Skip to content

EHP

Research Volume 121 | Issue 5 | May 2013

Environ Health Perspect; DOI:10.1289/ehp.1205793

Cardiovascular Outcomes and the Physical and Chemical Properties of Metal Ions Found in Particulate Matter Air Pollution: A QICAR Study

Qingyu Meng,1 Jennifer Richmond-Bryant,2 Shou-En Lu,1 Barbara Buckley,2 William J. Welsh,3 Eric A. Whitsel,4,5 Adel Hanna,6 Karin B. Yeatts,5 Joshua Warren,7 Amy H. Herring,7 and Aijun Xiu6

Author Affiliations open
1School of Public Health, University of Medicine and Dentistry of New Jersey, Piscataway, New Jersey, USA; 2National Center for Environmental Assessment, U.S. Environmental Protection Agency, Research Triangle Park, North Carolina, USA; 3Robert Wood Johnson Medical School, University of Medicine and Dentistry of New Jersey, Piscataway, New Jersey, USA; 4Department of Medicine, 5Department of Epidemiology, 6Institute for the Environment, and 7Department of Biostatistics, University of North Carolina at Chapel Hill, Chapel Hill, North Carolina, USA

PDF icon PDF Version (397 KB)

  • Background: This paper presents an application of quantitative ion character–activity relationships (QICAR) to estimate associations of human cardiovascular (CV) diseases (CVDs) with a set of metal ion properties commonly observed in ambient air pollutants. QICAR has previously been used to predict ecotoxicity of inorganic metal ions based on ion properties.

    Objectives: The objective of this work was to examine potential associations of biological end points with a set of physical and chemical properties describing inorganic metal ions present in exposures using QICAR.

    Methods: Chemical and physical properties of 17 metal ions were obtained from peer-reviewed publications. Associations of cardiac arrhythmia, myocardial ischemia, myocardial infarction, stroke, and thrombosis with exposures to metal ions (measured as inference scores) were obtained from the Comparative Toxicogenomics Database (CTD). Robust regressions were applied to estimate the associations of CVDs with ion properties.

    Results: CVD was statistically significantly associated (Bonferroni-adjusted significance level of 0.003) with many ion properties reflecting ion size, solubility, oxidation potential, and abilities to form covalent and ionic bonds. The properties are relevant for reactive oxygen species (ROS) generation, which has been identified as a possible mechanism leading to CVDs.

    Conclusion: QICAR has the potential to complement existing epidemiologic methods for estimating associations between CVDs and air pollutant exposures by providing clues about the underlying mechanisms that may explain these associations.

  • Citation: Meng Q, Richmond-Bryant J, Lu S, Buckley B, Welsh WJ, Whitsel EA, Hanna A, Yeatts KB, Warren J, Herring AH, Xiu A. 2013. Cardiovascular Outcomes and the Physical and Chemical Properties of Metal Ions Found in Particulate Matter Air Pollution: A QICAR Study. Environ Health Perspect 121:558–564; http://dx.doi.org/10.1289/ehp.1205793

    Address correspondence to J. Richmond-Bryant, 109 T.W. Alexander Dr., MC B243-01, Research Triangle Park, North Carolina 27711 USA. Telephone: (919) 541-4518. E-mail: richmond-bryant.jennifer@epa.gov

    We thank A. Farraj for his helpful comments in review of this manuscript.

    The research and this manuscript have been reviewed in accordance with U.S. Environmental Protection Agency (EPA) policy and approved for publication. Mention of trade names or commercial products does not constitute endorsement or recommendation for use. The views expressed in this article are those of the authors and do not necessarily reflect the views or policies of the U.S. EPA.

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

    Received: 19 July 2012
    Accepted: 4 March 2013
    Advance Publication: 5 March 2013
    Final Publication: 1 May 2013

