Bernard 2022 — Dermal exposure to hazardous chemicals in baby diapers: an EDANA-funded re-evaluation of the ANSES 2019 risk assessment

This is a single-author peer-reviewed review article by Alfred Bernard (IREC, UCLouvain, Brussels) published in MDPI’s International Journal of Environmental Research and Public Health in March 2022 and funded by the International Disposables and Nonwovens Association (EDANA), the European diaper-industry trade association. The paper is a methodological critique of the quantitative health risk assessment (QHRA) reported in the January 2019 ANSES opinion Sécurité des couches pour bébé (anses2019-baby-diaper-safety-france) and the October 2020 ANSES Annex XV restriction dossier to ECHA. Bernard argues that ANSES’s exceedances of health reference values for polycyclic aromatic hydrocarbons (PAHs, hazard quotients up to 66 and excess cancer risk up to 10⁻³), dioxins (PCDD/Fs), dioxin-like polychlorinated biphenyls (DL-PCBs, hazard quotient 12 for decreased adult sperm count), formaldehyde and several fragrances are products of (i) overconservative exposure assumptions (skin transfer T = 100% instead of ANSES’s own refined 7%; rewet factor R = 100% instead of ANSES’s refined 1.32% or the EDANA-recommended 1%, which Bernard characterises as conservative relative to Dey et al. 2016’s measured mean of 0.46%; dermal absorption A = 100% retained even for substances known to be poorly absorbed), (ii) PAH concentrations of LOQ/2 (limits of quantification 150 µg/kg) that are two orders of magnitude above the LOQs of methods used for PAHs in foodstuffs (EFSA 2008), and (iii) “illogical and atypical” PCDD/F vs DL-PCB congener patterns under different extraction modes. Bernard’s recomputations under scenario 2.1 with R = 1% drop all dioxin/DL-PCB hazard quotients below 1 and bring PAH cancer risks closer to acceptable bands, and his breast-milk-vs-diaper intake ratios (74.8 to 626 times more from breast milk under different scenarios) are presented as evidence that dietary background dose dwarfs the modelled dermal dose. Heavy metals are not discussed, not measured, and not assessed at any point in this paper. This page is ingested as out-of-core-scope regulatory-context evidence for the diapers product page — it documents the industry-funded peer-reviewed counter-position to the ANSES 2019 / 2020 regulatory case, providing methodological context (the contested skin-transfer and rewet-factor parameters; the LOQ-as-surrogate-concentration concern; the breast-milk-intake comparator) that any future heavy-metals dermal-exposure model in this product category will have to engage with — alongside its sibling ingest pages anses2019-baby-diaper-safety-france (the regulatory opinion being critiqued) and bfr2019-diaper-substances-anses-commentary (the BfR’s earlier preliminary commentary on the same ANSES opinion).

Key numbers

The paper presents no original measurements. All concentration values are reproduced from the ANSES 2019 opinion (anses2019-baby-diaper-safety-france) or its underlying SCL / INC test data. Bernard’s re-analyses change only the exposure parameters (T, R) applied to ANSES’s concentrations.

Dioxins and DL-PCBs — Table 2 (p. 5), ANSES scenarios as published

Concentrations in diapers under three ANSES extraction scenarios (pg TEQ/kg of diaper, WHO 2005 TEF values; intakes computed for an infant aged 0-6 months at 3.9 kg body weight using 7.98 diapers/day at 24 g/diaper; EFSA TDI 0.3 pg TEQ/kg/d; breast-milk intake computed for a 5 kg infant fed 700 mL/day of milk containing 25 g/L lipids, using Focant et al. 2013 French breast-milk data declined annually 10% to 2017 per Fång et al. 2013):

Bernard’s narrative finding (p. 5): in organic-solvent extracts, PCDD/Fs and DL-PCBs contribute almost equally to total TEQ (frequent pattern in environmental matrices, citing Strapácová et al. 2018). In urine-simulant extracts, DL-PCBs account for ~90% of total TEQ in whole diapers but only ~10% in shredded diapers. The inversion under the same extraction conditions is characterised as “illogical and atypical” (p. 5).

Dioxins and DL-PCBs — Table 3 (p. 7), Bernard’s re-evaluation under scenario 2.1 with R = 1%

Bernard recomputes intakes by applying the scenario 2.1 equation (DI = C × W × N × R × A / Bw) with R = 1% (EDANA-recommended; conservative vs. Dey et al. 2016’s 0.46% mean range 0.32-0.66%) and A = 100% (retained from ANSES for lipophilic substances):

Under R = 1%, every HQ falls below 1.

