Background

Epidemiological studies have shown that exposure to ambient particulate air pollution (particulate matter or PM) is associated with many health effects [1–3], which include premature death, increased hospitalization for cardiopulmonary diseases, airway complaints, and reduced lung function. Although estimates of relative risks are small, there is a public-health concern because many people are exposed and there are high-risk groups, such as the elderly, very young children, and people with cardiopulmonary diseases. Although the PM-associated adverse health effects have been found all over the world, a more closer look reveals that there seem to be heterogeneous across locations [4–8], which might be due to differences of anthropogenic sources such as traffic [9]. Particulate matter consists of many chemicals, but it is not very likely that some of them (sea salt, sulphate, and nitrate [10] in ambient air affect health adversely. Aerosolized combustion products from traffic, shipping, industry, and domestic heating are believed to be far more relevant. The risk can be effectively reduced by reducing the PM fraction that is most likely to cause adverse health effects.

Due to its the complexity, the best way to study PM is by studying the effects of inhaling it. Systems designed to deliver controlled amounts of concentrated ambient particles now exist and allow a mechanistic approach to determining the effect of inhaled PM in different size ranges [11–13]. Recently published studies have shown that exposing rodents [14–20], dogs [21] and human volunteers [22–26] to concentrated ambient particles (CAP) indicate that PM has the potential to cause adverse effects. Biological responses to high concentrations of PM (which were often well above ambient PM concentrations) were observed. The sensitivity of these toxicological studies is low because of the small number of observations, as well as the fact that exposure levels and PM composition vary from day to day. However, data from homogeneous populations, as well as the use of specific disease models that mimic human risk groups, should increase study sensitivity to the effects of CAP exposures. The results of a series of 1-day (6 h/day) inhalation exposures of compromised rats to fCAP [27] revealed that CAP can increase inflammation [polymorphonuclear leukocytes (PMNs)] and toxicity [protein and albumin in bronchoalveolar lavage fluid (BALF)], and it can also increase the risk of thrombotic vascular disorders (fibrinogen). Nonetheless, we were unable to prove consistent relationships between PM mass and biological effects. While alterations of biological endpoints were occasionally statistically significant and potentially biologically relevant, we found no convincing proof that ambient PM exposures (up to 3500 μg/m3) can modify homeostasis. In another study in which rats pre-treated with ozone or with induced pulmonary hypertension were exposed for 6 h to concentrated freshly generated diesel exhaust particles up to 9000 μg/m3, no noteworthy pulmonary toxicity was observed, though increased glutathione levels (in the case of ozone-treated rats) and increased blood fibrinogen levels in rats with existing pulmonary hypertension were observed [20]. Although these studies and those of others [14, 15] have shown that CAP exposure has adverse effects, no studies have yet been published that convincingly prove relationships between mass concentration and these biologically relevant outcomes [18, 27]. Bearing the available evidence of studies exposing animal or human subjects to CAP, PM mass concentrations do not seem to be the optimal metric to be associated with the adverse health effects. In that respect it is noteworthy that monotonic functions are usually sufficient to describe the relationship between air pollution and health effects in the epidemiological studies. However, Seagreave and colleagues [28] have recently shown that at least some parameters may respond in a way that achieves an optimum concentration beyond which the effects are reduced again.

Most toxicological studies that have used CAP exposures have focused on the accumulation mode (0.15 μm – 2.5 μm) [15, 17, 19] or coarse mode (2.5 μm – 10 μm) [17] of ambient PM. In recent years, more and more information has shown that the ultrafine fraction within PM might be more toxic than the fine mode. It has been suggested that the large surface area or particle number, or perhaps just the particle size, may play an important role in such differential responses [29, 30]. Other studies have shown that the ultrafine fraction of urban ambient aerosols is not necessarily more potent than the fine or coarse fractions in inducing inflammatory and toxic effects in lung cells [31].

