Cooking-related emissions are associated with environmental pollution and adverse health effects. Of the various chemical species emitted during cooking, polycyclic aromatic hydrocarbons (PAHs) and aldehydes are two chemical species with carcinogenic or tumor promoting characteristics. Although PAH exposure has been studied in commercial kitchen workers, few studies have investigated simultaneous exposure to PAHs and aldehydes in these workers. The aims of this study were to compare personal concentrations of PAH and aldehyde in three commercial cooking workplaces and to estimate their corresponding cancer risks. The three cooking workplaces included western fast food restaurant kitchens, Chinese cafeteria kitchens, and street food carts. Comparisons showed that workers in western fast food restaurant kitchens and Chinese cafeteria kitchens tended to have lower personal concentrations of these pollutants compared to workers in street food carts. The geometric mean (95% CI) cancer risks in the three workplaces were, from lowest to highest, 1.36 (1.12–1.67) × 10−5 for western fast food restaurant kitchens, 1.52 (1.01–2.28) × 10−5 for Chinese cafeteria kitchens, and 3.14 (2.45–4.01) × 10−5 for street food carts. The percentage contributions of aldehyde species to cancer risk were very high (74.9–99.7%). Street food cart workers had high personal exposure to aldehyde probably due to lack of effective exhaust systems. Thus, their cancer risk was significantly higher than those of workers in western fast food restaurant kitchens (p < 0.001) and Chinese cafeteria kitchens (p = 0.013).
Cooking-related emissions are a public health concern for several reasons. First, cooking activities produce harmful pollutants1,2,3 such as polycyclic aromatic hydrocarbons (PAHs), aldehydes, volatile organic compounds, ultrafine particles (particles smaller than 100 nm in diameter), and PM2.5 (particulate matters smaller than 2.5 μm in diameter). Second, epidemiological studies performed in China, Taiwan, Hong Kong, and Singapore have linked cooking oil fume (COF) exposure to lung cancer in nonsmoking women4,5. Notably, the International Agency of Research on Cancer has also categorized emissions from high-temperature frying as a probable carcinogen (Group 2A)6. Thus, cooking emissions have potentially adverse impacts on human health.
Of all pollutants emitted by cooking activity, the two most frequently investigated species are PAHs and aldehydes. The PAHs have attracted the interest of researchers because they are generated at the high temperatures used for cooking7 and because of their well-recognized carcinogenicity8. However, most studies of PAHs have only analyzed area concentrations in family/commercial kitchens and in exhaust air9,10. Personal exposure to PAHs is rarely reported11,12,13. Notable findings in the literature on PAH include the following: PAH levels increase with cooking temperature14, the cooking method that generates the most PAHs is barbecue cooking10, and particulate PAHs are a larger contributor to benzo(a)pyrene equivalent (BaPeq) concentrations compared to gaseous PAHs9.
Aldehydes are produced by degradation of fatty acids. Aldehyde emissions are associated with cooking temperature15,16 and with the fatty acid composition of oil used for cooking17,18. Whereas formaldehyde and acetaldehyde are known and probable carcinogens, respectively6, high carbon number aldehydes (e.g., t,t-2,4-nonadienal, t,t-2,4-decadienal (t,t-2,4-DDE)) are known mutagens with tumor promoting characteristics19,20,21.
Professional cooks have high potential risk of exposure to cooking-related emissions such as PAHs and aldehydes2. Few studies have investigated simultaneous occupational exposure to these two species. The objective of this study was to investigate occupational exposure to PAHs and aldehydes and their corresponding cancer risks.
Area air concentrations
The geometric mean (GM) concentration of total PAH was substantially higher in the street food cart group (8790.2 ng/m3) compared to the Chinese cafeteria kitchen and western fast food restaurant kitchen groups (3721.1 and 3171.0 ng/m3, respectively). Most PAHs were 2-ring or 3-ring PAHs, which have lower toxic equivalent factors compared to other PAHs. The most potent carcinogen, benzo(a)pyrene, was only detected in the barbecue stand and in the popcorn chicken stand. Analyses of total aldehyde revealed GM concentrations of 163.6, 222.8, and 233.7 μg/m3 in western fast food restaurant kitchens, Chinese cafeteria kitchens and street food carts, respectively (Table 1). The aldehyde analyses showed that the three workplaces had similar aldehyde concentration profiles. The most abundant aldehydes were hexaldehyde and nonanal (Supplementary Fig. S1).
Personal exposure concentrations
In the western fast food restaurant kitchens and Chinese cafeteria kitchens, half of the participants were female. In the street food carts, however, only one participant was female. No fume extractors were used in street food carts. The prevalence of personal protective equipment and fume extractors differed among the three working environments. The number of working years was shorter in the western fast food restaurant kitchen group compared to the other two groups (Table 2).