PAHs — Table 4 (p. 9), ANSES scenario 2.2 as published

Concentrations in diapers extracted from whole diapers with synthetic urine (ANSES scenario 2.2). Intakes calculated for an infant aged 0-6 months (body weight 3.9 kg; 7.98 diapers/day; diaper weight 24 g) assuming fractional dermal and oral absorption of 100%. TEF values per INERIS 2003. EPA oral RfD for benzo[a]pyrene 0.3 µg/kg/d. EPA oral CSF 1 (mg/kg/d)⁻¹. Breast-milk intake for a 5 kg infant fed 700 mL/d of milk with 25 g/L lipids, per Santonicola et al. 2017:

PAH concentrations of 249-598 µg/kg correspond to LOQ/2 of an analytical method with LOQs > 150 µg/kg per individual PAH (p. 9). This is “two orders of magnitude higher than the LODs of methods recommended to measure PAHs in foodstuffs” (EFSA 2008, ref. 14). The atypical concentration pattern showing little variation between individual PAHs (whereas environmental or biological matrices typically vary by factors of 10-100) is characterised as a methodological artefact of the LOQ/2 surrogate. Bernard notes (p. 9) that ANSES’s proposed concentration limit for benzo[a]pyrene of 2.7 ng TEQ/kg diaper is “five orders of magnitude lower than the LOD of the analytical method used in the ANSES risk assessment.”

PAHs — Table 5 (p. 11), Bernard’s re-evaluation under scenario 2.1 with R = 1%

Same column structure as Table 4 above. Intake from diapers recomputed with the scenario 2.1 equation incorporating R = 1%. Selected high-end values:

• Benzo[a]pyrene: intake from diapers 0.20 µg/kg/d; HQ 0.67; ECR 1.42 × 10⁻⁵; breast-milk/diaper ratio 0.55.
• Dibenzo[a,h]anthracene: intake from diapers 0.15 µg/kg/d; HQ 0.50; ECR 1.09 × 10⁻⁵; breast-milk/diaper ratio 4.07.
• Σ PAHs (10 in table): intake from diapers 1.82 µg/kg/d; intake from diapers as TEQ 0.34 µg TEQ/kg/d; HQ 1.13; ECR 2.41 × 10⁻⁵; breast-milk/diaper ratio 1.41.
• Σ 8 PAHs (PAH8): 1.05 µg/kg/d from diapers vs 2.56 µg/kg/d from breast milk (ratio 2.44).
• Σ 4 PAHs (PAH4, EFSA): 0.51 µg/kg/d from diapers vs 0.34 µg/kg/d from breast milk (ratio 0.67).

Under R = 1%, ΣPAHs HQ falls from 113 to 1.13 (two orders of magnitude lower); benzo[a]pyrene HQ falls from 66.3 to 0.67; cancer risks fall from the 10⁻³ to the 10⁻⁵ band.

PAHs — Table 6 (p. 12), skin cancer risks via dermal CSF

Dermal cancer slope factor 3.5 (µg/cm²/d)⁻¹ from Knafla et al. 2011 (ref. 11); skin contact area 234 cm² from Boniol et al. 2008 / EPA 2011 Exposure Factors Handbook (refs. 12, 13). Under ANSES scenario 2.2 equation: BaP excess skin cancer risk 8.28 × 10⁻². Under scenario 2.1 with R = 1%: BaP excess skin cancer risk 8.28 × 10⁻⁴. Σ PAHs (sum of all 10 PAHs listed in Table 6) skin cancer risk under scenario 2.1 + R = 1% is 1.79 × 10⁻³. “Even when incorporating the rewet factor of 1%, these estimates are even higher than those based on the oral CSF” (p. 11). Bernard’s framing (p. 11): the dermal CSF assumes PAHs cause skin tumours, which is the route-of-administration-appropriate critical effect per animal lifetime bioassays; the oral CSF assumes systemic carcinogenicity, which animal evidence “strongly challenged” for dermally absorbed PAHs.

PAHs — Table 7 (p. 12), margin of exposure (MOE)

EFSA MOE approach for food-product PAH risk assessment. BMDL10 values from EFSA 2008 (ref. 14); intake from diapers from ANSES scenario 2.2. Bernard reports MOEs under scenario 2.2 and under scenario 2.1 with R = 1%:

EFSA acceptable MOE is 10,000. Bernard’s framing (p. 12): even under R = 1%, the MOEs of 352, 471 and 669 are “largely below the acceptable levels,” and this cannot be explained by the TEF approach alone (which EFSA considers scientifically invalid for oral PAH carcinogenicity due to lack of data on individual PAHs). The combined effect of an “overconservative scenario 2.2” and LOQ/2 surrogate concentrations from an inadequate analytical method are the proposed explanation. The 2019 Swiss Federal Food Safety and Veterinary Office survey (ref. 33, Dudler 2021 personal communication) is cited as suggesting ANSES PAH concentrations were overestimated by 2-3 orders of magnitude.

