Research Article |
Corresponding author: Béla Tóthmérész ( tothmerb@gmail.com ) Academic editor: Michael Kleyer
© 2019 Dávid Tőzsér, Béla Tóthmérész, Sándor Harangi, Edina Baranyai, Gyula Lakatos, Zoltán Fülöp, Edina Simon.
This is an open access article distributed under the terms of the Creative Commons Attribution License (CC BY 4.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Citation:
Tőzsér D, Tóthmérész B, Harangi S, Baranyai E, Lakatos G, Fülöp Z, Simon E (2019) Remediation potential of early successional pioneer species Chenopodium album and Tripleurospermum inodorum. Nature Conservation 36: 47-69. https://doi.org/10.3897/natureconservation.36.32503
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Remediation with plants is a technology used to decrease soil or water contamination. In this study we assessed the remediation potential of two weed species (Chenopodium album and Tripleurospermum inodorum) in a moderately metal-contaminated area. Metal concentrations were studied in roots, stems and leaves, in order to assess correlations in metal concentrations between those in soil and plants. Furthermore, we calculated bioaccumulation factor (BAF), bioconcentration factor (BCF) and translocation factor (TF) values to study the accumulation of metals from soil to plants and translocation within plants. We found correlation in metal concentrations between soil and plants. The metal accumulation potential was low in both species, indicating low BAF and BCF values. In contrast, high TF values were found for Mn, Ni, Sr, Zn, Ba, Fe, Cu and Pb in C. album, and for Fe, Mn, Ni, Zn and Sr in T. inodorum. Our results demonstrated that the potential of C. album and T. inodorum might be limited in phytoextraction processes; however, when accumulated, metals are successfully transported to aboveground plant organs. Thus, to achieve the efficient remediation of metal-contaminated soils, removal of the aboveground plant organs is recommended, by which soil disturbance can also be avoided.
bioaccumulation, trace elements, phytoextraction, pollution, translocation
Unsustainable land use leads to the qualitative and quantitative deterioration of soils, which is an urgent worldwide problem (
Field application for phytoextraction purposes usually involves fast growing species characterized by high biomass production (
Among weeds with these characteristics, information on metal accumulation in Chenopodiaceae species has been widely reported. In this family, annual, stress tolerant Chenopodium album (L.) (Lamb’s quarters) is one of the most studied species (
Tripleurospermum inodorum (L.) Sch. Bip. (Scentless mayweed) is an annual, and in some regions overwintering species (
The aim of this study was to analyze the metal accumulation and translocation potential of two common, early successional pioneer weeds, Chenopodium album and Tripleurospermum inodorum, grown in moderately metal-contaminated soils. We explored the difference between the species in terms of their metal concentrations among plant organs and among the differently contaminated parts of the study area. Moreover, accumulation and translocation factors were used to evaluate whether the species, or any of their plant organs (root, stem, shoot (= stem + leaf) and leaf) were capable of accumulating metals in high concentrations. We hypothesized that C. album would show excellent remediation potential (high BAF, BCF and TF values). Based on the metal accumulation characteristics of related species, T. inodorum was also expected to have good remediation potential.
