1 Introduction

Lignite (brown coal) is an important fuel in the production of electricity and heat in many European countries. In Poland, it is extracted from several large, opencast mines near Bełchatów, Konin, Adamów, Turów, and Sieniawa. The amount of lignite mined in Poland in 2017 was 61 million tons, equaling approximately one-third of Germany’s production. Up to 2021, there had been expected reduction in lignite mining over the next years. However, considering the present political and economic situation in the world, this is no longer so reliable.

Lignite mining and processing constitutes one of the most important ecological and economic problems of the last several decades. Opencast mines cover large areas of strongly degraded environment, including the lithosphere, soils, hydrology, vegetation, and landscapes. In addition, contaminants can be dispersed over large distances. Among such pollutants, lignite dust is typical of mining activity, whereas ash and several other products originate from lignite burning (Kosztowniak et al., 2016; Pandey et al., 2014; Vrablik et al., 2017). These substances are carriers of nutrients, along with potentially toxic elements and various organic and inorganic contaminants. Acid mine drainage is another inherent phenomenon of areas affected by lignite mining (Fyson et al., 2006), as it affects the quality of water reservoirs. For instance, in the Lausitz area (Germany), approximately 170 lignite pit lakes have a pH range of 2.4 to 3.4 (Fyson et al., 2006). The water in the pits is also characterized by high concentrations of iron (Fe) (up to 800 mg dm–3), which occurs as sulfides (mostly pyrite and marcasite) as accessory minerals in the lignite. It should be noted that sulfides can also be a source of trace elements.

The influence of lignite dust and coarse fragments on the soil environment and the plant–soil system is multifaceted and ambiguous. Several studies have demonstrated that it can have a positive effect on the soil organic carbon content and pore structure, and can slow mineralization (Kołodziej et al., 2020; Sekhohola et al., 2013). Some authors (e.g., Kwiatkowska-Malina, 2015) have also tested the ability of humic acids extracted from lignite to improve soil quality. However, there is also some evidence that lignite used as a soil amendment negatively influences soil system. Frouz et al. (2005) showed that some lignite mine spoils inhibit the reproduction of pot worms (Enchytraeus crypticus), mainly due to their low pH (< 4) and/or high salinity. Simmler et al. (2013) found that high doses of lignite introduced to soil reduced the growth of ryegrass. Only a few studies have monitored the effects of lignite on soil microbial processes. Several authors (Bekele et al., 2015; Rumpel et al., 2001; Tran et al., 2015) have suggested that lignite can be utilized by soil microorganisms as a carbon (C) source, but the efficiency of this process is limited. Qin and Leskovar (2018) proved that lignite‐derived humic substances promote plant root growth and soil microbiota populations, which are essential for improving plant–microbial interactions under water-deficit stress. Baumann et al. (2005) showed that lignite can promote the relative abundance of arbuscular mycorrhizal fungi (AMF), which form symbiotic root associations with plants. This may be because, among rhizosphere microorganisms, the response of fungi to increasing C content is clearer than that of bacteria because fungal mycelia can accelerate the turnover cycle of the fungal C metabolism, while bacteria generally need much more time to turn over the C (Staddon et al., 2003).

Former lignite mining sites are reclaimed using various techniques. Areas of excavation and spoil heaps are usually leveled and afforested. Scots pine (Pinus sylvestris L.) and silver birch (Betula pendula Roth) have been commonly used for this purpose due to their high tolerance of such site conditions (Warfvinge & Svedrup, 1995), including aluminum (Al) stress (Clegg & Gobran, 1995) and contamination (Eltrop et al., 1991; Marguí et al., 2007; Ulbrichová et al., 2005). Knowledge on the feedbacks between soils and vegetation is crucial for the successful reclamation of degraded areas. Aspects related to nutrient cycling, including their uptake, bioaccumulation in fresh biomass, return to the soil via litterfall, and release during litter decomposition, are key importance. Rapid nutrient cycling is particularly important in nutrient-poor sites, which are often represented by degraded post-mining areas. The choice of silver birch is more suitable in this context than Scots pine. This is mainly due to the characteristics of the litterfall from these trees. Scots pine litter results in a strongly acidified, nutrient-poor biomass saturated with resins, which makes it resistant to decomposition (Jonczak, 2011). By contrast, silver birch litterfall is rich in essential nutrients and microelements (Brandtberg et al., 2004; Carnol & Bazgir, 2013; Jonczak et al., 2023), and the process of its decomposition is rapid (Hynynen et al., 2010; Shorohova & Kapitsa, 2016). The choice of tree species in the reclamation of degraded soils has another important aspect––phytoremediation. Silver birch is considered a hyperaccumulator of zinc (Zn) (Dmuchowski et al., 2012; Marguí et al., 2007). The latest studies by Rustowska (2022, 2024) and Jonczak et al. (2023) have also shown a strong accumulation of manganese (Mn) and copper (Cu). Their highest concentrations are typically recorded in the leaves (Jonczak et al., 2023; Rustowska, 2022).