  • PDF icon Supplemental Material (840 KB) PDF

Changes in the cardiovascular (CV) system may occur if particulate matter (PM) exposure initiates pulmonary oxidative stress and inflammation and/or pulmonary reflex responses. These responses can lead to adverse outcomes such as stroke, myocardial ischemia, and myocardial infarction [Brook et al. 2004, 2010; Chuang et al. 2007; Mills et al. 2007; U.S. Environmental Protection Agency (EPA) 2009; Zhang et al. 2009], as illustrated by the potential pathways for PM to affect the CV system (Figure 1). Oxidative stress occurs when the burden of reactive oxygen species [ROS (oxygen radicals and non-radical oxygen derivatives)] at a target site is larger than the target site’s antioxidant reserve (Halliwell and Gutteridge 2007). Oxidative stress can lead to altered cell signaling, DNA injury, or apoptosis (U.S. EPA 2009). In PM experimental exposure studies of in vitro macrophage cytotoxicity (Becker et al. 2002; Hatch et al. 1985) and in vivo intratracheal instillation in mice, oxidative stress was associated more strongly with PM components such as metal ions than with PM mass. Oxidative stress induced by exposure to metal ions can occur directly or indirectly (Ercal et al. 2001). When occurring directly, oxidation–reduction (redox)-active metal ions in PM, such as iron (Fe) and copper (Cu), have been shown to cause ROS formation through experimental in vitro testing of normal human bronchial epithelial and alveolar macrophage cells (Becker et al. 2005), an electron paramagnetic resonance assay (Boogaard et al. 2012), and a dithiothreitol assay (Cho et al. 2005) to replicate oxidation in the lung. Redox-active metal ions in PM participate in the Fenton reaction to produce the hydroxyl radical (OH), which is subsequently involved in ROS production (Cho et al. 2005; Shafer et al. 2010). Redox-inactive metal ions, such as cadmium (Cd) and lead (Pb), can reduce antioxidant levels in cells by forming complexes with antioxidants; this condition leaves the cell vulnerable to oxidation, as described by Ercal et al. (2001) and observed through imaging experiments employing hydrogen peroxide–specific and redox-specific fluorophores (Cheng et al. 2010). PM components, including metal ions, have been shown to move into the circulation in animal models (Nemmar et al. 2001; Oberdörster et al. 2002) and controlled human exposure studies (Nemmar et al. 2002), but it is unclear whether they remain free or become sequestered (Brook et al. 2004). The location of oxidative stress within the body can also be affected by other ion properties, such as solubility in lipids or epithelial lining fluid and electron exchange properties of metal ions, for both redox-active and redox-inactive metal ions (Miyata and van Eeden 2011). A rat inhalation study suggested that exposure to metal ions in PM may cause oxidative stress in the lung, leading to the production and release of proinflammatory cytokines and endothelin-1 into the circulatory system (Thomson et al. 2005). These mediators could then travel to the heart and blood vessels, where they may mediate downstream inflammatory effects (Brook et al. 2010). Alternatively, an epidemiology panel study of greater Boston-area coronary artery disease patients exhibiting ST segment depression suggested that exposure to both gaseous and particulate air pollutants may lead to the activation of pulmonary reflexes and local inflammation and subsequent alteration of the autonomic nervous system, and resulting heart rate variability changes (Chuang et al. 2008). Markers of inflammation and autonomic imbalance have also been associated with exposure to gaseous and particulate air pollutants in an epidemiology panel of healthy young adults in Taipei, China (Chuang et al. 2007). We hypothesize that relevant physical and chemical properties of metal ions can be used to predict adverse CV outcomes initiated by oxidative stress.

Figure 1 - Diagram of conceptual model.  Details in legend and Introduction.Figure 1 – Potential pathways for effects of PM exposure on the cardiovascular system. The five end points examined here—arrhythmia, myocardial ischemia, myocardial infarction, thrombosis, and stroke—are shown on the diagram in gray boxes. Question marks denote areas of the potential mechanisms of action that are less certain. Conceptual model from Brook et al. (2010) and U.S. EPA (2009)

View larger image (TIF File)

Quantitative ion character–activity relationships (QICARs) can be used to examine associations between biological end points and a set of physical and chemical properties describing inorganic metal ions present in exposures. Further, QICARs have been used to predict ecotoxicity of inorganic metal ions on the basis of a set of physical and chemical properties (e.g., McCloskey et al. 1996; Newman et al. 1998; Ownby and Newman 2003; Walker et al. 2003). For example, the lethal or effective concentrations for 50% of species have been predicted by the physical and chemical properties of metal ions such as softness (σp) and the log of the first hydrolysis constant (|log(KOH)|) (Mendes et al. 2010; Ownby and Newman 2003; Williams et al. 1982). QICAR is a powerful tool for evaluating chemical toxicity because it allows for examination across compounds to determine which properties are more strongly associated with adverse responses. In turn, analysis of these properties may provide key insights into the biological mechanisms and pathways or target receptor(s) affected by metal ions. As mentioned above, health end points for humans [e.g. CV disease (CVD)] could also be linked with the physical and chemical properties of the chemicals to which people are exposed. However, to our knowledge, QICAR has not been applied in any human health studies.

The goal of this exploratory effort was to determine whether QICAR can be employed to study associations of adverse CVDs with human exposure to inorganic metal ions. QICAR appears to be a useful tool for elucidating important physical and chemical properties among redox-active and redox-inactive metal ions that may have adverse effects on CVD. In the present study, QICAR is applied to human health in the context of air pollution.

