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Article

Recycling Lead–Zinc Tailings for Cemented Paste Backfill and Stabilisation of Excessive Metal

by
Zhu Su
,
Qiusong Chen
*,
Qinli Zhang
and
Deming Zhang
School of Resources and Safety Engineering, Central South University, Changsha 410083, China
*
Author to whom correspondence should be addressed.
Minerals 2019, 9(11), 710; https://doi.org/10.3390/min9110710
Submission received: 14 October 2019 / Revised: 15 November 2019 / Accepted: 16 November 2019 / Published: 17 November 2019
(This article belongs to the Section Mineral Processing and Extractive Metallurgy)
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Abstract

:
This study demonstrates the feasibility of recycling lead–zinc tailing (LZT) as a cemented paste backfill (CPB) by considering the mechanical properties and environmental effects, thus providing an approach for safe and environmentally friendly treatment of LZT. First, the mechanical properties of CPB samples were tested. When the cement/tailing ratio was 1:6 and the slurry concentration was 70%, the maximum unconfined compressive strength (UCS) of the CPB cured for 28 days reaching 2.05 MPa, which could ensure safe mining. Then, the metals with pollution potential in the backfill slurry were investigated through static leaching. Finally, after adding immobilisation materials to stabilise excessive metals, the environmental stability of the CPB was demonstrated through dynamic leaching and a toxicity characteristic leaching procedure. The results show that the lead leached from the backfill slurry still exceeds the Chinese standard for groundwater quality (GB/T14848-2017 Class III). The addition of 2 mg/L polyaluminium sulfate (PAS) can further improve the strength of the CPB and maintain the environmental friendliness of the CPB. Therefore, the technology of recovering LZT as a CPB proposed in this study is an effective alternative to deal with LZT, which can help lead–zinc mines meet the requirements of cleaner production.

1. Introduction

Lead and zinc resources are abundant in China, and the total output of lead and zinc ranks first in the world. Lead and zinc are widely used in the chemical, light, electrical, machinery, military, and pharmaceutical industries [1]. In addition, lead also has uses in new nuclear and petroleum industries. However, the current development of the lead and zinc industry faces a prominent bottleneck, which is the contradiction between the continuous mining of lead and zinc and the protection of the ecological environment [2]. Large-scale mining of lead and zinc will inevitably produce a large amount of tailing. In China, lead–zinc mines have more poor ores and fewer rich ores and are often associated with heavy metals, such as cadmium, nickel, and arsenic. In addition, incompletely separated lead and zinc are left in the tailings [3]. These toxic heavy metals pose a great threat to the ecological environment. At present, many lead–zinc mines in China still discharge tailings into tailing ponds, which will cause two very severe problems: one is that the solid tailings and tailing slurry will seriously pollute the soil and water system around the reservoir area, and the other is that tailing ponds will face the risk of a dam break with the accumulation of tailings [4].
In recent years, the backfill mining method, which fills the stope with tailings as filling material, has been greatly developed in China [5]. Several scholars have investigated the types of backfill materials along with the backfilling process [6,7]. The goal of recycling lead–zinc tailing (LZT) as cemented paste backfill (CPB) is to eliminate two current major problems faced by lead–zinc mining: specifically, (1) the instability of the mine in the mining process [8,9,10,11,12,13]; and (2) the ecological damage caused by the accumulation of tailings.
In view of the first problem, the study focuses on whether the strength of the CPB can meet the requirements of safe underground mining. Backfill materials are subject to load conditions [14,15]. Because they are small and have no agglomeration, the tailings are only fillers in the CPB [16]. To meet reasonable strength requirements, it is necessary to obtain the optimum ratio of binder. In general, Portland cement is often used as the main binder, but some studies have also confirmed that fly ash, slag, and superplasticisers can substitute part of the Portland cement to improve the performance of CPB [17,18]. The optimum cementing ratio must consider two factors comprehensively: one is to meet the suitable strength of safe mining, and the other is to save cement consumption as much as possible and reduce the economic cost of mining under the premise of safe mining.
In view of the second problem, the study focuses on whether the tailings will further pollute the underground environment after recycling as part of the CPB. Many studies have pointed out that the surface accumulation of LZT will release numerous toxic heavy metal elements, such as mercury, lead, and cadmium [19,20,21]. Whether these elements will continue to dissolve after the CPB is filled in the stope requires further testing and verification. If it is determined that the heavy metals leached from the CPB during setting will still pollute the underground environment, the next research topic will be how to stabilise these heavy metals with pollution risk to keep the CPB environmentally friendly.
The purpose of this study is to develop a safe and environmentally friendly way to recover LZT, which will be recycled as a CPB in the laboratory. The fluidity and mechanical properties of the CPB will be determined using slump and unconfined compressive strength (UCS) tests, respectively. In addition, to meet the needs of protecting the underground ecological environment, this study will also discuss the chemical toxicity of the CPB, detect harmful heavy metals in the backfill slurry, and explore a stabilisation method to avoid the release of heavy metals.