Considering the importance of silver birch in the reclamation of areas degraded by lignite mining, and the insufficiency of our knowledge on the feedbacks in the soil–silver birch system in such areas, we undertook a broad study on nutrient accumulation in the biomass of that tree. The study covered three stands, including a spoil heap near a mine pit, a stand near a power plant dust settling pond, and a control stand. We expected large differences in the contents of the studied nutrients in the silver birch biomass related to the location and site characteristics. Moreover, we hoped that this study would contribute to a better understanding of the ecology of this species under unfavorable conditions, and its suitability for the reclamation of soil in degraded areas.

2 Material and Methods

2.1 Study Area

The first geophysical exploration for lignite, near Bełchatów (central Poland), began during World War II (Ratajczak & Hycnar, 2017). Continued exploration resulted in lignite being found at a depth of 127 m below ground level in 1960. The thickness of the lignite deposit was estimated at 70 m. In 1975, after intense exploration works, the Presidium of the Government decided to start lignite operations and to build a thermal power plant. The lignite deposits near Bełchatów are of the tectonic type (Ratajczak & Hycnar, 2017). They occur within Mesozoic formations in the Łódź Basin (with a W–E orientation). The length and width of the deposits was estimated at 6.5 and 2.5 km, respectively. Based on the geology, the lignite deposits have been divided into three areas––Szczerców, Bełchatów, and Kamieńsk. The first two are currently being exploited. The boundary between the Szczerców and Bełchatów areas is represented by the Dębina salt dome, whereas the Kamieńsk and Bełchatów areas are divided by the Widawka Fault. In general, the lithostratigraphic profile in the study area allows the distinction of three major parts: (a) Quaternary sediments; (b) a Cenozoic lignite series; and (c) a Mesozoic base. The Quaternary sediments (35–80 m thick) are typically represented by sands, clays, gravels, fluvioglacial sands, and organic sediments. The parent rocks identified in the Mesozoic base are mostly limestones. In the Cenozoic lignite series, lignite, gray fine-grained sands, clays, lake chalks, sandstones, and marls have been identified (Wagner & Słomka, 2000). In the Bełchatów mine, the lignite is exploited by means of multi-bucket, wheeled excavators, the material transported using a belt conveyor (Borcz & Kozioł, 2015). Various technologies are used to take out the overburden and parent rocks, which are relatively resistant to crushing (Kozioł et al., 2011).

Our study was performed on three silver birch stands, including one on a reclaimed spoil heap formed from the overburden material, one in the vicinity of a fly ash settling pond, and one located approximately 8 km NE of the spoil heap and lignite opencast mine, which acted as the control (Fig. 1). Although, the stands were comparable in age (30–34 years), they varied in terms of density and diameter (Table 1).

Fig. 1
figure 1

Location of studied stands

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Table 1 Basic characteristics of the stands
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2.2 Soil and Biomass Sampling and Analysis

Silver birch trees and the soils were sampled once in June 2022. Biomass samples were collected from 10 average trees per stand, and included second-order roots, first-order roots, stemwood, and bark at a height ≈130 cm, and first-order branches, second-order branches, and leaves from the central part of the crown. The biomass samples were dried at 65 °C, then milled into powder, and analyzed. The total organic C (TOC), total nitrogen (N) and total sulfur (S) were determined by dry combustion (Vario MacroCube, Elementar, Germany), while the contents of phosphorus (P), potassium (K), calcium (Ca), magnesium (Mg), Fe, Mn, Cu, and Zn were obtained by inductively coupled–plasma atomic-emission spectrometry (Avio 200, Perkin Elmer, USA) after sample digestion in 65% nitric acid (HNO3) using a microwave digestion oven (Ethos Up, Milestone, Italy).

