Benzyl-C12-14-alkyldimethylammonium chlorides

Toxicity to birds

Administrative data

Endpoint:

long-term toxicity to birds: reproduction test

Data waiving:

study scientifically not necessary / other information available

Justification for data waiving:

other:

Cross-reference

Cross-reference 1

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Based on the results of the read across studies and in line with the biocides assessment report, the test substance is also considered to be readily biodegradable.

Biodegradation in water:

readily biodegradable

Type of water:

freshwater

Study 1: A study was conducted to determine the biodegradation of the read across substance, C12-16 ADBAC (80% active in hydroalcoholic solution), in water according to OECD Guideline 301B (CO2 evolution test). Flasks containing inoculum from a household water-treating plant dosed with the equivalent of 5 mg C/L test or 20 mg C/L reference substances were maintained for 28 d. Testing at low concentrations, was required due to the toxicity of the read across substance towards the inoculum at higher concentrations. Biodegradability was calculated from the released CO2 over time in the test and reference flasks compared to the blank control (a flask prepared without test or reference substance). CO2 production in the blank (inoculum control) was 39.2 mg. Biodegradability in the reference flask was determined to be 88.9% after 28 d. Under the test conditions, the biodegradation of the read across substance in water was determined to be 95.5% after 28 d (CO2 evolution). The read across substance was considered to be readily biodegradable (van Dievoet, 2005).

Study 2: A study was conducted to determine the biodegradation of the read across substance, C12-16 ADBAC (50.1% active in water) in water according to OECD Guideline 301D (closed bottle test), in compliance with GLP. Secondary activated sludge was used in this experiment and the percentage of degradation (O2 consumption) was measured. Since the substance was toxic to microorganisms, it was tested in the presence of silica gel to reduce the concentration in the water phase. During the test period, the substance was released slowly from the silica gel. The validity of the test was demonstrated by an endogenous respiration of 1.3 mg/L at Day 28. Furthermore, the differences between the replicate values at Day 28 were less than 20%. The biodegradation of the reference substance, sodium acetate, at Day 14 was 78%. Finally, the validity of the test was shown by oxygen concentrations being > 0.5 mg/L in the bottles. Under the conditions of the study, the biodegradation of the substance was determined to be 63% at Day 28. The substance was considered readily biodegradable (van Ginkel and Stroo, 1992).

Further, the C12-16 ADBAC Biocides assessment report available published by the Italian authorities in June 2015, reported the two key studies summarised above and stated that “The reliability factor of US ISC study (van Dievoet, 2005)is 1. Therefore, the study by US ISC should be considered for the environmental risk assessment at product authorization stage. In conclusion, ADBAC/BKC is ready biodegradable being the 10-day window criterion met (OECD 301B). On the other hand, the EQC study (van Ginkel and Stroo, 1992) has a reliability factor of 2 because it cannot distinguish between the degradation of ADBAC/BKC and Propan-2-ol (solvent). If we follow the argument that Propan-2-ol is readily biodegradable and might contribute more to the oxygen consumption. This results in an overestimation of ADBAC/BKC, and the 14-day window criteria were not met (OECD 301D). Alkyl (C12-16) dimethylbenzyl ammonium chloride is readily biodegradable.”  

Based on the results of the read across studies and in line with the biocides assessment report, the test substance is also considered to be readily biodegradable.

In general, the use of silica gel in the key study on biodegradation is supported by the findings from van Ginkel 2008, which showed that silica gel was the best adsorbent as compared to lignosulphonic acid and humic acid (see belowFigure 1):

Figure 1:Biodegradation of C18 TMAC in the Closed Bottle tests without additions () and with 2 g silica per bottle (  ), 2.0 mg/L lignosulphonic acid ( ) and 2.0 mg/L humic acid ( ) (adapted from van Ginkel, 2008).

Overall, the results obtained with the test substance are in agreement with what is reported in the literature, as summarized below inTable 4.4.

Table 4.4. Compilation of ready biodegradability test results obtained with quaternary ammonium salts (adapted van Ginkel, 2007)

Substance	Test	Results at Day 28 (%)
Tetradecylbenzyldimethylammonium Chloride (C14 ADBAC)	MITI	>80
Decylbenzyldimethylammonium Chloride (C10 ADBAC)	Closed bottle	>60
Hexadecyltrimethylammonium Chloride (C16 TMAC)	Headspace Carbon Dioxide	75*
Octadecyltrimethylammonium Chloride (C18 TMAC)	Sturm test	>70
Cocotrimethylammonium (Coco TMAC)	Closed bottle	>60
Octylbenzyldimethylammonium chloride (C18 ADBAC)	MITI	>80

*Mean from 10 laboratories; also cited in OECD TG 310 (adopted on 23 March 2006)

In addition, several literature data are available to clarify the metabolic basis of degradation by micro-organisms.Benzyldimethylamine was found as first metabolite of alkylbenzyldimethylammonium salts degradation byAeromonas hydrophila, activated sludge and aPseudomonas spp. community (Patrauchan and Oriel, 2003; van Ginkel, 2004; van Ginkel, 2007; Tezelet al.,2012). Alkyl-N fission is therefore the most probable strategy to gain access to the carbon of the alkyl chain. The next step in the biodegradation of these quaternary ammonium compounds was the successive removal of the two methyl groups. Benzylamine formed, in turn, is converted into benzaldehyde and ammonium (Patrauchan and Oriel, 2003). In contrast to the alkylbenzyldimethylammonium salts biodegradation pathway reported by Patrauchan and Oriel, (2003), neither benzylmethylamine nor benzylamine were identified as metabolites by two enrichment cultures. Exposure of activated sludge to decylbenzyldimethyl­ammonium chloride probably selects for three microorganisms that utilize the alkyl chain, the aromatic moiety, and dimethylamine (van Ginkel, 2004). Kinetic assays demonstrated that benzylmethylamine and benzylamine were not intermediates of alkylbenzyldimethylammonium salts transformation by the enrichedPseudomonasspp. community (Tezelet al., 2012). Thus, benzyldimethylamine is thought to be transformed to dimethylamine and benzoic acid via debenzylation. Dimethylamine is degraded by the successive removal of both methyl groups resulting in the formation of ammonium (Large, 1971). Both the pure and mixed culture studies showed that the degradation of the alkyl chain of alkylbenzyldimethylammonium chloride results in the formation of water, carbon dioxide and ammonium (seeFigure 2).

Alkylbenzyldimethylammonium salts are biodegraded by microorganisms first utilizing the alkyl chain. Subsequently, the methyl and benzyl groups are removed. 

 

Figure 2: Biodegradation pathway of alkyltrimethylammonium salts (van Ginkel, 2004, 2007) - See CSR

Further, according to the evidence presently available on the biodegradation rate, microorganisms readily oxidize the hydrophobic alkyl chains of the cationic surfactants, which is followed by a slower oxidation of the hydrophilic moiety (the corresponding amines) (van Ginkel, 2004). The above biodegradation process for the two moieties plays a key role in the differences in the results between the different cationic surfactants. However, based on the available experimental data and literature evidence, the alkyl chains and the trimethylamine of the test substance is readily biodegradable.

Overall, considering all the above information together, the test substance is considered to be readily biodegradable undergoing complete mineralization.

Cross-reference 2

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Based on the most recent and radiolabelled aerobic biodegradation study in soil with the read across substance, C12-16 ADBAC, the transformation of the C12 and C14 carbon chains of the substance was considered to be rapid with DT50 values ranging from 2.2-28.7 days with the SFO model and 1.6 – 23.3 days with the FOMC model at 20°C.​ Further, in the biocides dossier, a weighted estimate of the DT50 value at 12°C was extrapolated for C12-16 ADBAC by assuming the highest allowable concentrations for the major chains. These calculations resulted in the estimated FOMC DT50 of 17.1 days at 12°C and SOF DT50 of 19.2 days at 12°C. The DT50 of 17.1 days at 12°C based on the biphasic model (FOMC) showing better visual fit and lower error (c²)compared to the SFO model was used further for risk assessment.

Therefore, in line with the biocides dossier, the DT50 of 17.1 days at 12°C derived for the read across substance based on the biphasic model (FOMC) also has been considered further for hazard/risk assessment of the test substance. 

