Monitoring air pollution close to a cement plant and in a multi-source industrial area through tree-ring analysis.

Thirty-two trace elements were examined in the tree rings of downy oak to evaluate the pollution levels close to a cement plant isolated in a rural context and an industrial area where multiple sources of air pollution are or were present. Tree cores were collected from trees growing 1 km from both the cement plant and the industrial area that are located 8 km from each other. The analysis of the trace elements was performed on annual tree rings from 1990 to 2016 using laser ablation inductively coupled plasma mass spectrometry. Trace elements Cs, Mg, Mn, S and Zn reflected the emission history of the cement plant. Their values have increased since early 2000s, when the cement plant started its activity. However, the lack of significant trends of pollutants in the tree rings from the industrial area and the possible effect of translocation and volatility of some elements left open questions. The very weak changes of the other trace elements in the period 1990-2016 suggest those elements do not mark any additional effect of the industrial activity on the background pollution. The results confirm that downy oak trees growing close to isolated industrial plants must be considered a pollution forest archive accessible through dendrochemistry.

Introduction

Industrial activities are important source of organic and inorganic pollution, including metals and metalloids that are released in the environment (Ali et al. 2019). The emissions from cement plants, for example, include heavy metals and organic compounds, such as polycyclic aromatic hydrocarbons as well as dust and other pollutants (Baldantoni et al. 2014; Rovira et al. 2014). Here, the emission of heavy metals is caused by the use of fuels, such as coal or solid wastes as supplementary substitute and many other processes associated with the production (Rovira et al. 2014). Although metals are blocked within the clinker, some of them are volatilized and condensed on the dust particles (Schuhmacher et al. 2009). Cadmium, Cr, Cu, Mn, Pb and Zn have been found in the emissions from cement plants (Schuhmacher et al. 2009; Bermudez et al. 2010; Ogunkunle and Fatoba 2014; Arfala et al. 2018). These pollutants can be transported by the wind and reach long-distance range, with important impact in the environment. Heavy metals are toxic pollutants altering ecosystem processes, accumulating in plants, animals and soils and thus negatively affect human health (Schuhmacher et al. 2009).

Trees continuously exposed to air pollution can uptake pollutants through the root, leaf and bark, allocating them in the wood (Lepp 1975). Since the 1970s, many studies have focused on the analysis of the chemical composition of tree rings: the so-called dendrochemistry (Ault et al. 1970; Symeonides 1979; Baes and Ragsdale 1981; Watmough and Hutchinson 1999). In recent years, many researches have been carried out, expecially in industrial areas, in order to study the chemical composition of trees and to find associations between industrial history and the pattern of chemical elements in tree rings (Martin et al. 2006; Aznar et al. 2008; Hojdová et al. 2011; Cui et al. 2013; Bernini et al. 2016; Cocozza et al. 2016; Odabasi et al. 2016; Sensuła et al. 2017; Perone et al. 2018; Liu et al. 2018; Austruy et al. 2019; Zhang 2019; Muñoz et al. 2019). Many of these studies have concerned the identification and the dating of the heavy metal pollution (Morton-Bermea et al. 2016). The usefulness of the temporal approach of dendrochemistry is that, in regions where monitoring stations suitable to monitor industrial plants are not present (or in places were they have limited records), trees can represent an alternative source of pollution data for the past decades, helping to trace the history of the chemical contamination (Alterio et al. 2020).

Many studies (Aznar et al. 2008; Hojdová et al. 2011; Sensuła et al. 2017; Liu et al. 2018; Perone et al. 2018) have demonstrated the feasibility of the dendrochemistry in the environmental monitoring and have shown the presence of similar patterns between the industrial history and the chemical content of tree rings. Howover, some others (Watmough and Hutchinson 2002; Martin et al. 2006; Navrátil et al. 2017) have highlighted the inconsistency of dendrochemistry in describing the chemical variation over time. Therefore, further dendrochemical studies (testing new and different geographical regions, tree species, chemical elements and industrial processes) are needed, in order to understand in detail the principles of dendrochemistry and to demonstrate its efficacy for tracing the chemical contamination in the environment (Liu et al. 2018). Moreover, these studies can provide valuable data for scientific reviews and meta-analysis, in order to identify gaps in knowledge about the reliability of dendrochemistry in environmental monitoring (Borenstein et al. 2011).

