Next Article in Journal
Accounting for DEM Error in Sea Level Rise Assessment within Riverine Regions; Case Study from the Shatt Al-Arab River Region
Next Article in Special Issue
The Dynamics of Tungsten in Soil: An Overview
Previous Article in Journal
The Impact of Rural Fires on the Development of Invasive Species: Analysis of a Case Study with Acacia dealbata Link. in Casal do Rei (Seia, Portugal)
Previous Article in Special Issue
Evaluating the Pollution Risk of Soil Due to Natural Drainage of Orange Peel: First Results
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:

Comparison between a Traditional (Horse Manure) and a Non-Conventional (Cork Powder) Organic Residue in the Uptake of Potentially Toxic Elements by Lettuce in Contaminated Soils

LEAF, Instituto Superior de Agronomia, Universidade de Lisboa, 1349-017 Lisboa, Portugal
Author to whom correspondence should be addressed.
Environments 2021, 8(5), 45;
Submission received: 8 April 2021 / Revised: 9 May 2021 / Accepted: 13 May 2021 / Published: 18 May 2021
(This article belongs to the Special Issue Soil Pollution Assessment and Sustainable Remediation Strategies)


The use of natural organic correctives is a current agricultural practice that may have advantages for the production of plants in contaminated soils. Cork powder is a natural sub-product of the cork industry that has several potential benefits compared to more commonly used soil amendments. In this work, an evaluation was performed of the use of cork powder (a non-conventional organic residue) and horse manure (traditionally used in agriculture) to control the availability of potentially toxic elements in artificially contaminated soils. Four concentrations were used for each element: Cr (100 to 800 mg kg−1), Ni (37.5 to 300 mg kg−1), Zn (150 to 1200 mg kg−1), Cd (1.5 to 12 mg kg−1) and Pb (150 to 1200 mg kg−1). The accumulation of these elements in lettuce plants grown in pots under controlled conditions was evaluated. With the exception of Cd, no significant differences were detected in the absorption of the different elements by lettuce plants at the studied amounts of correctives applied (1% for cork powder and 0.5% for horse manure). Cadmium was the element that accumulated most in lettuce. Cork powder was shown to be less effective than horse manure in controlling the bioavailability of these elements in the soil. Further tests with chemically modified cork products could improve its efficiency.

Graphical Abstract

1. Introduction

The contamination of vegetables by potentially toxic elements (PTE), either essential or non-essential, is a widespread problem that spans different scientific areas like those related to the environment, agronomy, food production, and public health. Soil contamination with PTE results, in most cases, from anthropogenic causes like agricultural, mining and industrial activity, atmospheric deposition, waste water, domestic effluents, and the use of poor quality corrective materials [1].
Although contamination has been greatly reduced in most developed countries, many soils can still contain high levels of contaminants resulting from previous anthropogenic activities and, in many countries, this contamination remains [2,3]. The contamination of vegetables with PTE can thus occur, mainly, due to their presence of toxic levels of certain PTE in soils, irrigation water, and air [4,5].
While Cd, Cr, and Pb are non-essential elements for plants, Ni and Zn are essential micronutrients, but all can be toxic above critical concentrations [5].
Chromium is one of the most abundant metals in the earth’s crust and usual mass fractions in soils range from 0.1 to 0.3 mg kg−1 [6]. Both Portuguese and Canadian regulations define a limit of 67 mg kg−1 for the total Cr content in agricultural soils [7,8]. While Cr has several oxidation states, the most common are Cr3+ and Cr6+ which can interconvert depending on redox conditions, being Cr6+ the most toxic form [9]. The form Cr3+ is less toxic and predominates in most soils, presenting low mobility and occurring mostly linked to organic matter [10].
Nickel is an essential element for plants where it is usually found in low mass fraction in the range 0.05–10 mg kg−1 dry mass (DM), but it can reach higher mass fractions in plants growing in Ni contaminated soils leading to toxicity symptoms [11,12]. In soils, normal Ni values are reported to range between 0.5 and 10 mg kg−1 [13] and in Portuguese and Canadian regulations the limit for Ni in agricultural soils is defined as 37 mg kg−1 [7,8].
Zinc is also an essential element and is present in soils in mass fractions between 10 and 300 mg kg−1 with an average of around 55 mg kg−1 [14]. Although deficiency symptoms are usually a problem [15], toxic effects have also been reported [16]. Portuguese and Canadian regulations limit the amount of Zn in agricultural soils to 290 mg kg−1 [7,8].
Cadmium mass fractions in uncontaminated soils vary between 0.02 and 2.0 mg Cd kg−1 or higher in sedimentary rock soils (0.3 to 15 mg Cd kg−1) [1]. Several countries have regulated the maximum Cd mass fractions in soils and, for example, they must have levels below 1 mg Cd kg−1 in agricultural soil according to both Portuguese and Canadian regulations [7,8]. While Cd is relatively available for absorption by the plant, its bioavailability and mobility is highly dependent on soil properties like pH and organic matter [17]. Due to its high mobility Cd can easily accumulate inside the plants at toxic levels and induce different defence responses [18].
Lead is a widespread pollutant that can be toxic for animals and plants despite its relatively low mobility from soil to plants [19,20]. Although the use and emissions of Pb has been declining in recent years it can still present a severe environmental problem [21]. In soils used for agriculture, Portuguese and Canadian regulations define a maximum mass fraction of Pb of 45 mg kg−1 [7,8].
Contaminants, like the PTE described, cannot be easily removed from the soil. However, under certain conditions, soil amendments (like organic correctives) can be used to reduce the availability of PTE by changing soil pH and increasing the number of PTE binding sites [22]. The use of natural organic amendments, like manure, is a current practice that can have advantages for the production of plants in contaminated soils [23,24]. Different soil amendments have been used to improve soil quality and reduce PTE toxicity, like paper industry wastes [25], manure-based biochars and composts [26], or different type of polymers [27]. Although there are several reports on the effects of soil amendments to reduce PTE toxicity, there is still a lack of knowledge of the proper uptake mechanisms and of the use of environmentally friendly subproducts of several activities, like the cork industry.
Cork is an important economic activity in several Mediterranean countries and cork subproducts have been studied as absorbent materials for different pollutants, mainly in water [28]. However, to the best of our knowledge, there have been no reported studies on the capacity of cork subproducts to absorb PTE from contaminated soils.
The main objective of the present work was to evaluate the potential use of two natural organic amendments (a conventional one, horse manure and a non-conventional one, cork powder) on the capacity to reduce the availability (and, consequently, the uptake and toxicity) of five PTE (Cd, Cr, Pb, Ni, and Zn) in artificially contaminated soils for lettuce plants. While horse manure is traditionally used in agriculture, there are no known reports on the application of cork powder as an amendment. Lettuce was chosen as it is a widely consumed vegetable around the world and is also a model species reported to be highly tolerant to PTE [29].

