Current IssueEditorial BoardOnline First ArticlesArchive
Current IssueEditorial BoardOnline First ArticlesArchive

Full Research Article

Assessment of Metal Contents and Phytoremediation Potentials of Legume Species Growing around Iron Mine

Ç
Çağrı ŞAHİN1
0009-0008-9661-9030
H
Hava Şeyma İNCİ2,*
0000 0002 2670 401X
1Department of Field Crops, Institute of Science, Bingöl University, Bingöl, Türkiye.
2Department of Crop and Animal Production, Vocational School of Food, Agriculture and Livestock, Bingöl University, Bingöl, Türkiye.

  • Submitted30-01-2026|

  • Accepted23-02-2026|

  • First Online 17-03-2026|

  • doi 10.18805/LRF-936

ABSTRACT

Background: Although mines play a crucial role in the economy, their environmental impacts are equally significant. The screening of natural plant species in mining and mining facility sites facilitates the identification of species suitable for phytoremediation. This study aims to investigate the elemental concentrations and assess the phytoremediation potential of selected legume (forage) species growing in the vicinity of the iron mine located in Bingöl province, Türkiye.

Methods: In this area, Lathyrus sphaericus Retz., Trifolium nigrescens Viv., Trifolium campestre Schreb., Trifolium arvense L., Vicia cracca L., Lotus gebelia Vent. Species belonging to the legume family were collected. Element (Al, Cu, Cr, Fe, Mn and Ni) contents were measured in the above- and below-soil parts of the plants and Translocation Factor (TF) and Bioconcentration Factor (BCF) values were calculated.

Result: TFCr, Fe, Mn, Ni>1 in L. sphaericus and V. cracca, TFAl, Cu, Cr, Fe, Mn, Ni>1 in T. nigrescens and TFAl, Cu, Cr, Mn>1 in L. gebelia. It is thought that the phytoextraction potential of these species is strong in elements with TF>1. Since the BCF-root value of T. campestre was determined as 38.91 for the element Cr, the potential of this species to be used in phytostabilization in Cr contaminated areas is considered important. Although certain species collected from the vicinity of the mine (TF>1) appear to be promising candidates for phytoremediation, further studies using different doses of single-element toxicity in pot trials will provide clearer information on whether the species are phytoextractors or phytostabilizers.

INTRODUCTION

Heavy metals are inorganic elements with a density greater than about 5 g cm-3 (Brahma et al., 2026). The use of synthetic inputs, industrialization and urbanization activities increase heavy metal pollution that damages the natural environment (Paul et al., 2021). Among anthropogenic factors, mining can produce and release large amounts of heavy metals (Lin et al., 2023). The waste soils generated from mining activities can accumulate in certain areas, leading to the formation of heavy metal-laden waste zones that may contaminate the soil and groundwater (Fashola et al., 2016). Instead of shutting down mining enterprises, which are significant for the country’s economy, it is necessary to develop and implement methods and techniques that will minimize the effects of these activities on forests and the environment (Uzun and Bollukcu, 2009). Physical and chemical methods for soil remediation (such as soil exchange, thermal desorption, fixation and immobilization) are included (Rama et al., 2021). However, both physical and chemical methods are often costly and are likely to cause irreversible changes in the soil (Chamba-Eras et al., 2022). Phytoremediation is a bioremediation method that uses plants to reduce the toxic effects of heavy metals in the environment (Ashraf et al., 2019). Plants called hyperaccumulator plants, accumulate heavy metals in their shoots rather than in their roots (Divya et al., 2024). Among the phytoremediation technologies that can be applied to soils contaminated, two of the most widely used are phytoextraction and phytostabilization. Phytoextraction is considered a permanent solution for the removal of heavy metals, unlike phytostabilization, which retains metals underground (Yan et al., 2020). Phytoremediation potential can be estimated by calculating the bioconcentration factor (BCF) and translocation factor (TF) (Favas et al., 2014). If TF>1, the plant has transferred the metal from the root to the stem. BCF>10 means the plant is a hyperaccumulator, BCF>1 means the plant is an accumulator and BCF<1 means the plant is an excluder (Sevencan, 2022).
       
Plants with BCF, TF values higher than the limit value of 1 were classified as “phytoextractors”, while plants with TF values below the limit value and BCF values above the limit value of 1 were categorized as “phytostabilizers” (Yang et al., 2014). Surveying native plant species at mine sites can identify suitable plants for phytoremediation approaches.
       
In this study, we aimed to investigate the heavy metal contents of selected species that grow in the natural areas surrounding an iron mine that has been operational for several years and to evaluate their phytoremediation capacities.

MATERIALS AND METHODS

The study was conducted in the natural areas around the Avnik iron mine in Bingöl province of Türkiye (Sahin, 2025). In April, May and June 2024, leguminous forage plants were collected from an area (4 ha) approximately 350-700 m away from the mine site and elemental analyses were performed at the Bingöl University Central Laboratory. The coordinates of the study area (38°39'1”N-40°18'13”E and its neighborhood) were marked on the map and presented in Fig 1.

Fig 1: View of the mining area and work area.


       
In this area, leguminous plant species that had entered the generative stage were harvested from the field without damaging their roots as much as possible and were identified. The plants were separated into their organs (roots, stems, leaves and generative parts (flowers and/or pods), washed with tap water and distilled water, dried at 70°C for 2 days and milled.
       
Soil samples were collected from three different areas within (4 ha) to represent the locations. Characteristics of soil samples from the study region are shown in Table 1. According to the WHO's permitted limit values for toxic metals in soil and plants (WHO/FAO, 2007; Sönmez and Kiliç, 2021), only the Mn content in the soil was found to be higher than the permitted limit value.

Table 1: Characteristics of soil samples collected from the study region.


 
Plant species belonging to the legume family
 
Six common leguminous species were identified and collected (at least 15 plants of each species were randomly collected from the land, element analyses were performed in 3 repetitions and each replication contained 5 plants) from the area surrounding the mining site, then identified using the 11-volume Flora of Turkey and the East Aegean Islands (Davis, 1965-1985). The scientific names and authors of the taxa were checked against the current Turkey Plant List (Güner et al., 2012). The plant species identified as a result of the study are shown in Table 2.

Table 2: List of identified plant species.


       
The generative parts of the species are pods in Lathyrus sphaericus and flowers in Trifolium campestre, Trifolium nigrescens, Trifolium arvense, Vicia cracca and Lotus gebelia.
       
Images of species belonging to the legume family are presented in Fig 2.

Fig 2: Images of legume plants in the working region.


 
Determination of Al, Cu, Cr, Fe, Mn and Ni concentrations in plants
 
The combustion of ground plants was performed using a microwave method adapted from Miller (1998). After dilution and filtration, element contents were determined using an ICP-MS (Inductively Coupled Plasma Mass Spectrometry) device.
 
Translocation factor (TF)
 
They indicate the potential for metals to be transported from roots to above-ground organs. If TF>1, the plant has the potential to be considered a bioaccumulator in phytoremediation (Sürmen et al., 2019). The following formula is used in its calculation (Ortakcı, 2020; Gökdere et al., 2025).

 
Bioconcentration factor (BCF)
 
Values such as TF and/or BCF are used in the selection of plants to be used in phytoremediation. The extent to which plants take up metals into their tissues is expressed as the BCF. The BCF value is determined by the ratio of the metal content in the roots or shoots to the metal content in the soil (Sürmen et al., 2019).

 
Statistics
 
Two different ANOVAs (analysis of variance) were performed in the evaluation of the data. A two-factor analysis of variance was performed for the species × organ interaction, while a one-factor analysis of variance was performed to evaluate accumulation in a single organ individually. Results found to be significant (p<0.05) were compared using the Tukey test (JMP, 2018). Interaction results are presented in tables, while organ-based evaluation results are presented in graphs.

