Ambient air pollution is one of the leading five health risks worldwide. One of the most harmful air pollutants is particulate matter (PM), which has different physical characteristics (particle size and number, surface area and morphology) and a highly complex and variable chemical composition. Our goal was first to comparatively assess the effects of exposure to PM regarding cytotoxicity, release of pro-inflammatory mediators and gene expression in human bronchial epithelia (HBE) reflecting normal and compromised health status. Second, we aimed at evaluating the impact of various PM components from anthropogenic and biogenic sources on the cellular responses. Air-liquid interface (ALI) cultures of fully differentiated HBE derived from normal and cystic fibrosis (CF) donor lungs were exposed at the apical cell surface to water-soluble PM filter extracts for 4 h. The particle dose deposited on cells was 0.9–2.5 and 8.8–25.4 μg per cm2 of cell culture area for low and high PM doses, respectively. Both normal and CF HBE show a clear dose-response relationship with increasing cytotoxicity at higher PM concentrations. The concurrently enhanced release of pro-inflammatory mediators at higher PM exposure levels links cytotoxicity to inflammatory processes. Further, the PM exposure deregulates genes involved in oxidative stress and inflammatory pathways leading to an imbalance of the antioxidant system. Moreover, we identify compromised defense against PM in CF epithelia promoting exacerbation and aggravation of disease. We also demonstrate that the adverse health outcome induced by PM exposure in normal and particularly in susceptible bronchial epithelia is magnified by anthropogenic PM components. Thus, including health-relevant PM components in regulatory guidelines will result in substantial human health benefits and improve protection of the vulnerable population.
Citation: Leni Z, Cassagnes LE, Daellenbach KR, El Haddad I, Vlachou A, Uzu G, et al. (2020) Oxidative stress-induced inflammation in susceptible airways by anthropogenic aerosol. PLoS ONE 15(11): e0233425. https://doi.org/10.1371/journal.pone.0233425
Editor: Rodrigo Franco, University of Nebraska-Lincoln, UNITED STATES
Received: January 22, 2020; Accepted: April 24, 2020; Published: November 18, 2020
Copyright: © 2020 Leni et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: All relevant data are within the paper and its Supporting Information files.
Funding: This study was supported by the Swiss National Science Foundation (SNSF) grant CR32I3_166325. K.R.D. acknowledges support by the SNSF mobility grant P2EZP2_181599. M.S. and N.B. acknowledge funding by the National Institutes of Health (NIH) grants NIH R01-HL-139365 and NIH R01-HL-133240. G.U. and J.-L.J. acknowledge support by the "Investissements d’avenir” program (ANR-15-IDEX-02) and LABEX OSUG@2020 (ANR-10-LABX-56).
Competing interests: The authors have declared that no competing interests exist.
Ambient air pollution has negative impacts on human health resulting in more than 4.5 million premature deaths each year [1–3]. Epidemiological studies have found consistent relations between morbidity and mortality and mass concentration of particulate matter (PM) with aerodynamic diameters ≤ 2.5 μm (PM2.5) or ≤ 10 μm (PM10) .
Up to date, PM mass concentration has been considered as the only appropriate metric to describe its impact on health . Thus, this metric has been used to assess the global burden of premature deaths due to PM . Recent studies, however, revealed associations between health effects and sources and composition of aerosols [5, 6]. PM consists of the carbonaceous fractions, which are primarily secondary organic aerosol (SOA) and elemental carbon, of the secondary inorganic aerosol (SIA) including nitrate, sulfate and ammonium, as well as of metals, soil dust, and sea salt . Although exposure to PM has been linked to various adverse effects, there are only few reports on the role of each PM component or a mixture thereof in pathogenesis . At present, there are increasing indications that anthropogenic components of PM, particularly transition metals and SOA, are of particular concern due to their ability to induce oxidative stress through the generation of reactive oxygen species (ROS) [8–11]. ROS generation has been previously identified as a major mechanism underlying the toxicity of air pollutants by triggering multiple redox-sensitive signaling pathways . It has also been suggested that PM transition metals and organic species (e.g. quinones) lead to the generation of free radicals in the lung environment and thereby induce oxidative stress [13, 14]. The ability of PM from both primary and secondary sources to generate oxidative stress has been described as oxidative potential (OP). Hence, organic carbon and transition-metal particles are of particular importance, due to their ability to promote inflammation [8, 9, 15]. Up to date, knowledge is lacking regarding the impact of PM from different sources on acute responses of the primary target tissue of inhaled particles, i.e., the highly specialized, multifunctional respiratory epithelium . Therefore, it is important to identify PM components that lead to an OP responsible for impairing human health.