Other compounds at potentially unsafe levels per ANSES — Table 8 (p. 14)

ANSES scenario 1 (organic solvent extraction from shredded diapers) for an infant 0-6 months. Formaldehyde additionally quantified under scenario 2.2 in synthetic urine. 1,2,3-trichlorobenzene, coumarin, limonene, benzyl salicylate, HICC (Lyral®), BPMP (Lilial®), alpha-isomethyl ionone and formaldehyde reported at 25 mg/kg (= LOQ/2 for the fragrances) or specifically quantified for formaldehyde (37.4 mg/kg). Bernard’s HQs (with ANSES assumption of 100% dermal absorption):

Other compounds — Table 9 (p. 15), Bernard’s re-evaluation accounting for fractional dermal/oral absorption

Bernard substitutes ANSES’s 100% dermal absorption with literature-derived percentages for each fragrance (limonene 0.16% per Api et al. 2013; benzyl salicylate 0.031% per Belsito et al. 2007; HICC 14.3% per SCCS 2017 Lyral opinion; BPMP 5.1% per SCCS 2019 Lilial opinion; formaldehyde 0.5% per ATSDR 1999 / SCCS 2014 / Jeffcoat et al. 1983; alpha-isomethyl ionone 100% retained), and adjusts oral NOAELs/TDIs for fractional oral absorption (50% for HICC, BPMP, alpha-isomethyl ionone; 100% for others). Selected values:

• HICC: intake 1.23 × 10⁻² mg/kg/d; MOE 610; MOEref 300; MOEref/MOE 0.49.
• BPMP: intake 4.4 × 10⁻⁴ mg/kg/d; MOE 568; MOEref 100; MOEref/MOE 0.18.
• Alpha-isomethyl ionone: intake 8.59 × 10⁻² mg/kg/d; MOE 291; MOEref 100; MOEref/MOE 0.34.
• Formaldehyde (scenario 1): intake 0.65 × 10⁻³ mg/kg/d; HQ 0.87 × 10⁻² (i.e. ~0.009).
• Limonene: HQ 1.37 × 10⁻³.
• Benzyl salicylate: MOE 1.85 × 10⁶; MOEref/MOE 5.4 × 10⁻⁵.

Under fractional-absorption recomputation, HQ values are largely below 0.1 for limonene and formaldehyde; benzyl salicylate MOE > 10,000. HICC and BPMP retain MOEref/MOE values between 0.1 and 1 (which Bernard notes ANSES might still characterise as “potentially insufficient” protection).

Breast-milk vs diaper intake comparisons — narrative (p. 8, p. 13)

• Under scenario 1 (ANSES): total TEQ from breast milk is 74.8 times the total TEQ from diapers; under scenario 2.1, 336 times; under scenario 2.2, 6.1 times (Table 2 last column).
• Under Bernard’s scenario 2.1 + R = 1%: total TEQ intake from breast milk is more than 400 times the total TEQ intake from diapers (Table 3).
• ANSES’s restriction-proposal concentration limit for total TEQ in diapers (0.7 pg TEQ/kg diaper) is 171-342 times lower than concentrations in human milk in nine European countries 2014-2015 (range 120-240 pg TEQ/kg per ref. 15) (p. 8).
• For PAHs under R = 1%: ΣPAHs intake from diapers (Table 5) is “rather similar” to intake from breast milk; under Swiss-revised PAH concentrations (Swiss 2019 survey, 2-3 orders of magnitude lower than ANSES), intake from mother milk would be > 100 times greater than from diapers.

Reference age-class exposure parameters used (p. 3, p. 5, p. 9)

• Body weight: 3.9 kg (infant aged 0-6 months, per ANSES selection, ref. 7).
• Diapers per day: 7.98 (infant aged 0-6 months, per ANSES).
• Diaper weight: 0.024 kg = 24 g (infant aged 0-6 months, per ANSES).
• Refined scenario 1: T = 7% (ANSES’s refined-scenario T value; Bernard adopts ANSES’s refinement without an external citation in this paper. The Odio et al. 2000 attribution that appears in the underlying ANSES 2019 opinion Table 1 — see anses2019-baby-diaper-safety-france — is not carried into Bernard 2022’s text).
• Refined scenario 2.1: R = 1.32% is ANSES’s refined-scenario value (not Dey’s mean). Bernard substitutes R = 1% (EDANA-recommended per ref. 6) and characterises this as conservative relative to Dey et al. 2016 (ref. 4), in which urine-resurfacing-to-top-sheet under pressure averaged 0.46% with a range of 0.32-0.66%.
• Dermal absorption: 100% retained for PAHs, dioxins, DL-PCBs (lipophilic substances), per ANSES; revised to in vivo/in vitro values for substances known to be poorly absorbed (Table 9).
• Skin surface area in contact with diaper for dermal CSF computation: 234 cm² (Boniol et al. 2008 / EPA 2011, refs. 12, 13).

Critical-effect endpoints (Table 1, p. 4)

• PCDD/Fs and DL-PCBs: reduced sperm count at adult age in humans (used by ANSES, EFSA TDI 0.3 pg TEQ/kg/d) and/or non-cancer systemic effects (used by EPA, RfD 0.7 pg/kg/d for TCDD).
• PAHs: digestive tract tumours in mice (EPA oral CSF 1 (mg/kg/d)⁻¹), neurobehavioural changes in rats exposed during early life (EPA oral RfD 0.3 µg/kg/d), skin cancers in rats (Knafla et al. 2011 dermal CSF 3.5 (µg/cm²/d)⁻¹).
• Other compounds: systemic effects in animals (hepatotoxicity, nephrotoxicity, etc.).