In order to compare the potential of PM fractions to induce adverse biological effects, we performed a series of studies of spontaneously hypertensive (SH) rats in which we used both concentrated fine PM (fCAP) and ultrafine + fine PM (u+fCAP). We compared the effects of PM that included ultrafines at a site with traffic as the major source with toxicity of accumulation mode (fine PM) at an urban background site with no dominant source of PM emission. A strain of SH rats was selected as a strain that would be more sensitive to PM [19] and to allow interstudy comparison [27, 15].

Results

Exposure characteristics

Integrated and continuous exposure characterization techniques were applied to determine the concentration and the composition of the test atmospheres at the different exposures (Table 1). Temperature and relative humidity were 22 ± 2°C and 40 ± 10% for the fCAP exposure and both control exposures; they were 22 ± 2°C and 70 ± 10% for the u+fCAP exposure. The mean overall levels of some gaseous pollutants before passing the air through the concentrator were: 12 μg/m3 for ozone, 39 μg/m3 for carbon monoxide, 29 μg/m3 for sulphur dioxide, 19 μg/m3 for nitrogen monoxide, 13 μg/m3 for nitrogen dioxide and 28 μg/m3 for total nitrogen oxides (NOx). Ambient ozone is known to be efficiently removed in the concentrator due to the large metal surface, whereas all other gaseous components will remain at the same concentration or will show a little decrease. Table 1 shows that the sum of ammonium, nitrate, and sulphate ions accounts for 56 ± 16% of the total fCAP mass concentrations for the Bilthoven site (I), whereas it only accounts for 17 ± 6% of the u+fCAP mass concentrations at the HIA site (II). Most of the remaining mass is very likely associated with carbonaceous material, and the difference between site I and site II reflects the enrichment in organic and elemental carbon, as expected, given its proximity to mobile sources.

Table 1 Exposure characteristics for studies in spontaneously hypertensive rats exposed to concentrated ambient particulate matter
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Bronchoalveolar lavage

Table 2 presents the overall results of the BALF biochemical analyses. The contribution to the day-to-day variation was calculated in a two-way ANOVA for the biological indices of both the filtered air and the CAP- exposed animals. Some of the parameters showed substantial day-to-day differences that might be attributed to the assays and need to be taken into account as a confounding factor in the overall statistical analysis. The CAP exposures, with either the combined fCAP exposures (at site I Bilthoven) or the combined u+fCAP exposures (at site II HIA) did not result in statistically significant changes of most biochemical analyses measured in BALF compared to their filter-air controls. No signs of cytotoxicity as indicated by unchanged LDH and ALP levels were observed. No significant changes were found either in the number of cells or cell differentiation in the BALF. However, clear particle uptake was observed in macrophages lavaged from the rat lungs after exposure to fCAP or u+fCAP. MDA, a parameter for lipid peroxidation, is significantly lowered by u+fCAP exposures (Table 2).

Table 2 Health effect parameters measured in lung lavage fluid of spontaneously hypertensive rats 8 h afterexposure to concentrated ambient particulate matter or clean air as a control.
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Levels of the overall HO-1 values in BALF, as a measure for oxidative stress in the lungs, were increased by u+fCAP and fCAP exposures (after omitting data of the two experiments with the highest exposure concentrations, e.g. January 6th 2003 and February 11 2003) (Table 2). For the u+fCAP exposure, there was a significant increase to 0.664 ng/ml compared to the 0.517 ng/ml value of the control animals. However, more detailed data analyses of the fCAP data shows a clear nonmonotonic concentration-effect relationship with the HO-1. Maximum levels of HO-1 were observed at around 600 μg/m3 measured both in BALF and in lung homogenate (Figure 2). There is a correlation of r2= 0.79 for the HO-1 measured in BALF and in lung homogenate (Figure 3). Data corrected for the amount of protein present were very comparable to Figure 2 (data not shown). In none of the fCAP exposures did the LDH content in BALF change significantly upon exposure.