Half-life in soil:

17.1 d

at the temperature of:

12 °C

Study 1:

A study was conducted to determine the aerobic transformation/dissipation in the soil of the read across substance, C12 -16 ADBAC (radiochemical purity: 98.5%), according to the OECD Guideline 307, in compliance with GLP. Four different standard soils (LUFA 2.2, 2.3, 2.4 and 5M, field fresh sampled), varying in their organic carbon content, pH, clay content, cation exchange capacity and microbial biomass, were treated with [ring-U-14C] Benzalkonium chloride. Soil samples were incubated in the dark under aerobic conditions for up to 128 days under controlled laboratory conditions. After appropriate time intervals, soil samples were extracted, and the extracts were analysed for read across substance and transformation products to calculate DT50 and DT90 values. The mineralization was determined by trapping and analysis of the evolved 14CO2. Non-extractable residues (NER) were determined after combustion of the extracted soil samples. The total radioactivity of the soil extracts, the extracted soil (NER) and evolved 14CO2 was determined by LSC. Read across substance and transformation products in the soil extracts were analysed by LC-FSA (radio-HPLC). Evaluation of the transformation pathway was done by LC-HRMS. 

Transformation of the C12 chain of the read across substance [ring-U-14C]Benzalkonium chloride was rapid in all four soils. The transformation of the C14 chain started after a short adaptation phase but was thereafter rapid as well. Within 7 - 21 days the concentration of the C12 chain decreased from initially 67.2 – 69.6% of applied radioactivity (AR) to < 20 % of AR. The concentration of the C14 chain decreased from initially 23.8 – 24.6 % of AR to < 10 % of AR within 10 – 36 days. Formation of NER started directly after application of the read across substance. Further formation of NER increased in parallel to the start of increased mineralisation, indicating that a major amount of NER is comprised by radioactivity incorporated in microbial biomass. At the test end, the biomass concentration was in the range of 1.46 – 2.62 % of soil organic carbon content in all four soils, indicating that viable microbial biomass was present throughout the incubation time. The mass balance was in the range 99.9 – 103.0 % at test start and 90.4 – 94.0 % at test end.

The predominant initial degradation step was the oxidative removal of the alkyl chain. Dimethylbenzylamine was determined as the major metabolite, the highest concentrations of dimethylbenzylamine were determined until Day 22, thereafter the concentrations deceased continuously until test end. Methylbenzylamine was transient and only present in traces. Benzylamine, a suspected metabolite, was not detected. Further metabolites containing partly degraded alkyl chains were all transient and were not detected or only <0.2 % of AR (soil 2.3) at the test end.

With regard to the kinetics, the transformation showed a slight bi-phasic pattern, therefore the ‘Single First Order Model’ (SFO) and the ‘First-Order Multi-Compartment Model’ (FOMC) were compared. Based on the visual fit and x2 error, the transformation of [ring-U-14C]Benzalkonium chloride met the requirements for both models well for all four soils. The calculated DT50 values with the Single-First-Order Model (SFO) for the dissipation of [ring-U-14C]Benzalkonium chloride were 2.2 – 8.7 days (C12 chain) and 6.1 – 28.7 days (C14 chain), the DT90 values were 7.2 – 28.8 (C12 chain) days and 20.2 – 95.4 days (C14 chain). The calculated DT50 values with the FOMC model for the dissipation of [ring-U-14C]Benzalkonium chloride were 1.6 – 7.2 days (C12 chain) and 5.5 – 23.3 days (C14 chain), the DT90 values were 15.0 – 48.8 days (C12 chain) and 35.8 – 164.3 days (C14 chain).

The read across substance is predominantly C12-ADBAC and C14-ADBAC, with low to negligible amounts of C16-ADBAC. The chain length distribution is defined as follows:C12 (35-80%), C14 (20-55%), C16 (0-15%). C16-ADBAC was not included in this study because it is present in very low amounts; there are technical difficulties with having sufficient radioactivity for substances present in small amounts relative to other constituents. C16-ADBAC would be expected to degrade by the same route but at a slower rate than its C12 and C14 counterparts, as degradation rate tends to decrease with increasing chain lengths.Under the study conditions, transformations of both C12 and C14 carbon chains of the read across substance were determined to be rapid in all four soils and the DT50 values were determined to be 2.2 – 8.7 days [C12 chain] and 6.1 – 28.7 days [C14 chain] with the SFO model and 1.6 – 7.2 days [C12 chain] and 5.5 – 23.3 days [C14 chain] with the FOMC modelat 20°C (Fiebig, 2019).

 

Further, in the biocides dossier, to account for the potential contribution of C16 ADBAC to the overall DT50 of ADBAC, a geometric mean of SFO and FOMC DT50s for C12 and C14 ADBAC in the four soils (as recommended in BPR Vol IV Part B and C) was calculated and converted to 12° using the following equation (DT50 (12°) = DT50 (20°) * e(0.08*(20-12)). This was followed by linear extrapolation of the geometric mean DT50s for C12 and C14 ADBAC, to estimate the DT50 for C16 ADBAC. See tables below:

SFO DT50s
	Soil	2.2	2.3	2.4	5M	Geo. Mean	Adj. to 12° C
	C12 ADBAC	2.2	3.3	6.2	8.7	4.4	8.4
	C14 ADBAC	6.1	8.9	12.9	28.7	11.9	22.6
	C16 ADBAC	--	--	--	--	--	36.7

 

FOMC DT50s
	Soil	2.2	2.3	2.4	5M	Geo. Mean	Adj. to 12° C
	C12 ADBAC	1.6	3.2	5.8	7.2	3.8	7.3
	C14 ADBAC	5.5	8.3	12.1	23.3	10.7	20.2
	C16 ADBAC	--	--	--	--	--	33.1

A weighted estimate of the DT50 of ADBAC (C12-C16) at 12°C was calculated by assuming the highest allowable concentrations of C14- and C16- ADBAC and the balance of C12-ADBAC (i.e., 12% C16, 52% C14 and 36% C12), which resulted in the following estimated DT50s:

SFO DT50 = 19.2d at 12°C; FOMC DT50 = 17.1d at 12°C

However, due to the relatively low levels of C16-ADBAC, the overall estimated DT50s were considered rather insensitive to the assumed DT50 for C16-ADBAC. The DT50 of 17.1 days at 12°C based on the biphasic model (FOMC) showing better visual fit and lower error was used further for risk assessment. Based on the results of the read across study, similar degradation potential and half-life is considered for the test substance.

 

Study 2:A study was conducted to determine the aerobic biodegradation of the read across substance, C12-16 ADBAC (50% active in water) in loamy soil, according to the US FDA Environmental Assessment Handbook, Technical Assistance Document 3.12 (1987). The study comprised two treatments: test and chemical blank control group, each with three replicates. The read across substance was added into biometers at a concentration of 10 mg carbon per 50 g soil using appropriate amount of deionised water required for bringing the soils to 50-70% of the moisture capacity. Loam was added to the biometers after the test solutions to facilitate uniform moistening of the soils by capillary action. The test was then incubated at 22 ± 3°C and run for approximately 90 d. The side tube of the biometer contained 20 mL 0.2 M KOH for absorbing carbon dioxide produced by the microorganisms. The theoretical CO2 production of the read across substance was calculated from its carbon content. The amounts of carbon dioxide were calculated by subtracting the mean carbon dioxide production in the test systems containing the read across substance and the mean carbon dioxide production level in the control blank. Biodegradation was calculated as the ratio of experimental carbon dioxide production to theoretical carbon dioxide production [ThCO2P]. Under the study conditions, there was 64% degradation of the read across substance after 70 days. This percentage of the theoretical carbon dioxide production presumes complete mineralization. The DT50 was estimated to be 40 days (Ginkel, 1994). Based on the results of the read across study, similar degradation potential and half-life is considered for the test substance.  ​ 

 

Based on the most recent and radiolabelled aerobic biodegradation study in soil with the read across substance, C12-16 ADBAC, the transformation of the C12 and C14 carbon chains of the substance was considered to be rapid with DT50 values ranging from 2.2-28.7 days with the SFO model and 1.6 – 23.3 days with the FOMC model at 20°C.​ Further, in the biocides dossier, a weighted estimate of the DT50 value at 12°C was extrapolated for C12-16 ADBAC by assuming the highest allowable concentrations for the major chains. These calculations resulted in the estimated FOMC DT50 of 17.1 days at 12°C and SOF DT50 of 19.2 days at 12°C. The DT50 of 17.1 days at 12°C based on the biphasic model (FOMC) showing better visual fit and lower error (c²)compared to the SFO model was used further for risk assessment. Therefore, in line with the biocides dossier, the DT50 of 17.1 days at 12°C derived for the read across substance based on the biphasic model (FOMC) also has been considered further for hazard/risk assessment of the test substance. 