Methods

Data sources. Chemical and physical property data were obtained from physical chemistry reference handbooks for 17 metal ions commonly found in the atmosphere: lithium [Li(I)], sodium [Na(I)], potassium [K(I)], cesium [Cs(I)], magnesium [Mg(II)], calcium [Ca(II)], barium [Ba(II)], manganese [Mn(II)], iron [Fe(II)], cobalt [Co(II)], nickel [Ni(II)], silver [Ag(I)], copper [Cu(II)], zinc [Zn(II)], cadmium [Cd(II)], mercury [Hg(II)], and lead [Pb(II)] (James and Lord 1992; Kaye and Laby 1993). These physicochemical property data have been applied in several peer-reviewed QICAR studies (McCloskey et al. 1996; Mendes et al. 2010; Newman et al. 1998; Ownby and Newman 2003; Walker et al. 2003; Williams et al. 1982). Several of these metal ions (Pb, Hg, Mn, Ni) are well-known toxicants (Dreher et al. 1997; Ercal et al. 2001; Lippmann et al. 2006; Moriwaki et al. 2008). Properties included in this QICAR examination (Table 1) are related to the exchange of electrons and solubility of metal ions and, therefore, may be associated with ROS generation (Mendes et al. 2010; Walker et al. 2003). These properties include fundamental attributes of metal ions (e.g., ion mass, ion length scale) as well as solubility, softness, tendency of an ion to be oxidized, energy required for oxidation, oxidation state, oxidation energy, ability to produce hydroxyl ions (OH), and abilities to form covalent and ionic bonds. The value of each property for each metal ion is provided in Supplemental Material, Table S1 (http://dx.doi.org/10.1289/ehp.1205793). In addition to evaluating associations with the properties of the individual metal ions, we evaluated associations according to two groups of metal ions. The s-block group comprised Li, Na, K, Cs, Mg, Ca, and Ba, which are from the s-block of the periodic table. The transition group included the transition metal ions Mn, Fe, Co, Ni, Ag, Cu, Zn, and Hg from the d-block of the periodic table, which can have multiple oxidation states. Although Pb is from the p-block of the periodic table, it was included with the transition metal ions for this analysis because it also has multiple oxidation states.

Table 1 - See HTML link for full tableTable 1 – The ROS generation–related properties of metal ions used in the analysis.

View Table (HTML Version)
View larger image (TIF File)

Associations of CVDs with metal ion exposures examined in this analysis came from the publicly available Comparative Toxicogenomics Database (CTD; Davis et al. 2009, 2011). The CTD is a curated database of known interactions between chemicals and genes, genes and diseases, and infrequently, chemicals and diseases. Chemical–disease relationships are inferred in the CTD using established evidence of either chemical × gene and gene × disease interactions or chemical × disease interactions observed in curated laboratory studies within the CTD database. Chemical × gene or chemical × disease interactions curated in the CTD can include any study that demonstrates a chemical exposure can lead to a change in gene or disease status through any exposure pathway (Davis et al. 2009, 2011). The CTD database focuses on environmental chemicals and outcomes relevant to human health, but inferences may be based in part on information from animal studies if the animal contains a gene that is also present in humans and the study elucidates the effect of a chemical on the gene or a gene on a disease outcome.

Within the CTD, inference score is a measure of the degree of support for a given association between a disease and a chemical. An inference score is computed using principles of scale-free networks, where the probability (P) that a vertex in a large network interacts with another vertex decays according to a power law (Barabasi and Albert 1999). A vertex in the CTD can be a gene (G), chemical (C), or disease (D) with some number of connections (k) between them. For a set of nG genes, the inference score (Y) is computed as shown below (Li and Liang 2009):

Y = –ln[P(G associated with both C and D|k, nG)P(no other G connects C and D|k, nG)]. [1]

Each inference score used in this analysis is the log transform of the product of two probability functions: a) the probability that a gene is associated with both a chemical and a disease, and b) the probability that the chemical–gene–disease connection is unique. The CTD curates data for chemical × disease and gene × disease interactions for 27 disease categories, including CVDs. Within the CVD category, five end points were selected for this study based on the potential relevance of oxidative stress mechanisms to their development: cardiac arrhythmia, myocardial ischemia, myocardial infarction, stroke, and thrombosis (Godleski et al. 2000; Longhurst et al. 2001; U.S. EPA 2009). Inference score data for each CVD end point–metal ion pair is provided in Supplemental Material, Table S2 (http://dx.doi.org/10.1289/ehp.1205793). Arrhythmia inference scores were available for 6 of 7 s-block metal ions and 7 of 10 transition metal ions, myocardial infarction inference scores were available for 5 s-block metal ions and 8 transition metal ions, myocardial ischemia inference scores were available for 5 s-block metal ions and 9 transition metal ions, and thrombosis and stroke inference scores were available for 5 s-block metal ions and 10 transition metal ions.

Statistical analysis. All statistical analyses were conducted with SAS version 9.1 (SAS Institute Inc., Cary, NC). For each CVD end point, least-trimmed squares (LTS) regression was used to estimate associations of log-transformed inference scores for a set of metal ions (s-block or transition) with their ion properties. LTS regression minimizes the influence of outliers on the model fit (Rousseeuw and Hubert 2011; Rousseeuw and Leroy 2003). Rather than minimize the sum of squared residuals for all data points included in ordinary least squares regression, LTS minimizes the sum of squared residuals for a subset of data points that minimizes the sum of squared residuals to remove the influence of outliers from the regression. Trimmed data points are those data points excluded from the minimized sum of squared residuals function, and the number of trimmed data points (ntrim) is determined separately for each outcome and metal ion group model. The default approach provided by SAS (PROC ROBUSTREG) was employed to calculate LTS breakdown values to determine ntrim. Breakdown values estimate the smallest proportion of data that, if erroneous, could bias the estimator. Breakdown values for the simulations ranged from 8 tto 20%.

The overall significance level was 0.05. Given that 16 properties were tested, the multiple comparisons design led to a Bonferroni-corrected significance level of 0.003 (or 0.05/16). Log transformation of the inference scores was applied to reduce heteroscedascity and more closely meet the statistical modeling assumptions.