The soil samples were collected from close to each tree from depths of 0–10, 10–20, 20–40, and 40–80 cm using a 3 cm–diameter corer. One core was taken from the central part of the stand for the purposes of describing and classifying the soil. The soil samples were air-dried and passed through a 2.0 mm–mesh sieve. The < 2.0-mm fraction was used for the physical properties analyses. Additionally, part of the homogenized sample was milled into powder for chemical analysis. The particle size distribution was determined using the mixed pipette and sieve method. The Polish Soil Science Society (PTG) classification of textural fractions and groups was applied (PTG, 2009). The soil pH was determined using the potentiometric method (Mettler Toledo SevenDirect SD23 equipped with an InLab ExpertPro ISM electrode, Switzerland) in a soil:water proportion of 1:10. The total C (TC), N, and S contents were determined by dry combustion (Vario MacroCube, Elementar, Germany). The total inorganic C (TIC) was analyzed using the volumetric Scheibler method, and the TOC was calculated as TC – TIC. Approximately 0.3 g of soil sample was digested in 7.5 ml of 38% hydrochloric acid (HCl) and 2.5 ml of 65% HNO3. The solution was transferred into a 50-ml falcon tube, topped up with deionized water to 50 ml, and then filtered (through a hard paper filter). The contents of P, K, Ca, Mg, Fe, Mn, Cu, and Zn were determined by inductively coupled–plasma optical emission spectroscopy. Only high-quality, pure per-analysis reagents were used for biomass and soil sample digestion.

2.3 Statistical Analysis

Statistical evaluation of the results included obtaining the mean values and standard deviations for the biomass and soil samples. The statistical significances of the differences between the mean values were tested using the Kruskal–Wallis test. Principal component analysis (PCA) was applied to identify major sources of variability in the studied datasets.

3 Results

3.1 Basic Characteristics of the Soils

The studied soils represented three reference groups, according to the WRB 2022 (International Union of Soil Sciences, 2022) classification, that developed under the various impacts of natural and anthropogenic factors. These were a semi-natural Dystric Brunic Arenosol, representing the control location, an Albic Podzol (Arenic, Eutric), located in the vicinity of the settling pond, characterized by a natural or close-to-natural sequence of genetic horizons, albeit threatened by contamination from the settling pond, and a Spolic Technosol (Arenic, Eutric, Ochric), developed from the overburden material that comprised the spoil heap. The soils were characterized by a sandy texture, with the content of the sand fraction ranging from 91.5 to 99.6% (Table 2). The pH values varied among the stands and with depth (Fig. 2), being strongly acidic or acidic at the settling pond and control locations, showing low variability with depth. The observed pH values are typical of the sandy soils of Poland under forest vegetation. The soil of the spoil heap was acidic at the top, but with the pH strongly increasing with depth. This tendency indicates the leaching of basic cations and carbonates from the surface layers of anthropogenic materials. This process is typical under percolative water regimes, which can be additionally accelerated by forest vegetation. The studied soils were generally poor in TOC, despite the observed differences among the stands (Fig. 2).

Table 2 Particle size distribution of the studied soils
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Fig. 2
figure 2

pH and TOC content in the studied soils (the same letters indicate no statistically significant differences between the stands at a significance level of p < 0.05 based on the Kruskal–Wallis test)

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3.2 Soil Nutrient Content

Although having comparable textural characteristics, soil nutrient content was significantly different among the three sites (Table 3, Fig. 3). On the heap stand, soils were deficient in N and P, while being much more abundant in K, Ca, and Mg when compared to the settler and control locations. The differences were also apparent in the micronutrients. Generally, the contents of S, Mn, Zn, and Cu were low (close to natural), considering the proximity of the sources of pollution (opencast mine, settler, power plant).

Table 3 Soil mean ± standard deviation (SD) nutrient contents (mg kg–1) in the studied stands, and statistical significance of differences between the stands (the same letters indicate no statistically significant differences between the stands at a significance level of p < 0.05 based on the Kruskal–Wallis test)
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Fig. 3
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Mean ± SD soil nutrient content at depths of 0–10, 10–20, 20–40, and 40–80 cm (the same letters indicate no statistically significant differences between the stands at a significance level of p < 0.05 based on the Kruskal–Wallis test)

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3.3 Nutrient Content in Silver Birch Biomass