Heavy metals: not addressed in this paper at any point. Bernard’s re-evaluation is restricted to the substance classes for which ANSES reported HRV exceedances in 2019 (PAHs, PCDD/Fs, DL-PCBs, fragrances, formaldehyde). No metal is named in the introduction, methods, dioxin section (§3), PAH section (§4), other-compounds section (§5), conclusions (§6), or references. See Verification notes.

Methods (brief)

• Document type. Peer-reviewed review article (designated “Review” in the journal masthead, p. 1). Single-author. Academic editor Edward F. Fitzgerald.
• Source data. Concentration values, exposure parameters and risk-assessment outputs all reproduced from the ANSES 2019 opinion (ref. 7) and the October 2020 ANSES Annex XV restriction dossier to ECHA (ref. 8). No primary chemical analyses were performed for this re-evaluation.
• Exposure equations (p. 2). Bernard reproduces the three ANSES daily-intake (DI) equations: scenario 1 (organic-solvent extraction from shredded diapers or shredded diaper parts) DI = C × W × N × T × A / Bw; scenario 2.1 (synthetic-urine extraction from shredded diapers) DI = C × W × N × R × A / Bw; scenario 2.2 (synthetic-urine extraction from whole diapers) DI = C × W × N × A / Bw; where DI is daily intake, C concentration in diaper, W weight of diaper, N number of diapers used per day, T fraction transferred to skin (%), R rewet factor (%), A fraction absorbed by skin (%), Bw body weight. Bernard’s re-evaluations apply T = 7% (ANSES’s refined value; Bernard uses but does not separately cite a primary source for the 7% in this paper) and R = 1% (EDANA-recommended per ref. 6; characterised by Bernard as conservative relative to Dey et al. 2016’s measured mean of 0.46% with range 0.32-0.66%).
• Risk-assessment equations (p. 3). For threshold effects: HQ = D / TDI where D is daily intake and TDI tolerable daily intake (both in pg, µg or mg/kg body weight). For no-threshold (carcinogenic) effects assumed by ANSES for PAHs: ECR = DI × CSF × T × ADAF / 70 where ECR is excess cancer risk, DI daily intake in µg/kg/d, CSF cancer slope factor in (µg/kg/d)⁻¹, T duration of exposure (years), 70 the conventional lifetime duration, and ADAF age-dependent adjustment factor (default 10 for children < 2 years; 3 for age 2-< 16 years per ref. 10 EPA 2017 benzo[a]pyrene tox profile).
• Comparator: breast-milk intake. For dioxin/DL-PCB intake from breast milk: French breast-milk concentrations of Focant et al. 2013 (ref. 16) adjusted to 2017 by 10%/yr decline (Fång et al. 2013, ref. 17); 5 kg infant body weight, 700 mL/d milk, 25 g/L lipids. For PAHs from breast milk: Santonicola et al. 2017 (ref. 32) data, same 5 kg / 700 mL / 25 g/L assumptions.
• Comparator: Swiss FSVO 2019 PAH survey. Cited as personal communication from V. Dudler, FSVO Bern, 2021 (ref. 33). Five brands of diapers; absorbent-core PAHs < 0.15 to 4.6 µg/kg; benzo[a]pyrene and dibenzo[a,h]anthracene specifically < 0.12 to 1.4 µg/kg. “2-3 orders of magnitude lower than those at the basis of the quantitative health risk assessment performed by ANSES” (p. 9).
• Reference literature for absorption corrections. Limonene human in vivo: Api et al. 2013 (ref. 46). Benzyl salicylate human skin in vitro: Belsito et al. 2007 (ref. 47). HICC human skin in vitro: SCCS 2017 (ref. 48). BPMP human skin in vitro: SCCS 2019 (ref. 49). Formaldehyde monkey in vivo: Jeffcoat et al. 1983 (ref. 42) and ATSDR 1999 (ref. 43) and SCCS 2014 (ref. 44).
• Funding and conflict-of-interest declarations. Funding: International Disposables and Nonwovens Association (EDANA). Conflict of interest statement (p. 15): “The author declares no conflict of interest. The funder had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results.” See Verification notes for HMI’s framing of this disclosure.
• Author affiliation. Alfred Bernard, Institut de Recherche Expérimentale et Clinique (IREC), Université catholique de Louvain, 1200 Brussels, Belgium; Honorary Research Director of the National Fund for Scientific Research (Belgium).

