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Article

The First Inventory of Sardinian Mining Vascular Flora

Department of Life and Environmental Sciences, Centre for Conservation of Biodiversity (CCB), University of Cagliari, Viale Sant’Ignazio da Laconi 13, 09123 Cagliari, Italy
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Author to whom correspondence should be addressed.
Plants 2025, 14(8), 1225; https://doi.org/10.3390/plants14081225
Submission received: 5 March 2025 / Revised: 4 April 2025 / Accepted: 14 April 2025 / Published: 16 April 2025
(This article belongs to the Section Plant Systematics, Taxonomy, Nomenclature and Classification)

Abstract

Mining activities and associated waste materials pose significant environmental challenges, including soil, water, and air contamination, along with health risks to nearby populations. Despite the harsh conditions of metal-enriched soils and nutrient-poor substrates, certain plants known as metallophytes thrive in these environments. This study examined the vascular flora of Sardinia’s abandoned mining sites, with a focus on identifying metallophytes and their potential role in phytoremediation. A comprehensive floristic checklist was compiled using literature, field surveys, and herbarium samples. Of the 652 taxa identified, 49% were metallophytes, with the majority categorized as facultative species. Notably, 27% of metallophytes were identified as suitable for phytostabilization, while 20% showed potential for phytoextraction. This study also highlighted the presence of endemic and endangered species, emphasizing the need for conservation efforts. The findings suggest that native metallophytes could play a key role in the ecological restoration of mining sites, though careful consideration of invasive species is necessary to avoid ecological disruption. This research provides valuable insights into the biodiversity of Sardinian mining sites and the potential for sustainable remediation strategies using native plants.

1. Introduction

Mining areas and the related mine waste materials represent a significant source of environmental contamination, and at the same time leave landscapes with evident scars (open pits, dumps) and present a health hazard for local inhabitants [1,2]. Mining remains, particularly open dumps, tailing dams, quarries, or accidental release of mine waste are the main sources of metal(loid)s in the surrounding environments, especially those with fine granulometry, like muds and fine sands, which can be easily subjected to aeolian dispersion and water erosion [3]. However, equally important are areas naturally enriched in metal(loid)s, where their concentrations are often well above the threshold limits established by national policy, as has already been observed, for example, at Sardinian mine sites [4,5].
Mine waste also limits the ecological spaces available for plant species and for the establishment of natural vegetation. These consequences are due to the presence of important concentration of metal(loid)s, the absence of topsoil, the poorly developed structure of the substrate, and the lack of nutrients (particularly K, N, and P) and organic matter [5,6,7,8]. These conditions, as well as the frequent instability of the substrate, prevent pedogenesis. In particular, some metals like Zn, Pb, and Cd have toxic effects on plant development. Even though Zn is an essential micronutrient for plants that plays an important role in various metabolic processes [9,10], its toxicity (ca. 100–500 mg/Kg) is manifested by chlorosis of new leaves and depressed plant growth [11]. Lead is a toxic element for plants and living organisms and affects many processes such as photosynthesis, mitosis, and water absorption [12,13]. The most common macroscopic evidence of Pb poisoning in plants are dark green leaves, wilting of older leaves, stunted foliage, and brown, short roots [13]. Cd is highly toxic to living organisms [14]. The main symptoms of Cd toxicity in plants are chlorosis, shunted growth, and plant necrosis [14,15,16]. Cadmium affects plants by inhibiting carbon fixation, decreasing chlorophyll content, inhibiting photosynthetic activity [17], and inducing overproduction of ROS [18].
In the Mediterranean Basin, several studies of plant diversity and their potential use for phytoremediation have been carried out [19,20,21,22,23,24,25]. These studies highlighted that, despite these unfavorable conditions, mine environments host several taxa able to colonize these substrates and reaching high level of vascular plant diversity, including many endemic species [7,19,24,26,27], like Erica andevalensis Cabezudo & J. Rivera, which grows only in the Iberian Pyrite Belt area (Spain and Portugal) [20,21], or Limonium merxmuelleri Erben subsp. merxmuelleri, which is exclusive to the metalliferous ring of South West Sardinia [19,28]. Plants which grow on these substrates, generally called metallophytes, have developed an intrinsic resilience to metal(loid)s stress and the abovementioned conditions [29]. Metallophytes can be obliged, in that they live and thrive only on metal(loid)-enriched substrates (polluted or natural), or facultative, in that they can be found growing in unpolluted or metal(loid)-enriched substrates [5,30]. Metallophytes are just one face of the wide and complex concept of edaphism, the geo-ecological relationship between the prevalence of endemic species and special edaphic conditions, together with gypsophytes, serpentinophytes, quartz-island–phytes, and dolomitophytes [31,32,33,34].
In the Mediterranean Basin, several abandoned mine sites, including their waste materials, have been left to exposed to the weather, often without reclamation, causing several issues in terms of human health and metal(loid)s pollution of the hydrosphere, pedosphere and biosphere [7,8]. Generally, pollution levels are reflected by the floristic composition of the region: on poorly consolidated materials with high concentrations of heavy metals, annual or perennial meadows can be observed, which will be gradually replaced by increasingly more evolved formations such as garrigues and maquis when weather agents wash away the substrate, the heavy metal concentrations decrease, and pedogenetic process begins [7,19]. Mining environments have intrinsic resilience [35] due to the interaction of different aspects: the interaction between the geosphere and biosphere at the interface of surface and groundwater takes place at the hyporheic zone [36] and can lead to the development of natural chemical processes related to the attenuation of metal content. Also, the biosphere contributes, for example, pioneer plants are able to grow in deeply polluted sediments due to their ability to adapt [37,38,39]. Indeed, plants have the ability to remove trace metals from water through different processes like biological uptake, surface adsorption, and the formation of biominerals that can lead to a decrease in the bioavailability of metals [38]. Direct and active intervention to start or accelerate the recovery of degraded environment like mining contexts has been suggested, and several studies emphasize both the benefits of spontaneous succession and the negative aspects of technical reclamation projects, including their high costs [40]. Generally, projects with a high level of human intervention can be inappropriate, because they can compromise the efficient restoration of post-mining environments [41]. On the other hand, unassisted, passive, and assisted revegetation of mining environments can promote adsorption of metals from the substrate and improve their removal and retention through plant uptake [7,42]. A vegetational and multitemporal landscape analysis of land cover transformation in the mine district of Monteponi (SW-Sardinia) from 1955 to 1998 [43], showed that a passive approach led to evolution of the natural vegetation, with also the presence of rare, endemic and endangered species. Indeed, in mine dumps the main transformations are towards maquis, garrigue, and woods.
There are several technologies that are suitable for remediation, using physical, chemical, and biological approaches [44]. Physical-mechanical technologies imply excavation or handling of the substrates and could move the pollution if it is not efficiently disposed of [45]. Chemical-oriented technologies need to use large quantities of reagents (i.e., soil washing) and can be applied in small contexts [46]. Hence, the application of these kinds of technologies is unsuitable in wide polluted areas because they induce modification of the landscape and soil properties and have high implementation costs [47]. When the amounts of polluted materials are widespread and plentiful, biological technologies are a viable solution for remediation. Among a wide range of biotechnologies, phytoremediation and bioremediation are the most supported by the scientific community [3,46]. In detail, phytoremediation is solar-driven and well adaptable to local conditions and can be aided by the implementation of substrate amendments and/or augmentation with microbial strains [46].
Metallophytes may modify rhizosphere conditions, as the availability of metals in the substrate around roots is strongly affected by root exudates [48,49]. In hyperaccumulator species, roots can improve metal bioavailability in the rhizosphere through the secretion of protons, organic acids, phytochelatins (PCs), amino acids, and enzymes. Excluder plants restrict transport of metals to the epigean organs and maintain relatively low metal concentrations in the areal parts over a wide range of soil metal concentrations. This behavior is made possible by the restriction of metals from entering the plant due to the absence of an uptake mechanism, or by the influence of root exudates that reduce the bioavailability of contaminants [6].
Among the different applications of phytoremediation, the most important are phytostabilization and phytoextraction, which use tolerant and accumulator/hyperaccumulator species, respectively [7,50,51]. Phytostabilization is a viable solution when the pollution is widespread and is suitable for protecting substrates from weathering, for creating a long-term plant canopy, and for reducing the visual impact of excavation and mine waste accumulation in dumps [3,7,52]. On the other hand, phytoextraction is mainly devoted to the economic recovery of metal(loid)s and for application in phytomining [53].
Within the framework of remediation of metal(loid)-polluted sites, a deep knowledge of local flora is desirable, as well as a focus on the endemic and alien components. Indeed, nowadays the use of native taxa is recommended for several reasons: these plants (i) are well adapted to local climate and substrate conditions [54]; (ii) favor micro-niche formation; and (iii) improve substrate fertility and permit the establishment of other species in the long term [5,55,56,57]. Despite evidence of the usefulness of numerous alien taxa for phytoremediation (e.g., Arundo donax L.) [58], they may pose a potential risk for local biodiversity, especially invasive taxa.
Sardinia has a long history of mining activities dating back to prehistoric times, which has played a significant role in shaping its landscapes and ecosystems [19,28]. Numerous studies have shown that, in Sardinia, there are numerous metallophytes that have specifically adapted to thrive in environments with high concentrations of heavy metals, such as Pb, Zn, and Cd [7,19,28,55]. Furthermore, the island is recognized as a “Mediterranean biodiversity hotspot” (15% of the native flora is endemic) [28]. So, investigating these plants is crucial for biodiversity conservation, ecological research, and potential application to phytoremediation. While numerous floristic and vegetational studies have been carried out in abandoned mining sites in Sardinia [19,59,60,61], an update and a comprehensive checklist of Sardinian mining vascular flora is needed. Furthermore, in the last 20 years, a multidisciplinary approach have been used to study species like Euphorbia pithyusa L. subsp. cupanii (Guss. ex Bertol.) Radcl.-Sm., Helichrysum microphyllum Cambess. subsp. tyrrhenicum Bacch., Brullo & Giusso, Juncus acutus L., Phragmites australis (Cav.) Trin. ex Steud., Pistacia lentiscus L., Pinus halepensis Mill., and Scrophularia canina L. subsp. bicolor (Sm.) Greuter [5,62,63,64,65]. This approach includes different scientific disciplines such as botany, geochemistry, microbiology, and environmental engineering [7]. Botany can help in floristic and vegetational studies at mining sites by identifying potential tolerant species and applying germination tests under metal(loid)s stress. Geochemistry can provide information about the chemical composition of geochemical spheres and the availability of pollutants and carry out mineralogical investigations of substrates and plant tissues. Microbiology can help in phytoremediation through bioaugmentation and selection of plant growth–promoting bacteria (PGPB). Environmental engineering is fundamental for planning in situ phytoremediation and selecting soil amendments to improve recovery yield. This multidisciplinary approach was also followed in the Iberian Peninsula [9,20,66] and is still under development, with the addition of new tools.

Aims of This Study

In this study, we present the first inventory of the vascular flora found at abandoned mining sites in Sardinia devoted solely to metal(loid)s exploitation. Compiling a checklist of metallophytes is pivotal in order to set up environmental remediation interventions using phytoremediation activities. Indeed, a deep knowledge of mine flora permits selection of the most suitable plant species, favoring native and endemic taxa. The objectives of this study were to: (1) create and present the checklist, summarizing published and unpublished data; (2) provide a list of the metallophytes, classifying them into three categories (obligated, facultative, and occasional) and defining phytostabilizers and phytoextractors for potential remediation activities; and (3) provide information about life forms, chorology, and conservation status, through the development of general and metallophyte-specific biological and chorological spectra.

2. Results

The checklist presented here (Table S1, see Supplementary Materials) is composed of 652 taxa comprising 510 species and 144 subspecies belonging to 93 families and 355 genera. The most prevalent families were Fabaceae (72 taxa; 11%), Asteraceae (64 taxa; 9.8%), and Poaceae (60 taxa; 9.2%). Other prevalent families were Orchidaceae, Apiaceae, Brassicaceae, and Lamiaceae with more than 20 taxa each. As far as the distribution of genera is concerned, Trifolium and Ophrys were the most prevalent, with 12 and 11 taxa, respectively, followed by Euphorbia, Lotus, Galium, and Juncus with 9 taxa and Carex, Echium, Genista, and Lathyrus with 8 taxa.
As far as metallophyte character is concerned, 319 taxa (obligated, O + facultative, F + occasional, OC) out of the total flora (49%) showed this attribute. With regards to the categories of metallophytes identified, facultative metallophytes accounted for 62% (199 taxa), while the least common were obligated metallophytes (7 taxa; 2%; Figure 1). When phytoremediation potential was considered, 87 taxa of metallophytes (27%) are suitable for phytostabilization and 65 for phytoextraction (20%), while 52% of metallophytes have not yet been investigated (Figure 1).
Fabaceae, Poaceae, Brassicaceae, and Asteraceae were the most prevalent facultative metallophytes, although Brassicaceae and Fabaceae also count as obligated metallophytes, as well as Plumbaginaceae, Linaceae, Primulaceae, and Resedaceae. In detail, among the phytostabilizers, we observed that Poaceae and Fabaceae were predominant, whereas Asteraceae, Brassicaceae, Caryophyllaceae, and Polygonaceae were the most abundant among the phytoextractors (Figure 2).
Analysis of the total flora (Figure 3) showed that the most abundant species were therophytes (T; 37%), followed hemicryptophytes (H; 27%), geophytes (G; 13%), phanerophytes (P; 10%), chamaephytes (Ch; 9%), nanophanerophytes (NP; 4%), and hydrophytes (Hy; 1%).
Figure 4 shows the distribution of the different categories of metallophytes: F metallophytes were mainly present in T, H, Ch, and NP; OC metallophytes were well represented in each life form; and O metallophytes were present only among Ch, NP, and H.
Chorological data on the total flora (Figure 3) showed a prevalence of Mediterranean taxa (40%), followed by Euri-Mediterranean taxa (18%) and endemic taxa (13%), and these percentages were similar for the metallophytes alone (Figure 5). F and OC metallophytes were well represented in these three chorological forms, while the only obliged observed were endemics (Figure 5). Among the endemics present in the total flora (Figure 3), we observed 82 taxa in which Sardinian-Corsican (SA-CO) elements were predominant (70%), followed by Sardinian-Corsican-Tuscan Archipelago elements (SA-CO-AT; 8%) and Sardinian elements (SA; 5%). Minor categories (<2%) were observed in the Others category, which accounted for 7% of the total flora. As far as the metallophytes category is concerned, endemics accounted for 14%, and among them, the SA-CO component was predominant (75%), followed by SA-CO-AT (7%) and SA (5%), and with minor percentages (2% each) of the other components (Figure 5).
Analysis of the alien component identified 30 alien taxa (Figure 6; 5% of the total flora): among them were 20 invasive taxa (67%), 8 naturalized (27%), and 2 casual (7%), and the neophytes are predominant towards archaeophytes.
From a conservation point of view, only 15% (98 taxa) of the total flora is included on the Italian Red List: 67% of these taxa are classified as Least concern (LC), followed by Endangered (EN) at 13%, Near threatened (NT) at 11%, Vulnerable (VU; 4%), and Data deficient (DD; 4%, Figure 7).
If only the metallophyte category is considered, the 16% (51 taxa) are included on the Italian Red List. Among the IUCN-listed metallophytes, 73% (37 taxa) are endemics, of which 70% are LC, followed by 19% EN, 5% NT, and 3% VU and DD (Figure 8).
As far as the distribution of metallophytes among the different mine areas of Sardinia is concerned, the most represented was Iglesiente (72% of metallophytes), followed by Guspinese (59%) and Sarrabus (28%; Figure 9).