The Venafro plain in central Italy was considered as study case, focusing on a cement plant isolated in a rural context and 8 km away from a multi-source industrial area where different factories and sources of air pollution are placed. These factories had variable activities over time. In particular, a former foundry and an incinerator alternately worked from the 1970s until today, whereas the cement plant is active since the early 2000s. Since 2013, the Venafro plain has been defined as a highly polluted site in the Molise region (ARPA Molise 2020) because of road traffic in the town of Venafro and industrial pollution. The main objectives of this study are (a) to evaluate the cement plant and the industrial area as point sources of trace elements in tree rings and, consequently, (b) to assess if the trace elements in tree rings in each site refer to its emissions or not and if a higher number of pollution sources (as in the industrial area) can negatively affect on the reliability of the dendrochemical records.

Materials and methods

Study area

The study area is located in the Venafro plain, a small alluvial plain in central-southern Italy (Fig. 1). The most important human agglomeration in the area is the town of Venafro (41°28′57″ N, 14°02′51″ E; approximately 11,200 inhabitants). The plain covers an area of about 50 km2 and an altitude profile ranging between 130 and 250 m asl. The valley has a quasi-elliptical shape with the largest diameter arranged along the northeast-southwest axis and is surrounded by mountains (Lucenteforte 1877). The Venafro plain is a geological morphostructural depression, subsequently covered by river sediments of the Volturno river that flows on the east side of the valley (Amato et al. 2014). The main geological substrates are made up by alluvial deposits and compact calcareous rock layers (dolomites and travertines) (ISPRA 1983). The climate is temperate (14.5 °C mean annual air temperature, 1000–1200 mm mean annual precipitation) (Peel et al. 2007). The winds are predominantly from the NE or SW (ARPA Molise 2020) (Fig. 1).

Fig. 1

Study area, position of the cement plant, the foundry, the incinerator and the sampling sites P1 and P2. The wind rose shows the dominant winds direction in the study area

The Venafro plain has around 30 factories that work in metallurgy, chemistry, cement production, electronics and waste incineration processes. Monitoring campaigns highlighted the low level of air quality in the valley. Indeed, the PMx levels in the Venafro town are very high, as recorded by the Regional Agency for the Environmental Protection (ARPA Molise 2020).

The study area is characterized by (i) a cement plant, located in rural context representing an isolated industrial plant, and (ii) an industrial area (8 km from the cement plant) that is characterized by multiple factories and sources of air pollution, including an incinerator and a foundry (Fig. 1).

The history of the industrial activities was temporally reconstructed through technical reports and other press sources.

The cement plant was established on early 2000s (2000–2001) (Sigas 2015). In 2005, the cement plant started to use refuse-derived fuel (RDF) in the combustion process (Colacem SpA 2011). In 2015 and 2016, this plant has obtained the Integrated Environmental Authorization (IEA) and the ISO 14001:2015 certification, respectively (Regione Molise 2015; Colacem SpA 2017).

The incinerator is still running since the mid of 1990s. Until 2005 it burned organic matter and biomass and since 2007 RDF (Herambiente SpA 2014). The plant was officially closed between 2005 and 2007.

The foundry has been active from the mid of 1970s to 2005, with periods of company crisis and probably related lower production from the mid of 1990s (La Banca 2014) (Fig. 2).

Fig. 2

Industrial history in P1 and P2

The cement plant and the incinerator are reported as sources of air pollutants in the European Pollutant Release and Transfer Register (E-PRTR) of European Environment Agency (2019) and the Italian Atlas of Environmental Conflicts (Atlante Italiano dei Conflitti Ambientali) by the Center for the Documentation on Environmental Conflicts (Centro Documentazione sui Conflitti Ambientali 2020). A biomonitoring program using lichens close to the incinerator detected the exceeding of heavy metals thresholds in 2011 and 2012 for As, Cu, Fe, Hg, Mn, Pb and V (ARPA Molise 2020).

Tree-ring analysis

Trees of downy oak (Quercus pubescens Willd.) with average diameter at breast height (DBH) of 28 cm (± 6) and average age of 30 years (± 3) were selected in two sampling sites (P1 and P2). Three trees, two cores per tree, were collected in P1 and P2 sites. Oaks (and in particular the downy oak) are suitable indicators of the chemical contamination due to their low radial permeability, the small number of tree rings in the sapwood and the low heartwood moisture content (Cutter and Guyette 1993). P1 was located close to the cement plant and P2 close to the incinerator and the foundry placed in the industrial area (Fig. 1). Plots were at 1 km far from the emission sources (according to Cocozza et al. 2016; Perone et al. 2018).

