Abstract
With a substantial rise in both domestic and worldwide copper mining rates over the past decade, Iran has become a major producer of copper in the Middle East. The increasing need for copper-based products in a variety of industries, including as information technology, electronics, transportation, and construction, is driving this rise. However, the expansion of copper mining activities has led to environmental degradation, particularly in mining sites where potentially hazardous elements (PTEs) have contaminated the soil. Despite these significant environmental impacts, they have often been overlooked, posing long-term environmental challenges as copper extraction continues. This research extensively reviews the literature (from 2000 to 2023) on soil contamination in Iran’s copper mining districts, focusing on PTEs. It evaluates the extent of potentially hazardous elements’ pollution in soils, comparing findings with global data, and explores remediation strategies employed in these regions. Results suggest that studies predominantly center around the Sarcheshmeh copper mine, highlighting copper, lead, and molybdenum as dominant PTE pollutants. Phytoremediation emerges as the primary remediation method used in these areas, indicating Iran's sustainable approach to addressing potentially hazardous elements’ contamination. This review recommends comprehensive monitoring of PTEs across all Iranian copper mines and further exploration of native plant species that successfully grow and stabilize potentially hazardous elements grow in copper mining areas remediation.
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Introduction
Copper (Cu) is widely recognized as a significant metal for contemporary society, technology, and infrastructure, taking its place as the third most crucial element, following iron and aluminum (Sverdrup et al. 2014). The need for Cu resources has been steadily growing due to rapid growth of the world’s economy and industrialization (Buayam et al. 2019). Cu is a widely used metal in various industries, including electrical, automotive, and household sectors. Additionally, it has gained recognition for its antimicrobial properties, making it an effective surface in recent times (Elguindi et al. 2011). It is believed that human civilizations initially utilized this metal since it could be found in the native, metallic form, eliminating the need for smelting (Grass et al. 2011).
The majority of Cu deposits are extracted through open-pit mining, while underground mining methods are used less frequently (Berger et al. 2008). To produce 1 ton of copper, the typical process involves excavating and crushing over 150 tons of ore. The ore is then concentrated through froth flotation and extracted via various methods, which depend on whether the ore is sulfide or non-sulfide in nature (Wills and Napier-Munn 2006). The entire process generates significant quantities of tailings, which are the remnants of the ore after copper extraction. These tailings contain elevated levels of PTEs such as Zn, Pb, Fe, Cd, as well as metalloids like As. These harmful substances can be transferred to both aquatic and terrestrial ecosystems, impacting trophic circuits, biodiversity, water, sediments, soils, and human health (Baycu et al. 2015; Rzymski et al. 2017). In addition, the discharge of acidic water from mines, commonly referred to as acid mine drainage (AMD), contributes to the release of harmful components that are dissolved from rocks exposed to water with a very low pH. This process is predominantly caused by the oxidation of iron sulfide (Akcil and Koldas 2006; Rouhani et al. 2023a).
There is a significant risk of pollution from mining operations to the nearby environment. If waste materials from mining activities are improperly disposed without the implementation of proper monitoring systems, there is a considerable risk that pollutants will be dispersed into the nearby soil adjacent to the mine by wind, water, and rainfall (Boussen et al. 2013; García-Lorenzo et al. 2012; Wang et al. 2009). There can be significant increases—up to three times—in the content of several PTEs in the soil near mining sites. Owing to their extended stability in the soil and subsequent uptake by flora and fauna through plant consumption, these compounds pose a significant threat to human health as well as ecosystems. This risk is most noticeable in situations where mining operations are located near agricultural areas (Álvarez-Ayuso et al. 2012; Boussen et al. 2013; Khazaee et al. 2015).
To manage the discharge of PTEs into the environment, soil remediation strategies have been developed with some strategies still evolving. Phytoremediation has received significant interest from researchers as an easily applicable eco-friendly, and effective technique for soil remediation (Sytar et al. 2019; Nsanganwimana et al. 2021). Employing plants as a treatment method to remove pollutants from the environment is known as phytoremediation. The application of plants to eliminate pollutants is an environmentally friendly method that does not disturb the ecosystem, as it does not adversely impact topsoil (Erickson & Pidlisnyuk 2021). The most important step to successfully use plant-based remediation for polluted soils and mine tailings is the selection of appropriate hyperaccumulators (van der Ent et al. 2024). Hyperaccumulator plants have the potential to extract, accumulate, and endure elevated concentrations of PTEs. These plants can accumulate PTEs in their roots and shoots, by phytostabilization and phytoextraction, respectively. Phytostabilization comprises the immobilization of contaminants within the soil, whereas phytoextraction encompasses the utilization of plants to extract/remove contaminants from polluted soil (Erickson & Pidlisnyuk 2021; van der Ent et al. 2024). However, it is important to take into account that mining areas are not conducive for vegetation growth, due to issues such as low water availability, unfavorable pH, high concentrations of harmful PTEs, and low levels of organic matter and nutrients (Borbón-Palomares et al. 2024).
The mining and processing of Cu ore have a significant environmental impact, particularly due to the large volume of tailings left over after extracting copper from the ore, which poses serious environmental risks due to their high levels of toxicity from PTEs. According to the existing literature, there is a limited number of review studies that were conducted to investigate the prevalence and distribution of PTEs in Cu mining regions, as well as the remediation approaches employed worldwide. Thus, there is limited information available for PTEs and their successful remediation from the many Cu mining sites in Iran. With this background, the objective of the present review study is to understand and highlight the distribution of metals and major polluting PTEs in Cu mining areas from Iran. The study further assesses the remediation strategies applied in these areas.
Cu mines in Iran
Iran has a rich history of mining and associated industries. The country possesses a diverse range of mines, some of which have a history spanning thousands of years. In Iran, a transition from unscientific to scientific and systematized ore extraction occurred around 1847, marking the distinction between scientific and non-scientific mining periods (Pezeshkan et al. 2005). Currently, ownership of Iranian mines is divided between private and public (governmental) sectors. In general, mines that are controlled by the private sector are smaller in size and have less environmental risks in comparison to mines controlled by the government. Government-controlled mines, on the other hand, are usually bigger and often need a processing plant, particularly for minerals including lead, zinc, gold, copper, etc. (Monjezi et al. 2009). Unfortunately, there is only limited information available in the existing literature about Cu mining in Iran. Information about some of the most important copper mines in Iran presented further.
The Sarcheshmeh copper deposit, which has 1 billion tonnes with an average copper content of 0.9%, is regarded as the fourth-largest mine in the world. This ore body is situated in the southeastern region of Iran, specifically in Kerman province (Banisi and Finch 2001). Mining activities have been in progress at the copper mine complex since 1972, resulting in a significant increase in copper extraction from 15,000 to 70,000 tonnes. Copper mining has usually utilized both pyrometallurgical and hydrometallurgical methods for processing sulphide minerals (Sadeghi Pour Marvi et al. 2016). Open pit mining is utilized to extract Cu deposits in Sarcheshmeh, with approximately 40,000 tons of ore extracted daily (Banisi and Finch 2001). Biochemical and mechanical manipulation and processing of minerals have generated significant amounts of AMD, dust, and tailings (Sadeghi Pour Marvi et al. 2016). The Darrehzar porphyry copper mine is situated to the south of the Uromieh-Dokhtar volcano-magmatic belt, specifically in the southeast Dehaj-Sarduyeh volcano-magmatic belt. It is located approximately 10 km south of the well-known Sarcheshmeh porphyry copper mine in Kerman province. The deposit consists of 49 million tons of ore with a grade of 0.64% Cu and 0.004% Mo (Soltani et al. 2014). The Uromieh-Dokhtar magmatic belt is globally recognized as a significant area for copper deposits. The Alpine-Himalayan collisional orogenic belt extends from western Europe to Turkey, passing through Iran and extending into western Pakistan (Shafiei et al. 2008). The Porphyry copper mineralization found at Darrehzar has an association with granodioritic intrusive rocks from the Miocene period. These rocks are located within volcano-sedimentary rocks from the Eocene period and carbonate rocks from the Cretaceous period (Derakhshani and Abdolzadeh 2009; Soltani et al. 2014).