RESULTS AND DISCUSSION

Aluminum (Al) content of species (mg kg-1)
 
According to the two-way ANOVA results for Al concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 3.

Table 3: Al concentrations in the organs of the species.


       
The highest Al concentrations within the organs were determined in the roots of the plants, while the lowest was in the stem parts. Among species, the highest Al was found in T. nigrescens plants.
       
Aluminum has accumulated most in the roots of T. campestre and least in L. gebelia, most in the stem of T. nigrescens and least in V. cracca and L. gebelia, most in the leaves of T. nigrescens and least in T. arvense and most in the generative parts of T. campestre and T. nigrescens and least in L. sphaericus (Fig 3).

Fig 3: Graph showing Al concentrations in plant organs.


 
Chromium (Cr) content of species (mg kg-1)
 
According to the two-way ANOVA results for Cr concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 4.

Table 4: Cr concentrations in the organs of the species.


       
The highest Cr concentration within organs was found in plant roots, while the lowest was in leaves. Among species, the highest Cr was determined in T. campestre plants, while the lowest Cr was determined in L. sphaericus species (Table 4).
       
Chromium is accumulated most in the roots of T. campestre and least in L. sphaericus, most in the stems of T. nigrescens and least in L. sphaericus, most in the leaves of T. nigrescens and least in L. gebelia and most in the generative parts of T. campestre and least in L. sphaericus and L. gebelia (Fig 4).

Fig 4: Graph showing Cr concentrations in plant organs.


 
Copper (Cu) content of species (mg kg-1)
 
According to the two-way ANOVA results for Cu concentrations in different legume species, species, organs and (species × organ) interaction was found to be significant (p<0.01). The resulting means and groupings are shown in Table 5.

Table 5: Cu concentrations in the organs of the species.


       
Among species, the highest Cu concentration was found in L. sphaericus plants, while the lowest Cu was found in L. gebelia plants (Table 5).
       
Copper accumulated most in the roots of V. cracca and least in T. nigrescens and L. gebelia; most in the stems of L. sphaericus and least in T. nigrescens; most in the leaves of L. sphaericus and T. campstre and least in L. gebelia; and most in the generative parts of V. cracca and least in L. gebelia (Fig 5).

Fig 5: Graph showing Cu concentrations in plant organs.


 
Iron (Fe) content of species (mg kg-1)
 
According to the two-way ANOVA results for Fe concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 6.

Table 6: Fe concentrations in the organs of the species.


       
The highest Fe concentration within organs was found in plant roots, while the lowest was in stems. Among species, the highest Fe was found in T. campestre and T. nigrescens  plants, while the lowest Fe was found in L. sphaericus and L. gebelia species (Table 6).
       
In the roots, T. campestre accumulated the most, while L. sphaericus and L. gebelia accumulated the least; in the stem, T. nigrescens accumulated the most, while V. cracca and L. gebelia accumulated the least; in the leaves, T. nigrescens accumulated the most, while L. sphaericus accumulated the least. T. arvense and L. gebelia and in its generative parts, it accumulated the most T. nigrescens and the least L. sphaericus species (Fig 6).  

Fig 6: Graph showing Fe concentrations in plant organs.


 
Manganese (Mn) content of species (mg kg-1)
 
According to the two-way ANOVA results for Mn concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 7.

Table 7: Mn concentrations in the organs of the species.


       
The highest Mn content within the organs was found in the leaves of the plants, while the lowest was in the stems. Among species, the highest Mn was found in T. campestre plants, while the lowest Mn was determined in L. sphaericus, T. arvense and V. cracca species (Table 7).
       
Manganese accumulated most in the roots of T. campestre and least in L. sphaericus and L. gebelia; most in the stems of T. nigrescens and least in V. cracca; most in the leaves of T. campestre and least in T. arvense; and most in the generative parts of T. campestre and least in L. sphaericus (Fig 7).  

Fig 7: Graph showing Mn concentrations in plant organs.


 
Nickel (Ni) content of species (mg kg-1)
 
According to the two-way ANOVA results for Ni concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 8.

Table 8: Ni concentrations in the organs of the species.


       
The highest Ni content within organs was found in plant roots, while the lowest was in leaves and stems. Among species, the highest Ni was found in T. campestre plants, while the lowest Ni was found in L. sphaericus species (Table 8).
       
Nickel accumulated most in the roots of T. campestre and least in L. sphaericus; most in the stems and leaves of T. nigrescens and least in L. sphaericus; and most in the generative parts of T. campestre and least in L. sphaericus (Fig 8).

Fig 8: Graph showing Ni concentrations in plant organs.


 
Assessment of phytoremediation capacities of legume species (TF and BCF)
 
The TF, BCFroot and BCFshoot values for the examined elements of the species plant are given in Table 9-14.

Table 9: TF and BCF evaluations for Lathyrus sphaericus.



Table 10: TF and BCF evaluations for Trifolium campestre.



Table 11: TF and BCF evaluations for Trifolium nigrescens.



Table 12: TF and BCF evaluations for Trifolium arvense.



Table 13: TF and BCF evaluations for Vicia cracca.



Table 14: TF and BCF evaluations for Lotus gebelia.


       
In Lathyrus sphaericus, TF>1 was found for Cr, Fe, Mn, Ni; BCFroot>1 for Cu; and BCFshoot>1 for Cr, Cu (Table 9).
       
Trifolium campestre did not exhibit TF>1 for any element, but BCFroot>1 was determined for Cr, Cu, Ni and BCFshoot>1 was determined for Cr and Cu (Table 10).
       
In Trifolium nigrescens, TF>1 was determined for all elements, while BCFroot and BCFshoot>1 were determined for Cr, Cu (Table 11).
       
Trifolium arvense did not find TF>1 for any element, but BCFroot and BCFshoot>1 were determined for Cr and Cu (Table 12).
       
In Vicia cracca, TF>1 was calculated for Cr, Fe, Mn and Ni while BCFroot and BCFshoot>1 were calculated for Cr and Cu (Table 13).
       
In Lotus gebelia, TF>1 was calculated for Al, Cr and Mn elements and BCFroot and BCFshoot>1 were calculated for Cr and Cu elements (Table 14).
       
The uptake of metals by plants is influenced by several factors such as soil metal concentrations, cation exchange capacity, soil pH, organic matter content, plant species and varieties and plant age. However, the main factor is the concentration of metals in the soil and hence the existing environmental conditions (Annan et al., 2013).
       
Shahidi et al., (1999) reported that the vegetative parts of L. maritimus contained more Al than the generative parts. In this study, similar to the studies of Shahidi et al., (1999), the vegetative parts (leaves and stem) of L. sphaericus accumulated about 3.5 times more Al than the generative parts (seeds and pods). The study of Wheeler and Dodd (1995) with 15 different Trifolium and 6 different Lotus species is not similar to this study in terms of concentration. It is thought that the reasons for this may be related to the Al concentrations in the study areas. However, if a comparison is made between Trifolium and Lotus species, Trifolium species had higher Al, Cu and Fe content than Lotus species in Wheeler and Dodd (1995) study, as in this study.  In the leaves of V. cracca, about 2.2 times more Al accumulation was observed than in the stem. Similarly, Kolesnichenko et al., (2018) found about 2.1 times more Al in the leaves of V. cracca than in the stem.
       
Chromium concentration (1.21 mg kg-1) determined for the generative parts of Lathyrus sphaericus in this study was similar to the Cr concentration (1.10 mg kg-1) measured by Kodirova et al., (2024) in seeds of twelve different Lathyrus genotypes. Chromium concentrations of Trifolium species varied between 6.94-23.34 mg kg-1. Gounden et al., (2018) reported that the maximum concentration for Cr was 6 mg kg-1 in their study with five different Trifolium species. Chromium was determined as 2.24 mg kg-1 in shoots and 2.00 mg kg-1 in roots of Lotus gebelia; Sujkowska-Rybkowska et al. (2020) determined Cr content of Lotus corniculatus as 5.4 mg kg-1 in shoots and 20.5 mg kg-1 in roots.
       