2. Materials and Methods

2.1. Soil Contamination, Soil Amendment and Plant Production

In this work, experiments were performed with Lactuca sativa L. plants, variety capitata, cultivar “4 seasons” (a popular cultivar used in several countries). The soil used in the pot experiments (4 kg pots) was fully characterized (Table 1) and individually contaminated with each PTE (Cd, Cr, Pb, Ni and Zn) at 4 different mass fractions, plus control (Table 2) and left to stabilize for 6 months before use (maintaining 60% water saturation). The PTE were added to the soils as water solutions of appropriate concentrations using the salts described in Table 2. The mass fractions were chosen based on the values listed in Portuguese legislation regarding the use of sewage sludge in agricultural soils [30] and correspond to multiples of the maximum levels of each PTE allowed in the soil at the appropriate pH (0.5×, 1×, 2×, 4×).
For each PTE, 3 treatments were performed: S—control, with no organic amendment; SC—soil with added cork powder (1%); and SE—soil with added horse manure (0.5%). The percentage of each amendment was selected in order to obtain the same amount of organic matter added to the soil. Each of these modalities and each PTE was performed in triplicate (3 different pots, with one plant per pot) and so, for the 5 PTE mass fractions used, a total of 45 pots were used per PTE. A basal fertilization (N, P, and K) was performed prior to plants being placed in the pots and based on previous soil analysis (0.15 g N kg−1 soil added as NH4NO3, 0.033 g P kg−1 soil added as KH2PO4 and 0.125 g K kg−1 soil added as K2SO4).
Lettuce seeds were germinated in peat substrate and after 2 weeks plants were planted in each pot. The pots were kept in a greenhouse, randomly distributed, with periodic rotation. Plant material (lettuce leaves) were collected and analyzed after 80 days of growth.

2.2. Plant Determinations

Lettuce leaves were collected and immediately weighed to obtain the fresh weight (FW). Samples were washed with deionized water and dried at 70 °C until constant weight to obtain the dry weight (DW). Subsamples of the dried material with 0.5 g were digested with a mixture of 3 mL concentrated HNO3 with 10 mL concentrated HCl in a digestion block (DigiPREP MS) for 120 min. The solutions were then analyzed for Cd, Cr, Pb, Ni and Zn by ICP-OES (Thermo Scientific iCAP 7200 duo) as described previously [31].

2.3. Quality Assurance

All determinations were performed in triplicate, always including blanks. With each digestion, a certified reference material (CRM) was always analyzed (Wepal lettuce IPE 776). Deviations between measured and CRM values were always below 10%. All calibrations curves had R2 > 0.98. Calculated limits of quantification (mg/kg) were: Cr—1.0; Ni—1.5; Zn—1.0; Cd—0.05; and Pb—0.2.

2.4. Transfer Factor (TF)

The transfer factor measures the fraction of the PTE that is absorbed by the plant in relation to the total in soil and is calculated using the following expression:
TF = C P C S  
where Cp is the PTE mass fraction in lettuce leaves (mg kg−1 DW) and Cs is the PTE mass fraction in the soil (mg kg−1).

2.5. Tolerance Index (TI)

The tolerance index [32] measures the fresh weight of lettuce shoots growing in contaminated soil in relation to the fresh weight of lettuce shoots growing in non-contaminated (control) soil, using the following expression:
TI = FW M FW Ctr × 100
where FWM is the fresh weight of lettuce aerial parts (g) growing in contaminated soil and FWCtr is the fresh weight of lettuce aerial parts (g) growing in non-contaminated soil (control).

2.6. Statistical Treatment

The results were analyzed with a one-factor analysis of variance (ANOVA) performed with the SPSS 20.0 (SPSS Inc., Chicago, IL, USA) software and the Tukey test was used to determine significant differences between the means (p < 0.05) and was carried out to compare PTE contents between control and contaminated plants and with and without added organic amendments. In the figures, different lowercase letters reflect significant differences between treatments (S—control coil, SC—soil with cork subproducts, and SE—soil with horse manure) for the same PTE mass fraction while different uppercase letters reflect significant differences between PTE mass fractions for the same treatment. The experimental data obtained was classified using a partitioning clustering method (partitioning around medoids; PAM) [33] with three clusters, allowing to differentiate individuals based on two classes: PTE mass fraction in the soil and treatment (S, SC, SE). This was performed using a correlation matrix with six normalized variables (fresh weight of shoots, PTE mass fraction in the shoots, PTE mass fraction in the soil, extractable PTE in soil, soil pH, and soil organic matter), using the R studio software (Version 1.0.136, RStudio, Inc., Boston, MA, USA).

3. Results and Discussion

3.1. PTE Uptake Behavior in Lettuce

The contents of all PTE under study (Cd, Cr, Ni, Pb and Zn) in the plant increased with the respective mass fraction in soil, although the accumulation behavior can be explained by different models. The accumulation curves of the PTE in lettuce are shown in Figure 1a–e. The parameters of the adjusted models for each curve are presented in Table 3.
The accumulation curves describe the content in the plant as a function of the mass fractions of PTE present in the soil, being valid for the tested range. The accumulation of Cd and Ni is best described by a hyperbolic model while the accumulation of Cr, Pb, and Zn is best described by a linear model.
In the hyperbolic model, the accumulation tends to a plateau, after an initial increase the uptake tends to stabilize for higher mass fractions of the PTE in the soil. In the linear models there is a direct proportionality between the values accumulated in the plant and the values present in the soil.
The addition of the organic amendments (SC and SE) did not change the uptake behavior but led to significant decreases in the uptake of Cd. For the other PTE no differences in the uptake were observed.
The hyperbolic model was the one that best described the behavior of Cd and Ni uptake by lettuce as a function of the element mass fraction in soil (Figure 1a,c). This means that there is greater Cd and Ni uptake for lower element levels in the soil and, as these levels increase, the rate of PTE taken up by the plant is reduced tending towards a saturation value, which is given by the constant Cmax, obtained for higher mass fractions of PTE in the medium. This is probably due to the saturation of the root absorbing power at higher element mass fractions, which can be related to a defence mechanism to avoid the uptake of an excess amount of Cd and Ni. While Ni is an essential element for plants and Cd is non-essential, Ni is required only in low mass fractions for adequate plant functions [12].
The Cd-Cmáx coefficient, representing the predicted maximum mass fraction level of Cd absorbed by the plant, is higher in the control, S (222.3), compared to SC (149.9) and SE (133.5). Cmax has a lower value in the modalities in which organic residues were added to the soil, indicating that the organic correctives had a beneficial effect, SE being more effective than SC. The Ni-Cmáx coefficient was 90.8 for the control (S), 115.2 with cork powder (SC) and 88.1 with manure (SE). No beneficial effect was evident with SC in reducing the accumulation of Ni in the plant, and there is only a very small effect in SE. We can conclude that the presence of these organic correctives had no significant influence on the accumulation of Ni in lettuce.
Other studies have reported different behavior, but under different experimental conditions. Stritsis and Claassen [34] evaluated the Cd uptake kinetics on 4 different species (maize, sunflower, spinach, and flax) and noticed a linear relationship in Cd uptake, but their study was in nutrient solution, where all the Cd is readily available for uptake. This difference in experimental conditions and the use of different plants could explain the difference in behavior as in a study with lettuce in a field experiment, Chen, et al. [35] observed a behavior similar to our study, and the authors fitted a Michaelis-Menten equation to the Cd uptake. A similar behavior was also observed in the uptake of Cd by sunflower plants, also in soil [36], indicating that the uptake pattern is strongly dependent on the type of growing media.
For Cr, Pb (two non-essential elements for plants), and Zn (a plant micronutrient), the most adequate model to describe the accumulation in the plant was the linear model, for all the experimental treatments (S, SC, and SE). As was observed for Cd and Ni, the presence of the two amendments did not change the uptake behavior, as some differences were found but were not statistically significant. For Cr, Pb, and Zn the levels accumulated in the edible part of the contaminated plants increase proportionally to the levels present in the soil. This shows that up to the maximum mass fractions studied for these elements (800 mg kg−1 for Cr, 1200 mg kg−1 for Pb and for Zn) there is still no tendency for the uptake to stabilize in a plateau. The much higher slope for Zn reflects the much greater Zn uptake by lettuce compared to the uptake of the non-essential elements Pb and Cr.