Tree cores were collected at DBH using an incremental borer (Haglof Company Group, Sweden) in January 2018. In April 2018 tree cores were cut using a microtome (Gärtner and Nievergelt 2010) for dendrochemical analysis. In details, tree cores were not sanded, as usually done in dendrochronology, to avoid the contamination effect due to wood dust (Danek et al. 2015). The tree-ring width was measured using the LINTAB instrument (Rinntech, Heidelberg, Germany) and a Leica MS5 stereoscope (Leica Microsystems, Germany). The software TSAP Win 0.55 (Rinn 1996) was used to obtain raw tree-ring width chronologies and to statistically cross-date them in order to exactly identify the year of tree-ring formation (Speer 2012). Cross-dating was performed between the raw tree-ring width chronologies of each plot and between the mean chronologies of each plot (Perone et al. 2018). The Gleichläufigkeit statistical index and the relative significance value were calculated (Schweingruber 1988; Speer 2012). Moreover, the heartwood-sapwood boundary was identified. The delimitation was made through visual analysis based on the colour differences between heartwood and sapwood (the heartwood has a dark and distinctive colour while sapwood has a light colour) (Morais and Pereira 2012; Sohar et al. 2012). These analyses were conducted only on the tree cores used in the dendrochemical analysis (examples shown in Fig. S1).

Dendrochemistry analysis

The analysis of chemical elements was performed on annual tree rings from 1990 to 2016 using the laser ablation inductively coupled plasma mass spectrometry (LA-ICP-MS) (Danek et al. 2015; Perone et al. 2018). Only one of the two cores collected from each tree was used in this analysis. The ablation was performed in spots, with one large spot (257 μm crater) in each tree ring. Wood samples were ablated orthogonally to the tree rings. Tree rings were ablated in the latewood where the presence of narrow-lumen and thick-walled cells defines conditions for a better combustion during the ablation (Danek et al. 2015). A summary of the main standard operating conditions and parameters used in the laser ablation analysis is reported in Table 1. Isotopes of elements, 27Al, 137Ba, 209Bi, 79Br, 43Ca, 111Cd, 140Ce, 35Cl, 59Co, 53Cr, 133Cs, 63Cu, 65Cu, 57Fe, 39K, 25Mg, 55Mn, 95Mo, 23Na, 62Ni, 208Pb, 85Rb, 34S, 29Si, 88Sr, 232Th, 49Ti, 205Tl, 238U, 51V, 89Y and 66Zn, were measured. The data were processed with the Sills software (Signal Integration for Laboratory Laser Systems) to select integration intervals, remove spikes and calculate net count rates (cps) for all measured elements (Guillong et al. 2008). Finally, the cps of each element were normalized to 13C to correct differences in ablation yield. Each analysis consisted of about 30 s of gas blank data, used for background correction and 40 s of sample ablation. Since the absolute concentrations were not calculated (because of the lack of a suitable reference material), the ratio between the cps of each element and 13C was taken as proxy for the element level in tree ring according to the formula: where is the level of the n element in the x year, is the cps value of the n element in the x year and is the cps value of 13C in the x year.

Table 1

Main information, standard operating conditions, and parameters of the laser ablation analysis

LA-ICP-MS analysis: parameters and description
Instrument host	ETH Zurich
Type	Resolution 155S (asi)
ICP-MS	Element XR (Thermo Fisher)
Laser type	193 mm excimer
Setting	10 Hz
	3.5 J/cm2 single hole
	400 pulses
Spot size	257 μm of diameter
Normaliation	13C intensity

Subsequently, the level of elements was indexed (index level). In each tree core, the maximum and the minimum levels of each element were identified. Then, the time series of the index level were obtained according to the formula: where is the index calculated in the x year for the n element, is the level of the n element in the x year and and are the highest and the lowest level of the n element in the core, respectively (Perone et al. 2018). Time series of index level of tree cores of the same plot were averaged in order to obtain time series per plot (one in P1 and the other in P2).