Figure 2
figure 2

Relative heme oxygenase-1 present in bronchoalveolar lavage fluid () and in lung homogenate () versus the mass of fine, concentrated, ambient particulate matter. Relative heme oxygenase-1 is defined as ([HO-1]CAP- [HO-1]Control)/[HO-1]Control, where [HO-1] is the mean value of n = 8.

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Figure 3
figure 3

Correlation between heme oxygenase-1 present in bronchoalveolar lavage fluid versus heme oxygenase-1 present in lung homogenate. All animals were exposed to fine, concentrated, ambient particulate matter. Regression: Y = -0.15 + 0.217*X, correlation coefficient = 0.79.

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The only other parameter which showed significance at the individual fCAP exposures was CC16, which was significantly decreased at 457 μg/m3 fCAP and increased at the greatest exposure of 3613 μg/m3 fCAP (Figure 4).

Figure 4
figure 4

Clara cell secretory protein present in bronchoalveolar lavage fluid after rats were exposed to fine, concentrated, ambient particulate matter (fCAP) (site I) control, ■ fCAP exposed.

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Blood

After exposure to fCAP and u+fCAP, there was a significant decrease of WBCs (Table 3). Consequently, absolute numbers of neutrophils and lymphocytes are decreased (although the decrease is not statistically significant for the number of neutrophils after u+fCAP exposure). Significant changes in haematological parameters, i.e., the mean platelet volume (MPV) and the mean platelet component (MPC), were found after exposure to u+fCAP, but these effects are not observed for the fCAP-exposed rats (the MPC parameter has not been measured for the fCAP exposures). No changes in concentrations of fibrinogen and vWF were observed in plasma after exposure to u+fCAP or fCAP. However, a significant increase of the greatest concentration of the fCAP exposure was observed for vWF (Figure 5).

Figure 5
figure 5

Von Willebrand factor present in citrate plasma after rats were exposed to fine, concentrated, ambient particulate matter (fCAP) (site I) control, ■ fCAP exposed.

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Table 3 Health effect parameters measured in blood of spontaneously hypertensive rats 8 h after exposure to concentrated ambient particulate matter or clean air as a control.
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Pathology

There were no differences in the lung and body weights of sham and CAP-exposed animals (data not shown). The characteristic hallmarks of the strain of rats used as controls were clearly present in their lungs: small alveolar haemorrhages and extensive bronchus-associated lymphoid tissue (BALT) at many bifurcations of the airways. These signs were not affected by the CAP exposures (Table 4).

Table 4 Summary of histological lung changes due to 2-day filtered air control or exposure to concentrated ambient particulate matter
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No noticeable pathological changes could be observed for either the fCAP or the u+fCAP exposure. Deposition of PM was noted in most of the animals exposed to u+fCAP (52 of 64). This was not observed for animals exposed to fCAP only. Groups of alveolar macrophages were present in nearly all CAP-exposed animals, as in controls.

The lymphocytes in the BALT areas and the perivascular infiltrate of all SH rats were fairly strongly labelled as noted by BrdU incorporation in the DNA, and there was a slight labelling in the alveolar area, which reflects the background turnover. There was slightly more BrdU labelling in all components of those areas of the H&E slides where inflammatory foci were present: an increased proliferation rate in the bronchiolar and alveolar epithelium, as well as in alveolar macrophages. No change of cell proliferation was seen from the labelling-frequency data of nuclei in the control and CAP-exposed groups, and there were no differences between u+fCAP and fCAP groups in this respect (Table 4). The number of foci detected by the immunocytochemical BrdU procedure runs nearly parallel to the observed inflammatory foci with thickened septa in the H&E-stained sections.