Shahidi et al., (1999) reported that the vegetative parts of Lathyrus maritimus contained more Fe than the generative parts. In this study, similar to the studies of Shahidi et al., (1999), the vegetative parts of Lathyrus sphaericus contained more Fe than the generative parts. In this study, Fe accumulation in the leaves of Vicia cracca was observed to be approximately 2.5 times higher than in the stem, while in Kolesnichenko et al., (2018), Fe accumulation in the leaves of Vicia cracca was observed to be approximately 3.1 times higher than in the stem.
       
The Mn level measured in the leaves of Lathyrus maritimus by Maslennikov et al., (2020) is similar to the Mn level measured in the leaves of Lathyrus sphaericus in this study.  Wheeler and Dodd (1995), in their study with 6 different Lotus species, found that the average Mn concentration in the above-ground organs was similar to the average Mn concentration in the above-ground organs of Lotus gebelia, but the average above-ground Mn concentrations of Trifolium species were higher than those of Trifolium species in this study. While Mn accumulation in the leaves of Vicia cracca was observed approximately 3.6 times higher than in the stem, Kolesnichenko et al., (2018) observed Mn accumulation in the leaves of Vicia cracca plants approximately 4.8 times higher than in the stem.
       
Lathyrus sphaericus transported Ni to the above-ground organs. However, Jeddou et al., (2017) reported that Ni in Lathyrus ochrus had limited transport to the upper parts and nickel was mostly accumulated in the roots. Nickel concentrations of Trifolium species were found to be similar (<10 mg kg-1 Ni) to the study of Gounden et al., (2018) with 5 different Trifolium species.
       
The Ni concentration in the leaves and stems of Vicia cracca is similar to the Ni concentration in the leaves and stems of Vicia cracca in the study of Kolesnichenko et al., (2018).  Nickel content of L. gebelia was determined as 1.35 mg kg-1 in shoots and 2.25 mg kg-1 in roots; Sujkowska-Rybkowska et al. (2020) determined Ni content of Lotus corniculatus as 59.5 mg kg-1 in shoots and 167.1 mg kg-1 in roots. Saruhan et al., (2012) reported the Ni content of Lotus corniculatus in control plants similar to this study.
       
Plants having TF and especially BCF values less than one (TF<1) are not suitable for phytoextraction (Fitz and Wenzel, 2002), while TF>1 is a decisive factor in the classification of plant species for phytoremediation (Chanu and Gupta, 2016). However, plants having high bioconcentration factor and low translocation factor have phytostabilization potential (Yoon et al., 2006).
       
Unlike the value obtained for Ni (TF>1) in this study, Jeddou et al., (2017) reported that BCF and TF values were below 1 in Lathyrus ochrus. Wheeler and Dodd (1995) reported that the TF values obtained for Al (0.4), Cu (0.3), Fe (0.2) and Mn (0.7) were below 1 in their study with fifteen different Trifolium species. In this study, TF<1 was found for T. campestre and T. arvense, which was similar to the results of Wheeler and Dodd (1995), but for Trifolium nigrescens, contrary to the results of the researchers, Al, Cu, Fe and Mn were found to be TF>1. TFCu<1 was found in V. cracca and Saadaoui et al., (2022) found TF<1 (Vicia faba L. cv. Mamdouh: TFshoot 0.32, TFflower 0.18) in one of two different Vicia plants and TF>1 (Vicia faba L. cv. Badii: TFshoot 1.38, TFflower 1.48) in the other. Sujkowska-Rybkowska et al. (2020) reported TF values <1 for Cr (contrary to the results of this study) and Ni (similar to the results of this study) of Lotus corniculatus. The TF values obtained by Wheeler and Dodd (1995) for Al, Cu, Fe and Mn (<1) were found to be different from the TFMn,Al values obtained in this study, but similar to the TFFe,Cu  values.

CONCLUSION

The soils of the study area did not exceed the limit according to the toxic metal limit values allowed by WHO, except for Mn (allowed 80 mg kg-1). Considering the values determined in the above-ground organs of plants such as stems and leaves, the permissible limit values for Mn, Cu and Ni were not exceeded, only Cr and Fe concentrations exceeded the limit (Cr: 5 mg kg-1 and Fe: 450 mg kg-1) toxic metal level in some species. Since TFCr, Fe, Mn, Ni>1 in L. sphaericus and V. cracca, TFAl, Cu, Cr, Fe, Mn, Ni>1 in T. nigrescens and TFAl, Cu, Cr, Mn>1 in L. gebelia, these legume species are important for phytoextraction. For Cr metal, the BCF root value was 38.91 in T. campestre and this high value revealed the potential of this species for phytostabilization of Cr contaminated soils. Among these legume species collected from the mine site, those with TF>1 are promising for phytoremediation. Due to the high levels of Fe and Cr metals in the above-ground organs of some legume species, it is recommended that livestock grazing should be done more carefully in these areas.

ACKNOWLEDGEMENT

This article was produced from Çağrı ŞAHİN's master’s thesis. We would like to thank Dr. Mihriban AHISKALI for her help and support in the identification of the plants and the drawing of the visuals in the graphs (characteristic morphological parts specific to the legume family).

CONFLICT OF INTEREST

The authors declare that there is no conflict of interest. I confirm that there are no conflicts of interest regarding this manuscript.

REFERENCES


  1. Annan, K., Dickson, R.A., Amponsah, I.K. and Nooni, I.K. (2013). The heavy metal contents of some selected medicinal plants sampled from different geographical locations. Pharmacognosy Research. 5(2): 103.

  2. Ashraf, S., Ali, Q., Zahir, Z.A., Ashraf, S. and Asghar, H.N. (2019). Phytoremediation: Environmentally sustainable way for reclamation of heavy metal polluted soils. Ecotoxicology and Environmental Safety. 174: 714-727.

  3. Brahma, S., Lolesh, P., Barnali, S., Rajesh, C. and Dipankar, S. (2026). Heavy metal contamination in vegetables and their amelioration: A review. Agricultural Reviews. 47(1): 1-12. doi: 10.18805/ag.R-2737.

  4. Chamba-Eras, I., Griffith, D.M., Kalinhoff, C., Ramírez, J. and Gázquez, M.J. (2022). Native hyperaccumulator plants with differential phytoremediation potential in an artisanal gold mine of the ecuadorian amazon. Plants. 11(9): 1186.

  5. Chanu, L.B. and Gupta, A. (2016). Phytoremediation of lead using ýpomoea aquatica forsk. in hydroponic solution. Chemosphere.  156: 407-411.

  6. Davis, P.H. (1965-1985). Flora of Turkey and the East Aegean Islands. Vol. 1-9. Edinburgh University Press., Edinburgh.

  7. Divya V.U., Sindhu P.V. and Aiswarya N.S. (2024). Agromining: Agroremediation for heavy metal contaminated ecosystems: A review. Bhartiya Krishi Anusandhan Patrika. 39(1): 51-55. doi: 10.18805/BKAP682. 

  8. Fashola, M.O., Ngole-Jeme, V.M. and Babalola, O.O. (2016). Heavy metal pollution from gold mines: environmental effects and bacterial strategies for resistance. International Journal of Environmental Research and Public Health. 13(11): 1047.

  9. Favas, P., Pratas, J., Varun, M., Souza, R. and Paul, M. (2014). Phytoremediation of Soils Contaminated with Metals and Metalloids at Mining Areas: Potential of Native Flora. In Environmental Risk Assessment of Soil Contaminatio; IntechOpen: London, UK, pp. 485-517.

  10. Fitz, W.J. and Wenzel, W.W. (2002). Arsenic transformations in the soil-rhizosphere-plant system: Fundamentals and potential application to phytoremediation. Journal of Biotechnology. 99(3): 259-278. 

