- Open Access
High human exposure to pyrene (polycyclic aromatic hydrocarbon) in Kinshasa, a capital of the Democratic Republic of Congo
Archives of Public Health volume 71, Article number: 14 (2013)
Data on human exposure to chemicals in Africa are scarce. A biomonitoring study was conducted in a representative sample of the population in Kinshasa (Democratic Republic of Congo) to document exposure to polycyclic aromatics hydrocarbons.
1-hydroxypyrene (1-OHP) was measured by HPLC fluorescence in spot urine samples from 220 individuals (50.5% women), aged 6–70 years living in the urban area and from 50 additional subjects from the sub-rural area of Kinshasa. Data were compiled as geometric means and selected percentiles, expressed without (μg/L) or with creatinine adjustment (μg/g cr). Multiple regression analyses were applied to factors (creatinine, grilled meat habits and smoking habits) influencing 1-OHP (stepwise procedure, criteria: probability F to enter ≤ 0.05 and probability F to remove ≥ 0.10).
According to the regression models, creatinine, grilled meat habits and smoking habits contribute to explain 45% of the variation in population’s urinary 1-OHP by the environmental exposure. Overall, living in urban area of Kinshasa was associated with increased levels of 1-OHP in urine as compared to a population living in the sub-rural area [GM: 1.8 μg/L (n = 220) versus 1.4 μg/L (n = 50), p < 0.01] as well as compared to the reference values from databases involving American or German populations.
This study reveals the high pyrene (PAH) exposure of the Kinshasa population. However, more work, with a rigorous design in the exposed population (monitoring of air concentrations and identifying other sources of pyrene –PAH exposure), is needed to establish further documentation.
Polycyclic aromatic hydrocarbons (PAH) are produced when organic materials undergo incomplete combustion. They are composed of two or more benzene rings and occur, depending on the type of pyrolytic process and of source material, in various compounds, but always in the form of a mixture. Because so many incomplete combustion processes occur, PAH are ubiquitous environmental contaminants. Exposure to PAH is associated with lung, esophageal, gastric, colorectal, bladder, skin, prostate, and cervical cancers in human and animal models .
Pyrene is present in almost all PAH mixture in relatively high concentrations and there is a good correlation between pyrene and other components in PAH mixture . 1-OHP (1-hydroxypyrene), a major metabolite of pyrene, has been widely used as an indicator of internal exposure to PAH [3, 4].
The main source of PAH intake is food, on the one hand as a result of airborne PAH precipitating onto cereals, fruit and vegetables, and on the other hand as a result of PAH generated during the preparation of food. For example, smoked food and food grilled on open flames display substantial levels of PAH content .
A very important source of PAH exposure among the general population is tobacco smoke . Smokers’ intake of pyrene in cigarette smoke is of the same order of magnitude as intake from average food consumption .
In DRC (Democratic Republic of Congo), only 5% of the population has access to electricity. As a result, wood energy production accounts for 85% of total energy consumption and fuel wood and charcoal are by far the most heavily consumed energy sources in DRC [10, 11], used primarily for household heating and cooking.
In this study, we provide the first data for biomonitoring PAH in a representative sample of the Kinshasa population. The values were compared to those reported by the reference values from American  or German databases .
In the absence of reliable population registers and in view of the practical difficulties of conducting a truly random sampling in the population of Kinshasa, we applied a two-stage systematic sampling approach . In the first stage, the 22 administrative entities of Kinshasa were listed in alphabetical order and 11 out of them were selected as follows: a first entity was drawn randomly from the list and every other subsequent entity was then included, thus ensuring a comprehensive coverage of the entire urban area of Kinshasa. In the second stage, we aimed to recruit about 25 healthy male and female subjects between 6 and 70 years from each of the 11 entities. In a mobilization campaign (mainly by word of mouth), healthy subjects were invited to come to the local health center to provide a urine sample. After exclusion of 13 individuals because of possible direct occupational exposure to PAH (asphalt application, waste incineration, aluminum smelting), 220 individuals provided a urine sample and were included in the present study (80% of the target number was reached). Informed consent was obtained from each subject and information on age, gender, place of residence and smoking habits were recorded. With the same methods of mobilization campaign, fifty additional subjects living in the sub-rural area of Kinshasa were also included. The characteristics of two areas (urban/sub-rural) selected: urban area had high percentage of population density; motorization, old second hand vehicles and car traffic whereas sub-rural had high percentage of green area . This study was approved by the Congolese committee of medical ethics and the study results will be informed back to individuals sample donors with proper explanations.
