Skip to content
EHP Banner Ad

Environmental Health Perspectives

Facebook Page EHP Twitter Feed Open Access icon  

Research Articles August 2009 | Volume 117 | Issue 8

Email this to someoneShare on FacebookTweet about this on TwitterShare on LinkedInShare on Google+Share on StumbleUpon
Environ Health Perspect; DOI:10.1289/ehp.0900541

Autonomic Effects of Controlled Fine Particulate Exposure in Young Healthy Adults: Effect Modification by Ozone

Asghar A. Fakhri,1 Ljubomir M. Ilic,1,2 Gregory A. Wellenius,1 Bruce Urch,3,4 Frances Silverman,3,5 Diane R. Gold,6,7 and Murray A. Mittleman1,7

Author Affiliations open
1Cardiovascular Epidemiology Research Unit; Department of Medicine, Beth Israel Deaconess Medical Center, Harvard Medical School, Boston, Massachusetts, USA; 2Department of Medicine; Mount Auburn Hospital, Cambridge, Massachusetts, USA; 3Gage Occupational and Environmental Health Unit; St. Michael’s Hospital, Toronto, Ontario, Canada; 4Institute of Medical Science and 5Dalla Lana School of Public Health and Department of Medicine; University of Toronto, Toronto, Ontario, Canada; 6Channing Laboratory; Department of Medicine, Brigham and Women’s Hospital, Harvard Medical School, Boston, Massachusetts, USA; 7Department of Epidemiology; Harvard School of Public Health, Boston, Massachusetts, USA

PDF icon PDF Version (602 KB)

  • Background:

    Human controlled-exposure studies have assessed the impact of ambient fine particulate matter on cardiac autonomic function measured by heart rate variability (HRV), but whether these effects are modified by concomitant ozone exposure remains unknown.


    In this study we assessed the impact of O3 and particulate matter exposure on HRV in humans.


    In a crossover design, 50 subjects (19–48 years of age) were randomized to 2-hr controlled exposures to filtered air (FA), concentrated ambient particles (CAPs), O3, or combined CAPs and ozone (CAPs + O3). The primary end point was change in HRV between the start and end of exposure. Secondary analyses included blood pressure (BP) responses, and effect modification by asthmatic status.


    Achieved mean CAPs and O3 exposure concentrations were 121.6 ± 48.0 μg/m3 and 113.9 ± 6.6 ppb, respectively. In a categorical analysis, exposure had no consistent effect on HRV indices. However, the dose–response relationship between CAPs mass concentration and HRV indices seemed to vary depending on the presence of O3. This heterogeneity was statistically significant for the low-frequency component of HRV (p = 0.02) and approached significance for the high-frequency component and time-domain measures of HRV. Exposure to CAPs + O3 increased diastolic BP by 2.0 mmHg (SE, 1.2; p = 0.02). No other statistically significant changes in BP were observed. Asthmatic status did not modify these effects.


    The potentiation by O3 of CAPs effects on diastolic BP and possibly HRV is of small magnitude in young adults. Further studies are needed to assess potential effects in more vulnerable populations.

  • Citation: Fakhri AA, Ilic LM, Wellenius GA, Urch B, Silverman F, Gold DR, Mittleman MA. 2009. Autonomic Effects of Controlled Fine Particulate Exposure in Young Healthy Adults: Effect Modification by Ozone. Environ Health Perspect 117:1287–1292;

    Address correspondence to M.A. Mittleman, Cardiovascular Epidemiology Research Unit, Cardiovascular Division, Beth Israel Deaconess Medical Center, 330 Brookline Ave., MASCO 4th Floor, Boston, MA 02215 USA. Telephone: (617) 632-7694. Fax: (617) 632-7698. E-mail:

    The authors declare they have no competing financial interests.

    This research was supported in part by grants ES013804 and ES009825 from the National Institute of Environmental Health Sciences, National Institutes of Health, and R827353 and R832416 from the U.S. Environmental Protection Agency.

