Printer Friendly

Photochemically altered air pollution mixtures and contractile parameters in isolated murine hearts before and after ischemia.


Epidemiological studies have linked acute and chronic ambient air pollution exposure with cardiovascular diseases and shown that air pollution exposure increases the risk of mortality, ischemic heart disease, heart failure, and arrhythmias (Brook et al. 2010). The Clean Air Act (1970) and the Clean Air Act Amendments (1990) established National Air Quality Standards for individual "criteria pollutants." Consequently, air pollution health effects research studies have largely focused on characterizing the effects of exposure to these pollutants on an individual basis. However, "real-world" air pollution is far more complex than exposure to an individual agent because real-world air pollution contains freshly emitted primary aerosol as well as photochemically aged secondary aerosols formed in the atmosphere during the oxidation of gas-phase precursors (Kanakidou et al. 2005). There is a growing realization that a multipollutant experimental approach is needed to understand the relevant modes of action of ambient air pollutant mixtures on human health (Dominici et al. 2010). However, there is currently a paucity of data on how complex mixtures impact key target organ systems associated with morbidity and mortality. To fill this critical knowledge gap, we tested whether inhaled exposure to particle-free complex mixtures representative of gaseous mixtures found in urban environments can modulate pulmonary inflammation and cardiac mechanics.

We used an environmental photochemical reaction chamber located at the University of North Carolina at Chapel Hill to generate model multipollutant-mixture atmospheres. The chamber uses sunlight to imitate the natural photochemistry of urban mixtures and produce a combination of compounds that is similar in composition to that found in urban multipollutant mixtures (Jeffries 1995; Sexton et al. 2004). Previous in vitro studies have utilized these chambers to expose individual cell cultures to examine the toxicity of air pollution mixtures and have shown that exposure to photochemically altered particle-free urban mixtures causes significant inflammatory responses (Sexton et al. 2004) and greater genetic alterations (Rager et al. 2011) compared with exposure to primary urban mixtures.

Experimental studies have demonstrated the ability of individual air pollutants to cause cardiopulmonary toxicity in animals. For example, acute exposure to particulate matter can increase pulmonary and systemic inflammation and lung injury, cause vascular dysfunction, alter heart rate variability, induce arrhythmia, and enhance cardiac ischemic injury (Brook et al. 2010). We (Cho et al. 2009; Tong et al. 2010) and others (Cozzi et al. 2006) have shown that particulate matter exposure can enhance cardiac ischemia/ reperfusion injury in animals. However, extrapolation to multipollutant mixtures is far from simple. For instance, the redox cycling potential of a mixture, which is thought to be an important predictor of generation of inflammation, may be very different than that of its constituent parts. To address this issue, we tested the hypothesis that photochemically aged particle-free multipollutant mixtures can cause inflammation and impair cardiac function. Using a murine model, we evaluated the effects of multipollutant-mixture exposure on cardiovascular and pulmonary end points. We report here that exposure to multipollutant mixtures at concentrations that produce only minimal pulmonary effects significantly affect cardiac function--including decreased left ventricular developed pressure and contractility--but unexpectedly reduce cardiac ischemia/reperfusion injury.

Methods and Materials

Experimental animals. Mice were maintained at 22[degrees]C with a 12-hr light/dark cycle and free access to food (ProLab RMH 3000; PMI Nutrition, Saint Louis, MO) and water. We purchased 45 female C57BL/6 mice (5 months of age, mean weight 23.9 [+ or -] 0.39 g) from Jackson Laboratory (Bar Harbor, ME) and they were acclimated for 2 months before they were used. All experimental procedures were performed in compliance with protocols approved by the University of North Carolina at Chapel Hill Institutional Animal Care and Use Committee according to National Institutes of Health guidelines (National Research Council 2011). The animals were treated humanely and with regard for alleviation of suffering.

Generation of photochemical urban mixtures. The University of North Carolina at Chapel Hill's outdoor environmental photochemical reaction chamber was used to generate exposure atmospheres. Synthetic Urban Mix (Scott Specialty Gases, Plumsteadville, PA), a volatile organic compound (VOC) mixture (Jeffries 1995), and N[O.sub.x] [nitric oxide (NO) and nitrogen dioxide (N[O.sub.2])] were used as the starting materials for the test atmosphere. The synthetic particle-free urban mixture contains 55 different hydrocarbons at specific ratios that represent chemicals present in urban atmospheres (Sexton et al. 2004). On the morning of the exposure, the chamber was humidified naturally by pre-flushing with HEPA-filtered ambient air. At 0700 hours, the Synthetic Urban Mix volatile organics were drawn from a gas cylinder into the photochemical reaction chamber while a liquid mixture containing less-volatile organics was injected into the chamber. N[O.sub.x] was drawn from a gas cylinder (AirGas, National Welders, Morrisville, NC) into the chamber to establish a test atmosphere containing 2 ppm N[O.sub.x].