Statistical analysis

Time series of the index level were smoothed using a spline method (λ chosen with cross validation) (Wahba 1990; Aydin et al. 2013). The Kruskal-Wallis test was performed to test significant differences between the index levels of elements over time in relation to groups of years. In particular, the index levels were averaged in the following groups of years: 1990–1992, 1993–1995, 1996–1998, 1999–2001, 2002–2004, 2005–2007, 2008–2010, 2011–2013 and 2014–2016. Groups of years were tested as factors and were considered significantly different with p value ≤ 0.05, and, consequently, compared through LSD test.

The time series of index level were analysed to assess the trend of element level over time (increasing, decreasing, or no trend). The trend was estimated with the non-parametric Mann-Kendall test, obtaining the significance value (p value), the Kendall’s τ and the Kendall score (S) (Mann 1945; Hipel and McLeod 1994).

The S of a time series of values is: where x are the time series values and where:

An increasing trend is defined by positive values of S and a decreasing trend by negative values of S (Hipel and McLeod 1994). The Mann-Kendall test also provides the value of Kendall’s τ. Kendall’s τ is closely related to the S according to the formula: where D is the maximum value of S obtainable with the same series (x is always greater than x). So, τ ranges from 1 (when S = D and the trend is always increasing) to −1 (when S = D but values are negative and the trend is always decreasing) passing through 0 (S = 0, no trend). This classification defines the correlation between series within time (Hipel and McLeod 1994). Statistical analyses were performed using SPSS statistical package (Version 20.0) (IBM corp. 2011) and R software (Version 3.5.2) (R Core Team 2018). Maps and graphics were produced using R software.

Results

Mean tree-ring chronologies ranged from 1983 to 2017 in P1 (close to the cement plant) and from 1988 to 2017 in P2 (close to the industrial area). Mean tree-ring width was 4.97 mm (± 0.26 mm). Cross-dating between plot-mean chronologies was good, with a Gleichläufigkeit value of 66 (p < 0.05) (Fig. 3). The heartwood-sapwood boundary corresponded to a wide range of relative position among the sampled trees, with the limits associated to the tree rings from 1994 to 2008. In P1, the latest was found between 2007 and 2008, while the oldest was found between 1996 and 1997. In P2 the latest was between 2004 and 2005 and the oldest between 1994 and 1995 (Fig. 4 and Fig. S1).

Fig. 3

Mean tree-ring width chronologies of P1 and P2. Statistical values of the cross-dating (Gleichläufigkeit and significance) are given (significance level: * = 95%)

Fig. 4

Trend over time of the level of Cs, Mg, Mn, S and Zn in P1 and P2 (values of Kruskal Wallis p-level, Mann-Kendall p-level, Kendall Tau, Kendall score and an arrow indicating the trend are reported). In graphs, circles are the mean (± standard error) chemical level of element per each year (n = 3), and letters (from LSD test) refer to the groups of 3 years considered in statistical analysis and red lines are smoothing functions. The black dashed boxes indicate the range (latest-oldest) of the years corresponding to the heartwood-sapwood transition zones recorded in each plot. In the upper part of the figure main information on the history of the industrial plants (in grey the activity years, see Fig. 2 for more details)

Cesium, Mg, Mn, S and Zn showed significant trends in tree rings, in contrast to all the other elements (Al, Ba, Bi, Br, Ca, Cd, Ce, Cl, Co, Cr, Cu, Fe, K, Mo, Na, Ni, Pb, Rb, Si, Sr, Th, Ti, Tl, U, V and Y) (Fig. S2 and Fig. S3). According to the Kruskal-Wallis test, in P1 the index levels (thereafter levels) showed significant differences (p < 0.05) among the groups of years in Cs, Mg, Mn, S and Zn. (Fig. 4). The levels have been low from 1990 to 2000 and increased in more recent groups of years (recent time). In Cs, Mg, Mn and Zn, the peak level happened between 2011 and 2013. After this group of years, the level tended to decrease. On the other hand, S showed a continuous increasing trend that reached 0.699 in 2014–2016 from the low mean level of 0.052 in the years 1990–1992 (Fig. 4). In P2, the patterns of level in time were flat or with few weak peaks, resulting in shapes different from the ones observed in P1. Only Mn showed a significant difference of the level among the groups of years in the Kruskal-Wallis test (p < 0.05). According to the Mann-Kendall test, strong increasing trends were found in P1 in all the investigated elements. In P2, Mg, Mn, S and Zn showed increasing trend, whereas Cs showed no trends (Fig. 4).