Great care was taken to avoid contamination during all the steps of collection, transport and analysis. Spot urine specimens were collected in metal-free polystyrene containers and stored at −20°C. The samples were then kept frozen and transported in a cool box to be analyzed by the Louvain centre for Toxicology and Applied Pharmacology (Brussels, Belgium). We determined urinary 1-OHP by HPLC (High Performance Liquid Chromatography) as described previously [16, 17] with some modifications . Briefly, 2.0 mL urine was used for each sample, and the identification and quantification of 1-OHP were based on retention time and peak area measured using a linear regression curve obtained from internal standard solutions. The limit of quantification (LOQ) was 0.20 μg/L. The valid urine 1-OHP concentrations were expressed as μg/L or μg/g of creatinine. The determinations of urinary cotinine (LOQ = 50 μg/L) were done by HPLC according to the methods previously described . Creatinine was determined (LOQ = 0.1 g/L) on a Beckman Synchron LX 20 analyser (Beckman Coulter GmbH, Krefeld, Germany) by the Jaffe method . For quality control, internal controls and reference materials were run together with the samples on a daily basis.
Concentrations were log transformed for data analysis. Geometric means (GM), ninety-five percent confidence intervals (CI) and percentiles were calculated using NCSS version 2004 (NCSS Institute Inc. 2004). The limit of quantification (LOQ) divided by 2 was used for imputation of values lower than the LOQ . Differences between samples with normal distribution were examined by the T-test and Chi-square test. Stepwise multiple linear regression analyses of log-transformed data were used to estimate the influence independent variables (creatinine, grilled meat habits and smoking habits) on the 1-OHP (stepwise procedure, criteria: probability F to enter ≤ 0.05 and probability F to remove ≥ 0.10). A p-value lower than 0.05 was considered as statistically significant for all tests.
Age of these 220 urban subjects was between 6 and 70 years and 31 years on average (standard deviation: 18). Most participants were adults (74.5%) and nearly half (50.5%) were female. Among adults, thirty-six percent were current smokers. The characteristics of sub-rural subjects are also presented in Table 1.
Geometric mean (GM) urinary 1-OHP was 1.8 μg/L (95% CI: 1.6, 2.0) (Table 2). Three (1.4%) 1-OHP measurements were less than the LOQ. As expected, smokers had higher cotinine urinary levels (Cot-U) than non-smokers [GM (95% CI): 137.3 μg/L (115.5, 163.2) versus GM (95% CI): 87.7 μg/L (70.4, 104.3)].
There was a statistically significant difference (p-value < 0.01) with smoking habits (0 for no/1 for yes) for 1-OHP. Age (0 for 6 – 14 years/1 for > 14 years) and sex (0 for female/1 for male) were not shown a significant difference (Table 2).
In multivariable analyses, creatinine (continuous log-variable), grilled meat habits (0 for non-consumers/1 for consumers) and smoking habits (cotinine as continuous log-variable) were the parameters significantly associated with urinary excretion of 1-OHP with 0.449 as a value of R2 (Table 3).
None of the measured values of Urinary 1-OHP was significantly different among the 11 urban entities investigated; indicating that our sampling strategy “unweigted clusters” did probably not introduce a strong bias in the representativeness of our population sample.
Urinary 1-OHP, a metabolite of PAH, has been shown to be an indicator of both uptake of pyrene from foods and exposure to exogenous PAH . However, an important limitation of this biomarker is that it only reflects recent exposure and tends to vary widely within individuals [23–26].
The distribution of urinary 1-OHP levels of the reference population are not Gaussian. Normalization can be obtained when expressing experimental data as a base 10 logarithm. Our results (Table 2) showed a significant difference in 1-OHP levels between current smokers and non-smokers (GM: 2.3 μg/L versus 1.3 μg/L, p < 0.01), which may be due to the fact that tobacco smoking may influence levels of urinary of 1-OHP [7, 18, 27–29].