Given collinearity between several ion properties, only one ion property was used in a univariate regression each time as a predictor (Table 2). Scatter plots were developed during exploratory analysis to visualize the data [Figure 2 shows an example for atomic number (AN)]. Examination of these scatter plots revealed that the properties tended to cluster around the type of metal ion (i.e., s-block or transition), with potentially different slopes for each group. Therefore, LTS regressions for each disease–property combination were performed separately for s-block and transition metal ions. Slopes obtained from the LTS regressions are presented both as 1-unit changes in properties and as standardized by the interquartile range (IQR) of the property distribution.

Table 2 - See HTML link for full tableTable 2 – Spearman correlation coefficients among the physical and chemical properties across the metal ions included in the QICAR models.

View Table (HTML Version)
View larger image (TIF File)

Figure 2 - Five scatterplots, y-axis = log(inference score) for each outcome (cardiac arrhythmia, myocardial infarction, myocardial ischemia, stroke, thrombosis), x-axis = atomic number, data points = individual observations (metal ions) according to group (s-block or transition metal ions).  Details in legend and Methods under Statistical Analysis.Figure 2 – Scatter plots of ln(Inference Score) vs. AN for each CV end point. Arrhythmia (A), myocardial infarction (B), myocardial ischemia (C), stroke (D), and thrombosis (E). The solid lines represent LTS robust regressions for the s-block metal ions, and the dashed lines represent LTS robust regressions for the transition metal ions. All data points (trimmed and nontrimmed) are shown in the figure with the robust regression lines.

View larger image (TIF File)

To evaluate whether the results were sensitive to specific regression methods, additional regression approaches were also used to examine the robustness of the LTS results. Other regression approaches included in the analysis were maximum likelihood type robust (M) estimation (Huber 1973), minimization of robust scale (S) estimation (Rousseeuw and Yohai 1984), and high breakdown/high efficiency robust (MM) estimation (Yohai 1987). For M estimation, a bi-square weight function was applied. For MM and S estimations, the SAS default parameters in PROC ROBUSTREG for the MM and S options, respectively, were employed.

Because the data set had small sample sizes (i.e., it was limited to the number of metal ions included in each group evaluated), robustness of the LTS results was further evaluated via Monte Carlo simulation. The log-transformed inference scores, Yij, were sampled once from the corresponding normal distribution with a mean of β0,ikl + β1,iklxjk and a standard deviation of σikl for the ith disease, jth metal ion, kth metal ion property, and lth group (s-block vs. transition metal ions). β0 and β1 are the regression coefficients (treated as fixed values in the simulation) between log-transformed inference scores and metal ion properties, x is the metal ion property (treated as a fixed value in the simulation), and σ is the standard deviation of the regression residuals. The sampled Yij were regressed on xjk with the LTS approach for each combination of health end points, metal ion properties, and metal ion groups. The number of outliers [defined as Yij = (β0,ikl + β1,iklxjk) ± 3σikl ] included in each simulated data set was greater than the number of outliers identified by LTS in the original data set. The procedure was repeated 1,000 times. Centrality and variability of the regression coefficients based on the original data sets were compared with the simulation results.

Model validation. Validation of selected models was performed where data were available in the CTD and properties databases. Because there are more transition metal ions than s-block metal ions, four cardiac arrhythmia models were chosen for validation: AN, σp, melting point (MP), and density (ρ) (Dean 1999; Hammond 2003; James and Lord 1992; Kaye and Laby 1993). Relative L2 error norms were computed to compare ln(Inference Score) predictions from the regression models input with property data for aluminum [Al(III)], chromium [Cr(VI)], and vanadium [V(V)]. In other words, the relative L2 error norm approaches zero as the predicted ln(Inference Score) approaches that from the CTD. Relative L2 error norm is computed as

ehp.1205793.e001[2]

Results and Discussion

All associations between inference scores and ion properties (robust univariate regressions) are summarized [see Supplemental Material, Tables S3–S7 (Figure 2. Table 3 presents significant LTS regression results, with p-values of the slopes < 0.003. Table 3 also provides data for the number of metal ions included and trimmed from the robust model, SE, significance level, and coefficient of determination (R2). Table 4 displays a matrix illustrating statistically significant associations between inference scores and properties for each metal ion grouping (s-block or transition metal ions).

Table 3 - See HTML link for full tableTable 3 – The associations between the inference score relating CVD to metal exposures with the physical and chemical properties of metal ions using robust univariate regressions.

View Table (HTML Version)
View larger image (TIF File)

Table 4 - See HTML link for full tableTable 4 – The statistically significant associations (p < 0.003) between the CTD inference score relating CVD to metal exposures, and the physical and chemical properties of metal ions, by the groups of metal ions (s-block and transition metal ions).