We assessed the effects of exposure to PM with different physical characteristics and chemical composition with respect to cytotoxicity, release of pro-inflammatory mediators and gene expression on air-liquid interface (ALI) cultures of normal and diseased, i.e., cystic fibrosis (CF) human bronchial epithelia (HBE). This advanced in-vitro model mimics in-vivo characteristics, thus providing the archetypes of normal and susceptible respiratory epithelia, enabling experimental studies impossible in humans, primarily for ethical reasons. In addition, we directly evaluated the oxidative potential (OP) of PM using common acellular assays [15, 16].
Materials and methods
Aerosol sampling and sampling sites
In the present study, we assessed ambient particulate matter (PM) collected on filters from urban or rural sites in Switzerland during winter (January to March) and summer (July to August), reflecting the compositional complexity of PM. The PM10 and PM2.5 were collected within the Swiss National Air Pollution Monitoring Network (NABEL) onto quartz fiber filters (14.7 cm exposed diameter), using a high volume sampler (500 L/min, Digitel, Volketswil, Switzerland). The samples were 24-h integrated and collected every fourth day in 2013 (Bern PM10 and Bern PM2.5; sampling site: Bern-Bollwerk E 7° 26.452, N 46° 57.059), or 2013 and 2014 (Magadino PM10; sampling site: Magadino-Cadenazzo E 9° 0.735, N 46° 9.556). PM was determined gravimetrically by weighing the filters before and after exposure at a relative humidity (RH) of 50% and a temperature of 20°C after conditioning for 48 h. The uncertainty on PM mass is ~ 15%. All filter samples including the field blanks (unexposed quartz fiber filters) were wrapped in lint-free paper and stored at -18°C before further use. Magadino is located in an Alpine valley in the Southern part of Switzerland and the sampling station classifies as a rural background site. Bern is located on a plateau north of the Alpine crest with the sampling station situated in a street canyon and, thus, classifies as a traffic-influenced site. The average seasonal ambient particle concentrations at the urban roadside were 38 and 21 μg/m3 for PM10 and 28 and 14 μg/m3 for PM2.5, for winter and summer, respectively. Thus, in winter 74% and in summer 63% of PM10 appeared in the PM2.5 size fraction. At the rural alpine valley site, particle concentrations were 27 and 13 μg/m3 for PM10, winter and summer, respectively, in line with continuous measurements at these sites . While the mass concentrations at the rural site are only 30–40% lower, the main difference between the sites is the composition of PM, with a high contribution of biomass burning in Magadino during winter and a high contribution of vehicular emissions in Bern.
Preparation of water-soluble filter extracts for cell exposure
Filter punches (diameter 10 mm) were taken and weighted to determine the PM concentration before each cell exposure. Punches from different filters from winter or summer were pooled to form a seasonal composite and to avoid day-to-day variation due to traffic and meteorological conditions. For the field blanks, punches of the same filter surface area were pooled. On the day of cell exposure, punches were allowed to equilibrate for 60 min at room temperature before use, to avoid condensation of ambient humidity. Before cell exposure, filter punches were placed in a 14-mL sterile tube containing 7 mL ultrapure water (18.2 MΩ cm MilliQ water) and incubated for 15 min in a warm (30°C) water bath. Samples were thereafter homogenized by vortexing for 1 min and filtered through a nylon membrane syringe filter (0.45 μm mesh size; Infochroma AG, Zug, Switzerland) to remove insoluble material from the sampling filter as well as the insoluble fraction of the aerosol, i.e. elemental carbon, insoluble organic aerosol (OA) and crustal material [18, 19]. These filters are made to maximize the extraction efficiency for the soluble species, while maintaining compositional integrity, so that the final extraction solution yields sufficient PM10 and PM2.5 mass that remains representative of the ambient composition. In this study, the yield of PM after filtration compared to total PM was not analyzed. However, we estimate that ~ 80% of the PM2.5 is extracted and recovered [19, 20]. This includes all the inorganic ions (contributing ~ 50% of the total mass), most of the organic aerosol (extraction efficiency ~ 70%) and the water-soluble elements (varying according to the site and the element from 15 to 100%).