3. Discussion

Analysis of the distribution among families showed that the most abundant were Fabaceae, Poaceae, and Asteraceae, in agreement with data reported for the Iglesiente Guspinese, Sarrabus-Gerrei, and Quirra mining districts [5,19,59]. Orchidaceae immediately followed the abovementioned families, and their relative abundance was not a surprise. Indeed, there is evidence that, in the Mediterranean bioclimate, calcareous and serpentine substrates are common favorable conditions for orchids in Sardinia in the Iglesiente mine district [67] and Barbagia [68], as well as elsewhere like in the Balkans [69]. As far as the metallophyte character of the investigated flora is concerned, the results showed a high presence (49%) of taxa with this characteristic. Inside this cluster, the high percentage of F (62%) showed that many plant species have a survival/adaptation mechanism to the stressful conditions of mine waste materials like the absence of a topsoil, lack of nutrients and organic matter, and high concentration of metal(loid)s [7].
On the other hand, we found also a not negligible percentage of O metallophytes (2%), which shows the presence of extremely adapted endemic species to these unfavorable conditions with a strictness distribution of few km2, like Linum mulleri Moris, Limonium merxmuelleri Erben subsp. merxmuelleri, Genista insularis Bacch., Brullo & Feoli Chiapella subsp. fodinae Bacch., Brullo & Feoli Chiapella, and Centranthus pontecorvi Bacchetta & Brullo. However, 36% of the assessed metallophytes were OC, showing again that, even if they are not common in these environments, they are resilient to the stressful conditions of mining wastes. In our opinion, the Sardinian mining flora reflects the broad concept of edaphism. Indeed, the observed flora and vegetation followed many of the points noted by Mota et al. [32], such as: (i) the presence of characteristic species, some of them endemic and living only in these types of substrates; and (ii) sharp discontinuities with the surrounding vegetation, identifiable by physiognomic features. Moreover, also the presence of many edapho-physical-chemical factors that determine edaphism [32] were detected, like the lack of nutrients and organic matter, high concentrations of metals, the texture of mine substrate, the instability of the substrates on slopes, the presence of slow and poor biological processes and pedogenesis, and plant–plant interactions (i.e., nursery species). While other edaphism cases are directly linked to specific priority habitats by the EU Habitats Directive, like the Gypsophiletalia order [70], this is not the case for the Sardinian region. Indeed, Fois et al. [61] proposed an improvement to Annex I of Directive 92/43/EEC with the new habitat “Calaminarian vegetation of mining dumps, tailing dams and quarries”. In comparison with other plant communities typical of mining environments, in Europe these species are grouped in the Violetalia calaminariae order [71]. In Western-central and Western Europe, Thlaspion calaminariae alliance is common in heavy-metal soils [72], while in Central Europe Armerion halleri alliance is prevalent [71].
Within this framework, the predominance of Fabaceae, Asteraceae, and Poaceae as phytostabilizers and Asteraceae and Brassicaceae as phytoextractors (Figure 2) is common and has already been observed in different mine districts of Sardinia [59,60,73] and at other sites around the Mediterranean Basin [7]. These families are recognized as being in taxa with high levels of metal tolerance [7,74,75,76], and in many cases of accumulators and hyperaccumulators and being also the most representative families in the Mediterranean floras [77]. It is also important to highlight that the most common families among phytoextractors are often species that are highly palatable to humans (e.g., thistles, chard, and spinach) and farm animals, and this aspect can represent an important health problem.
Without a doubt, metallophytes must be considered primary when phytoremediation activities are planned, and their potential must be known. From our results, it appears that 27% of metallophytes are suitable for phytostabilization (ST) and for long-term rehabilitation of these sites. Indeed, these taxa, which exclude metal(loid)s in their roots or in the rhizosphere, limit the dispersion of contaminants, favoring the recovery of the natural vegetation dynamics and the establishment of a durable plant canopy. Regardless, 20% of the metallophytes were found to be suitable for phytoextraction (EX) and for the recovery of metals. These taxa have a greater potential of accumulation in epigeal organs and can be useful for the recovery of metals, but phytoextraction and phytomining must be carefully considered in terms of their intrinsic weaknesses, like the negative influence on biodiversity due to the extensive use of monotypic plantings, the disposal of harvested hazardous plants, and the risk of phytoextracts entering the food chain [7]. Furthermore, 52% of the metallophytes we identified have still not been investigated (ND), and assessing their phytoremediation potential is of noteworthy importance.
Analysis of the distribution among life forms highlighted a high presence of T and H in these kinds of environments that is linked to habitat degradation, although this value was lower than that in more disturbed environments like urban and overgrazed-trampled environments [51,52]. Moreover, the T and H abundance was in agreement with those observed in a single mine district in Sardinia [59,60,73]. T species are synanthropic species, common to degraded and altered habitats. In our case, T are predominant in mine dumps and mine wastes not already consolidated from a granulometric point of view and with a high concentration of heavy metals [19]. Therophytes create annual meadows that can evolve as the concentration of metals decreases and pedogenesis starts. Moreover, the absence of obligated metallophytes among therophytes indicates that, even if ephemeral species have not specialized to colonize contaminated substrates, they can tolerate the presence of toxic elements which may accumulate in their short life cycle, allowing them to bloom and disperse seeds. Despite the habitat and soil degradation with high concentrations of metal(loid)s in these environments, P and NP species showed percentages similar to those observed by Bacchetta et al. [55] at the Montevecchio mine sites (SW Sardinia) and by Pontecorvo at the Iglesiente mine sites and in more natural contexts [6,78], but higher than those observed by Iiriti [59] for the Sarrabus-Gerrei and Quirra districts. This can be explained by the frequent proximity of mining areas to woodland formations and scrublands of medium-high naturalness, which can spread inside mining sites in a relatively short time. Indeed, several plant coenoses comprising NP and P have been described, like Euphorbio cupanii-Santolinetum insularis Angiolini & Bacchetta 2003 or Dorycnio suffruticosi-Genistetum corsicae Angiolini, Bacchetta, Brullo, Casti, Giusso & Guarino, 2005 [19], which colonized old and well-consolidated mining dumps. Moreover, the high percentage of H can be correlated with the abundance of natural rocky crevices and Mediterranean climatic conditions [68]. Indeed, in incoherent mine dumps with high granulometry, similar ecological conditions of rocky crevices and torrential regime riverbed can occur. G species are typically common in areas outside and surrounding mine areas and have good adaptability to poor substrates; this life form is the third most abundant, confirming its high adaptability to some human disturbances, like overtrampling, vegetation degradation, woodland pastural activity, and fires, which are very common in Sardinia and in mine areas [70,79]. The G value reported here is similar to those observed in other mine districts in Sardinia [59,60,73]. As far as Hy species are concerned, although their percentage was low (1%), their ecological role in these environments is pivotal. The small percentage of hydrophytes, including some generally common ones such as Lemna spp., confirmed their high susceptibility to water contamination, which enables them to serve as useful bio-indicators [80,81]. However, mining environments contain quarry and mining ponds created by excavation activities. In many cases, they are considered a disservice to the ecosystem and a threat to human health and wildlife due to the polluted water. Once abandoned, they can be revegetated naturally by some pollution-resistant hydrophytes and other wetland plants, such as Typha spp. or Phragmites australis (Cav.) Trin. ex Steud., which provides an ecosystem service by purifying water and providing new habitats. If the distribution of metallophytes among life forms is taken into consideration (Figure 4), OC species are widespread among all life forms, suggesting that species with varying functional traits may be adapted to different ecological conditions; F species mainly presented as T, H, and Ch, confirming the typicality of such life forms at mine sites; and O species were distributed in a few categories (Ch, NP and H), showing their high rate of extreme adaptation to restrictive environments [60].
Considering chorological distribution, the Mediterranean and Euri-Mediterranean components were dominant, as has also been observed in other Sardinian mining floras [59,60,73]. Moreover, the Mediterranean character of the area was confirmed by the H/T index = 0.7 (T = 37%; H = 27%), as proposed by Cannucci et al. [82], where typical Mediterranean conditions occur if the H/T ratio is < 1. An important presence in terms of endemic taxa (13%) was found: this value can be explained by the generally high rate of Sardinian endemics (15% of the native flora) [28] and by the presence of very peculiar growing conditions. Some of the endemic taxa can be considered a case study in metal edaphism; in particular, L. mulleri and L. merxmuelleri subsp. merxmuelleri, whose habitats are strictly linked to metal-enriched substrates, behaving as obliged metallophytes. Also, other Mediterranean mining sites exhibit a large number of endemic species with metallophytic or serpentinophytic character, for instance E. andevalensis (Iberian Pyrite Belt, Spain and Portugal), different species of Onosma and Alyssum [23,24], and Odontarrhena stridii L. Cecchi, Španiel & Selvi [24] in Greece. The largest portion of the endemic flora is composed by taxa shared with Corsica (SA-CO), together with those shared with the Tuscan Arcipelago (SA-CO-AT), which are consistent with other Sardinian mining floras [59,60,73] and reflect the geological events that occurred in these areas. Indeed, Sardinia and Corsica are part of the Cyrno-Sardinian microplate that split apart from the current Gulf of Lion (S France) in the Oligocene and were intermittently connected until the Pleistocene glaciations [83,84,85,86]. During the same Plio-Pleistocene eustatic fluctuations, a land bridge connected the Italian Peninsula to Corsica and Sardinia through the Tuscan Archipelago [28]. Other minor components, like endemic taxa shared with Balearic Islands (2.4%), are also mainly explainable by the geological history until the Oligocene, as being part of the same Proto-Hercynian Ligurian massif [84]. Despite being the richest Sardinian endemic form, SA species were less frequent in mines: this is because SAs are generally concentrated in coastal and high mountain environments, where mining activities are uncommon [28]. Moreover, SA species are generally linked to carbonatic substrates, which are less present in mine areas (with few exceptions), whereas SA-CO and SA-CO-AT are more common in silicate substrates, which are typical of mining areas.
Although they represent a minority, alien species accounted for approximately 5% of the flora, primarily invasive species (neophytes and archaeophytes). While this low percentage reflects a high ecological value, it also raises concerns, posing a threat to local biodiversity. Notably, two identified species—Acacia saligna (Labill.) H.L. Wendl. and Ailanthus altissima (Mill.) Swingles—were classified as alien species of European concern under Regulation EU 1143/2014. Despite their metallophyte characteristics, which make them suitable for phytoremediation, their use should be avoided due to their potential negative impacts on local ecosystems and human well-being. Accordingly, it is widely recommended to prioritize the use of native species over non-native or alien species for phytoremediation efforts [46]. Nowadays, no efforts in terms of invasive alien species (IAS) eradication or mitigation in these environments are carried out; however, some methodologies have been proposed and applied in other contexts, for example the eradication of A. saligna from dunes and coastal habitats [87]. These methods can be tailored to mine environments and thus applied in these contexts.
From a conservation perspective, 15% of the total flora has been assessed based on IUCN criteria. Of this group, a moderate proportion has a threat category (EN, VU, NT; 29%), with 13% considered endangered (EN). If endemic taxa categorized as metallophytes are taken into account, 73% (37 taxa) are categorized on the Italian Red List, with 19% considered EN, like Dianthus cyathophorus Moris subsp. cyathophorus, Genista sardoa Vals., Hypericum scruglii Bacch., Brullo & Salmeri, and L. mulleri, and hold particular conservation significance due to their endemic status, conservation importance, and metallophyte characteristics. Nevertheless, L. mulleri is also included as a priority taxon of the Habitat Directive (92/43/ECC). Often, the main threat to these taxa is the fragility of the populations and of their habitat. Moreover, the narrow ecological range and their insulation represent risk factors for their persistence. A further threat is represented by environmental restoration of disused mining landfills using disruptive methods like excavation, which could lead to a decline in the availability and quality of the habitat suitable for the taxa.
The use of native and endemic species is compatible with the ecological, climatic, and soil conditions because they are already adapted to these environments [7]. Furthermore, it is suggested to avoid the use of IAS, as they would threaten local biodiversity.
If the distribution of metallophytes among the different Sardinia’s mine sites is take into consideration, Guspinese-Iglesiente and Sarrabus Gerrei mine sites are more represented than at others; however, it is important to highlight that these districts are more studied than others (i.e., Monte Albo, Barbagia).
From an economic point of view, phytoremediation is more advantageous than conventional techniques (mechanical excavation, etc.): it is sustainable, eco-friendly, and an efficient alternative to conventional methods [88].

4. Materials and Methods

4.1. Study Area

Sardinia is the second largest Mediterranean island (total surface area of 24,090 km2). The Sardinian landscape is heterogenous, with hills, plateaus, plains, and several isolated groups of low mountains or massifs [28]. This heterogeneity is reflected in the substrata: Palaeozoic limestone, metamorphites and batholiths, passing through a sedimentary lithostratigraphic complex of the Mesozoic, Tertiary marine and volcanic depositions, and Quaternary alluvial deposits [28]. There are two macrobioclimates (Mediterranean and temperate subMediterranean), eight thermotypic horizons (from lower thermoMediterranean to upper supratemperate), and seven ombrothermic horizons (from lower dry to lower hyperhumid) [28,89].
Sardinia was historically devoted to mining activities since the Bronze and Early Iron Ages during the Nuragic period [26]. Intensive exploitation started during the industrial period, in the second part of XIX century [7,90]. Mining activities mainly ceased in 1990s, especially because of competition with mines in other countries. However, hundreds of mining waste dumps exist, with millions of tons of polluted materials left to weathering and dispersal, affecting terrestrial and aquatic ecosystems, as well as human health [2,62,91]. Abandoned mine sites are spread all over the island, but the most important sites in terms of time of activity and extension are Sulcis-Iglesiente and Guspinese-Arburese (SW Sardinia), Sarrabus-Gerrei and Quirra (SE Sardinia), Barbagia (Centre Sardinia), Nurra-Anglona (NW Sardinia), and Monte Albo (NE Sardinia), as shown in Figure 10. The most extracted metals were Zn, Pb, Cd, Ag, Fe, and Sb, but some differences in terms of geochemistry characteristics are recognized in each sector. The substrate coming from Sulcis generally derived from orthogneiss during the Ordovician period, while those from Iglesiente derive from carbonate formations from the Palaeozoic period (mainly from the so called “Metalliferous”) and are rich in terms of Zn, Cd, and Pb mineralization [92]. As far as the substrates of Guspinese mine sites are concerned, these derived from a small lens of metamorphic rocks rich in Zn, Pb, and Ag originating from the Arburese batholith [93,94]. Mine wastes in this area undergo oxidation reactions accompanied by the release of metals. As a result, an extremely acidic environment is produced (pH between 2 and 4), with further dissolution of other sulfides [95]. The mineralization at Sarrabus-Gerrei and Quirra derives from stratabound rocks of the Ordovician and Devonian periods and from sulfides (barite, fluorite) [59]. In the Nurra-Anglona sector, mineralization is linked to vulcano-sedimentary oolit iron lenses and hydrothermal Pb-Zn– and Sb-bearing veins [96]. Considering the ore deposit of Barbagia, and in particular for “Funtana Raminosa”, they are generally hosted in hydrothermal rocks, with some skarn [97]. The Monte Albo sector is characterized by Jurassic limestone formations (limestones and dolomites of Monte Albo) and by Hercynian schists and plutonites. In addition to these lithologies, there are various vein manifestations, predominantly quartzose, mineralized with Pb, Ag, Zn, and fluorite [92]. However, the extraction of these metals was accompanied also by other harmful metal(loid)s (e.g., As), causing a health hazard and a serious case of environmental pollution [2,98,99,100]. Moreover, since cessation of exploitation, very few remediation actions have been designed and implemented [7]; hence, huge quantities of polluted materials were left abandoned (c.a. 70 Mm3). In Decree No. 334/1999, the Italian Government declared the mineralized areas of Sardinia as high-risk zones for environmental crises and potential threats to public health. From 2000 to 2024, many floristic and vegetational studies were carried out, highlighting the presence of numerous endemic taxa with phytogeographic interest, like Echium anchusoides Bacch., Brullo & Selvi, Galium schmidii Arrigoni, Helichrysum microphyllum Cambess. subsp. tyrrhenicum Bacch., Brullo & Giusso, Iberis integerrima Moris, Linum mulleri Moris, Ptilostemon casabonae (L.) Greuter, Santolina corsica Jord. & Fourr., Polygala padulae Arrigoni, Reseda luteola L. subsp. dimerocarpa (Müll.Arg.) Abdallah & de Wit, and Lysimachia monelli (L.) U. Manns & Anderb. In addition, the presence of plant assemblages peculiar to these environments, such as Coincyo recurvatae-Helichrysetum microphylli Angiolini, Bacchetta, Brullo, Casti, Giusso & Guarino, Resedo luteolae-Limonietum merxmuelleri Angiolini, Bacchetta, Brullo, Casti, Giusso Del Galdo & Guarino, or “the Sardinian special series of heavy metal–polluted mine substrates” were recognized [19,60]. With the end of mining activity, landfills and tailings basins were colonized by herbaceous communities. Substrates derived from mining activities, even before the onset of pedogenetic processes, were colonized mainly by ephemeral meadows, composed of therophytes on silty-clayey substrates (Aggr. of Centaurium erythraea Rafn and Bellium bellidioides L.) and on gravelly slopes with little coherence with high concentrations of heavy metals (Aggr. of Jasione montana L. and Rumex bucephalophorus L.). Whilst, on incoherent substrates consisting of coarse material, chamaephytic and hemicryptophytic vegetation are typical [43]. These garrigues are particularly interesting from a biogeographical point of view because they are rich in endemic species like P. casabonae, E. cupanii, L. merxmulleri subsp. merxmuelleri, I. integerrima, E. anchusoides, and S. canina subsp. bicolor. For this reason, Angiolini [19] proposed a new Sardinian-Corsican endemic alliance (Ptilostemono casabonae-Euphorbion cupanii Angiolini, Bacchetta, Brullo, Casti, Giusso Del Galdo & Guarino). Moving forward with vegetational evolution, low maquis, present only in landfills abandoned for several years that have been well consolidated, is characterized by a predominance of Genista corsica (Loisel.) DC. (Dorycnio suffruticosi-Genistetum corsica Angiolini, Bacchetta, Brullo, Casti, Giusso & Guarino). Finally, progressive evolution of the soil leads over time to the establishment of species and communities typical of uncontaminated environments [43].

4.2. Data Collection

The floristic checklist presented here was derived from a broad analysis of the literature concerning floristic and vegetational analyses of Sardinian mining areas (only areas devoted to metal(loid)s extraction), unpublished data from different field surveys carried out from 2000 to 2024 within the framework of a different project that our research group was involved in (i.e., germplasm collection, habitat monitoring), and analysis of CAG, SS, and SASSA herbaria exsiccata. It is undeniable that, over the years, some areas (for example Sulcis-Iglesiente) have been studied more than others, and therefore this aspect can lead to overestimation. However, since this is a checklist only, the presence of a certain taxa has been considered, and not the abundance in each place. Plant nomenclature follows Bartolucci et al. [101] and Galasso et al. [102] for native and alien plants, respectively. Family names follow PPG I [103] for pteridophytes, Pignatti et al. [104] for gymnosperms, and APG IV [105] for angiosperms. Life forms were assigned following Raunkiaer’s classification [106], whereas chorology follows the abbreviations proposed by Pignatti et al. [104]. Alien categorizations were made based on the national standardized system [102] basing on the definition of Pyšek et al. [107]. An alien taxon is defined as a plant whose presence can be ascribed to intentional or unintentional anthropogenic activities or to natural spread from the native area. A casual taxon is an alien plant that can bloom and occasionally produce offspring beyond cultivation or for unintended reasons. Regardless, persistence is limited because it is unable to establish self-sustaining populations. Naturalized alien plants generate self-maintaining populations without direct human intervention, whereas invasive plants produce fertile offspring at considerable distances and are able to spread in a large area without control. Alien plants generate self-maintaining populations without direct human intervention, produce fertile offspring at considerable distances from the parent individuals, and are able to spread over a large area. We also distinguished archaeophyte taxa, which are alien plant introduced to Europe before 1492, from neophyte taxa introduced after 1492. In order to assess conservation status, IUCN categories were assigned following the most recent Italian Red List [108].
The detected taxa were categorized into three metallophyte categories: obliged (O), facultative (F), and occasional (OC). This categorization was performed based on distribution along the island and presence on metal(loid)-polluted or naturally enriched substrates. Obliged metallophytes (O) are here defined as taxa present only on substrates polluted in metal(loid)s or on natural metal-enriched sites. Facultative metallophytes (F) are taxa able to grow in both metal-polluted/enriched and unpolluted substrates. Considering that some taxa seem to be uncommon at mining sites due to the extremely high concentration of metals, but are at times present anyway (i.e.,: Pistacia lentiscus L., Quercus ilex L.) and often have shown phytoremediation potential [7], in this study we created a third category of metallophytes in order to categorize this behavior. These taxa were defined as occasional (OC), indicating that they are present at mine sites but are generally uncommon in polluted/metal-enriched substrates. Taxa that did not fall into one of these three categories, even though they are present in mine environments, were rare (casual), so we do not include them in the calculations concerning metallophytes. Our proposed classification of a metallophyte based on the presence/absence of a taxon on polluted/unpolluted substrates is compatible to that proposed by Baker [109], which considered the metal survival strategy. For a better understanding of the terminology used, definitions related to metallophytes and phytoremediation are included in Table A1 (Appendix A).
Categorization of taxa as phytostabilizers or phytoextractors was performed based on the published literature as of 2024 (see Table S1), using biological indices used to estimate accumulation in plant tissue. The most common indices used for the estimation of phytoremediation potential are the Biological Concentration Factor (BCF) [110], the Biological Accumulation Coefficient (BAC) [111], and the Translocation Factor (TF) [110].

5. Conclusions

The checklist of the mining vascular flora in Sardinia shows the presence of abundant biodiversity, despite the restrictive environmental conditions common tomining environments. A large number of endemics with a very limited distribution were recognized, showing a high level of specialization of certain taxa (e.g., L. merxmuelleri subsp. merxmuelleri, L. mulleri, and G. insularis subsp. fodinae), as well as the presence of numerous endangered taxa. The presence of numerous obliged metallophytes demonstrated the presence of very peculiar flora that must be deeply investigated for future phytoremediation. Hence, a deep knowledge of the local flora of mine environments, including metallophytes and their suitability for phytoremediation, can help in the design of more sustainable phytoremediation approaches. Within this framework, when an unstudied taxon is chosen for deeper phytoremediation study, a multidisciplinary approach is desirable, as already shown in numerous studies. Furthermore, some metallophytes and their habitats must be better protected, as demonstrated by the presence of numerous endangered vascular plants. Last but not least, our work represents an initial inventory that can be expanded over time, adding new species and better investigating less explored mine sites in Sardinia.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/plants14081225/s1, Table S1: list of taxa of Sardinia metallophytes. Refs. [112,113,114,115,116,117,118,119,120,121,122,123,124,125,126,127,128,129,130,131,132,133,134,135,136,137,138,139,140,141,142,143,144,145,146,147,148,149,150,151,152,153,154,155,156,157,158,159,160,161,162,163,164,165,166,167,168,169,170,171,172,173,174,175,176,177,178,179,180,181,182,183,184,185,186,187,188,189,190,191,192,193,194,195,196,197,198,199,200,201,202,203,204,205,206,207,208,209] are cited in the Supplementary Materials.

Author Contributions

Conceptualization, M.E.B., M.S., M.F. and G.B.; methodology, M.E.B., M.S. and G.B.; resources, M.C., M.F. and G.B.; data curation, M.E.B. and M.S.; writing—original draft preparation, M.E.B. and M.S.; writing—review and editing, M.E.B., M.S., M.C., M.F. and G.B.; supervision, G.B.; funding acquisition, G.B. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by the National Recovery and Resilience Plan (NRRP), Mission 4 Component 2 Investment 1.5—Call for tender No. 3277 published on 30 December 2021, by the Italian Ministry of University and Research (MUR) funded by the European Union—NextGenerationEU. Project Code: ECS0000038—Project Title: eINS Ecosystem of Innovation for Next Generation Sardinia—CUP: F53C22000430001—Grant Assignment Decree No. 1056 adopted on 23 June 2022, by the Italian Ministry of Ministry of University and Research (MUR).

Data Availability Statement

Data are contained within the article and Supplementary Materials.

Acknowledgments

We also acknowledge the “Comune di Iglesias” within the framework of the “Progetto di conservazione e traslocazione di Limonium merxmuelleri nella Valle del Rio San Giorgio” for the postdoctoal fellowship granted to M.E.B.

Conflicts of Interest

The authors declare no conflicts of interest.

Appendix A

Table A1. Glossary of terminology related to metallophytes and phytoremediation.
Table A1. Glossary of terminology related to metallophytes and phytoremediation.
Definition
Accumulator speciesTaxa where metals are highly translocated and accumulate in epigeal organs. Suitable for phytoextraction.
Excluder speciesTaxa that exclude metal(loid)s in the rhizosphere region and prevent their translocation into epigeal organs. Suitable for phytostabilization.
Facultative metallophyteTaxa able to grow in both metal-polluted/enriched and unpolluted substrates.
MetallophytesPlants growing on metal(loid)-polluted substrates or substrates naturally enriched in metal(loid)s that have developed intrinsic resilience to metal(loid) stress.
Obligate metallophytesTaxa that can live and thrive only on metal(loid)-polluted substrates or substrates naturally enriched in metal(loid)s.
Occasional metallophytesTaxa that are present at mining sites but are generally uncommon in polluted/metal-enriched substrates.
PhytoextractorsTaxa that are suitable for phytoextraction. They are generally metal accumulator and hyperaccumulator species.
PhytoextractionApplication of phytoremediation devoted to the economic recovery of metals from substrates.
PhytoremediationTechnology by which vascular plant species and their associated microbiota, in combination with amendments and different kind of agronomic strategies, are used to remove or limit contamination or make it as harmless as possible.
PhytostabilizationApplication of phytoremediation suitable for stabilizing mine substrates from weathering, for creating a long-term plant canopy, and for reducing the visual impact of excavation and mine waste accumulation in dumps.
PhytostabilizerTaxa that are suitable for phytostabilization. They are generally metal excluder species.

References

  1. Coelho, P.; Costa, S.; Costa, C.; Silva, S.; Walter, A.; Ranville, J.; Pastorinho, M.R.; Harrington, C.; Taylor, A.; Dall’Armi, V.; et al. Biomonitoring of several toxic metal(loid)s in different biological matrices from environmentally and occupationally exposed populations from Panasqueira Mine Area, Portugal. Environ. Geochem. Health 2014, 36, 255–269. [Google Scholar] [CrossRef] [PubMed]
  2. Varrica, D.; Tamburo, E.; Milia, N.; Vallascas, E.; Cortimiglia, V.; De Giudici, G.; Dongarrà, D.; Sanna, E.; Monna, F.; Losno, R. Metals and metalloids in hair samples of children living near the abandoned mine sites of Sulcis-Iglesiente (Sardinia, Italy). Environ. Res. 2014, 134, 366–374. [Google Scholar] [CrossRef]
  3. Mendez, M.O.; Maier, R.M. Phytostabilization of mine tailings in arid and semiarid environments. Rev. Environ. Sci. Biotechnol. 2008, 7, 47–59. [Google Scholar] [CrossRef]
  4. Boni, M.; Costabile, S.; Vivo, B.; Gasparrini, M. Potential environmental hazard in the mining district of southern Iglesiente (SW Sardinia, Italy). J. Geochem. Explor. 1999, 67, 417–430. [Google Scholar] [CrossRef]
  5. Boi, M.E.; Cappai, G.; Giudici, G.; Medas, D.; Piredda, M.; Porceddu, M.; Bacchetta, G. Ex Situ phytoremediation trial of Sardinian mine waste using a pioneer plant species. Environ. Sci. Pollut. Res. 2021, 28, 55736–55753. [Google Scholar] [CrossRef]
  6. Zine, H.; Midhat, L.; Hakkou, R.; El Adnani, M.; Ouhammou, A. Guidelines for a phytomanagement plan by the phytostabilization of mining wastes. Sci. Afr. 2020, 10, e00654. [Google Scholar] [CrossRef]
  7. Boi, M.E.; Fois, M.; Podda, L.; Porceddu, M.; Bacchetta, G. Using Mediterranean native plants for the phytoremediation of mining sites: An overview of the past and present, and perspectives for the future. Plants 2023, 12, 3823. [Google Scholar] [CrossRef]
  8. Doumas, P.; Munoz, M.; Banni, M.; Becerra, S.; Bruneel, O.; Casiot, C.; Cleyet Marel, J.C.; Gardon, J.; Noack, Y.; Sappin-Didier, V. Polymetallic pollution from abandoned mines in Mediterranean regions: A multidisciplinary approach to environmental risks. Reg. Environ. Chang. 2018, 18, 677–692. [Google Scholar] [CrossRef]
  9. Lindsay, W.L. Zinc in soils and plant nutrition. Adv. Agron. 1972, 24, 147–181. [Google Scholar]
  10. Shkolnik, M.J. Microelements in Plant Life; Izd. Nauka: Leningrad, Russia, 1974; p. 323. [Google Scholar]
  11. Macnicol, R.D.; Beckett, P.H.T. Critical tissue concentrations of potentially toxic elements. Plant Soil 1985, 85, 107. [Google Scholar] [CrossRef]
  12. Zulfiqar, U.; Farooq, M.; Hussain, S.; Maqsood, M.; Hussain, M.; Ishfaq, M.; Anjum, M.Z. Lead toxicity in plants: Impacts and remediation. J. Environ. Manag. 2019, 250, 109557. [Google Scholar] [CrossRef] [PubMed]
  13. Kabata-Pendias, A.; Pendias, H. Trace Elements in Soils and Plants; CRC Press: Boca Raton, FL, USA, 2011; p. 534. [Google Scholar]
  14. Chellaiah, E.R. Cadmium (heavy metals) bioremediation by Pseudomonas aeruginosa: A mini review. Appl. Water Sci. 2018, 8, 154. [Google Scholar] [CrossRef]
  15. Jali, P.; Pradhan, C.; Das, A.B. Effects of cadmium toxicity in plants: A review. Acad. J. Biosci. 2016, 4, 1074–1081. [Google Scholar]
  16. Hermans, C.; Chen, J.; Coppens, F.; Inzé, D.; Verbruggen, N. Low magnesium status in plants enhances tolerance to cadmium exposure. New Phytol. 2011, 192, 428–436. [Google Scholar] [CrossRef]
  17. Gallego, S.M.; Pena, L.B.; Barcia, R.A.; Azpilicueta, C.E.; Iannone, M.F.; Rosales, E.P.; Benavides, M.P. Unravelling cadmium toxicity and tolerance in plants: Insight into regulatory mechanisms. Environ. Exp. Bot. 2012, 83, 33–46. [Google Scholar] [CrossRef]
  18. Abbas, T.; Rizwan, M.; Ali, S.; Adrees, A.; Zia-ur-Rehman, M.; Qayyum, M.F.; Ok, Y.S.; Murtaza, G. Effect of biochar on alleviation of cadmium toxicity in wheat (Triticum aestivum L.) grown on Cd-contaminated saline soil. Environ. Sci. Pollut. Res. 2017, 25, 25668–25680. [Google Scholar] [CrossRef]
  19. Angiolini, C.; Bacchetta, G.; Brullo, S.; Casti, M.; Giusso del Galdo, G.; Guarino, R. The vegetation of mining dumps in SW-Sardinia. Feddes Repert. 2005, 116, 243–276. [Google Scholar] [CrossRef]
  20. Abreu, M.M.; Tavares, M.T.; Batista, M.J. Potential Use of Erica andevalensis and Erica australis in Phytoremediation of Sulphide Mine Environments: São Domingos, Portugal. J. Geochem. Explor. 2008, 96, 210–222. [Google Scholar] [CrossRef]
  21. Monaci, F.; Leidi, E.O.; Mingorance, M.D.; Valdés, B.; Rossini Oliva, S.; Bargagli, R. Selective Uptake of Major and Trace Elements in Erica andevalensis, an Endemic Species to Extreme Habitats in the Iberian Pyrite Belt. J. Environ. Sci. 2011, 23, 444–452. [Google Scholar] [CrossRef]
  22. De la Fuente, V.; Rufo, L.; Rodríguez, N.; Amils, R.; Zuluaga, J. Metal Accumulation Screening of the Río Tinto Flora (Huelva, Spain). Biol. Trace Element. Res. 2010, 134, 318–341. [Google Scholar] [CrossRef]
  23. Cecchi, L.; Coppi, A.; Selvi, F. Evolutionary Dynamics of Serpentine Adaptation in Onosma (Boraginaceae) as Revealed by ITS Sequence Data. Plant Syst. Evol. 2011, 297, 185–199. [Google Scholar] [CrossRef]
  24. Cecchi, L.; Španiel, S.; Bianchi, E.; Coppi, A.; Gonnelli, C.; Federico, S. Odontarrhena stridii (Brassicaceae), a new nickel hyperaccumulating species from mainland Greece. Plant Syst. Evol. 2020, 306, 69. [Google Scholar] [CrossRef]
  25. Laplaze, L.; Doumas, P.; Smouni, A.; Brhada, F.; Ater, M. Phytoremédiation du Plomb par Cistus libanotis: Demande de Brevet Prioritaire. Patentscope. 2009. Available online: https://patentscope.wipo.int/search/fr/detail.jsf?docId=WO2010130730 (accessed on 31 March 2025).
  26. Fois, M.; Murgia, L.; Bacchetta, G. Plant diversity and species composition of the abandoned mines of the Iglesiente mining district (Sardinia, Italy): A restoration perspective. Ecol. Eng. 2023, 188, 106879. [Google Scholar] [CrossRef]
  27. Rodríguez, N.; Amils, R.; Jiménez-Ballesta, R.; Rufo, L.; Fuente, V. Heavy Metal Content in Erica andevalensis: An endemic plant from the extreme acidic environment of Tinto River and its soils. Arid. Land. Res. Manag. 2007, 21, 51–65. [Google Scholar] [CrossRef]
  28. Fois, M.; Farris, E.; Calvia, G.; Campus, G.; Fenu, G.; Porceddu, M.; Bacchetta, G. The endemic vascular flora of Sardinia: A dynamic checklist with an overview of biogeography and conservation status. Plants 2022, 11, 601. [Google Scholar] [CrossRef]
  29. Whiting, S.N.; Reeves, R.D.; Richards, D.; Johnson, M.S.; Cooke, J.A.; Malaisse, F.; Paton, A.; Smith, J.A.C.; Angle, J.S.; Chaney, R.L.; et al. Research priorities for conservation of metallophyte biodiversity and their potential for restoration and site remediation. Restor. Ecol. 2004, 12, 106–116. [Google Scholar] [CrossRef]
  30. Pollard, A.J.; Powell, K.D.; Harper, F.A.; Smith, J.A.C. The genetic basis of metal hyperaccumulation in plants. Crit. Rev. Plant Sci. 2002, 21, 539–566. [Google Scholar] [CrossRef]
  31. Ballesteros, M.; Cañadas, E.M.; Foronda, A.; Peñas, J.; Valle, F.; Lorite, J. Central role of bedding materials for gypsum-quarry restoration: An experimental planting of gypsophile species. Ecol. Eng. 2014, 70, 470–476. [Google Scholar] [CrossRef]
  32. Mota, J.F.; Garrido-Becerra, J.A.; Merlo, M.E.; Medina-Cazorla, J.M.; Sánchez-Gómez, P. The Edaphism: Gypsum, Dolomite and Serpentine Flora and Vegetation. In The Vegetation of the Iberian Peninsula, Plant and Vegetation Series; Loidi, J., Ed.; Springer: Berlin/Heidelberg, Germany, 2017; pp. 277–354. [Google Scholar]
  33. Mota, J.; Merlo, E.; Martínez-Hernández, F.; Mendoza-Fernández, A.J.; Pérez-García, F.J.; Salmerón-Sánchez, E. Plants on Rich-Magnesium Dolomite Barrens: A Global Phenomenon. Biology 2021, 10, 38. [Google Scholar] [CrossRef]
  34. Eibes, P.M.; Schaffrath, F.; Oldeland, J.; Thormahlen, W.; Schmiedel, U.; Irl, S.D.H. Testing the concept of edaphism for the quartz island flora of the Knersvlakte, South Africa. S. Afr. J. Bot. 2021, 151, 555–564. [Google Scholar] [CrossRef]
  35. Dore, E.; Fancello, D.; Rigonat, N.; Medas, D.; Cidu, R.; Da Pelo, S.; De Giudici, G. Natural attenuation can lead to environmental resilience in mine environment. Appl. Geochem. 2020, 117, 104597. [Google Scholar] [CrossRef]
  36. Bencala, K.E. Stream-groundwater interactions. In Treatise on Water Science; Elsevier: Newnes, Australia, 2011; pp. 537–546. [Google Scholar]
  37. Medas, D.; De Giudici, G.; Pusceddu, C.; Casu, M.A.; Birarda, G.; Vaccari, L.; Meneghini, C. Impact of Zn excess on biomineralization processes in Juncus acutus grown in mine polluted sites. J. Hazard. Mater. 2019, 370, 98–107. [Google Scholar] [CrossRef] [PubMed]
  38. Caldelas, C.; Weiss, D.J. Zinc homeostasis and isotopic fractionation in plants: A review. Plant Soil 2017, 411, 17–46. [Google Scholar] [CrossRef]
  39. De Giudici, G.; Medas, D.; Meneghini, C.; Casu, M.A.; Gianoncelli, A.A.A.S.P.; Iadecola, A.; Lattanzi, P. Microscopic biomineralization processes and Zn bioavailability: A synchrotron-based investigation of Pistacia lentiscus L. roots. Environ. Sci. Pollut. Res. 2015, 22, 19352–19361. [Google Scholar] [CrossRef]
  40. Poláková, M.; Straka, M.; Polášek, M.; Němejcová, D. 2022. Unexplored freshwater communities in post-mining ponds: Effect of different restoration approaches. Restor. Ecol. 2022, 30, e13679. [Google Scholar] [CrossRef]
  41. Řehounková, K.; Vítovcová, K.; Prach, K. 2020. Threatened vascular plant species in spontaneously revegetated post-mining sites. Restor. Ecol. 2020, 28, 679–686. [Google Scholar] [CrossRef]
  42. Pat-Espadas, A.M.; Loredo Portales, R.; Amabilis-Sosa, L.E.; Gómez, G.; Vidal, G. Review of Constructed Wetlands for Acid Mine Drainage Treatment. Water 2018, 10, 1685. [Google Scholar] [CrossRef]
  43. Zavattero, L.; Casti, M.; Bacchetta, G.; Di Pietro, R. Analisi multitemporale del paesaggio del distretto minerario di Monteponi (Sardegna sud-occidentale). Ital. J. Remote Sens. 2006, 37, 137–146. [Google Scholar]
  44. Khalid, S.; Shahid, M.; Niazi, N.K.; Murtaza, B.; Bibi, I.; Dumat, C. A comparison of technologies for remediation of heavy metal contaminated soils. J. Geochem. Explor. 2017, 182, 247–268. [Google Scholar] [CrossRef]
  45. Dybowska, A.; Farago, M.; Valsami-Jones, E.; Thornton, I. Remediation strategies for historical mining and smelting sites. Sci. Prog. 2006, 89, 71–138. [Google Scholar] [CrossRef]
  46. Bacchetta, G.; Cappai, G.; Carucci, A.; Tamburini, E. Use of native plants for the remediation of abandoned mine sites in Mediterranean semiarid environments. Bull. Environ. Contam. Toxicol. 2015, 94, 326–333. [Google Scholar] [CrossRef] [PubMed]
  47. Mulligan, C.N.; Yong, R.N.; Gibbs, B.F. Remediation technologies for metal-contaminated soils and groundwater: An evaluation. Eng. Geol. 2001, 60, 193–207. [Google Scholar] [CrossRef]
  48. Podar, D.; Maathuis, F.J. The role of roots and rhizosphere in providing tolerance to toxic metals and metalloids. Plant Cell Environ. 2022, 45, 719–736. [Google Scholar] [CrossRef]
  49. Tamburini, E.; Mandaresu, M.; Lussu, R.; Sergi, S.; Vitali, F.; Carucci, A.; Cappai, G. Metal phytostabilization by mastic shrub (Pistacia lentiscus L.) and its root-associated bacteria in different habitats of Sardinian abandoned mining areas (Italy). Environ. Sci. Pollut. Res. 2023, 30, 122107–122120. [Google Scholar] [CrossRef]
  50. Baker, A.J.M.; Reeves, R.D.; Haiar, A.S.M. Heavy metal accumulation and tolerance in British populations of the metallophyte Thlaspi caerulescens J. & C. Presl. (Brassicaceae). New Phytol. 1994, 127, 61–68. [Google Scholar]
