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Logo of nihpaAbout Author manuscriptsSubmit a manuscriptHHS Public Access; Author Manuscript; Accepted for publication in peer reviewed journal;
 
Toxicol Appl Pharmacol. Author manuscript; available in PMC 2011 May 26.
Published in final edited form as:
PMCID: PMC3102559
NIHMSID: NIHMS210916

Pulmonary effects of inhaled diesel exhaust in aged mice

Abstract

Pulmonary morbidity and mortality resulting from exposure to fine particulate matter (PM) increases with age. The present studies analyzed potential mechanisms underlying increased susceptibility of the elderly to PM using diesel exhaust (DE) as a model. Mice (2 m and 18 m) were exposed to DE (0, 300, and 1000 μg/m3) for 3 h once (single) or 3 h/day for 3 days (repeated). Bronchoalveolar lavage fluid (BAL), serum and lung tissue were collected 0 and 24 h later. Exposure to DE resulted in structural alterations in the lungs of older but not younger mice, including patchy thickening of the alveolar septa and inflammatory cell localization in alveolar spaces. These effects were most pronounced 24 h after a single exposure to the higher dose of DE. Significant increases in BAL nitrogen oxides were also noted in older mice, as well as expression of lipocalin 24p3, an oxidative stress marker in the lung with no effects in younger mice. Following DE inhalation, expression of Tumor Necrosis Factor alpha (TNFα) was upregulated in lungs of both younger and older mice; however, this was attenuated in older animals. Whereas exposure to DE resulted in increases in lung Interleukin-6 (IL-6) expression in both older and younger mice, IL-8 increased only in older animals. In younger mice, constitutive expression of manganese superoxide dismutase (MnSOD) decreased after DE exposure, while in older mice, constitutive MnSOD was not detectable and DE had no effect on expression of this antioxidant. Taken together, these results suggest that altered generation of inflammatory mediators and MnSOD may contribute to increased susceptibility of older mice to inhaled DE.

Keywords: Diesel exhaust, Aging, Lipocalin, Nitrogen oxides, Antioxidants

Introduction

Epidemiologic studies have demonstrated strong associations between increases in hourly or daily levels of air pollution and pulmonary morbidity and mortality (Dockery et al., 1992; Samet et al., 2000; USEPA, 2004). Of particular concern as a potential causal agent is ambient fine particulate matter (PM2.5; particles smaller than 2.5 μm in diameter). A significant source of fine PM in the atmosphere is DE which consists of a mixture of compounds in the gas and particle phases (Schlesinger, 2007). DE particles typically contain a carbon core that adsorbs many organic compounds including polycyclic aromatic and nitroaromatic hydrocarbons, heterocyclics, aldehydes, quinones and pyrenes (Schuetzle et al., 1981). These compounds stimulate both macrophages and bronchial epithelial cells to generate reactive oxygen species and proinflammatory cytokines (Hiura et al., 1999; Li et al., 2002). Exposure of humans and experimental animals to DE has been reported to cause airway inflammation, decrease lung function and aggravate asthma and chronic bronchitis (Salvi et al., 1999; Sydbom et al., 2001). Increased morbidity and mortality in individuals with existing cardiopulmonary disease have also been described (www.epa.gov/particles/health.html, 2008).

One of the most sensitive populations to the adverse health effects of inhaled PM is the elderly, typically individuals over 65 years of age. Aging is associated with deterioration of both innate and adaptive immunity (Kumar and Burns, 2008; Suvas, 2008). Most notable changes include age-related deficits in macrophage and neutrophil activity which are thought to underlie increased susceptibility of the elderly to respiratory infections (Liu and Kimura, 2007; Aprahamian et al., 2008; Murciano et al., 2008). Alterations in lung permeability and mechanics have also been described in elderly humans and rodents (Tankersley et al., 2003; Pride, 2005). These changes may also contribute to the increased sensitivity of older individuals to the adverse effects of inhaled pollutants.