View Table (HTML Version)
View larger image (TIF File)

Evaluation of the LTS regression results through comparison with other robust estimation methods and Monte Carlo simulations to address small sample size lend confidence to the results. LTS regression produced slopes that were often comparable to those associated with the other robust estimation approaches [see Supplemental Material, Tables S8–S12 (http://dx.doi.org/10.1289/ehp.1205793)]​,with equivalent slopes produced by the four methods for 50% of the simulations and slopes within 20% of each other for 63% of the simulations. The Monte Carlo simulation results also confirmed the robustness of slopes (see Supplemental Material, Tables S13–S17) by predicting the model slopes within ± 3%, although the SE of the LTS results tended to underestimate the SE computed during the Monte Carlo simulations. The LTS approach is very robust to outliers (Nevitt and Tam 1998; You 1999).

The validation exercise produced L2 error norms (i.e., the relative difference between the predicted inference score and the CTD inference score) for AN, σp, MP, and ρ of 29%, 14%, 25%, and 41%, respectively. These L2 error norms are high, but given that data from only three metals were used to validate the models, they suggest a reasonable fit.

Associations between health outcomes and properties varied among the diseases and metal ion groupings. Cardiac arrhythmia was not associated with any properties for the s-block elements (Tables 3 and 4). For the transition elements, cardiac arrhythmia was associated with ion mass and length scale (AN and ρ), solubility (MP), softness (σp), and the ability to form covalent bonds (Xm2r). Myocardial infarction was associated with two properties for the s-block element models and none for the transition metal ion models: ion mass (AN) and oxidation energy (AN/ΔIP). Myocardial ischemia was associated with six properties for the s-block metal ion models and none for the transition metal ion models. For the s-block metal ions, associations were observed for ion size [AN, AR, r], oxidation energy (AN/ΔIP), and ability to form covalent bonds (Xm, Xm2r). Stroke was associated with five properties for the s-block metal ion models and none for the transition metal ion models. For the s-block metal ions, associations were observed for ion mass (AN), solubility (MP), softness (σp), ability to form covalent bonds (Xm2r), and ability to form ionic bonds (Z). Thrombosis was associated with two properties for the s-block metal ions, ion mass and length scale (ρ) and softness (σp), and three properties for the transition metal ions, ion length scale (AR), softness (σp), and the ability to form ionic bonds (Z/AR). Thrombosis was the only end point for which both the s-block and transition metal ions had significant models.

Similarities and differences among the regression models are apparent for the health end points. The slopes, based on unit and IQR changes, were similar in magnitude and sign for myocardial ischemia and myocardial infarction for AN, AN/ΔIP, log(KOH), and ρ [see Supplemental Material, Tables S4 and S5, respectively (Table 3), suggest a common mechanistic pathway for both outcomes among the metal ions examined. Myocardial infarction is a severe potential consequence of myocardial ischemia, to which altered vasoreactivity, atherosclerotic plaque formation, and thrombosis may contribute (Figure 1). Estimated slopes for associations between cardiac arrhythmia and metal ion properties tended to differ from estimated slopes for other outcomes. For example, slopes for AN, AN/ΔIP, and ρ varied in magnitude between cardiac arrhythmia and myocardial ischemia [see Supplemental Material, Tables S3 and S5, respectively (http://dx.doi.org/10.1289/ehp.1205793)]​.The s-block model unit slope for AN was an order of magnitude lower for cardiac arrhythmia (0.00583) compared with myocardial infarction (0.0504) and myocardial ischemia (0.0584). It is possible that these observed differences reflect the role of autonomic nervous system imbalance in the development of cardiac arrhythmia (see also Campese et al. 2004; Creason et al. 2001; Gold et al. 2000; He et al. 2010, 2011; Liao et al. 2009, 2010; Pope et al. 1999). Differences were observed between the statistically significant property-based models for thrombosis and stroke. It is possible that differences among the stroke and thrombosis models may relate to etiologic differences between strokes of hemorrhagic, rather than thromboembolic, origin. Previous epidemiologic studies have reported associations between PM, nitrogen dioxide, carbon monoxide, and ozone with ischemic (i.e., thromboembolic) but not hemorrhagic stroke (Hong et al. 2002; Wellenius et al. 2005). However, the models for softness (σp) were statistically significant for stroke with s-block metal ions and for thrombosis with both s-block and transition metal ions.