  51. Wong, M.H. Ecological restoration of mine degraded soils, with emphasis on metal contaminated soils. Chemosphere 2003, 50, 775–780. [Google Scholar] [CrossRef] [PubMed]
  52. Álvarez-Rogel, J.; Peñalver-Alcalá, A.; Nazaret González-Alcaraz, M. Spontaneous vegetation colonizing abandoned metal(loid) mine tailings consistently modulates climatic, chemical and biological soil conditions throughout seasons. Sci. Total Environ. 2022, 838, 155945. [Google Scholar] [CrossRef]
  53. Mang, K.C.; Ntushelo, K. Phytoextraction and phytostabilisation approaches of heavy metal remediation in acid mine drainage with case studies: A review. Appl. Ecol. Environ. Res. 2019, 17, 6129–6149. [Google Scholar] [CrossRef]
  54. Solomou, A.D.; Germani, R.; Proutsos, N.; Petropoulou, M.; Koutroumpilas, P.; Galanis, C.; Maroulis, G.; Kolimenakis, A. Utilizing Mediterranean plants to remove contaminants from the soil environment: A short review. Agriculture 2022, 12, 238. [Google Scholar] [CrossRef]
  55. Bacchetta, G.; Casti, M.; Zavattero, L. Integration of vegetational and multitemporal analysis: A case study in the abandoned mine district of Montevecchio (South-western Sardinia). Ann. Botanic. 2007, 7, 163–174. [Google Scholar]
  56. Navarro-Cano, J.A.; Verdú, M.; Goberna, M. Trait-based selection of nurse plants to restore ecosystem functions in mine tailings. J. Appl. Ecol. 2018, 55, 1041–1565. [Google Scholar] [CrossRef]
  57. Vacca, A.; Aru, F.; Ollesch, G. Short-term impact of coppice management on soil in a Quercus ilex L. Stand of Sardinia. Land. Degrad. Dev. 2017, 28, 553–565. [Google Scholar] [CrossRef]
  58. Cristaldi, A.; Oliveri Conti, G.; Cosentino, S.L.; Mauromicale, G.; Copat, C.; Grasso, A.; Zuccarello Fiore, P.M.; Restuccia, C.; Ferrante, M. Phytoremediation potential of Arundo donax (Giant Reed) in contaminated soil by heavy metals. Environ. Res. 2020, 185, 109427. [Google Scholar] [CrossRef]
  59. Iiriti, G. Flora e Paesaggio Vegetale del Sarrabus Gerrei (Sardegna Sud Orientale). Ph.D. Thesis, Università degli Studi di Cagliari, Cagliari, Italy, 2006. [Google Scholar]
  60. Bacchetta, G.; Casti, M.; Mossa, L.; Piras, M.L. La flora del distretto minerario di Montevecchio (Sardegna sud-occidentale). Webbia 2007, 62, 27–52. [Google Scholar] [CrossRef]
  61. Fois, M.; Bacchetta, G.; Caria, M.C.; Cogoni, D.; Farris, E.; Fenu, G.; Manca, M.; Pinna, M.S.; Pisanu, S.; Rivieccio, G.; et al. Proposals for improvement of annex I of Directive 92/43/EEC: Sardinia. Plant Sociol. 2021, 58, 65–76. [Google Scholar] [CrossRef]
  62. Bacchetta, G.; Cao, A.; Cappai, G.; Carucci, A.; Casti, M.; Fercia, M.L.; Lonis, R.; Mola, F. A field experiment on the use of Pistacia lentiscus L. and Scrophularia canina L. subsp. bicolor (Sibth. et Sm.) Greuter for the phytoremediation of abandoned mining areas. Plant Biosyst. 2012, 146, 1054–1063. [Google Scholar]
  63. Boi, M.E.; Angotzi, M.S.; Porceddu, M.; Musu, E.; Mameli, V.; Bacchetta, G.; Cannas, C. Germination and early seedling development of Helichrysum microphyllum Cambess. subsp. tyrrhenicum Bacch., Brullo & Giusso in the presence of arsenates and arsenites. Heliyon 2022, 8, e10693. [Google Scholar]
  64. Caldelas, C.; Dong, S.; Araus, J.L.; Jakob Weiss, D. Zinc isotopic fractionation in Phragmites australis in response to toxic levels of zinc. J. Exp. Bot. 2011, 62, 2169–2178. [Google Scholar] [CrossRef]
  65. Medas, D.; De Giudici, G.; Casu, M.A.; Musu, E.; Gianoncelli, A.; Iadecola, A.; Lattanzi, P. Microscopic processes ruling the bioavailability of Zn to roots of Euphorbia pithyusa L. pioneer plant. Environ. Sci. Technol. 2015, 49, 1400–1408. [Google Scholar] [CrossRef]
  66. Mirete, S.; de Figueras, C.G.; González-Pastor, J.E. Novel Nickel Resistance Genes from the Rhizosphere Metagenome of Plants Adapted to Acid Mine Drainage. Appl. Environ. Microbiol. 2007, 73, 6001–6011. [Google Scholar] [CrossRef]
  67. De Agostini, A.; Caltagirone, C.; Caredda, A.; Cicatelli, A.; Cogoni, A.; Farci, D.; Cortis, P. Heavy metal tolerance of orchid populations growing on abandoned mine tailings: A case study in Sardinia Island (Italy). Ecotoxicol. Environ. Saf. 2020, 189, 110018. [Google Scholar] [CrossRef]
  68. Cuena-Lombraña, A.; Fois, M.; Calvia, G.; Bacchetta, G. An updated checklist of the vascular flora of Montarbu massif (CE Sardinia, Italy). Flora Medit. 2023, 33, 251–268. [Google Scholar]
  69. Djordjević, V.; Tsiftsis, S.; Lakušić, D.; Jovanović, S.; Jakovljević, K.; Stevanović, V. Patterns of distribution, abundance and composition of forest terrestrial orchids. Biodivers. Conserv. 2020, 29, 4111–4134. [Google Scholar] [CrossRef]
  70. Directive, H. Council Directive 92/43/EEC of 21 May 1992 on the conservation of natural habitats and of wild fauna and flora. Off. J. Eur. Union 1992, 206, 50. [Google Scholar]
  71. Baker, A.J.; Ernst, W.H.; van der Ent, A.; Malaisse, F.; Ginocchio, R. Metallophytes: The unique biological resource, its ecology and conservational status in Europe, central Africa and Latin America. Ecol. Ind. Poll. 2010, 18, 7–40. [Google Scholar]
  72. Brown, G. The heavy-metal vegetation of north-western mainland Europe. Bot. Jahrb. Fur Syst. 2001, 123, 63–110. [Google Scholar]
  73. Pontecorvo, C. La Flora dell’Iglesiente (Sardegna SW). Ph.D. Thesis, Università degli Studi di Cagliari, Cagliari, Italy, 2006. [Google Scholar]
  74. El Aafi, N.; Saidi, N.; Maltouf, A.F.; Perez-Palacios, P.; Dary, M.; Brhada, F.; Pajuelo, E. Prospecting Metal-Tolerant Rhizobia for Phytoremediation of Mining Soils from Morocco Using Anthyllis vulneraria L. Environ. Sci. Pollut. Res. 2015, 22, 4500–4512. [Google Scholar] [CrossRef]
  75. Cecchi, L.; Bettarini, I.; Colzi, I.; Coppi, A.; Echevarria, G.; Pazzagli, L.; Bani, A.; Gonnelli, C.; Selvi, F. The Genus Odontarrhena (Brassicaceae) in Albania: Taxonomy and Nickel Accumulation in a Critical Group of Metallophytes from a Major Serpentine Hot-Spot. Phytotaxa 2018, 35, 1–28. [Google Scholar] [CrossRef]
  76. Mengoni, A.; Cecchi, L.; Gonnelli, C. Nickel Hyperaccumulating Plants and Alyssum bertolonii: Model Systems for Studying Biogeochemical Interactions in Serpentine Soils. In Bio-Geo Interactions in Metal-Contaminated Soils; Springer: Berlin/Heidelberg, Germany, 2011; pp. 279–296. [Google Scholar]
  77. Thompson, J.D. Plant Evolution in the Mediterranean: Insights for Conservation; Oxford University Press: Cary, NC, USA, 2020. [Google Scholar]
  78. Calvia, G.; Ruggero, A. The vascular flora of Mount Limbara (northern Sardinia): From a troubled past towards an uncertain future. Flora Medit. 2020, 30, 293–313. [Google Scholar]
  79. Kirk, D.A.; Goldsmith, F.B. Grazing pressure versus environmental covariates: Effects on woody and herbaceous plant biodiversity on a limestone mountain in northern Tunisia. PeerJ 2018, 7, e7296. [Google Scholar] [CrossRef]
  80. Mherzi, N.; Lamchouri, F.; Khabbach, A.; Boulfia, M.; Zalaghi, A.; Toufik, H. Ecological types and bioindicator macrophyte species of pollution of riparian vegetation of Oued Lârbaa in Taza City of Morocco. Environ. Monit. Assess. 2020, 192, 256. [Google Scholar] [CrossRef]
  81. Cuena-Lombraña, A.; Fois, M.; Cogoni, A.; Bacchetta, G. Where we come from and where to go: Six decades of botanical studies in the Mediterranean wetlands, with Sardinia (Italy) as a case study. Wetlands 2021, 41, 69. [Google Scholar] [CrossRef]
  82. Cannucci, S.; Angiolini, C.; Anselmi, B.; Banfi, E.; Biagioli, M.; Castagnini, P.; Centi, C.; Fiaschi, T.; Foggi, B.; Gabellini, A.; et al. Contribution to the knowledge of the vascular flora of Miniera di Murlo area (southern Tuscany, Italy). Ital. Bot. 2017, 7, 51–67. [Google Scholar] [CrossRef]
  83. Cherchi, A.; Montadert, L. Oligo-Miocene rift of Sardinia and the early history of the western Mediterranean basin. Nature 1982, 298, 736–739. [Google Scholar] [CrossRef]
  84. Mansion, G.; Rosenbaum, G.; Schoenenberger, N.; Bacchetta, G.; Rosselló, J.A.; Conti, E. Phylogenetic analysis informed by geological history supports multiple, sequential invasions of the Mediterranean Basin by the angiosperm family Araceae. Syst. Biol. 2008, 57, 269–285. [Google Scholar] [CrossRef]
  85. Médail, F. The specific vulnerability of plant biodiversity and vegetation on Mediterranean islands in the face of global change. Reg. Environ. Change 2017, 17, 1775–1790. [Google Scholar] [CrossRef]
  86. Caković, D.; Frajman, B. An integrative approach supports the taxonomic distinction of the Sardo-Corsican endemic Euphorbia semiperfoliata from the widespread E. amygdaloides (Euphorbiaceae). Plant Biosyst. 2023, 157, 958–969. [Google Scholar] [CrossRef]
  87. Acunto, S.; Bacchetta, G.; Bordigoni, A.; Cadoni, N.; Cinti, M.F.; Duràn Navarro, M.; Sanna, A. The LIFE+ project “RES MARIS-Recovering Endangered habitatS in the Capo Carbonara MARIne area, Sardinia”: First results. Plant Soc. 2017, 54, 85–95. [Google Scholar]
  88. Burges, A.; Alkorta, I.; Epelde, L.; Garbisu, C. From phytoremediation of soil contaminants to phytomanagement of ecosystem services in metal contaminated sites. Int. J. Phytoremediation 2018, 20, 384–397. [Google Scholar] [CrossRef]
  89. Canu, S.; Rosati, L.; Fiori, M.; Motroni, A.; Filigheddu, R.; Farris, E. Bioclimate map of Sardinia (Italy). J. Maps 2015, 11, 711–718. [Google Scholar] [CrossRef]
  90. Cidu, R.; Biagini, C.; Fanfani, L.; La Ruffa, G.; Marras, I. Mine closure at Monteponi (Italy): Effect of the cessation of dewatering on the quality of shallow groundwater. Appl. Geochem. 2001, 16, 489–502. [Google Scholar] [CrossRef]
  91. Cidu, R.; Biddau, R. Transport of trace elements under different seasonal conditions: Effects on the quality of river water in a Mediterranean area. Appl. Geochem. 2007, 22, 2777–2794. [Google Scholar] [CrossRef]
  92. Carmignani, L.; Oggiano, G.; Barca, S.; Conti, P.; Salvadori, I.; Eltrudis, A.; Pasci, S. Geologia della Sardegna: Note Illustrative della Carta Geologica della Sardegna in scala 1: 200.000. Mem. Descr. Carta Geol. D’it. 2001, 60, 1–283. [Google Scholar]
  93. Barbafieri, M.; Dadea, C.; Tassi, E.; Bretzel, F.; Fanfani, L. Uptake of heavy metals by native species growing in a mining area in Sardinia, Italy: Discovering native flora for phytoremediation. Int. J. Phytoremediation 2011, 13, 985–997. [Google Scholar] [CrossRef]
  94. Da Pelo, S. L’area mineraria dismessa di Montevecchio: Il Bacino di Levante. Interazione Acqua-Roccia: Aspetti Mineralogici, Petrologici, Geochimici e Ambientali. In Gruppo Nazionale di Mineralogia; Note All’escursione: Montevecchio e Furtei; Scuola di Mineralogia Torre dei Corsari: Cagliari, Italy, 1999. [Google Scholar]
  95. Fanfani, L.; Caboi, R.; Cidu, R.; Cristini, A.; Frau, F.; Lattanzi, P.; Zuddas, P. Impatto ambientale dell’attività mineraria in Sardegna: Studi mineralogici e geochimica. Rend. Sem. Fac. Sc. Univ. Cagliari 2000, 70, 249–264. [Google Scholar]
  96. Marcello, A.; Pretti, S.; Valera, P. Metallogeny in Sardinia (Italy): From the Cambrian to the Tertiary. In Proceedings of the 32nd International Geological Congress, Florence, Italy, 20–28 August 2004. [Google Scholar]
  97. Cidu, R.; Mereu, L. The Abandoned Copper-Mine of Funtana Raminosa (Sardinia): Preliminary Evaluation of Its Impact on the Aquatic System. In Water in Mining Environments; Cidu, R., Frau, F., Eds.; IMWA Symposium: Cagliari, Italy, 2007. [Google Scholar]
