented based on the compartment of exposure. Results from the published and unpublished studies are summarized below and tabulated in table 8-1 for aquatic microorganisms and invertebrates, and table 8-2 for fish and for soildwelling organisms (Environment and Climate Change Canada 2014).

8.1.1 Water

Effects of melamine on sludge microorganisms were determined in several studies based on short-term exposure of up to 2 hours (ECHA c2007-2013; Hockenbury and Grady 1977), and longer-term 72-hour exposure (Xu et al. 2013). Short-term exposure studies suggest that melamine is not appreciably toxic to sludge microorganisms, whereas potential inhibition of activated sludge by melamine was observed in the 72-hour tests (Xu et al. 2013), suggesting that a longer exposure time may be an important factor that is not well characterized in the available dataset. Overall, study results suggest that melamine has a low toxicity to microorganisms.

The effects of melamine on unicellular organisms were studied in the ciliated protozoa, Tetrahymena pyriformis, and algae species, Scenedesmus pannonicus and Selenastrum capricornutum. Effects of melamine on T. pyriformis< were determined in two studies by Wang et al. (2009; 2011), who observed that melamine had concentrationdependent inhibitory effect. The inhibiting concentrations for 50% effect following 52-hour exposure, i.e., the IC₅₀ values, were determined to be 780 mg/L (Wang et al. 2009) and 820 mg/L (Wang et al. 2011). Similar results were observed by Li et al. (2015) during 20-hour exposure of T. pyriformis melamine. Effects on two algae species S. pannonicus and S. capricornutum were determined in unpublished studies dated 1982 (ECHA c2007-2013) and 1988 (US Testing Company 1988), respectively. Study summaries were available from ECHA (c2007-2013). In the 1982 study, effects of melamine on growth rate were noted, and a no-observed-effectconcentration (NOEC) of 320 mg/L and a 50% effect concentration (EC₅₀) of 940 mg/L were determined following 90.5 hours of exposure. Similarly, in the 1988 study, the NOEC and EC₅₀ at 48-hours were calculated as 97 mg/L and 325 mg/L, respectively, at 72-hours, the NOEC and EC₅₀ were 31 mg/L and 196 mg/L, and at 96-hours, the NOEC and EC₅₀ were 98 mg/L and 325 mg/L, respectively.

The aquatic invertebrate studies testing effects of melamine through water exposure were limited to one species, Daphnia magna. Effects were determined in two unpublished studies dated 1978 (ECHA c2007-2013) and 1988 (ABC Laboratories1988), and included both the short term 24- to 48-hour exposures, and longer-term exposure of up to 21 days. Study summaries were available from ECHA (c2007-2013). In the 1978 study, according to the study summary, D. magna were exposed to melamine for 48-hours, and 7 to 21 days at concentrations of up to 2000 mg/L. The 48-hour LC₅₀ was estimated to be greater than 2000 mg/L; however, it was noted that the condition of daphnids was poor at a much lower exposure concentration of 180 mg/L. Therefore, the 48-hour EC₅₀ for behaviour was established to be less than 180 mg/L. The 7day and 21day LC₅₀s were estimated to be greater than 32 and less than 56 mg/L, based on survival rates observed at exposure concentrations of 32 and 56 mg/L, where at the exposure concentration of 32 mg/L the survival percentage was over 90%, and at the exposure concentration of 56 mg/L no daphnids survived past day 7 of exposure. The 21day NOEC for reproduction and mortality was determined to be 18 mg/L. In the 1988 study (ABC Laboratories1988), melamine was tested at concentrations up to 1000 mg/L for 24 and 48 hours in static conditions. The 48-hour NOEC was estimated to be less than the lowest exposure concentration of 56 mg/L since effects of mortality, and behavioral effects including quiescence, surfacing and/or tending to the bottom of test vessels, were observed at all test concentrations. The 24- and 48-hour EC₅₀ values, based on the total adverse effects, were calculated to be 400 mg/L and 200 mg/L, respectively (ABC Laboratories1988).

Effects of melamine exposure through diet were observed in black tiger shrimp (Penaeus monodon) and Pacific white shrimp (Penaeus vannamei), resulting from administration of melamineadulterated feed in shrimp farms (Lightner et al. 2009). Although not representative of realistic exposure concentrations in the environment, this study highlights effects that arise from an alternate route of exposure, through diet. Analysis of feed samples indicated that melamine was present at concentrations of over 100 mg/kg (reported as ppm). Exposure to these levels of melamine through diet resulted in the presence of insoluble crystals of salts of melaminecyanuric acid in the antennal gland, manifesting as lesions of moderate severity. Increased mortality and prevalence of disease in farmed P. vannamei shrimps where melamine-laced feed had been used were also reported (Lighter et al. 2009).

Results from toxicity studies for sludge microorganisms, unicellular organisms, protozoa, and invertebrates are summarized in Table 8-1.

Abbreviations: EC₅₀, the concentration of a substance that is estimated to cause some effect on 50% of the test organisms; LC₅₀, the concentration of a substance that is estimated to be lethal to 50% of the test organisms; IC₅₀, the inhibiting concentration for a specified percent effect. A point estimate of the concentration of a test substance that causes a 50% reduction in a quantitative biological measurement such as growth rate; NOEC, the no observed effect concentration is the highest concentration in a toxicity test not causing a statistically significant effect in comparison to the controls; LOEC, the low observed effect concentration is the lowest concentration in a toxicity test that caused a statistically significant effect in comparison to the controls.

^a Robust study summaries (RSS) were conducted to determine the quality of the study and are either appended (for critical studies) or available upon request.

Effects of melamine were determined in numerous fish species based on short- and long-term exposures. Short term studies, with a goal to characterize effects on mortality, included four fish species, the guppy (Pecilia reticulata), rainbow trout (Oncorhynchus mykiss), ide (Leuciscus idus), and the Japanese killifish (Oryzias latipes). Summaries of these unpublished studies (dated 1978, 1982, and 1984) were available from ECHA (c2007-2013) and the Japanese database MITI (1992). Studies were typically performed according to protocols similar to the OECD or US EPA guidelines and included appropriate controls. Based on these studies, it is considered that melamine has low toxicity to fish in short term exposures. Observed endpoints included a 48-hour LC₅₀ of 1000 mg/L and a 96-hour NOEC for mortality of 3000 mg/L. Although some mortality was observed in the tested species, a determination of an acute/short term LC₅₀ for melamine was not feasible in most studies, given that the highest test concentrations used in studies approached melamine solubility limit of 4850 mg/L (determined at 25°C). Observations of other physiological effects were not mentioned in the available study summaries. Endpoints determined in these studies are summarized in Table 8-2.

Long term studies testing effects of melamine were carried out using two fish species, the rainbow trout (Salmo gairdneri) and the American flagfish (Jordanella floridae). In a 1984 study, summarized in ECHA (c2007-2013), a semi-static test was conducted over 28 days to characterize growth and mortality rates in juvenile rainbow trout (S. gairdneri) exposed to melamine at concentrations ranging from 750 to 3000 mg/L. Approximately 30% mortality was observed at exposure concentrations of 3000 mg/L, therefore, an LC50 for mortality of greater than 3000 mg/L was assigned, and the NOEC for mortality was determined to be 1500 mg/L. Weight loss in fish was also observed at 1500 mg/L and 3000 mg/L exposure concentrations. Therefore, based on these results, a NOEC for growth can be assigned as 750 mg/L. Two other long-term studies, conducted in 1982, examined effects of melamine exposure during early development stages. Ramusino and Vailati (1982) determined effects of melamine on hatching rates and malformations in rainbow trout (S. gairdneri) embryos. Embryos were exposed to melamine at concentrations 125, 250, 500 and 1000 mg/L until hatched. No mortality was observed in any of the treatments; however, a drop in up to 45% in hatching rates was observed at the highest treatment concentrations. An increase in malformations was also observed in all treatments, with a marked increase to as high as 90% in the 1000 mg/L treatment. It is noted that statistical analyses, that would take factors such as sample size into account, were not performed, and although the percentage drop in the hatching rates and observations of malformation occurrences suggest clear cut effects, it is not certain whether these observations confer statistical differences against controls. Based on the study results, a NOEC for mortality of 1000 mg/L and a LOEC of 125 mg/L for embryonic malformations can be assigned. Effects of melamine on the egg-larval development were also studied in the American flagfish (J. floridae) and study results were summarized in ECHA (c2007-2013). In this study melamine was tested at five concentrations ranging from 100 to 1000 mg/L for 35 days. No effects on hatching ability, appearance and mortality of larvae were noted. Minimal effect on the growth of larvae was noted at the highest concentration tested, but overall the differences in body weights were insignificant (ECHA c2007-2013). The NOEC and EC₅₀ values for survival, growth and condition were determined as 1000 mg/L and greater than 1000 mg/L, respectively.

Addition of melamine to feed also prompted numerous studies in fish used in aquaculture (Liu et al. 2009; Janlek et al. 2009; Xue et al. 2011 a, b; Phromkunthong et al. 2013). As noted in discussion of the shrimp study (Lightner et al. 2009), high dietary exposure to melamine is not expected under typical environmental conditions, rather it is limited to instances where melamine is deliberately added to feed given to farmed animals. Adverse effects were noted and included altered feed efficiency, histopathological changes, as well as statistically lower growth rates in all melamine-fed groups (Phromkunthong et al. 2013). Adverse effects on the fish renal system were noted at higher doses of melamine administered in food, and especially in combination with cyanuric acid. Renal crystal formation and renal failure in trout and catfish was confirmed by Reimschuessel et al. (2010b) following a sequential administration of melamine and cyanuric acid at 20 mg/kg.

Results from key studies in fish are summarized in Table 8-2.

Abbreviations: EC₅₀, the concentration of a substance that is estimated to cause some effect on 50% of the test organisms; LC₅₀, the concentration of a substance that is estimated to be lethal to 50% of the test organisms; NOEC, the no observed effect concentration is the highest concentration in a toxicity test not causing a statistically significant effect in comparison to the controls; LOEC, the low observed effect concentration is the lowest concentration in a toxicity test that caused a statistically significant effect in comparison to the controls.

^a Salmo gairdneri, commonly known as the rainbow trout, had been reclassified in the genus Oncorhynchus, and therefore, Salmo gairdneri is presently called Oncorhynchus mykiss (Smith and Stearley 1989). Since Latinnames that are featured in the original publications and sources are cited, both names mentioned in the table, i.e., Oncorhynchus mykiss and Salmo gairdneri,describe the same fish species.

For the aquatic compartment, a predicted no-effect concentration (PNEC) was derived from the short term toxicity value of 200 mg/L (as the most sensitive, valid experimental value) for the water flea, D. magna, and by dividing this value by an assessment factor of 30 (to estimate a long-term no-effects concentration from a short-term exposure study, and to account for inter- and intra-species variation) to give a value of 6.7 mg/L.