Chemical constituents inside the chamber during the experiment were assessed by gas measurement methods as described previously (Rager et al. 2011). NO and N[O.sub.2] levels were measured once per minute using a Teledyne model 9841 N[O.sub.x] analyzer (Teledyne Monitor Labs, Englewood, CO). Ozone ([O.sub.3]) was measured every minute with a Teledyne model 9811 monitor. Concentrations of these compounds were averaged during the exposure. Other secondary products such as the carbonyl-containing aldehydes and ketones were measured every 15 min by gas chromatography and mass spectrometry. Because the [O.sub.3] level was elevated to 0.243 ppm in the chamber, the same concentration of [O.sub.3] was used in the single-pollutant [O.sub.3] exposure. [O.sub.3] was generated from oxidized air using an [O.sub.3] generator (model OL80A; Ozone Services, Yanco Industries, Burton, British Columbia, Canada).

Animal exposure. Because the photochemical reaction depends on the weather condition and because the multipollutant mixtures generated are not reproducible, mice were exposed in groups to photochemically aged particle-free multipollutant mixtures (n = 15), 0.245 ppm [O.sub.3] (n = 14), or filtered air (FA; n = 16) for 4 hr (2000-2400 hours) during their dark cycle on 3 separate days in an outdoor photochemical reaction chamber. One group of mice per exposure (n = 7 in the multipollutant-mixture group; n = 6 in the [O.sub.3] group; n = 8 in the FA group) was used for the isolated heart perfusion and the other mice (n = 8 per group) were used for assessing lung inflammation.

Cardiac function. As described previously (Tong et al. 2009), 8-11 hr after exposure, mice were anesthetized with an intraperitoneal (ip) injection of sodium pentobarbital (80 mg/kg body weight). After injecting the mice with intravenous heparin (100 units), the hearts were excised rapidly and placed in ice-cold Krebs-Henseleit buffer. The aortas were cannulated and perfused retrograde at a constant pressure of 100 cm[H.sub.2]O. The nonrecirculating perfusate was Krebs-Henseleit buffer containing 120 mmol/L sodium chloride, 5.9 mmol/L potassium chloride, 1.2 mmol/L magnesium sulfate, 1.75 mmol/L calclium chloride, 25 mmol/L sodium bicarbonate, and 11 mmol/L glucose. The buffer was aerated with 95% oxygen and 5% carbon dioxide, and maintained at pH 7.4 and 37[degrees]C.

For assessment of contractile function, a latex balloon on the tip of a polyethylene catheter was inserted through the left atrium into the left ventricle. The catheter was connected to a pressure transducer (model 041500503; Argon Medical Devices, Athens, TX) at the same height as the heart. The pressure of the left ventricular balloon was inflated to 0-5 cm[H.sub.2]O. We used a PowerLab data acquisition system (AD Instruments, Milford, MA) to collect and process the heart rate, left ventricular developed pressure [LVDP, i.e., LV peak minus end-diastolic pressure (LVEDP)], and contractility (dP/dt) data. All hearts had been perfused for 25 min when the baseline measurements were taken. We then initiated 20 min of global no-flow ischemia followed by 2 hr of reperfusion. Onset of ischemic contracture was detected when the left ventricular pressure began to increase during ischemia. We measured recovery of LVDP, expressed as a percentage of the initial preischemic LVDP, at 40 min of reperfusion after 20 min of ischemia.

Cardiac necrosis evaluation. As described previously by Tong et al. (2009, 2010), at the end of 2 hr of reperfusion, we perfused the hearts with 15 mL of a 1% solution of 2,3,5-triphenyltetrazolium chloride (TTC) dissolved in Krebs-Henseleit buffer, incubated them in 1% TTC at 37[degrees]C for 10 min, and then fixed them in formalin. We measured the area of necrosis by taking cross-sectional slices through the ventricles, which were then photographed using a digital camera mounted on a stereo-microscope. We quantified the resulting images by measuring the areas of stained (viable tissue) versus unstained tissue (infarct) using Adobe Photoshop (Adobe Systems, San Jose, CA). Infarct size was expressed as a percentage of the total ventricular section and averaged from four images.