Cell cultures and exposures
Cultures of primary human bronchial epithelia (HBE) at the air-liquid interface (ALI) reproduce many features of the native respiratory epithelium like the pseudostratified morphology, distinct apical and basolateral secretomes, epithelial barrier function and mucociliary clearance [20–23]. HBE were isolated from donor lungs. Two normal lungs deemed not suitable for transplantation were obtained from the Life Alliance Organ Recovery Agency (LAORA) of the University of Miami, Miami, FL, USA. A cystic fibrosis (CF) lung, homozygous for the DF508 mutation, was donated by a transplant recipient. Appropriate consents, approved by the Institutional Review Board of the University of Miami, Miami, FL, USA, and conforming to the declaration of Helsinki, were used to obtain all lungs. Cells were collected from proximal conducting airways according to approved protocols [24, 25]. ALI cultures of re-differentiated HBE from all organ donors were evaluated for morphological and functional integrity and pre-phenotyped with respect to cytotoxicity and cytokine release before they were used in the experiments, as previously described .
Fully differentiated HBE were exposed at the apical cell surface to the water-soluble PM filter extracts for 4 h. Thereafter, the apical cell surface was washed with phosphate-buffered saline (PBS) to remove the particles, mimicking the defense mechanism of the respiratory epithelium. Control cell cultures were either exposed to extracts from field blanks (filters treated the same way apart from exposure to ambient air), or were left untreated in the incubator. As a positive control and to check for the (pro-)inflammatory response capacity, additional cell cultures were exposed to the bacterial endotoxin lipopolysaccharide (LPS) from Escherichia coli (Sigma Aldrich, Buchs, Switzerland) at 10 μg/mL in PBS for 4 h. Three independent experiments with triplicate HBE cultures in each experiment were performed.
Induction of cell death was evaluated by measuring the release of cytosolic lactate dehydrogenase (LDH) from damaged cells into the apical compartment. Apical washes were collected 4 h and 24 h post exposure and stored at 4°C until analysis using the colorimetric cytotoxicity detection kitPLUS (Roche Diagnostics AG, Rotkreuz, Switzerland) according to the manufacturer’s instructions. Maximum release of LDH was estimated in the supernatants of unexposed HBE lysed with 100 μL 1% Triton-X solution for 10 min at 37°C. Cytotoxicity is presented as percentage of maximum LDH release.
The release of the (pro-)inflammatory mediators interleukin (IL)-6 and IL-8 was assessed in the basolateral compartment collected at 24 h after exposure to PM filter extracts or to the positive control compound LPS, using the Bio-Plex multiplex bead-based suspension array system and the appropriate detection kit (Bio-Rad Laboratories AG, Cressier, Switzerland) according to the manufacturer’s protocol.
