Effect of Temperature on Biobeneﬁciation of Bulk Copper-Nickel Concentrate with Thermoacidophilic Microbial Communities

: Bioleaching of the bulk copper–nickel sulﬁde concentrate was proposed as a method to remove nickel from it and to obtain a concentrate containing copper as chalcopyrite. This approach is based on the different refractoriness of sulﬁde minerals in ferric sulfate solutions and oxidation by acidophilic microorganisms. The bulk concentrate contained 10.8% copper in the form of chalcopyrite (CuFeS 2 ) and 7.2% nickel that occurred in pentlandite ((Ni,Fe) 9 S 8 ) and violarite (FeNi 2 S 4 ). Three microbial communities grown at 35, 40, and 50 ◦ C were used for bioleaching. The microbial community at 40 ◦ C was the most diverse in the genus and species composition. At all temperatures of the process, the key roles in bioleaching belonged to mixotrophic and heterotrophic acidophiles. The highest levels of nickel leaching of 97.2 and 96.3% were observed in the case of communities growing at 40 and 50 ◦ C, respectively. At the same time, the bioleach residue, which could be characterized as a marketable high-grade copper (chalcopyrite) concentrate, was obtained only at 40 ◦ C. This solid contained 15.6% copper and 0.54% nickel. Thus, the biobeneﬁciation of bulk sulﬁde concentrates can be a promising ﬁeld of biohydrometallurgy.


Introduction
The beneficiation of bulk concentrates of nonferrous metals, such as copper-nickel and copper-zinc sulfide concentrates, is aimed at obtaining high-grade selective concentrates, which are of current importance for the metallurgical industry [1]. However, the selective separation of bulk concentrates is often difficult due to the textural and structural properties of raw materials. As a result of the difficulties of selective metal concentration, relatively simply produced bulk concentrates can circulate in flotation circuits for a long time [1,2].
To achieve selective metal leaching, environmentally sound cost-effective and easyto-use technologies are required. These technologies include biohydrometallurgical approaches (particularly, bioleaching/biooxidation) that are applied at industrial mining and metallurgical enterprises worldwide for the recovery of metals from sulfidic raw materials [3][4][5][6]. These bio-approaches are based on the activity of communities of acidophilic chemolithotrophic microorganisms that oxidize ferrous iron, elemental sulfur (S 0 ), reduced inorganic sulfur compounds (RISCs), and sulfide minerals [7]. The significance of the application of biohydrometallurgy is associated with relatively low environmental hazards in comparison with conventional pyrometallurgical methods [8,9]. Biohydrometallurgy allows the processing of low-grade raw materials, products, and metallurgical wastes, with reduced emissions and discharges of toxic substances to air [6,10].
Low-grade copper ores (copper is mainly in secondary sulfides) and gold-bearing (pyrite-arsenopyrite and pyrite) ores are the best-studied raw materials involved in bioprocessing [11,12]. Chalcopyrite is one of the most refractory minerals in ferric sulfate solutions, which determines the low efficiency/intensity of biohydrometallurgical approaches used for chalcopyrite processing [13]. In that regard, the idea of selective mineral leaching, associated with chalcopyrite concentration in the solids, seems promising for the processing of refractory bulk concentrates [14]. The possibility of the selective removal of zinc from the copper-zinc concentrate during leaching with a ferric sulfate solution obtained with an acidophilic chemolithotrophic microbial community, as well as during bioleaching, has been previously reported [15][16][17]. The varying composition of minerals in the copper-zinc concentrate has shown that a higher chalcopyrite/sphalerite ratio improves the rate of the oxidation of sphalerite [18].
The study of the bioleaching of the violarite-pentlandite-chalcopyrite concentrate at 40 • C allowed the removal of nickel and the obtainment of a high-grade copper concentrate. Violarite has been shown to dissolve more rapidly than pentlandite during bioleaching of the copper-nickel concentrate, with higher rates of nickel sulfide dissolution at 40 • C as compared to 30 • C [23]. At 40 • C, the community of microorganisms was dominated by bacteria of the species Leptospirillum (L.) ferriphilum and Acidithiobacillus (At.) caldus, as well as Sulfobacillus (S.) spp. and archaea of the genera Cuniculiplasma and Ferroplasma (Fr.) as minor components. After 22 days of the bioleaching, the efficiency of nickel leaching reached 67.6% (30 • C) and 86.7% (40 • C), while the copper content in the bioleach residue increased by 2.7 and 5.7%, respectively [23].
Thermophilic bioleaching of a low-grade copper-nickel concentrate at high temperatures (65, 70, 72, 73, 74, and 75 • C) has also been compared [24]. The process at 70 • C allowed the highest copper and nickel extractions of 95% and 99%, respectively. More than 98% of nickel could be extracted at both 45 and 70 • C; however, the kinetics of leaching was slower at the former temperature. While 95% Cu extraction was shown at 70 • C, the final copper extraction of only 74% could be obtained at 45 • C [24].
Nevertheless, bioleaching of nickel-containing sulfidic raw materials has been significantly less studied than bioprocesses for copper and zinc extraction. Moreover, the roles of the members of the microbial communities, as well as microbial interactions during the biooxidation of raw materials containing nickel sulfides, are not entirely clear. The determination of the microbial diversity in the communities formed during the biooxidation of sulfidic copper-nickel raw materials, as well as the possible roles of the community members, are decisive in assessing whether the biohydrometallurgical approach is promising for particular raw materials under the selected conditions. Therefore, efficient bioleaching of metals from copper-nickel concentrates by microbial communities is of high importance from both the fundamental and practical standpoints. The industrial biooxidation of sulfide raw materials is usually associated with exothermal reactions leading to increased temperatures of the medium in bioreactors. In this research, we used thermoacidophilic microbial communities for the biobeneficiation of bulk copper-nickel concentrates for the first time.
The goal of this research was to study changes in solids composition depending on the temperature during bioleaching of the copper-nickel concentrate by thermoacidophilic microbial communities. In addition, this study aimed to choose the temperature that allows obtaining a residue considered a marketable copper (chalcopyrite) concentrate.

Copper-Nickel Concentrate
The bulk sulfide concentrate of the copper-nickel ore (Shanuch district, Kamchatka territory, Russia) flotation was the object of this study. The concentrate was composed of chalcopyrite, pentlandite, violarite, pyrrhotite, and pyrite. Quartz, chabazite, jarosite, plagioclase, chlorite, and albite were gangue minerals. The content of the main elements is shown in Table 1. Table 2 shows the content of sulfide minerals in the concentrate. The particle size of the concentrate was d 80 < 44 µm. The methods used for obtaining these data are provided in Section 2.5.

Analysis of Microbial Community
The structure of the original microbial consortia (inocula) grown at 35, 40, and 50 • C, as well as microbial communities formed at the end of the process, were assessed by cell morphology using phase-contrast microscopy and metabarcoding using the 16S rRNA gene hypervariable region (V3-V4). To obtain biomass for metabarcoding analysis, a suspension was centrifuged (100× g, 2 min) to precipitate solids, and cell pellets were further collected by centrifugation (5000× g, 15 min) of the obtained supernatant. The biomass was sequentially washed by centrifugation (10,000× g, 5 min) with the iron-free 9K medium First, the iron-free 9K medium with pH 1.5 was used to wash the biomass by centrifugation (10,000× g, 5 min). In the next step, the biomass was washed using the same medium but with a neutral pH [27]. Homogenization of the samples was carried out in a MagNA Lyser (Roche, Basel, Switzerland) device. DNA was extracted according to the standard protocol for MagNA Pure Bacteria Lysis Buffer (Roche, Basel, Switzerland). The 16S library preparation and sequencing were carried out according to Illumina protocol. Briefly, amplification of the extracted DNA with standard 16S rRNA gene primers, complementary to the V3-V4 region and containing 5 -Illumina adapter sequences, was performed. After that, individual amplicons were PCR-indexed and pooled. Sequencing of DNA libraries was carried out with a MiSeq instrument (Illumina, San Diego, CA, USA) and the Miseq reagent kit v3 (Illumina, San Diego, CA, USA). After demultiplexing was performed [28], reads containing the 16S rRNA primer sequences were filtered out with the CLC Genomics Workbench version 10.0 (Qiagen, Redwood City, CA, USA). To choose operational taxonomic units (OTU) and to carry out the taxon-based assignment, the QIIME open-source software pipeline [29] and the Silva132 database [30] were used. All parameters were set to default values. The analysis included ≈12,000-30,000 fragments (an average length, 449 nucleotides).
To identify microorganisms at the species level, analysis of the similarity of nucleotide sequences of the 16S rRNA gene fragments was carried out using the Nucleotide Basic Local Alignment Search Tool (BLAST; Bethesda, MD, USA, https://blast.ncbi.nlm.nih.gov/ Blast.cgi, accessed on 25 October 2021).

Bioleaching Procedure
Batch bioleaching of the concentrate was carried out in a 2.0 L bioreactor (working volume, 1.0 L). Before the beginning of the bioleaching, the bioreactor containing 10 g of the solid sample was supplemented with 1.0 L of inoculum containing ≈0.1 × 10 9 cells/mL at 50 • C and 0.8 × 10 9 cells/mL at 35 and 40 • C (the pulp density, 1%(w/v)). Thus, the inoculum volume was 100%(v/v). The initial pH value was 1.1-1.2. The pH of the pulp was monitored, and concentrated sulfuric acid was added when necessary to maintain the pH values. The experiments were carried out at a stirring speed of 500 rpm using an overhead 8-blade Rushton turbine impeller, with aeration (4 v/(v·min)). Once a day, distilled water was added to the bioreactor to compensate for evaporation losses. At the end of bioleaching, the pulp from the bioreactor was centrifuged at 2000× g rpm for 5 min, and the residue was washed three times with distilled water and dried to constant weight.

Analytical Methods
The relative number of cells in 1 mL was determined by ten-fold dilutions and subsequent direct counting in the Goryaev chamber using a Mikmed-2 microscope equipped with a phase contrast device (LOMO, Moscow, Russia).
The values of the pH and redox potential were measured with a pH-150MI pH metermillivoltmeter (Izmeritelnaya tekhnika, Moscow, Russia). The concentration of the Fe 3+ ions in the liquid phase was determined by complexometric titration [31]. The same method was used to determine the total concentration of iron after the reaction with ammonium peroxydisulfate. The concentration of ferrous iron ions was calculated as the difference between the total and ferric iron. Flame atomic absorption spectroscopy (FAAS) (Perkin Elmer 3100, PerkinElmer, Waltham, MA, USA) was used to determine the concentrations of copper and nickel.
Solids were analyzed by a wet chemical method, using 1:3 concentrated nitric acid/ concentrated hydrochloric acid at the boiling temperature of the mixture. This analysis was followed by FAAS for metals and gravimetric analysis with BaCl 2 for sulfur [32]. The mineralogical composition of solids was determined with X-ray diffraction microscopy (DRON-2 diffractometer, Burevestnik, St. Petersburg, Russia). The Rietveld refinement of the XRD patterns was used to evaluate the relative mineral phase amounts [33]. For image acquisition, a reflected light optical microscopy (Olympus BX51 microscope, Olympus, Tokyo, Japan) was used. The microscope was set to operate using polarized reflected light. The samples of solids were mounted in polished sections embedded in epoxy resin.
According to the following equation, mass loss (wt %) was calculated: where m r -the weight of bioleach residue (g); m in -the weight of the original sample (g). Metal recovery (wt %) was calculated from the following equation: where C is the metal concentration in pregnant leach solution (mg/L); V is a solution volume (L); β in is the metal content in the original sample (wt%).
All experiments were carried out in duplicate. Statistical processing was performed using Microsoft Excel 2013. The standard deviation (SD) of the arithmetic mean was calculated, and the significance of the results was assessed using Student's t-test at the significance level p ≤ 0.1.

Pregnant Leach Solution Characteristics
The physicochemical parameters of the liquid phase of the pulp were measured during the concentrate bioleaching. These were the pH value, the ambient redox potential, the concentration of ferrous and ferric iron, as well as the copper and nickel concentrations. Based on these values, the extraction of metals from solids was calculated. Figure 1 shows changes in the pH and redox potential values in different temperature modes. An abrupt increase in the pH value on the first day of the bioleaching required the addition of 1 mL of concentrated sulfuric acid for the processes at 35 and 50 • C and 2 mL at 40 • C. The dissolution of gangue minerals could lead to an increase in pH according to the reaction: In all cases, after sulfuric acid was added on the first day of bioleaching, the pH value remained relatively constant in the range of 1.1-1.2. This was due to the simultaneous microbial oxidation of ferrous iron increasing pH, and elemental sulfur oxidation producing sulfuric acid. The redox potential value decreased sharply on the first day of the process due to the consumption of ferric iron for the oxidation of sulfide minerals according to Equations (1)-(3), as well as the following reaction: After that, it increased relatively rapidly, within 1-7 days, due to the microbial oxidation of ferrous iron (Equation (5)), and stabilized at the level of 860-911, 930-943, and 845 mV (vs. standard hydrogen electrode (SHE)) at 35, 40, and 50 • C, respectively. A lower value of the redox potential at 50 • C was due to the low concentration of ferric iron in the liquid phase of the pulp, as a result of its more pronounced precipitation in the form of jarosite (see Table 3). An increase in the temperature during the bioleaching of sulfidic raw materials is known to lead to a greater jarosite formation [34,35]. Changes in the ferrous and ferric iron concentrations in the liquid phase of the pulp at different temperatures ( Figure 2) confirmed this conclusion. At all temperatures studied, the microbial communities oxidized ferrous iron completely and relatively rapidly. Beginning from the fourth day of bioleaching, the ferric iron concentration remained almost constant due to the low pulp density and relatively low iron content (21.8 wt %) in the concentrate.   Figure 3 shows the dissolution of nickel and copper during bioleaching of the concentrate at different temperatures. The lowest dissolution of nickel was recorded at 35 • C. At 40 and 50 • C, the final nickel dissolution was close and reached 97.2 and 96.3 wt%, respectively. The highest dissolution of copper was observed at 50 • C. A greater dissolution of chalcopyrite (as well as other sulfide minerals) by thermotolerant and moderately thermophilic microorganisms in comparison with mesophiles is well known. Among other factors, it is caused by an increase in the rate of chemical reactions with increasing temperatures [36][37][38]. Moreover, an increase in the solubility of chalcopyrite in ferric sulfate solutions has been repeatedly shown at relatively low values of the redox potential [39][40][41]. Figure 2 indicates that the value of the redox potential was, on average, 100 mV less during bioleaching of the concentrate at 50 • C than at 40 • C. Choosing a more suitable temperature of these two and taking into account that the goal of bioleaching was to achieve the greatest removal of nickel and to obtain a high-grade copper concentrate as solids, a community growing at 40 • C should be selected.

Solids Composition
The solids obtained after 22 days of bioleaching of the copper-nickel concentrate were subjected to chemical and mineralogical analyses to determine their compositions. The results of powder X-ray diffraction and light microscopy of polished sections of solids in comparison with the original concentrate are shown in Figures 4 and 5, respectively. The calculations of the mineral contents are presented in Table 3. The content of the main elements in bioleach residues is shown in Table 4. Analysis of the original concentrate composition indicated the presence of the following sulfide minerals: pentlandite, violarite, pyrrhotite, pyrite, and chalcopyrite. According to the data presented, pyrrhotite and violarite were almost completely removed from the concentrate during the bioleaching at all three temperatures. At 35 • C, a small amount of pentlandite was found in the solids, while it was almost completely dissolved at other temperatures. Pyrite was present in all three bioleach residues. However, its content was the highest in the solid obtained at 35 • C. These patterns agree with the refractoriness of sulfide minerals in ferric sulfate solutions due to the rest potential of the sulfide minerals [42]. Mason and Rice [43] have previously shown that the solubility of sulfide minerals during the bioleaching of nickel concentrate may be ranked in the following order: pyrrhotite > violarite > pyrite > pentlandite > chalcopyrite.   In general, bioleach residues obtained with thermotolerant and moderately thermophilic microbial cultures at 40 and 50 • C contained mainly chalcopyrite, jarosite, quartz, and chabazite. In fact, these residues were copper concentrates. At the same time, according to the Russian Federation standard (GOST R 52998-2008), only the solid obtained at 40 • C was a high-grade copper concentrate, which contained 15.6 wt% copper.

Microbial Community Structure
The original microbial consortium was composed of acidophilic bacteria and archaea that were different in their phylogenetic position (see Section 2.2 and Table 5) and physiological characteristics. This community included sulfur-and iron-oxidizing microorganisms as well as heterotrophic bacteria and archaea, which showed active growth within the temperature range of 35-50 • C. After subsequent culturing in the medium containing ferrous iron and elemental sulfur, certain changes in the community structure were recorded (Table 5). During 22 days of bioleaching, the cell populations were monitored using microscopy and metabarcoding analysis at the beginning and the end of the process. Although closely related microorganisms are usually not differentiated only based on the differences in the V3-V4 region, some bacterial and archaeal species were predicted due to the high variability of the V3-V4 regions within the corresponding genera [25].  While the initial cell numbers at 35 and 40 • C were similar (0.8 × 10 9 cells/mL), the original microbial community was more diverse in genera at 40 C. At 50 • C, the cell number was approximately one order of magnitude lower (0.1 × 10 9 cells/mL), and the microbial diversity was the lowest among all three variants (Table 5). In the course of copper-nickel concentrate bioleaching at 35 and 40 • C, the total cell numbers increased up to 2.5 × 10 9 cells/mL during the first seven days of bioleaching, and this pattern did not change until the end of the process. At 50 • C, the cell abundance increased until the last day of the process, reaching 3.0 × 10 8 cells/mL after seven days of cultivation and 6.0 × 10 8 cells/mL on day 22. Such variations in microbial growth patterns are mainly due to the different microbial structures of the communities at these temperatures. At temperatures over 45 • C, the most abundant sulfur-oxidizing and iron-oxidizing members, such as Acidithiobacillus spp. that reach the numbers of >10 9 cells/mL, are usually eliminated due to their temperature growth limit [7]. At the end of the process, communities formed at 35 and 40 • C included Acidithiobacillus spp., Sulfobacillus spp., and Alicyclobacillus spp.
It is noteworthy that metabarcoding analysis indicated the presence of Sulfobacillus spp. and Alicyclobacillus spp. at all temperatures studied ( Table 5). Strains of different Sulfobacillus species are mixotrophic bacteria capable of both sulfur and iron oxidation in the presence of small amounts of organic substances in the temperature range of 20-60 • C, with an optimum of >35-55 • C [7,44]. Except for 35 • C, the genus Sulfobacillus in the microbial communities was represented by the species S. thermosulfidooxidans. Nucleotide sequences of the 16S rRNA gene fragment showed 100% similarity with those of S. thermosulfidooxidans strains and only 99.1 and 98.7% similarity to other closest species: S. sibiricus and S. benefaciens, respectively. In contrast, another species, S. thermotolerans (100% similarity to the type strain S. thermotolerans Kr1 T , as well as other S. thermotolerans strains, and only 97.5% similarity to the second closest species S. thermosulfidooxidans), was identified at all temperatures: 35, 40, and 50 • C. Previously, this species has been shown to play a crucial role in biotechnological processes and to possess high metabolic and resistance capacities [25,44].
As mentioned above, in addition to Sulfobacillus spp., bacteria assigned to the genus Alicyclobacillus were also detected at all temperatures. Most Alicyclobacillus species are known to possess organoheterotrophic metabolism. However, Al. tolerans can grow heterotrophically or mixotrophically, oxidizing elemental sulfur, ferrous iron, and/or sulfide minerals in the presence of organic substances in the medium, with the optimum growth temperature of 37-42 • C [45]. Most probably, it was this species that was present in the microbial communities in these bioleaching experiments. This conclusion was based on 100% similarity to nucleotide sequences of the 16S rRNA gene fragments of Al. tolerans strains, including the type strain Al. tolerans K1 T [45] and another close strain Al. tolerans PCG-3 [46], and only 93.8% similarity to the second closest species Al. disulfidooxidans. Thus, in all communities, the genus Alicyclobacillus was represented by the species Al. tolerans characterized by mixotrophic/heterotrophic metabolism.
Iron-oxidizing bacteria Leptospirillum spp. (most probably, L. ferriphilum, according to the results of metabarcoding analysis) were identified in the original communities grown at 35 and 40 • C. At 40 • C, Leptospirillum cells reached ≈50% of the total microbial population at the beginning of cultivation, substantially decreasing in number in the course of the process due to the prevailing oxidation of sulfur by the community in the middle and at the end of the bioleaching. Moreover, at this temperature, the original microbial community and the community formed at the end of the bioleaching process showed the highest diversity and was also represented by facultatively chemolithoheterotrophic bacterium Acidibacillus sp. The latter was most probably related to the species Ac. ferrooxidans based on the nucleotide sequences of the 16S rRNA gene fragment, similarly to the data on the bioleaching of another copper-nickel concentrate at 40 • C [23]. Acidibacillus spp. belong to the phylum Firmicutes, which is well separated from Sulfobacillus and Alicyclobacillus spp. and capable of sulfur and/or ferrous iron oxidation [47]. At 40 • C, a heterotrophic iron-oxidizing extremely acidophilic actinobacterium assigned to the genus Ferrimicrobium, Fm. acidiphilium [48], was also identified. Fm. acidiphilium is the only known species belonging to this genus. In addition to heterotrophic/mixotrophic Alicyclobacillus strains, another heterotrophic member of the community, archaeon Cuniculiplasma sp. [49], was also detected in the original community formed at 40 • C. At 50 • C, an iron-oxidizing archaeon Acidiplasma sp., which is known to oxidize ferrous iron at increased temperatures [50], was functioning in the community during bioleaching of the concentrate.
Thus, the microbial community at 40 • C (both the original one and the community formed at the end of the bioleaching process) was the most diverse in the genus and species composition. At the same time, the crucial roles in bioleaching belonged to mixotrophic and heterotrophic acidophiles at all temperatures of the bioleaching process. This result underlines the pivotal role of mixotrophs and the underestimated contribution of heterotrophic microorganisms that facilitate the growth of chemolithotrophic community members and oxidation of the concentrate components by them.

Conclusions
In this study, bioprocessing of the bulk copper-nickel concentrate with different thermoacidophilic microbial communities was compared at three different temperatures: 35, 40, and 50 • C. According to the results, the optimum temperature for copper-nickel concentrate bioleaching proved to be 40 • C, at which a high-grade copper concentrate was obtained and nickel was almost completely leached. At increased temperature (50 • C), the oxidation level of chalcopyrite was higher and yielded a decreased content of copper in the final solid. At a lower temperature (35 • C), relatively high content of nickel remained in the bioleach residue. Analysis of the microbial communities involved in the process indicated that the crucial roles in bioleaching belonged to mixotrophic and heterotrophic acidophiles. This result underlined an underestimated role of heterotrophic microorganisms that indirectly contributed to the efficiency of the bioprocess, facilitating the growth and oxidation of the concentrate components by other chemolithotrophic community members. Insights into the patterns of the biooxidation of nickel sulfidic minerals with acidophilic microbial communities in different modes of the process are the key issues to intensify the biohydrometallurgical treatment of nickel-containing raw materials. Such studies can increase the attractiveness of biotechnologies to industrialists and improve their commercial applications.