Bronchoalveolar lavage. Lung inflammation has been shown to be one of the pathways that mediate the cardiac effects (Brook et al. 2010); therefore, we examined whether exposure to multipollutant mixtures or to [O.sub.3] resulted in lung inflammation. Twelve hours after exposure, mice were anesthetized with an ip injection of pentobarbital sodium (50 mg/kg). The lungs were lavaged five times with 1 mL 1x Hanks' Balanced Salt Soultion (HBSS; Gibco, Life Technologies, Carlsbad, CA) and cellular components of the bronchoalveolar lavage (BAL) fluid were separated by centrifugation at 1,500 rpm for 10 min at 4[degrees]C. The cell pellet was resuspended in 500 [micro]L HBSS and total cells were counted using a hemocytometer. Cytospin preparations were made and stained with Hema 3 (Fisher Scientific, Waltham, MA) to evaluate the BAL cellular composition.

Statistical analysis. Data are expressed as mean [+ or -] SE. Nonparametric analyses were performed because the data were not normally distributed. We performed comparisons among the multipollutant-mixture, [O.sub.3], and FA control groups by Kruskal-Wallis U-test followed by Dunn's multiple comparison test. We used the Mann-Whitney U-test to compare the multipollutant-mixture or [O.sub.3] groups with the FA control group. The statistical significance level was set at p < 0.05.


Composition of particle-free photochemically generated multipollutant mixtures. Photochemical reactions of the original hydrocarbons and N[O.sub.x] mixtures generated > 300 carbonyl secondary products. Among those products, the levels of detected VOC compounds estimated in the chamber are listed in Table 1. As reported by Rager et al. (2011), the average chamber levels of NO and N[O.sub.2] decreased throughout the day, and levels of secondary chemical products such as [O.sub.3], formaldehyde, and acetaldehyde increased. The photochemical chamber contained 0.243 ppm of [O.sub.3] and secondary carbonyls. The formaldehyde level in the photochemical chamber was 5x higher than that in the [O.sub.3] and FA control chambers, and the acetaldehyde level was elevated in the photochemical chamber but not detectable in the [O.sub.3] and FA control chambers. No particulate matter or secondary organic aerosol was formed within the chamber.

Cardiac effects. When compared with the FA control, the baseline heart rate prior to ischemia decreased with [O.sub.3] exposure, whereas heart rate was unchanged in the hearts of mice exposed to the particle-free multipollutant mixtures (Figure 1A). We observed no differences in baseline coronary artery flow rate at constant pressure between the multipollutant-mixture or [O.sub.3] groups compared with the FA control group (Table 2). However, hearts from the multipollutant-mixture group had lower baseline LVDP (69.2 [+ or -] 16.0 cm[H.sub.2]O) compared with the FA group (146.4 [+ or -] 14.8 cm[H.sub.2]O; p < 0.05) although there was no significant difference between the FA- and [O.sub.3]-groups (134.2 [+ or -] 5.4 cm[H.sub.2]O) (Figure 1B). Exposure to multipollutant mixtures or [O.sub.3] decreased baseline left ventricular contractility. The baseline rate of contraction ([dP/dt.sub.maximum]; maximum first derivative of the change in left ventricular pressure/time) was lower in the multipollutant-mixture group (2,764 [+ or -] 558 cm[H.sub.2]O/sec) compared with the FA group (5,405 [+ or -] 400 cm[H.sub.2]O/sec; p < 0.05) (Figure 2A). Yet, the change in [dP/dt.sub.maximum] did not differ between the [O.sub.3] (4,070 [+ or -] 704 cm[H.sub.2]O/sec) and FA group. The baseline rate of relaxation ([dP/dt.sub.minimum]; minimum first derivative of the change in left ventricular pressure/time) was decreased by exposure to the multipollutant mixtures (-1,822 [+ or -] 335 cm[H.sub.2]O/sec; p < 0.01) and [O.sub.3] exposure (-2,477 [+ or -] 407 cm[H.sub.2]O/sec; p < 0.05) when compared with the FA control (-3,675 [+ or -] 242 cm[H.sub.2]O/sec) (Figure 2B).

Compared with the FA group (13.2 [+ or -] 1.4 min), time to ischemic contracture was not affected in the [O.sub.3] group (14.0 [+ or -] 1.8 min), but was prolonged in the multipollutant-mixture group during the 20 min of ischemia (17.3 [+ or -] 0.5 min; p < 0.05). There was also an increase in posti schemic recovery of LVDP at 40 min after reperfusion in the multipollutant-mixture group compared with the FA control group (70.7 [+ or -] 23.7% for multipollutant mixtures vs. 21.0 [+ or -] 7.1% for FA; p = 0.05) (Figure 3A). Infarct size was smaller in the multipollutant-mixture group (39.6 [+ or -] 6.6%) compared with the FA control (57.3 [+ or -] 4.6% for FA; p < 0.05) (Figure 3B). By 40 min of reperfusion, heart rate, LVDP, contractility, and coronary flow rate were not different among the multipollutant-mixture, [O.sub.3], and FA groups (Table 2).