Table 3 shows personal exposure results. In western fast food restaurant kitchens, Chinese cafeteria kitchens and street food carts, the respective GM concentrations of total PAH were 558.5, 4943.1, and 4576.1 ng/m3, and the respective GM concentrations of total aldehyde were 67.6, 62.1 and 165.3 μg/m3. In terms of PAH ring number wise distribution, the most frequently detected in the three workplaces were two-ring PAHs (78.2–92.3%) followed by three-ring PAHs (6.7–21.3%) and four-ring PAHs (0.4–1.8%) (Supplementary Fig. S2). The three workplaces significantly differed in personal exposure to naphthalene, acenaphthylene, fluorene, anthracene, total PAH, and total BaPeq (p-values 0.006, <0.001, <0.001, 0.020, 0.002, and <0.001 respectively, Supplementary Table S1). In post hoc analysis, the largest differences in PAH concentrations were observed in comparisons between western fast food restaurant kitchens and Chinese cafeteria kitchens and between western fast food restaurant kitchens and street food carts. The aldehyde analyses showed that the three workplace types significantly differed in formaldehyde, acrolein, crotonaldehyde, valeraldehyde, hexaldehyde, t-2-heptenal, t,t-2,4-DDE, nonanal and total aldehyde (p-value range < 0.001–0.018, Supplementary Table S1). Post hoc analysis showed that the largest differences in aldehyde concentrations were observed in comparisons between western fast food restaurant kitchens and street food carts and between Chinese cafeteria kitchens and street food carts. Personal exposure to aldehyde was higher in the street food cart group compared to the other two groups.
Incremental lifetime cancer risk (ILCR)
The ILCR ranged from 6.2 × 10−8 to 2.7 × 10−6 for total PAH and from 6.3 × 10−6 to 3.5 × 10−5 for aldehydes based on formaldehyde and acetaldehyde (Supplementary Table S2). Thus, total ILCR ranged from 8.0 × 10−6 to 3.6 × 10−5. The GM (95% confidence interval) ILCR was 1.36 (1.12–1.67) × 10−5 in western fast food restaurant kitchens, 1.52 (1.01–2.28) × 10−5 in Chinese cafeteria kitchens, and 3.14 (2.45–4.01) × 10−5 in street food carts (Fig. 1; Supplementary Table S2). In 18 (82%) workers, the ILCR exceeded 10−5. Overall ILCR was significantly higher in street food cart workers compared to western fast food restaurant kitchen workers (p < 0.001, power > 0.99) and Chinese cafeteria kitchen workers (p = 0.013, power = 0.985) (Fig. 1). However, overall ILCR did not significantly differ between western fast food restaurant kitchen workers and Chinese cafeteria kitchen workers (p = 0.924, power = 0.089).
Exposure concentrations and cooking methods
Workplace selection was based on cooking methods which generate substantial air pollutants, such as frying or barbecuing. Several studies reported these two cooking methods produced more pollutants than the other cooking methods did. For example, Yao, et al.7 reported that deep frying generates more PAHs compared to pan frying because deep frying uses oil at a hotter temperature and in a larger amount. In Zhao, et al.2 study, a comparison of night market stalls revealed that total PAH levels were highest in a barbecue food stall (43.145 μg/m3). The low indirect heat from burning charcoals used for barbecue cooking can result in incomplete combustion, which is the main mechanism of PAH formation22.
The BBQ stand was the only workplace using charcoal as its cooking fuel. Several studies reported that solid fuel use is a significant source of particulate matters and PAHs10,23,24. Our findings confirmed the results from the previous studies and showed that the BBQ stand had the highest PAH levels of the investigated workplaces; while its aldehyde level was moderate (Table S3). The highest personal aldehyde levels were found in the popcorn chicken and chicken steak stands which used deep frying as their cooking method. Our findings of aldehyde emissions were similar to those found in Ho et al. study25, in which a western fast-food chain shop using deep frying as its cooking method had high aldehyde emissions, while a Korean BBQ restaurant had moderate aldehyde emissions. Pollutant emission patterns of barbecuing and deep frying were similar. Both cooking methods generated aldehydes and PAHs with higher aldehyde concentrations in comparison with PAHs. The two chemical species have some compounds with carcinogenic potentials and corresponding cancer risks were estimated using the Eq. 1 accordingly. Both barbecuing and deep frying had similar emission pattern for producing carcinogenic compounds, and are considered as pollutant sources in cooking workplaces.
Comparison between area and personal concentrations
Correlation coefficients between area and personal GMs for individual workplace measurements were 0.650 (p = 0.058) and 0.383 (p = 0.308) for total PAH and total aldehyde, respectively (Table S3). PAH results showed a moderate correlation with a marginal trend toward significance, while aldehyde results showed no association. A possible explanation for marginal or no associations between area and personal measurements shows as follows. Area measurements were based on samples taken at fixed sites near the stoves whereas personal measurements were based on samples taken from workers who tended to move among various locations throughout the workday. For example, a single worker may have been sampled while in the cooking area, in the preparation area, in the dish-washing station, or in the rest area. Therefore, the carcinogenic risk estimation from personal sampling was more representative compared to those from area samples, which were often used to assess the carcinogenic potencies of cooking emissions in previous studies10,26,27.