2. Materials and Methods

2.1. Test Materials

2.1.1. Lead–Zinc Tailing

The LZT used in this study was taken from the Luoba lead–zinc mine in Gansu, China. The sampling position and process are shown in Figure 1. The specific sampling process at the site was as follows: (1) tailing slurry was collected using a filter cloth made into a container, and then low-concentration tailing slurry was poured into it; (2) regarding concentration and dewatering, the low-concentration tailing slurry was filtered using a filter cloth and was evaporated naturally to obtain a high-concentration tailing slurry. After the on-site sampling was completed, the high-concentration tailing slurry was transported to the laboratory of Central South University, China. The process of obtaining samples in the laboratory was as follows: the agglomerated tailings were chopped and sent to the oven for drying; the drying temperature was 55 °C, and the drying time was 10 h; due to the natural sedimentation of the tailing slurry during the sampling process and the agglomeration of some tailings during the drying process, the tailings were sieved and mixed.
At the same time, a small amount of the original low-concentration tailing slurry was also transported to the laboratory and dried under the same conditions as the LZT samples.
The major elemental composition of LZT samples and raw LZT was determined using a Philips MagiX PRO XR spectrometer (X-ray fluorescence; Amsterdam, The Netherlands). Table 1 shows that LZT samples represent the conditions of raw LZT on site.
The chemical composition of LZT was determined using X-ray diffraction (D8 Advance Diffractometer, Bruker AXS; Karlsruhe, Germany). As shown in Table 2, the main chemical components of LZT are SiO2 and CaO, which are beneficial to the strength development of the CPB [22]. The particle size distribution of LZT was measured using a Mastersizer 2000 particle size analyser (Malvern Instruments Ltd; Malvern, UK). The test results are shown in Figure 2. The physical properties of LZT are shown in Table 3. Because the median particle size is only 0.0281 mm and the proportion of particles smaller than 0.020 mm is 44.09%, LZT can be classified as medium tailings [23], which may have adverse effects on the strength development of the CPB [24]. The coefficient of uniformity (Cu) of LZT is greater than 12, and the coefficient of curvature (Cc) is less than 1, which indicates that LZT belongs to gap-graded aggregate [25]. When gap-graded aggregate is used as a backfill material, it will also cause slight adverse effects on the strength development of the CPB [26].

2.1.2. Binders

The binder used in this study was No.325 Portland cement, which was produced according to the common Portland cement standard of China [27]. Table 4 summarises the chemical compositions and physical properties of cement. The water used for static leaching was groundwater from the Luoba mining area, which was collected in sealed drums and transported to the laboratory of Central South University, China.

2.2. Test Methods

2.2.1. Cemented Paste Backfill Sample Preparation

The LZT, binders and water were mixed into 15 groups of slurries with different proportions. The cement/tailing ratios were 1:6, 1:8, 1:10, 1:15, and 1:20, and the mass concentration was 68%, 70% and 72%. The slurry was poured into the mixer at a speed of 200 r/min for mixing, and then the slurry was cast into the plastic mould with an internal size of 70.7 mm × 70.7 mm × 70.7 mm. After the initial setting of the slurry, the excess material on the surface of the mould was scraped with a shovel [28]. Finally, the samples were taken out of the mould after 24 h of setting and were placed in a curing box (YH -40B, Qingda, Tianjin of China) with constant temperature and humidity (20 ± 2 °C and 90% ± 5%, respectively).

2.2.2. Slurry Fluidity Test

Slurry fluidity was measured using a slump test [29]. The concrete operation was to place the conical slump cylinder (300 mm in height, 100 mm in diameter at the top, and 200 mm in diameter at the bottom) on the flat surface and press down tightly, then pour the stirred backfill slurry into the cylinder. After the slurry was filled with the slump cylinder, the slump cylinder was lifted steadily and vertically, and the process should be completed within 5–10 s. The slump cylinder was placed beside the slurry after lifting, and the vertical distance between the highest point of slurry and the top of the cylinder (in mm, accurate to 5 mm) was measured, which was the slump of the backfill slurry. The whole process from the start of loading to the end of lifting was completed in 150 s [30].

