Occupational cancer in Britain

The agents that the International Agency for Research on Cancer (IARC) has classified as either definite (Group 1) or probable (Group 2A) human carcinogens for SNC and pharyngeal cancer, for which estimation has been carried out, are summarised in Table 1 . Employment in isopropanol manufacture industry was not considered for the SNC-attributable fraction (AF) calculation, as no data were available on which to base estimates. Other exposures and industries/occupations that appear to be associated with an increased risk of SNC but not classified by IARC as a group 1 or 2A carcinogen include polycyclic aromatic hydrocarbons and the textile manufacturing industry. A detailed review of occupational risk factor studies identified for pharyngeal cancers (including NPC) and SNC is provided in the relevant Health and Safety Executive technical reports ( HSE, 2012a , 2012b ). Occupational exposure to fine particulate wood dust is an established cause of NPC and SNC. No consistent associations have been found between wood dust and other pharyngeal cancers. The highest exposures to wood dust have generally been reported for occupations in the furniture-making industry, although carpenters, machine operators, workers in the construction industry and in logging/forestry operations also experience exposure to wood dust ( Demers et al, 1995 ). In the United Kingdom, despite a decline in exposures to wood dust at levels in excess of the maximum exposure limit between 1990 and 2000, exposures to high levels of wood dust remain in some wood-working activities ( Dilworth, 2000 ). Associations appear to be strongest for exposure to hardwood dust and fine particulate dust, with a dose–response relationship reported for both wood dust levels and duration of exposure ( IARC, 1995 ). The risk estimates used for the calculation of the AF for both SNC and NPC have been taken from a pooled reanalysis of data from five cohort studies (British furniture workers, members of the union representing furniture workers in the United States, plywood workers and wood model makers; Demers et al, 1995 ). A significantly high excess of nasal cancer was observed (standardised mortality ratio (SMR)=3.1, 95% CI=1.6–5.6), particularly among furniture workers (SMR=4.3, 95% CI=2.2–7.8) and among those with definite wood dust exposure (SMR=8.4, 95% CI=3.9–16.0). The overall risk estimate for SNC (SMR=3.1, 95% CI=1.6–5.6) is based solely on cases from a British furniture worker cohort and has been used for the AF calculation for the high-exposure group. As no dose–response data are available, a RR of 2.0 (95% CI=0.3–5.2), based on a harmonic mean of the high/low ratios across all other cancer–exposure pairs in the overall project for which data were available, has been estimated for the low-exposure level category. Demers et al (1995) also report a statistically significant increase in mortality for NPC in woodworkers (specifically furniture and plywood workers: SMR=2.4, 95% CI=1.1–4.5), and this has been used to determine the AF for NPC for woodworkers in all relevant high-exposure industries. Although a dose–response relationship was identified for definite exposures (SMR=5.3, 95% CI=1.7–12.4), this risk estimate is considerably higher than that reported in other studies. As low-exposure risks are not easily converted from the qualitative grading provided in the paper by Demers et al (1995) , the risk estimate for low-exposed groups has been set to 1. Other studies have also found similar increased risks for SNC in relation to wood dust exposure in several countries. These include the following: an increased risk of SNC for men exposed to wood and wood dust in British Columbia, Canada (RR=2.3, P =0.02), which remained significant after adjusting for smoking and ethnicity (RR=2.5, P <0.03; Elwood, 1981 ); very high excesses of SNC in men working in furniture factories in Buckinghamshire, UK ( Rang and Acheson, 1981 ); and high risks in people working in the wood and paper industry, in furniture and cabinet making and in carpentry work, in a case–control study in the Netherlands ( Hayes et al, 1986 ). Two population-based case–control studies in Washington State also found that nasal cancer was strongly associated with employment in wood-related occupations (odds ratio (OR)=2.4, 95% CI=0.8–6.7) increasing to an OR of 3.1 (95% CI=1.0–9.0) after a 15-year induction period was considered ( Vaughan and Davis, 1991 ). The authors suggest that exposure to softwood dust increases the risk of sinonasal squamous cell cancer. Other studies also support the association between wood dust exposure and NPC, although there is potential coexposure to formaldehyde reported in some of these studies ( Armstrong et al, 2000 ; Vaughan et al, 2000 ). Formaldehyde is used mainly in the production of