Heavy Metals in Air Nanoparticles in Affected Industry Area
Abstract
The Moravian-Silesian Region is one of the most polluted sites by dust particles in the Czech Republic. Therefore, atmospheric concentrations of heavy metals as cadmium, cobalt, chromium, copper, nickel, lead, antimony, thallium, manganese, iron and zinc, were monitored at 10 localities in the region during summer of 2014. Heavy metals were monitored in 10 particle size classes from 18.3 nm to 9.93 μm. The percentage of the amount of heavy metals in the sum PM at all localities ranged from 0.2-2.5%. It was found that chromium, manganese, iron and zinc were mostly accumulated in dust particles with diameter greater than 1.6 μm. Lead, cadmium and antimony occur mainly in the class below 0.949 μm. These metals are more dangerous for human health, and can have potential carcinogenic effect. The influence of metallurgical industry evaluated on the basis of heavy metals in the individual particle size classes in the air within the Moravian-Silesian Region has not been unequivocally demonstrated.
The highest concentration of emissions of Particulate Matter (PM) in the atmosphere occurs in the Moravian-Silesian Region. The Ostrava-Karvina area is among the most polluted areas not only within the country but also in Europe. Inclusion among the areas with poor air quality is mainly due to excess concentrations of suspended particulate matter PM10. This is due to the high concentration of industries in this area. Metallurgical industry such as Třinecké železárny – Moravia Steel and ArcelorMittal Ostrava produces up to 590 t of PM/year in each company.
Metals in air are most often bound to dust particles that have a different aerodynamic diameter. In suspended particles, the ability to bind heavy metals increases with their decreasing size [1]. Heavy metals bound on dust particles in the air are affected by the processes occurring in the atmosphere only to a very low extent. Therefore, they can be used as useful indicators of pollution sources. The main anthropogenic sources of heavy metals as Vanadium (V), Cobalt (Co), Molybdenum (Mo), Nickel (Ni), Antimony (Sb), Chromium (Cr), Iron (Fe), Manganese (Mn) and Tin (Sn) include the combustion of fossil fuels; metals from industrial metallurgical processes are Arsenic (As), Cr, Copper (Cu), Mn and Zinc (Zn); road transport produces Fe, Barium (Ba), Lead (Pb), Cu, Zn and Cadmium (Cd) [2]. Metals from waste incineration are Zn, Pb, Cu, Cd and Mercury (Hg). Zn and Pb are mainly produced during the manufacture of iron and steel. During the processing of non-ferrous metals As, Sb, Cu, Zn, Pb, Cd and Hg are released into the atmosphere; during the production of copper it is Cu and Zn [3].
Trace elements originating from anthropogenic activities accumulate in fine-particulate matter with aerodynamic diameter < 2.5 μm, elements derived from natural sources are mainly present in particles larger than 2.5 μm [4]. These particles also contain metals released mainly from mechanical processes, e.g. resuspension of road dust, abrasion of tires and brake linings [5].
The solid particles contain particularly: V, Ni, Cd, Pb, which come from the high temperature processes such as the combustion of coal and waste [6]. Other metals such as Zn, Co, Mo, Cr come from both the mechanical and high temperature processes and occur in particles below and above 2.5 μm [7]. Iron, strontium (Sr) and barium accumulate mainly in larger particles with grain size 3–4 μm. This distribution of metals in PM is the result of a combination of processes in the atmosphere, local anthropogenic and natural resources, and remote transfer.
The impact of heavy metals on environment and human health is dependent on mobility of each metal and its occurrence in various components of the environment [8]. The long exposure of human organism to heavy metals is associated with many health risks e.g. development retardation, various forms of cancer and renal deficiency [9]. In addition, a long exposure can cause damage of plants, decrease of yield in agriculture, deterioration of soil structure and contamination of ground or surface water [10]. Many things manufactured from metal are endangered and damaged by accelerated corrosion [11]. Atmospheric deposition of heavy metals in the vicinity of metallurgical plants can influence the vegetation growing and can be responsible for damage of physiological functions of living organisms through food chains [12]. Approximately 70-90% of heavy metals are distributed in the particles of size smaller than PM10. The concentration of metals increases with decreasing particle size [13]. Potentially toxic metals, e.g. nickel, lead and cadmium are accumulated in the urban environment mainly in the particles of aerodynamic diameter < 1 μm [14].
The aim of this work is to identify priority occurrence of metal nanoparticles with possible identification of sources of influence on this distribution. Information on the distribution of metals in nanoparticles is new in the literature.