    Received: 5 January 2009
    Accepted: 23 April 2009
    Advance Publication: 24 April 2009
    Final Publication: 1 August 2009

Ambient air pollution has gained recognition as an important source of cardiovascular morbidity and mortality (Brook et al. 2004; Dockery et al. 1993; Pope et al. 1995). In addition to long-term mortality, daily fluctuations in fine particles [particulate matter with median aerodynamic diameter < 2.5 μm (PM2.5)] and ozone have been linked to short-term cardiovascular and pulmonary mortality (Bell et al. 2004; Brook et al. 2004; Dominici et al. 2006). Studies in subjects with implanted cardioverter defibrillators demonstrating an association between PM2.5 elevation and increased incidence of ventricular arrhythmias and rapid atrial fibrillation suggest autonomic dysregulation as a putative pathway to these clinical end points (Dockery et al. 2005; Peters et al. 2000; Rich et al. 2006). The role of PM2.5-mediated autonomic dysregulation has been explored using heart rate variability (HRV) as a surrogate for autonomic tone (Task Force of the European Society of Cardiology 1996) in epidemiologic studies (Creason et al. 2001; Gold et al. 2000; Liao et al. 1999; Magari et al. 2001), animal studies (Godleski et al. 2000), and human experimental studies (Devlin et al. 2003; Gong et al. 2003). Yet there is still a scarcity of knowledge about health effects of potential synergy between PM2.5 and ambient gaseous copollutants (National Research Council 2004). Of these copollutants, O3 interaction is of particular interest given its possible role in local oxidation, creation of free radicals, and potentiation of pollutant deposition onto surfaces (Finlayson-Pitts and Pitts 1997; Meng et al. 1997).

To assess whether the association between particulate exposure and autonomic function is altered by concomitant O3, we conducted a randomized, single-blind, crossover study, with subjects undergoing exposure to concentrated ambient particles (CAPs), O3, combined CAPs and O3, and filtered air. Secondary aims of the study included assessing for a dose–response relationship for CAPs exposure both with and without O3, assessing blood pressure (BP) response to exposures, and assessing whether a subgroup of subjects with asthma was more susceptible to autonomic dysregulation after exposures.

Materials and Methods

Study population. The study was approved by the Human Subjects Review Committee of the University of Toronto and was performed at the Gage Occupational and Environmental Health Unit in Toronto, Ontario, Canada. Informed consent was obtained from 50 male and female nonsmoking subjects, 19–48 years of age, without any history of cardiovascular disease or risk factors. Subjects were pooled from two separate studies, study A and study B. One subject participated in both studies.

From July 1999 through February 2003, study A conducted exposures on subjects with and without asthma (n = 21). Asthmatic status was determined by physician diagnosis and confirmed by methacholine challenge. Asthmatic subjects had been off of any short-acting bronchodilators from midnight onward and off of corticosteroid treatment for at least 1 month before all visits. Study B was conducted from January 2004 through October 2007, and included only subjects without asthma (n = 30). BP responses to exposure in study B have been reported previously (Urch et al. 2004).

Exposure protocol. All subjects were intended to receive four 2-hr exposures in random order as follows: a) sham filtered air (FA) with particles removed by a high-efficiency particulate arrester (HEPA) filter and no added O3; b) CAPs with target PM2.5 mass concentration of 150 μg/m3; c) O3 with target concentration of 120 ppb; and d) CAPs + O3. In addition, a subset of participants in study A underwent additional exposures with a target CAPs mass concentration of 60 μg/m3. Exposures within the same subject were separated by at least 2 weeks, and all exposures were conducted at the same time of day to avoid confounding by circadian variations (Brook et al. 2002; Task Force of the European Society of Cardiology 1996). In addition, subjects were seated at rest in the exposure chamber 15 min before receiving the intended exposure to allow for acclimation to sitting in the chamber.