In agreement with other studies, we found higher 1-OHP levels in consumers of grilled meat than in non-consumers (0 for non-consumers GM: 1.2 μg/L versus 1 for consumers GM: 4.0 μg/L, p < 0.01) (Figure 1; Table 2), which is not surprising since grilled meat represents an important source of PAH exposure [7, 30–32].
In Stepwise multivariable analyses, creatinine (continuous log-variable), grilled meat habits (yes/no) and smoking habits (continuous log-variable) were the independent parameters significantly associated with urinary unadjusted values of 1-OHP (depend parameter) with 0.45 as a value of R2 (Table 3).
As in other surveys, increased 1-OHP levels were measured in residents of urban areas compared to sub-rural settings [GM: 1.8 μg/L (n = 220) versus 1.4 μg/L (n = 50), p < 0.01]. The high percentage of smokers (Table 1) in the urban population could, at least partly, explain this difference.
The mean 1- OHP level in the sub-rural and the urban populations (smokers and non-smokers combined) exceeded the American and German levels (smokers and non-smokers combined) [12, 13]. Children from Kinshasa were found to have much higher levels (GM [95%CI]: 2.1 μg/L [1.6-2.6] for children 6–14 years) than American children (GM [95%CI]: 0.09 μg/L [0.07-0.11] for children 6–11 years; GM [95%CI]: 0.10 μg/L [0.085-0.129] for children 12–19 years) . Inhalation of emissions from charcoal burning or from cooking on open fires or traditional stoves fueled with biomass (wood, charcoal, crop and waste residues, …) either outdoor or in poorly ventilated spaces, and consumption of this broiled, smoked, fried or grilled food (Figure 1) are likely to contribute to the high levels of urinary 1-OHP in Kinshasa subjects.
The present study has several limitations. First, with regard to sample collection, selection of urinary sample donors did not follow rigid sampling strategy (such as random sampling) but by chance, which was practically inevitable under present survey conditions. Second, low number of subjects and characteristics selected. Third, passive smoking exposure is a factor affecting PAH exposure; this factor did not evaluate.
Despite such limitations, however, it is prudent to conclude that data from the present study constitutes levels generally exceeded in the Kinshasa population. Living in urban area of Kinshasa is associated with increased levels of 1-OHP in urine as compared to a reference population living in a sub-rural area of the same region. Increased levels were also found by comparison with the reference values from databases involving American or German populations.
This study reveals the high pyrene (PAH) exposure of the Kinshasa population requiring the determination of PAH concentrations in ambient air of Kinshasa and limits values for the protection of human health.
Agency for Toxic Substances and Disease Registry ATSDR: Toxicological Profile for Polycyclic Aromatic Hydrocarbons. Atlanta: Agency for Toxic Substances and Disease Registry, Available from http://www.atsdr.cdc.gov/toxprofiles/tp.asp?id=122&tid=25. Accessed 04. 05. 2013
Tsai PJ, Shih TS, Chen HL, Lee WJ, Lai CH, Liou SH: Urinary 1-hydroxypyrene as an indicator for assessing the exposures of booth attendants of a high way toll station to polycyclic aromatic hydrocarbons. Environ Sci Technol. 2004, 38: 56-61. 10.1021/es030588k.
Jongeneelen FJ, Anzion RBM, Henderson PT: Determination of hydroxylated metabolites of polycyclic aromatic hydrocarbons in urine. J Chromatogr. 1987, 413: 227-232.
Hansen AM, Mathiesen L, Pedersen M, Knudsen LE: Urinary 1- hydroxypyrene (1-HOP) in environmental and occupational studies–a review. Int J Hyg Environ Health. 2008, 211: 471-503. 10.1016/j.ijheh.2007.09.012.