Implications

• Certification (HMTc). This paper provides no heavy-metal occurrence data and contributes nothing directly to the HMTc 10-analyte panel (Pb, tAs, Cd, MeHg, tHg, iAs, Ni, Al, Cr-VI, Sn). For Category 9 Row 7 (diapers and diaper components), it is the industry-funded peer-reviewed counter-position to the ANSES 2019 regulatory case (anses2019-baby-diaper-safety-france), and as such it is an important methodological data point for any future HMI dermal-exposure model in this product category: the contested skin-transfer parameter (T = 100% vs 7%), rewet factor (R = 100% vs 1.32% vs 1%) and dermal-absorption assumptions (100% vs literature-derived fractional values) will all need to be engaged with regardless of analyte class, because the same DED framework applies to metals as to PAHs/dioxins. The breast-milk comparator that Bernard uses for PCDD/Fs and DL-PCBs is potentially reusable for HMI synthesis of dermal-vs-dietary metal exposure (Pb, Cd, MeHg specifically have breast-milk concentration data that could populate a parallel comparator), but the methodological choice to compare dermal-route diaper exposure with oral-route dietary exposure is itself contested in the paper (Bernard does it; ANSES does not). The paper’s principal regulatory contribution — the argument that ANSES PAH concentrations were 2-3 orders of magnitude overestimated due to LOQ/2 surrogate concentrations from an analytical method with LOQ > 150 µg/kg whereas food-method LODs are ~1.5 µg/kg — is a generalisable critique of LOQ-as-surrogate-concentration in low-detection-frequency datasets, which directly applies to how HMI should handle below-LOQ metal results in this product class. Useful only as adjacent regulatory/methodological context, never as standards-setting evidence.
• Courses. Useful for any HMTc Cat 9 module covering (i) the structure of an industry-funded peer-reviewed counter-position to a national-agency regulatory assessment, (ii) the methodological contest over skin transfer and rewet factor in diaper dermal-exposure modelling, (iii) the LOQ-as-surrogate-concentration problem and how analytical-method LODs affect risk-assessment outputs, and (iv) the breast-milk-intake comparator and its methodological limitations (oral vs dermal route; lifetime accumulation vs lactation transfer).
• App. Not directly applicable to the heavy-metals consumer app. Useful as background for a future app explainer on the diaper-safety controversy and the difference between regulatory and industry-funded risk assessments in this product class.
• Microbiome. Not addressed.

Wiki pages this source may touch

• diapers-and-components — primary routing destination (HMTc Cat 9 Row 7 scaffold). Industry-funded peer-reviewed re-evaluation of the ANSES 2019 regulatory opinion; methodological critique of skin-transfer, rewet-factor, dermal-absorption and LOQ/2 surrogate-concentration choices; breast-milk intake comparator for PCDD/Fs, DL-PCBs and PAHs.