Table 4 shows the PAH concentrations reported in earlier studies. Examples include 1.08–22.8 μg/m3 from hot cooking oil fumes28; 8.58–89.71 μg/m3, 24.7–130 μg/m3, and 1.14–7.84 μg/m3 in exhaust ducts of restaurants from several Asian studies10,26,29; 10–21 μg/m3 in commercial kitchens14; 1.44–56.9 μg/m3 found in five family kitchens9, and 24.6–53.4 μg/m3 from deep-frying and frying cooking oil fumes under a laboratory fume hood7. The PAH levels measured in the current study (1.18–147.59 μg/m3) were consistent with those in the literature. The PAH levels in this study were also comparable to levels measured in coke plant workplaces (10.98–146.98 μg/m3)30, in foundry plant workplaces (77.59 μg/m3)31, and in smoke from incense burned inside temples (3.35–9.24 μg/m3)32. Notably, some studies have also reported PAH concentrations in terms of BaPeq concentrations to evaluate their carcinogenic potencies. The range of BaPeq concentrations measured in the current study was 0.001–0.372 μg/m3 whereas previous studies have reported ranges of 0.041–0.233 μg/m3 for cooking emissions from five family kitchens in Taiwan9, 0.023 μg/m3 for ion casting emissions in a foundry plant31, and 0.20–10.87 μg/m3 in emissions from coke plants30.
Table 1 shows that the range of total aldehyde concentrations in the three cooking workplaces was 18.7–946.0 μg/m3. Concentrations reported in the literature include 159–3095 μg/m3 for 13 aldehydes in commercial kitchens25, mean concentrations of 185–241 μg/m3 for six aldehydes in residential kitchens33, and 21–170 μg/m3 for 18 carbonyl compounds in five commercial kitchens27. Thus, our data were again consistent with the literature. The aldehyde profile in this study showed high concentrations of hexaldehyde, t,t-2,4-DDE and nonanal detected in COFs, which was consistent with that reported in Peng et al.34.
Personal concentrations of total PAH measured in the 22 workers in the three commercial cooking workplaces investigated in this study ranged from 0.06 to 14.6 μg/m3 (Table 4). Zhao, et al.2 reported total PAH in a range of 23.4–44.2 μg/m3 in cooks at Taiwan night markets (Table 4). As expected, our data for the street food cart workers were consistent with those reported for night market workers due to their similar cooking conditions. In earlier studies of occupational exposure, mean personal concentrations of total PAH were 0.99 and 6.95 μg/m3 for side-oven workers and topside-oven workers in a coke plant35, respectively, and 5.05 μg/m3 for traffic policemen36 (Table 4). However, the PAHs measured in our study and for traffic policemen were predominantly 2-ring and 3-ring PAHs whereas PAHs measured in coke oven plants were predominantly 5-ring and 6-ring PAHs, which have a higher toxicity and potency. Mean total BaPeq was also assessed to account for the different toxicities and potencies of PAHs. Mean total BaPeq concentration were 0.004 μg/m3 in the current study. In contrast, the BaPeq concentrations reported previously were 0.18 μg/m3 for coke side-oven workers, 1.57 μg/m3 for coke topside-oven workers, and 0.082 μg/m3 for traffic policemen. Therefore, both total PAH and BaPeq concentrations should be investigated and compared to clarify their sources and toxic potencies.
Personal concentrations of the 13 aldehydes measured in this study ranged from 37.7 μg/m3 to 322.2 μg/m3. In contrast with many studies of personal exposure to PAHs, studies of personal exposure to aldehydes are rare. One example is Svendsen, et al.37, who reported total personal concentrations of formaldehyde, acetaldehyde and acrolein ranging from 8–186 μg/m3 in restaurant kitchens in Norway. Another study of three restaurant kitchens by Sjaastad and Svendsen11 reported total personal concentrations of 28.1–154.4 μg/m3 for 16 aldehydes and 1.03–17.67 μg/m3 for high carbon number aldehydes (C10~C11). The Sjaastad research group also investigated personal aldehyde levels emitted from pan frying (beefsteak) on an electric stove or on a gas stove using various cooking oils in a laboratory kitchen. In studies performed in 2008 and in 2010, the Sjaastad research group reported total aldehyde concentrations in ranges of 129.4–563.4 μg/m3 and 81.3–354.4 μg/m3, respectively20,38. Thus, the exposure levels measured in our study are similar to those reported in the literature.