We screened 20 genes to evaluate alterations in signaling pathways related to oxidative stress using Gene globe arrays. Gene expression in HBE was examined by isolation of total RNA followed by quantitative real-time polymerase chain reaction (RT-qPCR). Briefly, cells were lysed with TRIzol reagent (Invitrogen) and stored at -80°C until further processed. Isolated RNA (500 ng) was reverse transcribed into cDNA using the QuantiTect reverse transcription kit (Qiagen) following the manufacturer’s recommendations. Real-time PCR was performed in a reaction volume of 25 μL using the QuantiTect SYBR Green PCR kit (Qiagen) and the QuantiTect Primer Assays (Qiagen), amplifying a total of 25 ng cDNA of each sample. Real-time PCR was performed using the Applied Biosystems 7900HT-Fast Real-Time PCR System with a 15-min initial activation step at 95°C and 40 cycles with 15 s denaturation at 94°C, 30 s annealing at 55°C and 30 s extension at 72°C. Subsequently, a melting curve was performed to exclude primer-dimer artefacts and to ensure reaction specificity. Data were analyzed using the RQ Manager 1.2 software. The unsupervised heat map of the entire dataset, clustered based on the Euclidean distance, allowed evaluating the deregulation of specific genes in HBE (see S1 Fig). The deregulation of the gene pattern was confirmed after classification according to PM category (PM10, PM2.5) and collection site.
Offline aerosol mass spectrometry (AMS) and organic aerosol (OA) source apportionment
Following the offline AMS technique thoroughly described by Daellenbach et al. , four filter punches of 16 mm diameter each were extracted in 15 mL of ultrapure water (18.2 MΩ cm at 25°C with total organic carbon < 3 ppb). The liquid extracts were ultra-sonicated for 20 min at 30°C, then vortexed for 1 min and finally filtered through a nylon membrane syringe of 0.45 μm pore size (see also method section). The resulting solutions were inserted into an Apex Q nebulizer (Elemental Scientific Inc., Omaha, NE, USA) operating at 60°C. Aerosols generated in argon (≥ 99.998% Vol., Carbagas, Gümligen, Switzerland) were dried (Nafion dryer) and directed into a high resolution time-of-flight AMS (HR-ToF-AMS, Aerodyne Research, Inc., Billerica, MA, USA). Data processing was performed with the use of the Source finder toolkit (SoFi version 4.9)  for IGOR Pro software (Wavemetrics Inc., Portland, OR, USA). The organic mass spectra obtained by the AMS were analyzed by positive matrix factorization (PMF) with the use of Multilinear engine 2 . PMF application on organic mass spectra measured in Switzerland can be found in the literature [19, 28], while the specific dataset is described in detail by Daellenbach et al. . Briefly, PMF was used to decompose the input water soluble aerosol organic mass spectra (represented as 2D matrix X) into factor concentration time series (2D matrix G) and factor profiles (2D matrix F) by iteratively solving the bilinear equation X = GF + E, where the 2D matrix E represents the residual matrix. The solution that includes the optimum number of factors (in other words sources) is defined by: (i) the minimization of the sum of the squared residuals weighted by their respective uncertainties and (ii) correlations between factors and externally measured source specific compounds. To assess random errors as well as the robustness of the PMF solution, we adopted the bootstrap analysis, based on random resampling. The water soluble OA was quantified by using the externally defined OC (by Sunset OC/EC analyzer  with the EUSAAR2 protocol ) and the water soluble OC (by a total organic carbon analyzer ) concentrations. Finally, the water soluble OA was scaled to its total OA concentration with the use of recoveries .
Ion Chromatography (IC).
Soluble anions and cations (K+, Na+, Mg2+, Ca2+, NH4+, Cl-, NO3-, SO42-), as well as methane sulfonic acid were analyzed after ultrapure water extraction under mechanical agitation (30 min) by ion chromatography (IC, Dionex ICS3000) on the same extracts. AS/AG 11HC and CS/CG 12A columns were used for anion and cation analyses, respectively, following the protocol from Jaffrezo et al. . The anhydrous sugars levoglucosan, mannosan and galactosan were analyzed using a high-performance anion exchange chromatograph with pulsed amperometric detection .
Inductively coupled plasma mass spectrometry (ICP-MS).
An ELAN 6100 DRC II PerkinElmer or a NEXION PerkinElmer ICP-MS was used for the analysis of 15 trace elements (Al, Fe, Ti, As, Cd, Cu, Mn, Mo, Ni, Pb, Rb, Sb, Se, V, Zn). Briefly, samples from filter punches were mineralized before analysis, using 5 mL of HNO3 (70%) and 1.25 mL of H2O2, during 30 min at 180°C in a microwave oven (microwave MARS 6, CEM)  and filtered.
