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Article

Physical, Chemical, and Microbiological Characterization of Kettara Mine Tailings, Morocco

by
Leila Benidire
1,2,
Sofia I. A. Pereira
3,
Souad Loqman
4,
Paula M. L. Castro
3 and
Ali Boularbah
1,5,*
1
Laboratoire de Bioressources et Sécurité Sanitaire des Aliments, Faculté des Sciences et Techniques, Université Cadi Ayyad, Boulevard Abdelkrim Khattabi, BP 549, Marrakech 40000, Morocco
2
Ecole Supérieure de Technologie, Université Cadi Ayyad, El Kelâa des Sraghna, Marrakech 40000, Morocco
3
CBQF—Centro de Biotecnologia e Química Fina, Laboratório Associado, Escola Superior de Biotecnologia, Universidade Católica Portuguesa, Rua Diogo Botelho 1327, 4169-005 Porto, Portugal
4
Laboratory of Microbiology and Virology, Faculty of Medicine and Pharmacy, Cadi Ayyad University, P.O. Box 7010, Marrakesh 40000, Morocco
5
Center of Excellence for Soil and Africa Research in Africa, Agrobio Sciences Program, Université Mohammed VI Polytechnique (UM6P), Benguerir 43150, Morocco
*
Author to whom correspondence should be addressed.
Soil Syst. 2022, 6(1), 23; https://doi.org/10.3390/soilsystems6010023
Submission received: 20 November 2021 / Revised: 9 February 2022 / Accepted: 15 February 2022 / Published: 23 February 2022
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Abstract

:
The mining industry is of major importance to Morocco’s economy. However, the abandoned pyritic mines are a source of potentially toxic elements that can cause the disruption of the surrounding ecosystems, constituting a huge threat to wellbeing and human health. The present study aimed to analyze the physical and chemical characteristics of different types of tailings and to investigate the microbial populations of acidophilic bacteria involved in the oxidation of pyrite. Coarse and fine tailings collected from different zones of the mine (dike and pond) at two different depths (oxidized and non-oxidized residues) were analyzed for their pH, electrical conductivity, total organic carbon, total nitrogen, available P, major elements, and pseudo-total metal concentrations. The abundance of acidophilic bacteria was determined, and some acidophilic bacterial strains were isolated and tested for their metal tolerance. Tailings showed a pH ≈ 2, very low nutritional content, and high concentrations of Cu, As, Zn, and Pb, which were higher in the non-oxidized samples. The microbial counts of iron- and sulfur-oxidizing bacteria were higher than heterotrophic bacteria, with the highest numbers detected in the oxidized fine tailings. The five acidophilic bacteria isolated from the tailings were affiliated to genera Alicyclobacillus and Sulfobacillus, commonly found in this kind of environment.

1. Introduction

Soil is a dynamic system that provides a myriad of ecosystems services divided into four main categories: provisioning, supporting, regulating, and cultural services [1,2]. Ecosystems services ensure human well-being and rely on the interaction between the different soil components, including mineral and organic fractions, pore air, etc., and living organisms such as bacteria, fungi, protozoa, and macroinvertebrates [3].
The mining sector underpins the economic development of many countries [4]; however, intensive mining activity often leads to the disruption of natural ecosystems, causing high biodiversity losses [5,6,7].
Mining processes such as grinding, washing, and ore concentration, generate large amounts of waste rocks and tailings, which are heavily contaminated with metals easily dispersed into mine surrounding areas by wind and water erosion [8,9,10,11,12]. Mining wastes containing metal sulfide minerals, such as pyrite and pyrrhotite, are a global concern as they can suffer chemical and biological oxidation leading to acid mining drainage (AMD) [13,14]. These highly acid streams will contribute to amplifying the dispersion of metallic pollutants, causing the subsequent contamination of underground and surface water and deterioration of fertile soil layers [15].
Despite the harsh conditions for microbial growth, several autotrophic and heterotrophic bacterial communities colonize mine tailings and AMD [16,17,18]. The role of acidophilic bacteria in sulfur-containing mining wastes is controversial as sulfur- and iron-oxidizing bacteria can promote acid generation and metal mobilization, while heterotrophic and sulfur- and iron-reducing bacterial communities can be applied in bioremediation approaches to reduce the impact of mining activities on ecosystems [17,19]. Microbial-based strategies to reclaim mining areas encompass several mechanisms, including the formation of soluble metal chelates by the release of organic acids (bioleaching), enzyme-catalyzed reactions, mineralization, absorption of contaminants and/or sorption on the surface of cells, and extracellular sequestration [20].
The environmental damage caused by sulfide-containing mining wastes urge remediation strategies tailored for these degraded areas. In the present study, we aimed at evaluating the physical, chemical, and microbiological properties of coarse and fine tailings recovered from non-oxidized and oxidized zones in an abandoned pyrrhotite mine. We also intended to isolate and identify metal-tolerant acidophilic bacteria present in tailings for further application in bioremediation strategies.