  11. Gounden, T., Moodley, R. and Jonnalagadda, S.B. (2018). Elemental analysis and nutritional value of edible Trifolium (clover) species. Journal of Environmental Science and Health. Part B, 53(8): 487-492.

  12. Gökdere, H., Şahin, Ç., Erdem, S., Asutay, Z. and Arıgrekin, A. (2025). Determination of some trace element content of gum tragacanth (Astragalus gummifer Labill.) growing near mining sites. Agro Science and Technology Journal. 1(1): 1-8.

  13. Güner, A., Aslan, S., Ekim, T., Vural, M. and ve Babaç, M.T. (2012). Türkiye Bitkileri Listesi (Damarlı Bitkiler). Nezahat Gökyiğit Bahçesi ve Flora Araştırmaları Derneği Yayını. İstanbul.

  14. Jeddou, K., Vogıatzı, C., Stamatakıs, A., Grıgorakıs, S. and Sımantırıs, N.L. (2017). Heavy Metals Accumulation in Plant Tissues of Satureja Cretica and Lathyrus Ochrus Grown in Contaminated Soils. 15th International Conference on Environmental Science and Technology Rhodes, Greece, 31 August to 2 September 2017.

  15. JMP, (2018). Statistical Discovery from SAS, USA.

  16. Kodirova, S., Amanov, B., Muminov, K. H., Abdiyev, F., Buronov, A., Tursunova, N. and Kurbanbayev, I. (2024). Physıologıcal and bıochemıcal parameters of the exotıc specıes of grass pea (Lathyrus satıvus L.). Sabrao Journal of Breeding and Genetics. 56(4): 1513-1523.

  17. Kolesnichenko, L.G., Shepeleva, L.F., Rabtsevich, E.S., Ledeneva, E.A., Teslinova, M.S., Rozhkova-Timina, I.O. and Kirpotin, S.N. (2018). Elemental Chemical Composition of Some Meadow Plants in the Middle Ob Basin. In: IOP Conference Series: Earth and Environmental Science. IOP Publishing. 201(1): 012009.

  18. Lin, G., Zeng, B., Li, J., Wang, Z., Wang, S., Hu, T. and Zhang, L. (2023). A systematic review of metal organic frameworks materials for heavy metal removal: Synthesis, applications and mechanism. Chemical Engineering Journal. 460: 141710.

  19. Maslennikov, P., Golovina, E. and Artemenko, A. (2020). Ecological and geochemical conditions for the accumulation of antioxidants in the leaves of Lathyrus maritimus (L.) bigel. Plants. 9(6): 746.

  20. Miller, R.O. (1998). Microwave Digestion of Plant Tissue in a Closed Vessel. In: [Kaira, Y.P.  (Eds)] Handbook of Reference Methods for Plant Analysis CRC Boca Raton pp. 69-74.

  21. Ortakcı, G. (2020). Elazığ (Maden)'da işletmesi devam eden ve Amasya (Gümüşhacıköy)'da işletmesi bitmiş olan maden sahalarındaki bazı bitkilerde ağır metal bioakümülasyonları. Yüksek Lisans Tezi. Amasya Üniversitesi.

  22. Paul, I.A.R., Dhivyadharsini, D. and Mathivadhana, K.S. (2021). Rehabilitation of heavy metal contamination and soil erosion through ıntegrated management. Agricultural Reviews. 42(3): 300-307. doi: 10.18805/ag.R-2052.

  23. Rama, K., Nishita, O., Sadiqa, A. and Sonal, B. (2021). A review on heavy metal contamination at mining sites and remedial techniques. IOP Conference Series: Earth and Environmental Science. 796: 012013.

  24. Saadaoui, W., Gamboa-Rosales, H., Sifuentes-Gallardo, C., Durán- Muñoz, H., Abrougui, K., Mohammadi, A. and Tarchoun, N. (2022). Effects of lead, copper and cadmium on bioaccumulation and translocation factors and biosynthesis of photosynthetic pigments in Vicia faba L.(broad beans) at different stages of growth. Applied Sciences. 12(18): 8941.

  25. Saruhan, V., Gul, I., Kusvuran, A. and Aydin, F. (2012). Effects of sewage sludge used as fertilizer on heavy metal contents of bird’s-foot trefoil (Lotus corniculatus L.) and soil.  Asian Journal of Chemistry. 24(2): 866.

  26. Sevencan, T.A. (2022). Metal stresindeki bazı tıbbi bitkilerin fitoremediasyon potansiyelleri ve biyokütle kullanımları. Doktora tezi. İstanbul Üniversitesi.

  27. Shahidi, F., Chavan, U.D., Bal, A.K. and McKenzie, D.B. (1999). Chemical composition of beach pea (Lathyrus maritimus L.) plant parts. Food Chemistry. 64(1): 39-44. 

  28. Sönmez, O. and Kılıç, F.N. (2021). Heavy metal pollution in soil and removal methods. Turkish Journal of Agricultural Engineering Research. 2(2): 493-507.

  29. Sujkowska-Rybkowska, M., Kasowska, D., Gediga, K., Banasiewicz, J. and Stêpkowski, T. (2020). Lotus corniculatus-rhizobia symbiosis under Ni, Co and Cr stress on ultramafic soil. Plant and Soil. 451: 459-484.

  30. Sürmen, B., Kılıç, D.D., Kutbay, H.G. and Tuna, E.E. (2019). Doğal olarak yayılış gösteren Lepidium draba L. türünün fitoremediasyon yönteminde kullanılabilirliğinin araştırılması. Avrupa Bilim ve Teknoloji Dergisi. 17: 491-499. 

  31. Sahin, Ç. (2025). Demir Madeni İşletmesi Çevresindeki Doğal Alanlarda Yayılış Gösteren Yem Bitkisi Türlerinin Ağır Metal İçeriklerinin Araştırılması ve Fitoremediasyon Kapasitelerinin Değerlendirilmesi: Bingöl-Avnik Örneği. Yüksek Lisans Tezi. Bingöl Üniversitesi.

  32. Uzun, O. and Bollukcu, P. (2009). Bartın merkez ilçe sınırları içinde yer alan açık ocak işletmelerinin peyzaj onarımı-biyolojik onarım açısından değerlendirilmesi. Bartın Orman Fakültesi Dergisi I. Ulusal Batı Karadeniz Ormancılık Kongresi Bildiriler Kitabı. Özel Sayı. ISSN: 1302-0943.

  33. Wheeler, D.M. and Dodd, M.B. (1995). Effect of aluminium on yield and plant chemical concentrations of some temperate legumes. Plant and Soil. 173: 133-145.

  34. WHO/FAO (2007). Joint FAO/WHO Food Standard Programme Codex Alimentarius Commission 13th Session. Report of the Thirty-Eight Session of the Codex Committee on Food Hygiene, Houston, United States of America (07/ 30/13).

  35. Yan, A., Wang, Y., Tan, S.N., Yusof, M.L.M., Ghosh, S. and Chen, Z. (2020). Phytoremediation: a promising approach for revegetation of heavy metal-polluted land. Frontiers in Plant Science. 11: 359.

  36. Yang, S., Liang, S., Yi, L., Xu, B., Cao, J., Guo, Y. and Zhou, Y. (2014). Heavy metal accumulation and phytostabilization potential of dominant plant species growing on manganese mine tailings. Frontiers of Environmental Science and Engineering. 8: 394-404.

  37. Yoon, J., Cao, X., Zhou, Q. and Ma, L.Q. (2006). Accumulation of Pb, Cu and Zn in native plants growing on a contaminated florida site. Science of the Total Environment. 368(2-3): 456-464.
Published In
Legume Research
Article Metrics
Metrics Icon
0
Views
0
Citations
Reviewed By
Share Article
Download Article
In this Article
    Contact us
    Follow us

    Full Research Article

    Assessment of Metal Contents and Phytoremediation Potentials of Legume Species Growing around Iron Mine

    Ç
    Çağrı ŞAHİN1
    0009-0008-9661-9030
    H
    Hava Şeyma İNCİ2,*
    0000 0002 2670 401X
    1Department of Field Crops, Institute of Science, Bingöl University, Bingöl, Türkiye.
    2Department of Crop and Animal Production, Vocational School of Food, Agriculture and Livestock, Bingöl University, Bingöl, Türkiye.