Discussion

Although some epidemiological studies suggest that ultrafine particles have serious health effects [32–34], others fail to prove that this PM fraction is more relevant to health than the fine fraction of PM [35, 36], or they fail to separate the effects of ultrafine particles from other air pollutants [37]. The present study focuses on the hypothesis that the ultrafine fraction of PM2.5 dominates the biological responses of rats [32, 38, 39]. Although there are some small differences between repeated studies with fCAP and u+fCAP, these studies do not fully support our hypothesis.

Besides the normal pathological pulmonary characteristics of the SH rat, no differences (including differences in cell proliferation) were observed between the control rats and the fCAP or u+fCAP exposed rats. However, in contrast to the animals exposed to fCAP (in which more than half of the mass consists of sulphate, nitrate, and ammonium), black particles appeared in the alveolar macrophages of the rats exposed to u+fCAP. This indicates that significant amounts of insoluble particles were deposited in the lungs. It is likely that they originated from combustion processes. Since these exposures were carried out next to a busy freeway, a substantial part of the pollution will have been produced by traffic. Most of the biological endpoints were not affected at all, and the biological relevance of markers that were influenced by CAP exposures remains questionable. This is in line with a previous study [27], in which fCAP (1-day exposures) produced little effect in the bronchoalveolar lavage fluid of SH rats, with the exception of an increase of PMNs.

We added two additional parameters for oxidative stress to the present study: MDA as a measure of lipid peroxidation and HO-1 as a measure of antioxidant response. An increase of lipid peroxidation is expected after exposure to air pollution with oxidative capacity, such as pollution by ozone or PM containing polycyclic aromatic hydrocarbon (PAH) and metals. However, exposure to CAP in the present study resulted in either no significant change (fCAP) or a significant decrease (u+fCAP) of MDA levels in bronchiolar lavage fluid. The biological relevance of these observations is questionable, given the smallness of the decline. Inconsistent data regarding both humans and rats have been reported both as increases [40, 41] and decreases [42] of lipid peroxidation after exposure to particles. Where the increase is often seen as a direct result of the oxidative stress, the decrease is assigned to the adaptive capacity of the human organism after prolonged exposure [42].

Exposure to fCAP (after omitting the two highest exposure concentrations) or u+fCAP resulted in a significant increase in HO-1. The enzyme HO-1 is regulated by oxidative stress, catalysing heme oxidation into biliverdin, CO, and iron. The increase results in augmented production of the antioxidant biliverdin and CO, which acts as an anti-inflammatory agent [43]. Indeed, the present study finds no sign of developing inflammation. Various agents, such as endotoxins, cytokines, and heavy metals, as well as CO itself, are known to induce HO-1 [44, 45]. The use of HO-1 as a biologically relevant indicator of PM-induced stress has been exemplified in in vitro studies in which the PAH content derived from airborne PM positively correlates with increased HO-1 expression [46, 29]. It also has been proven that the oxidative potential of CAP in in vitro studies correlate well with HO-1 induction [47]. In vitro studies that use a murine macrophage cell line [47], have shown that ultrafine PM is a more potent inducer of HO-1 and depleter of intracellular glutathione (anti-oxidant) than ultrafine+fine PM. However, the present study gives no clear indications that, per unit mass, u+fCAP has a greater impact on HO-1 or glutathione than fCAP. Although this might occur at higher exposure levels for u+fCAP than were achieved in this study (550 μg/m3), the oxidative stress potency as measured by the HO-1 of ultrafine particles deposited in the lungs may not be significantly greater than that of fine particles.

A statistically significant decrease of WBCs after exposure to fCAP and u+fCAP was noted. There was a concomitant decrease of absolute numbers of neutrophils and lymphocytes. It has previously been reported that these systemic responses, such as a decrease in WBC, are observed 24 h after exposure [25], but not immediately after exposure to CAP [25, 26]. Ghio states that the extravasion of neutrophils from the blood into the lung would account for the time dependency of the decrement of the WBC count, since an inflammatory influx after PM exposure is not immediate, but certainly becomes evident at 24 h [25]. However, others [48] report that haematological changes (increase in blood neutrophils and a decrease in lymphocytes 3 h after exposure of rats to CAP (3 h for 110–350 μg/m3), but these changes were absent at 24 h after exposure. Such an increase in WBC counts purportedly reflects the inflammatory state after inhalation of PM. In a study similar to ours, Kodavanti et al. [15] report that there were no significant changes in haematological parameters 18–20 h after exposure.