3.2. PTE Accumulation

For all treatments (S, SC, and SE) there were significant increases in Cd content in lettuce leaves for all of the applied Cd levels in soil. A maximum of 93 ± 1 mg Cd kg−1 DW was detected in plants growing in non-amended soil (S) contaminated with 12 mg Cd kg−1. With the addition of organic correctives, there was a marked decrease in the accumulation of this PTE in plants, both with SC (80 ± 3 mg Cd kg−1 DW, a 14.7% decrease) and with SE (72 ± 1 mg Cd kg−1 DW, a 23.0% decrease). This difference between treatments was only significant from the mass fraction of 3 mg Cd kg−1 in the soil, and upwards. For all mass fractions, the addition of SE always caused a decrease in Cd uptake by lettuce plants. Under all conditions, no toxicity symptoms were detected in the plants.
Adding these amendments probably lead to Cd sorption to the added organic compounds, which explain the reduced availability to the lettuce plants. Another effect that can reduce the uptake of PTE by plants is the increase in pH due to the added amendments [22]. In the present work, although there was a slight increase in soil pH (S: 6.9 ± 0.1; SC: 7.2 ± 0.1; SE: 7.1 ± 0.1), it remained in the neutral zone and was not enough to affect the PTE uptake. These effects have been previously described in different studies regarding the reduced uptake of different PTE by plants under different soil amendments [37,38,39]. However, the effect is highly dependent upon the plant and the type and amount of amendment, as an increase in Cd uptake with the addition of organic amendments has also been reported [40,41].
To the best of our knowledge there have been no studies carried out with cork residues as soil amendments to reduce PTE uptake, which relate their capacity for adsorption of PTE in the soil, and use in the remediation of contaminated soils, with only a few references to its use as an adsorbent material in gases, water, and effluents [28]. In the present study, there was only a slight decrease in Cd uptake by plants in the presence of cork powder but the effect of a conventional amendment like horse manure proved to be more efficient in this regard. It should be noticed that the cork powder used suffered no type of pre-treatment, as it has been reported that some forms of chemical treatments can lead to an increase in PTE sorption capacity [42].
Lettuce plants accumulated Ni, and its values in lettuce ranged from 23 ± 4 mg kg−1 for the lowest mass fraction of Ni in soil (S, 37.5 mg Ni kg−1) up to 82 ± 11 mg kg−1 for the highest mass fraction (SC, 37.5 mg Ni kg−1). There were no significant differences in Ni uptake due to the presence of the organic amendments, although a slight increase tendency with both SC and SE was detected.
The uptake of Cr, Pb and Zn reached a maximum of 6.1 ± 0.2, 11 ± 1, and 608 ± 34 mg kg−1, respectively, at the highest mass fraction of each PTE in soil. These results show that lettuce plants are able to tightly control the uptake of a non-essential elements like Pb and Cr, as they are probably mostly retained at the root level with limited translocation to the shoots [43]. It has been proposed that this reduced translocation of Cr to the shoots is due to a conversion of Cr(VI) to Cr(III) and the binding of this latest form, to root cell walls [10]. Visual symptoms of toxicity were only detected for the highest Cr and Pb mass fraction in the soil of 800 mg kg−1 and 1200 mg kg−1, respectively. The accumulated Pb values were very similar to those accumulated by the lettuce plants contaminated with Cr, and much lower than those accumulated by the plant exposed to Cd, although the mass fractions applied in the soils are very different. In the case of Zn, the accumulated values are of a much higher order of magnitude, indicating a very high mass fraction of this element in the plant, resulting from its essential micronutrient character. Despite the fact that Zn is an essential micronutrient, visual symptoms were detected for Zn content in soil as low as 300 mg kg−1, although the effects were much more pronounced at 1200 mg kg−1. At this highest Zn levels in the soils, Zn contents in plants reached a maximum of 608 ± 34 mg kg−1 DW which is well above the usual Zn mass fraction usually considered as toxic for plants (300 mg kg−1 DW) [44], as this essential element is known to accumulate in lettuce leaves [45].
The presence of the two organic amendments did not affect the uptake of Cr or Pb, but seemed to alleviate some of the toxic effects of excess Zn, as the difference in biomass (see below) only decreased significantly for SC and SE plants under 1200 mg Zn kg−1. However, there were no differences in Zn uptake between control and amended soils for all the studied mass fractions.
Other studies on the application of different organic correctives to soils contaminated with Cr have also reported no significant effects in Cr uptake by different plants [46], while it has also been reported that soil amendments like manure and vermiculite can reduce Cr toxicity to crops [47,48]. McBride, et al. [49] also observed that a compost based on bovine manure had no significant effect in reducing the transfer of Pb from the soil to lettuce plants. The authors attribute these results to the low solubility and availability of Pb in the soil, due to the inherent high organic matter content and the fact that the soil pH is almost neutral. However other studies confirmed the reduced availability of Pb to plants, due to the application of different amendments [50,51]. Several studies on the effect of soil amendments on Zn absorption by plants have mentioned different effects, as these are probably highly dependent on the type of soil and of the amendment, plant species and Zn mass fraction [24,50].

3.3. Evaluation of Vegetable Contamination

Lettuce is a highly consumed vegetable and so it is important to evaluate the uptake of PTE in relation to its maximum acceptable levels. European Union regulations limit the amount of Cd in leaf vegetables to 0.2 mg kg−1 FW [52]. In all the Cd mass fractions in the soil (between 1.5 and 12 mg kg−1) and all the modalities under study (S, SC, and SE), the Cd levels in lettuce leaves exceeded that reference value. Considering the water content of lettuce (an average of 96.2%), the values of Cd mass fraction in lettuce leaves ranged from a lower value of 0.73 mg kg−1 FW (S, [Cd]soil = 1.5 mg kg−1) to the highest of 3.63 mg kg−1 FW (S, [Cd]soil = 12 mg kg−1). Thus, even at the lowest Cd mass fraction in the soil of 1.5 mg kg−1 lettuce plants in all modalities exceeded the legislated values, while at the same time the plants showed no toxicity effects, which can present a food safety hazard as there is no visual indication to the consumer that the plants are contaminated. Lettuce plants are reported to be accumulators of Cd and they can easily exceed the defined maximum allowable limits when grown in soils with relatively low Cd contents [53].
Normal Ni values in plants are reported to be around 1 mg kg−1 DW [5,54], although Marschner and Marschner [55] refer the critical toxicity levels of Ni as between 10 and 50 mg kg−1 DW, depending on crop species. The values detected in the present work (a maximum of 81.74 mg kg−1 DW) are higher compared to the reported values in lettuce in uncontaminated soils [56,57], although the plants showed no signs of toxicity. In a study of the growth of lettuce in Ni-contaminated soils, Zhao, et al. [58] reported Ni levels in leaves similar to the ones obtained in the present study and only detected a reduced growth for Ni mass fractions of 400 mg kg−1 and higher, thus confirming the high tolerance of lettuce plants to Ni. In a recent EFSA publication [59] a tolerable daily intake (TDI) of 13 µg kg−1 body weight (BW) was established. For a 70 kg adult this corresponds to a daily intake of 0.91 mg. Considering an average lettuce consumption of 22.5 g day−1 per person (adult) [60] and the maximum value of Ni measured in lettuce leaves in the present work (81.74 mg kg−1 DW, equivalent to 4.43 mg kg−1 FW), we get a daily intake of 0.10 mg for a 70 kg adult, which is below the TDI. Thus, even at the highest Ni mass fraction in the soil (300 mg kg−1) the Ni levels in lettuce are within safe levels.
Nagajyoti, et al. [5] give a range of between 0.2 and 1 mg Cr kg−1 DW as the normal values encountered in plants, and all the Cr mass fractions measured in the present work exceeded these values but are close to what is reported in plants growing in contaminated soils [61]. Considering the average lettuce consumption given above (22.5 g day−1) and the TDI established by EFSA for Cr(III) of 300 µg kg−1 BW [62], the uptake of Cr by eating lettuce even at the highest contamination level obtained in this work (0.43 mg kg−1 FW corresponding to an intake of 0.01 mg day−1) is below this limit (21 mg day−1 for a 70 kg person). This shows that, due to the low translocation of Cr to upper plant parts, it is safe to ingest lettuce that grows in soils moderately contaminated with Cr.
European Union regulations limit the amount of Pb in leaf vegetables to 0.3 mg kg−1 FW [52]. This value was exceeded for lettuce plants growing in soils containing more than 150 mg kg−1 for all the treatments under study (with the exception of S at 300 mg kg−1). For the highest mass fraction of Pb in the soil a maximum of 0.94 mg kg−1 FW of Pb in the leaves was detected. Thus, although Pb is not considered a very mobile element in plants, high mass fractions of this PTE in the soil can lead to excessive values in vegetables like lettuce.
In relation to Zn, European Union regulations consider a tolerable upper intake level (UL) of 25 mg Zn day−1 [63]. Considering the average consumption of lettuce referred above (22.5 g day−1) and even at the maximum mass fraction of Zn detected in the present study (70.56 mg kg−1 FW), the daily intake of Zn amounts to only 1.6 mg Zn day−1 which is considerable below the defined UL. It should be noticed that at this mass fraction, lettuce plants already show visual toxicity symptoms which might lead to its rejection by the consumer. Thus, the consumption of lettuce growing in soils with a high Zn content does not pose a toxicity hazard to humans.