Oxidative Potential (OP)
For OP evaluation, PM was extracted in simulated lung fluid (SLF) at iso-concentration (25 μg/mL) and subsequently analyzed by three different chemical acellular assays (dithiothreitol: DTT, 2’7’-dichlorofluorescin: DCFH, ascorbic acid: AA) to assess the intrinsic capacity of PM to oxidize a biological fluid. They all rely on the kinetic depletion of an anti-oxidant (AA) or surrogates (DTT, DCFH), when in contact with the extracted solution of PM. The PM solutions were not filtered to also allow surface reactivity of the PM. The depletion was followed during 30 min with a plate-reader using the absorbance mode at 265 nm for the AA assay, at 412 nm for the DTT assay (titration of DTT by 5,5-dithio-bis-(2-nitrobenzoic acid) DTNB) according to Calas et al. . The oxidation of DCFH into the fluorescent compound DCF was assessed by fluorescence at 530 nm for emission (excitation at 485 nm) according to Foucaud et al. . Samples were corrected for the values of the field blanks and for intrinsic absorbance of the particles present in the sample wells.
All biological data are expressed as mean values ± standard deviation. Statistical analyses were performed using GraphPad Prism 7.00 (GraphPad Software Inc., San Diego, CA). For cytotoxicity and release of inflammatory mediators, the arithmetic mean values from the triplicate cell cultures of each experiment were compared to the mean values of the untreated control cultures by one-way analysis of variance (ANOVA) followed by Dunnett’s t-test to compare the treated to the control group, or the Bonferroni test for multiple comparisons. To assess the correlation between IL release and OP, metal or inorganic salts composition, non-parametric Spearman correlation (rs) and statistical significance were calculated using the Student’s t-test. A value of p < 0.05 was considered statistically significant.
Deposited particle dose
The particle dose deposited on cells was 0.9–2.5 and 8.8–25.4 μg per cm2 of cell culture area for low and high PM doses, respectively (Table 1). The particles were deposited as bolus and left to interact for 4 h with the respiratory epithelium, where antioxidant defense and mucociliary transport replicate the defense mechanisms. In addition, the removal of the particles after 4 h by washing the apical surface mimics the average residence time of particles deposited in this lung compartment. Thus, the dose deposited reflects the effective dose over this time period. To roughly estimate how the experimentally deposited doses translate to real exposure conditions, the Multiple Path Particle Dosimetry model (MPPD v 3.04)  was used (S1 Table), which provides the dose the human tracheobronchial tract can acquire over 24 h. The result of such an approximation shows the high and low doses applied in this study to correspond to a deposited dose in the human tracheobronchial tract of days up to weeks in highly polluted areas reaching 1000 μg/m3, PM2.5, e.g. China , and of several months to years in urban areas in Europe, with typical concentrations of 20 μg/m3 .
Cellular responses to PM exposure
While epithelial morphology did not change upon exposure to PM (data not shown), we found a significant, dose-dependent increase of cytotoxicity. This is reflected by enhanced levels of the cytoplasmic enzyme lactate dehydrogenase (LDH) released from damaged cells into the apical compartment, on average 2.2 fold in normal (p-value = 0.0395) and 4.6 fold in CF HBE (p-value = 0.0289), compared to field blank controls (Fig 1A and Table 2).
(a) Cytotoxicity presented as percentage of total lactate dehydrogenase (LDH) released from damaged cells into the apical compartment. Low dose deposited on HBE = 0.9–2.5 μg per cm2 of cell culture area, high dose = 8.8–25.4 μg/cm2. The data are presented as mean values and error bars representing 1 standard deviation (SD) of three independent experiments with triplicate cell cultures (total n = 9 cell cultures). ANOVA, Dunnett’s multiple comparison). (b) Scatter plot and corresponding regression line for normal and CF HBE, evaluating the relationship of cytotoxicity and deposited particle dose (repeated measurements at the same dose are displayed for visualization). * p-value < 0.05 compared to filter blank. Abbreviation: R2 = R-square linear coefficient of determination.