As oxidative stress appears to be a common mechanism underlying the biological effects of PM and other air pollutants, a particularly important contributory factor may be age-related alterations in lung antioxidants and intracellular oxidative stress (Kelly et al., 2003). These include reduced levels of superoxide dismutase (SOD), vitamin C and dysregulation of vitamin B12 and folic acid metabolism in the lung (Ischiropoulos et al., 1990; van der Loo et al., 2003; Wolters et al., 2004). Aging is also associated with aberrant generation of reactive oxygen and nitrogen species by macrophages resulting in oxidative/nitrosative stress (Tasat et al., 2003). In the present studies, we compared the effects of inhaled DE in older and younger mice. We speculated that age-related decreases in antioxidant defense and alterations in production of inflammatory mediators contribute to the increased susceptibility of older animals to DE.

Materials and methods

Exposure system

A Yanmar, Model YDG 5500EE, 5.5 Kw, 406 cc, one-cylinder, two cycle, diesel-powered electrical generator was used as a source of diesel emissions. The generator was operated using premium low sulfur (<500 ppm; Petro, Inc.) diesel fuel and 40-weight motor oil (Proline HD40). A fraction of the total DE emissions was directed into the delivery system, where it was aged and diluted with HEPA-filtered air and then isokinetically drawn into the exposure chamber. The DE mass concentration in the delivery system and in the exposure chamber was controlled by adjusting the fraction of total DE directed into the system and the amount of dilution air. The flow of DE through the exposure chamber was maintained at 5 l/min by a pump downstream of the chamber. The engine was operated for 15–20 min before beginning animal exposure sessions to ensure that the aerosol mass concentrations were stable.

Exposure characterization

Particle mass concentrations in the chamber were measured in real-time by a SidePak personal aerosol mass monitor (TSI, Inc., Shoreview, MN), which was calibrated against gravimetric (filter) measurements of the DE. Particle number and volume distributions from 13 nm to 20 μm were determined using a Scanning Mobility Particle Sizer (SMPS) connected to a butanol-based condensation particle counter (CPC 3025A, TSI, Inc.) and an Aerodynamic Particle Sizer (APS) (TSI, Inc.). Data from the SMPS and the APS were combined using Data Merge Software Module (TSI, Inc.). Total particle number for each mass concentration was measured using stand-alone CPC 3025A which detects particles between 3 nm and 3 μm. Levels of co-pollutant gases (e.g., NO/NO2 and CO/CO2) were assessed using an IAQ RAE gas monitor with multi-gas sensors (RAE Systems). Particle number distribution measurements were made inside the delivery system (exhaust pipe from which diesel is drawn into the chamber) and inside the animal exposure chamber for both DE mass concentrations (300 and 1000 μg/m3). Characterization of DE particle size distribution and measurements of co-pollutant gases were performed prior to animal exposures while mass concentration measurements were made both prior to and during the animal exposures.

Animals and exposures

Young (2 m; average weight, 24 g; Harlan, Indianapolis, IN) and old (18 m; average weight, 41 g; National Institute of Aging, Bethesda, MD) CB6F1 male mice were used. Animals were housed in microisolator cages and maintained on sterile food (Picolab Rodent Diet 20, Fisher Scientific, Pittsburgh, PA) and pyrogen-free water ad libitum. Mice were randomly assigned to treatment groups. All animals received humane care in compliance with the institution's guidelines, as outlined in the Guide for the Care and Use of Laboratory Animals, published by the National Institutes of Health. Animals were exposed to ultra-pure air (Messer Gas, Allentown, PA), 300 or 1000 μg/m3 DE (as PM2.5) in a 17-l whole body plexiglass divided enclosure (16″l×8″w×8″h) for 3 h one time (single) or 3 h per day on 3 consecutive days (repeated).

Sample collection

Animals were euthanized immediately (0 h) or 24 h after exposure. The 0-h time point was selected for evaluation of inflammatory alterations that occur immediately after exposure, while the 24-h time point assessed the persistence of early inflammatory changes and the appearance of later pro-inflammatory and early repair markers. Animals were killed by Nembutal (200 mg/kg, i.p.) and blood was collected by cardiac puncture. Serum samples were centrifuged (1000×g, 10 min, 4 °C), aliquoted and stored at −80 °C. The thoracic cavity was then opened and the trachea and lungs were exposed. The largest lobe was clamped at the bronchus and reserved for histology, immunohistochemistry and RNA analysis (see below). The remaining lobes were lavaged three times through the trachea with 1 ml sterile, pyrogen-free, ice-cold phosphate buffered saline (PBS). The lavage fluid was transferred to tubes containing 5 mM diethylene triamine penta acetic acid (DTPA), centrifuged (300×g, 8 min, 4 °C) and supernatants were analyzed for protein content. Cell pellets were resuspended in 50 μl of PBS. Samples (10 μl) were stained with trypan blue for measurement of cell number and viability using a hemocytometer. Differential cell counts were determined microscopically on cytospin preparations of Giemsa stained cells. For all treatment groups, greater than 98% of the cells were identified as alveolar macrophages and 1–2% as lymphocytes.

For RNA analysis, the largest lobe was removed and stored at −80 °C in tubes containing 200 μl RNALater (Sigma-Aldrich Corp., St. Louis, MO). For histological analysis and immunohistochemistry, the lobe was instilled with 3% cold paraformaldehyde in PBS, removed and placed on ice for 4 h. Samples were then transferred to 50% ethanol.

Measurement of BAL protein and LDH (lactate dehydrogenase) activity

Total protein content was quantified in cell-free BAL using a BCA Protein Assay kit (Pierce Biotechnologies, Inc., Rockford, IL) with bovine serum albumin (BSA) as the standard. Samples (10 μl) were analyzed in triplicate at 540 nm. LDH activity was determined using the CytoTox 96 non-radioactive cytotoxicity assay kit from Promega Corporation (Madison, WI). BAL samples (50 μl) were analyzed in triplicate at 490 nm. Data were normalized to the volume of BAL collected. Samples from five to six animals per treatment group were assayed.

Histology and immunohistochemistry

Histological sections (4 μm) were stained with hematoxylin and eosin. Specimens were analyzed by light microscopy using ProgRes Capture Pro v2.5 software. The extent of inflammatory changes including macrophage and neutrophil localization, alterations in alveolar epithelial barriers and edema were assessed blindly by a board certified veterinary pathologist (S.R.). For immunohistochemistry, tissue sections were deparaffinized, blocked in 100% serum (room temperature, 3–4h) and incubated overnight at 4 °C with rabbit IgG or anti-MnSOD antibody (1:400; Stressgen Biotechnologies, Inc., San Diego, CA.), followed by 30-min incubation with biotinylated secondary antibody (Vector Labs, Burlingame, CA). Binding was visualized using a Peroxidase Substrate Kit DAB (Vector Labs). For both histology and immunohistochemistry, three mice per treatment group were analyzed.

Measurement of serum TNFα

TNFα levels in serum were quantified using a Quantikine immunoassay kit from R&D Systems (Minneapolis, MN). Serum samples were diluted 2-fold and analyzed at 450 and 540 nm in duplicate in 96-well plates. A standard curve was generated using a four parametric logistic (4-PL SoftMax Pro v4 software, R&D Systems) curve fit. Samples from two to four animals per treatment group were assayed.

Measurements of nitrogen oxides (NOx)

NOx levels in BAL samples were analyzed using an Ionics/Sievers Nitric Oxide Analyzer 280 (NOA 280) as previously described (Atochina et al., 2004). Samples were treated with an excess of vanadium chloride in 1 M HCl (0.4 g/50 ml) at 95 °C to reduce nitrate, nitrite and S-nitrosothiols (SNO) and to release nitric oxide. Sodium nitrate (Sigma Aldrich, St. Louis, MO) was used as a standard. Samples from three to six animals per treatment group were assayed in duplicate. Data were normalized to the volume of BAL collected.

Real-time quantitative polymerase chain reaction (RQ-PCR)

Total mRNA was extracted from tissue samples using an RNeasy Mini kit (Qiagen, Valencia, CA). RNA was reverse-transcribed using a High Capacity cDNA Reverse Transcription kit (Applied Biosystems, Foster City, CA) according to the manufacturer's protocol. Standard curves were generated using serial dilutions from pooled cDNA samples. Real-time PCR was performed using SYBR Green PCR Master Mix (Applied Biosystems, Foster City, CA) on a 7900HT thermocycler according to the manufacturer's protocol. All PCR primers were generated using Primer Express 3.0 software (Applied Biosystems). Samples from two to three animals per treatment group were analyzed and presented relative to GAPDH mRNA expression. Forward and reverse primer sequences were as follows: 24p3, AGG AAC GTT TCA CCC GCT TT, TGT TGT CGT CCT TGA GGC C; TNFα, AGG GAT GAG AAG TTC CCA AAT G, TGT GAG GGT CTG GCG CAT A; IL-6, CCA CGG CCT TCC CTA CTT C, GTT GGG AGT GGT ATC CTC TGT GA; IL-8: CAG CTG CCT TAA CCC CAT CA, CTT GAG AAG TCC ATG GCG AAA; and GAPDH, TGA AGC AGG CAT CTG AGG G, CGA AGG TGG AAG AGT GGG AG.

Statistical analysis

Data were analyzed in consultation with Rutgers University Department of Statistics using two-way ANOVA or unpaired t-test (unequal variances). A p-value of <0.05 was considered statistically significant. Changes in gene expression >2-fold were considered biologically significant.

Results

Aerosol characterization

Two different DE mass concentrations (300 and 1000 μg/m3) were used in these studies. Data obtained by the SMPS and APS particle sizers inside the animal chamber revealed that there were no significant differences in the particle number or volume distributions between these two mass concentrations (Table 1 and Fig. 1). The number and mass median diameters were approximately 240 and 450 nm, respectively. The mass size distribution showed a distinct size mode peaking at ~350 nm accounting for most of the particle mass, with an extended tail indicating the presence of larger particles presumably formed through coagulation (Fig. 1). For both particle mass concentrations (300 and 1000 μg/m3), the coefficient of variation over the 3-h exposure period was ≤15%, demonstrating that the aerosol concentration was stable. According to the particle volume distribution data, the median mass diameter was 487 and 411 nm, and the mean mass diameter was approximately 2200 and 1676 nm, for the 300 and the 1000 μg/m3 mass concentrations, respectively (Fig. 1).

Fig. 1
Particle number (upper panel) and particle volume (lower panel) distribution inside the exposure chamber. Measurements (n = 3) were made at 300 and 1000 μg/m3 using an SMPS and a butanol-based CPC and APS. One representative sample at each mass ...
TABLE 1
Characteristics of DE.

Particle number, NOx and COx concentrations were greater for the 1000 μg/m3 exposures, relative to the 300 μg/m3 exposures (Table 1). Thus, the particle number concentration was approximately 3-fold greater at the 1000 μg/m3 mass concentration. As the PM mass concentration increased from 300 to 1000 μg/m3, the concentration of NOx (NO + NO2) increased by a factor of 3.3, from 4.32 to 14.47 ppm (Table 1). Increases in COx (CO + CO2) concentrations were also noted as the PM mass concentration increased from 300 to 1000 μg/m3. This is likely due to the fact that a larger fraction of the primary DE was directed into the delivery system to achieve the desired 1000 μg/m3 mass concentration when compared to the 300 μg/m3 concentration and not to contaminants in the dilution air. In the dilution air, CO levels were <1 ppm, CO2 levels were approximately 350 ppm, and NO/NO2 levels were <0.02 ppm (data not shown).

Effects of DE on lung histology

A single exposure of younger mice to DE had no major effects on lung histology (Fig. 2A). In contrast, in older animals, an increase in neutrophils was noted in the lung immediately after low dose (300 μg/m3) exposure, which became more discernable after 24 h. At the higher DE concentration (1000 μg/m3), inflammatory changes were even more pronounced and included greater numbers of neutrophils in the lung and focal inflammatory infiltrates consisting predominantly of plasma cells and macrophages (Fig. 2A). Structural changes were also noted in older but not younger animals, immediately after repeated exposure to DE. At the lower dose, these consisted of patchy thickening of alveolar septa, cytomegaly in alveolar septal walls and an increase in the number of macrophages in alveolar spaces (Fig. 2B). By 24-h post-exposure, focal thickening of alveolar septal walls and increased numbers of neutrophils and erythrocytes were also evident in alveolar walls and capillaries. These effects were more prominent at the higher dose of DE immediately after repeated exposure and, as observed after a single DE exposure, included increased numbers of neutrophils in the lung and focal infiltrates consisting of plasma cells and macrophages.

Fig. 2
Effects of DE exposure on lung histology. Lung sections (4 μm), prepared from younger (2 m) and older (18 m) mice immediately (0 h) and 24 h after a single (upper panel) or repeated (lower panel) exposure to air (0 μg/m3) or DE (300 or ...

Effects of DE on markers of lung injury and oxidative stress

A 2-fold increase in BAL cell number was observed in younger mice 24 h after repeated exposure to high dose DE (Fig. 3). Repeated exposure of younger mice to DE also resulted in a significant increase in BAL protein levels (Fig. 4) as well as LDH activity (Fig. 5). In contrast, in older animals, a small but significant decrease in cell number was observed 24 h after exposure to DE, while no significant changes were noted in BAL protein or LDH activity. In older animals, exposure to DE resulted in an increase in NOx levels in BAL (Fig. 6). Although increases in BAL NOx were also noted in younger animals, this was significant only after a single exposure to the lower DE concentration.

Fig. 3
Effects of DE on BAL cell number. BAL fluid was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m3). Viable ...
Fig. 4
Effects of DE on BAL protein content. BAL fluid was collected immediately (0 h) or 24 hafter a single (upper panel) or repeated (lower panel) exposure of younger (2m) and older (18m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m3) and ...
Fig. 5
Effects of DE on BAL LDH activity. BAL fluid was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m3) and ...
Fig. 6
Effects of DE on BAL nitrogen oxides. BAL fluid was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m3) and ...

Acute phase proteins such as lipocalin 24p3 are rapidly produced in response to oxidative stress and tissue injury (Roudkenar et al., 2007). 24p3 mRNA expression was upregulated in the lung after both single and repeated exposure of older, but not younger mice to DE (Fig. 7). These effects were dose related and persisted for 24 h.

Fig. 7
Effects of DE on lipocalin 24p3 mRNA expression. Lung tissue was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m ...

Effects of DE on production of inflammatory mediators

TNFα is a pro-inflammatory cytokine implicated in tissue injury and repair (Lehmann et al., 2005; Gosselin and Rivest, 2007). Exposure of younger mice to a single low dose of DE resulted in a 5-fold increase in lung TNFα which was noted after 24 h (Fig. 8). DE exposure also resulted in increased lung TNFα expression in older mice; however, this response was significantly attenuated relative to younger animals. In contrast, an increase in serum TNFα was observed following a single DE exposure in older mice, which persisted for 24 h, while no effects were noted in younger animals (Fig. 9). In general repeated exposure of the mice to DE had no major effect on TNFα mRNA expression in the lung or on TNFα levels in serum.

Fig. 8
Effects of DE on TNFα expression. Lung tissue was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m ...
Fig. 9
Effects of DE on serum TNFα. Serum was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m3). TNFα ...

Significant increases in IL-6 and IL-8 mRNA expression were also observed in the lungs of older animals after exposure to DE. The effects of DE were dose related and persisted for 24 h (Fig. 10). Although IL-6 was also upregulated in younger mice, only a small increase in IL-8 mRNA expression was detected in these mice following a single exposure to low dose DE. Generally similar results were observed after repeated exposure to DE.

Fig. 10
Effects of DE on IL-6 and IL-8 mRNA expression. Lung tissue was collected immediately (0 h) or 24 h after a single (upper panel) or repeated (lower panel) exposure of younger (2 m) and older (18 m) mice to air (0 μg/m3) or DE (300 or 1000 μg/m ...

Effects of DE on MnSOD expression

Immunohistochemical analysis of lung sections revealed significant staining for MnSOD in younger but not older mice (Fig. 11A). This was most prominent in alveolar macrophages. Exposure to DE (single or repeated) resulted in a persistent decrease in MnSOD expression in younger animals, while levels remained undetectable in older animals (Figs. 11A and B).

Fig. 11
Effects of DE exposure on MnSOD expression. Lung sections (4 μm), prepared from younger (2 m) and older (18 m) mice immediately (0 h) and 24 h after a single (upper panel) or repeated (lower panel) exposure to air (0 μg/m3) or DE (300 ...

Discussion

The mechanisms underlying increases in the susceptibility of the elderly to the adverse effects of inhaled air pollutants are unknown. Innate immune system functioning declines with advancing age and this may contribute to xenobiotic-induced hyperresponsiveness. Altered oxidant/antioxidant balance may also be a key factor. To evaluate these possibilities, we compared inflammatory mediator and antioxidant expression in lungs of younger and older mice following exposure to inhaled DE.

Exposure of older but not younger mice to DE was associated with rapid and progressive morphological and structural alterations in the lung, which included neutrophil and macrophage accumulation in the tissue, focal cellular infiltrates of plasma cells and macrophages in the interstitum and patchy thickening of alveolar septa. These findings are consistent with previous reports of morphological and structural changes in lungs of older rodents and humans exposed to PM (Tankersley et al., 2003; Sunil et al., 2007a; Tsagareli et al., 2008) and confirm that aging is associated with increased sensitivity to PM-induced lung injury.

An accumulation of protein and inflammatory cells in BAL fluid and an increase in LDH activity have been used as markers of injury to the lower lung (Bhalla, 1999). Despite pronounced structural and histologic evidence of lung pathology in older mice after exposure to DE, no significant changes were noted in BAL protein or LDH activity. This suggests that these measures are not sensitive indicators of lung injury in the elderly. Alternatively, DE-induced injury may not be prominent in the lower lung of older mice. Interestingly, in older mice, BAL cell number was reduced 24 h following single or repeated exposure to DE. This is most likely due to increased adherence of inflammatory cells to alveolar epithelium, which is consistent with our histologic findings. In younger animals, increases in BAL cell number and protein were detected after single or repeated exposure to DE, whereas BAL LDH activity increased only after repeated exposure. However, no major structural alterations were noted in the lung of younger mice. These findings further indicate the limitations in the use of BAL protein and cell number as general markers of acute lung injury.

Nitric oxide possesses complex redox chemistry and is capable of forming a variety of cytotoxic reactive nitrogen species which are thought to contribute to lung pathology and disease (Dweik et al., 2001; Ricciardolo et al., 2006). At higher DE concentrations, biological effects may also be induced by the interaction between particles and co-pollutant gases, which are present at higher levels. The present studies demonstrate significantly greater levels of NOx in BAL from older animals following exposure to DE (single or repeated) relative to younger mice, providing additional evidence that elderly mice are more susceptible to adverse pulmonary effect of inhaled DE. NOx has been implicated in the pathogenesis of acute respiratory distress syndrome and bronchopulmonary dysplasia in animal models of lung injury (Linke et al., 2001; Haczku et al., 2002), and they may play a similar role in the increased responsiveness of elderly mice to inhaled DE.

Lipocalin 24p3 (Lcn2, NGAL) was originally identified as a liver-derived acute phase protein produced in response to hepatic injury (Liu and Nilsen-Hamilton, 1995). More recent studies have shown that 24p3 is upregulated in a number of tissues including the lung and kidney following injury, as well as in diseases such as colorectal and pancreatic cancer and inflammatory bowel disease (Nielsen et al., 1996; Missiaglia et al., 2004; Mishra et al., 2006; Roudkenar et al., 2007; Sunil et al., 2007b). It has also been suggested that 24p3 is important in the response of cells and tissues to oxidative stress (Roudkenar et al., 2007). We found that exposure of older, but not younger mice to DE, was associated with a rapid induction in 24p3 mRNA expression in the lung. cDNA microarray studies revealed a similar upregulation of 24p3 after exposure of mice to the combination of DE and lipopolysaccharide (Yanagisawa et al., 2004). Our findings that in older mice 24p3 is upregulated after exposure to DE alone suggest that this may be a highly sensitive biomarker of early oxidative stress in the elderly.

TNFα is a macrophage-derived cytokine implicated in the pathogenesis of lung injury induced by a number of air pollutants (Kelley, 1990; Schins and Borm, 1999; Fakhrzadeh et al., 2004; Gowdy et al., 2008). Recent studies suggest that TNFα plays a dual role in the pathogenic response, initially promoting inflammation and cytotoxicity and subsequently initiating tissue repair (Lehmann et al., 2005; Gosselin and Rivest, 2007). This latter activity is thought to be due to TNFα-induced upregulation of antioxidants, stimulation of epithelial cell proliferation and extracellular matrix turnover (Sasaki et al., 2000; Ryter et al., 2002; Chiu et al., 2003). In accord with previous studies (Saber et al., 2006; Gowdy et al., 2008), we observed a significant increase in expression of TNFα in the lung 24 h after a single exposure of younger mice to DE. Interestingly, this response was most notable at the lower DE dose. It may be that higher doses of DE cause suppression of inflammatory responses in the lung of younger mice (Yin et al., 2002). Although TNFα expression was also increased in lungs of older animals 24 h following a single exposure to DE, this response was attenuated relative to younger mice. A similar attenuation of TNFα production in lung or BAL fluid has previously been described in older animals after induction of endotoxin shock and after exposure to silica or terpene oxidation products (Corsini et al., 2004; Ito et al., 2007; Sunil et al., 2007a). Age-related decreases in production of TNFα have also been described in isolated monocytes and macrophages (Lloberas and Celada, 2002; Boehmer et al., 2004). After a single DE exposure, serum TNFα levels were increased significantly, but only in older mice. The origin of TNFα in serum is unknown and may reflect its rapid release in the lung following DE exposure. Alternatively, TNFα may be released by extra-pulmonary tissues responding to DE-induced oxidative stress and this remains to be determined.

IL-6 and IL-8 are known to be important in regulating inflammatory cell trafficking into injured tissues (Murtaugh et al., 1996; McClintock et al., 2008). Previous studies have reported DE-induced increases in IL-6 and IL-8 in cultured bronchial epithelial cells (Steerenberg et al., 1998). Similarly, we noted significant increases in IL-6 and IL-8 mRNA expression in lungs of younger and older animals after exposure to DE (single or repeated). Whereas the kinetics of IL-6 mRNA expression appeared to be independent of age, IL-8 expression increased in older animals immediately after DE exposure. These findings are consistent with reports of increased production of IL-8 and IL-8-like cytokines (e.g., MIP-2) with advancing age in rodents and humans (Himi et al., 1997; Pulsatelli et al., 2000). IL-8 is a potent chemoattractant for neutrophils (Matsuzaki et al., 2006). Our findings of increased expression of IL-8 in older mice following exposure to DE are consistent with our histologic data of increased accumulation of neutrophils in the lungs and with increased levels of NOx in BAL of these animals.

Antioxidants play a critical role in host defense by scavenging and detoxifying oxidants (Heffner and Repine, 1991; Lang et al., 2002). With increasing age, constitutive levels of tissue antioxidants and the capacity to respond to oxidative stress decline (Lykkesfeldt and Ames, 1999; Squier, 2001; Servais et al., 2005). Thus, while expression of antioxidant enzymes, such as SOD, rapidly decreases in younger animals as it is utilized following exposure to PM, in older mice this response is reduced or absent (Sagai et al., 1993; Sunil et al., 2007a). We found that MnSOD was constitutively expressed in lungs of younger animals, predominantly in alveolar macrophages. Moreover, exposure of younger animals to DE resulted in a rapid reduction in MnSOD expression. In contrast, constitutive expression of MnSOD was not evident in lungs of older mice and DE exposure did not alter its expression. It has been suggested that oxidative stress is a key mechanism underlying the adverse health effects of ambient PM (Li et al., 2004). A lack of constitutive MnSOD in the lung of older mice may contribute to their increased susceptibility to lung injury induced by inhaled DE.

In summary, the present studies demonstrate that single or repeated inhalation of DE results in significant structural and inflammatory changes in the lungs of older but not younger mice. However, no consistent differences were noted between the two exposure protocols, suggesting that the impact of diesel is rapid. Alternatively, more prolonged exposures may be required for differences in the effects of single and repeated DE exposures to be observed. It should be noted that the exposure doses used in our studies are relevant to human exposure in occupational and environmental settings (USEPA, 2002). Occupational exposures to DE can exceed 1000 μg/m3, and levels of PM in the world's largest cities have been shown to exceed 300 μg/m3 (WHO, 1992; USEPA, 2002). The data presented in our studies showing altered production of inflammatory mediators and reduced MnSOD in lungs of older mice suggest a potential mechanism for the increased susceptibility of the elderly to inhaled PM. However, at present we cannot exclude the possibility that some of these biological effects are due to different levels of NOx and COx in the DE. Identification of key inflammatory mediators involved in the response of older mice to DE may help in the design of new and effective approaches to mitigating pulmonary pathology in the geriatric population.

Acknowledgments

The authors acknowledge the help of Dr. Jianzhong Song, Ph.D. (Visiting Scholar, Department of Environmental Science, Rutgers University). This work was supported by grants from the Health Effects Institute, the American Lung Association of New Jersey, the USEPA and NIH Grants ES004738, ES013520, ES005022, GM034310, CA132624 and AR055073.

Footnotes

Conflict of interest statement

The authors declare that there are no conflicts of interest.

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