The nutrient distribution in the silver birch biomass varied strongly among the tissues and stands (Fig. 4). The highest concentrations were mainly noted in the leaves and the lowest in the stemwood. The only exceptions to this tendency were Fe and Mn. The trends for these nutrients were not fully clear, however large differences were noted between the stands. Also, relatively high contents of Ca, Cu, and Zn were recorded in the bark, branches, and roots. In the roots, there were also high concentrations of Fe. Based on the mean values of the tissues, the N contents were the highest among all the major nutrients in the silver birch biomass (2,337.5–24,786.3 mg kg–1), followed by Ca (720.2–16,418.4 mg kg–1), K (325.1–7,892.0 mg kg–1), Mg (164.3–2,899.2 mg kg–1), and P (68.9–1,651.1 mg kg–1). Micronutrients occurred in amounts of 7.3–2,341.3 mg kg–1 Mn, 54.7–1,246.5 mg kg–1 S, 10.8–1,114.4 mg kg–1 Fe, 18.0–179.3 mg kg–1 Zn, and 2.8–9.7 mg kg–1 Cu.

Fig. 4
figure 4

Mean ± SD nutrients content in birch biomass (the same letters indicate no statistically significant differences between the stands at a significance level of p < 0.05 based on the Kruskal–Wallis test). RII––second-order roots, RI––first-order roots, S––stemwood, B––bark at a height ≈130 cm, BrI––first-order branches, BrII––second-order branches, and L––leaves

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3.4 Principal Component Analysis (PCA)

A PCA analysis, based on the major soil characteristics and nutrient content of the soils and silver birch biomass, allowed us to identify the major sources of variability in, and the interrelationships between, the studied variables in a silver birch–soil system (Fig. 5). An analysis of the contributions of the variables in the model revealed no dominant role by any of them, highlighting the complicated nature of the studied system. However, the correlation matrix of the variables indicated strong feedbacks between the soil characteristics and nutrient contents in the silver birch biomass. These were both positive and negative correlations. Based on the projection of the cases on the plane of factors, separate clusters for each study plot are clearly visible, suggesting differences between them, considering the variables used for the analysis (Fig. 6).

Fig. 5
figure 5

PCA analyses of individual silver birch tissues and soil characteristics. RII––second-order roots, RI––first-order roots, S––stemwood, B––bark at a height ≈130 cm, BrI––first-order branches, BrII––second-order branches, and L––leaves

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Fig. 6
figure 6

PCA analyses of individual silver birch tissues (projection of cases on the plane of factors). RII––second-order roots, RI––first-order roots, S––stemwood, B––bark at a height ≈130 cm, BrI––first-order branches, BrII––second-order branches, and L––leaves

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4 Discussion

Site conditions, affected by anthropopressure, are often subject to strong fluctuations, which can be reflected in the plant nutrient status. For silver birch, this has been illustrated by several authors (e.g., Daugaviete et al., 2015; Hytönen et al., 2014; Kříbek et al., 2020; Pająk et al., 2016; Sitko et al., 2022). In the present study, the influence of the lignite operations was confirmed by the PCA analysis (Fig. 6), which clearly showed different effects on the nutrient composition in the silver birch tissues from each stand. This highlights the complex character of this process, in which the nutrient availability for plants is controlled by certain factors, particularly soil pH (Barrow & Hartemink, 2023). As we found, the soil nutrient profiles of the investigated stands were not homogeneous (Fig. 2). While we expected the soils of the settling pond and spoil heap locations to be acidic, as is typical of Podzols and Arenosols (Brożek & Zwydak, 2010), we found the soil of the heap to be alkaline in the deeper layers. This contrasts with the reports by Pająk et al. (2023) and Wójcik et al. (2012), who noted a strongly acidic reaction at this site, whereas it corresponds with the observations of Pająk and Krzaklewski (2006). A varying pH in the overburden was observed by Gruszczyński (2015) and Pudełko and Chodak (2020). Such discrepancies are common, being an effect of the heterogeneity of the deposited material (Wójcik & Krzaklewski, 2009). As mentioned, soil pH determines nutrient uptake and its accumulation in the plant biomass, along with the nutrient concentration in the substrate (Cataldo & Wildung, 1978), and the plant’s requirements for a given nutrient (Clark, 1983). Considering the environmental factors, either directly or indirectly shaped by anthropization, the influence of pH on the nutritional status of plants can be highly differentiated, depending also on the type of the nutrient.