In addition, Fig 1B shows a positive linear correlation between cytotoxicity and the deposited dose (R2 = 0.4011 and 0.3148 for normal and CF HBE, respectively). The increase of cytotoxicity within the same cell model (normal or CF HBE) was independent of seasonal PM collection as well as of sample size fractions, i.e. the coarse PM10 and fine PM2.5 fractions.
The release of both interleukins analyzed significantly increased in response to PM exposure (Fig 2A); IL-6 on average 1.4 fold in normal and 1.3 fold in CF HBE, as compared to field blanks (p-values < 0.0001), and IL-8 on average 2.2 fold in normal (p-value = 0.0002) and 1.6 fold in CF HBE (p-value < 0.0001) and irrespective of seasonal sampling. Although, the release of interleukins correlated well with the deposited dose in normal and CF HBE (R2 = 0.84 and 0.85 for IL-6; R2 = 0.73 and 0.78 for IL-8, Fig 2B–2C), there was no significant difference between PM10 and PM2.5. Exposure to the positive-control compound LPS caused the highest increases in the release of both cytokines (Fig 2A). IL-6 was on average 2.2 fold and IL-8 was 3.1 fold higher than in the field blank controls.
(a) Release of interleukin (IL)-6 and IL-8 into the basolateral compartment (dotted lines show interleukin release in incubator controls). The data are presented as mean values and error bars representing 1 standard deviation of three independent experiments (ANOVA, Dunnett’s multiple comparison) with triplicate cell cultures (total n = 9 cell cultures). (b) IL-6 and (c) IL-8 release vs. deposited particle dose associated with positive linear correlation using standard linear regression analysis. ** p-value < 0.01, *** p-value < 0.001 compared to filter blank. Abbreviations: LPS = lipopolysaccharide (10 μg/mL); L = low dose; H = high dose; R2 = R-square linear coefficient of determination.
Overall, the screening with gene globe array revealed common signatures of deregulated genes in both cell models, as compared to the filter blank controls. In normal HBE, the expression of 14 out of 20 genes was upregulated (seven highly and seven moderately), two were downregulated and four genes remained unchanged. In CF HBE, however, most of the selected genes (n = 18) were upregulated (two- to tenfold change) and only two remained unaltered (Fig 3 and S1 Fig). We further validated the upregulation of the genes with the highest degree of deregulation (superoxide dismutase 1 and 2: SOD1, SOD2; nuclear factor erythroid-derived 2-like 2: NFL2L; heme oxygenase 1: HMOX1; NAD(P)H quinone dehydrogenase: NQO1; peroxiredoxin 2: PRDX2 and ataxia telangiectasia mutated kinase: ATM) using real-time polymerase chain reaction (RT-qPCR) (Fig 3B–3E). Inflammation arising via oxidative stress response is reflected by the significantly increased expression of the oxidative stress genes SOD1 and SOD2 in both normal (p-value = 0.0415 for SOD1 and p-value = 0.0314 for SOD2) and CF HBE (p-value = 0.0318 and p-value = 0.0326) (Fig 3B). Parallel activation of the antioxidant response and of cytoprotection in normal and CF HBE is shown by upregulation of the HMOX1 (p-value = 0.0219, p-value = 0.0414), the NFL2L (p-value = 0.0409 and p-value = 0.0314), the PRDX (p-value = 0.0472, p-value = 0.0461) and the NQO1 genes (p-value = 0.0484, p-value = 0.0310) (Fig 3C and 3D). In contrast, DNA damage genes were significantly upregulated in addition to oxidative stress genes only in CF HBE (p-value = 0.0066 for ATM and p-value = 0.0452 for H2A histone family member X:H2FAFX, Fig 3E).