Cross-reference 3

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

The results of the read across study, supported with the estimated BCF value for the test substance together with its ionic nature indicates a low bioaccumulation potential. The experimental BCF value of 79 L/kg ww from the read across study and the growth corrected kinetic biomagnification factor (BMFkg) value of 0.0463 based on read across to C18 TMAC, has been considered further for hazard/risk assessment. 

BCF (aquatic species):

79 L/kg ww

BMF in fish (dimensionless):

0.046

Study 1:A study was conducted to determine the aquatic bioaccumulation of the read across substance, C12 -16 ADBAC (30.64% active; 98.9% radiolabeled purity) inLepomis macrochirus(bluegill fish) under flow-through conditions, according to EPA OPP 165-4, in compliance with GLP. The blue gill fish were continuously exposed to a nominal concentration of 0.050 mg/L of the read across substance (equivalent to a measured concentration of 0.076 mg/L) in well water for 35 days, followed by transfer of 35 fish into flowing uncontaminated water for a 21-d depuration period. Sampling was carried out on Days 0, 1, 3, 7, 9, 10, 14, 21, 23, 28 and 35 for the exposure period and Days 1, 3, 7, 10, 14 and 21 for the depuration period. Water samples were collected on Day 8 of the exposure period and Day 16 of the depuration for analytic determination of the read across substance concentration. Radiometric analyses of the water and selected fish tissues revealed that the mean steady state bioconcentration factor (BCF) in the edible, non-edible and whole-body fish tissue during the 35 days of exposure to be 33, 160 and 79 L/kg. The half-life for non-edible tissue was attained between Days 14 and 21, while it could not be reached for the edible and whole-body fish tissues by the end of 21-d depuration period. By Day 21 of the depuration period, the 14C residues present on the last day of exposure in the edible, non-edible and whole-body fish tissues had been eliminated by 29, 60 and 44% respectively. Analysis of skin tissue after 35 d of exposure showed residue levels somewhat higher than those observed for edible tissue at the same sampling period, indicating that there is likely significant binding of 14C-ADBAC to the skins and scales of exposed bluegill, as expected behaviour of cationic surfactants. Under the conditions of the study, the whole body BCF of the read across substance was determined to be 79, indicating low potential to bioaccumulate (Fackler, 1989).  

Study 2:The Bioconcentration factor (BCF) value of test substance, C12 -14 ADBAC was predicted using regression-based and Arnot-Gobas BAF-BCF models of BCFBAF v3.02 program (EPI SuiteTMv4.11).The Arnot-Gobas method, takes into account mitigating factors, like growth dilution and metabolic biotransformations, therefore the BCF value using this method is generally considered to be more realistic or accurate. However, ionic, pigments and dyes, perfluorinated substances are currently excluded from the applicability domain of this model. In the case of the test substance, considering that it is a UVCB consisting of a mix of ionic (e.g., the quaternary ammonium salts) and non-ionic constituents (e.g., amines), the BCF values were predicted using the regression-based method for the ionic constituents and the Arnot-Gobas BAF-BCF method for the non-ionic constituents, using SMILES codes as the input parameter.The BCF values for the constituents ranged from 1.55 to 275.3 L/kg ww (log BCF: 0.19 to 2.44), indicating a low bioaccumulation potential. On comparing with domain descriptors, all constituents were found to meet the MW, log Kow and/or maximum number of correction factor instances domain criteria as defined in the BCFBAF user guide of EPISuite. Further, given that the major constituents are structurally very similar and vary only in the carbon chain length, a weighted average value, which takes into account the percentage of the constituent in the substance, has been considered to dampen the errors in predictions (if any). Therefore, the weighted average BCF value was calculated as 73.21 L/Kg ww (Log BCF = 1.86). Overall, considering either the individual BCF predictions for the constituents or the weighted average values, the test substance is expected to have a low bioaccumulation potential. However, taking into consideration the model’s training set and validation set statistics and the fact that the training set only contains 61 ionic compounds, the BCF predictions for the individual constituents are considered to be reliable with moderate confidence. 

Study 3: A study was conducted to determine the biomagnification (BMF) potential of the read across substance, C18 TMAC (purity 95%), following the principles of OECD TG 305. For the main study rainbow trout (Oncorhynchus mykiss) with an average weight of 5.42 g were fed test diets enriched with read across substance (23.6 mg/kg read across the substance in feed. The resulting treatment and one control group (each 40 animals) were tested simultaneously. The uptake phase of 14 days was followed by a depuration phase lasting 14 days. All animals were fed the non-spiked feed during the depuration phase. The concentrations of the read across substance in fish samples were determined by chemical analysis and all tissue concentrations were calculated based on a wet weight basis. Chemical analysis of the read across substance was performed by liquid chromatography with coupled mass spectrometry (LC-MS/MS). In the main study five animals of each group were sampled randomized on Day 7 and Day 14 of the uptake phase and after 10 h, 24 h, 2 days, 3 days, 7 days and 14 days of depuration. Biomagnification factor (BMF) and distribution factor were calculated based on the tissue concentrations measured at the end of the uptake phase. No mortality or abnormal behaviour of the test animals was observed during the main study. The experimental diets were accepted by the test animals and showed a decent digestibility as confirmed by the texture and appearance of the feces. One fish was euthanized at Day 25 due to injuries. The specific growth rates of the animals ranged from 1.95 to 2.71 %/d over the entire experiment. During the study, the feed conversion ratio (FCR) was 0.69 to 0.95. Fish were measured and weighed at the beginning of the experiment as well as at respective sampling time points to monitor growth and associated growth-dilution effects during the feeding study. Growth rate constants were determined separately for the uptake and depuration phases, for the treatments and the control group, using the ln-transformed weights of the fish. A subsequent parallel line analysis (PLA, as suggested by the OECD Guideline) resulted in no statistical differences between the uptake and the depuration phase among the treated groups with the read across substance. No statistically significant difference was detected with regard to the growth of the treated groups. Hence it was deduced that neither adverse nor toxic effects were caused by the enriched diets. As steady state seemed to be reached after 14 days of exposure, steady state biomagnification factors (BMFss) could be calculated as 0.02709 g/g, which showed that read across substance did not biomagnify after dietary exposure. In general, the GIT and the liver showed the highest values for the BMFk and BMFkg. The kinetic BMF (BMFk) and growth-corrected biomagnification factor (BMFkg) were calculated for the read across substance to be 0.0404 and 0.0463, respectively. Overall, it was concluded from the screening that ionization lowers the tendency of a chemical to bioaccumulate, compared to non-ionized chemicals. Aside from the well-known lipophobicity of ionized groups, fast depuration seems to be a major reason for the observed low biomagnification of ionic compounds, in particular anions. Fast depuration may happen due to rapid metabolism or conjugation of charged compounds, and future studies should test this hypothesis. Under the study conditions, the read across substance BMFss, BMFk and BMFkg values on whole body wet weight basis in rainbow trout were determined to be 0.02709, 0.0404 and 0.0463 g/g, respectively, suggesting low biomagnification potential (Schlechtriem, 2021). Based on the results of the read across study, a similar low biomagnification potential is expected for the test substance. 

This is further supported by the no bioaccumulation potential evidence observed in in the two toxicokinetic studies in mammals with the read across substance, C12-16 ADBAC (Selim, 1987 and Appelqvist, 2006). Also, the biocides assessment reports available from RMS Italy on C12-16 ADBAC, concluded the substances to show low potential for bioaccumulation, based on the results from the above study (Fackler, 1989). They further stated this finding to be in line with the mode of action of the c12-16 ADBAC, which mainly possesses irritant/corrosive properties (ECHA biocides assessment report, 2015).