The study area was in the suburban area of Debrecen, Hungary. For the period between 1971 and 2000 the average annual temperature was 10.0 °C, the average annual rainfall was 549 mm and the average annual sunshine duration slightly exceeded 2000 hours (OMSZ n.d.). The 26 ha study area (Lovász-zug, 47°29.0'N; 21°47.3'E) used to function as a series of settling ponds in the communal wastewater treatment process of the city. Secondary biological purification was performed in the area from the 1930s until the 1950s, which was later supplemented by physical treatment. In the initial years of operation, earth deflector walls were formed to facilitate the wastewater stream; thus, the efficiency of purification was greatly increased. From the early 1970s, secondary treatment remained as the only function of the pond system, due to the establishment and continuous development of a modern wastewater treatment plant. The pond system had ceased to operate by the early 2000s (
Soil samples were collected with a 50-mm Dutch soil auger from the three differently contaminated parts of the study area (northern – moderately contaminated part 1; middle – strongly contaminated part 2; southern – moderately contaminated part 3, after
To measure the pH of soil solutions, soil samples (5 g) were put into plastic tubes, complemented with 20 ml of deionized water, shaken and left to settle overnight. Then, pH values were determined with a Hach HQ 40d portable multimeter. For the elemental analysis, we homogenized air-dried soil samples (0.2 g with accuracy of 0.005 g) with agate mortar, put into 100-ml glass beakers and dried at 105 °C overnight. Samples were digested in 4 ml 65% (m/m) HNO3 and 0.5 ml 30% (m/m) H2O2 on hot plates until total evaporation of the chemicals. Then, 5 ml of 3×-deionized water was added to the dried samples. Prior to pouring the solution into plastic tubes, we put glass beakers into an ultrasonic water bath to yield the sample residues which adhered to beaker walls. Then, samples were diluted to 10 ml using 1% (m/m) nitric acid. The following elements were analyzed with MP-AES (Microwave Plasma-Atomic Emission Spectrometry): Al, Ba, Ca, Cd, Cr, Cu, Fe, K, Mg, Mn, Na, Ni, Pb, Sr and Zn. These elements are of various levels of environmental concern; we refer to them as “metals” throughout the study, based on
Plant individuals were collected from the differently contaminated parts of the study area during early September 2015. We selected the plant sampling date to assess the metal accumulation potential of the species by the end of the vegetation period. Five individuals of C. album and T. inodorum were collected from a radius of 10 meters around each soil core. We put all samples into plastic packages and stored them at +4 °C until the laboratory process. In the laboratory, individuals were washed and plant organs such as roots, stems and leaves were separated. Each plant organ was air-dried in a paper bag for 24 hours. After this, plant organs were dried at 60°C for 48 hours.
Prior to elemental analyses, 0.2 g of plant samples (with an accuracy of 0.005 g) were homogenized with agate mortar. Then, plant samples were digested in 4 ml 65% (m/m) HNO3 and 0.5 ml 30% (m/m) H2O2. We put the solutions into glass beakers and supplemented them with 3×-deionised water to a quantity of 25 ml. After this, the solutions were put into plastic centrifuge tubes. The following metals were analyzed with MP-AES: Al, Ba, Ca, Cd, Cr, Cu, Fe, K, Mg, Mn, Na, Ni, Pb, Sr and Zn.
We used the bioaccumulation factor (BAF), bioconcentration factor (BCF) and translocation factor (TF) as widely applied indicators in assessing the remediation potential of plant species. For these factors, calculations were made for Al, Fe, Mn, Ba, Cr, Cu, Ni, Pb, Sr and Zn. The bioaccumulation factor refers to the ratio of metal concentration in shoots (Cshoot) and metal concentration in soil (Csoil) (
BAF = Cshoot/Csoil
The bioconcentration factor refers to the ratio of metal concentration in selected plant organs (also calculated for stem and leaves separately) (Cplant organ) and metal concentration in the soil (Csoil) (
BCF = Cplant organ/Csoil.
The translocation factor refers to the ratio of metal concentration in selected aboveground plant organs (Caboveground plant organ) and metal concentration in roots (Croots) (
TF = Caboveground plant organ/Croots.
For the statistical analyses the natural logarithms (ln) of the concentration values were used. Levene’s Test was used for analyzing the homogeneities of variances. The Generalized Linear Model (GLM) was used to test significant differences (p < 0.05) between the metal concentrations (I) of plants, (II) of plant organs and (III) of parts of the study area with different contamination levels. To study the differences in metal concentration between plant organs, we used a principal component analysis (PCA). To analyze the correlation in metal concentrations between soil samples and plant organs, Pearson’s correlation coefficient (r) was calculated and significance was assessed at the 0.05 level.
The Generalized Linear Model showed that there were significant differences (p < 0.05) in Al, Ca, Fe, K, Mg, Mn, Na, Ba and Zn among the differently contaminated parts of the study area. Soil pH did not differ significantly between the three parts of the study area (Table
Soil pH and metal concentrations in samples from the study area (mean ± SE).