8.1.2 Soil

Limited studies characterizing effects of melamine on soildwelling organisms were available. Plant studies including barley (Hordeum vulgare), radish (Raphanus sativus), garden cress (Lepidum sativum) and common wheat (Triticum aestivum) were limited to protocols that involved the use of melamine percolates, and the product Melfasik that contains 2.8% melamine was tested on pea (Pisum sativum) and string bean (Phaseolus vulgaris) (ECHA c2007-2013; OECD 2002). Another study investigated the rates of nitrification by soil microorganism exposed to melamine in soil perfusion experiments (Hauck and Stephenson 1964). Results from these studies generally point to a low toxicity of melamine in the tested species. The toxicity endpoints ranged from a 14day NOEC of 170 mg/kg, determined for germination and growth of pea and string beans, to a 4day EC50 of 1100 mg/L for root growth of garden cress. A detailed description of soil studies and endpoints is summarized in Environment and Climate Change Canada (2015).

Given the lack of standard protocols in the existing dataset for the soil medium, and no reliable (Q)SAR models, the PNEC could not be determined for this medium. While some melamine exposure in soil due to biosolids amendment may be expected, it is unlikely that there would be significant melamine concentrations in biosolids, given its low log Koc and log Kow, and high water solubility.

8.1.3 Sediment

Studies addressing the effect of melamine on benthic organisms were not identified.

8.2 Ecological exposure assessment

8.2.1 Measured environmental concentrations

Data concerning concentrations of melamine in the Canadian environment have not been identified. In addition, melamine is not on the list of substances reported to the National Pollutant Release Inventory (ECCC 2013).

Globally, baseline concentrations of melamine may be found in the environment as a result of widespread use of materials that contain the substance (WHO 2009). Due to adulteration in animal feed, and the worldwide food trade, animal excrement and urine are suggested to be potential important sources of melamine exposure for environment (Qui et al. 2010). Melamine was measured in water, sediment and in biota in Japan and China (OECD 2002; Qin et al. 2010) as well as in wastewater and soil in China (Qin et al. 2010). Melamine residue deposition and clearance was also studied in livestock (Qui et al. 2010), and provided an insight into melamine contamination of food sources. A summary of melamine concentrations that have been detected worldwide is provided below. Detailed results have been tabulated and are listed in Environment and Climate Change Canada (2014).

In Japan, levels of melamine were surveyed in the environment and biota between years 1986 and 1994 as part of the Environmental Survey and Monitoring of Chemicals led by the Japanese Ministry of Environment (MOE) (CHRIP c2008-; MOE c2005). Melamine was sampled in surface waters in 1986, 1987, and 1994, and was detected in concentrations ranging between 0.1 to 7.6 μg/L in those years (detection limit was reported as 0.1 μg/L). In those same years, melamine was also sampled and detected in sediment, in concentrations ranging from 0.01 to 0.4 μg/g dry weight (lowest detection limit was reported as 0.01 μg/g dry weight). In wild fish, melamine was detected in concentrations ranging from 0.02 to 0.55 μg/g wet weight (lowest detection limit was reported as 0.02 μg/g wet weight) in years 1987, 1988, and 1986. In 1994, melamine was also measured in air, and was detected in concentrations ranging from 2 to 55 ng/m³ (detection limit was reported as 2 ng/m³) (CHRIP c2008-; MOE c2005).

In a study supported by the Chinese Ministry of Agriculture, the presence of melamine was assessed in crops, soil, and water, including surface and ground water, and wastewater to determine the extent of melamine contamination in the environment and food products (Qin et al. 2010). In this study, samples were collected in 21 Chinese provinces and included crops (maize, soybean, and wheat), farmland soil (collected at least 150 km from a melamine factory) and soil near industrial operations (100 m from melamine operations), irrigation water (collected either from rivers or underground), and melamine factory wastewater (from sewage disposal at melamine factories).

The maximum melamine concentrations in the Chinese soil and wastewater samples collected near melamine-manufacturing factories were 41.1 and 226.8 mg/kg, respectively (Qin et al. 2010). The highest melamine concentration measured in the irrigation samples was 0.198 mg/L; other concentrations ranged between 21 and 100 μg/L, and many were not detected (detection limit of 20 μg/L). In farmland soil, melamine was detected in only one sample out of 124 tested, at a concentration of 0.176 mg/kg. Analysis of crop samples revealed that less than 20% of samples had melamine at concentrations above 0.1 mg/kg, three samples had melamine more than 1 mg/kg, and the maximum melamine concentration found was 2.05 mg/kg in a wheat sample. The source of the observed melamine levels was attributed to the general presence of melamine in the environment, and residues from the legitimate use of triazine pesticides (such as cyromazine), and melaminebased fertilizers (Qin et al. 2010).

8.2.2 Exposure scenarios and predicted environmental concentrations

No data on measured environmental concentrations (in water, soils or sediments) of melamine in Canada have been identified. Therefore, environmental concentrations have been estimated from available information, including substance quantities used, estimated release rates and characteristics of the receiving environment.

Melamine is a stable chemical, characterized by a slow biodegradation potential in the environment, a low bioaccumulation potential and a low potential for toxicity to aquatic and soil organisms. Melamine is used in high quantities in Canada and worldwide. Its potential for release into the Canadian environment as a result of industrial operations is expected to be mainly to water.

Exposure characterization is focused on scenarios which represent the highest potential for environmental releases and exposure. In general, the magnitude of releases is a direct function of the quantity of a substance manufactured or used and its applicable emission factors. To analyze environmental exposure to melamine in Canada, information for 2011 obtained from the section 71 survey and voluntary stakeholder submissions (ECCC 2013-2014), as well as information obtained from the Canadian International Merchandise Trade Database (Statistics Canada 2014) were considered.

Several companies reported imports of melamine as a pure substance for use in industrial processes to create products such as melamine-formaldehyde resins, plasticizers and products with flame retardant characteristics, as well as imports of melamine already blended into products and as part of manufactured items (ECCC 2013-2014). In these industrial applications, melamine is considered to be chemically bound within the finished product. Although some leaching of melamine out of products (such as plastics) has been identified, this has been limited to releases from melamine dishware and melamine kitchenware, and only when in contact with hot or warm matrices such as food or water (Wu et al. 2013; European Commission 2011). With respect to ecological exposure, the use of melamine in consumer and commercial products is not expected to lead to significant emissions to the environment due to the very low magnitude and dispersed nature of any resultant emissions.

In addition, biosolid amendment to agricultural lands is unlikely to be a significant route of exposure to soil organisms to melamine.Given its high water solubility and the low Log K_oc value, melamine will reside in water and is not expected to be associated with biosolids.

Quantitative estimates of melamine concentrations in surface water resulting from the manufacturing of resins and blending to make products with flame retardant qualities are considered in this assessment. These concentrations are based on available information on quantities of melamine, sector-specific emission factors, the characteristics of wastewater treatment systems and the receiving environment.

8.2.3 Exposure scenarios from industrial releases to aquatic medium

To estimate the potential of releases to water resulting from industrial use of melamine in its pure chemical form, conservative scenarios at several industrial facilities were developed. These scenarios were developed by using the substance quantities reported for use in 2011 (ECCC 2013-2014), as well as considering the characteristics of the receiving water bodies, wastewater treatment, and industrial operations at each site. To best characterize the exposure from multiple industrial sites that use melamine to make melamine-formaldehyde resin and melamine compounds, a range of potential situations in Canada is presented as Scenario 1. A second scenario, Scenario 2, for blending of melamine into a product with flame retardant properties is also presented.

Aquatic exposure to melamine could occur if this substance is released from industrial activities to a wastewater system that discharges its effluent to a receiving surface water body. The concentration of the substance in the receiving water near the discharge point of the wastewater system is used as the predicted environmental concentration (PEC) in evaluating the aquatic risk of the substance. It can be calculated using the equation:

C _water-ind = [1000 x Q x L x (1 - R)] / N x F x D

where:

C _water-ind:

aquatic concentration resulting from industrial releases, mg/L

Q:

total substance quantity used annually at an industrial site, kg/yr

L:

loss to wastewater, fraction

R:

wastewater system removal rate, fraction

N:

number of annual release days, d/yr

F:

wastewater system effluent flow, m ³/d

D:

receiving water dilution factor, dimensionless

Table 8-3 presents the inputs used to estimate resulting aquatic concentrations close to the industrial points of discharge. It is noted that the assumption of loss to water, although based on empirical data, is considered conservative for these specific industrial practices.

Based on the above-mentioned assumptions, these scenarios yielded predicted environmental concentrations (PECs) of 3 x 10^-3 mg/L to 1.8 mg/L for scenario 1, and 8 x 10^-3 mg/L for scenario 2. It is noted that the percentage loss of 0.6% to wastewater included in the calculation is based on empirical data from facilities that manufacture and blend melamine (OECD 2002). Since melamine is not manufactured in Canada, this is a very conservative evaluation of melamine releases and may contribute to overestimation of risk.

8.3 Characterization of ecological risk

Numerous lines of evidence were considered in the characterization of ecological risk posed by melamine, and included reliable toxicological experimental data, known use quantities, use and release patterns of melamine in Canada, and predicted concentrations in the environment based on industrial exposure scenarios. This information suggests that there is low risk of harm to organisms and the broader integrity of the environment in Canada from melamine.

8.4 Risk quotient analysis

A risk quotient analysis that integrated conservative estimates of exposure with toxicity information was performed for the aquatic medium. The scenarios for the aquatic medium yielded predicted environmental concentrations (PEC) of 3 x 10^-3 mg/L to 1.8 mg/L and 8 x 10^-3 mg/L for scenario 1, and 2 respectively. For both aquatic scenarios, a predicted no-effect concentration (PNEC) of 6.7 mg/L was derived from the acute toxicity value of 200 mg/L for daphnids and by applying an assessment factor of 30. The resulting risk quotients (PEC/PNEC) ranged from 0.001 to 0.27 for scenario 1. It is noted that the risk quotients obtained from scenario 1, i.e., 0.001 and 0.27, are the lowest and the highest risk quotients, calculated for industrial facilities using melamine, and therefore represent a range of encountered risk quotient values for this most common melamine application in Canada. The risk quotient for scenario 2 was 0.001. Table 8-4 provides a summary of this information. Results indicate that harm to aquatic organisms from releases of melamine in these conservative scenarios is unlikely.

8.4.1 Consideration of lines of evidence and conclusion

Melamine is expected to be persistent in water, soil and sediment and to have a low bioaccumulation potential. It has also been demonstrated that melamine has low to moderate potential for toxicity to aquatic organisms. High importation volumes of melamine into Canada, along with information on its uses, indicate potential for widespread release into the Canadian environment. Once released into the environment, melamine is expected to predominantly distribute to water. Predicted environmental concentrations (PECs) resulting from industrial uses of melamine were calculated based on industrial scenarios. Consideration of the PEC values, together with the toxicity of melamine to aquatic organisms, its potential to bioaccumulate and its long residence time in the aquatic media, formed the basis for evaluation of the potential to cause ecological harm. This information indicates that melamine is not causing ecological harm in Canada at use quantities reported for 2011.

8.4.2 Uncertainties in evaluation of ecological risk

There is uncertainty regarding assumptions used that may have resulted in over-estimation of the risk quotients calculated for the key industrial applications of melamine. In particular, the conservative assumption of substance loss to environmental media of 0.6%, based on empirical data from facilities that manufacture and blend melamine, may have led to an overestimation of risk. Melamine is not manufactured in Canada. Lack of monitoring data in Canada does not allow for direct comparison with PECs to verify whether they have been over- or under-estimated. PECs in water for melamine were determined to be in the range of 8 x 10^-3 to 1.6 mg/L. The measured surface water concentrations of melamine in Japanese rivers were in the range of 1 x 10^-4 - 7.6 x 10^-3 mg/L and up to 1.98 x 10^-1 mg/L in rivers in China that receive irrigation water. Therefore, in comparison with the sparse measured data, the derived PECs are likely conservative.