Airway inflammation. Compared with the FA controls, the BAL from mice exposed to the multipollutant mixtures or [O.sub.3] showed an increase in the number of macrophages (Figure 4). However, we found no influx of neutrophils or other cell types after any exposure.


Although our understanding of the health effects of single pollutants has advanced considerably over the last several decades, knowledge of the effects of multipollutant mixtures is limited. In the present study we used a photochemical reaction chamber to generate particle-free urban-like multipollutant mixtures for the purpose of evaluating the pulmonary and cardiac responses in mice to inhalation of an atmosphere containing complex multipollutant mixtures or [O.sub.3] at the same concentration as present in the multipollutant mixtures. Thus, any difference in measured responses between these two exposures can be ascribed to effects of the multipollutant mixtures. Short-term inhalation of photochemically altered particle-free multipollutant mixtures and [O.sub.3] alone depressed cardiac contractility (dP/dt) in the isolated perfused heart. However, exposure to the particle-free multipollutant mixtures delayed the onset of ischemic contracture and preserved contractile function during reperfusion in isolated mouse hearts. In addition, although we found no significant difference in the mechanical responses between the multipollutant mixtures and [O.sub.3] alone, the magnitude of the effect of [O.sub.3] alone was always less than the effect of the multipollutant mixtures. Thus, it appears that one or more of the multipollutant-mixture's component(s) contribute to an additional effect beyond that of [O.sub.3] alone.

Experimental studies by Gordon (2007) implicated particulate mass and the physicochemical properties of air pollutants as determinants of the health effects of air pollution inhalation. In particular, organic components of air pollution are thought to play an important role in affecting biological responses (Castranova et al. 2001). In the present study, mice were exposed to particle-free photochemically altered products of hydrocarbons and N[O.sub.x], indicating that the cardiac effects measured following exposure resulted from gaseous components of multipollutant mixtures. We have previously exposed cultured lung cells to similar multipollutant mixtures in the photochemical reaction chamber and showed that gaseous products elicited biological and biochemical responses in the absence of particles (Sexton et al. 2004). Furthermore, animal studies have shown that spontaneously hypertensive and mildly cardiomyopathic rats exposed to filtered diesel exhaust exhibited either a similar degree or a greater magnitude of electrophysiological changes compared with exposure to whole diesel exhaust (Carll et al. 2012; Lamb et al. 2012), implying that gaseous components of air pollution might be driving the cardiovascular effects.

As shown previously (Sexton et al. 2004), levels of secondary chemical products such as [O.sub.3], formaldehyde, acetaldehyde, and many volatile and semivolatile organic hydrocarbons increase as the photochemical reaction progresses. Therefore, the animals in our study were exposed to higher levels of secondary products, which may elicit biological effects on the cardiovascular system. Secondary products formed during the photochemical reactions can induce more robust inflammatory responses (Sexton et al. 2004) and greater genomic changes (Rager et al. 2011) in cultured lung cells. Secondary products, such as [O.sub.3] generated during the photochemical reactions, may have contributed to the biological effects, including the [O.sub.3]-induced heart rate and baseline rate of left ventricular relaxation changes that we report here. Epidemiological studies have linked short-term [O.sub.3] exposure with cardiovascular and respiratory mortality in 95 large U.S. communities (Bell et al. 2004). [O.sub.3] exposure has also been associated with increased hospital admissions for heart failure (Yang 2008). Most recently, a controlled human-exposure study (Devlin et al. 2012) demonstrated that short-term [O.sub.3] exposure increased pulmonary and systemic inflammation, altered autonomic control of heart rhythm, and induced changes in blood proteins involved in fibrinolysis. In addition, an animal study (Chuang et al. 2009) demonstrated that 5 days (8 hr/day) of 0.5 ppm [O.sub.3] exposure in mice altered heart rates and mean blood pressure, inhibited endothelial-dependent vasor elaxation, and induced mitochondrial damage and atherogenesis.