Incremental lifetime cancer risk
The ILCR from exposure to cooking emissions ranged from 8.04 × 10−6 to 3.60 × 10−5 (Table S4). Eighteen (18/22 = 82%) workers in this study had an ILCR higher than 1 × 10−5. The percentage contribution to cancer risk was much higher for aldehydes (range, 74.9–99.7%) than for total PAH (range, 0.3–25.1%). The three commercial cooking workplace types had similarity in cooking method (frying) and cooking oil (palm oil and soybean oil). Emissions from western fast food restaurant kitchens and Chinese cafeteria kitchens were regulated by Taiwan’s Air Pollution Control Act39. Under the Act, these kitchens needed to install air pollution control devices, maintain the devices under workable conditions, clean the devices regularly, and meet the emission standards. Street food carts had an exception from the Taiwan’s Air Pollution Control Act due to their small scale (capital investment < NT$ 100,000, and workplace area < 100 m2). This lead to air pollutants from street food carts uncontrolled. This could be the reason that workers in the street food cart group had significantly higher overall ILCRs compared to workers in the other two groups. One of the notable differences of these three types was exhaust systems. There was no effective mechanical exhaust systems in the street food cart group. Other studies have also indicated the need for effective ventilation systems to control cooking-related emissions. For example, a comparison of kitchens by Svendsen, et al.37 found that concentrations of fat aerosols and aldehyde concentrations were highest in kitchens with insufficient exhaust systems; another study by Yu, et al.9 similarly reported high PAH concentrations in kitchens with poor ventilation. Although the open air environment of street food carts enables rapid dispersal of pollutants, cooking emissions were higher in the street food cart group compared to the other two groups probably because street food carts are rarely equipped with fume extractors or other exhaust systems for collecting and removing pollutants from breathing zones. Additionally, other factors, such as equipment type, maintenance, cooking space etc. may be potential contributors for high PAH and aldehyde concentrations of street food cart workers.
In the literature, reported ranges of estimated cancer risk related to cooking emissions include 2.5 × 10−6 – 1.4 × 10−5 for household cooking emissions9, 9.0 × 10−5– 1.13 × 10−4 for night market workers2, and 1.96 × 10−8–1.31 × 10−6 for frequent customers of six restaurants27. For comparison, examples of median or mean ILCRs reported in the literature included 2.96 × 10−5 for inhalation exposure in temple workers40; 1.055 × 10−4 for traffic assistants (i.e., workers who assist police in controlling heavy traffic)41, 1.6 × 10−5 in motorcycle commuters based on an estimated daily BaPeq of 0.40 μg/d23, and 2.3 × 10−4 in topside coke oven workers based on personal exposure to 16 PAHs35. In comparison with other sources, cooking-related emissions showed a moderate cancer risk.
Aldehyde species are dominant chemical species in cooking-related emissions. The low carbon number aldehydes formaldehyde and acetaldehyde are confirmed and probable carcinogens, respectively6. Some high carbon number aldehydes also showed carcinogenic effects. For example, Wu, et al.21 reported that some high carbon number aldehydes (e.g., t,t-2,4-DDE, t,t-2,4-nonadienal, t-2-decenal and t-2-undecenal) were potent mutagens. The aldehyde t,t-2,4-DDE promotes cancer by inducing cancer cell proliferation and by inhibiting anti-oxidant enzyme activities19,42,43,44. However, data are insufficient for their classification as probable or possible carcinogens. High carbon number aldehydes were not be able to include in the risk analyses in the current study. Notably, the cancer risk might be even higher than the estimated values.
Limitations and strengths
This study has several limitations. First, since the street food carts were located on the roadside, vehicular emissions may have resulted in overestimated cooking emissions. On the other hand, the street food carts analyzed in this study were located on a street with a low traffic volume of ~5600 vehicles per day (Directorate General of Highways, 2014)45. The estimated total PAH emission of this traffic volume was 0.232 μg/m3 based on Ho, et al.46 findings which indicated total PAH emission of 2.211 μg/m3 at the traffic volume of 53000 vehicles per day. Therefore, the influence of automobile exhaust on these workplaces was probably limited. Nevertheless, future studies should recognize and control for the effects of traffic emissions when investigating cooking workplaces located on or near the roadside. Second, the findings of this study cannot be generalized to all commercial cooking workplaces because the analysis was limited to small or medium sized workplaces in which the primary cooking method was frying or barbecuing. For a comprehensive study of the PAH and aldehyde levels in cooking workplaces and for estimates of cancer risks in populations with high exposure to cooking-related emissions, future studies should include analysis of large-sized cooking workplaces, which may differ in terms of number and type of cooking activities, and in terms of the number of workers. Third, the small sample size precluded assessment of other contributing factors in exposure to PAH and aldehyde (e.g., cigarette smoking and cooking oil type). The small sample size also precluded assessment of gender-specific exposure and gender-specific cancer risk in the three groups. Further gender-specific analyses are needed because COF exposure associated with lung cancer in nonsmoking women. Despite the small sample size, however, this study demonstrated a significantly higher cancer risk in street food cart workers compared to workers in the other two groups.
This study is the first to estimate the cancer risk of personal exposure to both PAHs and aldehydes in cooking workplaces. The estimation was more representative of human exposure compared to previous studies that have used area samples to assess the carcinogenic potencies of cooking emissions10,26,27. This study investigated occupational exposure to cooking-related emissions and revealed that workers in the street food cart group had the highest ILCRs. Notably, aldehyde species were the main contributors to cancer risk. Although the street food cart group belongs to the small-scaled workplaces, it accounts for one third of all cooking workplaces, and the cooking emissions from street food carts affect not only workers, but also people in nearby areas. The considerable emissions generated from street food carts is problematic not only in Taiwan, but in many countries throughout the world. The data in this study suggest that cooking emissions and exposure from street food carts can be effectively controlled by installing mechanical exhaust systems and maintaining them in good condition.