International Programme on Chemical Safety (IPCS): Selected Non-heterocyclic Polycyclic Aromatic Hydrocarbons (Environmental Health Criteria 202). 1998, Geneva: International Programme on Chemical Safety, WHO
International Agency for Research on Cancer (IARC): IARC Monographs on the Evaluation of the Carcinogenic Risk of Chemicals to Humans, Vol. 38, Tobacco smoking. 1986, Lyon: International Agency for Research on Cancer
Van Rooij JGM, Veeger MMS, Bodelier-Bade MM, Scheepers PTJ, Jongeneelen FJ: Smoking and dietary intake of polycyclic aromatic hydrocarbons as sources of interindividual variability in the baseline excretion of 1-hydroxypyrene in urine. Int Arch Occup Environ Health. 1994, 66: 55-65. 10.1007/BF00386580.
Pandit G, Srivastava P, Rao A: Monitoring of indoor volatile organic compounds and polycyclic aromatic hydrocarbons arising from kerosene cooking fuel. Sci Total Environ. 2001, 279: 159-165. 10.1016/S0048-9697(01)00763-X.
Molnar P, Gustafsona P, Johannessona S, Bomanb J, Barregarda L, Sallstena G: Domestic wood burning and PM2.5 trace elements: Personal exposures, indoor and outdoor levels. Atmos Environ. 2005, 39: 2643-2653. 10.1016/j.atmosenv.2005.01.016.
Food and Agriculture Organization (FAO): Forests and energy in developing countries. Forests and energy working paper. 2007, 2: 32-
Marien JN: Conference on urban and peri-urban forestry «Trees connecting people: In action together» held in Bogotà (Colombia). Urban and peri-urban forestry in Africa: what perspectives for wood energy?. July 28th to August 1st, 2008
Centers for Disease Control and Prevention (CDC): National Health and Nutrition Examination Survey 2003–2004. 2009, Atlanta (GA): Fourth National Report on Human Exposure to Environmental Chemicals, http://www.cdc.gov/exposurereport/pdf/FourthReport.pdf. Accessed 20/01/2011
Becker K, Schulz C, Kaus S, Seiwert M, Seifert B: German environmental survey 1998 (GerES III): environmental pollutants in the urine of the German population. Int J Hyg Environ Health. 2003, 206: 15-24. 10.1078/1438-4639-00188.
Ancelle T: Statistique Epidémiologie.1ère. 2002, Paris: Maloine
Tuakuila J, Lison D, Mbuyi F, Haufroid V, Hoet P: Elevated Blood Lead Levels and sources of exposure in the Population of Kinshasa, the capital of The Democratic Republic of Congo. J Expo Sci Environ Epidemiol. 2013, 23 (1): 81-87. 10.1038/jes.2012.49.
Jongeneelen FJ: Biological monitoring of polycyclic aromatic hydrocarbons. Scand J Work Environ Health. 1986, 12: 137-143. 10.5271/sjweh.2166.
Li X, Leng S, Guo J, Guan L, Zheng Y: An improved high performance liquid chromatography method for determination of 1-hydroxypyrene in urine [in Chinese]. Wei Sheng Yan Jiu. 2003, 32: 616-617.
Liu AL, Lu WQ, Wang ZZ, Chen WH, Lu WH, Yuan J, et al: Elevated levels of urinary 8-hydroxy-2-deoxyguanosine, lymphocytic micronuclei, and serum glutathione S-transferase in workers exposed to coke oven emissions. Environ Health Perspect. 2006, 114: 673-677.
Benowitz NL: Cotinine as a biomarker of environmental tobacco smoke exposure. Epidemiol Rev. 1996, 18: 188-204. 10.1093/oxfordjournals.epirev.a017925.
Jaffe´ MZ: About the precipitation caused by pikrinic acid in normal urine and about a new reaction of creatinine. Z Physiol Chem. 1986, 10: 391-400.
Hornung RW, Reed LD: Estimation of average concentration in the presence of nondetectable values. Applied Occup Environ Hygiene. 1990, 5: 46-51. 10.1080/1047322X.1990.10389587.
Jongeneelen FJ: Benchmark guideline for urinary 1-hydroxypyrene as biomarker of occupational exposure to polycyclic aromatic hydrocarbons. Ann Occup Hyg. 2001, 45: 3-13.