2. Materials and Methods

2.1. Area of Study and Sampling

The Kettara mine is in the northeast region of Morocco in the central area of Jebilet massif, approximately 35 km from Marrakech city. This mine was heavily exploited from 1964 to 1981, with a production of more than 5.2 million tons of pyrrhotite enriched with high levels of sulfide minerals (16–145 mg g−1 of sulfur) [21]. The extraction of pyrrhotite generated high amounts of tailings which were deposited over an area of approximately 16 ha [8,11]. The Kettara mine tailings can be classified as coarse (fine gravel)—deposited in the 15-m high dike and in 1-m high tailings piles; and fine (silt)—deposited in the tailings pond [21]. The climate in the Kettara region is arid, with an average annual rainfall and temperature of 300 mm and 20 °C, respectively. The area in the vicinity of the mining dump is mainly colonized by heterogeneous herbaceous vegetation with scarce patches of spontaneous plants [22].
Composite samples of coarse and fine tailings were collected from the Kettara mine (Figure 1). Two samples were taken from the dike (31°52′25.4″ N, 8°10′43.9″ W) consisting of oxidized and non-oxidized coarse tailings (OC and NOC, respectively), while the other two samples were collected from the tailings pond (31°52′25.9″ N, 8°10′41.8″ W) consisting of oxidized and non-oxidized fine tailings (OF and NOF, respectively). The degree of oxidation was evaluated visually according to Hakkou et al. [21] who also confirmed it by mineralogical analysis. The oxidized layer was characterized by yellow to orange color, while the non-oxidized layer had a blue-grey color for fine tailings and a brown-red color for coarse tailings. The oxidized layer thickness varied between 5 and 15 cm. Two samples of runoff water (RW1, RW2) were also collected from the tailings pond during the rainy season.
The samples from coarse and fine tailings were collected using a thoroughly cleaned and disinfected shovel. The samples were then placed in sterile plastic bags for physical, chemical, and microbiological analysis. The runoff samples were collected in sterile polypropylene screw vials for chemical characterization. All samples were transported to the laboratory in an icebox and stored at 4 °C overnight. Bacterial isolation and enumeration were carried out within 48 to 72 h of collection.
Prior to physical and chemical analyses, the tailings samples were weighed and dried for 48 h at 45 °C. The samples were subsequently weighed, and the water content was calculated. Then, the samples were homogenized, sieved through a 2 mm mesh, and stored in sealed plastic bags until analysis. The pH and electrical conductivity were directly measured in runoff water in situ using a multi-parameter water quality analyzer (Orion 4-Star Portable pH/Conductivity Meter from Thermo Fisher Scientific, Waltham, MA, USA). For tailings, the measurements were made in the laboratory in aqueous solutions (1:2.5 and 1:5 w/v). The total organic carbon was determined by the dichromate oxidation method [23], while the total nitrogen and the available phosphorus were determined by Kjeldahl and molybdenum blue methods [24], respectively.

2.2. Multi-Element Analysis

The tailings samples were digested at high temperature using a mixture of HNO3/Br2/HF/HCl (2:1:1:1) as described by [25]. Briefly, 0.5 g of dry sample (particle size <2 mm) in a borosilicate flask was first mixed with HNO3 and gently boiled on a hot plate at 90 °C until a clear solution was obtained. Then, liquid bromine (Br2), HF, and HCl were successively added, and the mixture was heated (100 to 200 °C) until total digestion. The flask content was then evaporated to dryness and the extract was resuspended in ultrapure acidified water (2% nitric acid), filtered (<0.45 μm, ashless filter paper), and stored in polyethylene containers until analysis. The following elements Al, As, Ba, B, Ca, Co, Cr, Cu, Fe, Mg, Mn, Ni, Pb, S, Ti, and Zn were measured in acid digested samples using inductively coupled plasma–atomic emission spectroscopy (ICP-AES, Perkin Elmer Optima 3000, Norwalk, CT, USA).
The concentrations of Cu, Zn, and Pb in runoff water were determined by flame atomic absorption spectrometry (FAAS, Model Perkin Elmer AAnalyst 400, Waltham, MA USA). In prior analysis, water samples were filtered with an ashless filter paper to remove any particles and then acidified with nitric acid.