Workplace selection and sampling strategy
The three commercial cooking workplace types analyzed in this study were kitchens in western fast food restaurant chains (main product: fried chicken), kitchens in cafeteria-style Chinese restaurant chains, and street food carts. These workplace types were selected for analysis because the cooking methods that they use (frying or barbecuing) are known to generate substantial air pollutants23,34. Additionally, western fast food restaurant kitchens, cafeteria-style Chinese restaurant kitchens, and street food carts account for most of the commercial cooking workplaces in Taiwan (10%, 21%, and 32% of respectively)47. These cooking workplaces are associated with high personal exposure to cooking-related emissions. Table 5 shows the characteristics and sample sizes of the three cooking workplace types. The analysis included three restaurants or vendors in each of the three groups. All western fast food restaurant kitchens and Chinese cafeteria kitchens analyzed in this study followed Taiwan’s Air Pollution Control Act39; which regulated COFs of commercial kitchens by installing exhaust ventilation systems (hoods, ducts, air cleaning devices, and fans) above the frying units or stoves (Supplementary Fig. S3), maintaining the exhaust systems under workable conditions, and cleaning the system regularly. Street food carts were not obligated to install air pollution control devices due to their small scale in terms of capital investment and working counter area (1.5–3.0 m2), while some used wall-mounted fans to increase general ventilation (Supplementary Fig. S4). The room inside the cart was used for storage and to house the cooking machinery. Workers stood outside of the carts to prepare food.
Between September 4, 2014 and November 1, 2014, area and personal samples were collected to determine concentrations of PAHs and aldehydes (Supplementary Fig. S5). For each restaurant or vendor, all samples were collected for 8 h on the same day. Area samples were collected in the kitchen area or other working area at a height of 1.5 m to represent the breathing zone of a worker in a standing position. One to three area samples were taken at each restaurant or vendor; thus, five, six and seven samples were taken in western fast food restaurant kitchens, Chinese cafeteria kitchens, and street food carts. Personal samples were taken from workers who were responsible for cooking. The recruited workers included twelve western fast food restaurant kitchen workers, six Chinese cafeteria kitchen workers, and four street food cart workers (Table 5). All subjects gave written informed consent to participate before the study was performed. Each participating worker wore two personal samplers (one for PAHs and one for aldehydes) and completed questionnaires regarding personal demographic data and characteristics pertinent to this study, including lifestyle (e.g., tobacco and alcohol consumption), occupational history (e.g., work history, periods of employment, cooking method used, and protective equipment used), and health status (e.g., chronic disease, respiratory disease). The study protocol (IRB number: KMUH-IRB-990191) received ethical approval by the Institutional Review Board of Kaohsiung Medical University Hospital (IRB-KMUH). The study was performed in accordance with the guidelines and regulations of the IRB-KMUH. Names and other personal information that could be used to identify participants were excluded from the manuscript, including Supplementary Information.
Sampling and analysis methods
This study targeted the 16 PAHs prioritized for control by the United States Environmental Protection Agency (Supplementary Table S5) due to their high toxicity and high potential for human exposure. Particulate matter was collected with a Teflon filter (25 mm × 2 μm pore size, Pall Corporation, Port Washington, New York, USA) in an IOM (Institute of Occupational Medicine, Edinburgh, U.K.) sampler, and gaseous PAHs were collected with a polyurethane foam cartridge (ORBO™ 1000, 22 mm (OD) × 7.6 cm (L), Supelco, Bellefonte, Pennsylvania, USA). Particulate- and gas-phase PAHs were simultaneously collected with a specially designed single-pump sampling train. The IOM sampler had a Teflon filter in the front section of the sampling train. One tube was connected to a polyurethane foam cartridge, and another tube was connected to a flow regulator. The two tubes converged at a tee fitting connected to a pump34 (Supplementary Fig. S6). The flow regulator was adjusted to obtain the flow rates required by the particulate- and gas-phase sampling devices (2 L/min and 1 L/min, respectively). The flowrates were measured and confirmed by an air flow calibrator (Defender 510, Mesa Laboratories, Inc., Butler, NJ, USA). Collected samples were extracted using a 1:1 mixture of acetone and hexane in a microwave extraction system (START E, Milestone, Shelton, CT, USA)24,48. After extraction, the samples were analyzed by a gas chromatograph/mass spectrometer (Trace GC Ultra/DSQ II MS, Thermo Fisher Scientific, Waltham, Massachusetts, USA). The PAHs were separated with a capillary gas chromatography column (Equity®-5, 30 m × 0.25 mm × 0.25 μm, Supelco, Bellefonte, Pennsylvania, USA) with a temperature program. The analytical quality controls for the 16 PAHs are shown in Supplementary Table S5.