3.4. Transfer Factor

The transfer factor (TF) evaluates the transfer of PTE present in the soil to the plant, given by the proportion in the plant in relation to the levels in the growing medium. These values are shown in Figure 2 for the five PTE studied.
For Cd there was a clear decrease in TFCd both with increasing Cd content in soil and with the presence of both amendments, with manure (SE) having a more pronounced effect than cork (SC), confirming that these amendments decrease the plant’s ability to transfer the Cd present in the soil to the plant. The very high TFCd are in accordance with the values accumulated in the maximum tested mass fractions, which are still below the Cd-Cmax. The values for TFCd were the highest TF among the 5 PTE studied, confirming the high ability of lettuce to absorb Cd into its leaves [17]. Curiously, it was with this PTE that the amendments were most effective in reducing PTE uptake.
In the case of contamination with Ni, although a general decrease in TFNi was observed with increasing Ni mass fraction in soil (Figure 2c) there was no significant differences with the application of both soil amendments. This decrease in TFNi values indicates lower absorption rates, which is in accordance with the adjustment of accumulation to the hyperbolic model and the verification of a tendency towards saturation at a Ni-Cmax value, mentioned above. In fact, for Ni, the levels in the plant are closer to the Ni-Cmax value, and the TFNi reflects this situation, indicating that they are closer to saturation. Nickel uptake by plants has been reported to be reduced by composts [64], but with the amendments used in the present work this was not observed. A reduction of the TF of Ni in lettuce plants similar to the present work results has also been observed in a recent study with lettuce plants [58].
The values for Cr (TFCr) are very similar to the behavior observed for Ni, with a general decrease with increasing Cr mass fraction in soil and no visible effect of the added amendments (Figure 2d). This shows that despite the increasing Cr content in soil, the plant has adequate mechanisms to control the uptake of this element. Chromium mass fractions in the plant remained low, and TFCr values were also very low indicating a low translocation from the soil to the plant. Chromium is not a very mobile element, and it has been reported that amendments like biochar can reduce its uptake by plants [65].
The TF for Pb (TFPb) exhibits a different behavior from the other PTE (Figure 2b). Although there is also a general decrease with increasing Pb in soil, there is a significant increase with the presence of amendments (more pronounced for horse manure, SE), except at the highest mass fraction of 1200 mg kg−1. In absolute terms, the TFPb values, together with those for Cr, are the lowest of the five PTE studied, showing the low mobility of these elements in plants, which has been previously reported [66]. Despite the low TFPb values, the levels of Pb in the plant present a contamination hazard as described above.
In relation to Zn, there were no significant differences in TFZn for the two lowest soil Zn mass fractions (150 and 300 mg kg−1), but for the two highest mass fractions, there was an increase with the applied amendments, more pronounced for horse manure (Figure 2e). Thus, for the highest Zn mass fractions in soil, the presence of the amendments actually increased the uptake of Zn by lettuce plants in relation to the soil content.
Generally, the order of TF values was Cd > Ni > Zn > Cr ≈ Pb. Khan, et al. [67] also measured the TF values of several PTE and while they present the highest value for Cd, they also indicated a TF for Pb higher than for Zn or Ni (for lettuce plants). These differences could be due to PTE mass fraction in the soil (for example, in the present study we observed an almost five-fold difference in TFNi between the highest and the lowest Ni mass fractions in soil) and also to soil characteristics and contamination source. In a different study [68] TF in the order of Cd > Zn > Pb was also reported, with very low values for Pb similar to the ones of the present work (although at lower PTE mass fractions in the soil). Similar results were obtained in another study with lettuce with Cr having the lowest TF [69].

3.5. Tolerance Index

The Tolerance Index (TI) provides important information about phytotoxicity because it is based on plant biomass (fresh mass) and reflects the negative effect of accumulation on plant development. Thus, a decrease in TI indicates less biomass (in relation to the control) and therefore greater toxicity of each PTE. In Figure 3, the TI for all the PTE studied are presented.
In plants exposed to Cd, a lower TI only for control plants growing in the two highest Cd mass fractions (6 and 12 mg kg−1) was obtained, showing that both soil amendments attenuated, albeit slightly, the toxic effects for Cd.
For the Ni assay, no differences were observed in the TINi and this reflects the tolerance of lettuce to Ni toxicity, as no visual indicators of toxicity were detected. As the Ni effects were not noticeable (up to the mass fractions studied) there was also no differences with the application of both organic amendments.
In soils contaminated with Pb, the TIPb was reduced in non-amended soils for 600 and 1200 mg kg−1 mass fractions. The TIPb with amendments (SC and SE) improved slightly, showing that, although the Pb levels in lettuce are not significantly reduced, growing lettuce with these amendments (especially for manure) can attenuate the effects of Pb toxicity.
The effects for Cr and Zn were similar, with a general decrease in TI for the two highest mass fractions, much more noticeable at the higher mass fraction. Although in both cases there was a slight increase in TI with the presence of amendments, the differences are not significantly different. For a Cr mass fraction of 800 mg kg−1 and a Zn mass fraction of 1200 mg kg−1 the TI value is less than 50% for contaminated plants in all modalities (S, SC, and SE), showing that this is a critical mass fraction for plant development. This behavior was observed for all treatments, with no differences for S, SC, and SE, indicating that the application of organic residues does not reduce bioavailability for the plant and does not control toxicity for plants, thus it has no effect on contamination control. Similar results have been obtained by Shu, et al. [70] that observed a strong decrease in TI with increasing concentrations of Zn and also Pb.

