Abstract

Ambient particulate matter (PM) was sampled in Zabrze (southern Poland) in the heating period of 2009. It was investigated for distribution of its mass and of the masses of its 18 component elements (S, Cl, K, Ca, Cr, Mn, Fe, Ni, Cu, Zn, Ge, As, Br, Sr, Cd, Sb, Ba, and Pb) among 13 PM size fractions. In the paper, the distribution modality of and the correlations between the ambient concentrations of these elements are discussed and interpreted in terms of the source apportionment of PM emissions. By weight, S, Cl, K, Ca, Cr, Mn, Fe, Ni, Cu, Zn, Ge, As, Br, Sr, Cd, Sb, Ba, and Pb were 10 % of coarse and 9 % of ultrafine particles. The collective mass of these elements was no more than 3.5 % of the mass of the particles with the aerodynamic diameter Dp between 0.4 and 1.0 μm (PM0.4–1), whose ambient mass concentration was the highest. The PM mass size distribution for the sampling period is bimodal; it has the accumulation and coarse modes. The coarse particles were probably of the mineral/soil origin (characteristic elements: Ca, Fe, Sr, and Ba), being re-suspended polluted soil or road dust (characteristic elements: Ca, Fe, Sr, Ba, S, K, Cr, Cu, Zn, Br, Sb, Pb). The maxima of the density functions (modes) of the concentration distributions with respect to particle size of PM-bound S, Cl, K, Cu, Zn, Ge, Br, Cd, Sb, and Pb within the Dp interval from 0.108 to 1.6 μm (accumulation PM particles) indicate the emissions from furnaces and road traffic. The distributions of PM-bound As, Mn, Ba, and Sr concentrations have their modes within Dp ≤ 0.108 μm (nucleation PM particles), indicating the emissions from high-temperature processes (industrial sources or car engines). In this work, principal component analysis (PCA) is applied separately to each of the 13 fraction-related sets of the concentrations of the 18 PM-bound elements, and further, the fractions are grouped by their origin using cluster analysis (CA) applied to the 13 fraction-related first principal components (PC1). Four distinct groups of the PM fractions are identified: (PM1.6–2.5, PM2.5–4.4,), (PM0.03–0.06, PM0.108–0.17), (PM0.06–0.108, PM0.17–0.26, PM0.26–0.4, PM0.4–0.65, PM0.65–1, PM1–1.6), and (PM4.4–6.8, PM6.8–10, PM>10). The PM sources attributed to these groups by using PCA followed by CA are roughly the same as the sources from the apportionment done by analyzing the modality of the mass size distributions.

Highlights

  • Airborne particles can absorb practically any air contaminant

  • The particulate matter (PM) toxicity derives rather from the synergistic effects of physicochemical properties of the particles and the environmental circumstances (Saldiva et al 2002; Wellenius et al 2003); the elemental content of PM is proved to decide on the potential health effects of PM

  • In Zabrze and other Upper Silesian cities, the PM concentrations can be significantly higher at the turn of the year and in January–February (Pastuszka et al 2010; Rogula-Kozłowska et al 2014)

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Summary

Introduction

Airborne particles can absorb practically any air contaminant. This capability of particulate matter (PM), due240 Page 2 of 16 to its physicochemical properties, makes PM a great threat to human health, especially in big cities (Molina and Molina 2004; Lee and Lee 2008; Kong et al 2012). Airborne particles can absorb practically any air contaminant. This capability of particulate matter (PM), due. 240 Page 2 of 16 to its physicochemical properties, makes PM a great threat to human health, especially in big cities (Molina and Molina 2004; Lee and Lee 2008; Kong et al 2012). The exact mechanisms of the PM toxic action on living organisms remain unknown (Dreher 2000; Harrison and Yin 2000). The PM toxicity derives rather from the synergistic effects of physicochemical properties of the particles and the environmental circumstances (Saldiva et al 2002; Wellenius et al 2003); the elemental content of PM is proved to decide on the potential health effects of PM. Being water-soluble, they become bioavailable after entering water or soil

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