Verification notes

• Heavy metals null — strict reading. Bernard’s introduction (p. 1-2) frames the paper as a re-evaluation of ANSES’s exposure and risk-assessment findings for “polycyclic aromatic hydrocarbons (PAHs), dioxins (PCCD/Fs) and dioxin-like polychlorobiphenyls (DL-PCBs)” plus “formaldehyde and some fragrances.” Section 2 (Materials and Methods) limits scope to “PAHs, PCDD/Fs and DL-PCBs for which HRVs in the ANSES report were exceeded in all age groups of children” plus “substances for which HRVs were exceeded only during the first year of life or for which there was a risk of HRVs exceedance when aggregating intake from diapers with that from other potential sources of exposure” (p. 4 last paragraph). Heavy metals appear in neither in-scope category — ANSES did not report any heavy-metal HRV exceedance, so Bernard does not engage them. The references list (refs. 1-50) contains no heavy-metal-specific entry. Grep over the full extracted text for “lead” “cadmium” “arsenic” “mercury” “Pb” “Cd” “As” “Hg” “nickel” “Ni” “aluminium” “Al” “chromium” “Cr” “tin” “Sn” returns hits only for the chemical-symbol “As” used as the preposition “as” and tin-of-cans-style false matches; no heavy-metal scientific content. The page records metals: [] to reflect this strict reading. Readers needing per-metal evidence for this product class should consult anses2019-baby-diaper-safety-france (which records the agency-level null finding) and the underlying INC 2016/2017/2018 publications directly.
• Funder framing — Part 12 brand firewall and disclosure-honesty. The funder, International Disposables and Nonwovens Association (EDANA), is the European trade association for the disposable diaper industry — i.e. the industry whose products ANSES had recommended restricting via the October 2020 ECHA dossier. This is a substantive conflict of interest that the paper discloses on p. 15 (“Funding: This study was supported by the International Disposables and Nonwovens Association (EDANA)”) but characterises with the standard MDPI conflict-statement language (“The author declares no conflict of interest. The funder had no role in the design of the study…”). HMI does not adjudicate the truthfulness of the no-role declaration, but the funding source is a fact about the paper’s epistemic context that any downstream synthesis must engage with — particularly because Bernard’s substantive conclusions (overconservative ANSES assumptions; LOQ-based concentrations from inadequate analytical method; “totally unacceptable risks” Bernard recomputes back to acceptable bands; restriction-proposal limits “five orders of magnitude lower than the LOD”) are all directionally favourable to the funder’s regulatory interest. Part 12 brand-firewall does not exclude this paper: EDANA is named as a trade association (not a specific brand) and is named as the funding source, not as a measured product, so the disclosure is regulatory-process metadata (Part 12 Exception 1, regulatory-event subject). EDANA’s prior 2021 Call-for-Evidence response to ECHA (ref. 6) is also cited as a methodological source for the R = 1% recommendation; this is treated as a scientific-method citation (Part 12 Exception 2 analogue), not as a brand listing. The page does not name any specific diaper brand or commercial product.
• Evidence-tier B rationale. Peer-reviewed in a Web-of-Science/PubMed-indexed MDPI journal (IJERPH 2021 impact factor ~4.6 at time of publication; rapid open-access publication model). Single-author review article (not original measurements, not a systematic review). Substantial industry funding (EDANA) directly tied to the regulatory outcome being contested. Evidence tier B reflects: (i) peer-reviewed status (above C-tier), (ii) but single-author re-analysis rather than primary measurement or independent systematic review (below A-tier), (iii) with industry funding tied to the substantive conclusions (further weight against A-tier). Future synthesis should use Bernard 2022 as a critical-review balancing source, never as a standalone authority, and should pair every Bernard claim with the ANSES counter-statement.
• Atypical PAH concentration pattern — Bernard’s central methodological objection (p. 9). The PAH concentrations of 249-598 µg/kg in Table 4 show only ~2.4-fold variation across 10 PAHs, whereas individual PAHs in environmental and biological matrices typically vary by factors of 10-100 (Bernard cites EFSA 2008, ref. 14). Bernard interprets this flat pattern as artefactual, consistent with all values being clustered around LOQ/2 of the ANSES analytical method (LOQ > 150 µg/kg per individual PAH). Two independent observations cited in support: (i) the 2019 Swiss FSVO survey (ref. 33) of five diaper brands found absorbent-core PAHs < 0.15 to 4.6 µg/kg using a method with LODs comparable to food-PAH methods, 2-3 orders of magnitude lower than ANSES values; (ii) ANSES’s own proposed concentration limit for benzo[a]pyrene (2.7 ng TEQ/kg) is 5 orders of magnitude below the LOD of the analytical method that generated ANSES’s risk-assessment input data — a self-inconsistency Bernard flags as evidence that the ANSES analytical method cannot quantify PAHs at the levels its risk assessment is concerned with.
• PCDD/F vs DL-PCB extraction inversion — Bernard’s second methodological objection (p. 5). Under organic-solvent extraction of shredded diapers (scenario 1), PCDD/Fs and DL-PCBs contribute almost equally to total TEQ (39.8 and 43.4 pg TEQ/kg respectively, Table 2). Under synthetic-urine extraction of shredded diapers (scenario 2.1), PCDD/Fs dominate (92.0 pg TEQ/kg vs 7.55 pg TEQ/kg DL-PCBs; PCDD/Fs ~92% of TEQ). Under synthetic-urine extraction of whole diapers (scenario 2.2), DL-PCBs dominate (63.6 vs 8.84; DL-PCBs ~88% of TEQ). The inversion between scenarios 2.1 and 2.2 — same extraction medium (urine simulant), different sample preparation (shredded vs whole) — is characterised as “illogical and atypical” (p. 5). Bernard’s framing is that this inversion “raises questions about the accuracy of PCCD/Fs and DL-PCBs exposure data used by ANSES.” No alternative mechanism (e.g. matrix-dependent congener partitioning between liner and absorbent core) is proposed.
• PCB-126 contribution — Bernard’s third methodological objection (p. 6, p. 7). Under scenario 2.2, ANSES’s TEQ for DL-PCBs is dominated by PCB-126 (~90% of DL-PCBs TEQ per ANSES). Bernard cites Strapácová et al. 2018 (ref. 22) reporting that human-lung-cell relative effective potencies (REPs) of PCB-126 are 10-100× lower than the WHO 2005 TEF values derived from rat lung cells, and PCB-118 and PCB-156 were “almost inactive” in human cells. The Russian Children’s Study (Minguez-Alarcon et al. 2017, ref. 27) reported semen-parameter associations only with PCDDs TEQ, not with PCDFs, DL-PCBs or total TEQ. Bernard’s framing: if Russian-study evidence for the sperm-count endpoint is specific to PCDDs (Bernard’s reading), then ANSES’s HQ for total TEQ using EFSA TDI of 0.3 pg TEQ/kg/d overestimates the PCDD-specific risk by including PCDFs and DL-PCBs in the numerator while the denominator’s mechanistic basis applies only to PCDDs. This is a substantive but contested epidemiological interpretation; the EFSA expert panel’s published reading is that lack of DL-PCBs correlations reflects 10-100× lower human-cell AhR-activating potency rather than no contribution (ref. 15).