Part of the study area | |||
---|---|---|---|
Northern | Middle | Southern | |
pH | 7.7 ± 0.1 | 7.7 ± 0.1 | 7.8 ± 0.1 |
Al | 5.3 ± 0.2 | 5.6 ± 0.2 | 5.7 ± 0.2 |
Ba | 70.1 ± 5.6 | 65.6 ± 4.1 | 42.6 ± 1.7 |
Ca | 31.4 ± 2.3 | 28.2 ± 2.9 | 19.5 ± 2.2 |
Cd | 0.7 ± 0.1 | 1.4 ± 0.7 | 0.7 ± 0.1 |
Cr | 129 ± 21 | 303 ± 143 | 63.3 ± 41.8 |
Cu | 35.3 ± 7.2 | 49.3 ± 13.4 | 17.6 ± 4.8 |
Fe | 10.6 ± 0.4 | 11.6 ± 0.6 | 11.2 ± 0.6 |
K | 1.1 ± 0.1 | 1.4 ± 0.1 | 1.3 ± 0.1 |
Mg | 6.2 ± 0.4 | 5.9 ± 0.3 | 5.2 ± 0.6 |
Mn | 396 ± 26 | 380 ± 11 | 339 ± 20 |
Na | 362 ± 27 | 363 ± 61 | 244 ± 24 |
Ni | 23.8 ± 1.6 | 32.1 ± 5.5 | 25.8 ± 1.6 |
Pb | 27.4 ± 4.1 | 44.3 ± 17.7 | 8.0 ± 4.3 |
Sr | 88.9 ± 7.0 | 86.4 ± 7.6 | 55.8 ± 6.3 |
Zn | 153 ± 23 | 192 ± 45 | 60.8 ± 15.3 |
There were significant differences in metal concentrations in plant organs of C. album among the differently contaminated parts of the study area (Table
Principal component biplot of metal concentrations (mg kg-1) of Chenopodium album in roots, stems and leaves. Notations: square – roots, circle – stems, triangle – leaves.
In the cases of Mg, Mn and Zn, leaves accumulated metals in significantly higher concentrations than roots and stems in all the three parts of the study area. In the cases of Fe and Cu, leaves accumulated significantly higher concentrations of metals than roots and stems only in the strongly contaminated middle part. In the cases of Ca, K and Sr, leaves accumulated the highest concentrations of metals, as well; however, we found significant differences between leaves and stems and also between stems and roots. In the cases of Al and Ba, leaves and roots accumulated metals in significantly higher concentrations than stems. In the cases of Cr and Ni, accumulations in leaves and roots were comparable. Cd concentrations were always below the detection limit; thus, this metal was excluded from further analyses. In the cases of Na and Pb, significant differences were not found among plant organs within the parts of the study area (Suppl. material
We also studied metal concentrations in selected plant organs among the differently contaminated parts of the study area. We found higher metal concentrations in the southern part compared to the northern and middle parts of the study area (Table
Metal concentrations in plant organs of Chenopodium album among the three parts of the study area (mean ± SE).
Part of the study area | |||||||||
---|---|---|---|---|---|---|---|---|---|
Northern | Middle | Southern | |||||||
Root | Stem | Leaf | Root | Stem | Leaf | Root | Stem | Leaf | |
Al | 5.0 ± 0.6 | 2.0 ± 0.54 | 3.5 ± 0.6 | 6.4 ± 2.1 | 1.1 ± 0.2 | 2.9 ± 0.3 | 17.6 ± 3.9 | 1.2 ± 0.2 | 5.2 ± 1.8 |