The levels of the secondary products, formaldehyde and acetaldehyde, increased during the photochemical process in this study. Formaldehyde and acetaldehyde occur naturally in the environment and are produced in forest fires, automobile exhaust, and tobacco smoke. The ambient formaldehyde concentration was in the range of 0.4-7.5 ppb with a mean value of 2.2 ppb in New York City in the summertime in 2009 (Lin et al. 2012) and the ambient concentration of acetaldehyde averaged 5 [micro]g/[m.sup.3] (National Toxicology Program 2011). In the present study, exposure to formaldehyde may have contributed to the observed cardiac-depressive activity of the inhaled particle-free multipollutant mixtures. Similarly, acetaldehyde, another component of the multipollutant mixtures, could also affect cardiac function. Acetaldehyde has been shown to disrupt calcium ion ([Ca.sup.2+]) handling in the myocardium and to disturb cardiac excitation-contraction coupling (Oba et al. 2008), leading to reduced cardiac contractility. Therefore, the cardiac-depressive effects of inhalation of the multipollutant mixtures used in this study may have resulted from acetaldehyde-induced myocardial toxicity. Above all, the respiratory responses to volatile and semivolatile organic components of multipollutant mixtures, such as [O.sub.3], have been investigated in the past; yet the cardiovascular effects of those components are not well known. More research is needed to evaluate the cardiovascular effects of exposure to these ubiquitous air contaminants.

The mechanistic basis for the cardiac-mechanical effects of exposure to multipollutant mixtures and [O.sub.3] was not explored in this study. However, there are several pathways by which the air pollution mixtures could affect the cardiovascular system (Brook et al. 2010). Oxidative stress from multipollutant-mixture components such as [O.sub.3] could cause systemic oxidative stress, resulting in myocardial contractile dysfunction. In addition, activation of pulmonary receptors could initiate a neurocardiogenic effect, producing an intracardiac response affecting cardiac cellular function. It is also possible that some components of multipollutant mixtures might translocate into the circulation, with attendant direct oxidative effects on the heart and vasculature. We detected only macrophage accumulation in BAL in this study, suggesting that airway inflammation may not mediate the cardiac effects of inhalation to multipollutant mixtures or to [O.sub.3].

The decreased LVDP and cardiac contractility, delayed ischemic contracture, and preserved contractility during reperfusion consequent to exposure to inhaled multipollutant mixtures could indicate altered intracellular [Ca.sup.2+] regulation in the myocardium. The proredox components of multipollutant mixtures could modulate the cardiac myocytes' [Ca.sup.2+] handling by reducing the intracellular [Ca.sup.2+], or cause a change in the sensitivity of the contractile proteins to [Ca2.sup.+], resulting in decreased cardiac contractility. On the other hand, the reduced intracellular [Ca.sup.2+] overload during ischemia is associated with the preservation of mitochondrial function and adenosine triphosphate stores (Kowalchuk and Nesto 1989), as suggested by the multipollutant mixtures' induced delay of ischemic contracture and better recovery of posti schemic LVDP and smaller infarct size during reperfusion. Future studies are needed to better understand the role of intracellular [Ca.sup.2+] regulation in mediating cardiovascular physiological effects from air pollution exposure.

In this study we used a perfused isolated heart model to evaluate the ventricular function. However, isolated heart models lack innervation and blood supply and, therefore, lack influence by autonomic and hormonal control: This could alter findings in intact hearts.


Inhalation of particle-free photochemically altered multipollutant mixtures affects cardiac function in isolated mouse hearts. Specifically, inhalation of multipollutant mixtures depressed cardiac contractility in isolated non-ischemic hearts, and delayed ischemic contracture and preserved cardiac contractility in reperfused hearts, while eliciting mild pulmonary inflammation evidenced only by macrophage accumulation. Future studies are needed to identify the active components of photochemical reaction products responsible for the effects on myocardial mechanical performance as well as the mechanisms that underlie the cardiac effects.

Caption: Figure 1. Heart rate and cardiac function in isolated perfused murine hearts before ischemia. Heart rate (A) and LVDP (6) at baseline prior to ischemia in murine hearts isolated 8-11 hr after inhalation exposure to filtered air (FA), multipollutant mixtures (mixtures), or [O.sub.3] for 4 hr as described in "Materials and Methods." (n = 8 in the FA group, n = 6 in the [O.sub.3] group, and n = 7 in the mixtures group.)

* p < 0.05, compared with FA control group by Kruskal-Wallis U-test followed by Dunn's multiple comparison.

Caption: Figure 2. Multipollutant-mixture and [O.sub.3] inhalation reduced cardiac contractility in isolated, perfused murine hearts. Cardiac contractility assessed by maximum (A) and minimum (6) dP/dt at baseline prior to ischemia in murine hearts isolated 8 hr after inhalation exposure to FA (n = 8), mixtures (n = 7), or [O.sub.3] (n = 6) for 4 hr as described in "Materials and Methods."

* p < 0.05, and ** p < 0.01, compared with FA control group by Kruskal--Wallis U-test followed by Dunn's multiple comparison.