    • Submitted30-01-2026|

    • Accepted23-02-2026|

    • First Online 17-03-2026|

    • doi 10.18805/LRF-936

    ABSTRACT

    Background: Although mines play a crucial role in the economy, their environmental impacts are equally significant. The screening of natural plant species in mining and mining facility sites facilitates the identification of species suitable for phytoremediation. This study aims to investigate the elemental concentrations and assess the phytoremediation potential of selected legume (forage) species growing in the vicinity of the iron mine located in Bingöl province, Türkiye.

    Methods: In this area, Lathyrus sphaericus Retz., Trifolium nigrescens Viv., Trifolium campestre Schreb., Trifolium arvense L., Vicia cracca L., Lotus gebelia Vent. Species belonging to the legume family were collected. Element (Al, Cu, Cr, Fe, Mn and Ni) contents were measured in the above- and below-soil parts of the plants and Translocation Factor (TF) and Bioconcentration Factor (BCF) values were calculated.

    Result: TFCr, Fe, Mn, Ni>1 in L. sphaericus and V. cracca, TFAl, Cu, Cr, Fe, Mn, Ni>1 in T. nigrescens and TFAl, Cu, Cr, Mn>1 in L. gebelia. It is thought that the phytoextraction potential of these species is strong in elements with TF>1. Since the BCF-root value of T. campestre was determined as 38.91 for the element Cr, the potential of this species to be used in phytostabilization in Cr contaminated areas is considered important. Although certain species collected from the vicinity of the mine (TF>1) appear to be promising candidates for phytoremediation, further studies using different doses of single-element toxicity in pot trials will provide clearer information on whether the species are phytoextractors or phytostabilizers.

    INTRODUCTION

    Heavy metals are inorganic elements with a density greater than about 5 g cm-3 (Brahma et al., 2026). The use of synthetic inputs, industrialization and urbanization activities increase heavy metal pollution that damages the natural environment (Paul et al., 2021). Among anthropogenic factors, mining can produce and release large amounts of heavy metals (Lin et al., 2023). The waste soils generated from mining activities can accumulate in certain areas, leading to the formation of heavy metal-laden waste zones that may contaminate the soil and groundwater (Fashola et al., 2016). Instead of shutting down mining enterprises, which are significant for the country’s economy, it is necessary to develop and implement methods and techniques that will minimize the effects of these activities on forests and the environment (Uzun and Bollukcu, 2009). Physical and chemical methods for soil remediation (such as soil exchange, thermal desorption, fixation and immobilization) are included (Rama et al., 2021). However, both physical and chemical methods are often costly and are likely to cause irreversible changes in the soil (Chamba-Eras et al., 2022). Phytoremediation is a bioremediation method that uses plants to reduce the toxic effects of heavy metals in the environment (Ashraf et al., 2019). Plants called hyperaccumulator plants, accumulate heavy metals in their shoots rather than in their roots (Divya et al., 2024). Among the phytoremediation technologies that can be applied to soils contaminated, two of the most widely used are phytoextraction and phytostabilization. Phytoextraction is considered a permanent solution for the removal of heavy metals, unlike phytostabilization, which retains metals underground (Yan et al., 2020). Phytoremediation potential can be estimated by calculating the bioconcentration factor (BCF) and translocation factor (TF) (Favas et al., 2014). If TF>1, the plant has transferred the metal from the root to the stem. BCF>10 means the plant is a hyperaccumulator, BCF>1 means the plant is an accumulator and BCF<1 means the plant is an excluder (Sevencan, 2022).
           
    Plants with BCF, TF values higher than the limit value of 1 were classified as “phytoextractors”, while plants with TF values below the limit value and BCF values above the limit value of 1 were categorized as “phytostabilizers” (Yang et al., 2014). Surveying native plant species at mine sites can identify suitable plants for phytoremediation approaches.
           
    In this study, we aimed to investigate the heavy metal contents of selected species that grow in the natural areas surrounding an iron mine that has been operational for several years and to evaluate their phytoremediation capacities.

    MATERIALS AND METHODS

    The study was conducted in the natural areas around the Avnik iron mine in Bingöl province of Türkiye (Sahin, 2025). In April, May and June 2024, leguminous forage plants were collected from an area (4 ha) approximately 350-700 m away from the mine site and elemental analyses were performed at the Bingöl University Central Laboratory. The coordinates of the study area (38°39'1”N-40°18'13”E and its neighborhood) were marked on the map and presented in Fig 1.

    Fig 1: View of the mining area and work area.


           
    In this area, leguminous plant species that had entered the generative stage were harvested from the field without damaging their roots as much as possible and were identified. The plants were separated into their organs (roots, stems, leaves and generative parts (flowers and/or pods), washed with tap water and distilled water, dried at 70°C for 2 days and milled.
           
    Soil samples were collected from three different areas within (4 ha) to represent the locations. Characteristics of soil samples from the study region are shown in Table 1. According to the WHO's permitted limit values for toxic metals in soil and plants (WHO/FAO, 2007; Sönmez and Kiliç, 2021), only the Mn content in the soil was found to be higher than the permitted limit value.

    Table 1: Characteristics of soil samples collected from the study region.


     
    Plant species belonging to the legume family
     
    Six common leguminous species were identified and collected (at least 15 plants of each species were randomly collected from the land, element analyses were performed in 3 repetitions and each replication contained 5 plants) from the area surrounding the mining site, then identified using the 11-volume Flora of Turkey and the East Aegean Islands (Davis, 1965-1985). The scientific names and authors of the taxa were checked against the current Turkey Plant List (Güner et al., 2012). The plant species identified as a result of the study are shown in Table 2.

    Table 2: List of identified plant species.


           
    The generative parts of the species are pods in Lathyrus sphaericus and flowers in Trifolium campestre, Trifolium nigrescens, Trifolium arvense, Vicia cracca and Lotus gebelia.
           
    Images of species belonging to the legume family are presented in Fig 2.

    Fig 2: Images of legume plants in the working region.


     
    Determination of Al, Cu, Cr, Fe, Mn and Ni concentrations in plants
     
    The combustion of ground plants was performed using a microwave method adapted from Miller (1998). After dilution and filtration, element contents were determined using an ICP-MS (Inductively Coupled Plasma Mass Spectrometry) device.
     
    Translocation factor (TF)
     
    They indicate the potential for metals to be transported from roots to above-ground organs. If TF>1, the plant has the potential to be considered a bioaccumulator in phytoremediation (Sürmen et al., 2019). The following formula is used in its calculation (Ortakcı, 2020; Gökdere et al., 2025).

     
    Bioconcentration factor (BCF)
     
    Values such as TF and/or BCF are used in the selection of plants to be used in phytoremediation. The extent to which plants take up metals into their tissues is expressed as the BCF. The BCF value is determined by the ratio of the metal content in the roots or shoots to the metal content in the soil (Sürmen et al., 2019).

     
    Statistics
     
    Two different ANOVAs (analysis of variance) were performed in the evaluation of the data. A two-factor analysis of variance was performed for the species × organ interaction, while a one-factor analysis of variance was performed to evaluate accumulation in a single organ individually. Results found to be significant (p<0.05) were compared using the Tukey test (JMP, 2018). Interaction results are presented in tables, while organ-based evaluation results are presented in graphs.

    RESULTS AND DISCUSSION

    Aluminum (Al) content of species (mg kg-1)
     
    According to the two-way ANOVA results for Al concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 3.

    Table 3: Al concentrations in the organs of the species.