Discussion

The pollutants in the tree rings partially reflected the industrial activity in the study area. The cement plant emissions were recorded by the wood samples collected from the P1 sampling site, which were easily distinguishable from other pollution sources, namely, the emissions from the industrial area in P2. Moreover, almost all the elements analysed in this study are linked to the cement production. Magnesium is linked to the use of raw materials, as calcareous rocks (containing Mg), in the clinker production process (Schneider et al. 2011; Abdel Hameed et al. 2016). Sulphur is one of the main gases emitted by cement plants in form of SOx (Ruth 1998; Schuhmacher et al. 2004). Very high concentrations of Mn and Zn were found near cement plants by Schuhmacher et al. (2002) and by Al-Khashman and Shawabkeh (2006). Concerning the Cs (133Cs, stable isotope), the monitoring and detection in the environment are rarely performed due to its limited use in industry and manufacturing. The main cause of the presence of Cs in the air, water and soil is the erosion and weathering of rocks and minerals. However, Cs has also been detected in the fly ash of waste incinerators and coal burning power plants (Fernández et al. 1992; Mumma et al. 1990). Therefore, considering the use of both coals (coal or coke) and RDF for the energy production in the cement plant, Cs might be linked to the cement production. Cesium can be absorbed by trees, and it can be radially transported from the bark to stem wood through parenchyma, as showed by Aoki et al. (2017) in 3-year-old Japanese cedar seedlings. In P1, Cs, Mg, Mn, S and Zn showed very low levels until 2000. Since the early 2000s, the cement plant has operated around the P1 sampling site, and after 2000–2001, the levels of Cs, Mg, Mn, S and Zn in tree rings increased until 2011–2013. During 2014–2016 the levels of Cs, Mg, Mn and Zn have decreased, while S has showed a continuous increasing trend.

The overall pattern of chemical level in P1 seemed to be in accordance with the industrial history of the cement plant. Although at first only petroleum coke, coal and methane gas were used in combustion process of the cement plant, since 2005 the plant has activated the use of RDF in combustions (Colacem SpA 2011, 2017; Fig. 2). This change may have contributed to the increase of air pollution in the environment, as reflected by the level patterns in the tree rings. In addition to the potentially harmful combustibles mentioned above, spent tires have been also used as fuel in the cement plant (as reported in Caldiroli 2015). According to Carrasco et al. (2002), the use of spent tires in cement manufacturing cause an increase of emissions of S (SO2, + 24%) and heavy metals such as Zn (+ 487%) and Mn (+ 100%). In Cs, Mg, Mn and Zn, a maximum peak of level was found in 2013–2014, followed by a slight reduction in 2015–2016. This time pattern may match the implementation of some environmental certification programmes. Indeed, in 2015 and in 2016, the cement plant obtained the Integrated Environmental Authorization (IEA) and the ISO 14001:2015 certification, respectively (Regione Molise 2015; Colacem SpA 2017; Fig. 2). On the other hand, the continuous increasing trend shown by S, even after 2013–2014, leaves open questions, even if it matches with the statistics presented in recent technical reports published by the cement plant (Colacem SpA 2017).

The trends of trace elements in the P2 were different from P1. Only Mn pattern partially reflected the industrial history of the area. The foundry officially stopped its activity in 2005 after a period of manufacturing crisis since the mid of the 1990s (La Banca 2014) that probably caused lower production and, therefore, lower pollutant emissions. Then, in P2 the pollutant levels in tree rings were affected also by the incinerator. The incinerator intensified its activity in 2007 using RDF in combustion (Herambiente SpA 2014). Therefore, the period between 1995 and 2005 has been marked by the low emissions of foundry and not by incinerator, a change that could be traceable in the lower peaks of Mn in these years. Trace elements in tree rings from the P2 did not show significant trends related to the surrounding industrial history probably due to the wide diffusion of pollutants from the dense industrial area. Our results showed that the presence of several sources of pollution increases the noise in the tree-ring records.