The thirteen aldehydes selected for analysis in this study (Supplementary Table S6) were targeted because they have raised health concerns (e.g., formaldehyde and acetaldehyde) or because their chemical characteristics are representative of COFs34 (e.g., nonanal and t,t-2,4-DDE). The sampling train used to collect aldehydes was identical to that used to collect PAHs, i.e., an IOM sampler with a DNPH-coated glass fiber filter (25 mm × 2 μm pore size, Supelco, Bellefonte, Pennsylvania, USA) and a 2,4-DNPH cartridge (Supelco, Bellefonte, Pennsylvania, USA) were connected in series for particulate- and gaseous- phase aldehyde sampling. After sample collection, the samplers were stored at 4 °C in sealed aluminum bags until extraction. Samples were extracted by acetonitrile and then analyzed with a high performance liquid chromatograph (PU-2089, Jasco, Japan) equipped with an ultraviolet detector operated at 360 nm (Varian ProStar 320, Varian, USA). A reverse phase column (Ascentis® RP-Amide Column, 5 μm, 250 × 4.6 mm, Supelco, Bellefonte, Pennsylvania, USA) with a gradient mobile phase of acetonitrile/water was used to separate aldehydes. The gradient program was performed at a flowrate of 1.2 ml/min as follows: start with an acetonitrile/water ratio of 40/60 for 1 min, increase acetonitrile from 40% to 90% within 49 min, hold for 3 min, and decrease acetonitrile from 90% to 40% within 12 min. The analytical quality controls for the 13 aldehydes are shown in Supplementary Table S6.
Estimation of ILCR
For each participant, ILCR was estimated according to the risk assessment guidelines established by US Environmental Protection Agency49, which are used extensively in the literature, including our previous works9,27,50. The equation used to calculate ILCR was
where C is the concentration (μg/m3) of a pollutant in air, IR is the inhalation rate (0.83 m3/h for males and 0.69 m3/h for females), ET is exposure time (8 h, i.e., work hours per day), ED is exposure duration (40 years, i.e., age 20 to 60 years), BW is body weight (69.2 kg for males and 55.5 kg for females)9, LT is lifetime (70 years), and SF is slop factor ([μg/kg/day]−1). The slop factors for PAH, formaldehyde and acetaldehyde are 0.0039, 0.000021, and 0.00001, respectively51.
The ILCR was calculated for all 16 PAHs and for two aldehyde chemicals (formaldehyde and acetaldehyde). For each worker, total ILCR was obtained by adding the 18 ILCR values.
The PAH concentrations, aldehyde concentrations, and total ILCR data were log-normal distributed; therefore, they were log-transformed. The ANOVA test was then used to analyze the concentration or risk difference in the three commercial cooking types, and the Bonferroni method was used for post-hoc analysis. These statistical analyses were performed with IBM SPSS Statistics 21 software (IBM SPSS Inc., Armonk, NY, USA). All p values were two-tailed, and p values < 0.05 were considered statistically significant. Statistical power calculation was performed with R (R version 3.4.3).
Wan, M.-P., Wu, C.-L., To, G.-N. S., Chan, T.-C. & Chao, C. Y. H. Ultrafine particles, and PM2.5 generated from cooking in homes. Atmos. Environ. 45, 6141–6148 (2011).
Zhao, P., Yu, K. P. & Lin, C. C. Risk assessment of inhalation exposure to polycyclic aromatic hydrocarbons in Taiwanese workers at night markets. International Archives of Occupational and Environmental Health 84, 231–237 (2011).
Wang, L. et al. Role of Chinese cooking emissions on ambient air quality and human health. Science of the Total Environment 589, 173–181 (2017).
Lee, T. & Gany, F. Cooking oil fumes and lung cancer: a review of the literature in the context of the U.S. population. J Immigr Minor Health 15, 646–652 (2013).
Sun, S., Schiller, J. H. & Gazdar, A. F. Lung cancer in never smokers–a different disease. Nat. Rev. Cancer 7, 778–790 (2007).
IARC. Agents Classified by the IARC Monographs, http://monographs.iarc.fr/ENG/Monographs/PDFs/index.php (2012).
Yao, Z. et al. Characteristics of PAHs from deep-frying and frying cooking fumes. Environ. Sci. Pollut. Res. 22, 16110–16120 (2015).
Collins, J. F., Brown, J. P., Alexeeff, G. V. & Salmon, A. G. Potency Equivalency Factors for Some Polycyclic Aromatic Hydrocarbons and Polycyclic Aromatic Hydrocarbon Derivatives. Regulatory Toxicology and Pharmacology 28, 45–54 (1998).
Yu, K. P. et al. Indoor air pollution from gas cooking in five Taiwanese families. Build. Environ. 93, 258–266 (2015).
Chen, J. W., Wang, S. L., Hsieh, D. P., Yang, H. H. & Lee, H. L. Carcinogenic potencies of polycyclic aromatic hydrocarbons for back-door neighbors of restaurants with cooking emissions. Science of the Total Environment 417-418, 68–75 (2012).
Sjaastad, A. K. & Svendsen, K. Exposure to polycyclic aromatic hydrocarbons (PAHs), mutagenic aldehydes, and particulate matter in Norwegian a la carte restaurants. Annals of Occupational Hygiene 53, 723–729 (2009).