Ba | 0.1 ± 0.01 | 0.1 ± 0.01 | 0.2 ± 0.01 | 0.1 ± 0.02 | 0.1 ± 0.01 | 0.3 ± 0.02 | 0.2 ± 0.03 | 0.1 ± 0.01 | 0.2 ± 0.02 |
Ca | 0.01 ± 0.01 | 0.2 ± 0.02 | 0.9 ± 0.03 | 0.08 ± 0.01 | 0.3 ± 0.1 | 1.0 ± 0.06 | 0.07 ± 0.01 | 0.1 ± 0.02 | 0.9 ± 0.09 |
Cr | 0.1 ± 0.01 | 0.03 ± 0.01 | 0.1 ± 0.02 | 0.1 ± 0.03 | 0.03 ± 0.01 | 0.02 ± 0.01 | 0.1 ± 0.03 | 0.02 ± 0.01 | 0.03 ± 0.01 |
Cu | 0.4 ± 0.02 | 2.0 ± 1.7 | 0.5 ± 0.02 | 0.4 ± 0.01 | 0.3 ± 0.01 | 0.5 ± 0.02 | 0.4 ± 0.01 | 0.4 ± 0.01 | 12.2 ± 11.7 |
Fe | 4.9 ± 0.6 | 5.4 ± 3.3 | 6.6 ± 0.5 | 5.9 ± 1.8 | 2.1 ± 0.2 | 6.5 ± 0.5 | 15.0 ± 3.4 | 2.0 ± 0.2 | 29.6 ± 23.6 |
K | 0.9 ± 0.04 | 2.2 ± 0.1 | 2.9 ± 0.09 | 1.0 ± 0.03 | 2.6 ± 0.2 | 3.1 ± 0.08 | 1.0 ± 0.05 | 2.6 ± 0.2 | 3.0 ± 0.1 |
Mg | 0.1 ± 0.01 | 0.1 ± 0.01 | 1.0 ± 0.04 | 0.1 ± 0.01 | 0.1 ± 0.03 | 0.9 ± 0.03 | 0.1 ± 0.01 | 0.1 ± 0.02 | 1.2 ± 0.06 |
Mn | 0.5 ± 0.03 | 0.5 ± 0.03 | 1.3 ± 0.1 | 0.6 ± 0.1 | 0.6 ± 0.04 | 1.7 ± 0.1 | 1.3 ± 0.2 | 0.9 ± 0.1 | 4.9 ± 1.5 |
Na | 0.04 ± 0.01 | 0.01 ± 0.01 | 0.02 ± 0.02 | 0.03 ± 0.01 | 0.1 ± 0.1 | 0.01 ± 0.0 | 0.04 ± 0.02 | 0.03 ± 0.02 | 0.01 ± 0.01 |
Ni | 0.03 ± 0.01 | 0.02 ± 0.01 | 0.1 ± 0.1 | 0.04 ± 0.01 | 0.1 ± 0.04 | 0.04 ± 0.01 | 0.1 ± 0.02 | 0.03 ± 0.01 | 0.04 ± 0.01 |
Pb | 0.1 ± 0.01 | 0.1 ± 0.01 | 0.03 ± 0.01 | 0.1 ± 0.04 | 0.1 ± 0.01 | 0.03 ± 0.01 | 0.1 ± 0.01 | 0.1 ± 0.01 | 0.1 ± 0.01 |
Sr | 0.9 ± 0.04 | 1.6 ± 0.1 | 2.8 ± 0.1 | 0.8 ± 0.04 | 1.8 ± 0.2 | 3.0 ± 0.2 | 1.0 ± 0.1 | 1.6 ± 0.1 | 3.2 ± 0.2 |
Zn | 1.7 ± 0.1 | 1.5 ± 0.1 | 5.9 ± 0.3 | 1.6 ± 0.1 | 1.4 ± 0.1 | 5.7 ± 0.5 | 1.3 ± 0.1 | 1.1 ± 0.1 | 2.8 ± 0.2 |
We also found significant differences in metal concentrations in plant organs of T. inodorum among the differently contaminated parts of the study area (Table
Principal component biplot of metal concentrations (mg kg-1) of Tripleurospermum inodorum in roots, stems and leaves. Notations: square – roots, circle – stems, triangle – leaves.
Concentrations of Al, Ba, Cr and Pb were significantly the highest in roots, while concentrations of Ca, K, Mg and Mn were the highest in leaves. In the cases of Fe, Na, Cu, Ni and Sr, the highest concentrations were accumulated in roots and leaves. We found the lowest concentrations of these metals in stems. The concentration of Zn was comparable in all the plant organs, with only negligible differences among them. The concentration of Cd was below the detection limit in all of the cases; thus, this metal was excluded from further analyses.
Generally lower concentrations were found in the northern part compared to the middle and southern parts of the study area (Table
Metal concentrations in plant organs of Tripleurospermum inodorum among the three parts of the study area (mean ± SE).