Nitrogen and P are dominant limiting nutrients in plant growth, influencing productivity and the overall functioning of terrestrial ecosystems (Perring et al., 2008), especially those associated with industrial/post-industrial sites, which are often extremely poor in biogenic elements (Pająk et al., 2023; Pietrzykowski et al., 2013), as was also noted in this study (Fig. 3). The soil N and P contents were considerably lower than in the control (Fig. 3), as well as in other nutrient-poor, sandy soils under silver birch stands (Rustowska, 2022, 2024). This explains the limited accumulation of P in the birch biomass in the settler location. The comparable biomass P contents in the heap and control locations were probably influenced by a higher soil reaction increasing its uptake. In contrast to P, the N content in the birch biomass was not reduced in any stand in the mining zone, and was generally similar to the reports by other authors for various sites (Jonczak et al., 2023; Kuznetsova et al., 2010; Rustowska, 2022, 2024; Uri et al., 2007). This might be explained by the symbiotic interaction of the birch roots with AMF facilitating N uptake from the soil (Smith & Smith, 2011), promoted by their abundance due to the lignite (Baumann et al., 2005). Moreover, an increase in N content in the aboveground plant tissues, particularly the leaves (Fig. 3), might have been caused by the emission of N oxides (NOx) from the openpit mining (Huertas et al., 2012).

In terms of K, significantly lower contents were recorded in the birch trees growing near the ash settler pond and power plant in relation to the control (Fig. 3). This is possibly due to the typically small amounts of K that occur in Podzols (Brożek & Zwydak, 2010) (in this study, the K was lower than in the Arenosol of the control stand), as well as the lignite fly ash from the Bełchatów power plant (Bąk et al., 2023; Uzarowicz et al., 2018).

The fly ash from the Bełchatów lignite mine is characterized by a high Ca content (Giergiczny & Michniewicz, 1991; Peukert et al., 1986). As reported by Hycnar et al. (2017) and Uzarowicz et al. (2018), this is due to the presence of significant amounts of CaCO3-rich lake chalk in the combusted coal (Hycnar et al., 2017). What is more, the combustion lignite rich in Ca can lead to the formation of other Ca mineral phases, such as gehlenite (Ca2Al2SiO7), ye’elimite [Ca4Al6(SO4)], anhydrite (CaSO4), and lime (CaO), which have all been found in the Bełchatów fly ash (Bąk et al., 2023). Also, the soil of the heap stand contained higher contents of Ca than the control stand, which, as reported by Pająk and Krzeklewski (2006), is due to the presence of CaCO3 in these formations. Based on the above, the increased Ca content in the birch biomass growing in the vicinity of the mine was not surprising (Fig. 3). The Ca content was considerably higher than in birches in urban areas (Modrzewska et al., 2016), and also higher than in silver birch growing on post-mining spoil heaps formed from waste rock from the coal mine in Katowice (Sitko et al., 2022). The increased accumulation recorded in this study was probably influenced by the higher pH of the overburden materials (5.8 ± 0.4–8.1 ± 0.7) compared to that recorded by Sitko et al. (2022) (3.68 ± 0.06).

The Mg contents in some of the birch tissues varied from the control only at the heap location (Fig. 3), which differed in the soil reaction (Fig. 2). As confirmed by PCA analysis (Fig. 4), the increased uptake of Mg is positively correlated with soil pH, this being a significant factor determining the availability of this nutrient to plants (Hailes et al., 1997), which explains the observed trend.

Sulfur is typically accumulated by plants from the soil in the form of sulfates, although it can be also absorbed from the air as S dioxide (SO2) (Linzon et al., 1979) and hydrogen sulfide (H2S), released during the pyrolysis of lignite (Zhang & Yani, 2011). The presence of S in these forms is particularly common in industrial areas through its emission by several activities, such as smelting, combustion, and mining (Gordon & Gorham, 1963; Katz et al., 1939; Linzon, 1958, 1965), thus contributing to the elevated contents of this nutrient in plants. Frazer (1935) highlighted that some coniferous plants growing on industrial sites exhibited significantly higher levels of S compared to their counterparts growing in non-polluted areas. Also, Katz et al. (1939) observed that the S concentrations in coniferous foliage were the highest near a lead smelter, gradually decreasing with distance from this. A similar tendency was noted in our study, with the S contents in the silver birch tissues being usually significantly higher in both the heap and settler stands than in the control (Fig. 4).