(a) Gene expression profiles of the screened 20 genes, classified by PM category (PM10, PM2.5) and site (urban roadside and rural alpine valley). Fold changes of gene expressions relative to field blank controls are reported (n = 9). Abbreviations: IL = interleukin; GSTA1 = glutathione S-transferase alpha 1 = S100A9: S100 calcium binding protein A9; ATM = ataxia telangiectasia mutated kinase; NOX4 = NADPH oxidase 4; H2AFX = H2A histone family member X; SOD = superoxide dismutase; PRDX2 = peroxiredoxin 2; SRXN1 = sulfiredoxin 1; DUOX = dual oxidase; SCARA3 = scavenger receptor class A member 3; HMOX1 = heme oxygenase 1; NQO1 = NAD(P)H quinone dehydrogenase; GPX1 = glutathione peroxidase 1; CFLAR = CASP8 and FADD like apoptosis regulator; NFE2L2 = nuclear factor erythroid-derived 2-like 2. RNA18S5 = ribosomal RNA 18S5, used as reference gene in the unsupervised analysis. HPRT1 = hypoxanthine guanine phosphoribosyl transferase 1 and HSP90AB1 = heat shock protein 90 kDA alpha, class B, member 1 were selected as housekeeping genes. Validation of (b) oxidative stress, (c) antioxidant defense, (d) oxidative protection and (e) DNA damage response pathways in normal and CF HBE. The data are presented as mean values and standard error of the mean of three independent experiments (ANOVA, Dunnett’s multiple comparison). Filled bars represent exposure to high, banded bars to low PM dose. * p-value < 0.05; ** p-value < 0.01 referring to gene expression of CF compared to normal HBE.
Oxidant generation capacity and chemical composition of PM
Oxidative Potential (OP).
The assessment of the OP of PM by the acellular assays dithiothreitol (OPDTT), ascorbic acid (OPAA) and 2’7’-dichlorofluorescin (OPDCFH), shown in Fig 4A and 4C, revealed exposure to PM with a high OP to enhance the release of IL-6 in both cell models using the non-parametric Spearman’s rank correlation coefficient (rs OPDTT = 0.80, OPAA = 0.82, OPDCFH = 0.69 in normal and rs OPDTT = 0.74, OPAA = 0.69, OPDCFH = 0.76 in CF HBE) and thus triggering inflammation [28, 29, 40].
(a) and (b) non parametric correlation (Spearman rs), (c) and (d) Student’s t-test p-values of rs. The correlation was derived from the release of interleukins (IL-6 and IL-8) and lactate dehydrogenase (LDH) in normal and cystic fibrosis (CF) HBE after exposure to PM filter extracts. OPDTT, OPAA and OPDCFH refer to the oxidative potential of PM determined using the three acellular assays: dithiothreitol (DTT), ascorbic acid (AA) and 2’7’-dichlorofluorescin (DCFH). The following chemical components of PM are included (see Methods): exhaust (hydrocarbon-like OA–HOA) and non-exhaust (organic sulfur-containing OA—SCOA, metals: Cu, Fe, Mn) primary traffic emissions, cooking emissions (COA), primary biomass burning emissions (organic: BBOA, metals: Zn, Pb), crustal material (Ti, Al), anthropogenic SOA (aSOA), biogenic SOA (bioSOA) and secondary inorganic aerosol (SIA, NH4+, NO3-, SO42-).
To further evaluate the impact of the PM chemical composition and identify the relevant sources on the inflammatory response in HBE, we distinguished exhaust from primary traffic emissions (hydrocarbon-like OA–HOA) and non-exhaust (organic sulfur-containing OA–SCOA, metals: Cu, Fe, Mn), primary cooking emissions (COA), primary biomass burning emissions (organic: BBOA, metals: Zn, Pb), crustal material (Ti, Al), anthropogenic SOA (aSOA), biogenic SOA (bioSOA), and secondary inorganic aerosol (SIA, NH4+, NO3-, SO42-). The results, shown in Fig 4 and Table 3, clearly demonstrate increasing IL-6 release in normal and CF HBE to relate to increasing concentrations of anthropogenic PM components.
The evidence of health effects associated with source-specific PM does not indicate a clear ‘hierarchy’ of harmfulness for PM from different emission sources [2, 41]. However, results obtained suggest that a range of detrimental health effects are consistently associated with traffic-related PM, SOA, specific metals and elemental carbon in PM [5, 6, 42, 43]. Our results provide on the one hand experimental support for an increased susceptibility of persons with pre-existing pulmonary disorders to environmental PM exposure [23, 44–46]. On the other hand, we identified PM components and their biological mechanism leading to adverse effects.