Sungun Cu Mine has been in operation since 2008 and it is the largest open-pit copper mine in northwest Iran (Nasrabadi et al. 2009). The porphyry deposit is situated in the East Azarbaijan province of Iran, specifically on the Alp Himalaya international metallurgical belt. It is located approximately 105 km northeast of Tabriz. This deposit is well-known for its vast reserve of sulfide copper ore, estimated to be nearly one billion tons (Rezaei et al. 2020). Sungun porphyries are belonging to Oligo-Miocene age and have erupted into upper Cretaceous carbonate rocks along with various types of Eocene erinaceous-argillaceous rocks, pyroclastic rocks, and lavas (Calagari 2003). Ore deposits and extraction facilities have been situated within the Arasbaran forest; an environmentally protected area that has been formally declared by UNESCO as a Natural Heritage site (Aghili et al. 2018).
Baychebagh copper mine is situated adjacent to the town of Mahneshan, approximately 160 km west of Zanjan. The existence of underground mine workplaces, an extensive system of production galleries, as well as other mining facilities, are indicative of a long period of production. The district contains numerous prospect pits and mining tunnels, which have led to the excavation of over 5.6 km of exploration tunnels and 3.6 km of tunnels from nine large ore veins, measuring 20–50 cm in width. Cu production in this mine is about 215,000 tons, with ore reserves estimated to be approximately 12 million tons. Before World War II, ore processing facilities have been established and employed. The Baychebagh deposit is a type of polymetallic massive sulphide ore deposit. It is found within a series of volcano-sedimentary complexes that are part of the Sanandaj-Sirjan volcanic belt. This belt offers substantial economic importance due to its considerable mineral potential and confirmed reserves of copper ore (Ghazban et al. 2015). The distribution of the various Cu mines in Iran are presented in Figs. 1 and 2.
![figure 2](http://media.springernature.com/lw685/springer-static/image/art%3A10.1007%2Fs13762-024-05800-8/MediaObjects/13762_2024_5800_Fig2_HTML.jpg)
(Source: Eisa Mohammadi 2023)
Sarcheshmeh copper mine in SE Iran
Potentially toxic elements
Earlier investigations revealed that along with Cu many PTEs, including As, Cd, Cr, Mn, Ni, Pb, and Zn, accumulate in the topsoil surrounding Cu mines (Bidone et al. 2001; Hadjipanagiotou et al. 2020; Sun et al. 2023; Radi et al. 2023). These PTEs have the potential to persist in soils for a long period, causing potential adverse health effects to residents via the food chain and being exposed to soil contamination (Gustin et al. 2021; Rouhani & Shahivand 2020).
Several possible explanations exist for these findings. Firstly, excessive quantities of copper minerals, such as chalcopyrite, cuprite, covellite, chalcocite, and malachite, discharged into soil during mining activities. This is primarily caused by destructive mining processes and inadequate treatment of mineral waste residue and wastewater (Alizadeh et al. 2024; Punia 2021). Cu-tailing dams also contribute significantly to Cu contamination of soil (Das and Maiti 2008). Secondly, mining activities generate substantial quantities of slags and aerosols, which are by-products containing various pollutants such as Zn, Cd, As, Pb, and Cu, are major contributors to soil pollution with PTEs (Izydorczyk et al. 2021). In addition, minerals often contain associated contaminants including Zn, Pb, Cd, and As coupled with Cu. During the process of excavating ore, metallurgical dust is released, which contains elevated levels of these hazardous elements. Consequently, these contaminants migrate into the surrounding soils (Radi et al. 2023; Izydorczyk et al. 2021).
Acid mine drainage (AMD) occurs when pyrite and other sulfate metals (such as tailing pits and dams open exposed cuts, and ore and waste-rock piles) oxidize due to exposure to air and microbial activity in mining areas. Numerous studies have demonstrated the critical role that water plays in the distribution and mobility of PTEs in the vicinity of mining sites (Han et al. 2017; Liao et al. 2016; Rouhani et al. 2023b). High levels of PTEs and sulfate, as well as low pH values, are features associated with AMD. Furthermore, as prior studies have shown (Kefeni et al. 2017; Xie et al. 2018), the corrosive properties of AMD interact with rocks that contain mineral ores, causing PTEs to dissolve and subsequently elevating their concentrations in nearby water streams and soils.
The variation in pollutants between global Cu mining sites can be attributed to the diverse geological conditions and methods used to extract Cu mineral resources (Nirola et al. 2016). Additionally, the type of Cu mining practices (such as waste disposal techniques, opencast working, and underground mining) has a direct impact on the discharge of hazardous metals (such as Cu and Cd) to nearby soils (Radi et al. 2023; Izydorczyk et al. 2021). The concentration of PTEs in topsoil may also be strongly impacted by distance between sample locations and centers of Cu mines (Koz et al. 2012; Su et al. 2018). The distribution of PTEs in the copper mining area is influenced by climatic conditions, including wind, precipitation, and temperature. Particularly, the process of PTE transportation in Cu mining area is directly influenced by wind direction and intensity (Punia 2021; Mulenga et al. 2022). Furthermore, the distribution of PTE in soils associated with Cu mines was found to be affected by variables such as exploitation methods soil properties, and site use (Alizadeh et al. 2024).
Soil PTEs impact on human health
The dispersal of PTEs within the mine and its surrounding areas poses significant environmental and potential public health issues. Exposure to high concentrations of PTEs poses a threat to the environment due to the acute and chronic toxicity it causes in microorganisms (including soil fauna), aquatic organisms, animals, and plants (Gutiérrez et al. 2016). Human health implications are the adverse impacts that occur when individuals are directly exposed to PTEs through contact with their skin, ingestion or inhalation of polluted particles. Indirect exposure can also occur when PTEs are ingested through food chain (Tepanosyan et al. 2018; Rouhani et al. 2022). Epidemiological studies have discovered a connection between Cu mining activities and various diseases, such as cancer, renal failure, liver cirrhosis, and headaches, in inhabitants living near copper mining areas (Izydorczyk et al. 2021). PTEs, such as Ni, Cr, Pb, and Cu, detected in soils adjacent to Cu mining sites, have detrimental effects on the lung, kidney, stomach, small intestine, and cardiovascular tissues of humans, potentially leading to the development of cancer (Yang et al. 2019). Similarly, exposure to As can have detrimental effects on human health, including skin cancer, panasthenia, respiratory system disorders, and renal failure (Paithankar et al. 2021). Children living near Cu mines are at a higher risk of being exposed to polluted soil in comparison to adults in the same area. This is because children may show certain behaviors, for example pica behavior (eating non-food items) and finger/hand sucking, which can increase their exposure to the polluted soil (Ghanavati et al. 2019; Filimon et al. 2021).