In contrast to previous findings [15, 27], we do not observe changes in plasma fibrinogen concentrations as a result of exposure to both u+fCAP and fCAP. The fibrinogen concentration, a risk factor for cardiovascular disease, has been shown to increase after PM exposure in rodent studies [49–51] as well as in human studies [25, 52], although decreases have also been observed [49]. A strain-dependent effect in the increase of fibrinogen has also been observed: the effects seem more dominant in SH rats than in Wistar-Kyoto (WKY) rats. This supports the hypothesis that humans with cardiovascular diseases may be more susceptible to increased pulmonary and cardiac impairments [51, 53]. A significant increase of fibrinogen levels in SH rats (but not WKY rats) exposed to CAPs has been found [15]. Sela et al [54] proved that oxidative stress resulted in increased plasma MDA, fibrinogen, and PMN counts before hypertension developed in the rat. In this respect, the absence of increased serum fibrinogen levels is rather unexpected. Differences in CAP composition might explain these differences.

The significant changes on the haematological indices corpuscular volume (increased MPV and decreased MCV) in combination with unchanged platelet numbers found after exposure to u+fCAP suggests that the ultrafine particles might have effects on the platelet state. These observations are therefore in agreement with the hypothesis that PM can affect haematological indices [55]. It has been observed that a reduction of MPC may be used to detect in vitro platelet activation [56]. However, since the observed differences are very small and opposite in sign, it is questionable whether the changes are biologically relevant.

The fact is that u+fCAP contains less of the soluble inorganic aerosols, sulphates, nitrates, and ammonium than fCAP. Indeed, u+fCAP is very likely to be enriched with carbonaceous (combustion derived) PM since these exposures took place right next to a traffic tunnel. However, except for the black particles in the lung tissue and the changed haematological parameters concerning the platelet state, the effects observed for the fCAP and u+fCAP exposures do not differ.

Studies using concentrated PM are confronted with the fact that air pollution is a complex mixture that varies from day to day. As a consequence, duplication of experiments is virtually impossible. Epidemiological studies have consistently demonstrated that health effects can be predicted with monotonic functions of particle mass concentrations. In turn, CAP studies can be used to verify this relationship under more controlled conditions. In other words, this allows for testing the hypothesis that effects on biological systems due to exposure to PM are always linearly related to the mass concentration. However, the results of the present study indicate that, for example, HO-1 levels show a significant nonlinear relationship with particle mass concentrations. Similar response patterns were seen for CC16 in lavage fluid. In both cases, combined analysis of all experiments did not reveal a statistically significant effect due to CAP exposures. Some other studies report that linear regression shows correlations between a biomarker and the exposure concentrations [27, 18, 28], but the correlations are usually rather poor. Unfortunately, many of the other markers of biological effect in the present study were not affected at all, which precluded a similar analysis. Therefore, analysis of the combined data of multiple CAPs experiments should always consider that nonmonotonic relationships of concentration effects may be better descriptors of physiological processes. The phenomenon of nonmonotonic relationships of concentration effects applies to many biological processes, for example, enzymatic activity as a function of temperature.

The results of the present series of experiments indicate that minor pulmonary and systemic effects are due to exposure to fine and ultrafine+fine particles at concentrations well above ambient levels. No clear CAP mass correlation has been found for these effects based on the assumption that this relation is linear as shown in epidemiological studies. We even provide evidence that effects due to the oxidative potential of PM might be masked at greater than ambient concentrations, so that prudence is called for when sets of exposures of various concentrations are combined in order to increase the group number of observations in a statistical analysis. In addition, this study shows no proof that change of location, resulting in a larger traffic CAP component, results in noteworthy and biological relevant pulmonary or systemic effects.