  98. Biggeri, A.; Lagazio, C.; Catelan, D.; Pirastu, R.; Casson, F.; Terracini, B. Report on health status of residents in areas with industrial, mining or military sites in Sardinia, Italy. Epidemiol. Prev. 2006, 30, 5–95. [Google Scholar]
  99. Frau, F.; Ardau, C.; Fanfani, L. Environmental geochemistry and mineralogy of lead at the old mine area of Baccu Locci (South-East Sardinia, Italy). J. Geochem. Explor. 2008, 100, 105–115. [Google Scholar] [CrossRef]
  100. Sanna, E.; Floris, G.; Vallascas, E. Town and gender effects on hair lead levels in children from three sardinian towns (Italy) with different environmental backgrounds. Biol. Trace Elem. Res. 2008, 124, 52–59. [Google Scholar] [CrossRef]
  101. Bartolucci, F.; Peruzzi, L.; Galasso, G.; Alessandrini, A.; Ardenghi, N.M.G.; Bacchetta, G.; Banfi, E.; Barberis, G.; Bernardo, L.; Bouvet, D.; et al. A second update to the checklist of the vascular flora native to Italy. Plant Biosyst. 2024, 158, 219–296. [Google Scholar] [CrossRef]
  102. Galasso, G.; Conti, F.; Peruzzi, L.; Alessandrini, A.; Ardenghi, N.M.G.; Bacchetta, G.; Banfi, E.; Barberis, G.; Bernardo, L.; Bouvet, D.; et al. A second update to the checklist of the vascular flora alien to Italy. Plant Biosyst. 2024, 158, 297–340. [Google Scholar] [CrossRef]
  103. PPG, I. A community-derived classification for extant lycophytes and ferns. J. Syst. Evol. 2016, 54, 563–603. [Google Scholar] [CrossRef]
  104. Pignatti, S.; Guarino, R.; La Rosa, M. Flora d’Italia, 2nd ed.; Edagricole Calderini: Bologna, Italy, 2017. [Google Scholar]
  105. APG IV. An update of the Angiosperm Phylogeny Group classification for the orders and families of flowering plants: APG IV. Bot. J. Linn. Soc. 2016, 181, 1–20. [Google Scholar]
  106. Raunkiaer, C. The Life Forms of Plants and Statistical Plant Geography; Clarendon Press: Oxford, UK, 1934. [Google Scholar]
  107. Pyšek, P.; Richardson, D.M.; Rejmánek, M.; Webster, G.L.; Williamson, M.; Kirschner, J. Alien plants in checklists and floras: Towards better communication between taxonomists and ecologists. Taxon 2004, 53, 131–143. [Google Scholar] [CrossRef]
  108. Orsenigo, S.; Fenu, G.; Gargano, D.; Montagnani, C.; Abeli, T.; Alessandrini, A.; Bacchetta, G.; Bartolucci, F.; Carta, A.; Castello, M.; et al. Red list of threatened vascular plants in Italy. Plant Biosyst. 2021, 155, 310–335. [Google Scholar] [CrossRef]
  109. Baker, A.J.M. Accumulators and Excluders Strategies in Response of Plants to Heavy Metals. J. Plant Nutr. 1981, 3, 643–654. [Google Scholar] [CrossRef]
  110. Yoon, J.; Cao, X.; Zhou, Q.; Ma, L.Q. Accumulation of Pb, Cu, and Zn in native plants growing on a contaminated Floridasite. Sci. Total Environ. 2006, 368, 456–464. [Google Scholar] [CrossRef]
  111. Brooks, R.R. Plants that Hyperaccumulate Heavy Metals: Their Role in Phytoremediation, Microbiology, Archaeology, Mineral Exploration and Phyto-Mining; CAB International: Oxford, UK, 1998. [Google Scholar]
  112. Bacchetta, G.; Casti, M.; Zavattero, L. Analisi della vegetazione del distretto minerario di Montevecchio (Sardegna sud-occidentale). Fitosociologia 2007, 44, 83–108. [Google Scholar]
  113. Angius, R.; Bacchetta, G.; Pontecorvo, C. Floristic and vegetational features of Monte Marganai (SW Sardinia). In Biodiversity of Marganai and Montimannu (Sardinia). Research in the Framework of the ICP Forests Network; Nardi, G., Whitmore, D., Bardiani, M., Birtele, D., Mason, F., Spada, L., Cerretti, P., Eds.; Centro Nazionale per lo Studio e la Conservazione: Veron, Italy, 2011; Volume 1, pp. 57–132. [Google Scholar]
  114. Zavattero, L.; Casti, M.; Di Pietro, R.; Rosati, L.; Bacchetta, G. Analisi vegetazionale e geo-topologica dell’area mineraria di Monteponi (Iglesiente, Sardegna sud-occidentale). Inf. Bot. Ital. 2005, 37, 296–297. [Google Scholar]
  115. Bacchetta, G.; Brullo, S.; Cusma Velari, T.; Feoli Campiella, L.; Kosovel, V. Taxonomic Notes on the Genista ephedroides Group (Fabaceae) from the Mediterranean Area. Novon 2011, 21, 4–19. [Google Scholar] [CrossRef]
  116. Fois, M.; Cuena-Lombraña, A.; Boi, M.E.; McInnes, R.J.; Bacchetta, G. Changes to biodiversity and ecosystem services over time in post-mining and quarry ponds. Hydrobiologia, submitted.
  117. Bacchetta, G.; Cambria, S.; De Castro, O.; Fenu, G.; Brullo, S. Centranthus pontecorvi (Valerianaceae) a new species from Sardinia. Phytotaxa 2024, 661, 253–266. [Google Scholar] [CrossRef]
  118. Nirola, R.; Megharaj, M.; Aryal, R.; Naidu, R. Screening of metal uptake by plant colonizers growing on abandoned copper mine in Kapunda, South Australia. Int. J. Phytoremediation 2016, 18, 399–405. [Google Scholar] [CrossRef]
  119. Sinam, G.; Behera, S.K.; Mishra, R.K.; Sinha, S.; Mallick, S.; Khare, P.B. Comparison of two ferns (Adiantum capillus-veneris Linn. and Microsorium punctatum (Linn.) Copel) for their Cr accumulation potential and antioxidant responses. Int. J. Phytoremediation 2012, 14, 629–642. [Google Scholar] [CrossRef]
  120. Ramana, S.; Tripathi, A.K.; Kumar, A.; Dey, P.; Saha, J.K.; Patra, A.K. Phytoremediation of Soils Contaminated with Cadmium by Agave americana. J. Nat. Fibers 2021, 19, 4984–4992. [Google Scholar] [CrossRef]
  121. Pérez-de-Mora, A.; Madejón, E.; Burgos, P.; Cabrera, F. Trace element availability and plant growth in a mine-spill contaminated soil under assisted natural remediation. Sci. Total Environ. 2006, 363, 28–37. [Google Scholar] [CrossRef]
  122. Mohebzadeh, F.; Motesharezadeh, B.; Jafari, M.; Zare, S.; Aman, M.S. Remediation of heavy metal polluted soil by utilizing organic amendments and two plant species (Ailanthus altissima and Melia azedarach). Arab. J. Geosci. 2021, 14, 1211. [Google Scholar] [CrossRef]
  123. Widmer, J.; Norgrove, L. Identifying candidates for the phytoremediation of copper in viticultural soils: A systematic review. Environ. Res. 2023, 216, 114518. [Google Scholar] [CrossRef] [PubMed]
  124. Chaabani, S.; Abdelmalek-Babbou, C.; Ben Ahmed, H.; Chaabani, A.; Sebei, A. Phytoremediation Assessment of Native Plants Growing on Pb-Zn Mine Site in Northern Tunisia. Environ. Earth Sci. 2017, 76, 585–600. [Google Scholar] [CrossRef]
  125. Nahvi, H.; Torabian, S.; Hashemi, S.; Payam, H. Alnus glutinosa (Alder) sapling as a phytoremediator for cadmium in contaminated soil of industrial Park. Results Eng. 2024, 22, 102317. [Google Scholar] [CrossRef]
  126. Sipos, B.; Bibi, D.; Magura, T.; Tóthmérész, B.; Simon, E. High phytoremediation and translocation potential of an invasive weed species (Amaranthus retroflexus) in Europe in metal-contaminated areas. Environ. Monit. Assess. 2023, 195, 790. [Google Scholar] [CrossRef]
  127. Braglia, R.; Rugnini, L.; Malizia, S.; Scuderi, F.; Redi, E.L.; Canini, A.; Bruno, L. Exploiting the Potential in Water Cleanup from Metals and Nutrients of Desmodesmus sp. and Ampelodesmos mauritanicus. Plants 2021, 10, 1461. [Google Scholar] [CrossRef]
  128. Pratas, J.; Favas, P.J.; D’Souza, R.; Varun, M.; Paul, M.S. Phytoremedial assessment of flora tolerant to heavy metals in the contaminated soils of an abandoned Pb mine in Central Portugal. Chemosphere 2013, 90, 2216–2225. [Google Scholar] [CrossRef] [PubMed]
  129. Punetha, D.; Tewari, G.; Pande, C.; Kharkwal, G.C.; Tewari, K. Investigation on heavy metal content in common grown vegetables from polluted sites of Moradabad district, India. Indian Chem. Soc. 2015, 92, 97–103. [Google Scholar]
  130. Arsenov, D.; Župunski, M.; Pajević, S.; Borišev, M.; Nikolić, N.; Mimica-Dukić, N. Health assessment of medicinal herbs, celery and parsley related to cadmium soil pollution-potentially toxic elements (PTEs) accumulation, tolerance capacity and antioxidative response. Environ. Geochem. Health 2021, 43, 2927–2943. [Google Scholar] [CrossRef]
  131. Ning, W.; Yang, Y.; Chen, W.; Li, R.; Cao, M.; Luo, J. Effect of light combination on the characteristics of dissolved organic matter and chemical forms of Cd in the rhizosphere of Arabidopsis thaliana involved in phytoremediation. Ecotoxicol. Environ. Saf. 2022, 231, 113212. [Google Scholar] [CrossRef] [PubMed]
  132. Solis-Hernández, A.P.; Chávez-Vergar, B.M.; Aída, V.; Rodríguez-Tovar, A.V.; Beltrán-Paz, O.I.; Santillán, J.; Rivera-Becerril, F. Effect of the natural establishment of two plant species on microbial activity, on the composition of the fungal community, and on the mitigation of potentially toxic elements in an abandoned mine tailing. Sci. Total Environ. 2022, 802, 149788. [Google Scholar] [CrossRef]
  133. Vicente, C.S.; Pérez-Fernández, M.A. Broad environmental tolerance of native root-nodule bacteria of Biserrula pelecinus indicate potential for soil fertility restoration. Plant Ecol. Divers. 2016, 9, 299–307. [Google Scholar] [CrossRef]
  134. Lombini, A.; Poschenrieder, C.; Llugany, M.; Dinelli, E.; Barceló, J. Copper resistance in Silene armeria ecotypes: Does co-tolerance play a role? In Plant Nutrition; Springer: Dordrecht, The Netherland, 2001; pp. 456–457. [Google Scholar]
  135. Papazoglou, E.G.; Fernando, A.L. Preliminary studies on the growth, tolerance and phytoremediation ability of sugarbeet (Beta vulgaris L.) grown on heavy metal contaminated soil. Ind. Crop Prod. 2017, 107, 463–471. [Google Scholar] [CrossRef]
  136. Pistelli, L.; D’Angiolillo, F.; Morelli, E.; Basso, B.; Rosellini, I.; Posarelli, M.; Barbafieri, M. Response of Spontaneous Plants from an Ex-Mining Site of Elba Island (Tuscany, Italy) to Metal(loid) Contamination. Environ. Sci. Pollut. Res. 2017, 24, 7809–7820. [Google Scholar] [CrossRef]
  137. Evangelou, M.W.; Kutschinski-Klöss, S.; Ebel, M.; Schaeffer, A. Potential of Borago officinalis, Sinapis alba L. and Phacelia boratus for phytoextraction of Cd and Pb from soil. Water Air Soil Pollut. 2007, 182, 407–416. [Google Scholar] [CrossRef]
  138. Sajad, M.A.; Khan, M.S.; Ali, H. Lead phytoremediation potential of sixty-one plant species: An open field survey. Pure Appl. Biol. 2019, 8, 405–419. [Google Scholar] [CrossRef]
  139. Lin, L.; Shi, J.; Liu, Q.; Liao, M.A.; Mei, L. Cadmium accumulation characteristics of the winter farmland weeds Cardamine hirsuta Linn. and Gnaphalium affine D. Don. Environ. Monit. Assess. 2014, 186, 4051–4056. [Google Scholar] [CrossRef] [PubMed]
  140. Gutiérrez-Ginés, M.J.; Pastor, J.; Hernández, A.J. Heavy metals in native mediterranean grassland species growing at abandoned mine sites: Ecotoxicological assessment and phytoremediation of polluted soils. In Heavy Metal Contamination of Soils. Soil Biology; Springer: Cham, Switzerland, 2015; pp. 159–178. [Google Scholar]
  141. Fernández, S.; Poschenrieder, C.; Marcenò, C.; Gallego, J.R.; Jiménez-Gámez, D.; Bueno, A.; Afif, E. Phytoremediation capability of native plant species living on Pb-Zn and Hg-As mining wastes in the Cantabrian range, north of Spain. Geochem. Explor. 2017, 174, 10–20. [Google Scholar] [CrossRef]
  142. Ebrahimi, M. Enhanced phytoremediation capacity of Chenopodium album L. grown on Pb-contaminated soils using EDTA and reduction of leaching risk. Soil Sediment. Contam. 2016, 25, 652–667. [Google Scholar] [CrossRef]
  143. Wu, S.; Yang, Y.; Qin, Y.; Deng, X.; Zhang, Q.; Zou, D.; Zeng, Q. Cichorium intybus L. is a potential Cd-accumulator for phytoremediation of agricultural soil with strong tolerance and detoxification to Cd. J. Hazard. Mater. 2023, 451, 131182. [Google Scholar] [CrossRef]