Jongeneelen FJ, van Leeuwen FE, Oosterink S, Anzion RBM, van der Loop F, Bos RP, et al: Ambient and biological monitoring of cokeoven workers: determinants of the internal dose of polycyclic aromatic hydrocarbons. British J Industrial Med. 1990, 47: 454-461.
Buckley TJ, Lioy PJ: An examination of the time course from human dietary exposure to polycyclic aromatic hydrocarbons to urinary elimination of 1-hydroxypyrene. Br J Ind Med. 1992, 49: 113-124.
Boogaard PJ, van Sittert NJ: Exposure to polycyclic aromatic hydrocarbons in petrochemical industries by measurement of urinary 1-hydroxypyrene. Occup Environ Med. 1994, 51: 250-258. 10.1136/oem.51.4.250.
Viau C, Carrier A, Vyskocil A: Urinary excretion of 1-hydroxypyrene in volunteers exposed to pyrene by the oral and dermal route. Sci Total Environ. 1995, 163: 179-186. 10.1016/0048-9697(95)04494-L.
Zao ZH, Quan WY, Tian DH: Experiments on the effects of several factors on the l-hydroxypyrene level in human urine as an indicator of exposure to polycyclic aromatic hydrocarbons. Sci Total Environ. 1992, 113: 197-207. 10.1016/0048-9697(92)90001-9.
Heudorf U, Angerer J: Urinary monohydroxylated phenanthrenes and hydroxypyrene–the effects of smoking habits and changes induced by smoking on monooxygenase-mediated metabolism. Int Arch Occup Environ Health. 2001, 74 (3): 177-183. 10.1007/s004200000215.
Adonis M, Martinez V, Riquelme R, Ancic P, Gonzalez G, Tapia R, et al: Susceptibility and exposure biomarkers in people exposed to PAHs from diesel exhaust. Toxicol Lett. 2003, 144 (1): 3-15. 10.1016/S0378-4274(03)00225-X.
Vaessen HAMG: Dietary intake of polycyclic aromatic hydrocarbons. Toxicol Environ Chem. 1988, 16: 281-294. 10.1080/02772248809357267.
De Vos RH: Polycyclic aromatic hydrocarbons in Dutch total diet samples (1984–1986). Fd Chem Toxic. 1990, 28 (4): 263-268. 10.1016/0278-6915(90)90038-O.
Yang M, Kim S, Lee E, Cheong HK, Chang SS, Kang D, et al: Sources of polycyclic aromatic hydrocarbon exposure in non-occupationally exposed Koreans. Environ Mol Mutagen. 2003, 42 (4): 250-257. 10.1002/em.10196.
Chuang JC, Callahan PJ, Lyn CW, Wilson NK: Polycyclic Aromatic Hydrocarbon exposures of children in low-income families. J Expo Anal Environ Epidemiol. 1999, 9: 85-98. 10.1038/sj.jea.7500003.
Huang W, Caudill SP, Grainger J, Needham LL, Jr Patterson DG: Levels of 1-hydroxypyrene and other monohydroxy polycyclic aromatic hydrocarbons in children: a study based on US reference range values. Toxicol Lett. 2006, 163: 10-19. 10.1016/j.toxlet.2005.08.003.
We are highly indebted to the study participants and to the staff of investigators, as well as all the local health services and health centers of the Kinshasa Public Health System that supported the field work. We also thank Pr Lison, Pr Hoet, Pr Haufroid, Mr Boesmans and Mrs Lissenko for their collaboration. The financial support of the Belgian Technical Cooperation (Coopération Technique Belge-CTB/Belgische Technische Coöperatie-BTC) was gratefully acknowledged.
The authors declare that they have no competing interests.
JT drafted the manuscript. All authors commented the draft versions. All authors read and approved the final manuscript.
Authors’ original submitted files for images
Below are the links to the authors’ original submitted files for images.
About this article
Cite this article
Tuakuila, J., Kabamba, M. & Mata, H. High human exposure to pyrene (polycyclic aromatic hydrocarbon) in Kinshasa, a capital of the Democratic Republic of Congo. Arch Public Health 71, 14 (2013). https://doi.org/10.1186/0778-7367-71-14
- Environmental pollution
- Organic compounds
- Public health
- Polycyclic aromatic hydrocarbons