phenolics, urea, melamine and polyacetal resins, and as an intermediary in industrial chemical manufacture. These have wide uses as adhesives and binders for wood products, pulp and paper manufacture; in synthetic vitreous fibre industries, for the production of plastics and coatings; and in textile finishing. High formaldehyde exposure occupations include textile operations and wood product manufacture/processing (with coexposure to wood dust); short-term high-exposure episodes have been reported for embalmers, pathologists and paper industry workers. The risk estimate for the calculation of the AF for NPC in association with exposure to formaldehyde has been taken from a study of workers in formaldehyde industries in the US ( Hauptmann et al, 2004 ), which was cited as key defining evidence by IARC in support of the NPC and formaldehyde link ( IARC, 2006 ). The SMR value of 2.10 (95% CI=1.78–9.13) from this study has been used for the high-level-exposure industries, including embalmers and funeral directors. There is, however, some uncertainty about the risk of NPC at low-level exposure to formaldehyde, and the RR for low or background exposures to formaldehyde has thus been set to 1 for AF estimation. In addition to the study by Hauptmann et al (2004) , there are a large number of studies of different groups of workers investigating the association between exposure to formaldehyde and NPC with some positive and negative risk estimates ( HSE, 2012a ). Marsh et al (2007) reanalysed the cohort mortality data for >25,000 workers in 10 US plants (manufacturing formaldehyde or using it in the manufacture of other products) reported by Hauptmann et al (2004) , and suggested that the SMR calculated in Hauptmann's paper (2.1, 95% CI=1.05–4.21) may be biased because of unusual findings at one of the 10 factories included in the NCI cohort study. A study by Coggon et al (2003) of a cohort of ∼ 14,000 workers from UK chemical facilities employed between 1937 and 1965, reported fewer observed deaths from NPC than were expected (SMR 0.5, 95% CI=0.01–2.79). Pinkerton et al (2004) and Dell and Teta (1995) did not observe any cases of NPC in retrospective cohort studies of mortality in workers (garment and plastic manufacturing respectively) exposed to formaldehyde. Case–control studies such as those by Vaughan et al (2000) (OR=1.3, 95% CI=0.80–2.10) and Hildesheim et al (2001) (OR=1.4, 95% CI=0.93–2.2) generally reveal higher RRs than cohort studies. In addition, higher risks for NPC have been reported in studies of embalmers and funeral directors, for example, SMR=2.10 (95% CI=0.6–5.4; Hayes et al, 1990 ). The risk estimate used in the calculation of the AF for SNC in relation to exposure to formaldehyde was taken from a pooled analysis of European case–control studies, including use and production of formaldehyde ( Mannetje et al, 1999 ). No excess of SNC associated with formaldehyde was observed for female workers (OR=0.83, 95% CI=0.41–1.69); there was a significantly increased risk found in men (OR=1.66, 95% CI=1.27–2.17), adjusted for other concurrent exposures including wood dust. This has been used for the high-exposed industries. The RR for low and background exposures and exposures of female workers to formaldehyde has been set to 1 for AF estimation. Results from epidemiological studies of SNC and formaldehyde are inconsistent, with a number of studies showing an increased risk and others showing no excess risks, and often different findings for NPC and SNC ( HSE, 2012b ). For example, Hauptmann et al (2004) found too few deaths from SNC to confirm an association with formaldehyde exposure. Coggon et al (2003) also reported a lack of association for SNC (SMR=0.87, 95% CI=0.11–3.14) as for NPC. In contrast, Hansen and Olsen (1995) found, in a mortality study of 265 companies in Denmark where exposure to formaldehyde occurred, a significantly elevated risk for SNC cancer overall (standardised proportionate incidence ratio (SPIR)=2.3, 95% CI=1.3–4.0) plus elevated risks for workers exposed to both wood dust and formaldehyde (SPIR=5.0, 95% CI=0.5–13.4) and among workers moderately exposed to formaldehyde but with no probable exposure to wood dust (SPIR=3.0, 95% CI=1.4–5.7). Mustard gas was used as a vesicant in chemical warfare during the First World War, but its use was prohibited thereafter by the Geneva Convention of 1925. Currently, this chemical is only produced for use in military research and is a recognised carcinogen in humans ( IARC, 1987 ). A few studies have reported excesses of pharyngeal and/or laryngeal cancer in workers at mustard gas factories employed up to 1945 ( Blair and Kazerouni, 1997 ), but the manufacture of mustard gas ceased in the United Kingdom in the 1940s. Given the low numbers likely to be exposed during the relevant exposure period, an attributable