Materials and methods

Animals

Male SH rats, 11–13 weeks old, were purchased from Charles River Laboratories were assigned to 13 studies (Table 1). Immediately after arrival, the animals were weighed, randomized and then allowed to acclimatize for at least 7 days. The animals were housed in macrolon cages (type III) and fed with SSP-TOX pellets of a cereal-based rodent diet (SMR-A; Hope Farms, Woerden, the Netherlands) and tap water via the automatic drinking-water system, both ad libitum during nonexposure periods. The room temperature was maintained at 22 ± 2°C, the relative humidity at 40–70%, and a 12-h light/dark cycle was maintained.

Each study used eight animals for CAP exposure and eight animals for filtered air exposure (control group). Shortly before exposure, the animals were transported to the mobile exposure laboratory equipped with an ambient particle concentrator, where they were housed in macrolon type III cages, equipped with water bottles. The housing facilities were ventilated with HEPA filters and chemically (activated carbon and purafil) filtered air. Directly after the animals were exposed to CAP or clean air (which was done simultaneously), they were returned to the housing facilities. During exposure, the animals were deprived of water and food.

Study design

A total of 13 studies (which were identical apart from the CAP exposure) were performed at two locations. The SH rats were either exposed to fCAP (five replicate studies located in a city background in Bilthoven = site I) or to u+fCAP (eight replicate studies located in a freeway tunnel near Hendrik Ido Ambacht (HIA; site II)). Each study consisted of a control group of eight animals exposed to HEPA-filtered air, and a group of eight animals exposed to CAP. Exposures lasted 6 h on 2 consecutive days (Figure 1).

Figure 1
figure 1

Schematic representation of the study design. Animals were exposed to concentrated ambient particulate matter on day 1 and 2. Necropsy took place 18 h after exposure. SHR, spontaneously hypertensive rat.

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Generation and characterization of the test atmosphere

To obtain fCAP, ambient PM was generated by drawing ambient air through a size selective inlet that removes particles larger than 2.5 μm and subsequently through a four-stage set-up of the ambient fine particle concentrator (AFPC) [11]. The AFPC operates at an air-intake rate of 5000 l/min, and the output flow for PM is 10 l/min. The size distribution of the ambient aerosol after the air passed the PM2.5 size selective inlet was determined during the exposure period with a multi-orifice-impactor (MOI, MSP, Minneapolis, Minn., USA).

The PM mass concentrations were measured continuously at the inlet (ambient) and once an hour (for 5 min) at the outlet of a concentrator during the exposure with a nephelometer (DATARAM, MIE, Billerica, Mass., USA). The time-integrated mass concentrations were also measured at both the inlet and the outlet by means of collection on two 47-mm filters placed in parallel (polytetrafluoroethylene (PTFE) and Quartz), with sampling at a flow rate of 2 l/min. Ozone, carbon monoxide, sulphur dioxide, nitrogen oxides, and the particle number concentrations were recorded every minute in the ambient air behind the PM2.5 impactor. The size distribution of the concentrated aerosol in the range of 0.15 – 2.5 μm was determined once an hour with an aerodynamic particle sizer for particles greater than 0.5 μm (APS, TSI, St. Paul, Minn., USA).

The u+fCAP exposure atmospheres were generated by drawing ambient air through a modified single-stage set-up of a versatile aerosol concentration enrichment system (VACES) [12, 13]. The design of the VACES is such that particles greater than 2.5 μm are not concentrated. The VACES operates at an air intake flow rate of 500 l/min, and the output flow for PM is 15 l/min. The temperature of the coolers was kept at a constant -4°C. The temperature of the humidifiers was kept between 25°C and 30°C, depending on the ambient air conditions. The size distribution of the concentrated aerosol in the range of 0.01μm -2.5 μm was determined once an hour with an aerodynamic particle sizer (particles >0.5 μm) (APS, TSI, St. Paul, Minn., USA) for the fCAP experiments.