Details of the human exposure facility have been described previously (Brook et al. 2002; Petrovic et al. 2000; Urch et al. 2005). Briefly, ambient particles with aerodynamic diameter < 2.5 μm were drawn through an inlet outside of the laboratory, concentrated using a Harvard virtual impactor (Sioutas et al. 1995), diluted to the target concentration, and delivered via facemask to subjects seated at rest inside an enclosure (Petrovic et al. 2000). The achieved CAPs mass concentration was measured gravimetrically from samples obtained via a port proximal to the facemask (Petrovic et al. 2000). The concentrator was run during the non-CAPs exposures, but particles were removed with a HEPA filter proximal to the facemask (Petrovic et al. 2000; Urch et al. 2004). O3 was produced with an arc generator using medical-grade oxygen and delivered upstream of the particle concentrator. O3 concentration was maintained at approximately 120 ppb measured just upstream of the facemask by an O3 analyzer (model 1008-RS; Dasibi Environmental, Glendale, CA, USA). Ambient temperature, relative humidity, and ambient gaseous pollutant concentrations including carbon monoxide, carbon dioxide, sulfur dioxide, nitrogen oxide, and nitrogen dioxide were monitored during the exposure as previously described (Petrovic et al. 2000; Urch et al. 2004). In addition, CAPs mass concentration was continuously monitored using a tapered element oscillating microbalance monitor (TEOM) (model 1400a; Rupprecht & Patashnick Co. Inc., Albany, NY, USA).

Outcome measurement. The primary outcome measure was change in several HRV indices between the start and end of each 2-hr exposure (Figure 1). Electrocardiograms were continuously recorded using digital Holter monitors (Marquette Medical Systems, Milwaukee, WI, USA) and subsequently stored and analyzed on a Marquette Medical Systems (MARS) Unity workstation. Beat annotations were automatically assigned by the software and reviewed by an investigator blinded to the exposure status.

Figure 1Figure 1 – Timeline of BP and HRV measures.

View larger image (TIF File)

Calculations for time domain [standard deviation of NN intervals (SDNN); square root of the mean squared differences of successive NN intervals (rMSSD); proportion of successive NN intervals with differences > 50 msec (pNN50)] and frequency domain [low-frequency (LF) power (0.04–0.15 Hz), high-frequency (HF) power (0.04–0.15 Hz), and their ratio (LF/HF)] HRV parameters were evaluated on 5-min intervals of ECG data using standard techniques (Task Force of the European Society of Cardiology 1996). Only normal sinus beats were used. These measures were calculated at 0, 30, 60, 90, and 120 min into the exposure (Figure 1). For intervals with < 90% valid quality recording, the previous 5-min window was used instead.

In addition, systolic blood pressure (SBP) and diastolic blood pressure (DBP) were measured every 30 min throughout the 2-hr exposure (Figure 1) using a calibrated and automated sphygmomanometer (Oscar-1 or Oscar-2; SunTech Medical Instruments, Inc., Raleigh, NC, USA). Where the data were available, the analysis used a mean of three successive BP measurements at each time point. We also included mean arterial pressure (MAP) in our measurements, defined as the weighted average (2:1) of DBP and SBP. Furthermore, minute ventilation and respiratory frequency were recorded every 30 min during the exposure using a turbine-type flow transducer (VMM401; Interface Associates, Aliso Viejo, CA, USA).

Statistical analysis. We used linear mixed-effects models to evaluate the effects of exposure while accounting for the correlation between multiple measurements within each individual. In a first analysis, models included fixed effects for exposure (in four categories: FA, CAPs, O3, and CAPs + O3), age (linear continuous), sex, and asthmatic status (yes/no), and a random-subject intercept, modeling the primary outcome of change in HRV or BP between start and end of exposure as linear continuous variables. In a second analysis, we entered average measured CAPs mass concentration into the model as a linear continuous-exposure variable and stratified the CAPs dose–response analysis by presence or absence of O3.

We conducted several sensitivity analyses to evaluate the robustness of our main results. First, to assess whether additional time points of HRV and BP data would improve the resolution of the models, we modeled the mean change in outcome across five measurements taken every 30 min during the 2-hr exposure. Second, we evaluated whether the responses to CAPs and O3 differed in asthmatics versus non-asthmatics by adding exposure-by-asthmatic status interactions to the main model. Third, we controlled for potential confounding by minute ventilation and respiratory frequency, which can especially affect HF HRV (Hayano et al. 1991; Task Force of the European Society of Cardiology 1996). Fourth, we added average heart rate from the prior 5-min interval as a fixed effect.