Singh, A. et al. Heat and PAHs Emissions in Indoor Kitchen Air and Its Impact on Kidney Dysfunctions among Kitchen Workers in Lucknow, North India. PLOS ONE 11, e0148641 (2016).
Tiwari, M., Sahu, S. K. & Pandit, G. G. Probabilistic single box approach for modeling PAHs associated with combustion aerosols in a typical indoor environment. Biomass Bioenerg. 86, 172–179 (2016).
Zhu, L. & Wang, J. Sources and patterns of polycyclic aromatic hydrocarbons pollution in kitchen air, China. Chemosphere 50, 611–618 (2003).
Lin, J. M. & Liou, S. J. Aliphatic Aldehydes Produced by Heating Chinese Cooking Oils. Bulletin of Environmental Contamination and Toxicology 64, 817–824 (2000).
Fullana, A., Carbonell-Barrachina, Á. A. & Sidhu, S. Comparison of Volatile Aldehydes Present in the Cooking Fumes of Extra Virgin Olive, Olive, and Canola Oils. J. Agric. Food Chem. 52, 5207–5214 (2004).
da Silva, T. O. & Pereira, deP. P. A. Influence of Time, Surface-to-Volume Ratio, and Heating Process (Continuous or Intermittent) on the Emission Rates of Selected Carbonyl Compounds during Thermal Oxidation of Palm and Soybean Oils. J. Agric. Food Chem. 56, 3129–3135 (2008).
Katsuta, I., Shimizu, M., Yamaguchi, T. & Nakajima, Y. Emission of volatile aldehydes from DAG-rich and TAG-rich oils with different degrees of unsaturation during deep-frying. Journal of the American Oil Chemists Society 85, 513–519 (2008).
Chang, L. W., Lo, W. S. & Lin, P. Trans, trans-2,4-decadienal, a product found in cooking oil fumes, induces cell proliferation and cytokine production due to reactive oxygen species in human bronchial epithelial cells. Toxicological Sciences 87, 337–343 (2005).
Sjaastad, A. K. & Svendsen, K. Exposure to mutagenic aldehydes and particulate matter during panfrying of beefsteak with margarine, rapeseed oil, olive oil or soybean oil. Annals of Occupational Hygiene 52, 739–745 (2008).
Wu, S. C., Yen, G. C. & Sheu, F. Mutagenicity and identification of mutagenic compounds of fumes obtained from heating peanut oil. Journal of food protection 64, 240–245 (2001).
Kislov, V. V., Sadovnikov, A. I. & Mebel, A. M. Formation Mechanism of Polycyclic Aromatic Hydrocarbons beyond the Second Aromatic Ring. Journal of Physical Chemistry A 117, 4794–4816 (2013).
Kuo, C. Y., Hsu, Y. W. & Lee, H. S. Study of human exposure to particulate PAHs using personal air samplers. Archives of Environmental Contamination and Toxicology 44, 454–459 (2003).
Ding, J. et al. Occurrence and exposure to polycyclic aromatic hydrocarbons and their derivatives in a rural Chinese home through biomass fuelled cooking. Environmental Pollution 169, 160–166 (2012).
Ho, S. S., Yu, J. Z., Chu, K. W. & Yeung, L. L. Carbonyl emissions from commercial cooking sources in Hong Kong. Journal of the Air & Waste Management Association 56, 1091–1098 (2006).
Li, C. T., Lin, Y. C., Lee, W. J. & Tsai, P. J. Emission of polycyclic aromatic hydrocarbons and their carcinogenic potencies from cooking sources to the urban atmosphere. Environ. Health Perspect. 111, 483–487 (2003).
Cheng, J. H., Lee, Y. S. & Chen, K. S. Carbonyl compounds in dining areas, kitchens and exhaust streams in restaurants with varying cooking methods in Kaohsiung, Taiwan. J. Environ. Sci. 41, 218–226 (2016).
Siegmann, K. & Sattler, K. Aerosol from hot cooking oil, a possible health hazard. J. Aerosol Sci. 27 (1996).
Chen, Y. et al. Gaseous and particulate polycyclic aromatic hydrocarbons (PAHs) emissions from commercial restaurants in Hong Kong. Journal of Environmental Monitoring: JEM 9, 1402–1409 (2007).
Mu, L. et al. Characteristics of polycyclic aromatic hydrocarbons and their gas/particle partitioning from fugitive emissions in coke plants. Atmos. Environ. 83, 202–210 (2014).
Chen, H. L., Yang, C. H. & Lin, M. H. Removal efficiency of vapour/particulate phase PAHs by using alternative protective respirators in PAHs exposure workers. J Hazard Mater 219-220, 190–195 (2012).
Lin, T.-C., Chang, F.-H., Hsieh, J.-H., Chao, H.-R. & Chao, M.-R. Characteristics of polycyclic aromatic hydrocarbons and total suspended particulate in indoor and outdoor atmosphere of a Taiwanese temple. J. Hazard. Mater. 95, 1–12 (2002).