Associations between CVD and transition metal ion exposure have been found in toxicological and epidemiologic studies. Farraj et al. (2011) exposed rats to a PM designed to mimic metal ion–containing residual oil fly ash by composing the PM of a mix of NiSO4 (nickle sulfate), Fe2SO4 [iron(II) sulfate], and NaVO3 [sodium vanadate(V)] and observed cardiac arrhythmias with concurrent autonomic changes, with the magnitude of autonomic change corresponding to low, medium, or high exposure group and no effect for the no exposure group. Given that Farraj et al. (2011) studied only transition metal ions, this is somewhat consistent with the findings that the transition metal ion properties were significantly associated with cardiac arrhythmia. However, Farraj et al. (2011) did not look at associations between cardiac arrhythmia and individual metal ion compounds, so it is not possible to discern whether relative differences among the properties had differential effects on arrhythmogenesis. An epidemiologic study of hospital admissions for CVD among older adults (> 64 years of age) in Atlanta, Georgia, by Suh et al. (2011) reported significant associations between myocardial ischemia and transition metals in PM exposure, but did not study cardiac arrhythmias. However, our results indicate that for the transition metal ions, myocardial ischemia is not statistically significantly associated with any other properties examined. Hence, the results do not provide strong support for or negation of Suh et al.’s (2011) observations. Based on the results of the QICAR models, none of the CV health outcomes were associated with ionic exchange of electrons for transition metal ions, in contrast with with s-block metal ions, which were associated with myocardial ischemia and myocardial infarction. However, all five adverse CV health outcomes were associated with ion size for both transition and s-block metal ions. Ion size or mass may reflect greater reactivity, possibly resulting from stronger interatomic forces associated with complexes involving large ions (Walker et al. 2003). Softness (σp) was found to be a statistically significant predictor of cardiac arrhythmia for transition metal ions (Table 3). Mendes et al. (2010) concluded that σp caused covalent bonding of the metal ions to biological ligands in a study of fungi toxicity. σp also provided the most statistically significant association with adverse species outcomes in several other ecotoxicology studies (McCloskey et al. 1996; Ownby and Newman 2003; Zhou et al. 2011).

There are several limitations of this work. First, the sample sizes were small because the number of s-block and transition metal ions is small in general, and only a subset is available in the CTD. Small sample size also limits the model validation, given that data from only three metal ions were available for validation. However, our analysis was intended to explore development of models potentially associating adverse CV end points and chemical and physical properties, rather than to establish definitive conclusions about these relationships. Furthermore, Monte Carlo simulations yielded slope estimates within ± 3%, which added confidence to the results. Second, the properties evaluated were moderately to highly correlated (Table 2), thus limiting the linear regression analyses to univariate regressions. More sophisticated multivariate approaches not constrained by collinearity (e.g., partial least square regressions) need to be tested to examine further the associations between disease outcomes and ion properties. Third, the CTD is likely subject to selection bias because the inference scores reflect both data availability and inference of association between each chemical–disease pair in question. Moreover, given that the CTD inferred associations between disease outcomes and chemical exposures, the CTD may not have been limited to inhalation exposures, which is the primary exposure pathway for air pollutants. However, the inference score calculated within the CTD was attractive to use as a health outcome metric because it incorporates probabilities of association in a consistent manner across health outcomes and outcome–property pairs. These limitations will be addressed as the methodology of applying QICAR to human health outcomes is refined.

Conclusions

In this exploratory, hypothesis-generating work, we used QICAR to link human CVD and the properties of metal ions commonly observed in ambient PM. Cardiac arrhythmia, myocardial infarction, myocardial ischemia, stroke, and thrombosis were associated with some ion properties related to ROS generation. This work supports the feasibility of using ion properties to predict CVD. QICAR has the potential to complement existing epidemiologic methods for estimating associations between CVDs and air pollutant exposures by providing clues about the underlying mechanisms that may explain these associations. More sophisticated approaches will be applied to extend work to study the associations between diseases and properties of organic and inorganic chemicals.


References

Barabasi AL, Albert R. 1999. Emergence of scaling in random networks. Science 286:509–512.

Becker S, Dailey LA, Soukup JM, Grambow SC, Devlin RB, Huang YCT. 2005. Seasonal variations in air pollution particle-induced inflammatory mediator release and oxidative stress. Environ Health Perspect 113:1032–1038.

Becker S, Soukup JM, Gallagher JE. 2002. Differential particulate air pollution induced oxidant stress in human granulocytes, monocytes and alveolar macrophages. Toxicol In Vitro 16:209–218.

Boogaard H, Janssen NAH, Fischer PH, Kos GPA, Weijers EP, Cassee FR, et al. 2012. Contrasts in oxidative potential and other particulate matter characteristics collected near major streets and background locations. Environ Health Perspect 120:185–191.

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 109:2655–2671.

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 121:2331–2378.

Campese VM, Ye S, Zhong H, Yanamadala V, Ye Z, Chiu J. 2004. Reactive oxygen species stimulate central and peripheral sympathetic nervous system activity. Am J Physiol Heart Circ Physiol 287:H695–H703.

Cheng WY, Tong H, Miller EW, Chang CJ, Remington J, Zucker RM, et al. 2010. An integrated imaging approach to the study of oxidative stress generation by mitochondrial dysfunction in living cells. Environ Health Perspect 118:902–908.

Cho AK, Sioutas C, Schmitz DA, Kumagai Y, Singh M, Miguel AH, et al. 2005. Redox activity of airborne particulate matter (PM) at different sites in the Los Angeles Basin. Environ Res 99:40–47.

Chuang KJ, Chan CC, Su TC, Lee CT, Tang CS. 2007. The effect of urban pollution on inflammation, oxidative stress, coagulation, and autonomic dysfunction in young adults. Am J Respir Crit Care Med 176:370–376.

Chuang KJ, Coull BA, Zanobetti A, Suh H, Schwartz J, Stone PH, et al. 2008. Particulate air pollution as a risk factor for ST-segment depression in patients with coronary artery disease. Circulation 118:1314–1320.

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 11:116–122.