Although melamine is not expected to be associated with biosludge, some melamine may be removed through biosolids. This process is likely inefficient as dictated by melamine physical chemical properties including the high water solubility and a low soil organic carbon-water partitioning coefficient.

The limited existing empirical dataset for melamine effects in soildwelling organisms, and lack of reliable (Q)SAR models for the soil medium, prevented derivation of a reliable PNEC value. The soil scenario was therefore not pursued since too many uncertainties were associated with key information needed for its development. However, given the low observed toxicity of melamine to soildwelling organisms, and the likely low concentrations of melamine associated with biosolids, the potential risk to soildwelling organisms from this route of exposure is not perceived to be considerable.

There is also uncertainty regarding ecological effects from potential releases of melamine present in melaminebased flame retardants such as melamine cyanurate (CAS RN 37640-57-6), melamine phosphate (CAS RN 20208-95-1), and melamine polyphosphate (CAS RN 218768-84-4). These substances are not on the Domestic Substance List, and were therefore not subject to categorization under subsection 73(1) of CEPA. Potential ecological effects and risk characterization due to melamine contained in these melaminebased flame-retardant substances were not addressed in this screening assessment.

9. Potential to cause harm to human health

9.1 Exposure assessment

The potential for exposure to melamine via environmental media (drinking water, air, soil/dust), food, melaminecontaining tableware and dishware, and consumer products is discussed in this section, as well as estimates of exposure based on biomonitoring data.

9.1.1 Environmental media and food

9.1.1.1 Air

No data on concentrations of melamine in ambient or residential indoor air were identified.

9.1.1.2 Dust

No data on concentrations of melamine in dust were identified.

9.1.1.3 Soil

No data on melamine concentrations in North American soils were identified and a soil predicted environmental concentration (PEC) was not determined [see section 8.2]. In China, soils were tested at 100 m and approximately 150 km away from melamine manufacturing factories. At 100 m, melamine concentrations in soil ranged from not detected to 41.1 mg/kg. At approximately 150 km, concentrations in farmland soil ranged from nondetected to 0.176 mg/kg (Qin et al. 2010) [also discussed in section 8.2.1]. Concentrations measured further away from a melamine manufacturing facility would be more representative of soil concentrations to which the general population is likely to be typically exposed in Canada. The maximum concentration in farmland soil measured at 150 km away from the manufacturing facility in China was used in a deterministic estimate of daily intake.

The deterministic estimate of daily intake based on exposure to melamine via soil is negligible for all age groups.

9.1.1.4 Water

Canadian occurrence data for melamine in drinking or surface water were not available. The only results for melamine concentrations in drinking water were found in a European Food Safety Authority (EFSA 2010) Panel report. The EFSA report indicates that the data was provided by industry members sourced from various areas around the world (n = 20 tap water samples) and reported melamine concentrations ranging from 10 to 200 μg/kg (mean: 50 μg/kg). Individual results for each sample were not reported and there was no indication as to how many water samples had melamine concentrations below the limit of detection (LOD).

Due to the lack of Canadian data pertaining to this potential source, the EFSA data was used for exposure characterization of melamine from drinking water. Estimated intakes were 5.3 and 21 μg/kg/day for 0 to 6 month old infants (highest exposed group), for central tendency and upperbound concentrations, respectively (see Appendix B).

9.1.1.5 Food

As shown under "Uses" (Section 5), melamine is not listed as an approved food additive under the Food and Drugs Act, but it may be found in food packaging in Canada. In the USA, melamine is an indirect food additive used in the synthesis of melamine-formaldehyde resins intended for use in food processing and packaging.

Various international studies have investigated the migration of melamine (contained in can coatings and jar closures) into food and beverages. In the U.K., Bradley et al. (2011) tested migration from resins based on melamine-formaldehyde and related analogues (methylolated melamine) used to cross-link coatings inside food cans and metal closures on glass jars. For 13 coatings tested, migration rates ranged from less than 1.5 to 332 μg/kg depending on the conditions used (i.e. fluid matrix, temperature variation). Using the same experimental conditions, six different laboratories in Europe observed similar migration rates ranging from 1.5 to 327 μg/kg (EFSA 2010). Bradley et al. (2011) also tested migration of melamine into three different food types (food types varied based on acidity, fat content, and presence of meat or fish) in various conditions and observed migration rates ranging from less than 23 μg/kg to 220 μg/kg.

The aforementioned data show that melamine may migrate from food packaging into food, and that concentrations will increase if foods are subjected to heating.

Melamine has been measured in many foods in many countries, primarily as a follow-up to the identification of melamineadulterated formula and animal feed incidents in China and North America, respectively (WHO 2009; Hilts and Pelletier 2009; Dorne et al. 2013).

In Canada, surveys to measure levels of melamine in food were conducted by the Canadian Food Inspection Agency (CFIA) from 2008 to 2012, primarily for the purpose of identifying high concentrations that may have occurred from adulteration and to ensure continued compliance with Health Canada's Interim Maximum Levels for melamine in foods. As such, sample selection was biased and the methodology resulted in a relatively high limit of detection (LOD). Data from these surveys were not used in this assessment.

In addition to the above mentioned food compliance activities by the CFIA, Health Canada has conducted research to measure background levels of melamine in food and has analysed 94 samples of various infant formulas sold in Canada (analysed in the "as purchased" form), 246 samples of dairy and soybased dairy replacement products from Canadian retail outlets, and 378 samples of eggcontaining products, soybased meat substitutes, fish and shrimp products, and vegetable products (Tittlemier et al. 2009, 2010a, 2010b). The Health Canada surveys focused on foods with the greatest probability of containing residual levels of melamine. Such foods include dairy foods and other products containing milk, vegetable products^{Footnote 2} , and marine foods^{Footnote 3} .

Total dietary exposure to melamine was estimated using mean melamine concentration data for each food commodity type sampled by Health Canada and exposure to melamine was estimated using a semi-probabilistic approach^{Footnote 4} . Mean and 95^th percentile exposure estimates for various age groups are provided in Table 9-1 (see Appendix C for melamine concentration levels and dietary exposure assessment methodology)^{Footnote 5} .

^a males and females are both included in each age category.

Chocolate candy and milk coffee combined, account for almost 60 percent of the estimated dietary melamine exposure for the overall population. The high contribution of chocolate candy is the result of one sample that was found to have an elevated concentration of melamine, thereby significantly increasing the mean melamine level used to represent all chocolate candy (i.e. 667.2 ug/kg)^{Footnote 6} .

Of note, melamine food packaging migration concentrations (less than 1.5 to 332 μg/kg) reported in the European studies mentioned above are within the mean range of values reported in the Canadian food monitoring studies (see Appendix C, range: less than 4-667 μg/kg).

9.1.1.6 Breast milk

Yurdakok et al. (2014, 2015) measured melamine in breast milk of 77 healthy lactating mothers in Ankara, Turkey from June-September 2010 (babies were 3-10 days old). Breast milk samples (10 mL) from each mother were analyzed by HPLC with the LOD and LOQ determined at 10.6 and 41.6 μg/L, respectively. Melamine was detected in 16 of 77 samples (20.8%), with concentrations ranging from 10.1 to 76.4 μg/L (mean: 27.1 μg/L). There was no influence of body mass index on the distribution of melamine concentrations (mothers grouped into normal, overweight, and obese weight groups).

Since no Canadian data was identified regarding melamine presence in breast milk, the Turkish dataset was used for exposure characterization. Daily intake estimates from melamine presence in breast milk are 2.7 and 7.6 μg/kg/day, for mean and maximum concentrations, respectively.

9.1.2 Migration from melaware

Melamine reacts with formaldehyde to produce a thermoset plastic called "melamine" or "melaware" which can be used as dishware or kitchenware.

Studies on migration of melamine from melaware dishware into foods, water and other beverages were identified. In a Danish study, concentrations of melamine migrating into water from purchased melaware plates (n = 6) and used melaware cups (n = 11) ranged from less than 1500 to 2940 μg/L over a temperature range of 20 to 95°C (Lund and Petersen 2006). Bradley et al. (2010) also analyzed migration in melaware articles (bowls, cups etc.) purchased in 2010 from retail outlets in Germany, the Netherlands and the UK. Concentrations of melamine migrating into various types of food and liquid matrices (tomato sauces, water, beverages etc.) ranged from less than detection limit to 4194 μg/kg. Experimental conditions were also varied, i.e. samples were heated to temperature ranges of 40 to 100°C, or put under heating or microwave conditions.

In a Taiwanese study (Chien et al. 2011), melamine concentrations in a food simulant (3% acetic acid or distilled water), measured in 25 melaware cups, ranged from 30 μg/L (20°C) to 19,030 μg/L (90°C); migration was significantly higher in 3% acetic acid than in distilled water.

In a Malaysian study, melamine concentrations in 3% acetic acid or water, measured in 246 melaware dishware items, ranged from 1.31-140 μg/L at 25°C to 4.05-509 μg/L at 100°C (Chik et al. 2010). Additonally, reported mean or median concentrations of melamine migrating into water or other beverages from melaware dishware at room temperature ranged from 22 to 30 μg/L (Chik et al. 2010; Chien et al. 2011). These concentrations fall within the range used for beverages in the dietary intake assessment and are also below the mean drinking water concentration of 50 μg/kg reported by EFSA (2010).

Based on the studies conducted on food and beverages mentioned above, concentrations measured in food items heated (100°C) in melaware dishware appear to be significantly higher than concentrations measured in items left at room temperature. EFSA (2010) examined the migration of melamine from melaware dishware into food and water, citing some of the same data above, as well as additional data provided by other European countries (i.e. Finland, Cyprus, Netherlands). EFSA concluded that migration of melamine from melaware dishware is characterized by high variability, depending on various factors such as manufacturing process, alterations to the surface due to service life, time and temperature conditions of use, as well as characteristics of food (e.g., acidic, aqueous, fatty or dry). Consequently, this may result in higher levels of melamine residue.

EFSA estimated exposure to melamine from migration using "typical and high migration values" for different food classes. Both were considered conservative^{Footnote 7} .Concentrations in each type of food after migration from a melaminecontaining article estimated by EFSA are shown in Table 9-2.

Exposure to melamine from use of melaware dishware was estimated using conservative assumptions, e.g., assuming that all foods and beverages come into contact with melaware dishware. The highest EFSAderived typical migration levels (acidic and aqueous foods) were used to estimate exposure from this source (see Table 9-2). Although migration studies were not identified for melaminecontaining dishware in Canada, it is assumed that conditions and results for migration of melamine from such dishware would be similar to data generated elsewhere. Finally, exposure estimates for different age groups were derived using overall daily food consumption quantities estimated by EFSA (2006) (see Table 9-3).