3.6. Cluster Analysis

A cluster analysis was performed applying a correlation matrix to 6 normalized variables (PTE mass fraction in edible part and in soil, extractable fraction, leaf fresh weight, soil pH, and % of organic matter). The method followed was PAM partition into 3 classes in order to allocate different individuals according to the PTE mass fraction applied and treatment (S—non-amended soil, SC—soil with cork powder, SE—soil with horse manure). Figure 4 shows the PAM analysis for the 5 PTE applied (Cd, Cr, Ni, Pb, and Zn). This analysis allows an evaluation of toxicity parameters, as well as the main differences among amendments applied to soil. In all presented clusters it is possible to observe a clear differentiation among modalities.
As can be seen from these figures, the main effect is caused by the element mass fraction in soil, as the highest mass fractions appear in separate groupings. This effect is much more intense than the presence of either of the added amendments, as we have in most cases all three treatments (S, SC, and SE) present in the identified groups. For Cd, Ni, Cr, and Pb (Figure 4a–d) there are three clearly defined groups corresponding to the control and the lowest PTE mass fraction, another group for the intermediate ones, and another one for the highest mass fractions. For Zn, the most clearly defined group is for the highest Zn mass fraction of 1200 mg kg−1, where the effects were more pronounced. For Pb and Zn, two classes presented overlap conditions, namely the ones including control and lower mass fractions individuals and medium mass fractions, while in Cd the slight overlap was between the medium and the highest mass fractions, showing the more toxic effect of Cd.

3.7. Pratical Implications of This Work

The present work confirmed that different PTE can be absorbed by edible plants and can reach concentrations that are harmful to human beings, especially in relation to Cd and Pb. These two elements have very different mobilities in plants, but can both reach high contents. Although the amount of Cr and Ni taken up by the plants is not very high, there should be more clear legislation regarding the safe levels of these elements in edible vegetables. The application of amendments can lead to a reduction in PTE uptake by plants, but its efficiency is highly dependent on the type, characteristics, and mass fraction of the amendment in the soil. The cork subproduct was not very efficient in reducing PTE uptake by plants (except for Cd) so the possibility of making some sort of chemical treatment should be explored in the future.

4. Conclusions

Of the non-essential elements studied (Cd, Cr, and Pb), Cd is by far the most mobile in the plant with higher contents detected compared to Pb and Cr, even if its mass fraction in the soils is much lower. This resulted in Cd contents in lettuce that were higher than the maximum allowable limits. The legislated limits were also exceeded with Pb (but only for soil contents higher than 150 mg kg−1). The values of Cr, Ni and Zn accumulated in lettuce were considered acceptable at all mass fractions studied.
The addition of organic amendments only was effective on reducing the uptake of Cd by lettuce plants but has no effect on the uptake of the other PTE. For Cr, Ni, Zn, and Pb, the application of the amendments did not cause a significant reduction in uptake and accumulation in plants. When the results between both organic residues are compared, cork is shown to be less efficient than horse manure in controlling the bioavailability of PTE for plants.
It can be concluded that the application of these organic correctives (cork and horse manure) is only promising for the remediation of soils contaminated with cadmium, given that only for this element there was a decrease in accumulation in the plant. Under the conditions of the present work, the presence of both organic correctives had no influence on the Cr, Pb, Ni, and Zn content accumulated in the plant.
The application of mathematical models to explain the behavior of each PTE allows us, within certain limits, to predict and characterize the accumulation in the plant under the studied conditions. The application of higher amounts of these organic correctives should be considered, so that the accumulation of Cd in the plant is reduced to values that do not constitute a risk to the food chain. This is particularly important if we take into account that toxicity symptoms are not visible even for significant amounts of Cd in the plant.

Author Contributions

Conceptualization, methodology and supervision M.P.M. and L.L.M.; investigation, I.M. and I.L.; writing—original draft preparation, L.L.M. and I.L.; writing—review and editing, M.P.M. All authors have read and agreed to the published version of the manuscript.


This research was funded by FCT—Fundação para a Ciência e Tecnologia (PhD grant SFRH/BD/89557/2012 and grant PTDC/AGR-AAM/102821/2008) and FCT-funded research unit LEAF (UID/AGR/04129/2020).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Not applicable.


Horse manure and cork powder were kindly given by the Portuguese Equestrian Society (Sociedade Hípica Portuguesa) and by Robcork, respectively.

Conflicts of Interest

The authors declare no conflict of interest.