• Breast-milk comparator — methodological note. Bernard’s central rhetorical move is the breast-milk-vs-diaper intake ratio: under his preferred scenario (2.1 with R = 1%), breast-milk intake of total TEQ is more than 400× diaper intake; breast-milk intake of ΣPAHs is “rather similar” or higher than diaper intake; ANSES’s proposed total-TEQ diaper concentration limit (0.7 pg TEQ/kg) is 171-342× lower than European breast-milk concentrations. The implicit argument is that if breast-milk PAH/dioxin intake “is unanimously recognized as protective” against various diseases including cancers despite higher contaminant levels, then diaper dermal exposure at far lower intakes cannot plausibly pose the cancer/sperm-count risks ANSES estimated. HMI synthesis should engage this comparator carefully: the route (dermal vs oral), the matrix (synthetic-urine extract vs human-milk fat), the duration (24-36 months diaper use vs 6-24 months breastfeeding) and the population-frame (whole-population diaper exposure vs ~60-70% breastfeeding initiation rates in France) are all non-trivially different, and the “breast-milk is unanimously protective” framing elides that the protective effects are net of contaminant exposure, not because of it. This page reports Bernard’s comparison as he reports it without endorsing the implicit causal inference.
• Brand firewall — Part 12. The paper names no specific diaper brand at any point. The fragrance trade names “Lyral®” and “Lilial®” (= hydroxyisohexyl 3-cyclohexene carboxaldehyde and butylphenyl methylpropional) are scientific identifiers retained per Part 12 Exception 2 (scientific-method vendor/material names), consistent with handling in anses2019-baby-diaper-safety-france. EDANA is named as the funder and as the trade association whose 2021 Call-for-Evidence response (ref. 6) is the methodological source for the R = 1% rewet factor — Part 12 Exception 1 (regulatory-process metadata). The paper does not mention Group’Hygiène; only EDANA appears as a trade-association name. No brand-firewall scrubbing needed.
• Source-internal inconsistency — HQ 11.9 vs 11.8 for scenario 2.2 total TEQ. PDF Table 2 (p. 5) reports the scenario 2.2 hazard quotient for the sum of PCDD/Fs + DL-PCBs as 11.9, and the wiki Table 2 reproduction faithfully copies that value. The narrative on PDF p. 7 (“Under scenario 2.2, deemed the most reliable according to ANSES, the hazard quotient (HQ) for the total TEQ reached a value of 11.8”) states 11.8. This is a source-internal inconsistency (table vs narrative) of 0.1 unit. The wiki page uses the Table 2 value because tables are typically the more rigorously checked component of a manuscript at peer review; readers requiring the narrative value can read PDF p. 7 directly.
• Wiki/HMTc firewall — Part 2. This page reports what Bernard 2022 concludes about the ANSES 2019 risk assessment. It does not extrapolate to HMTc thresholds, does not advocate for an HMTc-relevant position on diaper safety, and does not synthesise across the three diaper-regulatory sources (anses2019-baby-diaper-safety-france, bfr2019-diaper-substances-anses-commentary, this page). The author’s industry funding is documented as a fact about the paper, not used to dismiss the substantive methodological points (which are independently checkable against the ANSES opinion and the cited Swiss survey and absorption literature). The page records both the funder relationship and the methodological claims; future Part 9 synthesis decides how to weight them.
• Document identity. Bernard A. 2022. Dermal Exposure to Hazardous Chemicals in Baby Diapers: A Re-Evaluation of the Quantitative Health Risk Assessment Conducted by The French Agency for Food, Environmental and Occupational Health and Safety (ANSES). Int. J. Environ. Res. Public Health 19(7):4159. DOI: 10.3390/ijerph19074159. Received 29 July 2021; accepted 25 September 2021; published 31 March 2022. CC BY 4.0. Funded by EDANA. Single-author. 18 pp. Cited 50 references.
• Routing destination check. products/diapers-and-components exists as wiki/products/diapers-and-components.md (HMTc Cat 9 Row 7 scaffold; same routing destination as anses2019-baby-diaper-safety-france and bfr2019-diaper-substances-anses-commentary).
• Audit subagent (2026-06-01, fresh-context general-purpose agent) — REVISE verdict; six findings applied, one rejected as false positive.
  • ❌ Finding 1a (verified correct, applied): Wiki Table 4 reproduction marked Cyclopenta[c,d]pyrene’s Hazard Quotient column as ”—” while PDF Table 4 p. 9 shows HQ = 5.51. Verified by re-reading p. 9: the row reads “Cyclopenta[c,d]pyrene 311 15.3 0.1 1.53 [merged RfD 0.3] 5.51 [merged CSF 1] 1.09 × 10⁻⁴”. Filled in HQ 5.51, EPA Oral RfD 0.3, EPA Oral CSF 1. Chrysene row also had merged-cell RfD/CSF filled in (0.3 and 1) for consistency with the rest of the BaP-family rows.
  • ❌ Finding 1b (verified incorrect, REJECTED as false positive): Audit claimed wiki Table 4 missed 5-methylchrysene HQ = 0.51. Re-read PDF Table 4 p. 9 carefully: the 5-methylchrysene row reads “5-methylchrysene 311 15.3 0.01 0.15 [merged RfD] [HQ cell blank] [merged CSF] 1.09 × 10⁻⁴”. The HQ cell is genuinely blank in the source table; the 0.51 value the audit reported is not in the source. The blank likely reflects that 5-methylchrysene’s TEQ-intake (0.15 µg TEQ/kg/d) divided by the BaP RfD (0.3 µg/kg/d) would give 0.5, which the authors apparently chose not to tabulate alongside the cancer-only assessment for this PAH, but no 0.51 value is printed. Wiki retained ”—” for this cell.
  • ❌ Finding 2 (verified correct, applied): Wiki attributed T = 7% to “Odio et al. 2000”. Re-checked the full PDF reference list (refs 1-50 across p. 16-18): no Odio entry. PDF p. 3 reads only “T value of 7% instead of 100%” with no citation tag. The Odio attribution was carried over from the underlying ANSES 2019 opinion (whose Table 1 does cite Odio et al. 2000 for the 7% — see anses2019-baby-diaper-safety-france Key numbers Exposure-parameters table) but is not present in Bernard 2022’s text. Corrected to “ANSES’s refined-scenario T value; Bernard adopts ANSES’s refinement without an external citation in this paper” in body, Methods, and frontmatter sample_population.
  • ⚠️ Finding 3 (verified correct, applied): Wiki attributed R = 1.32% to “Dey et al. 2016 mean”. Re-read PDF p. 3: the 1.32% is ANSES’s refined-scenario value (sentence “rewet factor under scenario 2.1 (R value of 1.32% instead of 100%)” with no Dey attribution at this point); Dey’s actual measured values are reported separately (“0.46% with a range of 0.32-0.66%”) to characterise Bernard’s R = 1% choice as “conservative since in the study of Dey et al. [4]…“. Corrected attribution to split: R = 1.32% is ANSES’s refined value; R = 1% is Bernard’s substitution per EDANA; Dey’s reported values are 0.46% mean / 0.32-0.66% range.
  • ⚠️ Finding 4 (verified correct, applied): Wiki Table 6 narrative used the label “Σ PAHs (8)” for the sum row whose source-table label is “S PAHs” and which sums all 10 PAHs listed in Table 6 (the same 10 from Table 4). Corrected to “Σ PAHs (sum of all 10 PAHs listed in Table 6)” to remove the spurious “(8)” subset implication.
  • ⚠️ Finding 5 (verified correct, applied): Wiki Table 4 ΣPAHs concentration “3.722 (sum)” preserved the printed source numeral but was ambiguous (the value is 3,722 µg/kg, the sum of ten individual PAH concentrations each in the hundreds of µg/kg, presented in European decimal notation 3.722 = 3,722). Corrected the three ΣPAHs sum rows to “3,722 (sum µg/kg)”, “2,133”, “1,035” using comma-thousands notation for HMI conventions.
  • ⚠️ Finding 6 (verified correct, applied): Wiki Verification notes mentioned “Group’Hygiène” as a trade association named in the PDF. Re-read PDF in full: Group’Hygiène does not appear in Bernard 2022. Only EDANA is named (as funder and as ref. 6 trade-association methodological source). The Group’Hygiène mention was a carry-over from anses2019-baby-diaper-safety-france where it does appear in the stakeholder-hearing list. Removed from the brand-firewall note in this page.
  • ⚠️ Finding 7 (audit advisory, applied as documentation): Wiki Table 2 reproduction shows HQ 11.9 for the scenario 2.2 total TEQ row (matches PDF Table 2 p. 5). PDF narrative p. 7 says 11.8 for the same value (source-internal table-vs-narrative inconsistency of 0.1 unit). Added a Verification note documenting this source-internal inconsistency and the wiki’s choice to use the Table 2 value over the narrative value.
  • Checks 2 (slug vocabulary), 5 (Part 2 wiki/HMTc firewall): both ✅ clean per audit, no changes needed.