^a The consumption scenario considered was taken from EFSA (2006). Values considered for the 6 month infant are the 95^th percentile of consumption of commercial baby foods and drinks and of powdered infant formula observed in 6 month infants in the Dortmund Nutritional and Anthropometrical Longitudinally Designed [DONALD] study (0.5 kg) (Kersting et al, 1998). For the child aged 1.5 years, the daily consumption of 1.33 kg of beverages and 0.67 kg of solid foods were considered (CEC 1993). For adults, daily consumption of 1 kg of solid foods and 2 kg of beverages were considered.

^b Infants assumed to weigh 7.5 kg; toddlers assumed to weigh 15.5 kg, and adults assumed to weigh 70 kg (Health Canada 1998).

^c Exposure from melaware at highest typical migration level observed for acidic (1 mg/kg) and aqueous foods (0.6 mg/kg) derived by EFSA (2010). For infants 0 to 6 months acidic foods migration rate (1 mg/kg) used for baby food/drink and formula intake calculations. For children 1.5 years old and adults, acidic foods migration rate (1 mg/kg) used for beverage intake calculations and aqueous foods migration rate (0.6 mg/kg) used for solid food intake calculation.

^d Exposure = (Migration from Melaware articles into food matrix (mg/kg) x Consumption of food type) / body weight.

9.1.3 Consumer products

As noted in section 5, melamine has uses in various types of products in Canada. Examples of these products include paints coatings, sealants, foam seats/backing/mattresses, thermally-fused melamine paper and shelves, whiteboards and flakeboards, inkjet ink, melamine coated dishware and tableware etc.

Due to considerations such as limited dermal contact, commercial and industrial use, and low melamine concentrations; exposure to paper and shelves, whiteboards and flakeboards, and inkjet inks were not assessed as exposure is expected to be low especially compared to other scenarios presented below. Additionally, potential exposure to melamine via dishware and tableware is addressed in the previous section.

9.1.3.1 Do-it-yourself products (paints, sealants, coatings)

Material Safety Data Sheets (MSDSs) from paint products sold in Canada containing melamine show that the maximum concentration in waterborne paints is 13% (Benjamin Moore & Co. 2011, 2013). MSDSs were also available for sealants sold in Canada for mechanical, electrical and plumbing applications that contain melamine at a maximum concentration of 60%. Although the MSDSs indicated that the product was for industrial and professional use only, these products are available to general consumers at retail outlets.

Both inhalation and/or dermal exposures from "per event use" were considered for users of airless paint spray equipment, brush and roller paint applications, as well as applications of sealing and caulking within the home. However, the following available evidence for melamine was considered:

1. Due to the negligible vapour pressure associated with melamine, inhalation exposure from brush and roller paint applications are considered negligible. Further, inhalation from airless paint spray applications would also be negligible as this application would not likely produce respiratory-sized droplets (majority of droplets would be greater than 15 μm in diameter).
2. Acute dermal administration of melamine in experimental animals does not result in skin reactivity (Fassett and Roudabush 1963; Rijcken 1995; Vernon et al. 1990) and structurally similar compounds show only maximum dermal absorptions of 10-16% in human skin (Ademola et al. 1993; Baynes et al. 2005).
3. Acute dermal and acute oral toxicity of melamine is comparatively low with LD₅₀ values reported above 1000 mg/kg bw in experimental animals (OECD 2002; US NTP 1983; Vernon et al. 1990). Inhalation acute toxicity is also low with LC₅₀ values reported above 3200 mg/m³ in rats (BASF 1969a; Muijser 1999; Ubaidullajev et al. 1993).

Based on the above considerations, one-time per event dermal and inhalation exposures to melamine from consumer use of airless paint spray equipment, brush and roller paints, and caulking and sealants in the home were determined to represent a low to negligible risk for the Canadian general population.

9.1.3.2 Foam Products (seating, bedding etc.)

As stated in the "Uses" section, melamine is also found in foam seating and bedding in Canada. Concentrations in this foam were reported at concentrations up to 29% (ECCC 2013-2014). The US CPSC (2005) analyzed 6 types of upholstery foam for melamine content and found concentrations ranging from nondetect (LOD = 0.005% w/w) to 34% w/w. This is consistent with reported melamine concentrations for Canadian foam furniture items and mattresses.

Since melamine is an additive flame retardant and can migrate out of a matrix, dermal exposure may occur from skin contact with melamine-treated foam furniture and mattresses. This migration may be mediated by sweat since melamine is associated with high water solubility. Data on migration of melamine were not identified. Instead, a migration rate for melamine was extrapolated from migration rates in relation to the water solubilities of other flame retardants, i.e. reported in screening assessments for TDCPP (CAS RN 13674-87-8) and TBB (CAS RN 183658-27-7), as shown in Table 9-4. The US CPSC (2006) used TDCPP and TBB migration rates to estimate potential dermal exposure adapted from exposure studies for mattress filling materials.

^a This measured maximum rate for covered foam over 6 hrs was converted to a rate per hour based on table 2 in CPSC 2005 (Cobb and Bhooshan section: mg in filter paper / cm² filter paper / 6 hrs).

^b Calculated based on plotting a straight line between water solubilities and migration rates for TDCPP and TBB with equation y = (2E-06 x water solubility) + 2E-05.

Based on this, a migration rate of 0.0065 mg/cm²/hr is derived for melamine. Using this migration rate, dermal exposure intakes were estimated for children and adults in direct contact with foamcontaining mattresses as a representative scenario of potential exposure to foam containing furniture. This scenario is considered to also be representative of potential exposure from textile backcoating in furniture. As shown in Appendix D, the estimates of dermal exposure to melamine via dermal contact with foam mattresses were 0.05 and 0.18 mg/kg bw/day in adults, and infants, respectively. Finally, due to melamine's negligible vapour pressure, inhalation exposure to melamine contained in foam furniture and mattresses is expected to be negligible.

Based on melamine's properties (additive flame retardant, high water solubility), it is expected that children may be exposed from mouthing a foam object. Although melamine concentration data in foam products were available, a melamine-specific migration rate from foam was not identified in the literature. In the absence of migration rates for mouthing, the same migration rate used for the dermal scenario was applied. As shown in appendix D, the estimate of oral exposure to melamine via mouthing of a foam object is 0.0034 mg/kg bw/day for toddlers.

9.1.4 Biomonitoring

Panuwet et al. (2012) published the results for melamine measurements in 492 spot samples of human urine collected from the general US population. These samples were collected in 2003-2004 as part of the U.S. National Health and Nutrition Examination Survey (NHANES) and included samples from both males and females aged 6 years and older (US CDC 2010a). Melamine was detected in 76% of the samples (population: 6 + years old, GM: 2.37 ng/mL, 95^th percentile: 12 ng/mL, maximum: 161 ng/mL, LOD = 0.66 ng/mL)^{Footnote 8} . Since the relative distribution of age groups (i.e. 6-11, 12 -19 years etc.) was not available from Panuwet et al. (2012); this information was derived from demographic data collected by NHANES (US CDC 2010b). Geometric mean and 95^th percentile concentrations, based on the different age groups, are presented in Table 9-5.

Regarding pharmacokinetic data, no studies were identified showing the fraction of melamine excreted in human urine; however Mast et al. (1983) showed that 90% of administered melamine was excreted in urine of male rats as melamine. In dogs, Lipschitz and Stokey (1945) showed that 60-86.5% of administered melamine was excreted as melamine24 hr after a single oral dose of melamine. Finally, although Liu et al. (2010) suggested that the amount excreted in monkey urine was much less than the oral dose, they could not document a mass balance for the excretion profile or cite the percentage of melamine dose excreted in the urine (see section 9.2.1 below and Health Canada 2015: Appendix B, table B-1).

Due to the variability in urinary excretion between species, the lowest percentage excretion of melamine in urine (60%; Lipschitz and Stokey 1945) was used to calculate biomonitoring intakes. Additionally, since information on urine volume excreted for each participant was not collected; ranges of typical 24 hour mean urine volumes identified from various sources and shown in the table below were also used to calculate intakes (see Appendix E for urine volume ranges and references). Biomonitoring intakes are presented in Table 9-5.

^a Based on age of participants at time of urine sampling (492 total).

^b Range of average urinary 24 hr volumes reported in the literature (see Appendix E).

^c Average body weights for 12-19, 20-59, and 60+ year groups from Health Canada (1998). Average body weight derived for 6-11 year olds, based on US EPA (2011) because Health Canada (1998) does not report body weights based on this age range.

^d Based on the lowest reported percentage excretion of melamine in urine in experimental animals 24 hr after dosing = 60% (Lipschitz and Stokey 1945; Mast et al. 1983; Liu et al. 2010).

^e For all age groups (except 6 - 11 year olds) 95^th percentile values were used for intake calculations. For 6 - 11 year olds, 5 individuals showed urinary melamine concentrations between 0.5 and 6.7 ng/mL and the other presented a urinary concentration of 161 ng/mL. Due to small sample size in this age group and the possibility that one of the concentrations was an outlier, a 95^th percentile intake calculation would be statistically unstable. Therefore, the second highest concentration was used to determine the upperbound intake.

^f Mean and upperbound intake estimates were calculated using the following equation (Aylward et al. 2012):
Daily intake (μg/kg bw/day) = [urine concentration (μg/L) x 24 hr urine volume (L/day)] ÷ [fraction excreted in urine x BW (kg)].

For the 12+ years old age groups, mean intakes ranged from 0.02 - 0.16 μg/kg bw/day and 95^th percentile intakes ranged from 0.06 - 0.79 μg/kg bw/day. For the group aged 6-11 years old, mean intakes ranged from 0.08 - 0.35 μg/kg bw/day. Due to the small sample size (n = 6) of this age group, 95^th percentile intakes were not derived because they would be statistically unstable. Also, one high recorded concentration of 161 ng/mL melamine was recorded for this age group, whereas other concentrations among the 6 individuals ranged from 0.5-6.7 ng/mL. Panuwet et al. (2012) did not discuss whether this high value was an artifact.

Other biomonitoring studies have been conducted in Taiwan and Hong Kong (see Appendix F) but the results based on the US population measured by Panuwet et al. (2012) were used as a surrogate for the Canadian population. It is important to note that ethnic differences between US and Canadian populations may lead to differences in intakes; however, given the close proximity of this population to Canada, the US NHANES dataset is considered more relevant.

9.2 Health effects assessment

Health effects information for melamine is summarized in this section. Further details may be found in the supporting document, Health Canada (2015).

9.2.1 Oral toxicokinetics

As shown in Health Canada (2015: Appendix B), melamine was excreted in rat and monkey urine after single oral doses of 1.3 and 1.4 mg/kg bw, respectively, but the following two metabolites were identified in addition to unchanged melamine, after large single oral doses in the rat (250 mg/kg bw) and dog (125 mg/kg bw): dimelamine monophosphate and monomelamine-monooxalate. Also, based on extensive toxicokinetic studies in rats, melamine was not metabolized at lower doses compared to higher doses (1.3 vs. 250 mg/kg bw), which suggests that oral exposure at environmental levels of melamine, may not be metabolized in the body. In the rats dosed at 1.3 mg/kg bw/day, mass balance calculations showed that 98% of the dose was recovered as melamine 96 hrs after dosing, confirming a lack of metabolism (Mast et al. 1983).