By integrating information from different disciplines, the present study reveals that the major mechanism by which PM acts on the bronchial epithelium, the primarily affected lung compartment in pulmonary disease, is to proceed through an oxidant/anti-oxidant imbalance to yield inflammatory response cascades. We further show that anthropogenic PM magnifies the adverse health outcome in normal and susceptible bronchial epithelia. In addition, the increase of the deposited PM dose progressively increases epithelial damage. The four to six times enhanced cytotoxicity in CF HBE compared to normal epithelia shows that individuals with pre-existing pulmonary diseases are more susceptible to PM exposure than healthy ones.
Thus, the main driver of the adverse health effects of PM pollution is the anthropogenic PM, in particular in vulnerable individuals. Our data on the assessment of cytotoxicity and interleukin release clearly demonstrate the relation of the observed cytotoxicity to the inflammatory processes induced by PM exposure. In addition, our results on the gene expression confirm the activation of the inflammatory response pathway and reveal the upregulation of oxidative stress genes (SOD1 and SOD2) and of the antioxidant response (HMOX-1 and NFL2L) together with enhanced cytoprotection (PRDX2 and NQO1) in both cell models. Lacking activation of other genes in normal HBE indicates that the antioxidant response sufficiently protects normal epithelia. In contrast, the significantly upregulated DNA damage and oxidative stress genes in CF HBE imply that the antioxidant defense in these compromised epithelia was overcome by exposure to PM. This ultimately explains the higher cytotoxicity in CF than normal HBE.
Overall, our data clearly demonstrate that inflammation arising via oxidative stress response is reflected by significantly increased expression of the oxidative stress genes (particularly SOD2). Moreover, there is a link to the season of sample collection, mirrored by the enhanced expression of genes in samples collected in winter compared to summer in both normal and CF HBE, in particular for genes related to inflammation (IL-6 and IL-8) and antioxidant defense (SOD2).
The limited number of samples in the study, however, does not allow establishing a clear link between the observed adverse effects and the sites of PM collection or the PM category (PM10 samples contain the PM2.5 fraction). However, we provide evidence that anthropogenic sources of atmospheric PM play a more important role than biogenic emissions in inducing adverse effects to bronchial epithelia, in particular in the vulnerable population.
While considerable efforts were allocated to decrease vehicle emissions, and although PM concentrations in Europe decreased significantly during the last decades [47, 48], mitigation strategies are not equally effective in decreasing the OP of PM . As outlined by Daellenbach et al. , due to the adoption of a renewable energy source for residential heating, the concentration of primary and aged biomass burning aerosol is expectedly rising and leads to enhanced OP . Consequently, the overall health impacts of PM may increase in the near future despite the decrease in total PM mass concentrations. Our data suggest that in order to reduce the adverse health effects of ambient pollution, the commitment to effectively decrease PM mass concentration and OP has to be intensified. Specifically targeting health-relevant anthropogenic PM components (from exhaust and non-exhaust car emissions, wood combustion) is key to mitigate the adverse health impacts of PM and in particular, to protect the vulnerable population.
S1 Table. Calculation of the deposited particle dose in the human tracheobronchial (TB) tract at different ambient concentrations.
S1 Fig. Screening and validation of the gene expression profile upon PM exposure in normal and CF HBE.
Unsupervised hierarchical clustering analysis using the differentially expressed genes in normal and CF HBE. The heat map (Ward linkage and Euclidean distance) represents log transformed Delta Ct values. The heat map color-palette represents gene expression as indicated in the color key. Blue, green and pink lines on the left side of the heat map represent clustered genes.
We thank the Swiss Federal Office for the Environment (FOEN) for providing the filter samples. We acknowledge Swiss Federal Laboratories for Materials Science and Technology (Empa) and the National Air Pollution Monitoring Network (NABEL) for providing the air quality data.
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