All hypothesis tests were two-sided, and p < 0.05 was considered statistically significant. We used the SAS statistical analysis package (version 9.1; SAS Institute, Cary, NC, USA) for all analyses. Regression diagnostics were performed to verify model assumptions.


Subject characteristics and exposures. A total of 50 subjects with complete Holter data were included from both studies in the analyses (Table 1). The main distinction between study A and study B was the inclusion of 10 mildly asthmatic subjects in study A. The number of exposures with complete Holter data in each exposure category was as follows: 53 exposures to CAPs; 53 exposures to CAPs + O3; 40 exposures to O3; and 42 exposures to FA (sham). By design, a subset of participants in study A underwent additional exposures to CAPs at a lower target concentration, resulting in relatively fewer FA- and O3-only exposures. The mean CAPs mass concentration was 121.6 ± 48.0 μg/m3 (Figure 2). The mean O3 concentration was 113.9 ± 6.6 ppb. During FA exposure, the mean CAPs mass and O3 concentrations were 2.3 ± 5.7 μg/m3 and 10.0 ± 7.4 ppb, respectively.

Table 1Table 1 – Baseline subject characteristics and exposure data.

View larger image (TIF File)

Figure 2Figure 2 – Percentage distribution of CAPs exposure concentrations. The line indicates the fitted normal density curve.

View larger image (TIF File)

Outcomes. Heart rate variability. As illustrated in Figure 3, for all of the exposures, subjects had a net increase in SDNN as the 2-hr exposure progressed. The trend with time was similar for the other indices of HRV. The primary analysis, change in HRV indices between the start and end of the 2-hr exposure period, yielded no consistent differences between the exposure categories (Table 2). HF HRV showed a statistically significant increase for the CAPs-only exposure (p = 0.046) and a similar trend for O3 exposure (p = 0.051) when compared with filtered air. Sensitivity analyses separately incorporating minute ventilation, respiratory frequency, average heart rate, or the asthma interaction term into the main model abolished this difference and did not materially alter findings for the other HRV outcomes. Analyses using the mean of all five HRV measurements during the 2-hr exposure or assessing change in HRV by minutes into exposure did not materially alter our conclusions. We did not find evidence of heterogeneity by asthmatic status.

Figure 3Figure 3 – Change in SDNN by exposure from baseline over 2 hr. Error bars indicate SE.

View larger image (TIF File)

Table 2Table 2 – Change in HRV (± SE) between start and end of 2-hr exposure period.

View larger image (TIF File)

We also analyzed the dose–response relationship between CAPs mass concentration and change in the HRV indices, stratified by presence or absence of O3. For those exposures without O3 (i.e., CAPs alone and FA), there was no significant dose–response relationship between gravimetric CAPs mass concentration and any measure of HRV. However, when analyzing the CAPs mass concentration relationship for exposures with O3 (i.e., CAPs + O3 and O3 alone), there was a suggestion of negative dose–response slopes (Table 3) between CAPs mass concentration and several HRV indices. This trend was seen in SDNN, rMSSD, and HF and was statistically significant for LF (p = 0.02).

Table 3Table 3 – Dose–response slope for CAPs mass concentration versus 2-hr change in HRV.

View larger image (TIF File)

Blood pressure. A statistically significant increase in DBP for CAPs + O3 relative to FA was previously reported for the subjects in study B (Urch et al. 2005). Therefore, in the current analysis, we focused only on the BP data from study A.

We assessed the change in BP between the start and end of the the 2-hr exposure (Table 4) as well as the change in BP at each 30-min interval. Similar to data from study B, subjects in study A demonstrated a statistically significant increase in DBP (1.97 mmHg, p = 0.02) in response to CAPs + O3. Figure 4 shows DBP at 30-min intervals throughout the exposure period. All the subjects experienced an equilibration period after entering the chamber when their DBP decreased initially with time. After this equilibration, the CAPs + O3 exposure began to diverge from the other exposures, demonstrating a statistically significant increase relative to filtered air at 60 min (p < 0.03). No clear pattern emerged among the exposures for SBP and MAP, although SBP tended to decrease in the O3-only exposure (Table 4).