  144. El Mamoun, I.; Mouna, F.; Mohammed, A.; Najib, B.; Zine-El Abidine, T.; Abdelkarim, G.; Didier, B.; Laurent, L.; Abdelaziz, S. Zinc, Lead, and Cadmium Tolerance and Accumulation in Cistus libanotis, Cistus albidus, and Cistus salviifolius: Perspectives on Phytoremediation. Remediation 2020, 30, 73–80. [Google Scholar] [CrossRef]
  145. Arenas-Lago, D.; Santos, E.S.; Carvalho, L.C.; Abreu, M.M.; Andrade, M.L. Cistus monspeliensis L. as a potential species for rehabilitation of soils with multielemental contamination under Mediterranean conditions. ESPR 2018, 25, 6443–6455. [Google Scholar] [CrossRef]
  146. Abreu, M.M.; Santos, E.S.; Magalhães, M.C.F.; Fernandes, E. Trace Elements Tolerance, Accumulation and Translocation in Cistus populifolius, Cistus salviifolius and Their Hybrid Growing in Polymetallic Contaminated Mine Areas. J. Geochem. Explor. 2012, 123, 52–60. [Google Scholar] [CrossRef]
  147. Rossini-Oliva, S.; Santos, E.S.; Abreu, M.M. Accumulation of Mn and Fe in Aromatic Plant Species from the Abandoned Rosalgar Mine and Their Potential Risk to Human Health. Appl. Geochem. 2019, 104, 42–50. [Google Scholar]
  148. Gardea-Torresdey, J.L.; Peralta-Videa, J.R.; Montes, M.; De la Rosa, G.; Corral-Diaz, B. Bioaccumulation of cadmium, chromium and copper by Convolvulus arvensis L.: Impact on plant growth and uptake of nutritional elements. Bioresour. Technol. 2004, 92, 229–235. [Google Scholar] [CrossRef]
  149. Onyia, P.C.; Ozoko, D.C.; Ifediegwu, S.I. Phytoremediation of arsenic-contaminated soils by arsenic hyperaccumulating plants in selected areas of Enugu State, Southeastern, Nigeria. Geol. Geogr. Ecol. 2021, 5, 308–319. [Google Scholar] [CrossRef]
  150. Millán, R.; Gamarra, R.; Schmid, T.; Sierra, M.J.; Quejido, A.J.; Sánchez, D.M.; Vera, R. Mercury content in vegetation and soils of the Almadén mining area (Spain). Sci. Total Environ. 2006, 368, 79–87. [Google Scholar] [CrossRef] [PubMed]
  151. Al-Sayaydeh, R.S.; Al-Hawadi, J.S.; Al-Habahbeh, K.A.; Al-Nawaiseh, M.B.; Albdaiwi, R.N.; Ayad, J.Y. Phytoremediation potential of selected ornamental woody species to heavy metal accumulation in response to long-term irrigation with treated wastewater. Water 2022, 14, 2086. [Google Scholar] [CrossRef]
  152. Lago-Vila, M.; Arenas-Lago, D.; Rodríguez-Seijo, A.; Andrade, M.L.; Vega, F.A. Ability of Cytisus scoparius for phytoremediation of soils from a Pb/Zn mine: Assessment of metal bioavailability and bioaccumulation. JEM 2019, 235, 152–160. [Google Scholar] [CrossRef]
  153. Brunetti, G.; Soler-Rovira, P.; Farrag, K.; Senesi, N. Tolerance and accumulation of heavy metals by wild plant species grown in contaminated soils in Apulia region, Southern Italy. Plant Soil 2009, 318, 285–298. [Google Scholar] [CrossRef]
  154. Mahdavian, K.; Ghaderian, S.M.; Torkzadeh-Mahani, M. Accumulation and phytoremediation of Pb, Zn, and Ag by plants growing on Koshk lead–zinc mining area, Iran. JSS 2017, 17, 1310–1320. [Google Scholar] [CrossRef]
  155. Baycu, G.; Tolunay, D.; Ozden, H.; Csatari, I.; Karadag, S.; Agba, T.; Rognes, S.E. An Abandoned Copper Mining Site in Cyprus and Assessment of Metal Concentrations in Plants and Soil. Int. J. Phytoremediation 2015, 17, 622–631. [Google Scholar] [CrossRef]
  156. González, H.; Fernández-Fuego, D.; Bertrand, A.; González, A. Effect of pH and citric acid on the growth, arsenic accumulation, and phytochelatin synthesis in Eupatorium cannabinum L., a promising plant for phytostabilization. Environ. Sci. Pollut. Res. 2019, 26, 26242–26253. [Google Scholar] [CrossRef] [PubMed]
  157. Cao, A.; Carucci, A.; Lai, T.; Bacchetta, G.; Casti, M. Use of Native Species and Biodegradable Chelating Agent in Phytoremediation of Abandoned Mining Area. J. Chem. Technol. Biotechnol. 2009, 84, 884–889. [Google Scholar] [CrossRef]
  158. Massa, N.; Andreucci, F.; Poli, M.; Aceto, M.; Barbato, R.; Berta, G. Screening for heavy metal accumulators amongst autochtonous plants in a polluted site in Italy. Ecotoxicol. Environ. Saf. 2010, 73, 1988–1997. [Google Scholar] [CrossRef] [PubMed]
  159. Martínez-Sánchez, M.J.; García-Lorenzo, M.L.; Pérez-Sirvent, C.; Bech, J. Trace element accumulation in plants from an aridic area affected by mining activities. J. Geochem. Explor. 2012, 123, 8–12. [Google Scholar] [CrossRef]
  160. Sinha, S.; Mishra, R.K.; Sinam, G.; Mallick, S.; Gupta, A.K. Comparative Evaluation of Metal Phytoremediation Potential of Trees, Grasses, and Flowering Plants from Tannery-Wastewater-Contaminated Soil in Relation with Physicochemical Properties. Soil Sediment Contam. 2013, 22, 958–983. [Google Scholar] [CrossRef]
  161. Bacchetta, G.; Boi, M.E.; Cappai, G.; Giudici, G.; Piredda, M.; Porceddu, M. Metal tolerance capability of Helichrysum microphyllum Cambess. subsp. tyrrhenicum Bacch., Brullo & Giusso: A candidate for phytostabilization in abandoned mine sites. Bull. Environ. Contam. Toxicol. 2018, 101, 758–765. [Google Scholar]
  162. Boi, M.E.; Medas, D.; Aquilanti, G.; Bacchetta, G.; Birarda, G.; Cappai, G.; Carlomagno, I.; Casu, M.A.; Gianoncelli, A.; Meneghini, C.; et al. Mineralogy and Zn Chemical Speciation in a Soil-Plant System from a Metal-Extreme Environment: A Study on Helichrysum microphyllum subsp. tyrrhenicum. Minerals 2020, 10, 259. [Google Scholar]
  163. Nematian, M.A.; Kazemeini, F. Accumulation of Pb, Zn, Cu and Fe in plants and hyperaccumulator choice in Galali iron mine area, Iran. Int. J. Agric. Crop Sci. 2013, 5, 426–432. [Google Scholar]
  164. Poschenrieder, P.; Bech, J.; Llugany, M.; Pace, A.; Fenés, E. Copper in Plant Species in a Copper Gradient in Catalonia (North East Spain) and Their Potential for Phytoremediation. Plant Soil 2001, 2, 247–256. [Google Scholar] [CrossRef]
  165. Moreira, H.; Marques, A.P.; Rangel, A.O.; Castro, P.M. Heavy Metal Accumulation in Plant Species Indigenous to a Contaminated Portuguese Site: Prospects for Phytoremediation. Water Air Soil Pollut. 2011, 221, 377–389. [Google Scholar] [CrossRef]
  166. Branković, S.; Glišić, R.; Topuzović, M.; Simić, Z.; Đekić, V.; Nenadović, N. The Bioacumulation Potential of Species Juncus articulatus L. in the Mine Drainage Water Basin and Flotation “Rudnik”, DOO, Serbia. Water Res. Manag. 2020, 10, 3–7. [Google Scholar]
  167. Pérez-Sirvent, C.; Hernández-Pérez, C.; Martínez-Sánchez, M.J.; García-Lorenzo, M.L.; Bech, J. Metal uptake by wetland plants: Implications for phytoremediation and restoration. JSS 2017, 17, 1384–1393. [Google Scholar] [CrossRef]
  168. Paniagua-López, M.; García-Robles, H.; Aguilar-Garrido, A.; Romero-Freire, A.; Lorite, J.; Sierra-Aragón, M. Vegetation establishment in soils polluted by heavy metal(loid)s after assisted natural remediation. Plant Soil 2024, 497, 257–275. [Google Scholar] [CrossRef]
  169. Ben Jeddau, K.; Vogiatzi, C.; Stamatakis, A.; Grigorakis, S.; Lydakis Simantiris, N. Heavy Metals Accumulation in Plant Tissues of Satureja cretica and Lathyrus ochrus Grown in Contaminated Soils. In Proceedings of the 15th International Conference on Environmental Science and Technology, Rhodes, Greece, 31 August–2 September 2017. [Google Scholar]
  170. Saleem, M.H.; Ali, S.; Hussain, S.; Kamran, M.; Chattha, M.S.; Ahmad, S.; Aqeel, M.; Rizwan, M.; Aljarba, N.H.; Alkahtani, S.; et al. Flax (Linum usitatissimum L.): A Potential Candidate for Phytoremediation? Biological and Economical Points of View. Plants 2020, 9, 496. [Google Scholar] [CrossRef]
  171. Akacha, B.B.; Michalak, M.; Romdhane, W.B.; Kačániová, M.; Saad, R.B.; Mnif, W.; Kukula-Koch, W.; Stefania Garzoli, S.; Hsouna, A.B. Recent advances in phytochemistry, pharmaceutical, biomedical, phytoremediation, and bio-preservative applications of Lobularia maritima. S. Afr. J. Bot. 2024, 165, 202–216. [Google Scholar] [CrossRef]
  172. Desjardins, D.; Brereton, N.J.; Marchand, L.; Brisson, J.; Pitre, F.E.; Labrecque, M. Complementarity of three distinctive phytoremediation crops for multiple-trace element contaminated soil. Sci. Total Environ. 2018, 610, 1428–1438. [Google Scholar] [CrossRef] [PubMed]
  173. Gutiérrez-Ginés, M.J.; Hernández, A.J.; Pastor, J. Impacts of soil-soluble anions on wild cultivated herbaceous species: Implications for soil phytoremediation. J. Soil Sci. Plant Nutr. 2016, 16, 423–437. [Google Scholar] [CrossRef]
  174. Safronova, V.I.; Piluzza, G.; Zinovkina, N.Y.; Kimeklis, A.K.; Belimov, A.A.; Bullitta, S. Relationships between pasture legumes, rhizobacteria and nodule bacteria in heavy metal polluted mine waste of SW Sardinia. Symbiosis 2012, 58, 149–159. [Google Scholar] [CrossRef]
  175. Bashir, S.K.; Irshad, M.; Bacha, A.U.R.; An, P.; Faridullah, F.; Ullah, Z. Investigation of heavy metals uptake in root-shoot of native plant species adjoining wastewater channels. Environ. Monit. Assess. 2024, 196, 6. [Google Scholar] [CrossRef]
  176. Aloud, S.S.; Alotaibi, K.D.; Almutairi, K.F.; Albarakah, F.N. Assessment of Heavy Metals Accumulation in Soil and Native Plants in an Industrial Environment, Saudi Arabia. Sustainability 2022, 14, 5993. [Google Scholar] [CrossRef]
  177. Perlein, A.; Bert, V.; de Souza, M.F.; Papin, A.; Meers, E. Field evaluation of industrial non-food crops for phytomanaging a metal-contaminated dredged sediment. Environ. Sci. Pollut. Res. 2023, 30, 44963–44984. [Google Scholar] [CrossRef]
  178. Midhat, L.; Ouazzani, N.; Aziz, F.; Esshaimi, M.; Hejjaj, A.; Mandi, L. Screening of new native metallophytes from copper abandoned mining site: Promising tool for phytoremediation. Land Degrad. Dev. 2023, 34, 3700–3711. [Google Scholar] [CrossRef]
  179. Manousaki, E.; Kalogerakis, N. Halophytes present new opportunities in phytoremediation of heavy metals and saline soils. Ind. Eng. Chem. Res. 2011, 50, 656–660. [Google Scholar] [CrossRef]
  180. Márquez-García, B.; Córdoba, F. Antioxidative System in Wild Populations of Erica andevalensis. Environ. Exp. Bot. 2010, 68, 58–65. [Google Scholar] [CrossRef]
  181. Stavi, I. Ecosystem services related with Opuntia ficus-indica (prickly pear cactus): A review of challenges and opportunities. ASFS 2022, 46, 815–841. [Google Scholar] [CrossRef]
  182. Benhabylès, L.; Djebbar, R.; Miard, F.; Nandillon, R.; Morabito, D.; Bourgerie, S. Biochar and compost effects on the remediative capacities of Oxalis pes-caprae L. growing on mining technosol polluted by Pb and As. ESPR 2020, 27, 30133–30144. [Google Scholar] [CrossRef]
  183. Shu, W.S.; Ye, Z.H.; Lan, C.Y.; Zhang, Z.Q.; Wong, M.H. Lead, zinc and copper accumulation and tolerance in populations of Paspalum distichum and Cynodon dactylon. Environ. Pollut. 2002, 120, 445–453. [Google Scholar] [CrossRef] [PubMed]
  184. Kharazian, P.; Bacchetta, G.; Cappai, G.; Piredda, M.; Giudici, G. An Integrated Geochemical and Mineralogical Investigation on Soil-Plant System of Pinus halepensis Pioneer Tree Growing on Heavy Metal Polluted Mine Tailing. Plant Biosyst. 2022, 157, 272–285. [Google Scholar] [CrossRef]
  185. Kharazian, P.; Cappai, G.; Boi, M.E.; Porceddu, M.; Piredda, M.; De Giudici, G.; Bacchetta, G. Greenhouse investigation on the phytoremediation potential of pioneer tree Pinus halepensis Mill. in abandoned mine site. Int. J. Phytoremediation 2023, 26, 773–783. [Google Scholar] [CrossRef] [PubMed]
  186. Heckenroth, A.; Rabier, J.; Dutoit, T.; Torre, F.; Prudent, P.; Laffont-Schwob, I. Selection of native plants with phytoremediation potential for highly contaminated Mediterranean soil restoration: Tools for a non-destructive and integrative approach. JEM 2016, 183, 850–863. [Google Scholar] [CrossRef]