Various metals as Cd, Co, Cr, Cu, Ni, Pb, Sb, thallium (Tl), Mn, Fe and Zn were observed in nanoparticles in the air within the Moravian-Silesian Region, the Czech Republic. Sampling was performed in the summer season (from June to August) due to the assessment of the impact of large industrial sources as metallurgy and minimizing the impact of local heating on air quality.
Sampling of dust particles was performed at ten selected locations (Figure 1), using an electric low-pressure cascade impactor- ELPI+, Dekati Company. These 10 locations were chosen from the 40 sampling sites selected for monitoring the composition of PM. ELPI+ spectrometer was used for measuring the particle size distribution. The device can be used as on-line, using information about the number of particles, particle volume, weight of the particles, etc. from the software of the device, or also as an off-line device, capture of dust particles which can be subsequently subjected to chemical analysis. The cascade impactor system can separate the particle matter following aerodynamic equivalent cut-off diameter at 50% efficiency in 14 particle size fractions ranging from 18.3 nm to 9,930 nm. The particles are charged in a positive unipolar particle charger – corona charger according to their Stokes diameter before entering the impactor stages. After being charged by the corona charger, the atmospheric particles are introduced in the impactor in order to be classified owing to their aerodynamic diameter and inertia. A multistage electrometer enables counting the charged aerosol particles. The current is simultaneously measured for the 14 impactor stages and directly converted by the electrometer in particles number and concentrations using mathematical algorithms [15].
Samřpling sites: Ostrava Radvanice (1); Trřnec (2); Trřnec Oldrichovice (3); Ostrava Mariánské Hory (4); Havířov (5); Frýdek Místek (6); Karvináη (7); Ostravice (8); Ostrava Poruba (9); Hradec nad Moravicí (10)
To determine the distribution of iron in emissions, particulate sampling was performed using gravimetric isokinetic kit TESO GTE equipped with the control and evaluation system IZOMAT. Particulate sampling was carried out applying the method ISO 9096/EPA/CSN EN 14385 by the company Technical Services for Air Protection Ostrava - TESO Ostrava. Emissions were categorized into three particle size classes: below 2.5 μm, 2.5–10 μm, and over 10 pm. Emissions were sampled from ten large energy sources at 16 boilers, six technological processes in the two ironworks: ArcellorMittal and Třinecké železárny – Moravia Steeland for four technological processes in the coking plants.
Samples of emissions and air pollution were decomposed in the microwave equipment in a mixture of acids HF, HCl, HNO3 and H2O2, followed by ICP analysis carried out in the laboratories of the Czech Geological Survey (CGS), Prague. For samples from two localities, namely Ostrava Marianské Hory and Ostrava Radvanice, the chemical nature of the particles in the class below 1 ^m was monitored using microanalysis. Analysis of PM10 particles retained on the filters was performed by Scanning Electron Microscope (SEM) (FEI Quanta 650 FEG), using the energy dispersive analyser EDAX.
Based on the mineralogical analysis of Total Suspended Particles (TSP), specifically content of hematite [16] and magnetite [17], the localities were divided into 4 groups. Hematite and magnetite are among the typical minerals forming PM that are associated with metallurgical processes, or they are used as raw materials in these processes. Matysek et al., reported that PM consisting of hematite and magnetite are able to bind heavy metals [18].
Localities significantly affected by the metallurgical industry – 1, 2 and 3;
Localities affected by the metallurgical industry – 4, 5 and 6;
Localities less significantly affected by the metallurgical industry – 7 and 8;
Localities not affected by the metallurgical industry – 9 and 10.
The presence and distribution of heavy metals was studied in 10 particle size classes from 18.3–93.7 nm, 93.7–156 nm, 156–263 nm, 263–383 nm, 383–614 nm, 614–949 nm, 949 nm–1.6 μm, 1.6–2.39 μm, 2.39–6.69 μm and 6.69–9.93 μm (Figure 2).
Concentration of sum of heavy metals in PM10 particle size class
From the sum of metals in PM (Figure 3), it is evident that they occurred mainly in the grain size classes: 0.093–0.156 μm, 0.383–0.949 μm, 0.949–1.6 μm, and 6.69–9.93 μm. The results stated in Table 1 show that based on the arithmetic average for the 10 localities, most metals occur mainly in the class from 1 to 2.5 μm, namely Cd, Co, Pb, Sb, and Zn, only the concentration of Cu and Ni is higher in the class from 2.5–9.93 μm. For metals Cd, Tl, Pb, it has been found that a substantial amount is present in the particle size class PM 1 – 2.5 μm. The concentration of manganese, iron and chromium are almost comparable in both particle size classes 1–2.5 μm, 2.5–9.93 μm. In the class below one μm, mostly secondary aerosols composed of sulphates, nitrates, ammonium ions, and Ca2+, Mg2+, Na+, K+ ions occur [18], therefore the metal content is minimal.