Davis AP, King BL, Mockus S, Murphy CG, Saraceni-Richards C, Rosenstein M, et al. 2011. The Comparative Toxicogenomics Database: update 2011. Nucleic Acids Res 39:D1067–D1072.

Davis AP, Murphy CG, Saraceni-Richards CA, Rosenstein MC, Wiegers TC, Mattingly CJ. 2009. Comparative Toxicogenomics Database: a knowledgebase and discovery tool for chemical–gene–disease networks. Nucleic Acids Res 37:D786–D792.

Dean JA (ed). 1999. Section 3; Table 3.2: Physical constants of inorganic compounds. In: Lange’s Handbook of Chemistry. 15th ed. New York:McGraw-Hill. Available: http://fptl.ru/biblioteka/spravo4niki/de​an.pdf [accessed 19 March 2013].

Dreher KL, Jaskot RH, Lehmann JR, Richards JH, McGee JK, Ghio AJ, et al. 1997. Soluble transition metals mediate residual oil fly ash induced acute lung injury. J Toxicol Environ Health 50:285–305.

Ercal N, Gurer-Orhan H, Aykin-Burns N. 2001. Toxic metals and oxidative stress. Part I: Mechanisms involved in metal induced oxidative damage. Curr Top Med Chem 1:529–539.

Farraj AK, Hazari MS, Kaykal-Coates N, Lamb C, Winsett C, Winsett DW, et al. 2011. ST depression, arrhythmia, vagal dominance, and reduced cardiac micro-RNA in particulate-exposed rats. Am J Respir Cell Mol Biol 44:185–196.

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.

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

Halliwell B, Gutteridge J. 2007. Free Radicals in Biology and Medicine. New York:Oxford University Press.

Hammond CR. 2003. Section 4, Properties of the elements and inorganic compounds; melting, boiling, and critical temperatures of the elements. In: CRC Handbook of Chemistry and Physics. 84th ed. Boca Raton, FL:CRC Press, 4-1–4-158.

Hatch GE, Boykin E, Graham JA, Lewtas J, Pott F, Loud K, et al. 1985. Inhalable particles and pulmonary host-defense: in vivo and in vitro effects of ambient air and combustion particles. Environ Res 36:67–80.

He F, Shaffer ML, Rodriguez-Colon S, Yanosky JD, Bixler E, Cascio WE, et al. 2011. Acute effects of fine particulate air pollution on cardiac arrhythmia: the APCAR study. Environ Health Perspect 119:927–932.

He M, Ichinose T, Yoshida S, Nishikawa M, Mori I, Yanagisawa R, et al. 2010. Urban particulate matter in Beijing, China, enhances allergen-induced murine lung eosinophilia. Inhal Toxicol 22:709–718.

Hong YC, Lee JT, Kim H, Kwon HJ. 2002. Air pollution: a new risk factor in ischemic stroke mortality. Stroke 33:2165–2169.

Huber PJ. 1973. Robust regression: asymptotics, conjectures and Monte Carlo. Ann Stat 1:799–821.

James AM, Lord, MP. 1992. Macmillan’s Chemical and Physical Data. London:Macmillan.

Kaye GWC, Laby TH. 1993. Tables of Physical and Chemical Constants. 15th ed. London:Longman.

Li H, Liang S. 2009. Local network topology in human protein interaction data predicts functional association. PLoS ONE Jul 29. 4. (7):

Liao D, Shaffer ML, Rodriguez-Colon SM, He F, Li X, Wolbrette DL, et al. 2010. Acute adverse effects of fine particulate air pollution on ventricular repolarization. Environ Health Perspect 118:1010–1015.

Liao D, Whitsel EA, Duan Y, Lin HM, Quibrera PM, Smith R, et al. 2009. Ambient particulate air pollution and ectopy—the environmental epidemiology of arrhythmogenesis in Women’s Health Initiative study, 1999–2004. J Toxicol Environ Health A 72:30–38.

Lippmann M, Ito K, Chen LC, Hwang JS, Maciejczyk P. 2006. Cardiovascular effects of nickel in ambient air. Environ Health Perspect 114:1662–1669.

Longhurst JC. , Tjen-a-looi SC, Fu LW. 2001. Cardiac sympathetic afferent activation provoked by myocardial ischemia and reperfusion. Mechanisms and reflexes. Ann NY Acad Sci 940:74–95.

McCloskey JT, Newman MC, Clark SB. 1996. Predicting the relative toxicity of metal ions using ion characteristics: Microtox bioluminescence assay. Environ Toxicol Chem 15:1730–1737.

Mendes LF, Bastos EL, Stevani CV. 2010. Prediction of metal cation toxicity to the bioluminescent fungus gerronema viridilucens. Environ Toxicol Chem 29:2177–2181.

Mills NL, Tornqvist H, Gonzalez MC, Vink E, Robinson SD, Soderberg S, et al. 2007. Ischemic and thrombotic effects of dilute diesel-exhaust inhalation in men with coronary heart disease. N Engl J Med 357:1075–1082.

Miyata R, van Eeden SF. 2011. The innate and adaptive immune response induced by alveolar macrophages exposed to ambient particulate matter. Toxicol Appl Pharmacol 257:209–226.