PTEs in Cu mines in Iran
The study conducted on the pollution of stream water and sediments by the Sungun porphyry copper deposit in northwestern Iran revealed significantly increased levels of PTEs in samples analyzed. These increased concentrations of PTEs pose a potential risk to health of communities that directly utilize untreated river water for household uses and recreational activities. In the Sungun region, metal pollution, particularly by Ni, Pb, Mo, and Cu, was a major factor in the sediments, which highlighted the necessity of additional research to determine the long-term impacts of pollutants, as well as waste dumps, and tailing dams, on the sediment chemistry (Moore et al. 2011). In a more recent study, the spatial distribution and vertical variations of PTEs in the sediment of Pakhir River, located downstream of the Sungun copper mine in northwest of Iran have been assessed. The findings indicated that the highest level of contamination was detected in the sample taken from Pakhir valley, with Cu being the primary contributor to sediment contamination. The first 50 cm of the ground surface revealed the highest level of PTEs, which subsequently decreased in amount as the sediment depth increased (Aghili et al. 2018).
The average concentration of Cu in soil surrounding the Mazraeh copper mine in northwestern Iran was found to be twice as high as the global guideline values. This elevated concentration might be attributed to the collapse of the tailing dam, which happened as a result of severe rains in May 2009 (Shahbazi et al. 2013). Soil samples taken from the Sorkheh and Mazraeh Cu mining sites in northwestern Iran showed significant levels of contamination with As, as well as moderate contamination with Pb and Zn (Hoseinpour et al. 2020). Similarly, Petrović et al. (2021) reported significant levels of As within a Cu mining region located near Bor, Serbia. Mining activities in Darrehzar Cu mine deposit (Kerman, Iran) have resulted in contamination of water and sediments with Cu, Cd, and Mo (Soltani et al. 2014). The study conducted on PTEs contamination in water and sediments from the Ghalechay river, particularly in the Baychebagh Cu mine area, revealed moderate levels of Cu contamination in the sediments. Additionally, the sediments were highly contaminated with Pb and Cd (Ghazban et al. 2015). High levels of Cu and Se elements in soil surrounding the Taknar Cu mine (located in NE Iran) have been attributed to anthropogenic sources, primarily associated with mining and mineral processing activities (Khosaravi et al. 2020). Mining activities carried out at the Maiduk Cu Complex have resulted in a significant increase in the levels of Cd, Pb, and Cu detected in soil samples taken from Shahr-e-Babak in the Kerman province of Iran (Damangir et al. 2015). In another study, it has been found that the levels and distribution of PTEs (Pb, Zn, Mo) were higher in Meiduk Cu mine areas, where elevated levels were observed in areas adjacent to the mine pits and waste dumps, indicating that these locations are likely sources of metal contamination (Rezaei et al. 2019).
The primary cause of soil contamination by Zn, Pb and Cu in surrounding areas of the Sarcheshmeh Cu mining and smelter in southeastern Iran was emissions resulting from recently mining and smelting operations. These emissions eventually spread through atmospheric transport, leading to contamination of the surrounding soil (Shamsaddin et al. 2020). In a more recent study, it was evident that soil and sediment surrounding the Sarcheshmeh Cu mine were polluted with Cu, and pollution levels showed a decreasing trend from the mine site towards Rafsanjan city (Ganjeizadeh Rohani & Mohamadi 2022). Sedimentary systems surrounding the Dar-e-Allo Cu mine in Iran showed higher levels of Cu, S, and Mo pollution, with alarming contamination level of Cu in this area (Bavi et al. 2023). Similar results were obtained from two Cu mining areas in China. Soils surrounding the Dexing Cu mine in Jiangxi Province, China, were contaminated by several PTEs including Hg, As, Cd, Pb, Zn, Cu, and to some extent by Cr. In particular, the pollution caused by Cu posed a significant risk to the soil quality (Ni et al. 2023). In soil samples taken from a typical Cu mining city located in eastern China, it was found that Cu had the highest mean concentration of 184.29 mg/kg, followed by Hg, Cd, Tl, Ni, As, and Pb. About 54.2% of this study area showed moderate contamination levels of Tl, As, Cd, and Cu (Sun et al. 2023).
Based on Fig. 3a, 21 different elements were studied in soils around Cu mining areas in Iran and between them Cu, Cd, Pb, and Zn were the most frequent metals. Cu is the dominant contaminant in polluted soils of Cu mining areas in Iran, followed by Mo and Pb (Fig. 3b). As shown in Table 1, the majority of conducted studies were from Sarcheshmeh copper mine as it is the biggest and most important Cu mine in Iran. Although soils around the most important Cu mines have been studied, there are still some other Cu mines that have not gained attention for environmental impact assessment studies. The mean concentration of some PTEs in impacted soils by copper mining in Iran is presented in Table 2.
Similarly, studies done globally, PTEs that were identified as polluting elements in addition Cu included Pb, Cd, As and Zn. In a study on soil contamination nearby a Cu mine in Yedidalga (Northern Cyprus), it was found that 78.0% of the sampling locations were extremely polluted with Cu, additionally, 55.6% and 22.2% of the sampling locations were found to be moderately to extremely contaminated by Cd and Pb respectively (Barkett and Akün, 2018). High levels of Cd, as well as Cu and As, were detected in the agricultural soils surrounding the Dongchuan Cu mining area in China (Cheng et al. 2018). Agricultural soil and stream sediments in the vicinity of the Agrokipia abandoned Cu mine in Cyprus were found to be polluted with PTEs, more particularly by Li, Ag, Cr, Cd, Pb, Zn, and Cu. The contamination was primarily attributed to AMD and stream waters, as proven by the elevated levels of PTEs in both stream waters and sediments in comparison to background levels (Hadjipanagiotou et al. 2020). Soils impacted by Cu mining in Sibay city (Russia), were severely polluted by anthropogenic sources particularly by Zn, as a consequence of mining waste storage and proximity of a nearby mining and processing plant to this city. The unfavorable environment in this area resulted in the accumulation of PTEs, alterations in agrochemical characteristics, soil cover disturbance, and destruction of vegetation (Suleymanov et al. 2022). Significantly high levels of Cu and As were observed in tailings and surrounding soils of the Tamesguida abandoned Cu mine area in Médéa, Algeria. These levels were considerably higher than local soils, crustal average, and world average shale (Radi et al. 2023).
Applied remediation strategies
Issues resulting from mining or metallurgical-related PTEs are prevalent worldwide (Schreck et al. 2020). In addition, management of contaminated environmental spheres, particularly soil, is a globally important challenge due to its role as a natural reservoir for diverse contaminants (Pavoni et al. 2017). A wide range of technologies utilizing different chemical, thermal, electrical, physical, or biological processes have been assessed to determine their effectiveness in effectively and safely reducing or entirely eliminating PTEs from contaminated areas. The investigations that were conducted yielded both positive and negative results for every single strategy, as well as when the approaches were combined. Initially, the potential of various methods was assessed based on their effectiveness, duration, expenses, and any possibility of additional disruption to the treated matrix (Petrović et al. 2021). Based on existing literature, phytoremediation has been the sole strategy employed for soil amendment in copper mining areas in Iran so far. Most probably due to its advantages over other remediation strategies including low cost, its applicability, environmentally-friendly, etc.