risk has not been calculated. The risk estimate used in the calculation of the AF for SNC in relation to boot and shoe manufacture and repair has been taken from a mortality study of men employed in the boot and shoe manufacturing industry in Great Britain ( Fu et al, 1996 ). An increased overall risk of nasal cancer was found and has been used for the AF calculation (SMR=7.41, 95% CI=3.83–12.94). The risk in the English cohort appeared to be associated with exposure to leather dust (probable: SMR=11.70, 95% CI=5.34–22.20, based on nine cases; high: SMR=25.00, 95% CI=0.63–139.00, based on one case). In the same paper, Fu et al (1996) also investigated an Italian cohort and found an excess risk of 9.09 (95% CI=0.23–50.65, based on one case) for nasal cancer. The results support earlier studies where RRs for SNC well in excess of 10-fold have been reported, with workers in the dustiest operations at greatest risk ( Pippard and Acheson, 1985 ; Merler et al, 1986 ). However, not all epidemiological studies have reported an excess of nasal cancer ( HSE, 2012b ). Nickel is used in the production of stainless steel, copper–nickel alloys and other corrosion-resistant alloys, as well as in electroplating, as a chemical catalyst, and in the manufacture of alkaline batteries, coins, welding products, magnets, electrical contacts and electrodes, spark plugs, machinery parts and surgical and dental prostheses. Exposure to nickel occurs by inhalation, ingestion and skin contact of airborne fumes, dusts and mists in nickel and nickel alloy production plants, as well as in welding, electroplating, grinding and cutting operations. Early studies of industrial cohorts suggested that the risk of SNC associated with nickel exposure arose in the course of the nickel refining process, probably through exposure to nickel oxides or a mixture of oxides and sulphides of nickel ( Roush et al, 1980 ). Most of the observations of elevated risk appear to be in workers exposed to high levels of soluble nickel compounds through processes that have not been used in Britain for many years. The risk estimate used in the calculation of the AF for SNC in relation to nickel exposure has been taken from a study by Grimsrud and Peto (2006) of workers employed at the largest nickel carbonyl refinery in Europe, located in Clydach, Swansea, Wales (SMR=8.70, 95% CI=1.05–31.41, based on only two cases). Similar to nickel, chromium VI (Cr VI) is resistant to corrosion and is widely used in chromium alloys and chrome plating, as well as in steel production. Exposures to chromium and particularly Cr VI occur during a range of mining, refining and production activities including chromate production, welding, chrome pigment manufacture, chrome plating and spray painting. The risk estimate used in the calculation of the AF for SNC in relation to Cr VI exposure has been taken from a cohort of chromium smelter workers at four plants in New Jersey, USA, employed between 1937 and 1971 ( Rosenman and Stanbury, 1996 ). After adjustments for age and time period, a significantly elevated risk for SNC was found in white male employees (proportionate cancer mortality ratio=5.18, 95% CI=2.37–11.30). This risk estimate has been used for the high-exposure group, offering a more cautionary estimate than risk estimates from other, smaller studies ( HSE, 2012b ). Positive associations were found for duration of employment, as well as time from first employment to last known employment, and deaths were distributed across all four plants. Because of the absence of sufficient dose–response data specific to chromium and sinonasal cancer (SNC), a risk estimate of 3.34 (95% CI=0.4–10.5) was estimated for the low-exposure-level category based on a harmonic mean of the high/low ratios across all other cancer–exposure pairs in the overall project for which data were available. Mineral oils are primarily used as a lubricant base to produce further refined oil products, including engine oils, machine oils and metalworking oils for a variety of industries. Few studies have evaluated the association between occupational exposure to mineral oils and SNC. However, Roush et al (1980) reported a case–control study that identified a positive association between employment involving exposure to cutting oils and SNC (OR=2.8, 95% CI=1.4–5.7), although exposure to individual substances was not evaluated. This estimate has been used for the high-exposure group. A risk estimate of 1.8 (95% CI=0.2–5.3) has been estimated for the low-exposure-level category based on a harmonic mean of the high/low ratios across all other cancer–exposure pairs in the overall project for which data were available. An RR of 1 was used for background-level exposure. The data sources, major industry sectors and jobs for estimation of numbers ever exposed over the risk exposure