Huang, Y. et al. Characteristics and health impacts of VOCs and carbonyls associated with residential cooking activities in Hong Kong. J. Hazard. Mater. 186, 344–351 (2011).
Peng, C. Y., Lan, C. H., Lin, P. C. & Kuo, Y. C. Effects of cooking method, cooking oil, and food type on aldehyde emissions in cooking oil fumes. J. Hazard. Mater. 324, 160–167 (2017).
Lin, Y. C. et al. Associations between exposure to polycyclic aromatic hydrocarbons and temporal change of urinary 1-hydroxypyrene levels in Taiwanese coke-oven workers. Journal of occupational and environmental medicine 48, 930–936 (2006).
Liu, Y. et al. Inhalation exposure of traffic police officers to polycyclic aromatic hydrocarbons (PAHs) during the winter in Beijing, China. Science of the Total Environment 383, 98–105 (2007).
Svendsen, K., Jensen, H. N., Sivertsen, I. & Sjaastad, A. K. Exposure to Cooking Fumes in Restaurant Kitchens in Norway. Annals of Occupational Hygiene 46, 395–400 (2002).
Sjaastad, A. K., Jorgensen, R. B. & Svendsen, K. Exposure to polycyclic aromatic hydrocarbons (PAHs), mutagenic aldehydes and particulate matter during pan frying of beefsteak. Occupational and Environmental Medicine 67, 228–232 (2010).
Taiwan Environmental Protection Administration. Air Pollution Control Act, https://oaout.epa.gov.tw/law/EngLawContent.aspx?lan=E&id=154 (2012).
Chiang, K.-C., Chio, C.-P., Chiang, Y.-H. & Liao, C.-M. Assessing hazardous risks of human exposure to temple airborne polycyclic aromatic hydrocarbons. J. Hazard. Mater. 166, 676–685 (2009).
Xue, X. et al. Exposure measurement, risk assessment and source identification for exposure of traffic assistants to particle-bound PAHs in Tianjin, China. Journal of environmental sciences (China) 26, 448–457 (2014).
Hung, H. S. et al. Association of cooking oil fumes exposure with lung cancer: Involvement of inhibitor of apoptosis proteins in cell survival and proliferation in vitro. Mutat. Res. 628, 107–116 (2007).
Chang, Y. C. & Lin, P. Trans, trans-2,4-decadienal induced cell proliferation via p27 pathway in human bronchial epithelial cells. Toxicology and Applied Pharmacology 228, 76–83 (2008).
Lin, P.-P. et al. Proteomic analysis of proteins associated with tt-DDE induced toxicity in BEAS-2B cells. Biochem. Biophys. Res. Commun. 376, 519–524 (2008).
Directorate General of Highways. Traffic Volume Statistical Tables, https://www.thb.gov.tw/sites/ch/modules/download/download_list?node=bcc520be-3e03-4e28-b4cb-7e338ed6d9bd&c=83baff80-2d7f-4a66-9285-d989f48effb4 (2014).
Ho, K. F. et al. Emissions of gas- and particle-phase polycyclic aromatic hydrocarbons (PAHs) in the Shing Mun Tunnel, Hong Kong. Atmos. Environ. 43, 6343–6351 (2009).
Taiwan Food and Drug Administration. Food industry registration data set, http://data.fda.gov.tw/frontsite/data/DataAction.do?method=doList&groupType=infoDepartment&id=16 (2014).
Castro, D. et al. Analysis of polycyclic aromatic hydrocarbons in atmospheric particulate samples by microwave-assisted extraction and liquid chromatography. J. Sep. Sci. 32, 501–510 (2009).
US EPA. Risk Assessment Guidance for Superfund Volume 1: Human Health Evaluation Manual (Part A). Report No. EPA/540/1 -89/002, (Environmental Protection Agency, Washington, DC, 1989).
Peng, C. Y., Hsiao, S. L., Lan, C. H. & Huang, Y. L. Application of passive sampling on assessment of concentration distribution and health risk of volatile organic compounds at a high-tech science park. Environmental Monitoring and Assessment 185, 181–196 (2013).
Office of Environmental Health Hazard Assessment. Hot Spots Unit Risk and Cancer Potency Values, https://oehha.ca.gov/media/CPFs042909.pdf (2016).
This work was supported by the grants from Kaohsiung Medical University Hospital (KMUH105-5R65), Institute of Labor, Occupational Safety and Health, Ministry of Labor (ILOSH-103-3002 and ILOSH-105-0007), Ministry of Science and Technology (MOST 104-2314-B-037-012-MY2; 105-2632-B-037-002-), and Kaohsiung Medical University (Aim for the Top Universities Grant No. KMU-TP105A00 and No. KMU-TP105A11).The authors also thank the western fast food restaurant chains, Chinese cafeteria restaurant chains, and street food carts that participated in this study.
The authors declare no competing interests.
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Wu, MT., Lin, PC., Pan, CH. et al. Risk assessment of personal exposure to polycyclic aromatic hydrocarbons and aldehydes in three commercial cooking workplaces. Sci Rep 9, 1661 (2019). https://doi.org/10.1038/s41598-018-38082-5
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