  1. Alloway, B.J. Heavy Metals in Soils, 3rd ed.; Springer: Berlin/Heidelberg, Germany, 2013; Volume 22. [Google Scholar]
  2. Tóth, G.; Hermann, T.; Szatmári, G.; Pásztor, L. Maps of heavy metals in the soils of the European Union and proposed priority areas for detailed assessment. Sci. Total Environ. 2016, 565, 1054–1062. [Google Scholar] [CrossRef]
  3. Gall, J.E.; Boyd, R.S.; Rajakaruna, N. Transfer of heavy metals through terrestrial food webs: A review. Environ. Monit. Assess. 2015, 187, 1–21. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  4. Clemens, S.; Ma, J.F. Toxic Heavy Metal and Metalloid Accumulation in Crop Plants and Foods. Annu. Rev. Plant Biol. 2016, 67, 489–512. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  5. Nagajyoti, P.C.; Lee, K.D.; Sreekanth, T.V.M. Heavy metals, occurrence and toxicity for plants: A review. Environ. Chem. Lett. 2010, 8, 199–216. [Google Scholar] [CrossRef]
  6. Ertani, A.; Mietto, A.; Borin, M.; Nardi, S. Chromium in Agricultural Soils and Crops: A Review. Water Air Soil Pollut. 2017, 228, 190. [Google Scholar] [CrossRef]
  7. Agência Portuguesa do Ambiente Solos Contaminados-Guia Técnico. 2019. Available online: (accessed on 8 March 2021).
  8. Canadian Ministry of the Environment. Soil, Ground Water and Sediment Standards for Use under Part XV.1 of the Environmental Protection Act. in 2011; Canadian Ministry of the Environment: Toronto, ON, Canada, 2011. [Google Scholar]
  9. Shanker, A.K.; Cervantes, C.; Loza-Tavera, H.; Avudainayagam, S. Chromium toxicity in plants. Environ. Int. 2005, 31, 739–753. [Google Scholar] [CrossRef] [PubMed]
  10. Shahid, M.; Shamshad, S.; Rafiq, M.; Khalid, S.; Bibi, I.; Niazi, N.K.; Dumat, C.; Rashid, M.I. Chromium speciation, bioavailability, uptake, toxicity and detoxification in soil-plant system: A review. Chemosphere 2017, 178, 513–533. [Google Scholar] [CrossRef] [PubMed]
  11. Chen, C.; Huang, D.; Liu, J. Functions and Toxicity of Nickel in Plants: Recent Advances and Future Prospects. Clean Soil Air Water 2009, 37, 304–313. [Google Scholar] [CrossRef]
  12. Yusuf, M.; Fariduddin, Q.; Hayat, S.; Ahmad, A. Nickel: An Overview of Uptake, Essentiality and Toxicity in Plants. Bull. Environ. Contam. Toxicol. 2011, 86, 1–17. [Google Scholar] [CrossRef]
  13. De Temmerman, L.; Vanongeval, L.; Boon, W.; Hoenig, M.; Geypens, M. Heavy Metal Content of Arable Soils in Northern Belgium. Water Air Soil Pollut. 2003, 148, 61–76. [Google Scholar] [CrossRef]
  14. Broadley, M.R.; White, P.J.; Hammond, J.P.; Zelko, I.; Lux, A. Zinc in plants. New Phytol. 2007, 173, 677–702. [Google Scholar] [CrossRef] [PubMed]
  15. Alloway, B. Zinc in Soils and Crop Nutrition, 2nd ed.; IZA: Brussels, Belgium; IFA: Paris, France, 2008. [Google Scholar]
  16. Sofo, A.; Moreira, I.; Gattullo, C.E.; Martins, L.L.; Mourato, M. Antioxidant responses of edible and model plant species subjected to subtoxic zinc concentrations. J. Trace Elem. Med. Biol. 2018, 49, 261–268. [Google Scholar] [CrossRef] [PubMed]
  17. Degryse, F.; Smolders, E.; Merckx, R. Labile Cd Complexes Increase Cd Availability to Plants. Environ. Sci. Technol. 2006, 40, 830–836. [Google Scholar] [CrossRef] [PubMed]
  18. Rizwan, M.; Ali, S.; Adrees, M.; Ibrahim, M.; Tsang, D.C.; Zia-Ur-Rehman, M.; Zahir, Z.A.; Rinklebe, J.; Tack, F.M.; Ok, Y.S. A critical review on effects, tolerance mechanisms and management of cadmium in vegetables. Chemosphere 2017, 182, 90–105. [Google Scholar] [CrossRef]
  19. Yan, K.; Dong, Z.; Wijayawardena, M.; Liu, Y.; Naidu, R.; Semple, K. Measurement of soil lead bioavailability and influence of soil types and properties: A review. Chemosphere 2017, 184, 27–42. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  20. Shahid, M.; Pinelli, E.; Dumat, C. Review of Pb availability and toxicity to plants in relation with metal speciation; role of synthetic and natural organic ligands. J. Hazard. Mater. 2012, 219–220, 1–12. [Google Scholar] [CrossRef] [PubMed]
  21. Datko-Williams, L.; Wilkie, A.; Richmond-Bryant, J. Analysis of U.S. soil lead (Pb) studies from 1970 to 2012. Sci. Total Environ. 2014, 468-469, 854–863. [Google Scholar] [CrossRef]
  22. Khan, M.A.; Khan, S.; Khan, A.; Alam, M. Soil contamination with cadmium, consequences and remediation using organic amendments. Sci. Total Environ. 2017, 601–602, 1591–1605. [Google Scholar] [CrossRef] [PubMed]
  23. Gautam, M.; Agrawal, M. Effects of red mud addition in soil fertilized with cowdung manure on growth performance and metal accumulations in Brassica juncea cultivars Kranti and Pusa Bold. Commun. Soil Sci. Plant Anal. 2019, 50, 1214–1231. [Google Scholar] [CrossRef]
  24. Wolf, M.; Baretta, D.; Becegato, V.A.; Almeida, V.D.C.; Paulino, A.T. Copper/Zinc Bioaccumulation and the Effect of Phytotoxicity on the Growth of Lettuce (Lactuca sativa L.) in Non-contaminated, Metal-Contaminated and Swine Manure-Enriched Soils. Water Air Soil Pollut. 2017, 228, 152. [Google Scholar] [CrossRef]
  25. Alvarenga, P.; Rodrigues, D.; Mourinha, C.; Palma, P.; De Varennes, A.; Cruz, N.; Tarelho, L.A.; Rodrigues, S. Use of wastes from the pulp and paper industry for the remediation of soils degraded by mining activities: Chemical, biochemical and ecotoxicological effects. Sci. Total Environ. 2019, 686, 1152–1163. [Google Scholar] [CrossRef] [PubMed]
  26. Sigua, G.C.; Novak, J.M.; Watts, D.W.; Ippolito, J.A.; Ducey, T.F.; Johnson, M.G.; Spokas, K.A. Phytostabilization of Zn and Cd in Mine Soil Using Corn in Combination with Biochars and Manure-Based Compost. Environments 2019, 6, 69. [Google Scholar] [CrossRef] [Green Version]
  27. Guiwei, Q.; De Varennes, A.; Martins, L.L.; Mourato, M.; Cardoso, A.; Mota, A.M.; Pinto, A.; Gonçalves, M. Improvement in soil and sorghum health following the application of polyacrylate polymers to a Cd-contaminated soil. J. Hazard. Mater. 2010, 173, 570–575. [Google Scholar] [CrossRef] [PubMed]
  28. Pintor, A.M.; Ferreira, C.I.; Pereira, J.C.; Correia, P.; Silva, S.P.; Vilar, V.J.; Botelho, C.M.; Boaventura, R.A. Use of cork powder and granules for the adsorption of pollutants: A review. Water Res. 2012, 46, 3152–3166. [Google Scholar] [CrossRef] [PubMed]
  29. Peijnenburg, W.; Baerselman, R.; De Groot, A.; Jager, T.; Leenders, D.; Posthuma, L.; Van Veen, R. Quantification of Metal Bioavailability for Lettuce (Lactuca sativa L.) in Field Soils. Arch. Environ. Contam. Toxicol. 2000, 39, 420–430. [Google Scholar] [CrossRef]
  30. MAOTDR, Ministério do Ambiente, do Ordenamento do Território e do Desenvolvimento Regional. Decreto-Lei No. 276/2009. 2009. Available online: (accessed on 8 March 2021).
  31. Ribeiro, D.M.; Scanlon, T.; Kilminster, T.; Martins, C.F.; Greeff, J.; Milton, J.; Oldham, C.; Freire, J.P.B.; Mourato, M.P.; De Almeida, A.M. Mineral profiling of muscle and hepatic tissues of Australian Merino, Damara and Dorper lambs: Effect of weight loss. J. Anim. Physiol. Anim. Nutr. 2020, 104, 823–830. [Google Scholar] [CrossRef] [PubMed]