Caption: Figure 3. Multipollutant-mixture exposure improved recovery of postischemic cardiac function and reduced size of infarct in murine hearts. (A) Recovery of LVDP, expressed as a percentage of the initial baseline preischemic LVDP, was measured after 20 min of ischemia and 40 min of reperfusion in mouse hearts isolated 8 hr after inhalation exposure to FA (n = 8), mixtures (n = 7), or [O.sub.3] (n = 6) for 4 hr as described in "Materials and Methods." (6) Infarct size, expressed as a percentage of the total ventricular section, was measured after 20 min of ischemia and 2 hr of reperfusion as described in "Materials and Methods."

* p < 0.05, compared with FA control group by Kruskal--Wallis U-test followed by Dunn's multiple comparison.

Caption: Figure 4. Multipollutant-mixture and [O.sub.3] exposure increased macrophage number in BAL fluid. Macrophage number in BAL 12 hr after exposure to FA, multipollutant mixtures (mixtures), or [O.sub.3] for 4 hr as described in "Materials and Methods" (n = 8 per group).

* p < 0.05, compared with FA control group by Kruskal-Wallis U-test followed by Dunn's multiple comparison.


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

Brook RD, Rajagopalan S, Pope CA III, Brook JR, Bhatnagar A, Diez-Roux AV, et al. 2010. Particulate matter air pollution and cardiovascular disease: an update to the scientific statement from the American Heart Association. Circulation 121(21):2331-2378.

Carll AP, Hazari MS, Perez CM, Krantz QT, King CJ, Winsett DW, et al. 2012. Whole and particle-free diesel exhausts differentially affect cardiac electrophysiology, blood pressure, and autonomic balance in heart failure-prone rats. Toxicol Sci 128(2):490-199.

Castranova V, Ma JY, Yang HM, Antonini JM, Butterworth L, Barger MW, et al. 2001. Effect of exposure to diesel exhaust particles on the susceptibility of the lung to infection. Environ Health Perspect 109(suppl 4):609-612.

Cho SH, Tong H, McGee JK, Baldauf RW, Krantz QT, Gilmour MI. 2009. Comparative toxicity of size-fractionated airborne particulate matter collected at different distances from an urban highway. Environ Health Perspect 117:1682-1689; doi:10.1289/ehp.0900730.

Chuang GC, Yang Z, Westbrook DG, Pompilius M, Ballinger CA, White CR, et al. 2009. Pulmonary ozone exposure induces vascular dysfunction, mitochondrial damage, and atherogenesis. Am J Physiol Lung Cell Mol Physiol 297(2):L209-L216.

Clean Air Act. 1970. Public Law 91-604 [[section]112; 42 U.S.C.A. [section]7412(f)(2)].

Clean Air Act Amendments of 1990. 1990. Public Law 101-549.

Cozzi E, Hazarika S, Stallings HW III, Cascio WE, Devlin RB, Lust RM, et al. 2006. Ultrafine particulate matter exposure augments ischemia-reperfusion injury in mice. Am J Physiol Heart Circ Physiol 291(2):H894-H903.

Devlin RB, Duncan KE, Jardim M, Schmitt MT, Rappold AG, Diaz-Sanchez D. 2012. Controlled exposure of healthy young volunteers to ozone causes cardiovascular effects. Circulation 126(1):104-111.

Dominici F, Peng RD, Barr CD, Bell ML. 2010. Protecting human health from air pollution: shifting from a single-pollutant to a multipollutant approach. Epidemiology. 21(2):187-194.

Gordon T. 2007. Linking health effects to PM components, size, and sources. Inhal Toxicol 19(suppl 1):3-6.

Jeffries H. 1995. Photochemical air pollution. In: Composition, Chemistry, and Climate of the Atmosphere (Singh HB, ed). New York:Van Nostrand-Reinhold, 308-348.

Kanakidou M, Seinfeld JH, Pandis SN, Barnes I, Dentener FJ, Facchini MC, et al. 2005. Organic aerosol and global climate modelling: a review. Atmos Chem Phys 5:1053-1123.

Kowalchuk GJ, Nesto RW. 1989. Calcium antagonists and myocardial protection. Am J Cardiol 64(11):10F-17F.

Lamb CM, Hazari MS, Haykal-Coates N, Carll AP, Krantz QT, King C, et al. 2012. Divergent electrocardiographic responses to whole and particle-free diesel exhaust inhalation in spontaneously hypertensive rats. Toxicol Sci 125(2):558-568.

Lin Y, Schwab JJ, Demerjian KL, Bae MS, Chen WN, Sun Y, et al. 2012. Summertime formaldehyde observations in New York City: ambient levels, sources and its contribution to H[O.sub.x] radicals. J Geophys Res 117:D08305; doi:10.1029/2011JD016504.

National Research Council. 2011. Guide for the Care and Use of Laboratory Animals. 8th ed. Washington, DC: National Academies Press.

