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EC number: 629-732-4
CAS number: 1224966-13-5
Refined sorption/desorption tests according to OECD 106 have been performed with DETA and PEPA (polyethylenepolyamines) based Fatty acid C18 unsaturated imidazoline. These tests resulted in in almost identical equilibrium constants (Kd's) of 47249, 19022 and 145295 L/kg for loamy sand, silt and clay soil for the AAI-DETA and 42721, 44324 and 165856 for the PEPA based imidazoline. For risk assessment purposes, the Kd of loamy sand (Speyer 2.2) as observed for AAI -DETA of 47249 L/kg will be used as realistic worst-caseAs there is no direct relationship with the sorption behaviour of the substance and the organic carbon content of the soil because other soil properties like the Cation Exchange Capacity and the pH are maybe even more important to predict the sorption behaviour, no Koc's are given.Because there is no direct relationship of the sorption with the organic matter content in the soil, there is no principal difference between soil and sediments in respect to the sorption properties. Therefore the same sorption Kd is considered to be acceptable for both soil and sediment.
Due to the cationic
surface-active properties of Fatty acids C18 unsaturated poly
ethyleneamine based imidazolines, these substances will adsorb strongly
onto the solid phase of soil and sediments. The substance can adsorb
both onto the organic fraction and, dependent on the chemical
composition, onto the surface of the mineral phase, where sodium and
potassium ions can be exchanged against the alkyl ammonium ion. The
determination of a Koc from log Kow is not opportune, because the common
equations for Koc derivation are not valid for both ionic and surface
The adsorption behaviour
DETA and PEPA based tall oil poly ethyleneamine imidazolines was
studied in batch equilibrium experiments according to a refined OECD 106
(Farnback, 2010). In both studies three soils were used, encompassing a
range of clay and organic matter. The test substance adsorbed partially
onto the container walls which was considered for the determination of
the adsorption coefficients. Adsorption kinetics was determined by
measurements at different sampling times (up to 24 h), equilibrium was
reached after 24 hours but after 3 hours there was only a limited
difference observed. Desorption occurred to a lesser extent than
adsorption. The tables below present a summary of the most important
soil properties and observed partitioning constants for both
Overview of sorption test results
of Fatty acids C18 unsaturated diethylenetriamine imidazoline (CAS No
Overview of sorption test results
Fatty acids C18 unsaturated PEPA based imidazoline (CAS no. 68910-93-0)
The number of soils which
was used in this test deviates from the recommendation in OECD guideline
106 (2000) in that three soils were used instead of the recommended five
soils. In addition is the partitioning to soil is not based on a
Freundlich isotherm but evaluated based on only one test concentration.
These deviations is based on results of earlier adsorption desorption
tests with cationic surfactants. The ammonium ions will interact with
the negative surface of mineral particles or with negative charges of
humic substances. The ionic interactions play a more important role than
hydrophobic partitioning with organic matter. The log Koc is therefore
considered as a poor predictor of the partitioning behaviour of cationic
surfactants in the environment. These earlier results showed that using
three soils with at least one loamy sand and a clay soil, can give as
much information as using the full number of soils. These earlier tests
also revealed that only rarely linear adsorption isotherms were obtained
for cationic surfactants and that extrapolation to lower concentrations
based on these non-linear isotherms leads to unrealistic results (e.g.
RAR primary fatty amines Oct. 2008). According to the Danish EPA (2004)
a more reliable method of extrapolation to lower concentrations, is to
use the data originating from the lowest measured concentration
and to assume that the coefficient remains constant at lower
concentrations. The test as described is therefore performed using only
one concentration which is as low as reasonably possible in relation to
the detection limit.
The initial concentration
used for the determination of the soil partitioning constant was 10.2
mg/L (1.9 mg/l for the individual components). The observed aquatic
equilibrium concentrations in the experiment range from 1.6 to 10 µg/L. For
the prediction of the partitioning of the alkyl polyethylene
Because there is no
principal difference between soil and sediments considering the sorption
properties and because for cationic surfactants the degree of sorption
is not related to the organic carbon content, the value for soil will
also be used for sediment and suspended particles. For sludge which
consists mainly of organic matter the sorption data as observed for soil
is not considered to be representative.
In the table below the
distribution constants used in this assessment is summarized:
With a Kpsuspof
94498 L/kg and a concentration of 15 mg/L suspended matter in surface
waters, the adsorbed fraction is calculated as 59%.
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