A condensation particle counter (CPC, TSI, St. Paul, Minn., USA) was used to determine the particle number concentrations after the particles had passed through the concentrator. PM was collected on three 47-mm filters (2 × PTFE and 1 × Quartz) placed in parallel at flow rate of 10 l/min. Similar, PM was collected at a flow rate of 1 l/min after the air passed the concentrator. A carbon sampler tube was placed downstream of one of the PTFE filters at the outlet to collect the VOCs. Ozone, carbon monoxide, sulphur dioxide, nitrogen oxides, and the particle number concentrations were recorded every minute in the ambient air upstream of the humidifier impactor. The size distribution of the concentrated aerosol in the range of 0.02 – 2.5 μm was determined once an hour with an aerodynamic particle sizer (for particles >0.5 μm) (APS, TSI, St. Paul, Minn., USA).

Temperature and relative humidity was recorded once every 5 minutes in the exposure chambers and control exposure chambers, as well as in the ambient air during the exposures. A Sartorius MC-5 microbalance (Sartorius, Goettingen, Germany) was used in controlled relative humidity (40 – 45%) and temperature (22 – 24°C) conditions to do the mass measurements, and the PTFE filters were weighed before and after each field test. Laboratory and field blanks were used for quality assurance. We then analysed the PTFE filters by means of ion chromatography to determine the concentrations of particulate sulphate, nitrate, and ammonium ions. The Quartz filters and activated carbon samplers were stored for future use. At this stage, no efforts have been made for chemical characterization of the PM samples since hardly any effect due to CAP exposure was observed.

Exposure chamber

Rats were exposed to the test atmosphere in a nose-only exposure chamber placed inside an inhalation unit, which was lighted with tubular fluorescent lamps. The animals were placed in nose-only tubes (Novoplast Tube T, Münster, Muttenz, Switzerland), restrained, and attached to the exposure chamber. The animals could breathe a continuous supply of test atmosphere during exposure (about 8 l/min). Control groups were exposed to air drawn from a concentrator down stream to the size selective inlet, and a HEPA filter filtered the air to provide a particle-free exposure atmosphere. To minimize stress, the animals were allowed to become accustomed to the tubes for 3 days in advance of the exposure, 1 h each day without exposure to the test atmosphere.

Necropsy

Eighteen hours after exposure, the rats were anaesthetized with Ketamine/Rompun (0.1 ml/100 g body weight of a mix of 0.85 ml 100 mg/ml Ketamine (Aesculaap, Boxtel, The Netherlands) and 0.65 ml of 20 mg/ml Rompun (Bayer, Leverkusen, Germany) and sacrificed by exsanguination via the abdominal aorta. A cannula was inserted in the trachea, and bronchoalveolar lavage fluid (BALF) was taken from the right lung after ligation of the left bronchus. The right lungs were lavaged (three times up and down) with a volume of saline corresponding with 27 ml/kg body weight at 37°C. The fluid recovered from the lavage was placed on ice. The left lung was dissected, weighed, and fixed for 1 h under a constant pressure of 20 cm H2O with 10% phosphate-buffered formalin. Five μm paraplast lung sections were stained with haematoxylin and eosin (H&E) and examined under a light microscope.

Morphometry

To measure cumulative cell proliferation, the animals were injected prior to CAPs exposure and 2 h prior to necropsy with bromodeoxyuridine (BrdU) measured to100 mg/kg body weight (Sigma-Aldrich, Zwijndrecht, The Netherlands). Lung sections from these animals were immunohistochemically stained with anti-BrdU antibody (Boehringer, Mannheim, Germany) and labelled with peroxidase. Since only the inflammatory foci displayed a focally increased proliferation rate, only a semi quantitative labelling score for the size of areas with an increased labelling was assigned. Labelling the frequency in square millimetres of bronchiolar epithelium, for example, makes no sense, as this procedure is fully dependant on how much epithelium is measured both inside and outside an inflammatory focus.