Ingest log

• 2026-06-01 fresh ingest (Claude Opus 4.7, autonomous v2.0 manual-fetch skill). NEW path. Three identity checks against wiki/sources/ returned no hits: DOI 10.3390/ijerph19074159 not present; raw_handle MFK_11-ijerph-19-04159-2022 not present; cite-key stem bernard2022 not present. PDF SHA-256 e45478f7fffbeb2d3a1cea1ab69a5da57d7415812bd8deb665e2847d578080ec. Folder: raw/Manual Fetch Kimi /May 21 Kimi_Agent_Download Corruption Issue/_extracted_infantcontact_03_Diapers/03_Diapers/. Source is an industry-funded (EDANA) single-author peer-reviewed re-evaluation of the ANSES 2019 baby-diaper safety opinion (18 pp.); metals: [] reflects that the paper does not engage heavy metals at any point (paper scope is restricted to substances for which ANSES reported HRV exceedances: PAHs, PCDD/Fs, DL-PCBs, formaldehyde, fragrances). Routed to [[products/diapers-and-components]] per matrices: [diaper]. near_duplicates flags the upstream ANSES opinion (anses2019-baby-diaper-safety-france) and the parallel BfR commentary (bfr2019-diaper-substances-anses-commentary); the three pages together cover the regulatory-and-industry-counter-position triangle on this dossier as of 2026-06-01.

Page history

The five most recent substantive edits to this page. The full version history lives in git; when DOI minting comes online (see schema docs), each entry below will also link to a version-pinned DataCite DOI.