In recent years, there has been significant progress in the application of phytoremediation technology for mitigating PTEs contamination in solid waste within mining regions. Soil phytoremediation is a widely studied topic comprising two primary strategies. The first strategy, known as phytoextraction, refers to metal absorption by plant roots, followed by their translocation and accumulation in aboveground biomass, specifically in shoots. The second strategy, phytostabilization, relies on special ability of root exudates to stabilize or immobilize metals in soil. Effectiveness of phytoextraction is dependent upon plant's ability to absorb and transport metals from soil to shoot, along with shoot’s capacity to accumulate these metals. Furthermore, the amount of green biomass formation also plays a significant role. Plants that show the highest potential for metal absorption or accumulation were identified within a relatively small group that are known as hyperaccumulators (Perlatti et al. 2015; da Silva et al. 2017; Shojaee Barjoee et al. 2023). The vast majority of hyperaccumulator plants that have been identified mostly belong to the group of herbaceous wild species. These plants are often found only in their native habitats and have low biomass yield, slow growth rate, and shallow root systems (Rascio and Navari-Izzo 2011). These plants, which are mostly small weeds, can tolerate and concentrate large quantities of PTEs in their aerial parts, allowing them to grow in metalliferous soils without showing any potential toxic impacts (Liu et al. 2018). Phytoextraction is associated with some challenges including the sustainable disposal of contaminated biomass and the possible transfer of PTEs to the food chain (Patra et al. 2020). Thus, phytostabilization of PTEs, using plant known as excluders may reduce challenges as there will be low chance of transfer of PTEs to the food chain and limited contaminated waste (roots only) as the biomass may be utilized.
Although, it is important to consider that absorption of metals from soil can be strongly influenced by several factors, including redox state, organic matter and clay contents, soil pH, etc. (Alloway 2013; Kabata-Pendias 2011), it has been widely understood that detecting metal levels in plant parts (such as roots) is not a reliable indicator of soil contamination (Alagić et al. 2018). Meanwhile, the concentration of metals in aboveground plant parts has been commonly utilized as a convenient method for assessing airborne contamination. Many biomonitoring investigations carried out in heavily polluted areas, including mining and metallurgical areas, have been depending on measuring metal concentrations in various plant parts (both washed and unwashed), including stems, branches, leaves, or shoots (Alagić et al. 2018; Khalid 2019; Schreck et al. 2020; Simon et al. 2011). Several researchers have pointed out that concentrations of metal in these regions are derived not only from contaminated soil but also from contaminated atmosphere. This knowledge has provided a strong foundation for conducting various thorough environmental quality evaluations, such as food chains quality in the areas of interest. In conclusion, it is worth noting that a variety of higher plants have frequently been observed growing well in the impacted regions. As a result, many researchers have utilized the various parts of these plants as cost-effective and easily available biomonitoring tools (Alagić et al. 2018; Petrović et al. 2021).
Phytoremediation studies in Cu mining areas in Iran have identified various different plants that have successfully remediated sites with various PTEs. Malayeri et al. (2008) investigated efficacy of accumulator plants for phytoremediation in soil contaminated by the Hame Kasi Cu mine in northwest region of Hamedan city, Iran. Their results showed that species of Verbascum speciosum, Chenopodium botrys, Cirsium comgestum, Scariola orientalis, and Cousin asp. are suitable high accumulator plants for mitigating Cu. Later, another study on this area revealed that Chenopodium botrys, Cousinia sp. and Ziziphora clinopodioides were the most efficient plants in phytostabilization of Zn, while, Euphorbia macroclada was the most suitable plant for phytostabilization of Cu and Fe, and also Stipa barbata and Chondrila juncea had the highest potential for phytostabilization of Mn (Lorestani et al. 2011). Around the Sarcheshmeh Cu mine, it was reported that Urtica urens has the greatest potential for Sr absorption (Shahraki et al. 2008). Subsequent research by Ghaderian & Ghotbi Ravandi (2012) revealed that two specific plant species, namely E. hirsutum and P. fugax can be tentatively regarded as hyperaccumulators of Cu in the Sarcheshmeh Cu mining area. In a more recent study, Z. fabago, A. leucoclada, C. dactylon, and T. ramosissima, were found to possess high tolerance and high potential for adsorbing various PTEs at Sarcheshmeh Cu mine tailings (Tabasi et al. 2018). Sonchus oleraceus grown nearby the Cheshmeh-Konan Cu deposit (NW Iran) was evaluated by Samadi et al. (2019) for PTE absorption. This study revealed that S. oleraceus has a high potential to absorb Sc, Sn, Sr, Mo, and Cd. Three prevalent plants in Sorkheh and Mazraeh mines, including Cirsium vulgare, Stachys inflata, and Alhaji maurorum, were evaluated by Hoseinpour et al. (2020) for their potential to absorb metals from polluted soils. They reported that S. inflata and A. maurorum have significant potential for the accumulation of Sc, Mo, and Cd from impacted soils in the Sorkheh region. The implemented phytoremediation using various phytoagents show that phytoextraction is the most common method employed with only one study employing phytostabilization which was successful for Cu. Thus, it will be important to also identify plant excluders that can stabilize the most polluting PTEs; Pb and Mo.
Similarly, phytoextraction of Cu has been successful in various Cu mines in other parts of the world. Different plant species have successfully absorbed Cu. Albeit the success with Cu extraction, there is little information on the phytoremediation of other prevalent PTEs in Cu mines. Cultivation of Brassica juncea L resulted in several positive effects in impacted soil from the Cu mine in Touro, Galicia, Spain. These effects included an increase in content of C and total N in soil, a reduction in extreme soil acidity, and a decrease in the pseudototal concentration of Cu (Rodríguez-Vila et al. 2014). In order to identify ideal hyperaccumulators, Wang et al. (2019) investigated dominant plants species in the Machangqing Cu mine area (Yunnan Province, China). They identified that P. yunnanensis and P. massoniana showed substantial Cd uptake as well as an extreme capacity to transfer PTEs from roots to leaves. Such characteristics make these plants valuable for phytoremediation in mining areas for mitigating environmental pollution. In cases where soil pollution is not too high, Ptychostomum capillare was able to absorb Cu, according to research done on biomonitoring of PTE contamination in a former Cu mine in Central Spain (Elvira et al. 2020). Petrović et al. (2021) conducted a study in Bor, Serbia, an area known for Cu mining and discovered that sun spurge (Euphorbia helioscopia L.) had the highest concentration of each metal compared to other plants, particularly Cu. This suggests that sun spurge has more effective mechanisms for extracting, transferring, and accumulating metals than common nettle (Urtica dioica L.).
Conclusion and future perspectives
Cu mining produces large amounts of waste, such as tailings and acid outflows, which pose threats to human health as well as potentially serious and long-lasting environmental effects. Scholars from all over the world, including those in different parts of Iran, have examined soil metal pollution resulting from Cu mining in great detail. This study offers the first thorough evaluation of the amounts of pollutants known to be PTEs in the soils of Iranian Cu mining sites. Since Sarcheshmeh Copper Mine is the largest and most significant Cu mine in Iran, the majority of research that have been undertaken have focused on it. Environmental impact assessment studies have focused on the soils surrounding the most significant Cu mines in Iran, while several other Cu mines have not received the same attention. Various elements were analyzed in the soils surrounding copper mining areas, with Cu, Cd, Pb, and Zn being the most frequently measured metals. The results show that PTEs discharged during mining operations have seriously contaminated the soils in these areas, with Cu, Pb, and Mo showing up as the most common contaminants. These substances have the potential to negatively impact soil fertility and quality, which could have an impact on animal and human health by way of the food chain. In Iranian Cu mining sites, phytoremediation—especially phytoextraction—has been the only used remediation technique, indicating a sustainable solution to dealing with PTE contamination. Identifying the most efficient plant species for phytoremediation in these areas primarily involved studying native plant species growing in polluted soils. To address issues with phytoextraction, like PTE transmission to the food chain and biomass disposal, more research must be done on phytostabilization strategies, especially for Pb and Mo. In order to improve remediation efforts and environmental management techniques, this review emphasizes the significance of thorough PTE monitoring throughout all Iranian copper mines and additional research on native plant species that successfully stabilize PTEs in copper mining sites. Thus, for future studies related to soil pollution by PTEs in Cu mine sites and surrounding environments, the following recommendations should be considered:
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More investigations of PTEs are needed in the different Cu mines in Iran with suitable phytoremediation strategies for most common PTEs.