Concentrations of sum of heavy metals in < PM1, PM1-2.5, PM2.5-10 classes
[μm] |
N total |
Mean |
St. deviation |
Minimum |
Median |
Maximum |
|
|---|---|---|---|---|---|---|---|
Cd |
< 1 |
31 |
0.12 |
0.14 |
0.03 |
0.07 |
0.76 |
1–2.5 |
5 |
0.46* |
0.79 |
0.06 |
0.13* |
1.87 |
|
2.5–10 |
3 |
0.12 |
0.11 |
0.02 |
0.11 |
0.23 |
|
Co |
< 1 |
6 |
0.13 |
0.09 |
0.06 |
0.07 |
0.25 |
1–2.5 |
3 |
0.28* |
0.38 |
0.06 |
0.06 |
0.71 |
|
2.5–10 |
3 |
0.13 |
0.12 |
0.03 |
0.09* |
0.26 |
|
Cr |
< 1 |
59 |
6.50 |
4.80 |
1.32 |
5.07 |
23.00 |
1–2.5 |
20 |
13.62* |
10.87 |
3.86 |
9.95 |
46.59 |
|
2.5–10 |
20 |
13.57 |
10.52 |
2.36 |
10.24* |
35.37 |
|
Cu |
< 1 |
13 |
2.84 |
2.91 |
0.06 |
2.26 |
8.86 |
1–2.5 |
5 |
1.07 |
0.58 |
0.32 |
1.13 |
1.87 |
|
2.5–10 |
5 |
5.10* |
5.13 |
1.86 |
2.81* |
13.99 |
|
Fe |
< 1 |
54 |
126.27 |
159.93 |
19.04 |
71.50 |
902.81 |
1–2.5 |
19 |
279.09* |
250.38 |
58.93 |
248.22* |
1,189.14 |
|
2.5–10 |
19 |
242.77 |
173.76 |
53.37 |
231.18 |
619.00 |
|
Mn |
< 1 |
60 |
3.92 |
5.19 |
0.07 |
2.00 |
30.06 |
1–2.5 |
20 |
6.57* |
5.52 |
1.26 |
5.39 |
22.17 |
|
2.5–10 |
20 |
5.76 |
4.55 |
1.08 |
5.76* |
15.73 |
|
Ni |
< 1 |
36 |
1.65 |
1.51 |
0.13 |
1.02 |
5.77 |
1–2.5 |
12 |
3.75 |
4.34 |
0.53 |
1.82 |
13.20 |
|
2.5–10 |
13 |
4.34* |
3.77 |
0.65 |
3.62* |
10.81 |
|
Pb |
< 1 |
59 |
2.49 |
2.80 |
0.21 |
1.33 |
13.57 |
1–2.5 |
20 |
5.21* |
8.79 |
0.27 |
1.89* |
31.27 |
|
2.5–10 |
20 |
2.19 |
2.25 |
0.19 |
1.10 |
7.20 |
|
Sb |
< 1 |
33 |
1.81 |
2.52 |
0.07 |
1.00* |
12.71 |
1–2.5 |
8 |
5.88* |
12.70 |
0.26 |
0.64 |
36.87 |
|
2.5–10 |
8 |
1.91 |
2.64 |
0.09 |
0.39 |
7.27 |
|
Tl |
< 1 |
19 |
2.41 |
1.79 |
0.62 |
1.57 |
5.81 |
1–2.5 |
4 |
10.06* |
11.56 |
1.66 |
6.21* |
26.16 |
|
2.5–10 |
4 |
6.35 |
7.82 |
0.72 |
3.42 |
17.84 |
|
Zn |
< 1 |
59 |
17.88 |
20.94 |
2.18 |
10.59 |
99.97 |
1–2.5 |
20 |
27.39* |
27.61 |
6.65 |
18.04* |
116.07 |
|
2.5–10 |
20 |
21.16 |
15.46 |
3.81 |
15.87 |
56.07 |
Localities of group I |
Localities of group II |
Localities of group III |
Localities of group IV |
|
|---|---|---|---|---|
[μm] |
[%] |
[%] |
[%] |
[%] |
0.0183–0.0937 |
0.001–0.2 |
0.04–0.2 |
0.03–0.3 |
0.2–0.3 |
0.0937–0.156 |
0.1–0.6 |
0.1–9.1 |
0.1–0.4 |
0.3–0.5 |
0.156–0.263 |
0.04–0.2 |
0.04–0.1 |
0.03–0.1 |
0.4–1.1 |
0.263–0.383 |
0.04–0.3 |
0.04–0.4 |
0.02–0.04 |
0.2–0.3 |
0.383–0.614 |
0.1–1.5 |
0.3–3.4 |
0.1–0.1 |
0.3–3.1 |
0.614–0.949 |
0.2–0.3 |
0.4–1.7 |
0.1–0.7 |
0.3–0.9 |
0.949–1.6 |
0.3–4.7 |
0.5–3.0 |
0.1–2.3 |
5.6–6.4 |
1.6–2.39 |
0.2–1.4 |
0.3–1.6 |
0.2–1.3 |
1.1–4.4 |
2.39–6.69 |
0.1–0.6 |
0.1–1.3 |
0.05–0.6 |
0.2–1.0 |
6.69–9.93 |
1.0–2.2 |
0.1–5.9 |
0.3–8.3 |
8.6–10.9 |
< PM1 |
0.07–0.32 |
0.13–0.58 |
0.05–0.17 |
0.34–0.58 |
PM1–2.5 |
0.22–2.94 |
0.44–2.17 |
0.14–1.54 |
2.66–4.86 |
PM2.5–10 |
0.36–0.77 |
0.08–2.7 |
0.12–1.65 |
1.48–2.28 |
V ΣPM |
0.2–0.6 |
0.2–0.7 |
0.1–0.4 |
0.9–1.0 |
The highest percentage |
The second highest percentage |
The lowest percentage |
||