Volatility of chemical species and heavy metals may affect their availability in the environment and, thus, their occurrence in tree wood. Volatility depends on the chemical element and the industrial/combustion process. Elements involved in volatilization process are those characterized by low boiling points. On the other hand, also semi-volatile elements may be strongly present in fly ashes even if a large portion generally remains in the bottom ashes (Abanades et al. 2015). In solid waste incinerator process, Zn is partially volatilized, while a small fraction can remain in the bottom ashes (Abanades et al. 2015). Pedersen et al. (2010) analysed the fate of several elements from the combustion of a dedicated waste and expected to contain high concentrations of potentially harmful elements such as heavy metals, S and Cl. They found that S and Zn were strongly volatilized. The release pattern depends on the combustion temperature: the higher is the temperature, the higher is the occurrence of these elements in the fly ashes. Conversely, Mg was not released, in accordance with its non-volatile nature. Another feature that may influence pollutant volatilization is the redox atmosphere during combustion. Indeed, it has been shown that a reductive combustion atmosphere favours the volatilization of Cd and Zn (Dong et al. 2015). Cesium is a semi-volatile toxic metal that can be released during the combustion of coal. It can vaporize in the hottest parts of the combustion elements (Seames and Wendt 2001). Manganese is a low volatile element. However, volatilization may happen, especially in coal combustion (Dıaz-Somoano and Martinez-Tarazona 2003; Tang et al. 2018). According to this framework, the five elements chosen to be discussed in this study show different volatility. Mg has non-volatile nature. Cs, Mn and Zn are semi-volatile elements, whereby the presence in the fly ashes, thus in the air, depends on several technical features during industrial process such as temperature and redox atmosphere during combustion. Conversely, S is a volatile element (Bøjer et al. 2008; Pedersen et al. 2010), converted into gaseous pollutants, especially during coal combustion (Hodges and Richards 1989; Folgueras et al. 2004; Schuhmacher et al. 2004; Buhre et al. 2006). In this work, S showed a strong increasing trend in P1, where coal and coke have been used as fuel in combustion process. However, the fate of the other elements leaves open questions about the consistency of chemical species with the background industrial history.

The element translocation throughout the xylem is a key issue in dendrochemistry (Alterio et al. 2020), because it may affect the reliability of dendrochemistry in environmental monitoring. Translocation means different xylem-xylem movement. Among them, the most common is the accumulation of elements in the transition zone, namely, the boundary layers between heartwood and sapwood (Cutter and Guyette 1993; Binda et al. 2021; Nováková et al. 2021). Considering the heartwood-sapwood transition zones recorded in each plot (as shown in Fig. 4 with black dashed boxes), the high peak showed by Zn in P2 and the weaker ones showed by Cs and Mg in P1 may be the result of an element accumulation into the heartwood-sapwood transition zone. Conversely, in the case of Cs and Mn in P2, the transition zone was characterized by the lowest values in the record. On the other hand, other translocation phenomena may have influenced the element trend, including translocation from heartwood to sapwood. The movement of elements could cause a reduction of the accuracy of the pollution time patterns, and thus it must be taken into account.

Nevertheless, the cement plant and the industrial area in the Venafro plain represent point sources of trace elements pollution, detectable in tree rings. In particular, the single pollution source (cement plant in P1) located in an agro-industrial land cover pattern (sensu Alterio et al. 2020), increased pollutants levels in tree rings consistently with the industrial history of the area, by showing considerably increased Cs, Mg, Mn, S and Zn levels in the recent years. On the other hand, the high variability of emitted pollutants in a multi-source industrial area did not define univocal pollutants levels in tree rings in P2, where the pollution sources are different and mixed, highlighting the difficulty to find unequivocal traces of the industrial history in the wood.

Conclusions

Trace elements Cs, Mg, Mn, S and Zn had reflected the emission history of a cement plant isolated in a rural context. However, the lack of significant trends of pollutants in tree rings from an industrial area with multiple sources of air pollution and the possible effect of translocation and volatility of some elements left open questions by stimulating research in (a) the definition of the specificity of chemical species in the definition of pollutants in tree rings (does downy oak uptake all pollutants?) and (b) the assessment of threshold of pollutant concentration in the environment able to induce uptake in trees (what is the pollutant threshold that make the storage in tree rings detectable?). Moreover, further research should address the effect of pollutant source in tree rings, in order to define the pollutant level in the wood in relation to the distribution of trees and, consequently, to improve strategies in sampling design, as well as to assess the contribution of soil and groundwater in the pollutant accumulation in tree rings. Results from these researches would be incorporated into landscape or urban planning processes with the aim at protecting agricultural lands and humans living nearby and the trees that represent the elements of pollution forest archives.

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