  32. Rossato, L.; Macfarlane, J.; Whittaker, M.; Pudmenzky, A.; Doley, D.; Schmidt, S.; Monteiro, M. Metal-binding particles alleviate lead and zinc toxicity during seed germination of metallophyte grass Astrebla lappacea. J. Hazard. Mater. 2011, 190, 772–779. [Google Scholar] [CrossRef]
  33. Batra, D.A. Analysis and Approach: K-Means and K-Medoids Data Mining Algorithms. In Proceedings of the 5th IEEE International Conference on Advanced Computing & Communication Technologies, Panipat, India, 5 November 2011; Choudhary, R.K., Verma, M., Saini, S., Eds.; pp. 274–279. [Google Scholar]
  34. Stritsis, C.; Claassen, N. Cadmium uptake kinetics and plants factors of shoot Cd concentration. Plant Soil 2013, 367, 591–603. [Google Scholar] [CrossRef] [Green Version]
  35. Chen, W.; Li, L.; Chang, A.C.; Wu, L.; Kwon, S.-I.; Bottoms, R. Modeling uptake kinetics of cadmium by field-grown lettuce. Environ. Pollut. 2008, 152, 147–152. [Google Scholar] [CrossRef]
  36. Rivelli, A.R.; Puschenreiter, M.; De Maria, S. Assessment of cadmium uptake and nutrient content in sunflower plants grown under Cd stress. Plant Soil Environ. 2014, 60, 80–86. [Google Scholar] [CrossRef] [Green Version]
  37. Liu, L.; Chen, H.; Cai, P.; Liang, W.; Huang, Q. Immobilization and phytotoxicity of Cd in contaminated soil amended with chicken manure compost. J. Hazard. Mater. 2009, 163, 563–567. [Google Scholar] [CrossRef] [PubMed]
  38. Clemente, R.; Escolar, Á.; Bernal, M.P. Heavy metals fractionation and organic matter mineralisation in contaminated calcareous soil amended with organic materials. Bioresour. Technol. 2006, 97, 1894–1901. [Google Scholar] [CrossRef]
  39. Lee, S.-H.; Lee, J.-S.; Jeong Choi, Y.; Kim, J.-G. In situ stabilization of cadmium-, lead-, and zinc-contaminated soil using various amendments. Chemosphere 2009, 77, 1069–1075. [Google Scholar] [CrossRef] [PubMed]
  40. Bai, Y.; Gu, C.; Tao, T.; Chen, G.; Shan, Y. Straw incorporation increases solubility and uptake of cadmium by rice plants. Acta Agric. Scand. Sect. B Plant Soil Sci. 2013, 63, 193–199. [Google Scholar] [CrossRef]
  41. Pinto, F.R.; Mourato, M.P.; Sales, J.R.; Fangueiro, D.; Martins, L.L. Effect of Cattle Slurry on the Growth of Spinach Plants in Cd-contaminated Soil. Commun. Soil Sci. Plant Anal. 2020, 51, 1370–1381. [Google Scholar] [CrossRef]
  42. Chubar, N.; Carvalho, J.R.; Correia, M.N. Heavy metals biosorption on cork biomass: Effect of the pre-treatment. Colloids Surf. A Physicochem. Eng. Asp. 2004, 238, 51–58. [Google Scholar] [CrossRef]
  43. Chandra, R.; Bharagava, R.; Yadav, S.; Mohan, D. Accumulation and distribution of toxic metals in wheat (Triticum aestivum L.) and Indian mustard (Brassica campestris L.) irrigated with distillery and tannery effluents. J. Hazard. Mater. 2009, 162, 1514–1521. [Google Scholar] [CrossRef]
  44. Noulas, C.; Tziouvalekas, M.; Karyotis, T. Zinc in soils, water and food crops. J. Trace Elem. Med. Biol. 2018, 49, 252–260. [Google Scholar] [CrossRef] [PubMed]
  45. Roy, M.; McDonald, L.M. Metal Uptake in Plants and Health Risk Assessments in Metal-Contaminated Smelter Soils. Land Degrad. Dev. 2015, 26, 785–792. [Google Scholar] [CrossRef]
  46. Karak, T.; Paul, R.K.; Sonar, I.; Sanyal, S.; Ahmed, K.Z.; Boruah, R.K.; Das, D.K.; Dutta, A.K. Chromium in soil and tea (Camellia sinensis L.) infusion: Does soil amendment with municipal solid waste compost make sense? Food Res. Int. 2014, 64, 114–124. [Google Scholar] [CrossRef]
  47. Singh, G.; Brar, M.S.; Malhi, S.S. Decontamination of Chromium by Farm Yard Manure Application in Spinach Grown in Two Texturally Different Cr-Contaminated Soils. J. Plant Nutr. 2007, 30, 289–308. [Google Scholar] [CrossRef]
  48. Malandrino, M.; Abollino, O.; Buoso, S.; Giacomino, A.; La Gioia, C.; Mentasti, E. Accumulation of heavy metals from contaminated soil to plants and evaluation of soil remediation by vermiculite. Chemosphere 2011, 82, 169–178. [Google Scholar] [CrossRef] [PubMed]
  49. McBride, M.B.; Simon, T.; Tam, G.; Wharton, S. Lead and Arsenic Uptake by Leafy Vegetables Grown on Contaminated Soils: Effects of Mineral and Organic Amendments. Water Air Soil Pollut. 2012, 224, 1–10. [Google Scholar] [CrossRef] [PubMed]
  50. Shaheen, S.M.; Antoniadis, V.; Kwon, E.E.; Biswas, J.K.; Wang, H.; Ok, Y.S.; Rinklebe, J. Biosolids application affects the competitive sorption and lability of cadmium, copper, nickel, lead, and zinc in fluvial and calcareous soils. Environ. Geochem. Health 2017, 39, 1365–1379. [Google Scholar] [CrossRef] [PubMed]
  51. Tang, X.; Li, X.; Liu, X.; Hashmi, M.Z.; Xu, J.; Brookes, P.C. Effects of inorganic and organic amendments on the uptake of lead and trace elements by Brassica chinensis grown in an acidic red soil. Chemosphere 2015, 119, 177–183. [Google Scholar] [CrossRef]
  52. Commission Regulation (EC). No 1881/2006 setting maximum levels for certain contaminants in foodstuffs. Off. J. Eur. Union 2006, 49, L173/6. [Google Scholar]
  53. Gaw, S.K.; Kim, N.D.; Northcott, G.L.; Wilkins, A.L.; Robinson, G. Uptake of ΣDDT, Arsenic, Cadmium, Copper, and Lead by Lettuce and Radish Grown in Contaminated Horticultural Soils. J. Agric. Food Chem. 2008, 56, 6584–6593. [Google Scholar] [CrossRef] [PubMed]
  54. Markert, B. Establishing of ‘Reference Plant’ for inorganic characterization of different plant species by chemical fingerprinting. Water Air Soil Pollut. 1992, 64, 533–538. [Google Scholar] [CrossRef]
  55. Marschner, H.; Marschner, P. Marschner’s Mineral Nutrition of Higher Plants, 3rd ed.; Elsevier: London, UK; Academic Press: Waltham, MA, USA, 2012; Chapter XV; 651p. [Google Scholar]
  56. Atkinson, N.R.; Young, S.D.; Tye, A.M.; Breward, N.; Bailey, E.H. Does returning sites of historic peri-urban waste disposal to vegetable production pose a risk to human health?—A case study near Manchester, UK. Soil Use Manag. 2012, 28, 559–570. [Google Scholar] [CrossRef]
  57. França, F.C.; Albuuerque, A.M.; Almeida, A.C.; Silveira, P.B.; Filho, C.A.; Hazin, C.A.; Honorato, E.V. Heavy metals deposited in the culture of lettuce (Lactuca sativa L.) by the influence of vehicular traffic in Pernambuco, Brazil. Food Chem. 2017, 215, 171–176. [Google Scholar] [CrossRef] [PubMed]
  58. Zhao, J.; Lu, C.; Tariq, M.; Xiao, Q.; Zhang, W.; Huang, K.; Lu, Q.; Lin, K.; Liu, Z. The response and tolerance mechanisms of lettuce (Lactuca sativa L.) exposed to nickel in a spiked soil system. Chemosphere 2019, 222, 399–406. [Google Scholar] [CrossRef] [PubMed]
  59. EFSA Panel on Contaminants in the Food Chain (CONTAM); Schrenk, D.; Bignami, M.; Bodin, L.; Chipman, J.K.; del Mazo, J.; Grasl-Kraupp, B.; Hogstrand, C.; Hoogenboom, L.; Leblanc, J.-C.; et al. Update of the risk assessment of nickel in food and drinking water. EFSA J. 2020, 18, e06268. [Google Scholar] [PubMed]