At 100 mg/kg bw/day oral dosing, there appears to be saturation of excretion. When Wu et al. (2010b) dosed Sprague-Dawley (SD) rats at 100 mg/kg bw, they wrote "About 63.2% of the administered dose was recovered from the urine within 96 h. The previous study indicated a value of 90% elimination within the first 24 h [Mast et al. 1983], and this discrepancy might result from a much higher dose (100 mg/kg, po) in our study, possibly leading to the saturation of urinary elimination and delayed elimination time. This result suggests that most of the administered melamine was absorbed and eliminated via the urine in unchanged form".

Dorne et al. (2013) reported plasma elimination half-lives ranging from 2.7 to 5 hrs from various rat studies upon single oral dosing. Jacob et al. (2012) showed it to be 1.6-1.9 hr at 1 mg/kg bw, Wu et al. (2010b) indicated 1.3 hr at 50 mg/kg bw and Pang et al. reported it at 2.5 hr at 100 mg/kg bw in rats; in monkeys dosed orally at 1.4 mg/kg bw, the plasma elimination half-life was 4-5 hrs. Dorne et al. (2013) considered the rates comparable at these oral doses, and in all cases, support the observation of rapid excretion of melamine in urine. As shown below, Wang et al. (2013) reported a plasma elimination half-life of 9.9 hr in pigs subjected to 42 days of melamine in the diet. Although slightly longer than the half-lives reported for other species, they also confirmed that melamine was primarily eliminated via renal filtration.

Wu et al. (2010b) also showed that oral bioavailability in the rat was 98%, whereas Yang et al. (2009) reported it to be 73±13%, confirming high and rapid oral absorption in the gastrointestinal tract. Rats administered a single oral dose of 100 mg/kg bw showed a maximum melamine concentration in plasma of 78 mg/ml at 1.2 hr and concentration in the kidney was less than 1 mg/g (Pang et al. 2013). After rats were dosed daily for 14 days with 100 mg/kg bw/day, there was limited accumulation of melamine in organs (less than 12 ppm), with highest concentrations found in the bladder and spleen (approximately 7 and 4 ppm, respectively), and trace amounts in the brain; the concentration in plasma was 0.045 μg/mL (Wu et al. 2010b). This study and those conducted by Yang et al. (2009) and Pang et al. (2013) in rats, indicate that melamine does not extensively distribute to most tissues, being mostly restricted to blood or extracellular fluids upon oral dosing.

Chu et al. (2013) conducted a toxicokinetic study in pregnant and developing rats. Pregnant females were given a single dose by gavage of 24 mg/kg bw melamine on gestation days (GD) 10, 15, or 20 and by gavage in pups on postnatal weeks 2, 4, 6 or 8 (P2W, P4W, P6W, or P8W, respectively). Distribution of melamine in maternal serum was about 30% higher in late pregnancy than that in early pregnancy and it was two folds higher in postnatal serum in early pups than in young adulthood (P2W vs. P4W-P8W). Melamine distribution in all postnatal organs was higher than that in prenatal organs. In early pups, postnatal kidneys had the highest maximum concentration and the lowest clearance rate of melamine than the other postnatal organs (Cmax = 10.85 mg/kg vs. 1.06 - 2.36 mg/kg and apparent clearance = 0.62 l/hr vs. 1.85-2.75 l/hr in liver, lung, heart, brain and spleen, respectively at P2W). The increased distribution of melamine in serum and kidneys of 2-week old rats compared to other life stages suggests an increased risk of melamine toxicity to the kidney after birth. The developmental toxicity studies of Kim et al. (2011) and Stine et al. (2014; see "Developmental toxicity and fertility studies") showed kidney toxicity in pregnant dams at oral doses of 800 and 1000 mg/kg bw/day melamine; however, no kidney toxicity was observed in fetuses at these doses (although other effects were observed) and the dams were not allowed to litter.

Wang et al. (2013) conducted a repeated dose toxicokinetic study in pigs. Pigs were fed melamine in the diet at doses 0, 18, or 35 mg/kg bw/day for 42 days with a 5 day recovery period. There was a dose-related increase in residual melamine concentrations in all tissues measured (plasma, brain, duodenum, liver, heart, muscle and kidney), and melamine concentration in kidney was significantly higher than in other tissues (p less than 0.01). Five days after melamine withdrawal from the diet, the residue concentration in tissues fell to less than 2.5 mg/kg. After 42 days at the 35 mg/kg bw/day dose, the average Cmax in plasma = 9.56 μg/ml at an average time of 3.67 h, the half-life was 9.90 h, the clearance was 0.076 l/h/kg, and the steady state volume of distribution =1.07 l/kg. The authors noted that the clearance of melamine in this study was consistent with the clearance observed in pigs subjected to single intravenous doses (0.076 versus 0.061 l/h/kg) conducted by Baynes et al. (2008),and thus, melamine is primarily cleared by renal filtration in the pig.

EFSA (2010) also reported that there is indirect evidence that melamine is not metabolized in humans. In a study in which [¹⁴C]-ring-labelled hexamethylmelamine was administered to humans orally, 5% of the dose of hexamethylmelamine (as ¹⁴C) was excreted as melamine in urine, but no metabolites of melamine were reported The authors conducted the same study in rats dosed intraperitoneally with [14C]-ring-labelled hexamethylmelamine. In this case, 2% of the dose of hexamethylmelamine (as ¹⁴C) was excreted as melamine in urine, but no metabolites of melamine were reported. In both the rat and human studies, only 5% of the urinary radioactivity was unidentified.

EFSA (2010) summarized toxicokinetic data for experimental and farm animals and humans. It's overall description of toxicokinetics of melamine is consistent with findings from the more recent studies mentioned above: 1) Studies in animals indicate that melamine is rapidly absorbed from the gastro-intestinal tract and rapidly eliminated from the body with a plasma-half-life of a few to several hours. 2) The major route of elimination is via the urine, and the limited information available suggests that the substance is hardly metabolised at environmentally relevant doses.

9.2.2 Carcinogenicity/chronic toxicity

The International Agency for Research on Cancer (IARC) has classified melamine as Group 3 (not classifiable as to its carcinogenicity to humans), based on inadequate evidence in humans for carcinogenicity, but sufficient evidence in experimental animals for its carcinogenicity under conditions in which it produces bladder calculi (IARC 1999).

In a 2-year study, F344 rats were administered melamine in the diet for 2 years, at doses of 0, 126/262, or 263/542 mg/kg bw/day in males/females, respectively. Transitionalcell carcinomas in the urinary bladder of male rats occurred at a significantly (p less than or equal to 0.016) higher incidence in the high dose group (8/49) than in the controls (0/45). There was also a statistically significant association (p less than 0.001) between bladder stones (observed in 10/49 males) and bladder tumours in male rats fed melamine at the high dose. Urinary bladder tumours were not observed in the lowdose (126 mg/kg bw/day) male rat group, while bladder stones were observed in only one of 50 rats in this low dose group (US NTP 1983; Melnick et al. 1984). Due to the statistically significant association between bladder stones and bladder tumours at the high dose (263 mg/kg bw/day), a re-evaluation of the histopathology from this study was conducted. The results showed a significant increase in the incidence of reflux nephropathy in male rats [7/50 vs. 1/49 in controls] but not of bladder stones [1/50 vs. 0/45 in controls] at 126 mg/kg bw/day (Hard et al. 2009), which suggests that increased duration of exposure to melamine at these lower doses does not result in carcinogenicity.

In another 2-year study conducted in an unnamed strain, rats were administered melamine in the diet at doses of 0, 67 or 667 mg/kg b/day. An increase in the incidence urinary bladder stones associated with an increased incidence of benign papillomata, was reported (American Cyanamid 1955).

F344 rats were administered melamine in the diet for 24-30 months at doses of 0, 5/5, 25/50, or 50/100 mg/kg bw/day in males/females, respectively. An increased incidence of bladder tumours was not observed. Although a dose-related trend for dilated glands in glandular gastric mucosa and inflammation in non-glandular gastric mucosa was observed at 5 mg/kg bw/day and higher, it was not specified whether this trend applied to one or both sexes in the secondary source (OECD 2002). However, the secondary source stated that the NOEL was thought to be the high dose (Hazleton Laboratories 1983 cited in OECD 2002).

Two 36-week studies were conducted on male F344 rats only; in one, animals were administered melamine in the diet at doses of 0, 110, 367 or 1100 mg/kg bw/day (Okumura et al. 1992), and in the other, animals were administered melamine in the diet at doses of 0, 430 or 1200 mg/kg bw/day (Ogasawara et al. 1995). In both studies, a dose-related increase in the incidence of transitional cell/urinary carcinomas and bladder papillomas was observed, which was associated with dose-related increases in the incidence of papillary/nodulary hyperplasia of the bladder epithelium. These increased incidences, along with a nondose related increase in bladder stones, resulted in the determination of a LOAEL of 110 mg/kg bw/day in the Okumura et al. (1992) study. Okumura et al. (1992) observed a significant statistical correlation between the incidence of bladder stones and tumours, and concluded that melamine-induced calculi can induce carcinomas in the urinary bladder. Ogasawara et al. (1995) determined that the bladder stones were composed of equal molar ratios of melamine and uric acid, and concluded that proliferative lesions of the urinary tract of F344 male rats were directly due to the irritative stimulation of the calculi, and not to molecular interactions between melamine itself or its metabolites with the bladder epithelium.

B6C3F1 mice were administered melamine in the diet for 103 weeks at doses of 0, 327/523 or 688/1065 mg/kg bw/day in males/females, respectively, which was followed by two weeks of no treatment with melamine. No carcinogenic effects were observed in this study (US NTP 1983; Melnick et al. 1984).

In summary, five carcinogenicity studies have been conducted in rats and one in mice; in all cases, melamine was administered through the feed of the animals. In 4 of the rat studies, bladder tumours or papillomas were observed at doses ranging from 263 to 1200 mg/kg bw/day. In the one study where tumours were not observed, male and female Fischer 344 rats had been exposed to melamine in the diet for 24-30 months at levels of 5 to 100 mg/kg bw/day (Hazleton Laboratories 1983). The four other rat studies were conducted in both sexes of F344 rats at doses of 126 to 542 mg/kg bw/day for 2 years (followed by 2 weeks untreated), in both sexes of an unnamed strain of rats at 67 or 667 mg/kg bw/day for 2 years, and in male F344 rats at doses of 100 to 1100 or 1200 mg/kg bw/day in two different studies in which the animals were exposed for 36 weeks followed by 4 weeks of no treatment with melamine. In all cases, bladder tumours were observed in male rats for three of the studies but one study did not indicate whether the increased incidences of bladder papillomas observed at 667 mg/kg bw/day, occurred in one or both sexes (American Cyanamid Co. 1955; US NTP 1983; Melnick et al. 1984; Okumura et al. 1992; Ogasawara et al. 1995). No carcinogenic effects were observed in a 2-year mouse feeding study at melamine doses of 327 to 1065 mg/kg bw/day.

9.2.3 Genotoxicity

Many in vitro genotoxicity studies have been conducted on melamine. All reverse mutation studies conducted with several strains of S. typhimurium, a bioluminescence test using Photobacterium phosphoreum, and a mutation assay using S. cerevisiae, were negative for gene mutation, both with and without activation (Seiler 1973; Litton Bionetics 1977a; American Cyanamid Co. 1981; Mast et al. 1982b; Haworth et al. 1983; Zeiger 1987; Elmore and Fitzgerald 1990; Ishiwata et al. 1991). Gene mutation assays in mouse lymphoma and Chinese hamster ovary (CHO) cells were also negative with and without activation (Mast et al. 1982b; McGregor et al. 1988). Two chromosome aberration assays and one sister chromatid exchange assay in CHO cells were negative with and without activation (American Cyanamid Co. 1982b; Galloway et al. 1987). Four unscheduled DNA synthesis studies, three in rat hepatocytes and one in E. coli, and one SOS/umu test in S. typhimurium, were all negative with and without activation (Litton Bionetics 1977c; American Cyanamid Co. 1982b; Mirsalis et al. 1983; Yasunaga et al. 2004). One non-standard test, which measured lambda prophage induction in E. coli as an indicator of DNA damage, was positive both with and without metabolic activation (Rossman et al. 1991). There were two in vivo micronucleus assays; one in male and female mice administered 1000 mg/kg bw of melamine via oral gavage, and the other in male mice administered 500, 1000, or 2000 mg/kg bw/day of melamine for 3 days via intraperitoneal injection. In both cases, results were negative for chromosomal aberration in the bone marrow and peripheral blood (Pharmakon Research 1981; Mast et al. 1982a; Shelby et al. 1993). Overall, the genotoxicity database indicates that melamine is not genotoxic.

9.2.4 Carcinogenic mode of action

The mode of action for induction of the observed tumours has not been fully elucidated. It has been postulated, however, that the malignancies in the urinary bladder are based on a threshold mechanism due to reactive hyperplasia that develops in response to a localized tissue irritation effect, which then progresses to bladder neoplasia, and is supported by lack of any mutagenic or genotoxic activity in standard assays (WHO 2009). WHO (2009) also noted that renal papillary mineralization was reported in some studies, but it is unknown if such mineralization may slough and provide a nidus for stones to form in the bladder. As shown under "Repeatdose oral toxicity", a recent study by Sun et al. (2014) showed that bladder hyperplasia and calculi significantly or completely regressed in mice during withdrawal periods of 8 or 42 days after they were fed melamine in the diet for periods of 14 or 56 days. This is strong support for the threshold mechanism of induction of bladder tumours.

9.2.5 Repeatdose oral toxicity

In addition to the chronic toxicity/carcinogenicity studies, many repeatdose oral studies have been conducted in rats, mice, rabbits, cats and dogs for periods ranging from 7 days to 36 weeks. In a 7day oral feeding study in rats, scattered crystals were observed in renal tubules at the one dose tested, 200 mg/kg bw/day (Jacob et al. 2011). In 14day oral studies in rats (one via gavage, the other via the diet), one study did not find effects at the highest dose tested, 240 mg/kg bw/day (Kobayashi et al. 2010), and the other showed hard crystalline solids in the urinary bladder of males and females at doses of 835 and 1668 mg/kg bw/day and higher, respectively (both sexes dosed at 0, 417, 835, 1251, 1668 or 2500 mg/kg bw/day). The NOAEL in this study was 417 mg/kg bw/day (US NTP 1983).

Studies of 28 days in rats resulted in observations of dosedependent increases in urinary bladder calculi (containing melamine) and hyperplasia, crystalluria and excretion of acid urine at doses of 266 to 12,678 mg/kg bw/day of melamine in an oral feeding study in rats (RTI 1982; American Cyanamid Co. 1984), as well as observations of an influence on the hippocampus, which induced learning and memory deficits in a study in which rats were gavaged with melamine at 300 mg/kg bw/day (An et al. 2011; Yang et al. 2011). In another 28day gavage study in rats, kidney microstructure was damaged and clinical chemistry parameters were significantly changed in serum (blood urea nitrogen, creatinine), kidney (glutamate, lactate, choline, glucose, amino acid, 3-hydroxybutyrate, pyruvate), liver (Nacetylglycoprotein, choline, creatine, lactate, trimethylamine-N-oxide, glutamate, glucose), and urine (succinate, citrate) at doses of 250 to 1000 mg/kg bw/day (Sun et al. 2012). In the oral feeding studies, a NOAEL of 133 mg/kg bw/day was determined by RTI (1982), whereas no adverse effects were observed at doses of 40 to 357 mg/kg bw/day (American Cyanamid Co. 1984).

For other species, the doses tested resulted in i) no adverse effects observed in cats treated with doses up to 181 mg/kg bw/day in an 11day feeding study (Puschner et al. 2007), ii) no adverse effects observed following administration of 126 mg/kg bw/day (only dose tested) in 1 to 4-week feeding studies in both rabbits and dogs (Lipschitz and Stokey 1945a,b), and iii) a NOAEL of 3000 mg/kg bw/day, based on hard crystalline solids in the bladders of mice dosed at 6000 mg/kg bw/day in a 14day oral gavage study (US NTP 1983).

In mice, short-term studies were conducted to analyze the relationhip between bladder hyperplasia and calculi. Three-4 wk old or 5-6 wk old male and female mice were fed melamine in the diet at doses of 0 or 9373 ppm, equivalent to 0 or 1218.5 mg/kg bw/day, respectively (dose conversion as per Health Canada 1994) for 14 days or 14 days with recovery periods ranging from 4 or 8 days (5-6 wk mice) to 42 days (3-4 wk mice). Another group of 3-4 wk mice were fed melamine in the diet at the same doses for 56 days or 56 days with a 42day recovery period. Bladder epithelial hyperplasia (BEH) and bladder calculi incidence was 100% in all treated groups with no recovery period. BEH regression was observed toward more regression/significant regression in mice dosed 14 days with 8 days compared to 4 days recovery, and there was significant (60-63%) and/or complete (38-40%) regression in all mice dosed 14 or 56 days with a 42 day recovery. With the rapid regression, bladder calculi completely disappeared. Regression of BEH initiated soon after melamine withdrawal, and the regression occured through rapid ageing/apoptosis of cells in the superficial regions of BEH regression tissue (Sun et al. 2014).

Three different 13-wk feeding studies in rats all showed dose-related increases in urinary bladder stones at doses ranging from 63 to 1500 mg/kg bw/day in both sexes, and also increased calcareous deposits in the kidney proximal tubules. The lowest LOAEL was 63 mg/kg bw/day (lowest dose tested) based on the above effects. Relative incidences of bladder stones in both sexes were not changed when rats were administered diet at 1500 mg/kg bw/day, with or without the addition of 1% ammonium chloride in the drinking water (US NTP 1983; Melnick et al. 1984). Two 36-week feeding studies in male rats at doses ranging from 110 to 1200 mg/kg bw/day resulted in a dose-related increase in hyperplasia of the bladder epithelium and nondose related increase in bladder stones, as well as decreased body-weight gain at 430 mg/kg bw/day and higher (Okumura et al. 1992; Ogasawara et al. 1995). For other species, the lowest critical effect levels observed in subchronic studies were, i) LOAEL of 1600 mg/kg bw/day (lowest dose tested) based on decreased body weights in males in a 13-week oral feeding study in mice (US NTP 1983; Melnick et al. 1984), and ii) LOAEL of 1200 mg/kg bw/day (only dose tested) based on crystalluria observed after 60-90 days in a 1-year feeding study in dogs (American Cyanamid Co. 1955).

A few studies have been conducted to determine composition of calculi in exposed rats. Male rats were fed melamine in the diet at doses 0, 0.1 or 1.0% (equal to 0, 84.8 or 863 mg/kg bw/day) for four weeks. At the top dose, stones were observed in the urinary tract in 45% of the rats, urine volume was increased, and several urinary parameters were affected, but there was no effect on urine pH. Composition of the stones were 99 -100% melamine with 0.1% uric acid. The stone composition of a 10 -month old infant who had ingested melamineadulterated formula was also analyzed and found to show a ratio of 1:2 melamine:uric acid. The difference in stone composition between the human infant and those of the rats was explained by differences in urine pH between human infants (5.0 -6.5) and rats (7.0-8.0), which would result in urine uric acid in the rats forming as urate (much greater than 90 %), and thus little free uric acid could complex with melamine (Cong et al. 2014a,b). Male rats were administered 20,000 ppm (equivalent to 1800 mg/kg bw/day) melamine in the diet for 13 weeks. All rats developed bladder stones and 7/10 rats showed haematuria. Bladder stones were composed mainly of melamine and a small amount of proteins, of which 1051 proteins were identified. Gene Ontology classification of the identified proteins showed that most were from injured cells (Liu et al. 2012). The above short-term and subchronic studies indicate a difference in stone composition (almost 100% melamine) from the equal ratio of melamine and uric acid determined in the 36-wk study in male rats conducted by Ogasawara et al. (1995; see "Carcinogenicity/Chronic Toxicity"). This difference may be due to differences in duration of exposure to melamine or due to the different analytical techniques used by the different authors for determining calculi composition.

9.2.6 Human studies

In humans, a large retrospective casecontrol study was conducted comparing 683 children with nephrolithiasis (presence of calculi in the kidney) with 6,498 children without nephrolithiasis aged less than 3 years in Beijing hospitals and their exposure to melamine via adulterated formula (Li et al. 2010). The children in this study were exposed to 4 of 22 brands of melamineadulterated formula sold in Beijing, and were part of a larger city sample size population of 41 000 children subjected to a Children's Health and Feeding Status survey. In general, the adjusted odds ratios between melamine dose and nephrolithiasis increased with greater daily level of melamine intake (from 1.7 to 11.3 for daily melamine intakes ranging from greater than 0-0.2 mg/kg bw/day to greater than 102.4 mg/kg bw/day), and also increased with the increasing duration of exposure. In children exposed to melamine levels of less than 0.2 mg/kg bw/day, the adjusted odds ratio expressing the risk for nephrolithiasis was still 1.7 times higher than in those without melamine exposure (Li et al. 2010; EFSA 2010). There were several limitations associated with this study: the reported melamine intakes were based on intakes that were not measured but retrospectively calculated from consumption data; the recruitment of children was done in two phases instead of one; the reference population could be defined in more than one way (6500 children or a larger group based on 41 000 children); and the authors provided no information about the distribution of the individually calculated exposure levels when aggregating the exposure data into exposure intervals (EFSA 2010).

A casecontrol study of children and pregnant women was conducted in Hong Kong. In project one, 152 pregnant women were recruited in 2008, 74 with a dietary history of exposure to melaminecontaminated food products and 78 age-matched controls who did not have a history of consuming melamine contaminated food products. Median daily exposure of the melamine group was 0.0015 (range, 0.0001-0.08) mg/kg bw/day. When samples from 20 patients with the highest melamine exposure were compared to 20 control patients, there was no significant difference in melamine concentrations in all the biological samples (mother urine [median = 1.3 vs. 1.2 μg/mmole creatinine in controls], blood [median less than 5 ppb in both groups], placenta, breast milk [median less than 50 ppb in both groups], amniotic fluid and cord blood; neonate urine [median less than 5 ppb in both groups]). In project two, 302 children under 12 years with prolonged melamine-tainted milk product exposure (greater than 0.2 mg/kg bw/day) who had persistent urinary abnormalities and/or clinical features suggestive of renal diseases, and 203 age-matched controls with no history of melamine-tainted milk product consumption were recruited for analysis of urine neutrophil gelatinaseassociated lipocalin (NGAL), to determine its usefulness as a surrogate marker for early detection for kidney injury. Urine NGAL concentrations were not significantly different in the melamine-exposed and control groups, which suggested absence of renal tubular injury in the melamine-exposed children. One of limitations of this study was that melamine intakes were based on intakes that were not measured but retrospectively calculated from consumption data (Wong et al. 2013).

9.2.7 Developmental toxicity and fertility studies

Three oral developmental toxicity studies in rats were available. In pregnant rats orally gavaged with melamine during gestation days 6-20, developmental and maternal toxicity were observed at the top dose of 800 mg/kg bw/day (decreased fetal weights, increased incidence of skeletal variations and delay in fetal ossification; in dams, increased incidences of clinical signs and death, decreased body weight gain and kidney toxicity). No maternal or developmental toxicity were observed at lower doses (200 and 400 mg/kg bw/day) (Kim et al. 2011). Pregnant rats were orally gavaged with melamine during gestation days 10-20 and non-pregnant females were gavaged for 10 consecutive days at 1000 mg/kg bw/day. In both cases, effects included clinical signs of toxicity (listlessness, reluctance to groom, anorexia), decreased body-weight gain, increased kidney weights and renal lesions (tubular dilation with cellular necrosis) which correlated well with the incidence of renal crystals, and melamine was found in the amniotic fluid of pregnant rats. Developmental effects included increased numbers of early and late fetal deaths, and decreases in litter size, average fetal body weight, and average crown rump length (Stine et al. 2014). In pregnant rats fed melamine in the diet during gestation days 6-16, no developmental toxicity was observed but maternal toxicity was observed at the top dose of 1060 mg/kg bw/day (decreased body weight, blood in urine, indrawn flanks) (Hellwig et al. 1996).

A 17-week inhalation study in rats showed impaired liver function and effects on blood biochemistry parameters at concentrations of 0.058 and 0.5 mg/m³ melamine. Rats were mated after the 17-week exposure period and effects were noted in animals that had been exposed to 0.5 mg/m³ melamine (effects on spermatogenesis and fertility, and fetal deaths observed) (Ubaidellajev et al. 1993). Due to limited information on study protocol in the English translation of this Russian study, it is considered of limited use for hazard characterization.

9.2.8 Irritation and sensitization

Skin irritation studies in guinea pigs and rabbits were negative (American Cyanamid Co. 1955; Fassett and Roudabush 1963; BASF 1969a; Vernon et al. 1990; Rijcken 1995), whereas rabbits showed no to mild eye irritation upon exposure to melamine (American Cyanamid Co. 1955; BASF 1969a; Marhold 1972; Vernon et al. 1990). Melamine was not a skin sensitizer in guinea pigs (Fassett and Roudabush 1963); this was the only skin sensitization study identified in experimental animals. There are a number of human case reports on sensitization observed in occupational settings, as well as one volunteer study in workers. In both the volunteer study and the case reports, patients who did show contact allergy to products containing melamine-formaldehyde, showed no reaction when patch-tested with melamine alone (Isaksson et al. 1999; Fregert 1981; Soubrier and Burlet 1972; Aalto-Korte et al. 2003; Garcia-Gavin et al. 2008).

9.2.9 Noncarcinogenic mechanisms of toxicity

In terms of noncarcinogenic endpoints, potential mechanisms of toxicity on the urinary system and other physiological systems have been discussed in some reviews. The proposed mechanism of melamine-induced nephrotoxicity involves induction of oxidative stress and an inflammatory response triggered by renal crystals (EFSA 2010; Chu and Wang 2013; Rai et al. 2014). Kidney injury molecule-1 (KIM-1) was the top up-regulated gene in rats, with other proteins, such as clusterin and osteopontin, also showing increases in levels (Chu and Wang 2013). Kim-1 and blood urea nitrogen have also been proposed as biomarkers of melamine exposure in serum and urine (Dorne et al. 2013). Rai et al. (2014) and Chu and Wang (2013) pointed to studies which showed how melamine may affect the hippocampus of the brain, blood proteins/enzymes (see "Repeatdose oral toxicity"), sperm cells and that it can be transferred via the placenta and lactation (see "Developmental toxicity and fertility studies" and "Breast milk"). Dorne et al. (2013) noted that developmental or neurotoxic effects occur at doses higher than or subsequent to melamine-induced nephrotoxicity.

9.3 Characterization of risk to human health

Based principally on weight of evidence, assessments of international agencies (WHO (2009) and EFSA (2010)), and available information, critical effects associated with exposure to melamine are carcinogenicity and effects on the urinary system. There is evidence to show that these effects are not due to melamine per se but to its propensity to form calculi or crystals in the kidney and/or bladder and it is the irritative effects of these calculi that lead to other effects, including reactive hyperplasia and bladder tumours in rats.

Also, based on the collective information, melamine is not genotoxic, and a threshold mechanism for kidney specific carcinogenicity is supported.

The lowest overall LOAEL was identified in a 13-week feeding study in Fischer 344 rats, in which a dosedependent increase in the incidence of bladder calculi and increased calcareous deposits in the kidney (not dose-related) were observed in animals fed melamine at all doses tested, the lowest one being 63 mg/kg bw/day.

WHO (2009) calculated a benchmark dose (BMD) and its lower confidence limit (BMDL10), based on this 13-week oral study, of 104 and 35 mg/kg bw/day, respectively, for a 10% increased incidence of the observed effects (urolithiasis occurrence and incidence of hyperplasia of the bladder epithelium). The WHO (2009) then derived a tolerable daily intake (TDI) of 0.2 mg/kg bw/day, using this BMDL10 of 35 mg/kg bw/day in combination with a total uncertainty factor of 200, which comprised a factor of 100 for intra- and inter-species variability and an extra uncertainty factor of 2 to "fully account for the potential increased sensitivity of infants and for data uncertainties ". The resultant TDI for melamine was considered applicable to the whole population, including infants. At the time of the melamine infant formula incident of 2008, the World Health Organization (WHO) Collaborating Centre for Food Contamination Monitoring within Health Canada's Food Directorate participated in the WHO's expert toxicology meeting to review of melamine and related analogues. This consultation recommended a tolerable daily intake for melamine of 0.2 mg/kg bw/day, which Health Canada supported.

EFSA (2010) also calculated a BMD10 and its lower confidence limit (BMDL10) based on the same study, but applied different assumptions in application of the benchmark dose models than the WHO (2009), which resulted in slightly different values (41 and 19 mg/kg bw/day, respectively, for a 10% increased incidence of the observed effects). EFSA (2010) derived the same TDI of 0.2 mg/kg bw/day from these data for melamine using a default uncertainty factor of 100 (EFSA 2010).

The EFSA Panel also derived a BMD based on the epidemiological study by Li et al. (2010). They calculated a BMD10 of 1.1 mg/kg bw/day and a BMDL10 of 0.74 mg/kg bw/day for a 10% increased incidence of nephrolithiasis. Due to uncertainties in the study design and exposure estimates, the data were not considered robust enough by EFSA for use as the basis for deriving a TDI. However, EFSA considered the human BMDL10 of 0.74 mg/kg bw/day to provide supporting evidence for the adequacy of the TDI of 0.2 mg/kg bw/day derived from animal data (EFSA 2010). The epidemiological study information was not available when the WHO TDI was derived (WHO, 2009).

The oral BMDL of 35 mg/kg bw/day derived by the WHO (2009) is considered appropriate for use in the characterization of risk from chronic oral exposure to melamine as it is based on the study with the lowest LOAEL of 63 mg/kg bw/day, and it is protective of calculi or crystals formation, since long-term rat feeding studies showed evidence for bladder tumours at 263 mg/kg bw/day of melamine. As the bladder tumours are a result of a progression of events (bladder hyperplasia to irritation to neoplasia) from oral exposure to melamine, this BMDL is also protective of precursor events.

The main sources of exposure to melamine for the general population in Canada are expected to be from environmental media, food and from the use of consumer products.

Comparison of central tendency and upperbound estimates of intake, for formula fed infants (highest exposed group) with the BMDL10 of 35 mg/kg bw/day results in MOEs ranging from 1522 - 5833. These MOEs are considered adequate to account for the uncertainties in the exposure and health effects database. See Table 9-6.

Comparison of the upper bound estimate of toddler exposure from use of melaware with the BMDL10 results in an MOE of 313. Given the conservative nature of the assumptions (e.g. all food consumed would be warm and in contact with melaware dishware), exposure from use of melaware is expected to be lower and this MOE is considered adequate to account for uncertainties in the exposure and health effects database. See Table 9-6.

^a Mean estimates from environmental and food summed together (mean values for drinking water summed with mean food intake value for infants from Appendix B).

^b This range is based on a range of drinking water concentrations.

^c Estimate from table 9-3.

^d See table 9-5 for more information.

Biomonitoring intakes provide exposure estimates from all routes and sources of exposure. The highest melamine intakes, based on urinary biomonitoring from the US population, were 0.41, 0.79, and 0.62 μg/kg bw/day for the 12-19, 20-59, and 60 plus year old age groups, respectively. MOEs based on these intakes range from 44,300 to 85,400 (see table 9-6). Although biomonitoring intakes were also calculated for the 6-11 year old age group, given the small sample size (n=6) and uncertainty associated with all statistics derived from them, MOEs were not generated for these intakes.

Exposure of the general population to melamine in Canada may also occur through the use of consumer products, i.e., dermal exposure to foam products, and oral exposure to toddlers from mouthing foam products containing melamine. No repeated dose dermal toxicity studies were identified and the oral 13-week feeding study in rats, which is the basis for BMDL10 of 35 mg/kg bw/day, was used for characterization of risk from both oral and dermal exposure to melamine. MOEs for exposure from foam products are outlined in table 9-7.

Given that these MOEs are based on the BMDL10, the margins of exposure from use of consumer products are considered adequate to account for uncertainties in the exposure and health effects databases.

With regard to the foam product scenario, this assessment is consistent with the US CPSC (2006) conclusion that "melamine-treated foam is not expected to present a hazard to consumers".

Finally, regarding exposure from do-it-yourself (DIY) products, given the rationale outlined in section 9.1 (negligible vapour pressure, low dermal absorption, low acute toxicity, etc.) dermal and inhalation exposures to melamine from one time use of DIY products is determined to be a negligible risk. Therefore, margins of exposure were not generated for these products.

9.4 Uncertainties in evaluation of risk to human health

Overall, the confidence of estimates of concentrations of melamine in the environment is considered to be moderate to high. There was sufficient empirical data on melamine concentrations in foods available in Canada, including data on background concentrations. Although no Canadian data were available for concentrations in drinking water or dust/soil, the limited drinking water and soil data available were considered to be upper bound. The confidence in the estimates of daily intake from environmental media is moderate based on moderate to high confidence in the estimates of melamine concentrations in environmental media.

A number of generally conservative assumptions were made in deriving dietary exposure estimates for melamine which likely resulted in overestimating actual daily exposure to melamine from food. True dietary estimates for concentrations of melamine in food would remove the use of assumptions in this assessment.

There are also uncertainties in the assessment of exposure from melaware, as assumptions regarding frequency of use and type used were made. The conservative nature of these assumptions is likely to overestimate the chronic dietary exposure to melamine.

There is moderate confidence in the estimates of daily intake based on urine biomonitoring data. There are several uncertainties with determining intake based on urine samples from the US population, such as routes of exposure and timing of exposure in relation to timing of sampling and the assumption that exposure conditions are the same for Canadians as they are for the American population that was sampled. There is more confidence in estimates derived from geometric mean concentrations of spot urine samples rather than those derived from upperbound concentrations (i.e. 95th percentile) because upperbound spot urine concentrations probably overestimate longer-term average exposure levels given the within-individual temporal variability in biomarker concentrations (especially for fast clearing compounds like melamine). Finally, the assumption that all melamine measured in urine is associated with exposure to melamine, is considered to be conservative as melamine is also a metabolite (human and environmental) of the pesticide, cyromazine (see section 6).

There is uncertainty due to the high variability in daily urine volumes both between and within individuals, however a range of typical mean urine volumes identified from various sources was selected to account for this uncertainty. There is also significant uncertainty in the assumption that melamine levels in human urine represent an excretion of 60% of daily intake. It is uncertain as to whether the metabolism and excretion parameters are the same for humans as laboratory animals (dogs and/or rats), especially since there is inter-species variation in urinary excretion fraction. Also, there is evidence that 60% excretion may be a result of high doses and when low and environmentally relevant doses are used, the fraction excreted in urine may approach 90-100%.

The confidence in the toxicity database for melamine is considered to be moderate to high, as sufficient information is available to address effects that may be of concern and identify critical endpoints based on oral exposures, as well as sufficient information from human studies to indicate that the exposure route of concern is oral. Although there is strong evidence for a threshold mechanism for development of bladder tumours in experimental animals, fully elucidated modes of action for induction of the observed tumours have not been identified. There were only very limited studies via the dermal and inhalation routes and adequate critical effect levels for such studies could not be determined.

There is low confidence in the estimates of exposure from mouthing of foam objects and dermal exposure to foam furniture and mattresses, based on lack of data on a melamine-specific migration rate from foam, which was subsequently extrapolated for melamine based on the migration behaviour of other flame retardants. However, assumptions made in estimating exposure for these scenarios are considered highly conservative.

There is also uncertainty in the characterization of risk from chronic exposure based on the limited occurrence and toxicological information on co-exposure to melamine and cyanuric acid (for additional information on cyanuric acid, see Health Canada 2015).

• Depending on the purification process, melamine may contain different levels of structurally related substances such as cyanuric acid;
• Cyanuric acid residues may occur in food as a result of the use of dichloroisocyanurates in disinfection agents, especially when used for water;
• Due to its physicochemical properties, melamine can form complexes with its structural analogues and with other substances such as cyanuric acid. Complex formation is highly pH dependent.

10. Proposed conclusion

Based on the information presented in this draft screening assessment, it is proposed to conclude that melamine is not entering 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, or that constitute or may constitute a danger to the environment on which life depends.

On the basis of the adequacy of the margins between estimates of exposure and critical effect levels in experimental animals, it is proposed to conclude that melamine does not meet the criteria under paragraph 64(c) of CEPA as 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.

It is therefore proposed to conclude that melamine does not meet any of the criteria under section 64 of CEPA.

References

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Appendices

Appendix A: Modelled degradation results for melamine

Abbreviations: N/A, not available

^a Estimation is based on a 12-hour day, and a mean tropospheric OH concentration of 1.5x10⁶ OH/cm³.

Abbreviations: N/A, not available.

^a Model does not provide an estimate for this type of structure.

^b EPI Suite (2010).

^c Output is a numerical score from 0 to 5.

^d Output is a probability score.

Appendix B: Upperbounding estimates of daily intake of melamine (μg/kgbw per day) by the general population of Canada from food, water and dust

NA = not available.

^a The daily intake from food is based on a semi-probabilistic assessment; mean intake is included here to aid in discussion of table 9-6. The semi-probabilistic assessment results are discussed in the text in section 9.1.1, and presented in table 9.1.

^b Based on less than 1 year old age group instead of 0-6 months; includes both formula-fed and not formula-fed infants.

^c Based on 1-4 year old age group instead of 0.5-4 years.

^d No data were identified on concentrations of melamine in Canadian breast milk. In Turkey, melamine was measured in the breast milk of 77 healthy lactating mothers. Melamine was detected in 21% of the 77 samples, with concentrations ranging from 10.1 to 76.4 μg/L (mean: 27.1 μg/L) melamine. The mean and maximum concentrations for melamine in breast milk was used in the estimate of daily intake.

^e Assumed to weigh 7.5 kg, to breathe 2.1 m3 of air per day, to drink 0.8 L of water per day (powdered formula fed) or 0.2 L/day (not formula fed) and to ingest 30 mg of soil per day (Health Canada 1998).

^f Assumed to weigh 15.5 kg, to breathe 9.3 m3 of air per day, to drink 0.2 L of water per day and to ingest 100 mg of soil per day (Health Canada 1998).

^g Assumed to weigh 31.0 kg, to breathe 14.5 m3 of air per day, to drink 0.4 L of water per day and to ingest 65 mg of soil per day (Health Canada 1998).

^h Assumed to weigh 59.4 kg, to breathe 15.8 m3 of air per day, to drink 0.4 L of water per day and to ingest 30 mg of soil per day (Health Canada 1998).

ⁱ Assumed to weigh 70.9 kg, to breathe 16.2 m3 of air per day, to drink 0.4 L of water per day and to ingest 30 mg of soil per day (Health Canada 1998).

^j Assumed to weigh 72.0 kg, to breathe 14.3 m3 of air per day, to drink 0.4 L of water per day and to ingest 30 mg of soil per day (Health Canada 1998).

^k No data were identified on concentrations of melamine in Canadian drinking water. However, concentrations of melamine in drinking water sourced from various areas around the world ranged from 10 to 200 μg/kg (mean and median = 50 μg/kg) based on 20 samples of tap water sampled by industry and reported to EFSA (2010). The mean and maximum concentrations for melamine in drinking water was used for exposure characterization.

^l No data on concentrations of melamine in dust and no data on melamine concentrations in North American soils were identified. However, in China, soils were tested at 100 m and approximately 150 km away from melamine manufacturing factories. At 100 m away, melamine concentrations in soil ranged from nondetect to 41.1 mg/kg. At approximately 150 km away from the factories, concentrations in farmland soil ranged from nondetect to 0.176 mg/kg (Qin et al. 2010).Since concentrations measured further away than close to a melamine manufacturing facility would be more representative of melamine soil concentrations in Canada, the maximum concentration in farmland soil measured at 150 km away from the manufacturing facility was used in a deterministic estimate of daily intake.

Appendix C: Summary of melamine occurrence data used to estimate dietary exposure and dietary assessment methodology

^a Data sourced from Tittlemier et al. 2009; Tittlemier et al. 2010a; Tittlemier et al. 2010b.

^b Samples where melamine was not detected were assigned a value equivalent to the limit of detection of 4 μg/kg LOD; limit of detection.

Dietary assessment methodology and assumptions

Food consumption data were obtained from the 2004 Canadian Community Health Survey (CCHS) cycle 2.2 (Statistics Canada 2004). Measured and self-reported body weights collected through the CCHS were also used. If consumption figures for certain foods were not available in the CCHS (milk coffee or tea, energy bar), closely related foods were used (instant coffee or tea, granola bars) and certain food types which were analyzed for melamine due to possible presence of milk protein, were used to represent concentrations in all these food types (e.g. chicken, sausage, and cookie products). In both these cases, exposure may be overestimated due to the higher frequency of consumption of the surrogate foods or due to the presence of melamine in milk protein but not in other parts of the food type. Similarly, the melamine concentrations detected in a limited number of processed spinach, potato, mushroom, onion, and tomato products were conservatively used to represent the melamine concentrations in all food products containing those vegetables, including the fresh vegetables.

Appendix D: Exposure estimates of melamine from products

Based on the available information, dermal exposure intakes were estimated for direct contact with foamcontaining mattresses and related manufactured items for young children and adults. Oral exposure estimates were also derived for young children mouthing (sucking) on foam manufactured items intended for children. The exposure parameters and values used to estimate exposures are presented in Tables D-1 and D-2, and are based on conservative assumptions.

Uptake = [SA × SCF × M × ED × DA] / BW

^a For this scenario, it is assumed that an individual is wearing shorts and a t-shirt. The surface area of exposure is based on exposure to a fraction of the lower limbs and the back of the head. The surface area of the lower limbs (Health Canada 1995) was multiplied by one third to account for the triangular shape of limbs, where only one side is directly in contact with the mattress (CPSC 2006b). The surface area of the head (Health Canada 1995) was multiplied by a factor of 0.5 to represent exposure to the back of the head only.

^b o melamine-specific skin contact factor, i.e., the fraction of substance on a surface adhering to skin, was identified in the literature. As such, a value of 0.13, an average of multiple substances (i.e., malathion, glyphosate, permethrin and TRIS [tris-(2,3dibromopropyl) phosphate]) to various textiles in wet and dry simulations (US CPSC 2006), was selected.

^c Migration rate from foam to surface of upholstery (extrapolated from TBB and TDCPP migration rates as shown in table 9-5).

^d Exposure duration for sleeping was adjusted from durations reported in CPSC (2006) for leisure sitting to account for longer sleeping durations relative sitting.

^e See text under "Consumer Products", subheading "Do-it-yourself products".

^f Health Canada (1998).

^a Surface area based on professional judgment reflecting twice the surface area of the opening of a toddler's mouth.

^b The migration rate of 6.5 × 10^-3 mg/cm²/hr as presented in the dermal scenario were also used to estimate oral exposure.

^c The mouthing duration for children's foam products such as nap mats, car seats, small furniture was based on the duration for "other objects" in Norris and Smith (2002) cited in US EPA (2011).

^d Health Canada (1998).

Appendix E: Range of typical daily urine volumes

Appendix F: International melamine studies

The studies by Kong et al. (2011) and Wu et al. (2010a) are not comparable to the Panuwet et al. (2012) study because different units were used (ng/mL vs μg/mmol of creatinine). The study by Liu et al. (2011) shows concentrations ranging from less than the method detection limit (MDL) to 192 ng/mL in a total of 422 adult subjects from Taiwan. This is comparable to the range of concentrations found in 492 subjects from the US population (less than LOD - 161 ng/mL).

Wu et al. (2013) conducted a unique biomonitoring study, in which the urinary melamine concentration was measured in 12 Taiwanese adults, who had consumed hot noodle soup from both melamine and ceramic bowls at different periods. The total melamine excretion in urine was 8.35±1.91 μg 12 hr after consuming noodle soup from melamine bowls, and 1.31± 0.44 μg 12 hr after consuming noodle soup from ceramic bowls (urine volumes per person were not reported). Peak urinary excretion occurred at the greater than 4-6 hr period, and was approximately 6.8 μg/mmol creatinine (interpreted from figure A of article). With a reported half-life of 6 hrs urinary elimination of melamine, this translates to about 12.8 μg/mmol creatinine after 24 hrs. These values fall within the range of 0.02-20 μg/mmol creatinine of melamine in urine reported by Wu et al. 2010a for 22 adults in Taiwan shown in table 9.4b. Wu et al. (2013) stated that one brand of melamine bowl was chosen for this study, and it was one of 5 brands tested in the Chien et al. (2011) study (see section 9.1.1.6 "Migration from Melaware").