Part of the study area | |||||||||
---|---|---|---|---|---|---|---|---|---|
Northern | Middle | Southern | |||||||
Root | Stem | Leaf | Root | Stem | Leaf | Root | Stem | Leaf | |
Al | 19.5 ± 2.8 | 7.2 ± 2.0 | 11.0 ± 1.3 | 37.4 ± 6.9 | 7.5 ± 1.3 | 6.8 ± 0.9 | 28.3 ± 3.4 | 6.6 ± 0.8 | 16.2 ± 5.1 |
Ba | 0.4 ± 0.03 | 0.2 ± 0.02 | 0.2 ± 0.01 | 0.7 ± 0.1 | 0.3 ± 0.02 | 0.2 ± 0.01 | 0.5 ± 0.1 | 0.3 ± 0.02 | 0.2 ± 0.02 |
Ca | 0.2 ± 0.02 | 0.1 ± 0.01 | 0.8 ± 0.3 | 0.2 ± 0.02 | 0.2 ± 0.02 | 0.6 ± 0.01 | 0.2 ± 0.03 | 0.1 ± 0.02 | 0.6 ± 0.06 |
Cr | 0.2 ± 0.04 | 0.2 ± 0.04 | 0.1 ± 0.02 | 0.4 ± 0.1 | 0.1 ± 0.02 | 0.1 ± 0.01 | 0.2 ± 0.03 | 0.1 ± 0.01 | 0.1 ± 0.02 |
Cu | 0.6 ± 0.04 | 0.3 ± 0.02 | 0.8 ± 0.1 | 0.6 ± 0.1 | 0.3 ± 0.01 | 0.7 ± 0.03 | 0.5 ± 0.04 | 0.3 ± 0.04 | 22.2 ± 21.5 |
Fe | 17.3 ± 2.5 | 7.1 ± 1.9 | 12.2 ± 1.2 | 32.6 ± 6.0 | 7.0 ± 1.1 | 9.2 ± 1.0 | 22.6 ± 2.6 | 5.8 ± 0.9 | 60.4 ± 47.8 |
K | 0.7 ± 0.07 | 0.6 ± 0.05 | 1.5 ± 0.1 | 0.9 ± 0.04 | 0.6 ± 0.05 | 1.8 ± 0.05 | 0.7 ± 0.04 | 0.7 ± 0.04 | 1.6 ± 0.1 |
Mg | 0.1 ± 0.01 | 0.03 ± 0.01 | 0.3 ± 0.06 | 0.1 ± 0.01 | 0.04 ± 0.01 | 0.2 ± 0.03 | 0.1 ± 0.01 | 0.04 ± 0.01 | 0.2 ± 0.01 |
Mn | 1.5 ± 0.2 | 1.4 ± 0.2 | 3.6 ± 0.6 | 2.5 ± 0.3 | 3.2 ± 0.6 | 4.9 ± 0.5 | 3.1 ± 0.4 | 3.8 ± 0.7 | 9.6 ± 1.3 |
Na | 0.2 ± 0.01 | 0.1 ± 0.01 | 0.3 ± 0.3 | 0.1 ± 0.01 | 0.03 ± 0.01 | 0.1 ± 0.07 | 0.2 ± 0.02 | 0.1 ± 0.01 | 0.02 ± 0.01 |
Ni | 0.1 ± 0.01 | 0.1 ± 0.1 | 0.1 ± 0.01 | 0.2 ± 0.02 | 0.1 ± 0.02 | 0.1 ± 0.02 | 0.2 ± 0.01 | 0.1 ± 0.01 | 0.1 ± 0.02 |
Pb | 0.2 ± 0.1 | 0.1 ± 0.01 | 0.1 ± 0.03 | 0.1 ± 0.02 | 0.04 ± 0.01 | 0.03 ± 0.01 | 0.1 ± 0.01 | 0.03 ± 0.01 | 0.1 ± 0.01 |
Sr | 1.7 ± 0.1 | 1.2 ± 0.1 | 1.7 ± 0.1 | 1.7 ± 0.1 | 1.3 ± 0.1 | 1.5 ± 0.1 | 1.6 ± 0.1 | 1.4 ± 0.1 | 1.9 ± 0.2 |
Zn | 2.6 ± 0.2 | 1.9 ± 0.2 | 2.6 ± 0.4 | 2.9 ± 0.2 | 2.7 ± 0.3 | 2.9 ± 0.3 | 1.4 ± 0.1 | 1.4 ± 0.1 | 1.7 ± 0.2 |
In the northern part of the study area, no significant correlation was found in metal concentrations between the soil and the plant organs of C. album (Suppl. material
In the northern part of the study area, Fe concentrations of soil and stems were positively correlated (r = 0.683, p = 0.042) (Suppl. material
Bioaccumulation factor (BAF) values were lower than 1 for all metals, which indicates that accumulation was not found in C. album (Suppl. material
Corresponding to C. album, bioaccumulation factor (BAF) values and bioconcentration factors (BCF) were lower than 1 for T. inodorum (Suppl. material
In the literature discussing environmental pollution, metals are usually classified as (i) trace metals which strongly exceed critical values and (ii) toxic metals which are known as strong contaminants (
We demonstrated that metal concentrations were very low in plant organs of C. album. In a previous study
We found that metal concentrations were also very low in plant organs of T. inodorum. However, in some cases, we observed significant differences among plant organs even in low concentration ranges.