  60. World Health Organization. GEMS/Food Regional Diets: Regional per Capita Consumption of Raw and Semi-Processed Agricultural Commodities/Prepared by the Global Environment Monitoring System/Food Contamination Monitoring and Assessment Programme (GEMS/Food), Rev. ed.; World Health Organization: Geneva, Switzerland, 2003. [Google Scholar]
  61. Adamo, P.; Iavazzo, P.; Albanese, S.; Agrelli, D.; De Vivo, B.; Lima, A. Bioavailability and soil-to-plant transfer factors as indicators of potentially toxic element contamination in agricultural soils. Sci. Total Environ. 2014, 500–501, 11–22. [Google Scholar] [CrossRef]
  62. EFSA Panel on Contaminants in the Food Chain (CONTAM). Scientific Opinion on the risks to public health related to the presence of chromium in food and drinking water. EFSA J. 2014, 12, 3595. [Google Scholar]
  63. Scientific Committee on Food Opinion of the Scientific Committee on Food on the Tolerable Upper Intake Level of Zinc; European Commission, Health Consumer Protection Directorate-General: Brussels, Belgium, 2003.
  64. Baldwin, K.R.; Shelton, J.E. Availability of heavy metals in compost-amended soil. Bioresour. Technol. 1999, 69, 1–14. [Google Scholar] [CrossRef]
  65. Bashir, M.; Wang, X.; Naveed, M.; Mustafa, A.; Ashraf, S.; Samreen, T.; Nadeem, S.; Jamil, M. Biochar Mediated-Alleviation of Chromium Stress and Growth Improvement of Different Maize Cultivars in Tannery Polluted Soils. Int. J. Environ. Res. Public Health 2021, 18, 4461. [Google Scholar] [CrossRef] [PubMed]
  66. Dala-Paula, B.M.; Custódio, F.B.; Knupp, E.A.; Palmieri, H.E.; Silva, J.B.B.; Glória, M.B.A. Cadmium, copper and lead levels in different cultivars of lettuce and soil from urban agriculture. Environ. Pollut. 2018, 242, 383–389. [Google Scholar] [CrossRef]
  67. Khan, S.; Rehman, S.; Khan, A.Z.; Khan, M.A.; Shah, M.T. Soil and vegetables enrichment with heavy metals from geological sources in Gilgit, northern Pakistan. Ecotoxicol. Environ. Saf. 2010, 73, 1820–1827. [Google Scholar] [CrossRef]
  68. Luo, C.; Liu, C.; Wang, Y.; Liu, X.; Li, F.; Zhang, G.; Li, X. Heavy metal contamination in soils and vegetables near an e-waste processing site, south China. J. Hazard. Mater. 2011, 186, 481–490. [Google Scholar] [CrossRef] [PubMed]
  69. Wang, Y.; Qiao, M.; Liu, Y.; Zhu, Y. Health risk assessment of heavy metals in soils and vegetables from wastewater irrigated area, Beijing-Tianjin city cluster, China. J. Environ. Sci. 2012, 24, 690–698. [Google Scholar] [CrossRef]
  70. Shu, W.; Ye, Z.; Lan, C.; Zhang, Z.; Wong, M. Lead, zinc and copper accumulation and tolerance in populations of Paspalum distichum and Cynodon dactylon. Environ. Pollut. 2002, 120, 445–453. [Google Scholar] [CrossRef]
Figure 1. Accumulation curves of PTE content in lettuce leaves of plants growing in non-amended soil (S), soil amended with cork powder (SC) and soil amended with horse manure (SE): (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Figure 1. Accumulation curves of PTE content in lettuce leaves of plants growing in non-amended soil (S), soil amended with cork powder (SC) and soil amended with horse manure (SE): (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Environments 08 00045 g001
Figure 2. Transfer factor (TF) for each PTE and each treatment, non-amended soil (S), soil amended with cork powder (SC) and soil amended with horse manure (SE): (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Figure 2. Transfer factor (TF) for each PTE and each treatment, non-amended soil (S), soil amended with cork powder (SC) and soil amended with horse manure (SE): (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Environments 08 00045 g002
Figure 3. Tolerance Index (TI) for each PTE and each treatment, non-amended soil (S), soil amended with cork powder (SC) and soil amended with horse manure (SE): (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Figure 3. Tolerance Index (TI) for each PTE and each treatment, non-amended soil (S), soil amended with cork powder (SC) and soil amended with horse manure (SE): (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Environments 08 00045 g003
Figure 4. Clusters obtained using the PAM method for the effects of the 5 PTE under study: (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Figure 4. Clusters obtained using the PAM method for the effects of the 5 PTE under study: (a) Cd; (b) Pb; (c) Ni; (d) Cr; (e) Zn.
Environments 08 00045 g004aEnvironments 08 00045 g004bEnvironments 08 00045 g004c
Table 1. Soil characterization.
Table 1. Soil characterization.
Parameter Value
Conductivity (1:2) (mS cm−1) 0.10 ± 0.02
pH (H2O) (1:2.5) 6.9 ± 0.1
Organic matter (g kg−1) 13.6 ± 0.2
Extractable P (mg kg−1) 73.8 ± 5.2
Extractable K (mg kg−1) 57.5 ± 4.4
Ammoniacal nitrogen (N-NH4) (mg kg−1) 2.35 ± 0.15
Nitric nitrogen (N-NO3) (mg kg−1) <1.0
Extractable micronutrients (mg kg−1)Fe31.1 ± 1.9
Cu4.8 ± 0.2
Zn1.4 ± 0.1
Mn35.2 ± 2.0
Table 2. PTE mass fractions used in the pot experiment.
Table 2. PTE mass fractions used in the pot experiment.
PTEMass Fractions (mg kg−1)Applied Form
non essentialCd01.53612CdCl2.5/2 H2O
Table 3. Parameters of the models fitted to the PTE accumulation curves.
Table 3. Parameters of the models fitted to the PTE accumulation curves.
Hyperbolic Model
CdS222.3 ± 35.416.8 ± 4.00.9955
SC143.9 ± 9.99.8 ± 1.20.9980
SE133.5 ± 18.410.6 ± 2.50.9926
NiS90.8 ± 15.293.1 ± 39.70.9476
SC115.2 ± 28.4146.0 ± 77.30.9351
SE88.2 ± 11.752.1 ± 22.50.9419
Linear model
CrS0.0037 ± 0.00032.313 ± 0.1320.9826
SC0.0045 ± 0.00032.288 ± 0.1040.9906
SE0.0046 ± 0.00032.404 ± 0.1280.9877
PbS0.0076 ± 0.00050.719 ± 0.2880.9897
SC0.0084 ± 0.00141.349 ± 0.8450.9282
SE0.0081 ± 0.00212.087 ± 1.2690.8343
ZnS0.41 ± 0.0317.6 ± 20.40.9812
SC0.42 ± 0.0121.1 ± 7.20.9977
SE0.49 ± 0.029.9 ± 11.70.9955
Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Share and Cite

MDPI and ACS Style

Moreira, I.; Leitão, I.; Mourato, M.P.; Martins, L.L. Comparison between a Traditional (Horse Manure) and a Non-Conventional (Cork Powder) Organic Residue in the Uptake of Potentially Toxic Elements by Lettuce in Contaminated Soils. Environments 2021, 8, 45.

AMA Style

Moreira I, Leitão I, Mourato MP, Martins LL. Comparison between a Traditional (Horse Manure) and a Non-Conventional (Cork Powder) Organic Residue in the Uptake of Potentially Toxic Elements by Lettuce in Contaminated Soils. Environments. 2021; 8(5):45.

Chicago/Turabian Style

Moreira, Inês, Inês Leitão, Miguel P. Mourato, and Luisa L. Martins. 2021. "Comparison between a Traditional (Horse Manure) and a Non-Conventional (Cork Powder) Organic Residue in the Uptake of Potentially Toxic Elements by Lettuce in Contaminated Soils" Environments 8, no. 5: 45.

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop