Aquatic Environment Exposure and Toxicity of Engineered

Overview

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Key numbers

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• assessment (9,20). For instance, as little as 0.007 to 0.5% of PR–ENMs (nAg and nTiO2 ) was
• released from textile and paint products’ NEPs (20,21). From sunscreens, 0.16–1.16 µg/L
• in NEPs. The ENMs’ sample was selected because of the high production rates (Table 1),
• Table 1. The global production and application of selected engineered nanomaterials (ENMs) based
• Twenty–five percent (25%) of all NEPs in the consumer market are reported to be
• nTiO2 is one of the most highly produced ENMs globally (Table 1) as a white pigment
• stable form of nTiO2 , while anatase is metastable and transforms into the rutile phase at
• range of ~10–100 nm, with near-spherical, spherical and irregular shapes (10,24,124–126).
• cleaners was reported to be in the range of <10–101 nm (128–130) in quasi-spherical, and
• spherical shapes (128,129). The nAg zeta potential range in household surface cleaners has
• extensive application of nSiO2 in NEPs suggests notable environmental release potential.
• products, paints, textiles/clothing, washing machine, baby products and toothbrushes (Table 2).
• over 48 h. Total Ti released from the sunscreens ranged from 19–32 wt% (dark condi-
• The total released Ti was, respectively, 1.16 and 0.7 µg/L in DI water and tap water. The
• release rate was in the order of 8–72% (100). No further characterisation was undertaken
• washing them off by stirring in tap water (76). From the liquid type sunscreen, ca. 40% of
• cream type sunscreen released only 20% of the initial ENMs’ (nZnO and nTiO2 ) loading
• three sunscreens (140). Approximately 0.4–8% (w/w) of the sunscreen’s initial loading
• Table 2. The total concentrations released from different nano-enabled products (NEPs). ENMs = engineered nanomaterials.
• Sunscreen nZnO 0.58 mg/L (100)
• brushes, respectively. The nAg particle size ranged between 42 and 47 nm and was
• spherical (25). Benn et al. (141) reported 100% Ag release from toothbrushes of their initial
• PR-nTiO2 was elongated in shape with a size range of 8–9 ± 3 × 60–66 ± 9 nm (width × length)
• to be between 0.5 and 20 mg/L over the exposure period, and there was an average loss of
• about 30% of the initially applied surface Ag (1.5 mg/m2 ). The PR–nAg was detected as
• after three months was 0.67 µg/L. During the first three months of exposure, the average
• Ag concentration released from one of the façade panels ranged between 1 and 21 µg/L.
• between 0.08 and 0.86 µg/L. The total amount of nAg released from the wooden façade
• panels was 15.7 and 1.7 µg/L for the first and second panel, respectively, both accounting
• for less than 1% of the nAg in the initial coating. Neither nanoparticle tracking analysis
• summer and 8.1 × 105 particle/mL to 1.2 × 107 in winter. Overall, 55% of PR–nTiO2 was
• The stained surfaces released over 30 µg/m2 PR–nTiO2 with a size range of 15–100 nm.
• Overall, the total release accounted for 5 × 10–5% for painted surfaces and 6% for stained
• released a total Ti of <0.7–4.7 mg/L in the washing solution and 0.64 mg/L in the subsequent
• released from the 24-h study. However, only 1% of the initial TiO2 content released was in
• 1.5–650 µg in 500 mL of distilled water. The total silver release ranged from <1% in some
• socks to 100% of the initial silver loading in other socks. Most of the released Ag was in
• other five fabrics ranged from 1.3 to 35%, with the amount of Ag released decreasing with
• subsequent washes (15). The concentration of released Ag ranged from 0.3 to 377 µg/g (15).
• with the initial Ag content of 1.5–2925 mg/kg of textile that were washed and rinsed and the
• tively, indicating the release of 15–20% (120). Elsewhere, a standard laboratory method was
• used to release nAg from five textiles (138). The textiles released 18 ± 2–2925 ± 10 mg/kg

Methods (brief)

• in NEPs. The ENMs’ sample was selected because of the high production rates (Table 1),
• elevated temperatures (68). From a sample of six sunscreens, rutile nTiO2 was present
• façades were collected and analysed for nTiO2 . In the samples from the aged façade,
• was collected and analysed for nAg (23). The total Ag released in the runoff was determined
• nAg from paint exposed to outdoor conditions for one year (121). The runoff was collected
• demolition landfill discarded materials (127). The leachate samples contained spherical
• under actual weathering conditions (85). The PR–nTiO2 was analysed in the collected
• panels over 10 weeks. Considerable amounts of PR–nTiO2 were obtained in the collected
• precipitate samples; the PR-nTiO2 concentration averaged 2–4 × 106 particles/mL in
• samples were exposed also influence the release.
• recreational activity (143). Samples collected downstream during the highest recreational
• ENMs’ release (144). Water samples collected from 15 points were analysed for PR–nAg,
• PR–nTiO2 and PR-nCeO2 using spICP-MS. The total Ag in the river samples was quantified
• was detected in river samples and the total Ti was 0.2–8.1 µg/L, whereas nTiO2 size was
• ational area, Vienna, Austria (145). Samples were collected from the lake during the bathing
• PR–nTiO2 was confirmed to exist as heteroaggregates; the PR-nTiO2 samples were linked
• Künniger et al. (121) evaluated the toxicity of paint PR–nAg where the collected runoff
• water samples from wooden façades were coated and exposed to the precipitation over

Implications

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Wiki pages this source may touch

• Fish — marine, non-predatory (sardines, anchovies, salmon, cod)
• Shellfish (shrimp, crab, lobster, clams, oysters, mussels)
• Baby Wipes
• Baby Sunscreen, Mineral (ZnO + TiO2)
• Cadmium
• Aluminum

Verification notes

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Update history

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