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In Iran only the phytoremediation strategy has been used in Cu mining areas. Therefore, future studies should focus on implementing developed and environmentally friendly techniques to enhance soil health in Cu mines. Some potential approaches to consider include the utilization of biochars and nano materials.
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Different routes of PTEs emission in soil from Cu mining sites should be extensively investigated for future studies.
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Assessment and monitoring of the risk element’s contamination of the air-borne dust derived from copper mining should be considered for future studies.
Data availability
The datasets generated during this study are presented in the tables in this manuscript.
References
Aghili S, Vaezihir A, Hosseinzadeh M (2018) Distribution and modeling of heavy metal pollution in the sediment and water mediums of Pakhir River, at the downstream of Sungun mine tailing dump. Iran Environ Earth Sci 77:1–13. https://doi.org/10.1007/s12665-018-7283-z
Akcil A, Koldas S (2006) Acid Mine Drainage (AMD): Causes, treatment and case studies. J Cleaner Prod 14(12–13):1139–1145. https://doi.org/10.1016/j.jclepro.2004.09.006
Alagić SČ, Tošić SB, Dimitrijević MD, Nujkić MM, Papludis AD, Fogl VZ (2018) The content of the potentially toxic elements, iron and manganese, in the grapevine cv Tamjanika growing near the biggest copper mining/metallurgical complex on the Balkan peninsula: phytoremediation, biomonitoring, and some toxicological aspects. Environ Sci Pollut Res 25:34139–34154. https://doi.org/10.1007/s11356-018-3362-7
Alloway BJ (2013) Heavy metals in soils. Trace metals and metalloids in soils and their bioavailability. Environmental pollution (22), third edition. Springer. New York. https://doi.org/10.1007/978-94-007-4470-7
Alizadeh A, Ghorbani J, Motamedi J, Vahabzadeh G, van der Ent A (2024) Edraki M (2024) Soil contamination around porphyry copper mines: an example from a semi-arid climate. Environ Monit Assess 196:204. https://doi.org/10.1007/s10661-024-12384-w
Álvarez-Ayuso E, Otones V, Murciego A, García-Sánchez A, Regina IS (2012) Antimony, arsenic and lead distribution in soils and plants of an agricultural area impacted by former mining activities. Sci Total Environ 439:35–43. https://doi.org/10.1016/j.scitotenv.2012.09.023
Banisi S, Finch J (2001) Testing a flotation column at the Sarcheshmeh copper mine. Miner Eng 14(7):785–789. https://doi.org/10.1016/S0892-6875(01)00073-5
Barkett MO, Akün E (2018) Heavy metal contents of contaminated soils and ecological risk assessment in abandoned copper mine harbor in Yedidalga. Northern Cyprus Environ Earth Sci 77(10):378. https://doi.org/10.1007/s12665-018-7556-6
Bavi H, Gharaie MHM, Moussavi-Harami R, Zand-Moghadam H, Mahboubi A, Tohidi MR (2023) Spatial dispersion hot spots of contamination and human health risk assessments of PTEs in surface sediments of streams around porphyry copper mine. Iran Environ Geochem Health 45(6):3907–3931. https://doi.org/10.1007/s10653-022-01471-x
Baycu G, Tolunay D, Ozden H, Csatari I, Karadag S, Agba T, Rognes SE (2015) An abandoned copper mining site in Cyprus and assessment of metal concentrations in plants and soil. Int J Phytorem 17(7):622–631. https://doi.org/10.1080/15226514.2014.922929
Berger BR, Ayuso RA, Wynn JC, Seal II RR (2008) Preliminary model of porphyry copper deposits (No. 2008–1321–55 p). US Geological Survey
Bidone ED, Laybauer L, Castilhos ZC, Maddock JEL (2001) Environmental risk increase due to heavy metal contamination caused by a copper mining activity in Southern Brazil. An Acad Bras Ciênc 73(2):277–286. https://doi.org/10.1590/S0001-37652001000200011
Borbón-Palomares DB, González-Méndez B, Loredo-Portales R, Tinoco-Ojanguren C, Molina-Freaner F (2024) Phytostabilization alternatives for an abandoned mine tailing deposit in northwestern Mexico. Plant Soil 497:199–218. https://doi.org/10.1007/s11104-023-06095-3
Boussen S, Soubrand M, Bril H, Ouerfelli K, Abdeljaouad S (2013) Transfer of lead, zinc and cadmium from mine tailings to wheat (Triticum aestivum) in carbonated Mediterranean (Northern Tunisia) soils. Geoderma 192:227–236. https://doi.org/10.1016/j.geoderma.2012.08.029
Buayam N, Davey MP, Smith AG, Pumas C (2019) Effects of copper and pH on the growth and physiology of desmodesmus sp. AARLG074. Metabolites 9(5):84. https://doi.org/10.3390/metabo9050084
Calagari AA (2003) Concentration variations of major and minor elements across various alteration zones in porphyry copper deposit at Sungun, East Azerbaijan. Iran J Sci 14:21–36
Cheng X, Drozdova J, Danek T, Huang Q, Qi W, Yang S, Zou L, Xiang Y, Zhao X (2018) Pollution assessment of trace elements in agricultural soils around copper mining area. Sustainability 10(12):4533. https://doi.org/10.3390/su10124533
Damangir AA, Baghvand A, Monavari SM, Moattar F (2015) Metal pollution assessment in soil samples of mining area, Shahr-E-Babak. Iran Int J Adv Biol Biomed Res 3(1):24–34
da Silva WR, da Silva FBV, Araújo PRM, do Nascimento CWA, (2017) Assessing human health risks and strategies for phytoremediation in soils contaminated with As, Cd, Pb, and Zn by slag disposal. Ecotoxicol Environ Saf 144:522–530. https://doi.org/10.1016/j.ecoenv.2017.06.068
Das M, Maiti SK (2008) Comparison between availability of heavy metals in dry and wetland tailing of an abandoned copper tailing pond. Environ Monit Assess 137:343–350. https://doi.org/10.1007/s10661-007-9769-0
Derakhshani R, Abdolzadeh M (2009) Geochemistry, mineralization and alteration zones of Darrehzar porphyry copper deposit, Kerman. Iran J Appl Sci 9(9):1628–1646
Elguindi J, Hao X, Lin Y, Alwathnani HA, Wei G, Rensing C (2011) Advantages and challenges of increased antimicrobial copper use and copper mining. Appl Microbiol Biotechnol 91:237–249. https://doi.org/10.1007/s00253-011-3383-3
Elvira NJ, Medina NG, Leo M, Cala V, Estébanez B (2020) Copper content and resistance mechanisms in the terrestrial moss Ptychostomum capillare: a case study in an abandoned copper mine in central Spain. Arch Environ Contam Toxicol 79(1):49–59. https://doi.org/10.1007/s00244-020-00739-6
Erickson LE, Pidlisnyuk V (2021) Phytotechnology with Biomass Production: Sustainable Management of Contaminated Sites, 1st edn. CRC Press, Boca Raton. https://doi.org/10.1201/9781003082613
Filimon MN, Caraba IV, Popescu R, Dumitrescu G, Verdes D, Petculescu Ciochina L, Sinitean A (2021) Potential ecological and human health risks of heavy metals in soils in selected copper mining areas—A case study: The Bor area. Int J Environ Res Public Health 18(4):1516. https://doi.org/10.3390/ijerph18041516