2.3. Enumeration of Indigenous Acidophilic Bacteria of Mine Tailings

The abundance of indigenous acidophilic bacteria including iron-oxidizing bacteria (IOB), sulfur-oxidizing bacteria (SOB), and heterotrophic acidophilic bacteria (HAB) was determined in mine residues using the most probable number (MPN) method described by [26]. Briefly, 3 tubes MPN series with different growth media (pH = 2.5) were inoculated with a bacterial suspension prepared from tailing samples and their dilutions. The bacterial growth after an incubation period of 15 days at 30 °C with agitation (150 rpm) was assessed. The number of total bacteria present was then estimated by counting the number of tubes giving a positive reaction (i.e., presence of turbidity) and comparing the pattern of positive results with Mac Grady tables. The iron-oxidizing acidophiles were quantified in TK liquid medium (per liter: 33.4 g of FeSO4·7H2O; 0.4 g of (NH4)2SO4; 0.4 g of MgSO4·7H2O, and 0.4 g of K2HPO4) [27]. Sulfur-oxidizing acidophiles were quantified using elemental sulfur or thiosulfate as a substrate for bacteria in modified 9KS medium (per liter: 3 g of (NH4)2SO4; 0.5 g of MgSO4 7H2O; 0.5 g of K2HPO4; 0.1 g of KCl; 0.012 g of Ca(NO3)2; and 1% (w/v) of elemental sulfur added) [28], while Luria-Bertani (LB) medium (per liter: 10 g of peptone; 5 g of yeast extract and 10 g of NaCl) was used for the quantification of HAB. A tube was considered positive in LB medium when turbidity in the culture medium was observed. For the TK medium, a positive result was estimated when the medium became orange, indicating the production of jarosite as a result of the oxidation of iron sulphates by bacteria [29]. Concerning acidophilic sulfur-oxidizing cultures, the tubes were found to be positive if rod-shaped cells were visible under a microscope [29].

2.4. Isolation and Identification of Acidophilic Bacteria

2.4.1. Isolation

The acidophilic bacteria were isolated from oxidized and non-oxidized Kettara mine tailings and from runoff water in contact with the fine tailings using a pre-enrichment culture in Tryptone-Soy Broth (TSB; Biokar Diagnostics, Allonne, France) supplemented with iron (FeTSB; per liter: 0.25 g of TSB, 1.25 g of (NH4)2SO4, 0.5 g of MgSO4, 25 mM FeSO4). This medium was used as it allows the growth of iron- and sulfur-oxidizing bacteria and heterotrophic acidophilic bacteria [30]. For this purpose, 1 g of tailings (fine and coarse oxidized and non-oxidized) or 1 mL of runoff water was inoculated separately in 250 mL Erlenmeyer flasks containing 100 mL of FeTSB. All cultures were then incubated with agitation (150 rpm) at 30 °C for about 15 days. Five cycles of successive subcultures on liquid media have been carried out since successive subcultures of acidophilic bacteria strains under the same conditions help to obtain better cell growth in a solid medium. Periodically, microscopic observations were made to confirm the presence of microorganisms. Then, the cultures were transferred for FeTSB medium supplemented with agar (15 g L−1) and colonies isolated according to their different morphologies.

2.4.2. DNA Extraction

The genomic DNA of each isolate was extracted using the DNeasy UltraClean®Microbial Kit, Qiagen, Germantown, MD, USA, according to the protocol established by the manufacturer. The extraction procedure was performed using bacterial pellets obtained after centrifugation at 13,000× g for 5 min of 2 mL of a bacterial culture grown for 15 days in FeTSB medium.

2.4.3. Amplification of the 16S rRNA Gene and Sequencing

The 16S rDNA amplification was performed with universal primers 27F (50-GAGTTTGATCCTGGCTCAG-30) and 1492R (5′-ACCTTGTTACGACTT-3′) (MWG-Biotech, Huntsville, AL, USA). The PCR amplifications were performed in a 50 μL reaction mix containing: 1× buffer (Promega, Madison, WI, USA), 2.5 mM MgCl2, 0.2 mM dNTPs (Bioron), 1 μM of each primer, 1.5 μL of Dimethylsulfoxide, 0.5 U Taq polymerase (GoTaq, Promega, Madison, WI, USA), and 2 μL of DNA. The amplifications were performed in a Bio-Rad MJ Mini thermal cycler according to the following program: an initial denaturation step at 94 °C for 5 min, followed by 30 cycles of 94 °C for 1 min, 52 °C for 1 min, and 72 °C for 1 min, with a final extension at 72 °C for 10 min. A negative control was systematically included in each series of reactions to ensure the sterility of the different reagents used. PCR products were purified using the GRS PCR & Gel Band Purification kit (GRISP, Porto, Portugal) according to the manufacturer’s recommendations and sent to Macrogen Inc. (Amsterdam, The Netherlands) for sequencing. The nucleotide sequences were edited using the BioEdit software (version 7.0) and a similarity search was performed using the BLAST program (www.ncbi.nlm.nih.gov/blast (accessed on 10 November 2011)). Phylogenetic trees were constructed by the maximum likelihood method using MEGA software (version 6.0) [31]. The 16S rRNA sequences of acidophilic bacteria were deposited in GenBank under the accession numbers OL456194 to OL456197.