The large-scale mining and burning of coal often poses a risk of soil contamination by trace elements (Dang et al., 2002; Rout et al., 2013). However, studies conducted at the Bełchatów lignite mine site have indicated that both the combustion waste and the overburden heap do not show elevated concentrations of these (Hycnar et al., 2017; Stolecki, 2005). We can confirm these reports––the contents of Cu and Zn in the soils of the studied stands were low and, according to legal regulations (Regulation of the Minister of the Environment of 1 September 2016 on the Method of the Contamination Assessment of the Earth Surface), they did not exceed permissible norms. Therefore, the impact of lignite mining activities on the accumulation of these micronutrients by silver birch was negligible (Fig. 4), and their contents did not differ from those presented by Rustowska (2022) from Arenosol stands. Contrastingly to Cu and Zn, Mn exhibited significant differences between the heap and the settler stands vs the control stand in all tissues, showing a considerable decrease in concentration in the stands that experienced anthropogenic impacts (Fig. 4). The accumulation of Mn is primarily dependent on soil pH, which is the most effective in acidic soils (Kabata-Pendias & Pendias, 1999). Reimann et al. (2007) revealed that birches will accumulate Mn in their leaves up to 4,888 mg kg−1 in soils with low pH. This explains the higher content of Mn in the birches growing in the control stand. At the settler location, the Mn content was considerably lower than at the control stand, despite the acidic reaction of the soil. This seems to be related to the extremely low Mn contents in the soils of the settler and heap stands, which had much lower concentrations than in other soils under silver birch stands reported in the literature (Jonczak et al., 2023; Rustowska, 2022; Sitko et al., 2022). Deficiency in Mn is prevalent among plants that thrive in soils originating from parent materials with low Mn contents, as well as in soils that have undergone extensive leaching (Ivanov et al., 2022). The other explanation of the observed differences between the stands can be the impact of stand density. As presented in the work of Machava and Barna (2005), Mn content in in the foliage of dominant beech was the highest on plots with the highest density, which is in line with our study. Positive correlation of the amount of accumulated nutrients in different parts of Scots pine with stand density indicated also Węgiel et al. (2018).

According to Hycnar et al. (2017), fly ash from the Bełchatów power plant contains a number of mineral forms of Fe, including hematite (Fe2O3), magnetite (Fe3O4), wüstite (FeO), goethite (FeO(OH)), lepidocrocite (FeO(OH)), and pyrrhotite (FeS), indicating the possible capture of this nutrient from dust by birch, and an increase in the Fe content of the sites close to the settling pond and power plant. However, we found no such trend (Fig. 3), the statistical analysis showing significant differences between the heap and control stands, but the trend being unclear.

The distribution of nutrients accumulated in trees is dependent on the specific nutrient demands and functions of each organ (Martins et al., 2019; Miller, 1995; Tromp, 1983). In addition, in deciduous trees, this is controlled by the retranslocation process, which is an important strategy for preserving the loss of nutrients from senescent leaves (Jonczak et al., 2023; Scalon et al., 2017). This tissue usually contains the highest content of nutrients, followed by the branches, bark, or roots, while stemwood has the lowest (Alifragis et al., 2001; Sharma & Sharma, 2013; Vos et al., 2023). In this study, the distribution of the majority of the nutrients showed a similar pattern (see Supplementary material), which was also consistent with the findings reported for silver birch by Novák et al. (2017) and Rustowska (2022, 2024).

5 Conclusions

Based on the obtained data, our hypothesis that the site characteristics in the lignite mining zone would be reflected in the nutritional status of the silver birch stands seems to have been confirmed for the majority of nutrients. However, depending on the nutrient and the site conditions, the effect was diverse. Statistical analysis demonstrated that silver birch growing on the heap comprising overburden material deposited during lignite mining had increased contents of, particularly, S, followed by Fe and Mg, while the birches growing in the vicinity of the fly ash settling pond and power plant showed a capacity to retain mainly Ca and S in the majority of their tissues. We found lower accumulations of some nutrients, especially Mn, which was considerably decreased in both of the polluted stands compared to the control. Additionally, P and K accumulation in the zone under the impact of fly ash was reduced in relation to the undisturbed forest stand. In the case of Fe, although significant differences were present in some cases, the tendency was not clear. The impact of lignite mining operations on the accumulation of Cu and Zn was negligible. The distribution of nutrients was typical for tree species, with the leaves being the most abundant tissue (except for Fe), while the stemwood was the poorest. Overall, the results of this study, in tandem with the anthropogenically altered nature of the site, indicate the complexity of the issue of nutrient accumulation in silver birch trees growing in the investigated area, in which soil-related parameters and the nutrient composition of the fly ash seem to have play important roles. Our findings expanded knowledge in the field of silver birch ecology of the areas affected by lignite opencast mining, and they have the potential to be applied to the effective reclamation and restoration of degraded areas.