Ganjeizadeh Rohani F, Mohamadi N (2022) Distribution and risk assessment of toxic metal pollution in the soil and sediment around the copper mine. Environ Health Eng Manag J 9(3):295–303. https://doi.org/10.34172/EHEM.2022.30
García-Lorenzo M, Pérez-Sirvent C, Martínez-Sánchez M, Molina-Ruiz J (2012) Trace elements contamination in an abandoned mining site in a semiarid zone. J Geochem Explor 113:23–35. https://doi.org/10.1016/j.gexplo.2011.07.001
Ghaderian SM, Ghotbi Ravandi AA (2012) Accumulation of copper and other heavy metals by plants growing on Sarcheshmeh copper mining area. Iran J Geochem Explor 123:25–32. https://doi.org/10.1016/j.gexplo.2012.06.022
Ghanavati N, Nazarpour A, De Vivo B (2019) Ecological and human health risk assessment of toxic metals in street dusts and surface soils in Ahvaz. Iran Environ Geochem Health 41(2):875–891. https://doi.org/10.1007/s10653-018-0184-y
Ghazban F, Parizanganeh A, Zamani A, Taghilou B (2015) Assessment of heavy metal pollution in water and sediments from the Ghalechay River, Baychebagh copper mine area. Iran Soil and Sedim Contam: Int J 24(2):172–190. https://doi.org/10.1080/15320383.2014.937391
Grass G, Rensing C, Solioz M (2011) Metallic copper as an antimicrobial surface. Appl Environ Microbiol 77(5):1541–1547. https://doi.org/10.1128/AEM.02766-10
Gustin MS, Hou D, Tack FM (2021) The term “heavy metal(s)”: history, current debate, and future use. Sci Total Environ 789:147951. https://doi.org/10.1016/j.scitotenv.2021.147951
Gutiérrez M, Mickus K, Camacho LM (2016) Abandoned PbZn mining wastes and their mobility as proxy to toxicity: a review. Sci Total Environ 565:392–400. https://doi.org/10.1016/j.scitotenv.2016.04.143
Hadjipanagiotou C, Christou A, Zissimos AM, Chatzitheodoridis E, Varnavas SP (2020) Contamination of stream waters, sediments, and agricultural soil in the surroundings of an abandoned copper mine by potentially toxic elements and associated environmental and potential human health–derived risks: a case study from Agrokipia. Cyprus Environ Sci Pollut Res 27:41279–41298. https://doi.org/10.1007/s11356-020-10098-3
Han Y, Youm S, Oh C, Cho Y, Ahn JS (2017) Geochemical and eco-toxicological characteristics of stream water and its sediments affected by acid mine drainage. CATENA 148:52–59. https://doi.org/10.1016/j.catena.2015.11.015
Hoseinpour F, Hosein-Nejad Mohtarami M, Alipour S, Torbati S (2020) Heavy metal contaminations at two iranian copper mining areas and the remediation by indigenous plants. Iran J Toxicol 14(2):81–92. https://doi.org/10.32598/ijt.14.2.501
IDOE (Iran Department of Environment) (2014) Iranian soil quality guidelines for the protection of environmental and human health. Tehran: Iranian Department of Environment. http://www.doe.ir/Portal/file/?692345/1395-standards.pdf
Izydorczyk G, Mikula K, Skrzypczak D, Moustakas K, Witek-Krowiak A, Chojnacka K (2021) Potential environmental pollution from copper metallurgy and methods of management. Environ Res 197:111050. https://doi.org/10.1016/j.envres.2021.111050
Kabata-Pendias A (2011) Trace elements in soils and plants, 4th edn. CRC Press, Taylor and Francis Group, LLC, Boca Raton, London, New York
Khamseh A, Shahbazi F, Oustan S, Najafi N, Davatgar N (2017) Impact of tailings dam failure on spatial features of copper contamination (Mazraeh mine area, Iran). Arabian J Geosci 10:1–12. https://doi.org/10.1007/s12517-017-3040-y
Kefeni KK, Msagati TA, Mamba BB (2017) Acid mine drainage: Prevention, treatment options, and resource recovery: A review. J Cleaner Prod 151:475–493. https://doi.org/10.1016/j.jclepro.2017.03.082
Khalid S (2019) Phytomonitoring of air pollution around brick kilns in Balochistan province Pakistan through air pollution index and metal accumulation index. J Cleaner Prod 229:727–738. https://doi.org/10.1016/j.jclepro.2019.05.050
Khazaee M, Hamidian AH, Alizadeh Shabani A, Ashrafi S, Mirjalili SAA, Esmaeilzadeh E (2015) Accumulation of heavy metals and As in liver, hair, femur, and lung of Persian jird (Meriones persicus) in Darreh Zereshk copper mine. Iran Environ Sci Pollut Res 23:3860–3870. https://doi.org/10.1007/s11356-015-5455-x
Khorasanipour M, Tangestani MH, Naseh R (2012) Application of multivariate statistical methods to indicate the origin and geochemical behavior of potentially hazardous elements in sediment around the Sarcheshmeh copper mine. SE Iran Environ Earth Sci 66:589–605. https://doi.org/10.1007/s12665-011-1267-6
Khosaravi M, Saadat S, Dabiri R (2020) Evaluation of heavy metal contamination in soil and water resources around Taknar copper mine (NE Iran). Iran J Earth Sci 12(3):212–222
Khosravi V, Ardejani FD, Gholizadeh A, Saberioon M (2021) Satellite imagery for monitoring and mapping soil chromium pollution in a mine waste dump. Remote Sens 13:1277. https://doi.org/10.3390/rs13071277
Koz B, Cevik U, Akbulut S (2012) Heavy metal analysis around Murgul (Artvin) copper mining area of Turkey using moss and soil. Ecol Indic 20:17–23. https://doi.org/10.1016/j.ecolind.2012.02.002
Liao J, Wen Z, Ru X, Chen J, Wu H, Wei C (2016) Distribution and migration of heavy metals in soil and crops affected by acid mine drainage: Public health implications in Guangdong Province. China Ecotoxicol Environ Saf 124:460–469. https://doi.org/10.1016/j.ecoenv.2015.11.023
Liu L, Li W, Song W, Guo M (2018) Remediation techniques for heavy metal-contaminated soils: principles and applicability. Sci Total Environ 633:206–219. https://doi.org/10.1016/j.scitotenv.2018.03.161
Lorestani B, Cheraghi M, Yousefi N (2011) Phytoremediation potential of native plants growing on a heavy metals contaminated soil of copper mine in Iran. Int J Geol Environ Eng 5(5):299–304
Malayeri BE, Chehregani A, Yousefi N, Lorestani B (2008) Identification of the hyper accumulator plants in copper and iron mine in Iran. Pak J Biol Sci: PJBS 11(3):490–492
Mohammadi E (2023) Vast copper mines in southeastern Iran attract potential investors. https://www.aa.com.tr/en/middle-east/vast-copper-mines-in-southeastern-iran-attract-potential-investors/2949566
Moore F, Esmaeili K, Keshavarzi B (2011) Assessment of heavy metals contamination in stream water and sediments affected by the Sungun porphyry copper deposit, East Azerbaijan Province. Northwest Iran Water Qual Expo Health 3:37–49. https://doi.org/10.1007/s12403-011-0042-y
Moore F, Dehghani S, Keshavarzi B (2014) Characterization of soil contamination in Miduk mining district, SW Iran. Soil Sedim Contam: Int J 23(6):614–627. https://doi.org/10.1080/15320383.2014.856856
Monjezi M, Shahriar K, Dehghani H, Samimi Namin F (2009) Environmental impact assessment of open pit mining in Iran. Environ Geol 58:205–216. https://doi.org/10.1007/s00254-008-1509-4
Mulenga C, Clarke C, Meincken M (2022) Bioaccumulation of Cu, Fe, Mn and Zn in native Brachystegia longifolia naturally growing in a copper mining environment of Mufulira. Zambia Environ Monit Assess 194(1):8. https://doi.org/10.1007/s10661-021-09656-0
Nasrabadi T, Nabi Bidhendi GR, Karbassi AR, Hoveidi H, Nasrabadi I, Pezeshk H, Rashidinejad F (2009) Influence of Sungun copper mine on groundwater quality, NW Iran. Environ Geol 58:693–700. https://doi.org/10.1007/s00254-008-1543-2
Ni S, Liu G, Zhao Y, Zhang C, Wang A (2023) Distribution and source apportionment of heavy metals in soil around dexing copper mine in Jiangxi Province. China Sustain 15(2):1143. https://doi.org/10.3390/su15021143
Nirola R, Megharaj M, Aryal R, Naidu R (2016) Screening of metal uptake by plant colonizers growing on abandoned copper mine in Kapunda. S Aust Int J Phytorem 18(4):399–405. https://doi.org/10.1080/15226514.2015.1109599
Nsanganwimana F, Al Souki KS, Waterlot C, Douay F, Pelfrêne A, Ridošková A, Brice L, Pourrut B (2021) Potentials of Miscanthus x giganteus for phytostabilization of trace element-contaminated soils: Ex situ experiment. Ecotoxicol Environ Saf 214:112125. https://doi.org/10.1016/j.ecoenv.2021.112125
Paithankar JG, Saini S, Dwivedi S, Sharma A, Chowdhuri DK (2021) Heavy metal associated health hazards: An interplay of oxidative stress and signal transduction. Chemosphere 262:128350. https://doi.org/10.1016/j.chemosphere.2020.128350
Patra DK, Pradhan C, Patra HK (2020) Toxic metal decontamination by phytoremediation approach: concept, challenges, opportunities and future perspectives. Environ Technol Innov 18:100672. https://doi.org/10.1016/j.eti.2020.100672
Pavoni E, Petranich E, Adami G, Baracchini E, Crosera M, Emili A, Lenaz D, Higueras P, Covelli S (2017) Bioaccumulation of thallium and other trace metals in Biscutella laevigata nearby a decommissioned zinc-lead mine (Northeastern Italian Alps). J Environ Manage 186:214–224. https://doi.org/10.1016/j.jenvman.2016.07.022
Perlatti F, Ferreira TO, Romero RE, Costa MCG, Otero XL (2015) Copper accumulation and changes in soil physical–chemical properties promoted by native plants in an abandoned mine site in northeastern Brazil: implications for restoration of mine sites. Ecol Eng 82:103–111. https://doi.org/10.1016/j.ecoleng.2015.04.085
Petrović JV, Alagić SČ, Milić SM, Tošić SB, Bugarin MM (2021) Chemometric characterization of heavy metals in soils and shoots of the two pioneer species sampled near the polluted water bodies in the close vicinity of the copper mining and metallurgical complex in Bor (Serbia): Phytoextraction and biomonitoring contexts. Chemosphere 262:127808. https://doi.org/10.1016/j.chemosphere.2020.127808
Pezeshkan M, Jazayeri SA, Damghani B (2005) Mines and mining in Iran. Public relations department of Iranian Mines and Mining Industries Development and Renovation Organization (IMIDRO)
Punia A (2021) Role of temperature, wind, and precipitation in heavy metal contamination at copper mines: a review. Environ Sci Pollut Res 28(4):4056–4072. https://doi.org/10.1007/s11356-020-11580-8
Radi N, Hirche A, Boutaleb A (2023) Assessment of soil contamination by heavy metals and arsenic in Tamesguida abandoned copper mine area, Médéa. Algeria Environ Monit Assess 195(1):247. https://doi.org/10.1007/s10661-022-10862-7
Rascio N, Navari-Izzo F (2011) Heavy metal hyperaccumulating plants: how and why do they do it? and what makes them so interesting? Plant Sci 180(2):169–181. https://doi.org/10.1016/j.plantsci.2010.08.016
Rezaei A, Hassani H, Fard Mousavi SB, Hassani S, Jabbari N (2019) Assessment of heavy metals contamination in surface soils in Meiduk copper mine area. SE Iran. Earth Sciences Malaysia (ESMY) 3(2):01–08. https://doi.org/10.26480/esmy.02.2019.01.08
Rezaei S, Ranjineh Khojasteh E, Faridazad M (2020) Improving geostatistical predictions of two environmental variables using Bayesian maximum entropy in the Sungun mining site. Stochastic Environ Res Risk Assess 34:1775–1794
Rodríguez-Vila A, Covelo EF, Forján R, Asensio V (2014) Phytoremediating a copper mine soil with Brassica juncea L., compost and biochar. Environ Sci Pollut Res 21:11293–11304. https://doi.org/10.1007/s11356-014-2993-6
Rouhani A, Shahivand R (2020) Potential ecological risk assessment of heavy metals in archaeology on an example of the Tappe Rivi (Iran). SN Appl Sci 2:1–11. https://doi.org/10.1007/s42452-020-3085-5
Rouhani A, Azimzadeh H, Sotoudeh A, Ehdaei A (2022) Health risk assessment of heavy metals in archaeological soils of Tappe Rivi impacted by ancient anthropogenic activity. Chem Afr 5(5):1751–1764. https://doi.org/10.1007/s42250-022-00428-y
Rouhani A, Gusiatin MZ, Hejcman M (2023a) An overview of the impacts of coal mining and processing on soil: Assessment, monitoring, and challenges in the Czech Republic. Environ Geochem Health, 1–32. https://doi.org/10.1007/s10653-023-01700-x
Rouhani A, Skousen J, Tack FM (2023b) An overview of soil pollution and remediation strategies in coal mining regions. Minerals 13(8):1064. https://doi.org/10.3390/min13081064
Rzymski P, Klimaszyk P, Marszelewski W, Borowiak D, Mleczek M, Nowiński K, Pius B, Niedzielski P, Poniedziałek B (2017) The chemistry and toxicity of discharge waters from copper mine tailing impoundment in the valley of the Apuseni Mountains in Romania. Environ Sci Pollut Res 24(26):21445–21458. https://doi.org/10.1007/s11356-017-9782-y
Sadeghi Pour Marvi M, Pourbabaee AA, Alikhani HA, Haidari A, Manafi Z (2016) The diversity of sulfur-oxidizing bacterial populations at an Iranian copper mine and the surrounding agricultural soils. Appl Ecol Environ Res 14(3):509–533. https://doi.org/10.15666/aeer/1403_509533
Saffari M, Moosavirad SM, Hassani MJ, Ghazanfari Moghadam MS, Shakeri M, Nazari N (2021) Investigation of quantitative status and pollution indices of some pollutants in surface soils as affected by tailings dam (Case study: Chahar Gonbad copper mine). Iran J Soil Water Res 52(2):421–437. https://doi.org/10.22059/ijswr.2021.313579.668800
Samadi M, Torbati S, Alipour S (2019) Metal (loid) uptake of Sonchus oleraceus grown around Cheshmeh-Konan copper deposit. NW Iran J Min Environ 10(2):517–528
Schreck E, Viers J, Blondet I, Auda Y, Macouin M, Zouiten C, Freydier R, Dufréchou G, Chmeleff J, Darrozes J (2020) Tillandsia usneoides as biomonitors of trace elements contents in the atmosphere of the mining district of Cartagena-La Unión (Spain): New insights for element transfer and pollution source tracing. Chemosphere 241:124955. https://doi.org/10.1016/j.chemosphere.2019.124955
Shafiei B, Haschke M, Shahabpour J (2008) Recycling of orogenic arc crust triggers porphyry Cu mineralization in Kerman Cenozoic arc rocks, southeastern Iran. Miner Deposita 44:265–283. https://doi.org/10.1007/s00126-008-0216-0
Shahbazi F, Oustan S, Khamseh A, Davatgar N (2013) Spatial distribution of copper in soils around the Mazraeh mine, north-west of Iran. In 2nd International Scientific Conference, Soil and Crop Management: Adaptation and Mitigation of Climate Change, 26–28 September, 2013, Osijek, Croatia, pp. 279–287. Croatian Soil Tillage Research Organization (CROSTRO)
Shamsaddin H, Jafari A, Jalali V, Schulin R (2020) Spatial distribution of copper and other elements in the soils around the Sarcheshmeh copper smelter in southeastern Iran. Atmos Pollut Res 11(10):1681–1691. https://doi.org/10.1016/j.apr.2020.07.002
Shahraki SA, Ahmadimoghadam A, Naseri F, Esmailzaded E (2008) Study the accumulation of strontium in plant growing around Sarcheshmeh Copper Mine. Iran. VSB-Technical University of Ostrava, Ostrava, pp 239–242
Shojaee Barjoee S, Malverdi E, Kouhkan M, Alipourfard I, Rouhani A, Farokhi H, Khaledi AA (2023) Health assessment of industrial ecosystems of Isfahan (Iran) using phytomonitoring: Chemometric, micromorphology, phytoremediation, air pollution tolerance and anticipated performance indices. Urban Clim. https://doi.org/10.1016/j.uclim.2022.101394
Simon E, Braun M, Vidic A, Bogyó D, Fábián I, Tóthmérész B (2011) Air pollution assessment based on elemental concentration of leaves tissue and foliage dust along an urbanization gradient in Vienna. Environ Pollut 159(5):1229–1233. https://doi.org/10.1016/j.envpol.2011.01.034
Soltani N, Moore F, Keshavarzi B, Sharifi R (2014) Geochemistry of trace metals and rare earth elements in stream water, stream sediments and acid mine drainage from Darrehzar Copper Mine, Kerman. Iran Water Qual Expo Health 6:97–114. https://doi.org/10.1007/s12403-014-0114-x
Su J, Mathur R, Brumm G, D’Amico P, Godfrey L, Ruiz J, Song S (2018) Tracing copper migration in the Tongling area through copper isotope values in soils and waters. Int J Environ Res Public Health 15(12):2661. https://doi.org/10.3390/ijerph15122661
Suleymanov R, Dorogaya E, Gareev A, Minnegaliev A, Gaynanshin M, Zaikin S, Belan L, Tuktarova I, Suleymanov A (2022) Assessment of chemical properties, heavy metals, and metalloid contamination in floodplain soils under the influence of copper mining: a case study of sibay. South Urals Ecol 3(4):530–538. https://doi.org/10.3390/ecologies3040039
Sun K, Kong J, Gao J, Fang Y, Shi J, Jiang Z, Ouyang K, Ge T, Fang T, Shi Y, Zhang N, Dong X, Zhang Y, Li H (2023) Pollution characteristics and probabilistic human health risks of thallium and other heavy metals in soils from a typical copper mining city in the Yangtze river Delta, eastern China. Environ Pollut Bioavailability 35(1):2250912. https://doi.org/10.1080/26395940.2023.2250912
Sverdrup HU, Ragnarsdottir KV, Koca D (2014) On modelling the global copper mining rates, market supply, copper price and the end of copper reserves. Resour Conserv Recycl 87:158–174. https://doi.org/10.1016/j.resconrec.2014.03.007
Sytar O, Kumari P, Yadav S, Brestic M, Rastogi A (2019) Phytohormone priming: regulator for heavy metal stress in plants. J Plant Growth Regul 38:739–752. https://doi.org/10.1007/s00344-018-9886-8
Tabasi S, Hassani H, Azadmehr AR (2018) Field study on Re and heavy metal phytoextraction and phytomining potentials by native plant species growing at Sarcheshmeh copper mine tailings. SE Iran. J. Min. Environ. 9(1):183–194. https://doi.org/10.22044/jme.2017.5969.1413
Tepanosyan G, Sahakyan L, Belyaeva O, Asmaryan S, Saghatelyan A (2018) Continuous impact of mining activities on soil heavy metals levels and human health. Sci Total Environ 639:900–909. https://doi.org/10.1016/j.scitotenv.2018.05.211
van der Ent A, Kopittke PM, Schat H (2024) Chaney RL (2024) Hydroponics in physiological studies of trace element tolerance and accumulation in plants focussing on metallophytes and hyperaccumulator plants. Plant Soil. https://doi.org/10.1007/s11104-024-06537-6
Wang J, Zhang C, Jin Z (2009) The distribution and phytoavailability of heavy metal fractions in rhizosphere soils of Paulowniu fortunei (seem) Hems near a Pb/Zn smelter in Guangdong. PR China Geoderma 148(3–4):299–306. https://doi.org/10.1016/j.geoderma.2008.10.015
Wang Z, Liu X, Qin H (2019) Bioconcentration and translocation of heavy metals in the soil-plants system in Machangqing copper mine, Yunnan Province. China J Geochem Explor 200:159–166. https://doi.org/10.1016/j.gexplo.2019.02.005
Wills BA, Napier-Munn T (2006) Wills’ mineral processing technology (Seventh Edition). An introduction to the practical aspects of ore treatment and mineral recovery. Elsevier. Amsterdam
Xie Y, Lu G, Yang C, Qu L, Chen M, Guo C, Dang Z (2018) Mineralogical characteristics of sediments and heavy metal mobilization along a river watershed affected by acid mine drainage. PLoS ONE 13(1):e0190010. https://doi.org/10.1371/journal.pone.0190010
Yang S, Zhao J, Chang SX, Collins C, Xu J, Liu X (2019) Status assessment and probabilistic health risk modeling of metals accumulation in agriculture soils across China: A synthesis. Environ Int 128:165–174. https://doi.org/10.1016/j.envint.2019.04.044
Acknowledgements
The authors are grateful to Dr Robert Ato Newton (Department of Environmental Chemistry and Technology, Faculty of Environment, Jan Evangelista Purkyně University in Ústí nad Labem, Czech Republic), who kindly assisted us for revising and proofreading the manuscript.
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Abdulmannan Rouhani: Conceptualization, Methodology, Investigation, Visualization, Writing—original draft, Writing—review & editing. Michal Hejcman: Conceptualization, Writing—review & editing. Josef Trögl: Conceptualization, Writing—review & editing. All authors reviewed the results and approved the final version of the manuscript.
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Rouhani, A., Hejcman, M. & Trögl, J. A review of soil pollution by potentially toxic elements and remediation strategies in copper mining areas in Iran. Int. J. Environ. Sci. Technol. (2024). https://doi.org/10.1007/s13762-024-05800-8
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DOI: https://doi.org/10.1007/s13762-024-05800-8