Moriwaki H, Osborne MR, Phillips DH. 2008. Effects of mixing metal ions on oxidative DNA damage mediated by a Fenton-type reduction. Toxicol In Vitro 22:36–44.

Nemmar A, Hoet PHM, Vanquickenborne B, Dinsdale D, Thomeer M, Hoylaerts MF, et al. 2002. Passage of inhaled particles into the blood circulation in humans. Circulation 105:411–414.

Nemmar A, Vanbilloen H, Hoylaerts MF, Hoet PHM, Verbruggen A, Nemery B. 2001. Passage of intratracheally instilled ultrafine particles from the lung into the systemic circulation in hamster. Am J Respir Crit Care Med 164:1665–1668.

Nevitt J, Tam HP. 1998. A comparison of robust and nonparametric estimators under the simple linear regression model. MLRV 25:54–69.

Newman MC, McCloskey JT, Tatara CP. 1998. Using metal-ligand binding characteristics to predict metal toxicity: Quantitative ion character–activity relationships (QICARs). Environ Health Perspect 106:1419–1425.

Oberdörster G, Sharp Z, Atudorei V, Elder A, Gelein R, Lunts A, et al. 2002. Extrapulmonary translocation of ultrafine carbon particles following whole-body inhalation exposure of rats. J Toxicol Environ Health A 65:1531–1543.

Ownby DR, Newman MC. 2003. Advances in quantitative ion character-activity relationships (QICARs): using metal-ligand binding characteristics to predict metal toxicity. QSAR Comb Sci 22:241–246.

Pope CA III, Verrier RL, Lovett EG, Larson AC, Raizenne ME, Kanner RE, et al. 1999. Heart rate variability associated with particulate air pollution. Am Heart J 13:890–899.

Rousseeuw PJ, Hubert M. 2011. Robust statistics for outlier detection. WIREs Data Mining Knowl Discov 1:73–79; doi: 10.1002/widm.2.

Rousseeuw PJ, Leroy AM. 2003. Robust Regression and Outlier Detection. Hoboken, NJ:John Wiley & Sons.

Rousseeuw PJ, Yohai V. 1984. Robust regression by means of S estimators. In: Robust and Nonlinear Time Series Analysis (Franke J, Härdle W, Martin RD, eds). Lecture Notes in Statistics, Vol. 26. New York:Springer-Verlag, 256–274.

Shafer MM, Perkins DA, Antkiewicz DS, Stone EA, Quraishi TA, Schauer JJ. 2010. Reactive oxygen species activity and chemical speciation of size-fractionated atmospheric particulate matter from Lahore, Pakistan: an important role for transition metals. J Environ Monit 12:704–715.

Suh HH, Zanobetti A, Schwartz J, Coull BA. 2011. Chemical properties of air pollutants and cause-specific hospital admissions among the elderly in Atlanta, GA. Environ Health Perspect 119:1421–1428.

Thomson E, Kumarathasan P, Goegan P, Aubin RA, Vincent R. 2005. Differential regulation of the lung endothelin system by urban particulate matter and ozone. Toxicol Sci 88:103–113.

U.S. EPA (U.S. Environmental Protection Agency). 2009. Integrated Science Assessment for Particulate Matter. Final Report. EPA/600/R-08/139F. Research Triangle Park, NC:U.S.EPA, National Center for Environmental Assessment. Available: http://cfpub.epa.gov/ncea/cfm/recordispl​ay.cfm?deid=216546 [accessed 20 February 2013].

Walker JD, Enache M, Dearden JC. 2003. Quantitative cationic activity relationships for predicting toxicity of metal ions from physicochemical properties and natural occurrence levels. QSAR Comb Sci 26:522–527.

Wellenius GA, Schwartz J, Mittleman MA. 2005. Air pollution and hospital admissions for ischemic and hemorrhagic stroke among Medicare beneficiaries. Stroke 36:2549–2553.

Williams MW, Hoeschele JD, Turner JE, Jacobson KB, Christie NT, Paton CL, et al. 1982. Chemical softness and acute metal toxicity in mice and Drosophila. Toxicol Appl Pharmacol 63:461–469.

Wolterbeek HT, Verburg TG. 2001. Predicting metal toxicity revisited: general properties vs. specific effects. Sci Total Environ 279:87–115.

Yohai VJ. 1987. High breakdown point and high efficiency robust estimates for regression. Ann Stat 15:642–656.

You J. 1999. A Monte Carlo comparison of several high breakdown and efficient estimators. Comput Stat Data Anal 30:205–219.

Zhang ZM, Whitsel EA, Quibrera PM, Smith RL, Liao D, Anderson GL, et al. 2009. Ambient fine particulate matter exposure and myocardial ischemia in the Environmental Epidemiology of Arrhythmogenesis in the Women’s Health Initiative (EEAWHI) study. Environ Health Perspect 117:751–756.

Zhou DM, Li LZ, Peijnenburg WJGM, Ownby DR, Hendriks AJ, Wang P, et al. 2011. A QICAR approach for quantifying binding constants for metal-ligand complexes. Ecotoxicol Environ Saf 74:1036–1042.


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