The lowest percentage occurrence of the sum of heavy metals was found in the smallest particles in the range from 0.0183 to 0.383 μm. After the particle size distribution into three typical groups below PM1; PM1–2.5 a PM2.5–10, it was found that most metals occur in particle size class PM1–2.5. For locations not affected by the metallurgical industry, the highest content of heavy metals was found in PM2.5–10. From these results, it is evident that within the study of the distribution of heavy metals in the individual classes, the localities of group IV cannot be regarded as background ones.
From the results of this study it was found that sum of heavy metals does not exceed 2.5% of total concentration of PM. It is an optimistic finding in the region with pronounced consequences of intensive industrial and metallurgical activities. The negative influence of heavy metals on human organism is not so important, compared with the original assumption when relatively much higher concentrations of heavy metals were expected. Alarming information is that most of the studied heavy metals are accumulated in particles of grain size PM1–2.5. It is known that these particles can penetrate deeply into pulmonary alveolar. Concentrations of heavy metals originate in substantial proportions from traffic sources, long-distance transport, and also other industrial sources.
The percentages of the sum of heavy metals in the sum μm at all the localities amounted to 0.2–2.5%. The occurrence of heavy metals in different particle size classes of dust particles in the air within the Moravian-Silesian Region is variable. At the localities Hradec nad Moravicí, Karviná, and Havířov, a higher percentage of most of heavy metals was found in PM > 1.6 μm. At the localities Ostravice, Ostrava Marianské Hory, and Ostrava Radvanice, higher proportions of most heavy metals in PM < 0.949 μm were found.
Cr, Mn, Fe, and Zn are mostly accumulated in the dust particles with a diameter greater than 1.6 μm. Fe, Mn, and Zn occurred at 8 of 10 localities in PM > 1.6 μm, only the localities Ostrava Marianské Hory and Ostrava Radvanice were different (over 66% occurred in PM0.949).
Pb, Cd, and Sb occurred mainly in the class below 0.949 μm. At 8 of 10 localities, cadmium occurred in the particle size class μm < 0.949 μm, with the exception of Hradec nad Moravicí and Ostrava Poruba.
The influence of metallurgical industry on the basis of heavy metals in the individual particle size classes in the air within the Moravian–Silesian Region has not been unequivocally demonstrated. In the samples taken, the microanalysis was used to identify particles that are formed during metallurgical processes: Fe–oxides containing Co, Cr, Cu, Mn, Ni, and Zn, and iron–based particles based on silicates containing: Ca-Mg-K in various proportions, originating from combustion processes. Further, in particles below 1 μm, sulphates of Zn-Fe and Pb-Ca, which affect the correlation between the content of Fe and Pb were proven.