National Toxicology Program. 2011. Acetaldehyde: CAS No. 75-07-0. In: Report on Carcinogens. 12th ed. Washington, DC:National Toxicology Program, 21-24. Available: [accessed 5 November 2013].

Oba T, Maeno Y, Nagao M, Sakuma N, Murayama T. 2008. Cellular redox state protects acetaldehyde-induced alteration in cardiomyocyte function by modifying [Ca.sup.2+] release from sarcoplasmic reticulum. Am J Physiol Heart Circ Physiol 294(1):H121-H133.

Rager JE, Lichtveld K, Ebersviller S, Smeester L, Jaspers I, Sexton KG, et al. 2011. A toxicogenomic comparison of primary and photochemically altered air pollutant mixtures. Environ Health Perspect 1 19:1583-1589; doi:10.1289/ehp.1003323.

Sexton KG, Jeffries HE, Jang M, Kamens RM, Doyle M, Voicu I, et al. 2004. Photochemical products in urban mixtures enhance inflammatory responses in lung cells. Inhal Toxicol 16(suppl 1):107-114.

Tong H, Cheng WY, Samet JM, Gilmour MI, Devlin RB. 2010. Differential cardiopulmonary effects of size-fractionated ambient particulate matter in mice. Cardiovasc Toxicol 10(4):259-267.

Tong H, McGee JK, Saxena RK, Kodavanti UP, Devlin RB, Gilmour MI. 2009. Influence of acid functionalization on the cardiopulmonary toxicity of carbon nanotubes and carbon black particles in mice. Toxicol Appl Pharmacol 239(3):224-232.

Yang CY. 2008. Air pollution and hospital admissions for congestive heart failure in a subtropical city: Taipei, Taiwan. J Toxicol Environ Health A 71(16):1085-1090.

Rachel Mcintosh-Kastrinsky, (1) David Diaz-Sanchez, (2) Kenneth G. Sexton, (1) Corey M. Jania, (3) Jose Zavala, (1) Stephen L. Tilley, (3) Ilona Jaspers, (4) M. Ian Gilmour, (2) Robert B. Devlin, (2) Wayne E. Cascio, (2,5) and Haiyan Tong (2)

(1) Department of Environmental Sciences and Engineering, Gillings School of Global Public Health, University of North Carolina at Chapel Hill, Chapel Hill, North Carolina, USA; (2) Environmental Public Health Division, National Health and Environmental Effects Research Laboratory, U.S Environmental Protection Agency, Research Triangle Park, North Carolina, USA; (3) Department of Medicine, Division of Pulmonary and Critical Care Medicine, (4) Center for Environmental Medicine, Asthma, and Lung Biology, and (5) Department of Medicine, Division of Cardiology, School of Medicine, University of North Carolina at Chapel Hill, Chapel Hill, North Carolina, USA

Address correspondence to H. Tong, Environmental Public Health Division, NHEERL/U.S. EPA, 109 T.W. Alexander Dr., Research Triangle Park, NC 27711 USA. Telephone: (919) 966-4993. E-mail:

We thank B. O'Brien for excellent technical assistance in the execution of this study. We also thank Y. Ge for review of the manuscript.

The U.S. Environmental Protection Agency (EPA) Intramural Research Program supported this research. This work was also supported in part by the U.S. EPA Cooperative Agreement CR83346301 with the Center for Environmental Medicine, Asthma and Lung Biology at the University of North Carolina at Chapel Hill.

The research described in this article has been reviewed by the National Health and Environmental Effects Research Laboratory, U.S. EPA, and approved for publication. The contents of this article should not be construed to represent agency policy nor does mention of trade names or commercial products constitute endorsement or recommendation for use.

The authors declare they have no actual or potential competing financial interests.

Received: 4 February 2013; Accepted: 17 October 2013; Advance Publication: 22 October 2013; Final Publication: 1 December 2014.

Table 1. Average concentrations (ppb) of compounds
measured in the photoreaction chamber.

Chemical                           Pollutant exposure

                              Mixtures    [O.sub.3]   FA

[O.sub.3]                          243          245      10
NO                                   0            0       1
N[O.sub.2]                          18            4       7
CO                                 500          300     300
Peroxyacetyl nitrate               1.3        < 0.2   < 0.2
Formaldehyde                      64.2         12.2    12.2
Acetaldehyde                      22.1            0       0
Acetone                           11.1            0       0
2-Hexanone                        17.1            0       0
Glyoxal                           11.7          0.6     0.6
Methylglyoxal                     15.7          0.8     0.8
Unknown cluster                   74.9          9.5     9.5
Estimated total carbonyls        286.0         23.1    23.1
Total organic precursors         2,000         < 20    < 20
Alkanes (23 total)               1,133
  Isopentane                       173
  n-Butane                         147
  Propane                           92
  Ethane                            77
Alkenes (16 total)                 262
  Ethene                            53
  2,3,3-Trimethyl-1 -butene         32
  cis-2-Pentene                     27
  trans-2-Butene                    23
Aromatics (13 total)               605
  Toluene                          138
  1,2,4-Trimethylbenezene          112
  m-Xylene                          74
  Benzene                           44

CO, carbon monoxide; FA, filtered air; mixtures,
multi-pollutant mixtures.