period (REP) defined as the period during which exposure occurred that was relevant to the development of the cancer in the target year 2005, are given in Table 1 . Wood dust exposure was categorised as high in the construction, furniture-making, wood product manufacture and forestry/logging industries where exposure to fine particulate dust was common. High exposures to formaldehyde were assumed for textile and glass manufacture, education, research, health, household and personal services. In the boot and shoe manufacturing and repair industry, only individuals exposed to vegetable-tanned leather dust are believed to be at risk (Coggon, personal communication). Estimation for nickel was restricted to men employed since 1953 at the only British refining plant at Clydach, South Wales. For exposure to mineral oils, work involving exposure to metalworking fluids as a fine mist spray was assumed to have high exposure; this included metal workers such as machine operators, tool setters and fitters. Because of assumptions made about cancer latency and working age range, only cancers in patients aged 25 years and above in 2005/2004 could be attributable to occupation. In the present study, a latency period of at least 10 years and up to 50 years has been assumed for NPC and SNC, which corresponds well with the mean latency period of 43 years reported for SNC ( Roush, 1996 ). Attributable fractions for NPC and SNC have been calculated for formaldehyde and wood dusts (for both cancers) and in addition for SNC, leather dust, nickel, Cr VI and mineral oils. Table 2 provides a summary of the attributable deaths and registrations in Britain for 2005 and 2004 and shows the separate estimates for men and women, respectively. For all exposure scenarios combined, the overall AFs and attributable deaths and registrations for NPC and SNC were 8.03% (95% CI=1.78–34.33%) and 32.67% (95% CI=21.53–55.01%), respectively, giving in total 8 (95% CI=2–33) deaths and 15 (95% CI=3–65) registrations for NPC, and 38 (95% CI=25–63) deaths and 126 (95% CI=83–212) registrations for SNC. In total, there were an estimated 342 048 men and 182 153 women exposed to formaldehyde across the various industries and professions over the REP. For NPC, the overall AF from exposure to formaldehyde was 0.44% (95% CI=0.00–2.18%), with 0 (95% CI=0–2) attributable deaths and 1 (95% CI=0–4) attributable registration. The overall AF for SNC from exposure to formaldehyde was 0.17% (95% CI=0.10–0.45%), with 0 (95% CI=0–1) attributable deaths and 1 (95% CI=0–2) attributable registration. There were an estimated 1 744 690 men and 404 352 women in total exposed to wood dusts across the various wood industries over the REP (1956–1996). For NPC, the overall AF from exposure to wood dust was 7.62% (95% CI=1.08–17.98%), with 7 (95% CI=1–17) attributable deaths and 14 (95% CI=2–34) attributable registrations. The overall AF for SNC from exposure to wood dust was 10.02% (95% CI=3.85–19.60%), with 11 (95% CI=4–22) attributable deaths and 39 (95% CI=15–76) attributable registrations. Over the REP, 446 917 men and 244 475 women were ‘ever exposed’ to Cr VI. The total AF for SNC associated with Cr VI was 5.69% (95% CI=2.16–15.50%), with 7 deaths (95% CI=2–18) and 22 (95% CI=8–59) registrations for SNC. Approximately 72% of the deaths and registrations that could be attributable to chromium were for men. Chromium VI exposure in manufacture of machinery (except electrical) had the most attributable registrations and deaths for both men (four and one, respectively) and women (one registration). Manufacture of fabricated metal products, except machinery and equipment also had three male and one female registration and one male death. There were an estimated 216,814 men and 384,132 women ‘ever exposed’ to leather dust over the REP. The overall AF for SNC from leather dust was 8.39% (95% CI=4.17–15.19%), resulting in 10 (95% CI=5–17) attributable deaths and 31 (95% CI=16–57) attributable registrations. Individuals involved in the manufacture of footwear had the most registrations and deaths attributable to occupation for both men (9 and 3, respectively) and women (13 and 4, respectively). The total AF for SNC associated with nickel exposure was 0.00% (95% CI=0.00–0.02%). For the Clydach factory alone there were 164 men ever potentially exposed to nickel over the relevant exposure period, resulting in no attributable deaths or registrations. There were an estimated 4 426 581 men and 466 252 women ‘ever exposed’ to mineral oils over the REP. The total AF was 13.84% (95% CI=1.37–38.97%), with 16 (95% CI=2–45) deaths and 55 (95% CI=5–154) registrations. Metal workers were at the most risk (43 male and 5 female registrations), particularly machine tool operators for both men (18 registrations and 5 deaths) and women (4 registrations and 1 death).