           
    The highest Al concentrations within the organs were determined in the roots of the plants, while the lowest was in the stem parts. Among species, the highest Al was found in T. nigrescens plants.
           
    Aluminum has accumulated most in the roots of T. campestre and least in L. gebelia, most in the stem of T. nigrescens and least in V. cracca and L. gebelia, most in the leaves of T. nigrescens and least in T. arvense and most in the generative parts of T. campestre and T. nigrescens and least in L. sphaericus (Fig 3).

    Fig 3: Graph showing Al concentrations in plant organs.


     
    Chromium (Cr) content of species (mg kg-1)
     
    According to the two-way ANOVA results for Cr concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 4.

    Table 4: Cr concentrations in the organs of the species.


           
    The highest Cr concentration within organs was found in plant roots, while the lowest was in leaves. Among species, the highest Cr was determined in T. campestre plants, while the lowest Cr was determined in L. sphaericus species (Table 4).
           
    Chromium is accumulated most in the roots of T. campestre and least in L. sphaericus, most in the stems of T. nigrescens and least in L. sphaericus, most in the leaves of T. nigrescens and least in L. gebelia and most in the generative parts of T. campestre and least in L. sphaericus and L. gebelia (Fig 4).

    Fig 4: Graph showing Cr concentrations in plant organs.


     
    Copper (Cu) content of species (mg kg-1)
     
    According to the two-way ANOVA results for Cu concentrations in different legume species, species, organs and (species × organ) interaction was found to be significant (p<0.01). The resulting means and groupings are shown in Table 5.

    Table 5: Cu concentrations in the organs of the species.


           
    Among species, the highest Cu concentration was found in L. sphaericus plants, while the lowest Cu was found in L. gebelia plants (Table 5).
           
    Copper accumulated most in the roots of V. cracca and least in T. nigrescens and L. gebelia; most in the stems of L. sphaericus and least in T. nigrescens; most in the leaves of L. sphaericus and T. campstre and least in L. gebelia; and most in the generative parts of V. cracca and least in L. gebelia (Fig 5).

    Fig 5: Graph showing Cu concentrations in plant organs.


     
    Iron (Fe) content of species (mg kg-1)
     
    According to the two-way ANOVA results for Fe concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 6.

    Table 6: Fe concentrations in the organs of the species.


           
    The highest Fe concentration within organs was found in plant roots, while the lowest was in stems. Among species, the highest Fe was found in T. campestre and T. nigrescens  plants, while the lowest Fe was found in L. sphaericus and L. gebelia species (Table 6).
           
    In the roots, T. campestre accumulated the most, while L. sphaericus and L. gebelia accumulated the least; in the stem, T. nigrescens accumulated the most, while V. cracca and L. gebelia accumulated the least; in the leaves, T. nigrescens accumulated the most, while L. sphaericus accumulated the least. T. arvense and L. gebelia and in its generative parts, it accumulated the most T. nigrescens and the least L. sphaericus species (Fig 6).  

    Fig 6: Graph showing Fe concentrations in plant organs.


     
    Manganese (Mn) content of species (mg kg-1)
     
    According to the two-way ANOVA results for Mn concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 7.

    Table 7: Mn concentrations in the organs of the species.


           
    The highest Mn content within the organs was found in the leaves of the plants, while the lowest was in the stems. Among species, the highest Mn was found in T. campestre plants, while the lowest Mn was determined in L. sphaericus, T. arvense and V. cracca species (Table 7).
           
    Manganese accumulated most in the roots of T. campestre and least in L. sphaericus and L. gebelia; most in the stems of T. nigrescens and least in V. cracca; most in the leaves of T. campestre and least in T. arvense; and most in the generative parts of T. campestre and least in L. sphaericus (Fig 7).  

    Fig 7: Graph showing Mn concentrations in plant organs.


     
    Nickel (Ni) content of species (mg kg-1)
     
    According to the two-way ANOVA results for Ni concentrations in different legume species, species, organs and the interaction (species × organ) were found to be significant (p<0.01). The resulting means and groupings are shown in Table 8.

    Table 8: Ni concentrations in the organs of the species.


           
    The highest Ni content within organs was found in plant roots, while the lowest was in leaves and stems. Among species, the highest Ni was found in T. campestre plants, while the lowest Ni was found in L. sphaericus species (Table 8).
           
    Nickel accumulated most in the roots of T. campestre and least in L. sphaericus; most in the stems and leaves of T. nigrescens and least in L. sphaericus; and most in the generative parts of T. campestre and least in L. sphaericus (Fig 8).

    Fig 8: Graph showing Ni concentrations in plant organs.


     
    Assessment of phytoremediation capacities of legume species (TF and BCF)
     
    The TF, BCFroot and BCFshoot values for the examined elements of the species plant are given in Table 9-14.

    Table 9: TF and BCF evaluations for Lathyrus sphaericus.



    Table 10: TF and BCF evaluations for Trifolium campestre.



    Table 11: TF and BCF evaluations for Trifolium nigrescens.



    Table 12: TF and BCF evaluations for Trifolium arvense.



    Table 13: TF and BCF evaluations for Vicia cracca.



    Table 14: TF and BCF evaluations for Lotus gebelia.


           
    In Lathyrus sphaericus, TF>1 was found for Cr, Fe, Mn, Ni; BCFroot>1 for Cu; and BCFshoot>1 for Cr, Cu (Table 9).
           
    Trifolium campestre     did not exhibit TF>1 for any element, but BCFroot>1 was determined for Cr, Cu, Ni and BCFshoot>1 was determined for Cr and Cu (Table 10).
           
    In Trifolium nigrescens, TF>1 was determined for all elements, while BCFroot and BCFshoot>1 were determined for Cr, Cu (Table 11).
           
    Trifolium arvense     did not find TF>1 for any element, but BCFroot and BCFshoot>1 were determined for Cr and Cu (Table 12).
           
    In Vicia cracca, TF>1 was calculated for Cr, Fe, Mn and Ni while BCFroot and BCFshoot>1 were calculated for Cr and Cu (Table 13).
           
    In Lotus gebelia, TF>1 was calculated for Al, Cr and Mn elements and BCFroot and BCFshoot>1 were calculated for Cr and Cu elements (Table 14).
           
    The uptake of metals by plants is influenced by several factors such as soil metal concentrations, cation exchange capacity, soil pH, organic matter content, plant species and varieties and plant age. However, the main factor is the concentration of metals in the soil and hence the existing environmental conditions (Annan et al., 2013).
           
    Shahidi et al., (1999) reported that the vegetative parts of L. maritimus contained more Al than the generative parts. In this study, similar to the studies of Shahidi et al., (1999), the vegetative parts (leaves and stem) of L. sphaericus accumulated about 3.5 times more Al than the generative parts (seeds and pods). The study of Wheeler and Dodd (1995) with 15 different Trifolium and 6 different Lotus species is not similar to this study in terms of concentration. It is thought that the reasons for this may be related to the Al concentrations in the study areas. However, if a comparison is made between Trifolium and Lotus species, Trifolium species had higher Al, Cu and Fe content than Lotus species in Wheeler and Dodd (1995) study, as in this study.  In the leaves of V. cracca, about 2.2 times more Al accumulation was observed than in the stem. Similarly, Kolesnichenko et al., (2018) found about 2.1 times more Al in the leaves of V. cracca than in the stem.
           
    Chromium concentration (1.21 mg kg-1) determined for the generative parts of Lathyrus sphaericus in this study was similar to the Cr concentration (1.10 mg kg-1) measured by Kodirova et al., (2024) in seeds of twelve different Lathyrus genotypes. Chromium concentrations of Trifolium species varied between 6.94-23.34 mg kg-1. Gounden et al., (2018) reported that the maximum concentration for Cr was 6 mg kg-1 in their study with five different Trifolium species. Chromium was determined as 2.24 mg kg-1 in shoots and 2.00 mg kg-1 in roots of Lotus gebelia; Sujkowska-Rybkowska et al. (2020) determined Cr content of Lotus corniculatus as 5.4 mg kg-1 in shoots and 20.5 mg kg-1 in roots.
           