[O.sub.3], NO, N[O.sub.2], and CO were measured every
minute during the exposure period and averaged for
reporting. The other compounds were measured every 15
min during the exposure period. All samples were
measured by gas chromatography and mass spectrometry,
using a direct cryogenically trapped sample taken
from the chamber. Because the exposures were conducted
in the dark, concentrations were stable and homogeneous.

Table 2. Hemodynamic measures (means [+ or -] SEs)
of isolated mouse hearts.

Experimental group             FA (n = 8)

Baseline condition

  Heart rate (bpm)            331 [+ or -] 10
  LVDP (cm[H.sub.2]O)       146.4 [+ or -] 14.8
  dP/[dt.sub.maximum]       5,405 [+ or -] 400
  dP/[dt.sub.minimum]      -3,675 [+ or -] 242
  Coronary flow rate          2.0 [+ or -] 0.2

At 40 min of reperfusion

  Heart rate (bpm)            290 [+ or -] 21
  LVDP (cm[H.sub.2]O)        33.5 [+ or -] 11.4
  dP/[dt.sub.maximum]       1,418 [+ or -] 467
  dP/[dt.sub.minimum]        -801 [+ or -] 257
  Coronary flow rate          1.6 [+ or -] 0.1

Experimental group            [O.sub.3] (n = 6)

Baseline condition

  Heart rate (bpm)            280 [+ or -] 10 *
  LVDP (cm[H.sub.2]O)       134.2 [+ or -] 25.4
  dP/[dt.sub.maximum]       4,070 [+ or -] 704
  dP/[dt.sub.minimum]      -2,477 [+ or -] 407 *
  Coronary flow rate          1.6 [+ or -] 0.3

At 40 min of reperfusion

  Heart rate (bpm)            278 [+ or -] 28
  LVDP (cm[H.sub.2]O)        86.5 [+ or -] 34.9
  dP/[dt.sub.maximum]       2,963 [+ or -] 1212
  dP/[dt.sub.minimum]      -1,751 [+ or -] 674
  Coronary flow rate          1.2 [+ or -] 0.2

Experimental group            Mixtures (n = 7)

Baseline condition

  Heart rate (bpm)            286 [+ or -] 30
  LVDP (cm[H.sub.2]O)        69.2 [+ or -] 16.0 *
  dP/[dt.sub.maximum]       2,764 [+ or -] 558 *
  dP/[dt.sub.minimum]      -1,822 [+ or -] 335 **
  Coronary flow rate          1.8 [+ or -] 0.2

At 40 min of reperfusion

  Heart rate (bpm)            280 [+ or -] 23
  LVDP (cm[H.sub.2]O)        38.0 [+ or -] 8.8
  dP/[dt.sub.maximum]       1,612 [+ or -] 352
  dP/[dt.sub.minimum]        -872 [+ or -] 150
  Coronary flow rate          1.5 [+ or -] 0.2

dP/[dt.sub.maximum], maximum first derivative of
the change in left ventricular pressure/time;
dP/[dt.sub.minimum], minimum first derivative of
the change in left ventricular pressure/time.

* p < 0.05, and ** p < 0.01, compared with FA
control group by Kruskal-Wallis U-test followed
by Dunn's multiple comparison.


Please note: Illustration(s) are not available due to copyright restrictions.
COPYRIGHT 2013 National Institute of Environmental Health Sciences
No portion of this article can be reproduced without the express written permission from the copyright holder.
Copyright 2013 Gale, Cengage Learning. All rights reserved.

Article Details
Printer friendly Cite/link Email Feedback
Title Annotation:Research
Author:McIntosh-Kastrinsky, Rachel; Diaz-Sanchez, David; Sexton, Kenneth G.; Jania, Corey M.; Zavala, Jose;
Publication:Environmental Health Perspectives
Article Type:Report
Date:Nov 1, 2013
Previous Article:Disruption of aryl hydrocarbon receptor homeostatic levels during embryonic stem cell differentiation alters expression of homeobox transcription...
Next Article:Population-based biomonitoring of exposure to organophosphate and pyrethroid pesticides in New York City.

Terms of use | Privacy policy | Copyright © 2021 Farlex, Inc. | Feedback | For webmasters