2.5. Metal Tolerance of Bacterial Isolates

The tolerance of bacterial isolates to Cu (CuSO4·5H2O), Zn (ZnSO4·7H2O), and Co (Co(NO3)2) was achieved by determining the minimum inhibitory concentration (MIC) in FeTSB medium supplemented with six concentrations of different metals. The concentrations varied between 317.73 to 7943.25 mg L−1 for Cu, from 3269 to 65,380 mg L−1 for Zn, and from 589.332 to 8250.648 mg L−1 for Co. Controls without metal but with bacterial inocula were also performed. All experiments were performed in triplicate. Isolates showing growth after 15 days of incubation at 30 °C were considered tolerant to the metal concentration tested.

3. Results

3.1. Physical and Chemical Characterization of Mine Tailings

The mine tailings showed a very acidic pH, ranging from 2.06 to 3.51 for fine residues and 2.40 to 2.80 for coarse residues. The non-oxidized samples showed lower pH than oxidized for both types of residues (Table 1). The mine tailings showed high EC (1.93–3.01 mS cm−1), with the highest values being recorded in the oxidized samples (2.45 and 3.01 mS cm−1 for fine and coarse residues, respectively). The Kettara mine tailings had very low nutrient content with TOC and P Olsen levels not exceeding 3.40 and 0.06 mg g−1, respectively. The TN was below the limit of detection in most samples.
The concentration of major elements and trace metals in oxidized and non-oxidized residues is shown in Table 2. The major elements found in the different mining residues were Fe, Mg, Al, S, Ca, and Ti. Iron was the most abundant element reaching values of 45.0 mg g−1 in oxidized fine samples (OF) and 296.0 and 339.0 mg g−1 in oxidized (OC) and non-oxidized (NOC) coarse residues, respectively, followed by Al with levels varying between 11.2 and 77.2 mg g−1 in oxidized (OF) and non-oxidized fine residues (NOF), respectively. Sulfur was the third most abundant element varying between 20.8 and 37.9 mg g−1. The oxidized and non-oxidized samples showed similar contents of S, however, coarse residues showed lower levels of S than fine. The different types of mine tailings were also characterized by high amounts of Mg (12.6 to 49.8 mg g−1), while Ca levels were low, not exceeding 10.1 mg g−1. The tailings samples were mainly contaminated with Cu, Zn, Pb, and As. The pseudo-total concentration of Cu in the different types of tailings were higher than those found for Pb, Zn, and As ranging from 0.65 mg g−1 in NOC and 1.89 mg g−1 in NOF samples. The Pb concentrations varied between 0.11 mg g−1 in fine residues (oxidized and non-oxidized) and 0.22 and 0.07 mg g−1 in oxidized and non-oxidized coarse residues, respectively. The pseudo-total Zn concentrations ranged from 0.05 to 0.57 mg g−1 with the highest concentration being recorded in non-oxidized fine residues (NOF), while the higher As concentrations were found in coarse residues (0.14–0.16 mg g−1).
The physical and chemical properties of runoff water collected near the Kettara mine are summarized in Table 3. The results showed that runoff waters were characterized by very acidic pH (≈2) and moderate salinity (≈7 mS cm−1). The runoff water samples presented high concentrations of Zn, Cu, and Pb, with the highest values being recorded in sample RW1 (45.81 mg of Cu L−1, 97.04 mg of Zn L−1 and 2.12 mg of Pb L−1).

3.2. Enumeration of IOB, SOB and HAB

The MPN of acidophilic bacteria in tailings and contaminated runoff waters collected in the Kettara mine are shown in Table 4. The number of cells of iron (IOB)- and sulfur (SOB)-oxidizing bacteria varied according to the type of tailing and the oxidation status. The IOB and SOB were more abundant (+2–3 log units) than heterotrophic bacteria. The highest counts of IBO, SBO, and HAB were detected in oxidized fine tailings (6.5 × 105, 5.9 × 105, 3.1 × 102 CFU g−1 dry weight, respectively). In coarse residues, no meaningful differences were observed between oxidized and non-oxidized samples, except for IOB which were more abundant (+1 log unit) in oxidized residues.
All bacterial groups were also detected in runoff waters, although in a lower number for SOB. On the other hand, the abundance of IOB was slightly higher in runoff waters than in tailings.