Table 4Table 4 – Change in BP between exposure start and exposure end.

View larger image (TIF File)

Figure 4Figure 4 – Change in DBP over 2 hr by exposure. Error bars indicate SE.

View larger image (TIF File)

Sensitivity analyses additionally controlling for minute ventilation, respiratory frequency, or heart rate did not materially alter the results. We did not find evidence of heterogeneity of effect by asthmatic status.


To our knowledge, this is the largest study assessing the acute impact of CAPs exposure on HRV in young healthy adults. In addition, with recent evidence in animals showing effects of combined O3 and particulate exposure on HRV (Hamade et al. 2008), this is also the largest human controlled-exposure study looking at the impact of combined exposure to CAPs and O3 on HRV.

In this study, HRV indices were used as surrogate markers of autonomic tone (Task Force of the European Society of Cardiology 1996). The time-domain measures rMSSD and pNN50 are thought to reflect parasympathetic influences, whereas SDNN may also have sympathetic influence (Dekker et al. 2000; Hayano et al. 1991; Task Force of the European Society of Cardiology 1996). Among the frequency-domain parameters, HF almost exclusively reflects parasympathetic influence and respiratory variation (Hayano et al. 1991; Task Force of the European Society of Cardiology 1996). Interpreting changes in LF and LF/HF is controversial; LF may to some extent reflect sympathetic influences, whereas LF/HF possibly reflects sympathovagal balance (Task Force of the European Society of Cardiology 1996).

There is a large body of evidence suggesting that cardiovascular response to pollutants varies with age and comorbidities (Brook et al. 2004; Dockery et al. 1993; Goldberg et al. 2001; Katsouyanni et al. 2001). In this group of young healthy adult subjects, we did not detect a consistent pattern for changes in HRV indices among the exposure categories. HF had a statistically significant difference in some of the exposures relative to filtered air. However, given that HF is particularly sensitive to respiratory variation (Task Force of the European Society of Cardiology 1996), adjusting for respiratory parameters abolished this difference. Despite the absence of a clear pattern of difference in the categorical exposure models, the dose–response analysis in the setting of concomitant O3 demonstrated a trend toward negative linear association between CAPs mass concentration and change in several HRV indices, with a statistically significant relationship for LF HRV. No such relationship existed without O3 present. Our findings for CAPs alone agree with findings in other studies reporting the lack of significant effect of CAPs alone on HRV in young healthy subjects, despite significant effects noted in elderly subjects (Devlin et al. 2003; Gong et al. 2003). The suggestion of dose–response CAPs effects in the presence of O3 is of import, given emerging research priorities emphasizing studies of copollutants and dose–response relationships (National Research Council 2004).

Our results corroborate previous findings of increase in DBP with CAPs + O3 (Urch et al. 2005). The effect became statistically significant at 60 min and became more pronounced toward the end of the exposure. With regard to SBP, only one human controlled-exposure study (Gong et al. 2003) has demonstrated modest changes with CAPs exposure, whereas other studies have not shown effects (Devlin et al. 2003; Urch et al. 2005). In one exposure study conducted in canines exposed to CAPs, the increase in DBP was of greater magnitude than the increase in SBP (Bartoli et al. 2009). One possible explanation for the apparent disparity between SBP and DBP change in our study is the attenuation of peripheral SBP amplification in young adults (Franklin et al. 2005). It has been shown in adults < 50 years of age that for a given increase in central and peripheral DBP, peripherally measured SBP does not increase in parallel as it does for older adults (Wilkinson et al. 2001). Alternatively, the baseline increase in SBP in our filtered-air control group and the greater variation and lability of SBP measurements relative to DBP in our study may have made it more difficult to appreciate a meaningfully different change in SBP.

The effects of CAPs + O3 on BP, and possibly in a dose–response fashion on HRV, raise important questions about the interaction and possible synergy between the two components in their impact on cardiovascular physiology. With regard to possible mechanisms for pollutant-mediated changes in systemic physiology, it has been demonstrated in animal models that O3 exposure leads to lung hyperpermeability (Kleeberger et al. 2000), possibly increasing systemic toxin absorption or increasing local inflammation. Other possibilities include O3-mediated free radical production or conversion of particles to compounds with greater tendency to deposit on surfaces, the latter having been demonstrated with ammonium nitrate particles (Meng et al. 1997). In humans, generated ammonium nitrate particle with O3 combination exposure has recently been shown to suppress HRV (Power et al. 2008). The changes in DBP may be related to changes in autonomic tone, as shown in cohort studies demonstrating correlation among HRV measures and incident hypertension (Singh et al. 1998), but the data in our study do not consistently validate this hypothesis. Alternatively, the DBP response may be related to direct vasoconstriction (Brook et al. 2002; Urch et al. 2004, 2005) or increased peripheral vascular resistance independent of autonomic changes, but we did not directly test this hypothesis in this study.

Our study has several potential limitations that need to be considered. First, we could not control for ambient pollutant exposure prior to each visit. Future studies may address this limitation with personal monitoring, detailed time–activity diaries, or optimally, having study participants sleep onsite the night preceding any experiments. Second, because the study was designed to examine acute effects, we could not assess more prolonged time-dependent effects of exposures (McDonnell et al. 2007) or effects resulting from sequential rather than concomitant exposures. Future studies may address this limitation using staggered and/or prolonged exposures. Third, because our particle concentrator does not concentrate particles < 0.1 μm, limiting particle size to predominantly accumulation mode, we could not assess the role of ultrafine particles. Controlled-exposure studies comparing the toxicity of ultrafine, fine, and coarse particles in humans are clearly needed. Fourth, we did not measure or remove volatile organic compounds, which likely have independent effects (Bhatnagar 2006). However, the crossover design of this study reduced potential confounding either by exposure variation or by other unmeasured confounders.

An important strength of this study is that CAPs exposures were derived from real-world ambient particles from an urban environment. According to one sampling campaign in 1997 through 1999, PM2.5 in Toronto typically includes approximately one-quarter organic carbon, similar portions sulfates, nitrates, ammonium, and black carbon, and small portions of soil or other constituents (Bhatnagar 2006). The large sample size of our study and the fact that composition of CAPs changes daily in these experiments can be exploited in future analyses to identify components or constituents of CAPs that may be associated with greater effects.


In summary, ambient PM2.5 has been shown to impact HRV in epidemiologic studies of populations considered vulnerable on the basis of age or chronic diseases (Creason et al. 2001; Gold et al. 2000; Liao et al. 1999; Magari et al. 2001; Pope et al. 1999). Whereas most epidemiologic studies focus on effects ranging from several hours to days (Creason et al. 2001; Liao et al. 1999; Magari et al. 2001; Pope et al. 1999), we attempted to study acute effects within the span of 2 hr. Our data suggest that in younger subjects, CAPs alone does not produce significant effects, but when combined with O3, there is an increase in DBP that may be mediated through autonomic changes. The possibility of an autonomic effect is suggested in the dose–response relationship of HRV to CAPs mass concentration, although this is of small magnitude and borderline statistical significance in this group of young healthy adult subjects. Given that CAPs alone produce HRV changes in more vulnerable populations (Creason et al. 2001; Devlin et al. 2003; Gold et al. 2000; Liao et al. 1999; Magari et al. 2001; Pope et al. 1999), elderly subjects or subjects with comorbidities may experience even stronger synergistic effects with simultaneous controlled exposure to CAPs and O3.


Bartoli CR, Wellenius GA, Diaz EA, Lawrence J, Coull BA, Akiyama I, et al. 2009. Mechanisms of inhaled fine particulate air pollution–induced arterial blood pressure changes. Environ Health Perspect 117:361–366.

Bell ML, McDermott A, Zeger SL, Same JM, Dominici F. 2004. Ozone and short-term mortality in 95 US urban communities, 1987–2000. JAMA 292(19):2372–2378.

Bhatnagar A. 2006. Environmental cardiology: studying mechanistic links between pollution and heart disease. Circ Res 99(7):692–705.

Brook RD, Brook JR, Urch B, Vincent R, Rajagopalan S, Silverman F. 2002. Inhalation of fine particulate air pollution and ozone causes acute arterial vasoconstriction in healthy adults. Circulation 105(13):1534–1536.

Brook RD, Franklin B, Cascio W, Hong Y, Howard G, Lipsett M, et al. 2004. Air pollution and cardiovascular disease: a statement for healthcare professionals from the Expert Panel on Population and Prevention Science of the American Heart Association. Circulation 109(21):2655–2671.

Creason J, Neas L, Walsh D, Williams R, Sheldon L, Liao D, et al. 2001. Particulate matter and heart rate variability among elderly retirees: the Baltimore 1998 PM study. J Expo Anal Environ Epidemiol 11(2):116–122.

Dekker JM, Crow RS, Folsom AR, Hannan PJ, Liao D, Swenne CA, et al. 2000. Low heart rate variability in a 2-min rhythm strip predicts risk of coronary heart disease and mortality from several causes: the ARIC Study. Atherosclerosis Risk In Communities. Circulation 102(11):1239–1244.

Devlin RB, Ghio AJ, Kehrl H, Sanders G, Cascio W. 2003. Elderly humans exposed to concentrated air pollution particles have decreased heart rate variability. Eur Respir J Suppl 40:76s–80s.

Dockery DW, Luttmann-Gibson H, Rich DQ, Link MS, Mittleman MA, Gold DR, et al. 2005. Association of air pollution with increased incidence of ventricular tachyarrhythmias recorded by implanted cardioverter defibrillators. Environ Health Perspect 113:670–674.

Dockery DW, Pope CA, Xu X, Spengler JD, Ware JH, Fay ME, et al. 1993. An association between air pollution and mortality in six U.S. cities. N Engl J Med 329(24):1753–1759.

Dominici F, Peng RD, Bell ML, Pham L, McDermott A, Zeger SL, et al. 2006. Fine particulate air pollution and hospital admission for cardiovascular and respiratory diseases. JAMA 295(10):1127–1134.

Finlayson-Pitts BJ, Pitts JN. 1997. Tropospheric air pollution: ozone, airborne toxics, polycyclic aromatic hydrocarbons, and particles. Science 276(5315):1045–1051.

Franklin SS, Pio JR, Wong ND, Larson MG, Leip EP, Vasan RS, et al. 2005. Predictors of new-onset diastolic and systolic hypertension: the Framingham Heart Study. Circulation 111(9):1121–1127.

Godleski JJ, Verrier RL, Koutrakis P, Catalano P, Coull B, Reinisch U, et al. 2000. Mechanisms of morbidity and mortality from exposure to ambient air particles. Res Rep Health Eff Inst (91) 5–88. discussion 89–103.

Gold DR, Litonjua A, Schwartz J, Lovett E, Larson A, Nearing B, et al. 2000. Ambient pollution and heart rate variability. Circulation 101(11):1267–1273.

Goldberg MS, Burnett RT, Bailar JC 3rd, Tamblyn R, Ernst P, Flegel K, et al. 2001. Identification of persons with cardiorespiratory conditions who are at risk of dying from the acute effects of ambient air particles. Environ Health Perspect 109(suppl 4):487–494.

Gong H Jr, Linn WS, Sioutas C, Terrell SL, Clark KW, Anderson KR, et al. 2003. Controlled exposures of healthy and asthmatic volunteers to concentrated ambient fine particles in Los Angeles. Inhal Toxicol 15(4):305–325.

Hamade AK, Rabold R, Tankersley CG. 2008. Adverse cardiovascular effects with acute particulate matter and ozone exposures: interstrain variation in mice. Environ Health Perspect 116:1033–1039.

Hayano J, Sakakibara Y, Yamada A, Yamada M, Mukai S, Fujinami T, et al. 1991. Accuracy of assessment of cardiac vagal tone by heart rate variability in normal subjects. Am J Cardiol 67(2):199–204.

Katsouyanni K, Touloumi G, Samoli E, Gryparis A, Le Tertre A, Monopolis Y, et al. 2001. Confounding and effect modification in the short-term effects of ambient particles on total mortality: results from 29 European cities within the APHEA2 project. Epidemiology 12(5):521–531.