We found a significant negative correlation in Pb concentrations between the soil and stems of C. album.
In the case of T. inodorum we found a significant positive correlation in Sr concentrations between the soil and leaves.
Bioaccumulation factor (BAF) and bioconcentration factor (BCF) values were simultaneously very low in C. album, while translocation factor (TF) values were high in several cases. We found high (> 1) translocation factor (TF) values for Fe, Mn, Ba, Ni, Pb and Sr in the stems and for Fe, Mn, Ba, Cu, Ni, Pb, Sr and Zn in the leaves of C. album. In a study on the phytoextraction capacity of C. album
Bioaccumulation factor (BAF) and bioconcentration factor (BCF) values were also very low for T. inodorum, while translocation factor (TF) values deserved attention. We found high (> 1) TF values for Mn, Cu, Ni and Zn in the stems and for Fe, Mn, Cu, Sr and Zn in the leaves of T. inodorum.
Translocation factor (TF) values in C. album and T. inodorum are influenced by several soil parameters. Interactions between metals are typical not only in soils but also in plants. As a common phenomenon, based on their ionic radius, Cd and Zn are in competition for the binding sites located in the transport proteins; thus, they can hinder the accumulation and translocation of each other into and within plants (
The results of this study indicated that both Chenopodium album and Tripleurospermum inodorum showed low metal accumulation potential in the moderately contaminated study area. Comparing the two species, T. inodorum appeared to be a better accumulator of Al, Fe, Mn, Na, Ba, Cr and Ni, while C. album was a better accumulator of K, Mg and Sr. Metal concentrations in the two species were generally low. Bioaccumulation factor (BAF) and bioconcentration factor (BCF) values for metals were also low (BAF and BCF < 0.1). In contrast, translocation factor (TF) values were high (> 1) for Fe, Mn, Ba, Cu, Ni, Sr, Pb and Zn in C. album and for Fe, Mn, Cu, Sr and Zn in T. inodorum. We found that several factors, such as metal interactions and soil characteristics, could influence metal accumulation in plant organs causing a lower accumulation potential of the studied species than reported by the previous studies. Based on the high TF values, aboveground plant organs, especially leaves, could be metal-rich depositories. Summarizing, C. album and T. inodorum are capable of indicating and accumulating several soil metals, and thus have good potential in the early stages of phytoremediation, assisting the further remediation characterized by woody species.
We acknowledge the Agilent Technologies and the Novo-Lab Ltd. (Hungary) for providing the MP-AES 4200. Research was supported by OTKA K 116639, KH 126481 and KH 126477 projects and by “Nemzet Fiatal Tehetségeiért” (NTP-NFTÖ-17) Scholarship.
Tables S1–S11
Data type: statistical data
Explanation note: Table S1. Results of General Linearized Model analysis. Table S2. Mean element concentrations of Chenopodium album and Tripleurospermum inodorum. Table S3. Differences in element concentrations among plant organs of Chenopodium album within each part of the study area by p significance values. Table S4. Differences in element concentrations in selected plant organs of Chenopodium album among the parts of the study area by p significance values. Table S5. Differences in element concentrations among plant organs of Tripleurospermum inodorum within each part of the study area by p significance values. Table S6. Differences in element concentrations in selected plant organs of Tripleurospermum inodorum among the parts of the study area by p significance values. Table S7. Correlations in element concentrations between soil and plant organs of Chenopodium album in the three parts of the study area. Table S8. Correlations in element concentrations between soil and plant organs of Tripleurospermum inodorum in the three parts of the study area. Table S9. Bioaccumulation factor (BAF) values of Chenopodium album and Tripleurospermum inodorum. Table S10. Bioconcentration factor (BCF) values of Chenopodium album and Tripleurospermum inodorum. Table S11. Translocation factor (TF) values of Chenopodium album and Tripleurospermum inodorum.