3.3. Isolation and Identification of Acidophilic Bacteria

The oxidation of ferrous ions was observed in the enrichment culture of FeTSB medium (pH 2.5), reflecting the growth of acidophiles in this growth medium. Based on morphology, color, and growth rate, five strains were isolated from the Kettara tailings and runoff waters. The morphological characteristics of these strains are reported in Table 5. The isolates AMK1 and AMK5 were able to grow on FeTSB, TK, and 9KS medium, being classified as mixotrophic, whereas the isolates AMK2, AMK3, and AMK4 were only able to grow in FeTSB medium, being for that reason considered heterotrophic.
The partial sequences of the gene coding for the 16S rRNA of strains AMK1, AMK3, AMK4, and AMK5 were compared with sequences representative of the species Alicyclobacillus and Sulfobacillus (Figure 2). According to the phylogenetic tree, the strains AMK3 and AMK5 had a high similarity with the genus Alicyclobacillus sp., while the strains AMK1 and AMK4 were closely related to the Sulfobacillus species. It was not possible to identify strain AMK2.

3.4. Metal Tolerance

According to the results presented in Table 6 all strains showed a high metal tolerance. The strains AKM1 and AKM3 showed the highest tolerance to Cu with a maximum MIC value of 3177.30 mg L−1. The strains AKM1, AKM2, and AKM4 showed the best performance for Zn (MIC: 26,152–39,288 mg L−1) and for Co (MIC: 2357.33 mg L−1). The strain AKM5 showed the lowest resistance to Cu (635.46 mg L−1) and AKM2 to Zn (6538 mg L−1) if compared to other strains, while AKM1 was the strain with a higher tolerance to all metals.

4. Discussion

4.1. Physical and Chemical Properties of Mine Tailings and Runoff Water

Increasing knowledge of the physical, chemical, and microbiological properties of mine tailings, more specifically of sulfide residues, is crucial to assess their impact on ecosystems. It also provides valuable information to help the selection of methods suitable for remediation. The physical, chemical, and mineralogical characterization of Kettara mine tailings has already been the subject of several studies [8,10,21,33]. However, little is known about the acidophilic bacterial populations able to oxidize pyrrhotite and to generate AMD harbored in Kettara mine tailings. The present study is therefore a pioneer not only for the mines near Marrakesh but also in the entire country.
In this study, tailings showed lower S levels (20.8 to 37.9 mg g−1) than those reported by Hakkou et al. [21], where S levels reached in some samples 145.0 mg g−1. Despite the low S content, tailings showed a very acid pH (average value of 2.7), suggesting that the increasing acid generation may be due to the lack of neutralizing capacity of the substrate [34,35]. It was also observed that a lower total S content in coarse tailings if compared to fine suggested a depletion of this element over time in surface horizons. This is related to the particle sizes in the coarse tailings deposit which facilitates the access of water and oxygen to the fine particles which are more reactive thus leading to the oxidation of the sulfurous minerals of the waste rock and therefore a large production of sulfuric acid [36,37].
The lowest pH values were recorded in non-oxidized samples of both types of tailings (fine and coarse), which can be explained by the drainage of acidic waters from the surface to the deeper zones of tailings. The Kettara mine tailings presented very low contents of TOC, TN, and available P, constituting major limiting factors for the establishment and development of plants in these areas [8,22,38,39]. Indeed, low levels of organic matter and nutrients are commonly found in mine tailings [40,41,42,43], which may be explained by the fact that these wastes have resulted from a succession of ore processing stages [44].
The Kettara mine tailings showed very high concentrations of metals compared to the mean concentrations in the earth’s crust [32]. Indeed, these high levels are a direct consequence of the processes of extraction and concentration of ores. Some metals (Cr, Co, Zn, Pb and Cu) are presented at lower concentrations in the oxidized layers than in the non-oxidized, indicating that these elements are leached from the upper areas of residues and then concentrated at the bottom. The pseudo-total concentrations of Zn, Pb, As, and Cu in oxidized and non-oxidized residues were, in most cases, above the recommended levels for residential and parkland uses as defined by the Canadian Soil Quality Guidelines. For Cu and As, the concentrations registered were on average 12 and 9 times higher, respectively, than the recommended limits for industrial use, indicating that both elements were in very dangerous concentrations in tailings.
These results suggest that tailings from this mine are likely to generate AMD and corroborate previous studies carried out in this mining area [8,10,21]. The runoff water also showed very acidic pH values (2.19 to 2.23) and moderate electrical conductivity (6.81 to 7.32 mS cm−1), exceeding 8 times the limit allowed for irrigation water (<0.75 mS cm−1) [45]. The concentrations of Cu and Zn in these waters were also very high (68.02–97.04 mg L−1 and 25.42–45.81 mg L−1, respectively) and greatly exceeded the allowable limits settled by FAO [46] for irrigation water (0.2 and 2 mg L−1 for Cu and Zn, respectively). The high concentrations of both metals in runoff waters were expected as both metals were part of the mineralogical composition of Kettara ore. In fact, these concentrations were similar to those found by El Khalil et al. [10].

4.2. Microbiological Properties of Mine Tailings and Runoff Water

In the present study, the acidophilic bacterial communities varied considerably between the oxidized and non-oxidized residues. Indeed, the highest MPN numbers for IOB, SOB, and HAB were detected in the upper layers of tailings, which can be explained by the aerobic nature of these bacteria [47], suggesting that pyrite is likely oxidized by these bacterial communities. These results are in agreement with previous studies, where it was found that soil microbial communities changed with depth, the highest cell numbers being detected in oxidized zones [48,49,50,51]. Moreover, Bruneel et al. [16] also reported that bacterial diversity was slightly greater in the oxidized zones compared to the non-oxidized residues of the Kettara mine. Heterotrophic bacteria are likely to exist using the little organic carbon released by chemolithotrophs in sulfide mine wastes [52,53]. The abundance of IOB and SOB communities were quite high compared to the values obtained by Mendez et al. [50]. However, the number of IOB reported by [48] was 10 times higher than the values found in this study, which could be explained by differences in physical and chemical properties and by the clime of the region. The results obtained in this study clearly showed that the sulfide minerals in the Kettara tailings are oxidized by biological and chemical processes, explaining the AMD in this area, which have been reported by several authors [8,10,21].
All bacterial strains isolated from tailings were acidophiles affiliated with previously identified genera in AMD ecosystems. The sequences of the 16S rRNA fragments of strains AMK3 and AMK5 showed a high similarity with heterotrophic and iron-oxidative bacteria classified in the genus Alicyclobacillus. Species of this genus, such as A. disulfidooxidans [54] and A. aeris [55], have often been identified in AMD. The strains AMK1 and AMK4 were closely related to Sulfobacillus, a genus that includes acidophilic mixotrophs with an optimal pH of 1.5–2.5 [56,57]. As mixotrophs, these species may switch between chemoheterotrophy and chemoautotrophy depending on the environmental conditions, which is an advantage in oligotrophic environments such as AMD [58,59]. In addition, many species belonging to these genera have also shown resistance to metals such as Cu, Ni, Co, and Zn which are commonly found in these environments [60]. All strains isolated from Kettara tailings showed very high tolerance to metals, with MIC values of up to 3177.30 mg L−1 for Cu, 39,228 mg L−1 for Zn and 2357.33 mg L−1 for Co, corresponding respectively to 50 mM of Cu, 600 mM of Zn, and 40 mM of Co. These concentrations were 2- to 3-fold lower than those reported by Johnson et al. [61] for Cu and Co (130 and 120 mM) and 2-fold higher for Zn (360 mM) in a strain of Sulfobacillus benefaciens isolated from bioleaching operations for sulfide ores. The high metal tolerance of these indigenous bacteria is attributed to the very high metal concentrations in mining wastes (0.650–1.89 mg Cu g−1, 0.05–0.57 mg Zn g−1 and 0.01–0.06 mg Co g−1) that largely exceed the average levels present in the earth’s crust (0.025 mg Cu g−1, 0.065 mg Zn g−1 and 0.024 mg Co g−1) [42]. Exposure to high concentrations of metals is therefore likely to exert selective pressure on bacterial communities favoring the emergence of highly metal-tolerant acidophilic bacteria [62]. Indeed, several authors have reported that bacteria isolated from mining areas that are highly contaminated are shown to exhibit high tolerance to different metals [63,64].

5. Conclusions

The Kettara tailings contain significant amounts of potentially toxic metal-rich sulfide minerals which can pose serious environmental threats. The physical, chemical, and microbiological parameters suggested the existence of chemical and biological processes responsible for the oxidation of sulfide minerals. This may cause the solubilization of metallic elements presented in millions of tons of mining waste rock, resulting in very acidic and highly metal contaminated runoff waters, as observed in this study.
These highly acidic, high-metal, and nutrient-deprived tailings harbor chemolithoautotrophic and heterotrophic acidophilic bacteria capable of oxidizing iron and sulfur compounds. The higher abundance of these bacterial communities is correlated with a high proportion of the oxidation of pyrite in the upper layers of tailings. This suggested that the oxidation of sulfide minerals is strongly influenced by the microbial activity in Kettara mine tailings.
Plants are not able to grow in mining wastes due to their inhospitable physical and chemical properties. This results in large areas devoid of vegetation cover and directly exposed to erosion, leading to a consequent contamination of the surrounding environment. Therefore, it is necessary to improve the quality of these wastes in order to facilitate the establishment of plants and to accelerate the recovery of these ecosystems. According to previous studies the combined use of chemical and biological remediation techniques is very often a suitable strategy to accelerate and increase the success of reclamation of mining areas either by enhancing tailings fertility or preventing AMD, rendering a viable approach for the remediation of the Kettara mine.

Author Contributions

L.B. designed the study, performed the experiments, and wrote the manuscript. S.I.A.P. carried out the DNA extraction and treatment of acidophilic bacteria sequences, wrote and revised the manuscript. S.L. contributed to the analysis of tailings and interpretation of the results. P.M.L.C. provided critical feedback and helped shape the final manuscript. A.B. conceived the original idea and oversaw overall direction and planning of this work. All authors have read and agreed to the published version of the manuscript.

Funding

This study was financially supported by the Convention de coopération CNRST-Morocco/FCT-Portugal, Centre National de Recherche Scientifique et Techniques [grant no. PPR 22/2015] and the project Phy2Sudoe—Advancing in the application of innovative phytomanagement strategies in contaminated areas of the SUDOE space (SOE4/P5/E1021), funded by the European Regional Development Fund (European Commission) through the V Interreg Sudoe Programme.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

All data generated or analyzed during this study are included in this published article.

Acknowledgments

The authors would like to thank the scientific collaboration of Fundação Ciência e Tecnologia (FCT) project UIDB/50016/2020. The authors would also thank to T. Hogg for correcting the English of this paper.

Conflicts of Interest

The authors declare that they have no known conflict of interest or personal relationships that could have appeared to influence the work reported in this paper.

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Soilsystems 06 00023 g001 550
Figure 1. Location and panoramic view of Kettara mine (A); AMD effluent (B); Coarse tailings (C,E); Fine tailings (D,F).
Figure 1. Location and panoramic view of Kettara mine (A); AMD effluent (B); Coarse tailings (C,E); Fine tailings (D,F).
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Soilsystems 06 00023 g002 550
Figure 2. Maximum likelihood phylogenetic tree based on partial 16S rRNA sequences, showing the relationships between the sequences of representative strains and their closest phylogenetic relatives. Bootstrap values based on 1000 replications are indicated at the nodes.
Figure 2. Maximum likelihood phylogenetic tree based on partial 16S rRNA sequences, showing the relationships between the sequences of representative strains and their closest phylogenetic relatives. Bootstrap values based on 1000 replications are indicated at the nodes.
Soilsystems 06 00023 g002
Table
Table 1. Physical and chemical properties of oxidized and non-oxidized fine and coarse tailings of Kettara Mine.
Table 1. Physical and chemical properties of oxidized and non-oxidized fine and coarse tailings of Kettara Mine.
Fine ResiduesCoarse Residues
OFNOFOCNOC
pH3.512.062.802.40
EC (mS cm−1)2.451.933.012.30
TOC (mg g−1)1.901.402.001.30
TN (mg g−1)0.40<dL<dL<dL
C/N8.25ndndnd
P Olsen (mg g−1)0.050.060.010.01
<dL: below detection limit; nd: not determined; EC: Electrical conductivity; TOC: Total organic carbon; TN: Total nitrogen; P Olsen: Available phosphorus. OF: oxidized fine residues; NOF: non-oxidized fine residues; OC: oxidized coarse residues; NOC: non-oxidized coarse residues.
Table
Table 2. Major elements and trace elements content in oxidized and non-oxidized fine and coarse tailings of Kettara mine.
Table 2. Major elements and trace elements content in oxidized and non-oxidized fine and coarse tailings of Kettara mine.
Fine ResiduesCoarse Residues
OFNOFOCNOC
Major Elements (mg g−1)
Mg13.849.820.712.6
Al11.277.240.127.5
Stotal37.934.920.821.7
Ca10.14.55.96.4
Fe405.0197.0296.0339.0
Ti1.12.02.83.1
Ba<dL<dl<dl<dl
Trace Metals (mg g−1)Earth’s Crust *
Cr0.030.100.060.070.1260
Mn0.131.120.580.350.7160
Co0.010.060.030.020.0240
Ni<dL0.030.010.010.056
Cu0.941.891.100.650.0250
Zn0.050.570.130.080.0650
As0.04<dL0.160.140.0017
Pb0.110.110.0700.220.0004
OF: oxidized fine residues; NOF: non-oxidized fine residues; OC: oxidized coarse residues; NOC: non-oxidized coarse residues; <dL: below detection limit; * Average levels in the earth’s crust [32].
Table
Table 3. Values of pH, electrical conductivity, and pseudo-total metal concentrations (Zn, Cu, and Pb) in runoff waters collected in Kettara mine spoil.
Table 3. Values of pH, electrical conductivity, and pseudo-total metal concentrations (Zn, Cu, and Pb) in runoff waters collected in Kettara mine spoil.
pHEC
(mS cm−1)		Trace Metals (mg L−1)
ZnCuPb
RW12.237.3245.8197.042.12
RW22.196.8125.4268.021.63
Table
Table 4. MPN-determined cell densities of iron-oxidizing (IOB), sulfur-oxidizing (SOB), and heterotrophic acidophilic (HAB) bacteria in residues (MPN g−1) and runoff waters (MPN ml−1) of Kettara mine.
Table 4. MPN-determined cell densities of iron-oxidizing (IOB), sulfur-oxidizing (SOB), and heterotrophic acidophilic (HAB) bacteria in residues (MPN g−1) and runoff waters (MPN ml−1) of Kettara mine.
SamplesFine ResiduesCoarse ResiduesRunoff Water
OFNOF OCNOC RW1RW2
IOB6.5 × 1054.8 × 1054.3 × 1058.9 × 1049.9 × 1058.6 × 105
SOB5.9 × 1057.3 × 1044.6 × 1045.5 × 1046.1 × 1038.3 × 103
HAB3.1 × 1021.2 × 1022.3 × 1021.0 × 1021.0 × 1021.3 × 102
OF: oxidized fine residues; NOF: non-oxidized fine residues; OC: oxidized coarse residues; NOC: non-oxidized coarse residues.
Table
Table 5. Phenotypic characteristics of bacterial strains.
Table 5. Phenotypic characteristics of bacterial strains.
Strain OriginGramMobilityMorphology of Colonies
ColorShapeBorderTrophic Level
AMK1RW+Not mobileRusty appearanceCircularRegularMixotrophic
AMK2OF+Not mobileOrangeCircularRegularHeterotrophic
AMK3OC+Not mobileOrangeStringyRegularHeterotrophic
AMK4NOF+Not mobileOrange with colorless edgesCircularRegularHeterotrophic
AMK5NOC+Not mobileRusty appearanceCircularRegularMixotrophic
OF: oxidized fine residues; NOF: non-oxidized fine residues; OC: oxidized coarse residues; NOC: non-oxidized coarse residues.
Table
Table 6. Minimum Inhibitory Concentration (MIC) for Cu, Zn and Co.
Table 6. Minimum Inhibitory Concentration (MIC) for Cu, Zn and Co.
Strains Nearest NeighborMIC (mg L−1)
CuZnCo
AKM1Sulfobacillus sp.3177.3039,2282357.33
AKM2Not identified1588.6565382357.33
AKM3Alicyclobacillus sp.3177.3026,1521178.66
AKM4Sulfobacillus sp.1588.6539,2282357.33
AKM5Alicyclobacillus sp.635.4613,0761178.66
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Benidire, L.; Pereira, S.I.A.; Loqman, S.; Castro, P.M.L.; Boularbah, A. Physical, Chemical, and Microbiological Characterization of Kettara Mine Tailings, Morocco. Soil Syst. 2022, 6, 23. https://doi.org/10.3390/soilsystems6010023

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Benidire L, Pereira SIA, Loqman S, Castro PML, Boularbah A. Physical, Chemical, and Microbiological Characterization of Kettara Mine Tailings, Morocco. Soil Systems. 2022; 6(1):23. https://doi.org/10.3390/soilsystems6010023

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Benidire, Leila, Sofia I. A. Pereira, Souad Loqman, Paula M. L. Castro, and Ali Boularbah. 2022. "Physical, Chemical, and Microbiological Characterization of Kettara Mine Tailings, Morocco" Soil Systems 6, no. 1: 23. https://doi.org/10.3390/soilsystems6010023

APA Style

Benidire, L., Pereira, S. I. A., Loqman, S., Castro, P. M. L., & Boularbah, A. (2022). Physical, Chemical, and Microbiological Characterization of Kettara Mine Tailings, Morocco. Soil Systems, 6(1), 23. https://doi.org/10.3390/soilsystems6010023

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