Kleeberger SR, Reddy S, Zhang LY, Jedlicka AE. 2000. Genetic susceptibility to ozone-induced lung hyperpermeability: role of toll-like receptor 4. Am J Respir Cell Mol Biol 22(5):620–627.

Liao D, Creason J, Shy C, Williams R, Watts R, Zweidinger R. 1999. Daily variation of particulate air pollution and poor cardiac autonomic control in the elderly. Environ Health Perspect 107:521–525.

Magari SR, Hauser R, Schwartz J, Williams PL, Smith TJ, Christiani DC. 2001. Association of heart rate variability with occupational and environmental exposure to particulate air pollution. Circulation 104(9):986–991.

McDonnell WF, Stewart PW, Smith MV. 2007. The temporal dynamics of ozone-induced FEV1 changes in humans: an exposure-response model. Inhal Toxicol 19(6–7):483–494.

Meng Z, Dabdub D, Seinfeld JH. 1997. Chemical coupling between atmospheric ozone and particulate matter. Science 277(5322):116–119.

National Research Council. 2004. Research Priorities for Airborne Particulate Matter IV: Continuing Research Progress. Washington, DC:National Academies Press.

Peters A, Liu E, Verrier RL, Schwartz J, Gold DR, Mittleman M, et al. 2000. Air pollution and incidence of cardiac arrhythmia. Epidemiology 11(1):11–17.

Petrovic S, Urch B, Brook J, Datema J, Purdham J, Liu L, et al. 2000. Cardiorespiratory effects of concentrated ambient PM2.5: a pilot study using controlled human exposures. Inhal Toxicol 12(1):173–173.

Pope CA, Thun MJ, Namboodiri MM, Dockery DW, Evans JS, Speizer FE, et al. 1995. Particulate air pollution as a predictor of mortality in a prospective study of U.S. adults. Am J Respir Crit Care Med 151(3 Pt 1):669–674.

Pope CA, Verrier RL, Lovett EG, Larson AC, Raizenne ME, Kanner RE, et al. 1999. Heart rate variability associated with particulate air pollution. Am Heart J 138(5 Pt 1):890–899.

Power KL, Balmes J, Solomon C. 2008. Controlled exposure to combined particles and ozone decreases heart rate variability. J Occup Environ Med 50(11):1253–1260.

Rich DQ, Kim MH, Turner JR, Mittleman MA, Schwartz J, Catalano PJ, et al. 2006. Association of ventricular arrhythmias detected by implantable cardioverter defibrillator and ambient air pollutants in the St Louis, Missouri metropolitan area. Occup Environ Med 63(9):591–596.

Singh JP, Larson MG, Tsuji H, Evans JC, O’Donnell CJ, Levy D. 1998. Reduced heart rate variability and new-onset hypertension: insights into pathogenesis of hypertension: the Framingham Heart Study. Hypertension 32(2):293–297.

Sioutas C, Koutrakis P, Burton RM. 1995. A technique to expose animals to concentrated fine ambient aerosols. Environ Health Perspect 103:172–177.

Task Force of the European Society of Cardiology and the North American Society of Pacing and Electrophysiology. 1996. Heart rate variability. Standards of measurement, physiological interpretation, and clinical use. Circulation 93(5):1043–1065.

Urch B, Brook JR, Wasserstein D, Brook RD, Rajagopalan S, Corey P, et al. 2004. Relative contributions of PM2.5 chemical constituents to acute arterial vasoconstriction in humans. Inhal Toxicol 16(6–7):345–352.

Urch B, Silverman F, Corey P, Brook JR, Lukic KZ, Rajagopalan S, et al. 2005. Acute blood pressure responses in healthy adults during controlled air pollution exposures. Environ Health Perspect 113:1052–1055.

Wilkinson IB, Franklin SS, Hall IR, Tyrrell S, Cockcroft JR. 2001. Pressure amplification explains why pulse pressure is unrelated to risk in young subjects. Hypertension 38(6):1461–1466.

WP-Backgrounds Lite by InoPlugs Web Design and Juwelier Schönmann 1010 Wien