Overall, the results of the read across study, supported with the estimated BCF value for the test substance together with its ionic nature indicates a low bioaccumulation potential. The experimental BCF value of 79 L/kg ww from the read across study and the growth corrected kinetic biomagnification factor (BMFkg) value of 0.0463 based on read across to C18 TMAC, has been considered further for hazard/risk assessment. ​

Cross-reference 4

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Based on the results of the read across study and in line with the C12-16 ADBAC biocides assessment report, the 16-d EC50 value of 277 mg a.i./kg dw of soil obtained forBrassica alba(mustard) due to effects on growth has been considered further for hazard/risk assessment. Additionally, in accordance with the ECHA R.7c guidance (2017), the 16-d NOEC value of 856.2 mg a.i./kg dw of soil obtained forTrifolium pratense(red clover) due to effects on growth can be considered as the long-term equivalent value.

Short-term EC50 or LC50 for terrestrial plants:

277 mg/kg soil dw

Long-term EC10, LC10 or NOEC for terrestrial plants:

856.2 mg/kg soil dw

Study 1:A study was conducted to determine the toxicity of the read across substance, C12-16 ADBAC (49.9% active in water) to terrestrial plants, according to OECD Guideline 208, in compliance with GLP. Three plant species:Sinapis alba(mustard),Trifolium pratense(red clover) andTriticum aestivum(wheat) were used. Using 0.5 L capacity plastic pots, the read across substance was first applied to natural soil at nominal concentrations of 0, 476.6, 856.2, 1540.9, 2772.2 and 4990.0 mg a.i./kg and to sand at nominal concentrations of 0, 28.8, 55.8, 93.4, 166.8 and 300.5 mg a.i./kg. This was followed by planting of 40 seeds per replicate of the three plant species. Analytical verification was performed for the read across substance. Three parameters: emergence, dry and wet weight of the plants were observed. Emergence was recorded daily until stabilisation. The plants in natural soil and sand were harvested 16 and 14 d respectively after 50% of the control seeds had been emerged. Wet and dry weight were determined immediately after harvesting. The test was considered as valid on the basis of percent emergence and further growth of the plant in the water control. The extraction of the active substance proved that the natural soil had a strong sorbing effect and the total recovery was not achieved even when acidified methanol was used as an extraction solvent. That was not the case with quartz sand. The LC50 values in natural soil based on effect on emergence were 3881, >4990 and >4990 mg a.i./kg dw of soil for mustard, red clover and wheat respectively; while those in sand were 130, 197, 234 mg a.i./kg dw soil. The corresponding NOEC values were 2772.2, 856.2, >4990 mg a.i./kg dw in natural soil and 55.8, 93.4 and 93.4 mg a.i./kg dw in sand. The EC50 values in natural soil, based on the effect on growth were 342, 309, 684 mg a.i./kg dw of soil (based on changes in wet weight) and 537, 634 and 1960 mg a.i./kg dw of soil (based on changes in dry weight) for mustard, red clover and wheat respectively, respectively; while those in sand were 31, 19, 105 mg a.i./kg dw of soil (based on changes in wet weight) and 73, 74 and 141 mg a.i./kg dw soil (based on changes in dry weight) of sand respectively. The difference in toxicity in the two substrates were correlated with the lower bioavailability of test substance in soil due to a stronger adsorption potential. Further, as the toxicity to terrestrial plants in sand is not representative of the natural environment, the EC50 in natural soil was considered as a reasonable worst case for representing toxicity terrestrial plant species. Under the conditions of the study, based on effect on emergence and wet weight changes (growth) red clover was identified to be the most sensitive species with lower NOEC and EC50 value of 856.2 and 309 mg a.i./kg dw soil respectively (Servajean, 2004).    

Study 2:  A study was conducted to determine the toxicity of the read across substance, C12-16 ADBAC (49.5% active in water) to terrestrial plants, according to OECD Guideline 208, in compliance with GLP. Three plant species:Phaeolus aureus(mung beans)Brassica alba(mustard) andTriticum aestivum(wheat) were used. Each plant species was sown into treated soil and assessed for 14 - 16 days following germination. For each species, groups of 40 seeds (eight replicate pots of five seeds) were sown into a garden loam soil treated with the read across substance. Untreated controls were also included. Treatment levels for the definitive study were based on the results of a preliminary range finding study. The dose levels of the read across substance used were 156, 313, 625, 1250 and 2500 mg a.i./kg dry soil for mung beans and 12, 37, 117, 375 and 1200 mg a.i./kg dry soil for mustard and wheat. After application and sowing, the pots were checked daily and the number of seedlings emerging recorded. Survival and sub-lethal effects were recorded every day following emergence. Plants were harvested 14-16 days after germination and the wet weights were measured. The plants were then dried before being re-weighed to obtain a dry weight measurement. There was no treatment-related effect on the germination and seedling survival of any of the plant species treated with the read across substance up to the highest tested concentrations. The growth inhibition occurred at higher rates of application for all the plant species. For mung bean, there was 25-40 and 50-75% inhibition at 1250 and 2500 mg a.i./kg, respectively. For mustard, there was 75-80 and >80% inhibition at 375 and 1200 mg a.i./kg, respectively and 50-75% for wheat at 1200 mg a.i./kg. Darker pigmentation was observed for all species at the higher rates of application. The 14-16 d EC50 values based on growth inhibition in mung beans, mustard and wheat were determined to be1900, 277 and 670 mg a.i./Kg dry soil respectively. Under the conditions of the study, based on effect on growth, mustard was identified to be the most sensitive species with lower EC50 value of 277 mg a.i./kg dw soil (Gray, 2004). 

Based on the above studies, same effect levels and low toxicity potential were concluded in the biocide assessment report on C12-16 ADBAC by RMS Italy. They further stated that:“The great deviation in the effects recorded in sand and natural soil can be attributed to the lower bioavailability of C12-16 ADBAC in natural soil caused by stronger adsorption to the soil particles as consequence of several binding processes. Since the results obtained in the test with silica sand are considered unrealistic worst case, only data from the tests conducted with natural soils are taken into account (this approach was agreed at TMII2013); among these, the most sensitive species was Brassica alba with an EC50 = 277 mg/kg dw soil (US ISC), which is the endpoint to be taken into account at product authorization stage” (ECHA biocides assessment report, 2015).   

 In line with the C12-16 ADBAC biocides assessment report and given that the read across to C12-16 ADBAC can be justified for the test substance based on a category approach, the 16-d EC50 value of 277 mg a.i./kg dw of soil obtained for Brassica alba (mustard) due to effects on growth has been considered further for hazard/risk assessment. Additionally, in accordance with the ECHA R.7c guidance (2017), the 16-d NOEC value of 856.2 mg a.i./kg soil dw obtained for Trifolium pratense(red clover) due to effects on growth can be considered as the long-term equivalent value. 

Cross-reference 5

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Based on the above information and in line with the biocides assessment report on the read across substance C12-16 ADBAC, the 14 d LC50 of 7070 has been selected to express the acute toxicity of the test substance. Further, based on the chronic toxicity study with the read across substance, the 28-d NOEC of 125 mg/kg bw/day has been considered further for hazard/risk assessment.    

Short-term EC50 or LC50 for soil macroorganisms:

7 070 mg/kg soil dw

Long-term EC10, LC10 or NOEC for soil macroorganisms:

125 mg/kg soil dw

Short-term toxicity studies:  

Study 1.  A study was conducted to determine the toxicity to soil macroorganisms of the read across substance C12-16 ADBAC (49.5% active) according to OECD Guideline 207, in compliance with GLP. Six groups of forty earthworms (Eisenia foetida) were allocated to an artificial soil containing 0, 953, 1715, 3086, 5556 or 10000 mg a.i./kg soil dw (nominal concentrations). No analytical dose verification was performed. Mortality was recorded on Days 7 and 14. Worms were weighed at the beginning and end of the study. After 7 days, all worms at 10000 and 2 worms at 5556 mg a.i./kg soil dw were dead. By Day 14, one additional worm died at 5556 mg a.i./kg soil dw. A treatment-related reduction in body weight was observed. Group mean body weights were affected by treatment with read across substance at 1715 mg a.i./kg soil dw and above. Under the study conditions, the 7 and 14 d LC50 values were 7160 and 7070 mg a.i./kg soil dw, respectively and the NOEC was 953 mg a.i./kg soil dw (nominal) (Rodgers, 2004).

 

Study 2. A study was conducted to determine the toxicity to soil macroorganisms of the read across substance, C12 -16 ADBAC (51.7% active) according to OECD Guideline 207, in compliance with GLP. Earthworms (Eisenia foetida) were exposed to a single dose of the read across substance at nominal concentrations of 100, 180, 320, 580 or 1,000 mg/kg dw of artificial soil. No analytical dose verification was performed. The individual live weights of the worms were reported after 14 d of exposure. Other effects (pathological symptoms, behaviour of the worms) were reported after 7 and 14 d of exposure. Results of the reference test with 2 -chloracetamide show that the method was sensitive and valid. The substance did not cause a change in behaviour, weight and mortality of the earthworm at any of the tested concentrations after 14 d of exposure. This was probably due to adsorption onto soil. The highest tested concentration without mortality and any other effects was 1000 mg/kg dw. Under the study conditions, the 14 d NOEC in earthworm was 1000 mg/kg dw (or 517 mg a.i./kg dw) and the 14 d LC0 was > 1000 mg/kg dw (or > 517 mg a.i./kg dw) (Noack, 1999).

Based on the above two studies, the same effect levels were concluded in the biocide assessment report on C12-16 ADBAC by RMS Italy. They further stated that: “The findings of the two tests, although different in absolute values, are not in contrast. Since the second test provides a “higher than” value corresponding to a complete lack of lethal or sublethal effects, the 14d LC50 = 7070 mg/kg dry soil (US ISC) is selected to express the acute toxicity of Alkyl (C12-16) dimethylbenzyl ammonium chloride to soil dwelling invertebrates.” 

Long-term toxicity study: 

A study was conducted to determine the effects of read across substance (50% active in water) on mortality, biomass and the reproductive potential of the earthworm species Eisenia fetida (Annelida, Lumbricidae), according to the OECD TG 222, in compliance with GLP. The study was conducted under static conditions over 8 weeks with the read across substance concentrations 125, 250, 500, 1000, 2000 mg//kg solid dry weight (SDW) corresponding to 62.5, 125, 250, 500, 1000 mg a.i./kg SDW. Each application rate was mixed into artificial soil containing 5% peat. A control including untreated artificial soil was tested under the same conditions as the read across substance treatments. A total of 80 test organisms were divided equally into 8 control replicates adnd another total of 40 test organisms were divided equally into 4 replicates for each read across substance treatment (i.e., 10 earthworms per replicate). They had an individual body weight between 0.36 and 0.55 g at the experimental starting. Each concentration level and control were analysed via LC-MS/MS analysis on Day 0, Day 28 and Day 55 using pooled samples of all replicates. The measured concentrations of the pooled samples of replicates were within the range of 83 to 101 % of the nominal values on Day 0, demonstrating the right preparation of the tested concentrations. After 28 days of exposure in soil, no read across substance-related earthworm mortalities (<10%), pathological symptoms or changes in the behaviour of adult earthworms were observed in the control or all read across substance concentrations. There were no statistically significant differences in earthworm body weights in all read across substance concentrations compared to the control. After an additional 4 weeks, the reproduction rate (average number of juveniles produced) was 83 juveniles in the control and ranged from 18 to 74 juveniles in the read across substance treatment rates. There were no statistically significant differences in earthworm reproduction in the treatment rates 125 and 250 mg read across substance/kg SDW compared to the control. However, at the read across substance concentrations, 500 to 2000 mg read across substance/kg SDW the earthworm reproduction was statistically significantly reduced. All validity criteria recommended by the test guidelines were fulfilled. Under the study conditions, the LOEC (mortality, biomass), NOEC (mortality, biomass), LOEC (reproduction), NOEC (reproduction) and EC50 (reproduction) values for read across substance were reported to be >2000, ≥2000, 500, 250 and 589 mg read across substance/kg SDW, respectively (equivalent to >1000, ≥1000, 250, 125 and 295 mg a.i./kg SDW, respectively). Based on the results of the read across study, similar effect levels can be considered for the test substance.

Therefore, based on the above information and in line with the biocides assessment report on the read across substance C12 -16 ADBAC, the 14 d LC50 of 7070 has been selected to express the acute toxicity of the test substance. Further, based on the chronic toxicity study with the read across substance, the 28-d NOEC of 125 mg/kg bw/day has been considered further for hazard/risk assessment.    

Cross-reference 6

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Based on the results of the read across study and in line with the C12-16 ADBAC biocides assessment report, the 28d EC50 = 153 mg a.i./kg dw and a 28d EC10 = 83 mg a.i./kg dw soil due to inhibition of microorganisms has been considered further for hazard/risk assessment.

Short-term EC50 for soil microorganisms:

153 mg/kg soil dw

Long-term EC10 or NOEC for soil microorganisms:

83 mg/kg soil dw

Study 1. A study was conducted to determine the toxicity of the read across substance, C12-16 ADBAC (49.9% active in water) to soil microorganisms, according to OECD Guideline 216, in compliance with GLP. In this study, the inhibition of microbial nitrogen transformation was investigated in sandy loam soil by evaluating the nitrite, nitrate and ammonium formation following 28 d exposure to the read across substance. A volume of 6.04 mL of deionized water containing the read across substance was added to 50-g of soil. The samples were incubated for 7 d at 20°C and at 10% of its water holding capacity. The samples were dosed with read across substance at nominal concentrations 0, 50, 100, 200, 400, 800, 1600, 3200 and 6400 mg a.i./kg soil ww. Analytical dose verification of the stock solutions indicated good correlation with the nominal concentrations. Therefore, doses were presented as nominal concentrations. The nitrogen transformation measurements were carried out at the beginning of the test and at the end at Day 28. The activity of the microorganisms transforming nitrogen in soil was slightly inhibited at 50 mg a.i./kg soil ww. The EC50 calculated was 130 mg a.i./kg soil ww with 95% confidence limits of 80 and 190 mg a.i./kg soil ww. The EC10, EC20 and EC80 of the read across substance were determined at 70, 90 and 200 mg a.i./kg soil ww respectively. In soil not only formation of nitrate occurs but also reduction of nitrate to nitrogen gas by denitrifying microorganisms. Decrease of the nitrate concentrations in the soil was observed at 400 mg a.s./kg soil ww and higher after 28 d. This was probably the result of the activity of these denitrifying microorganisms. The denitrifying microorganisms were inhibited at 6400 mg a.i./kg soil ww (highest concentration), as only a limited amount of the nitrate was removed after 28 d at this concentration. Under the study conditions, the 28 d EC50 and EC10 values were determined to be at 130 and 70 mg a.i./kg soil ww respectively (van Ginkel, 2004).

Study 2. A study was conducted to determine the toxicity of the read across substance, C12-16 ADBAC (49-51% active in water) to soil microorganisms, according to OECD Guideline 216 and 217, and US EPA OPPTS 850.5100, in compliance with GLP. In this study, the effects of the read across substance on carbon mineralization and nitrogen transformation activity of soil micro-organisms were investigated in two soil types (sandy loam soil and a low humic content sand) by evaluating nitrite, nitrate, ammonium and carbon dioxide formation following 28 d exposure. Fifty grams dry weight of soil samples were mixed with lucerne meal (13:1 carbon:nitrogen) and placed in 100 mL bottles. The samples were incubated in the dark at 20±2°C for 28 d. The moisture content of the samples was checked weekly. The samples were dosed with read across substance at nominal concentrations 0, 10, 100 and 1000 µg a.i./g soil dw. No analytical dose verification was performed for the read across substance. Samples were taken to determine nitrogen metabolite content on days 5 and 28 and the CO2 evolution was determined on Days 5 – 8 and 25 – 28. No significant reduction in ammonium formation was observed. The difference in the CO2 production and nitrogen transformation between the treated and untreated soil samples did not exceed 25% after 28 d of incubation. The highest inhibition recorded was 82.5% in the nitrite formation rate after 5 d at 10 mg a.i./kg soil dw in the sandy loam soil. After 28 d of incubation, however, no relevant effect was observed (<25% reduction). Therefore, it was not necessary to extend the test beyond 28 d. Under the conditions of the study, the read across substance was therefore considered to have a low potential for adversely affecting the microbial functions of sandy loam and low humic content sand soils and the 28 d EC50 and NOEC were considered to be at >1000 and ≥1000 µg a.i./g soil dw respectively (de Vette, 2001).

Based on the above studies, same effect levels and low toxicity potential were concluded in the biocide assessment report on C12-16 ADBAC by RMS Italy. They further stated that: “The studies from the two dossiers, although all rated 1, show marked difference in the results, even when the soil characteristics were similar like in the case of tests conducted with sandy loam soils. The endpoint with the lowest values is therefore selected to be taken into account, i.e., 28d EC50 = 153 mg a.i./kg dw (130 mg/kg wwt soil) and a 28d EC10 = 83 mg a.i./kg dw soil (70 mg a.i./kg ww soil), retrieved from the EQC dossier.”(ECHA biocides assessment report, 2015).

In line with the biocides assessment report on the read across substance C12 -16 ADBAC, the lower 28d EC50 = 153 mg a.i./kg dw and a 28d EC10 = 83 mg a.i./kg dw soil due to inhibition of microorganisms has been considered further for hazard/risk assessment.

Cross-reference 7

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Based on the available weight of evidence and the cationic nature, the test substance, C12-14 ADBAC, is expected to have a low absorption potential followed by excretion primarily via feces. Based on QSAR predictions and data on read across substance, it is likely to undergo aliphatic hydroxylation as the first metabolic reaction. Further, based on its ionic nature, molecular weight and key physico-chemical properties it is likely to have no or very bioaccumulation potential. 

Bioaccumulation potential:

low bioaccumulation potential

Absorption rate - oral (%):

10

Absorption rate - dermal (%):

10

Absorption rate - inhalation (%):

50

ABSORPTION:  

Oral absorption  

Based on physicochemical properties:  

According to REACH guidance document R7.C (May 2014), oral absorption is maximal for substances with molecular weight (MW) below 500. Water-soluble substances will readily dissolve into the gastrointestinal fluids; however, absorption of hydrophilic substances via passive diffusion may be limited by the rate at which the substance partitions out of the gastrointestinal fluid. Further, absorption by passive diffusion is higher at moderate log Kow values (between -1 and 4). If signs of systemic toxicity are seen after oral administration (other than those indicative of discomfort or lack of palatability of the test substance), then absorption has occurred. 

C12-14 ADBAC is an Alkyl dimethyl benzyl ammonium chloride (ADBAC) type of cationic surfactant. It is a UVCB with majorly C12 to C14 alkyl chains with molecular weight ranging from 283.9 to 424.2 g/mol. The purified formbased on read across to C12-16 ADBAC, the test substance, iscrystalline, hygroscopic, sticky white solid. Based on read across to C12-16 ADBAC, the test substance, C12-14 DBAC is considered to have a moderate water solubility of 500-1000 mg/L at 20°C (based on CMC) and a low log Kow of 2.75 value, which was determined based on solubility ratios.

Based on the R7.C indicative criteria, together with the fact that the test substance is cationic with a strong adherence potential to the negatively charged surfaces of the membranes, suggests that it is not expected to easily pass biological membranes.

Based on experimental data on read across substances:  

A study was conducted to determine the basic toxicokinetics of the read across substance, C12-16 ADBAC (49.9% active in water with 99.4% radiolabelled purity), according to OECD Guideline 417, in compliance with GLP. In this study, Sprague-Dawley rats were treated with single and repeated oral doses (50 or 200 mg/kg bw) as well as a single dermal dose (1.5 or 15 mg/kg bw) of the radiolabelled read across substance. Following single and/or repeated oral doses, the plasma, blood and organ radioactivity levels were essentially non-quantifiable, indicating a low oral bioavailability. The actual fraction of the oral dose absorbed was around 8% (urine and bile fractions). This was eliminated rapidly, essentially within a 48 to 72 h period. The majority of the oral dose was excreted in the faeces. At the high oral dose level only, quantifiable levels of radioactivity (2,386 to 23,442 ηg equivalent/g) were found in some central organs at 8 h post-dosing; otherwise, the vast majority of the dose was confined to the intestines, where their levels decreased over time and were all non-quantifiable by 168 h (i.e., 7 d). Only about 4% of the oral dose was eliminated in the bile in a 24 h period, of which about 30% during the first 3 h. Under the conditions of the study and following oral administration the read across substance was found to have limited absorption (ca. 10%), low distribution (below quantification limits within 4-7 d) and majorly excreted via faeces (ca. 80%) (Appelqvist, 2006). Further, a biocides assessment report available on the read across substance by RMS Italy, concluded that the read across substance“is highly ionic and, therefore, it is expected not to be readily absorbed from the gastrointestinal tract or skin. The vast majority of the oral dose was excreted in the faeces (80%) as unabsorbed material (only about 4% of the oral dose was eliminated in the bile in a 24-hour period). The actual fraction of the oral dose absorbed was about 10%, based on the urinary mean value 3-4% (with a single peak value of 8.3%) and biliary excretion values (3.7-4.6%), as well as on the absence of residues in the carcass, as measured at 168 h. Excretion was rapid (within a 48 to 72-hour period). The radioactivity excreted in the urine was not associated with the parent compound, but with more polar metabolites which were not identified”(ECHA biocides assessment report, 2015).

In another study conducted according to EPA OPP 85-1, Sprague-Dawley rats (10 animals per sex per group) were treated with radiolabelled read across substance, C12-16 ADBAC (30% active in water with 99.4% radiolabelled purity). The study was conducted in four phases: a single low dose (10 mg/kg); a single high dose (50 mg/kg); a 14 d repeated dietary exposure with non-radiolabelled read across substance (100 ppm) and single low dose of radiolabelled (14C) read across substance (10 mg/kg); and single intravenous dose (10 mg/kg). Following the single doses or the last dietary dose, urine and faeces were collected for 7 d. A preliminary study had indicated that insignificant 14CO2 was generated. Tissues, urine and faeces were collected and analysed for radioactivity and faeces were analysed by TLC, HPLC and MS for metabolites and parent compound. Following oral administration, radiolabelled read across substance was rapidly absorbed, although in very limited amounts, consistent with its highly ionic nature. Residual 14C in tissues was negligible after administration by gavage both after single and repeated dosing, indicating low potential for bioaccumulation. After i.v. administration a higher amount of radioactivity (30−35%) was found as residue in the tissues. About 6−8% of orally administered read across substance is excreted in the urine whereas, 87−98% was found in the faeces. Since no data on bile duct-cannulated rats are available, it was not possible to conclude if this radioactivity accounts exclusively for unabsorbed read across substance or not. However, the i.v. experiment showed that 20−30% was excreted in the urine and 44-55% in the faeces, suggesting that both the kidney and liver are capable of excreting read across substance once absorbed and that absorption is higher than the % found in the urine after oral administration. Based on the urinary mean value 3-4% (with a single peak value of 8.3%) and biliary excretion values (3.7-4.6%), as well as on the absence of residues in the carcass, as measured at 168 h, it can be expected that the read across substance absorption through the g.i. tract is about 10% (conclusion not included in the study report; as assessed by the Italian Rapporteur Member state in the biocides dossier; ECHA biocides assessment report, 2015). Less than 50% of the orally administered read across substance was found to be metabolised to side-chain oxidation products. In view of the limited absorption of the read across substance, the four major metabolites identified were expected to be at least partially formed in the gut of rats, apparently by microflora. No significant difference in metabolism between male and female rats or among the dosing regimens was observed. Repeated dosing did not alter the uptake, distribution or metabolism of read across substance. Under the conditions of the study, the read across substance was found to have limited absorption (ca. 10%; due to its ionic nature), negligible distribution (no bioaccumulation), and majorly excreted majorly via faeces (87-98%) following oral administration. However, following i.v. administration, it was found to be widely distributed (30-35%) in tissues and excreted both via faeces (40-55%) and urine (20-30%). Four major metabolites were identified, formed via oxidation of the alkyl chain (Selim, 1987). Further, the biocides assessment report concluded that“the oral absorption can be considered to be approximately 10%, based on the 5-8% of the C12-16-ADBAC administered dose eliminated via urine and tissue residues (less than 1% of the administered dose 7 days after single and repeated oral dosing). More than 90% is excreted in the faeces and the pattern did not change after repeated doses. Although it was not possible to discriminate between unabsorbed/absorbed material, based on the chemical nature of the test substance, it can be anticipated that about 90% is present in faeces as unabsorbed material. The majority of C12-16-ADBAC metabolism is expected to be carried out by intestinal flora; the metabolites, which account for less than 60% of the administered dose, include hydroxyl- and hydroxyketo- derivatives of the dodecyl, tetradecyl and hexadecyl chains. No metabolite accounted for more than 10% of the total administered dose”(ECHA biocides assessment report, 2015).  

Assessment from biocides assessment report available on read across substances:  

As indicated above the biocides assessment reports available on the read across substance C12-16 ADBAC indicated that given its ionic nature, C12-16 ADBAC was not expected to be readily absorbed from the gastrointestinal tract or skin. And based on the results from thein vivostudies with rats andin vitrostudies with human skin, an oral and dermal absorption value of 10% could be considered at non-corrosive concentrations.

Conclusion:Overall, based on the available weight of evidence information and given the ionic nature, the test substance can be expected to overall have low absorption potential through the oral route at non-corrosive concentrations. Therefore, in line with the biocide assessment report and as a conservative approach a maximum oral absorption value of 10% can be considered for the risk assessment. 

Dermal absorption  

Based on physicochemical properties:  

According to REACH guidance document R7.C (ECHA, 2017), dermal absorption is maximal for substances having MW below 100 together with log Kow values ranging between 2 and 3 and water solubility in the range of 100-10,000 mg/L. Substances with MW above 500 are considered to be too large to penetrate skin. Further, dermal uptake is likely to be low for substances with log Kow values <0 or <-1, as they are not likely to be sufficiently lipophilic to cross the stratum corneum (SC). Similarly, substances with water solubility below 1 mg/L are also likely to have low dermal uptake, as the substances must be sufficiently soluble in water to partition from the SC into the epidermis. 

The test substance is soilidbased on read across to C12-16 ADBAC,with an MW exceeding 100 g/mol, moderate water solubility and an estimated log Kow exceeding above 2.This together with the fact that the test substance is cationic with a strong adherence potential to the negatively charged surfaces, suggests that the test substance at non-corrosive concentrations is likely to have a low penetration potential through the skin. 

At higher corrosive concentrations although there is a likelihood of exposure to the test substance due to disruption of the barrier properties of the skin, the likelihood of occurrence of these cases is expected to be minimal due to the required risk management measures and self-limiting nature of the hazard. Therefore, this scenario has not been considered further for toxicokinetic assessment.

Based on QSAR predictions:  

The two well-known parameters often used to characterise percutaneous penetration potential of substances are the dermal permeability coefficient (Kp[1]) and maximum flux (Jmax). Kp reflects the speed with which a chemical penetrates across SC and Jmax represents the rate of penetration at steady state of an amount of permeant after application over a given area of SC. Out of the two, although Kp is more widely used in percutaneous absorption studies as a measure of solute penetration into the skin. However, it is not a practical parameter because for a given solute, the value of Kp depends on the vehicle used to deliver the solute. Hence, Jmax i.e., the flux attained at the solubility of the solute in the vehicle is considered as the more useful parameter to assess dermal penetration potential as it is vehicle independent (Robert and Walters, 2007).  

In the absence of experimental data, Jmax can be calculated by multiplying the estimated water solubility (using WATERNT v.1.02) with the Kp values from DERMWIN v2.02 application of EPI Suite v4.11. The calculated Jmax values for the different carbon chains of the UVCB substance was determined to be range between 5.00E-07 to 8.5E-05 μg/cm2/h, leading to a weighted average value of 5.86E-06 μg/cm2/h. As per Kroeset al.,2004 and Shenet al. 2014, the default dermal absorption for substances with Jmax ≤0.1 μg/cm2/h can be considered to be less than 10%. Based on this, the test substance can be predicted to have low absorption potential through the dermal route.  

Based on experimental data on read across substances:  

Following a single dermal application of the read across substance, C12-16 ADBAC in the Appelqvist (2006) study, the plasma and blood radioactivity levels were non-quantifiable at nearly all time-points. For the 1.5 mg/kg bw group, around 2 and 43% of the dose was eliminated in the urine and faeces, respectively, mostly within a 48-h period, suggesting that the dermal dose was highly absorbed via the skin. However, this apparent high absorption via the skin may have been due to the animal licking the test site. This was also supported with the finding that, after oral dosing, only about 4% was excreted via bile back to the intestine and 4% excreted via urine. If similar routes of excretion are expected for dermally absorbed doses, it would not be possible to find levels of 50% of applied doses in intestine with only 2% excreted via urine. This indicates that about 50% of the dermally applied dose was taken up orally after all. Excretion in urine (2%) following dermal exposure was similar to that following oral exposure. At 24 h post-dosing, most of the radioactivity was in the “stripped” skin (dermis/epidermis) application site (15.02/8.74% [male/female] and 33.8/24.2% of the dose for the high and low dose groups respectively) and intestines for both dose levels (5.76/8.32% and 5.61/7.79% of the dose for the high and low dose groups respectively), though some radioactivity was in the skin adjacent to the application site and minor traces were in the eyes (both most likely from cross-contamination due to grooming). At 168 h, levels in the application site of the individual animals of the low dose were 5.19 to 9.21% of the radioactive dose, suggesting the skin acted as a drug reservoir. In the stratum corneum of the application site, the levels of radioactivity were of similar magnitude in the different layers at each time-point. For all tissues/organs, the radioactivity levels decreased over time. All data showed generally a low inter-animal variability. In addition, there was no evidence of gender differences (Appelqvist, 2006). Further, the biocides assessment report concluded that “The available data on BKC dermal absorption do not allow to quantify exactly the % of the dose which was absorbed after dermal application. However, due to the radioactivity recovered at the skin application site after removal of the stratum corneum layers (6.5-8.7% of the dose) and the ionic nature of the test item, it can be anticipated that the dermal absorption is not different from the oral one (10% at non corrosive concentration)”(ECHA biocides assessment report, 2015).  

Anin vitrostudy was conducted to determine the rate and extent of dermal absorption of the read across substance, C12-16 ADBAC (80.5% active; >99% radiolabelled purity), according to OECD Guideline 428, in compliance with GLP. The study was conducted with radiolabelled read across substance at 0.03% and 0.3% concentrations, which was topically applied over split-thickness human skin membranes mounted into flow-through diffusion cells. Receptor fluid was pumped underneath the skin at a flow rate of 1.5 mL/hour. The skin surface temperature was maintained at approximately 32°C. A barrier integrity test using tritiated water was performed and any skin sample exhibiting a permeability coefficient (kp) greater than 2.5 x 10-3 cm/h was excluded from subsequent absorption measurements. The 14C- radiolabelled read across substance was applied at an application rate of 10 mg/cm2. Absorption was assessed by collecting receptor fluid in hourly intervals from 0-6 h post dose and then in 2-hourly intervals from 6-24 h post dose. At 24 h post dose, the exposure was terminated by washing and drying the skin. The stratum corneum was then removed from the skin by 20 successive tape strips. All samples were analysed by liquid scintillation counting. Under the conditions of the study, the mean absorbed dose and mean dermal deliveries were determined to be 0.05% (0.01 ηg equiv. /cm2) and 2.22% (0.07 ηg equivalent/cm2) of the applied dose for the low concentration test preparation, respectively, and 0.03% (0.01 ηg equivalent /cm2) and 2.16% (0.67 ηg equivalent/cm2) of the applied dose for the high concentration test preparation, respectively. The stratum corneum acted as a barrier to absorption, with the mean total unabsorbed doses (recovered in skin wash, tissue swabs, pipette tips, cell wash, stratum corneum and unexposed skin) of 96.80 and 94.68% of the applied dose for the low and high concentration test preparations, respectively. The maximum fluxes for the low and high doses were 0.12 ηg equivalent /cm2/h and 0.74 ηg equivalent /cm2/h, respectively, at 2 h (Roper, 2006). Based on literature evidence, substances with Jmax ≤ 0.1μg/cm2/h, can be expected to have low skin penetration potential and can be assigned a default skin absorption of <10% (Shenet al., 2014, Kroeset al.,2004). Further, the dermal absorption of the read across substance was concluded in its biocides assessment report (by RMS Italy) to be 8.3%, which was obtained by summing up the radioactivity present in the receptor fluid (0.05%), at the application site (after 20 consecutive tape stripping procedures) and the one present in tape strips (n°6-20) (ECHA biocides assessment report, 2015). 

Assessment from biocides assessment report available on read across substances: 

As indicated above the biocides assessment reports available on the read across substance C12-16 ADBAC indicated that given its ionic nature, C12-16 ADBAC was not expected to be readily absorbed from the gastrointestinal tract or skin. And based on the results from thein vivostudies with rats andin vitrostudies with human skin, an oral and dermal absorption value of 10% could be considered at non-corrosive concentrations (ECHA biocides assessment report, 2015). 

Conclusion:Overall, based on all the available weight of evidence information, the test substance can be expected to have a low absorption potential absorption through the dermal route at non-corrosive concentrations.As a conservative approach and in line with the biocide assessment report a maximum dermal absorption value of 10% can be considered for risk assessment. 

Inhalation absorption  

Based on physicochemical properties:  

According to REACH guidance document R7.C (ECHA, 2017), inhalation absorption is maximal for substances with VP >25 KPa, particle size (<100 μm), low water solubility and moderate log Kow values (between -1 and 4). According to Rothe et al (2011), upon inhalation, deposition and absorption of large particles/droplets would occur in the upper airways depending on their physical chemical properties. Water soluble substances are expected to be absorbed where deposited.

The test substance, based on read across to C12-16 ADBAC, of its crystalline, hygroscopic, sticky white solid like physical state and relatively low vapour pressure of <5.8E-3 Pa at 25°C, will not be available as vapours for inhalation under ambient conditions. In the case of spraying applications, coarse droplets would be formed which typically settle on the ground and result in a very lower respiratory fraction. Of the inhalable fraction, due to the droplet size and the moderate water solubility, almost all droplets are likely to be retained in the mucus and will not be available to reach the deeper lungs. The deposited droplets in the upper respiratory tract are expected to be absorbed in a relatively slower rate compared to the deeper lungs due to differences in vascularity. Some amounts of these deposited droplets are also expected to be transported to the pharynx and swallowed via the ciliary mucosal escalator. Therefore, the systemic uptake of the test substance via the respiratory route can be considered to be similar to the oral route.

Conclusion:Based on all the available weight of evidence information, together with the fact that the test substance is cationic with an adherence potential to the negatively charged surfaces, the test substance can be expected to have low to moderate absorption potential through the inhalation route, depending on the droplet size. Therefore, a value of 50% can be considered for the risk assessment as a conservative approach.  

METABOLISM:  

Based on experimental data on read across substances:  

As discussed in the Selim, 1987 study, less than 50% of the orally administered C12-16 ADBAC is metabolised to side-chain oxidation products. In view of the limited absorption of the test substance, the four major metabolites identified may be at least partially formed in the gut of rats, apparently by microflora. The metabolites, which account for less than 60% of the administered dose, include hydroxyl- and hydroxyketo- derivatives of the dodecyl, tetradecyl and hexadecyl chains. No metabolite accounted for more than 10% of the total administered dose. No significant difference in metabolism between male and female rats or among the dosing regimens was observed. Repeated dosing did not alter the uptake, distribution or metabolism of the test substance (Selim, 1987). 

Based on QSAR modelling: 

The OECD Toolbox (v.4.4.1) and FAME 3were used to predict the first metabolic reaction, since the rat liver S9 metabolism simulator performs predictions for salts, while SMARTCyp and MetaPrint2D are not powered enough for this type of substance. The second simulator of the OECD Toolbox (in vivorat metabolism simulator) was not used as it does not consistently perform predictions for salts. As per the rat liver S9 metabolism simulator, the major constituents are primarily predicted to undergo ω or ω-1 aliphatic hydroxylation reactions. Similar results were found with FAME 3 metabolism simulation tool (which currently covers only CYP metabolism). See the below table for the reaction sites. For further details, refer to the read across justification.

 

Major constituents (major chains >=10%)		Rat liver S9 metabolism simulator / Fame 3
Benzyldimethyldodecylammonium chloride		ω or ω-1 aliphatic hydroxylation
Benzyldimethyltetradecylammonium chloride		ω or ω-1 aliphatic hydroxylation

Overall, similar reactive sites were predicted for other TMACs and ADBACs from the category. 

Conclusion:Based on all the available weight of evidence information, the test substance is considered to be primarily metabolised by alkyl chain hydroxylation, which is carried out by the intestinal flora.  

DISTRIBUTION 

Based on physico-chemical properties: 

According to REACH guidance document R7.C (ECHA, 2017), the smaller the molecule, the wider the distribution. Small water-soluble molecules and ions will diffuse through aqueous channels and pores, although the rate of diffusion for very hydrophilic molecules will be limited. Further, if the molecule is lipophilic (log P >0), it is likely to distribute into cells and the intracellular concentration may be higher than extracellular concentration particularly in fatty tissues. Identification of the target organs in repeated dose studies are also indicative of the extent of distribution. 

Generally given the ionic nature of the test substance, the test substance is not likely to readily partition across the blood membranes into the different organs, leading to an overall low distribution potential. Moreover, even if the test substance distributes to a certain extent, it is not expected to bioaccumulate based on the read across experimentalBCF values of C12-16 ADBACor the predicted BCF values generated for the test substance using ionic BCF regression-based equation from BCFBAF v. 3.02 program of EPISuite^TM(see section 4.3 of the CSR). 

Based on experimental data on read across substances: 

As discussed above, in the Appelqvist, 2006 study, quantifiable levels of radioactivity (2,386 to 23,442 ηg equivalent/g) were found in some central organs at 8 h post-dosing at 200 mg/kg bw; otherwise, the vast majority of the dose was confined to the intestines, where their levels decreased over time and were all non-quantifiable by 168 h (i.e., 7 d). In the Selim, 1987 study, residual 14C in tissues was negligible after administration by gavage both after single and repeated dosing, indicating a low potential for bioaccumulation. However, following i.v. administration, it was found to be widely distributed (30-35%) in tissues (Selim, 1987). 

Conclusion:Based on all the available weight of evidence information, the test substance is expected to have a low distribution and bioaccumulation potential.  

EXCRETION: 

Based on physicochemical properties: 

Given the expected low absorption potential of the test substance due to its ionic nature and physico-chemical properties, it can be expected to be primarily excreted through faeces. 

Based on experimental data on read across substances: 

Based on the evidence from the available oral studies (Appelqvist, 2006; and Selim, 1987), the test substance is primarily expected in faeces (>90%) and less via urine (<10%). 

Conclusion:Based on all the available weight of evidence information, the test substance is expected to be primarily excreted via faeces.  

[1] Log Kp = -2.80 + 0.66 log kow – 0.0056 MW 

Cross-reference 8

Reason / purpose for cross-reference:

data waiving: supporting information

Reference

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

repeated dose toxicity

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

repeated dose toxicity

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

acute toxicity

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

repeated dose toxicity

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

repeated dose toxicity

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

acute toxicity

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

medium hazard (no threshold derived)

Most sensitive endpoint:

skin irritation/corrosion

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

repeated dose toxicity

Hazard assessment conclusion:

no hazard identified

Most sensitive endpoint:

acute toxicity

Hazard assessment conclusion:

medium hazard (no threshold derived)