    Shahidi et al., (1999) reported that the vegetative parts of Lathyrus maritimus contained more Fe than the generative parts. In this study, similar to the studies of Shahidi et al., (1999), the vegetative parts of Lathyrus sphaericus contained more Fe than the generative parts. In this study, Fe accumulation in the leaves of Vicia cracca was observed to be approximately 2.5 times higher than in the stem, while in Kolesnichenko et al., (2018), Fe accumulation in the leaves of Vicia cracca was observed to be approximately 3.1 times higher than in the stem.
           
    The Mn level measured in the leaves of Lathyrus maritimus by Maslennikov et al., (2020) is similar to the Mn level measured in the leaves of Lathyrus sphaericus in this study.  Wheeler and Dodd (1995), in their study with 6 different Lotus species, found that the average Mn concentration in the above-ground organs was similar to the average Mn concentration in the above-ground organs of Lotus gebelia, but the average above-ground Mn concentrations of Trifolium species were higher than those of Trifolium species in this study. While Mn accumulation in the leaves of Vicia cracca was observed approximately 3.6 times higher than in the stem, Kolesnichenko et al., (2018) observed Mn accumulation in the leaves of Vicia cracca plants approximately 4.8 times higher than in the stem.
           
    Lathyrus sphaericus     transported Ni to the above-ground organs. However, Jeddou et al., (2017) reported that Ni in Lathyrus ochrus had limited transport to the upper parts and nickel was mostly accumulated in the roots. Nickel concentrations of Trifolium species were found to be similar (<10 mg kg-1 Ni) to the study of Gounden et al., (2018) with 5 different Trifolium species.
           
    The Ni concentration in the leaves and stems of Vicia cracca is similar to the Ni concentration in the leaves and stems of Vicia cracca in the study of Kolesnichenko et al., (2018).  Nickel content of L. gebelia was determined as 1.35 mg kg-1 in shoots and 2.25 mg kg-1 in roots; Sujkowska-Rybkowska et al. (2020) determined Ni content of Lotus corniculatus as 59.5 mg kg-1 in shoots and 167.1 mg kg-1 in roots. Saruhan et al., (2012) reported the Ni content of Lotus corniculatus in control plants similar to this study.
           
    Plants having TF and especially BCF values less than one (TF<1) are not suitable for phytoextraction (Fitz and Wenzel, 2002), while TF>1 is a decisive factor in the classification of plant species for phytoremediation (Chanu and Gupta, 2016). However, plants having high bioconcentration factor and low translocation factor have phytostabilization potential (Yoon et al., 2006).
           
    Unlike the value obtained for Ni (TF>1) in this study, Jeddou et al., (2017) reported that BCF and TF values were below 1 in Lathyrus ochrus. Wheeler and Dodd (1995) reported that the TF values obtained for Al (0.4), Cu (0.3), Fe (0.2) and Mn (0.7) were below 1 in their study with fifteen different Trifolium species. In this study, TF<1 was found for T. campestre and T. arvense, which was similar to the results of Wheeler and Dodd (1995), but for Trifolium nigrescens, contrary to the results of the researchers, Al, Cu, Fe and Mn were found to be TF>1. TFCu<1 was found in V. cracca and Saadaoui et al., (2022) found TF<1 (Vicia faba L. cv. Mamdouh: TFshoot 0.32, TFflower 0.18) in one of two different Vicia plants and TF>1 (Vicia faba L. cv. Badii: TFshoot 1.38, TFflower 1.48) in the other. Sujkowska-Rybkowska et al. (2020) reported TF values <1 for Cr (contrary to the results of this study) and Ni (similar to the results of this study) of Lotus corniculatus. The TF values obtained by Wheeler and Dodd (1995) for Al, Cu, Fe and Mn (<1) were found to be different from the TFMn,Al values obtained in this study, but similar to the TFFe,Cu  values.

    CONCLUSION

    The soils of the study area did not exceed the limit according to the toxic metal limit values allowed by WHO, except for Mn (allowed 80 mg kg-1). Considering the values determined in the above-ground organs of plants such as stems and leaves, the permissible limit values for Mn, Cu and Ni were not exceeded, only Cr and Fe concentrations exceeded the limit (Cr: 5 mg kg-1 and Fe: 450 mg kg-1) toxic metal level in some species. Since TFCr, Fe, Mn, Ni>1 in L. sphaericus and V. cracca, TFAl, Cu, Cr, Fe, Mn, Ni>1 in T. nigrescens and TFAl, Cu, Cr, Mn>1 in L. gebelia, these legume species are important for phytoextraction. For Cr metal, the BCF root value was 38.91 in T. campestre and this high value revealed the potential of this species for phytostabilization of Cr contaminated soils. Among these legume species collected from the mine site, those with TF>1 are promising for phytoremediation. Due to the high levels of Fe and Cr metals in the above-ground organs of some legume species, it is recommended that livestock grazing should be done more carefully in these areas.

    ACKNOWLEDGEMENT

    This article was produced from Çağrı ŞAHİN's master’s thesis. We would like to thank Dr. Mihriban AHISKALI for her help and support in the identification of the plants and the drawing of the visuals in the graphs (characteristic morphological parts specific to the legume family).

    CONFLICT OF INTEREST

    The authors declare that there is no conflict of interest. I confirm that there are no conflicts of interest regarding this manuscript.

    REFERENCES


    1. Annan, K., Dickson, R.A., Amponsah, I.K. and Nooni, I.K. (2013). The heavy metal contents of some selected medicinal plants sampled from different geographical locations. Pharmacognosy Research. 5(2): 103.

    2. Ashraf, S., Ali, Q., Zahir, Z.A., Ashraf, S. and Asghar, H.N. (2019). Phytoremediation: Environmentally sustainable way for reclamation of heavy metal polluted soils. Ecotoxicology and Environmental Safety. 174: 714-727.

    3. Brahma, S., Lolesh, P., Barnali, S., Rajesh, C. and Dipankar, S. (2026). Heavy metal contamination in vegetables and their amelioration: A review. Agricultural Reviews. 47(1): 1-12. doi: 10.18805/ag.R-2737.

    4. Chamba-Eras, I., Griffith, D.M., Kalinhoff, C., Ramírez, J. and Gázquez, M.J. (2022). Native hyperaccumulator plants with differential phytoremediation potential in an artisanal gold mine of the ecuadorian amazon. Plants. 11(9): 1186.

    5. Chanu, L.B. and Gupta, A. (2016). Phytoremediation of lead using ýpomoea aquatica forsk. in hydroponic solution. Chemosphere.  156: 407-411.

    6. Davis, P.H. (1965-1985). Flora of Turkey and the East Aegean Islands. Vol. 1-9. Edinburgh University Press., Edinburgh.

    7. Divya V.U., Sindhu P.V. and Aiswarya N.S. (2024). Agromining: Agroremediation for heavy metal contaminated ecosystems: A review. Bhartiya Krishi Anusandhan Patrika. 39(1): 51-55. doi: 10.18805/BKAP682. 

    8. Fashola, M.O., Ngole-Jeme, V.M. and Babalola, O.O. (2016). Heavy metal pollution from gold mines: environmental effects and bacterial strategies for resistance. International Journal of Environmental Research and Public Health. 13(11): 1047.

    9. Favas, P., Pratas, J., Varun, M., Souza, R. and Paul, M. (2014). Phytoremediation of Soils Contaminated with Metals and Metalloids at Mining Areas: Potential of Native Flora. In Environmental Risk Assessment of Soil Contaminatio; IntechOpen: London, UK, pp. 485-517.

    10. Fitz, W.J. and Wenzel, W.W. (2002). Arsenic transformations in the soil-rhizosphere-plant system: Fundamentals and potential application to phytoremediation. Journal of Biotechnology. 99(3): 259-278. 

    11. Gounden, T., Moodley, R. and Jonnalagadda, S.B. (2018). Elemental analysis and nutritional value of edible Trifolium (clover) species. Journal of Environmental Science and Health. Part B, 53(8): 487-492.

    12. Gökdere, H., Şahin, Ç., Erdem, S., Asutay, Z. and Arıgrekin, A. (2025). Determination of some trace element content of gum tragacanth (Astragalus gummifer Labill.) growing near mining sites. Agro Science and Technology Journal. 1(1): 1-8.

    13. Güner, A., Aslan, S., Ekim, T., Vural, M. and ve Babaç, M.T. (2012). Türkiye Bitkileri Listesi (Damarlı Bitkiler). Nezahat Gökyiğit Bahçesi ve Flora Araştırmaları Derneği Yayını. İstanbul.

    14. Jeddou, K., Vogıatzı, C., Stamatakıs, A., Grıgorakıs, S. and Sımantırıs, N.L. (2017). Heavy Metals Accumulation in Plant Tissues of Satureja Cretica and Lathyrus Ochrus Grown in Contaminated Soils. 15th International Conference on Environmental Science and Technology Rhodes, Greece, 31 August to 2 September 2017.

    15. JMP, (2018). Statistical Discovery from SAS, USA.

    16. Kodirova, S., Amanov, B., Muminov, K. H., Abdiyev, F., Buronov, A., Tursunova, N. and Kurbanbayev, I. (2024). Physıologıcal and bıochemıcal parameters of the exotıc specıes of grass pea (Lathyrus satıvus L.). Sabrao Journal of Breeding and Genetics. 56(4): 1513-1523.

    17. Kolesnichenko, L.G., Shepeleva, L.F., Rabtsevich, E.S., Ledeneva, E.A., Teslinova, M.S., Rozhkova-Timina, I.O. and Kirpotin, S.N. (2018). Elemental Chemical Composition of Some Meadow Plants in the Middle Ob Basin. In: IOP Conference Series: Earth and Environmental Science. IOP Publishing. 201(1): 012009.

    18. Lin, G., Zeng, B., Li, J., Wang, Z., Wang, S., Hu, T. and Zhang, L. (2023). A systematic review of metal organic frameworks materials for heavy metal removal: Synthesis, applications and mechanism. Chemical Engineering Journal. 460: 141710.

    19. Maslennikov, P., Golovina, E. and Artemenko, A. (2020). Ecological and geochemical conditions for the accumulation of antioxidants in the leaves of Lathyrus maritimus (L.) bigel. Plants. 9(6): 746.

    20. Miller, R.O. (1998). Microwave Digestion of Plant Tissue in a Closed Vessel. In: [Kaira, Y.P.  (Eds)] Handbook of Reference Methods for Plant Analysis CRC Boca Raton pp. 69-74.

    21. Ortakcı, G. (2020). Elazığ (Maden)'da işletmesi devam eden ve Amasya (Gümüşhacıköy)'da işletmesi bitmiş olan maden sahalarındaki bazı bitkilerde ağır metal bioakümülasyonları. Yüksek Lisans Tezi. Amasya Üniversitesi.

    22. Paul, I.A.R., Dhivyadharsini, D. and Mathivadhana, K.S. (2021). Rehabilitation of heavy metal contamination and soil erosion through ıntegrated management. Agricultural Reviews. 42(3): 300-307. doi: 10.18805/ag.R-2052.

    23. Rama, K., Nishita, O., Sadiqa, A. and Sonal, B. (2021). A review on heavy metal contamination at mining sites and remedial techniques. IOP Conference Series: Earth and Environmental Science. 796: 012013.

    24. Saadaoui, W., Gamboa-Rosales, H., Sifuentes-Gallardo, C., Durán- Muñoz, H., Abrougui, K., Mohammadi, A. and Tarchoun, N. (2022). Effects of lead, copper and cadmium on bioaccumulation and translocation factors and biosynthesis of photosynthetic pigments in Vicia faba L.(broad beans) at different stages of growth. Applied Sciences. 12(18): 8941.

    25. Saruhan, V., Gul, I., Kusvuran, A. and Aydin, F. (2012). Effects of sewage sludge used as fertilizer on heavy metal contents of bird’s-foot trefoil (Lotus corniculatus L.) and soil.  Asian Journal of Chemistry. 24(2): 866.

    26. Sevencan, T.A. (2022). Metal stresindeki bazı tıbbi bitkilerin fitoremediasyon potansiyelleri ve biyokütle kullanımları. Doktora tezi. İstanbul Üniversitesi.

    27. Shahidi, F., Chavan, U.D., Bal, A.K. and McKenzie, D.B. (1999). Chemical composition of beach pea (Lathyrus maritimus L.) plant parts. Food Chemistry. 64(1): 39-44. 

    28. Sönmez, O. and Kılıç, F.N. (2021). Heavy metal pollution in soil and removal methods. Turkish Journal of Agricultural Engineering Research. 2(2): 493-507.

    29. Sujkowska-Rybkowska, M., Kasowska, D., Gediga, K., Banasiewicz, J. and Stêpkowski, T. (2020). Lotus corniculatus-rhizobia symbiosis under Ni, Co and Cr stress on ultramafic soil. Plant and Soil. 451: 459-484.

    30. Sürmen, B., Kılıç, D.D., Kutbay, H.G. and Tuna, E.E. (2019). Doğal olarak yayılış gösteren Lepidium draba L. türünün fitoremediasyon yönteminde kullanılabilirliğinin araştırılması. Avrupa Bilim ve Teknoloji Dergisi. 17: 491-499. 

    31. Sahin, Ç. (2025). Demir Madeni İşletmesi Çevresindeki Doğal Alanlarda Yayılış Gösteren Yem Bitkisi Türlerinin Ağır Metal İçeriklerinin Araştırılması ve Fitoremediasyon Kapasitelerinin Değerlendirilmesi: Bingöl-Avnik Örneği. Yüksek Lisans Tezi. Bingöl Üniversitesi.

    32. Uzun, O. and Bollukcu, P. (2009). Bartın merkez ilçe sınırları içinde yer alan açık ocak işletmelerinin peyzaj onarımı-biyolojik onarım açısından değerlendirilmesi. Bartın Orman Fakültesi Dergisi I. Ulusal Batı Karadeniz Ormancılık Kongresi Bildiriler Kitabı. Özel Sayı. ISSN: 1302-0943.

    33. Wheeler, D.M. and Dodd, M.B. (1995). Effect of aluminium on yield and plant chemical concentrations of some temperate legumes. Plant and Soil. 173: 133-145.

    34. WHO/FAO (2007). Joint FAO/WHO Food Standard Programme Codex Alimentarius Commission 13th Session. Report of the Thirty-Eight Session of the Codex Committee on Food Hygiene, Houston, United States of America (07/ 30/13).

    35. Yan, A., Wang, Y., Tan, S.N., Yusof, M.L.M., Ghosh, S. and Chen, Z. (2020). Phytoremediation: a promising approach for revegetation of heavy metal-polluted land. Frontiers in Plant Science. 11: 359.

    36. Yang, S., Liang, S., Yi, L., Xu, B., Cao, J., Guo, Y. and Zhou, Y. (2014). Heavy metal accumulation and phytostabilization potential of dominant plant species growing on manganese mine tailings. Frontiers of Environmental Science and Engineering. 8: 394-404.

    37. Yoon, J., Cao, X., Zhou, Q. and Ma, L.Q. (2006). Accumulation of Pb, Cu and Zn in native plants growing on a contaminated florida site. Science of the Total Environment. 368(2-3): 456-464.
    In this Article
      Contact us
      Follow us
      Published In
      Legume Research

      Editorial Board

      View all (0)