The analySIS soft imaging system (SIS, Münster, Germany) was used to quantify the BrdU-stained cells per millimetre of terminal bronchiolar epithelium. Terminal bronchioles were defined as those bronchioles flowing into alveolar ducts, as well as bronchioles smaller than 250 μm in diameter that are situated in the periphery of the lung and in the close vicinity of a centriacinar area. The total length of examined terminal bronchioles per animal varied between 15 mm and 25 mm.

Bronchoalveolar lavage analyses

The BALF collected from each animal was centrifuged at 400 g and 4°C for 10 min. The cell-free fluid from the lavage was used for biochemical assays. We used a commercial reagent kit (Roche Nederland, Mijdrecht, The Netherlands) to determine the activities of lactate dehydrogenase (LDH), N-acetyl glucosaminidase (NAG), alkaline phosphatase (ALP). The levels of uric acid (UA-B) were determined using a reagent kit obtained from Roche (Almere, the Netherlands) and malondialdehyde (MDA) was determined using a HPLC kit obtained from Chromsystems (Munich, Germany). We determined the total protein levels with a reagent kit obtained from Pierce (Oud-Beijerland, The Netherlands). Methods for the determination of glutathione, both its reduced (GSH) and oxidized (GSSG) forms, and Clara cell secretory protein (CC16) have been described previously [27].

We determined the total cell number by mixing 0.5 ml of the cell suspension with 9.5 ml of Isoton II (Beckman Coulter, Mijdrecht, The Netherlands) and then counting them in a Coulter Counter Z1 and Z2 (Beckman Coulter, Mijdrecht, The Netherlands). For differential cell counts, cytospin preparations were made and stained with the May-Grünwald and Giemsa method. Each cytospin preparation counted 400 cells, and the proportion of each cell type (macrophages, neutrophilic granulocytes, eosinophilic granulocytes, and lymphocytes) was calculated on the basis of total cells per BALF sample.

Blood analysis

Fibrinogen was determined as a risk factor for thrombotic vascular disorder and von Willibrand factor (vWf) as a marker for early endothelial injury, both as previously described [27].

Cell differentials were determined in ethylenediaminetetraacetic acid (EDTA; Terumo Europe, Leuven, Belgium), and anticoagulated blood was analysed in an H1-E Multi Species Haematology Analyser (Bayer, Mijdrecht, The Netherlands). The following parameters were measured: white blood cell (WBC) and red blood cell (RBC) concentrations, haemoglobin (HGB) and platelet concentrations (PLT), the mean platelet volume (MPV), and the haematocrit value (HCT). The mean corpuscular volume (MCV), mean platelet component (MPC), mean cell haemoglobin (MCH), mean cell haemoglobin concentration (MCHC), red blood cell distribution width (RDW) and haemoglobin distribution width (HDW) are also provided.

Statistical analysis

All effect parameters were log-transformed before two-way analysis of variance (ANOVA) was performed. Log-transformation is used to account for the increased variation in groups of animals exposed to CAPs versus the animals that were sham exposed. Two-way ANOVA techniques (simple factorial) were used to assess differences due to the factors "CAP exposure", "day-to-day variation" and their interaction while treating "CAP exposure" as a binary term. For those biological parameters that showed a significant effect of "CAP exposure" factor between control animals and CAP-exposed animals, the binary exposure factor was replaced by particle mass CAP as a continuous grouping factor, after which another two-way ANOVA and univariate regression analysis were performed. S-Plus software was used for all statistical analyses. The criterion for significance was set at p < 0.05.