  187. González, R.C.; González-Chávez, M.C.A. Metal accumulation in wild plants surrounding mining wastes. Environ. Pollut. 2006, 144, 84–92. [Google Scholar] [CrossRef]
  188. Saghi, A.; Rashed Mohassel, M.H.; Parsa, M.; Hammami, H. Phytoremediation of lead-contaminated soil by Sinapis arvensis and Rapistrum rugosum. Int. J. Phytoremediation 2016, 18, 387–392. [Google Scholar] [CrossRef]
  189. Hasnaoui, S.E.; Fahr, M.; Keller, C.; Levard, C.; Angeletti, B.; Chaurand, P.; Triqui, Z.E.A.; Guedira, A.; Rhazi, L.; Colin, F.; et al. Screening of Native Plants Growing on a Pb/Zn Mining Area in Eastern Morocco: Perspectives for Phytoremediation. Plants 2020, 9, 1458. [Google Scholar] [CrossRef]
  190. Chirilă Băbău, A.M.; Micle, V.; Damian, G.E.; Sur, I.M. Lead and copper removal from sterile dumps by phytoremediation with Robinia pseudoacacia. Sci. Rep. 2024, 14, 9842. [Google Scholar] [CrossRef]
  191. Afonso, T.F.; Demarco, C.F.; Pieniz, S.; Quadro, M.S.; Camargo, F.A.; Andreazza, R. Bioprospection of indigenous flora grown in copper mining tailing area for phytoremediation of metals. JEM 2020, 256, 109953. [Google Scholar] [CrossRef] [PubMed]
  192. Marques, A.P.; Moreira, H.; Rangel, A.O.; Castro, P.M. Arsenic, lead and nickel accumulation in Rubus ulmifolius growing in contaminated soil in Portugal. J. Hazard. Mater. 2009, 165, 174–179. [Google Scholar] [CrossRef] [PubMed]
  193. Barrutia, O.; Garbisu, C.; Hernández-Allica, J.; García-Plazaola, J.I.; Becerril, J.M. Differences in EDTA-assisted metal phytoextraction between metallicolous and non-metallicolous accessions of Rumex acetosa L. Environ. Pollut. 2010, 158, 1710–1715. [Google Scholar] [CrossRef]
  194. Zhuang, P.; Yang, Q.W.; Wang, H.B.; Shu, W.S. Phytoextraction of heavy metals by eight plant species in the field. Water Air Soil Pollut. 2007, 184, 235–242. [Google Scholar] [CrossRef]
  195. Ieviņa, S.; Karlsons, A.; Osvalde, A.; Andersone-Ozola, U.; Ievinsh, G. Coastal wetland species Rumex hydrolapathum: Tolerance against flooding, salinity, and heavy metals for its potential use in phytoremediation and environmental restoration technologies. Life 2023, 13, 1604. [Google Scholar] [CrossRef]
  196. Urošević, J.; Stanković, D.; Jokanović, D.; Trivan, G.; Rodzkin, A.; Jović, Đ.; Jovanović, F. Phytoremediation Potential of Different Genotypes of Salix alba and S. viminalis. Plants 2024, 13, 735. [Google Scholar] [CrossRef]
  197. Medina-Díaz, H.L.; López-Bellido, F.J.; Alonso-Azcárate, J.; Fernández-Morales, F.J.; Rodríguez, L. A new hyperaccumulator plant (Spergularia rubra) for the decontamination of mine tailings through electrokinetic-assisted phytoextraction. Sci. Total Environ. 2024, 912, 169543. [Google Scholar] [CrossRef]
  198. Anishchenko, O.V.; Tolomeev, A.P.; Ivanova, E.A.; Drobotov, A.V.; Kolmakova, A.A.; Zuev, I.V.; Gribovskaya, I.V. Accumulation of elements by submerged (Stuckenia pectinata (L.) Börner) and emergent (Phragmites australis (Cav.) Trin. ex Steud.) macrophytes under different salinity levels. PPB 2020, 154, 328–340. [Google Scholar] [CrossRef]
  199. Marchiol, L.; Fellet, G.; Boscutti, F.; Montella, C.; Mozzi, R.; Guarino, C. Gentle remediation at the former “Pertusola Sud” zinc smelter: Evaluation of native species for phytoremediation purposes. Ecol. Eng. 2013, 53, 343–353. [Google Scholar] [CrossRef]
  200. Escarré, J.; Lefèbvre, C.; Raboyeau, S.; Dossantos, A.; Gruber, W.; Cleyet Marel, J.C.; Frérot, H.; Noret, N.; Mahieu, S.; Collin, C.; et al. Heavy metal concentration survey in soils and plants of the Les Malines mining district (Southern France): Implications for soil restoration. Water Air Soil Pollut. 2011, 216, 485–504. [Google Scholar] [CrossRef]
  201. Accogli, R.; Tomaselli, V.; Direnzo, P.; Perrino, E.V.; Albanese, G.; Urbano, M.; Laghetti, G. Edible halophytes and halo-tolerant species in Apulia region (Southeastern Italy): Biogeography, traditional food use and potential sustainable crops. Plants 2023, 12, 549. [Google Scholar] [CrossRef]
  202. Poschenrieder, C.; Llugany, M.; Lombini, A.; Dinelli, E.; Bech, J.; Barceló, J. Smilax aspera L. an evergreen Mediterranean climber for phytoremediation. J. Geochem. Explor. 2012, 123, 41–44. [Google Scholar] [CrossRef]
  203. Zu, Y.; Li, Y.; Chen, J.; Chen, H.; Li, Q.; Schvartz, C. Hyperaccumulation of Pb, Zn and Cd in herbaceous grown on lead–zinc mining area in Yunnan, China. Environ. Int. 2005, 31, 755–762. [Google Scholar]
  204. Santos, E.S.; Abreu, M.M.; Peres, S.; Magalhães, M.C.F.; Leitão, S.; Santos Pereira, A.; Cerejeira, M.J. Potential of Tamarix africana and Other Halophyte Species for Phytostabilisation of Contaminated Salt Marsh Soils. J. Soils Sediments 2017, 17, 1459–1473. [Google Scholar] [CrossRef]
  205. Moreno-Jiménez, E.; Peñalosa, J.M.; Esteban, E.; Pilar Bernal, M. Feasibility of Arsenic Phytostabilisation Using Mediterranean Shrubs: Impact of Root Mineralisation on As Availability in Soils. J. Environ. Monit. 2009, 11, 1375–1380. [Google Scholar] [CrossRef] [PubMed]
  206. Vural, A. Trace element accumulation behavior, ability, and propensity of Taraxacum officinale FH Wigg (Dandelion). Environ. Sci. Pollut. Res. 2024, 31, 16667–16684. [Google Scholar] [CrossRef]
  207. Mohamed, H.; Mohamed, H.; Mostefa, T.; Yasmina, B.; Ayoub, K. Phytoremediation potential of spontaneous plant species in soils contaminated by hexavalent chromium in Djelfa city (Algeria). Res. J. Chem. Environ. 2022, 26, 66–74. [Google Scholar]
  208. Pajuelo, E.; Carrasco, J.A.; Romero, L.C.; Chamber, M.A.; Gotor, C. Evaluation of the metal phytoextraction potential of crop legumes. Regulation of the expression of O-acetylserine (thiol) lyase under metal stress. Plant Biol. 2007, 9, 672–681. [Google Scholar] [CrossRef]
  209. Panich-Pat, T.; Upatham, S.; Pokethitiyook, P.; Kruatrachue, M.; Lanza, G.R. Phytoextraction of metal contaminants by Typha angustifolia: Interaction of lead and cadmium in soil-water microcosms. J. Environ. Prot. 2010, 1, 431. [Google Scholar] [CrossRef]
Figure 1. Kinds of metallophytes and their phytoremediation potential. O = obliged (blue); F = facultative (orange); OC = occasional (grey); ST = phytotabilizer (green); EX = phytoextractor (blue); ND = not yet determined (yellow). Data are presented as percentages (%).
Figure 1. Kinds of metallophytes and their phytoremediation potential. O = obliged (blue); F = facultative (orange); OC = occasional (grey); ST = phytotabilizer (green); EX = phytoextractor (blue); ND = not yet determined (yellow). Data are presented as percentages (%).
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Figure 2. Distribution of phytostabilizers (green) and phytoextractors (orange) among the families.
Figure 2. Distribution of phytostabilizers (green) and phytoextractors (orange) among the families.
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Figure 3. Biological and chorological spectra and details on endemics. T = therophytes; H = hemicryptophytes; G = geophytes; Ch = chamaephytes; NP = nanophanerophytes; P = phanerophytes; Hy = hydrophytes; SA = Sardinia; CO = Corse; BL = Balearic Islands; AT = Tuscan Archipelago. Data are presented as percentages (%).
Figure 3. Biological and chorological spectra and details on endemics. T = therophytes; H = hemicryptophytes; G = geophytes; Ch = chamaephytes; NP = nanophanerophytes; P = phanerophytes; Hy = hydrophytes; SA = Sardinia; CO = Corse; BL = Balearic Islands; AT = Tuscan Archipelago. Data are presented as percentages (%).
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Figure 4. Distribution of metallophytes. F = facultative; O = obliged; OC = occasional; H = hemicryptophytes; Ch = chamaephytes; G = geophytes; NP = nanophanerophytes; P = phanerophytes; T = therophytes. Data are presented as percentages (%).
Figure 4. Distribution of metallophytes. F = facultative; O = obliged; OC = occasional; H = hemicryptophytes; Ch = chamaephytes; G = geophytes; NP = nanophanerophytes; P = phanerophytes; T = therophytes. Data are presented as percentages (%).
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Figure 5. Distribution of metallophytes among chorological forms and details regarding the endemic component. F = facultative; O = obliged; OC = occasional; SA = Sardinia; CO = Corse; BL = Balearic Islands; SI = Sicily; AT = Tuscan Archipelago; IT = Italy. Data are presented as percentages (%).
Figure 5. Distribution of metallophytes among chorological forms and details regarding the endemic component. F = facultative; O = obliged; OC = occasional; SA = Sardinia; CO = Corse; BL = Balearic Islands; SI = Sicily; AT = Tuscan Archipelago; IT = Italy. Data are presented as percentages (%).
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Figure 6. Native and alien flora in mine environments. A = archaeophytes; N = neophytes; cas = casual; nat = naturalized; inv = invasive. Data are presented as percentages (%).
Figure 6. Native and alien flora in mine environments. A = archaeophytes; N = neophytes; cas = casual; nat = naturalized; inv = invasive. Data are presented as percentages (%).
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Figure 7. IUCN assessment and details of their risk categories. DD = Data deficient; LC = Least concern; NT = Near threatened; VU = Vulnerable; EN = Endangered. Data are presented as percentages (%).
Figure 7. IUCN assessment and details of their risk categories. DD = Data deficient; LC = Least concern; NT = Near threatened; VU = Vulnerable; EN = Endangered. Data are presented as percentages (%).
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Figure 8. IUCN assessment of metallophytes and details of endemic risk categories. DD = Data deficient; LC = Least concern; NT = Near threatened; VU = Vulnerable; EN = Endangered. Data are presented as percentages (%).
Figure 8. IUCN assessment of metallophytes and details of endemic risk categories. DD = Data deficient; LC = Least concern; NT = Near threatened; VU = Vulnerable; EN = Endangered. Data are presented as percentages (%).
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Figure 9. Distribution of metallophytes among different mine areas in Sardinia. Data are presented as percentages (%).
Figure 9. Distribution of metallophytes among different mine areas in Sardinia. Data are presented as percentages (%).
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Figure 10. Maps of the main mine areas in Sardinia and the most commonly extracted metal(loid)s.
Figure 10. Maps of the main mine areas in Sardinia and the most commonly extracted metal(loid)s.
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Boi, M.E.; Sarigu, M.; Fois, M.; Casti, M.; Bacchetta, G. The First Inventory of Sardinian Mining Vascular Flora. Plants 2025, 14, 1225. https://doi.org/10.3390/plants14081225

AMA Style

Boi ME, Sarigu M, Fois M, Casti M, Bacchetta G. The First Inventory of Sardinian Mining Vascular Flora. Plants. 2025; 14(8):1225. https://doi.org/10.3390/plants14081225

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Boi, Maria Enrica, Marco Sarigu, Mauro Fois, Mauro Casti, and Gianluigi Bacchetta. 2025. "The First Inventory of Sardinian Mining Vascular Flora" Plants 14, no. 8: 1225. https://doi.org/10.3390/plants14081225

APA Style

Boi, M. E., Sarigu, M., Fois, M., Casti, M., & Bacchetta, G. (2025). The First Inventory of Sardinian Mining Vascular Flora. Plants, 14(8), 1225. https://doi.org/10.3390/plants14081225

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