2.2.3. Unconfined Compressive Strength Test

In the mining process, CPB must meet the appropriate strength requirements, and different mines determine the minimum compressive strength of CPB according to actual production needs. The UCS of CPB samples were cured for 7, 14, and 28 days and were measured using a WDW-2000 rigid hydraulic pressure servo machine (Ruite, Guilin, China). The displacement rate of the machine load was 0.5 mm/min per minute [31]. Each test was repeated three times, and the average was used for further analysis.

2.2.4. Static Leaching

The static leaching test was conducted by adding a mixture of 90 g of LZT and 15 g of cement into 400 mL of groundwater, and the comparative leaching test was conducted by adding 90 g of LZT to 400 mL of groundwater. The leachate samples of both groups were fully stirred by centrifuge at first, then filtered with a 0.45-um filter at different time intervals within 48 h, and the leachate was collected for chemical analysis.

2.2.5. Stabilisation Test of Excessive Elements

The excessive elements could be further stabilised by adding corresponding immobilisation materials. The methods of stabilising excessive elements included chemical precipitation [32], coagulation precipitation, ion exchange [33] and adsorption. When the coagulation precipitation process was used to treat excessive elements, the dosage of coagulant was not much, but the precipitation speed was fast. At the same time, this process could adapt to a wide range of pH values, and the effect was obvious. The coagulation precipitation process was widely used in the stabilisation test [34].
The results of the static leaching test show that the leaching concentration of lead in the early setting of backfill samples does not meet the environmental standard of groundwater in China. Some scholars have pointed out that polyaluminium salt has a good stabilising effect on metal ions [35], and the commonly used polyaluminium salts include polyaluminium chloride (PAC) and polyaluminium sulfate (PAS). Yuan et al. [36] demonstrated that PAS had a better stabilisation effect on lead than PAC, which would be designed for the stabilisation test for lead in this study.
The PAS with concentrations of 1 mg/L, 2 mg/L, 2.5 mg/L, 3 mg/L, and 4 mg/L were added to the CPB slurry with the optimal ratio (cement/tailing ratio 1:6, slurry concentration 70%), which was determined in the previous test. The bleeding of each slurry after 24 h of setting was collected and filtered through a 0.45-μm filter for the detection of lead concentration.

2.2.6. Dynamic Leaching and Strength Retest

To investigate the strength change and environmental stability of the CPB after adding immobilisation materials to remove excessive elements, the UCS of the CPB samples with a curing age of 7, 14, and 28 days after adding immobilisation materials was measured, and then the samples were crushed into ash to maintain the same appearance as the LZT. The ash samples of different ages were dried at room temperature and screened with a 200-um screen, 10 g of which was added into 100 mL of deionised water, and then soaked in an incubator at 20 °C for 24 h. Moreover, 10 mL of the leachate was filtered through a 0.45-μm filter after 24 h, which was divided into two portions, one was acidified with 0.1 mL of 1 + 1 nitric acid (HNO3) solution for the ICP test, and the other for pH and conductivity detection. After the leachate was extracted, deionised water was added to the ash again, maintaining a solid-liquid ratio of 1:10. The leaching process was repeated five times to imitate the leaching of elements at different curing ages after the CPB is filled into the stope.

2.2.7. Toxicity Characteristic Leaching Procedure

The toxicity characteristic leaching procedure (TCLP) is the most commonly used toxicity characteristic leaching test, and the evaluation method of the release potential of heavy metals is recommended by the US Environmental Protection Agency (EPA). This test can simulate the process of metal elements permeating into groundwater after the CPB is filled into the stope [37,38]. The CPB samples of different curing ages were ground and sieved into ash of less than 9.5 mm in diameter. The ash was added to a 0.1 N acetic acid solution at a solid–liquid ratio of 1:20 and then was immersed in a rotary oscillator at a speed of 30 ± 2 rpm for 18 h. The leachate was filtered through a 0.45-μm filter after 18 h and was acidified with 0.1 mL of 1 + 1 HNO3 solution for the ICP test.

2.2.8. Chemical Measurement

The pH was measured using a pH meter (HSCAN 20 S, ±0.01, China). The conductivity was measured using a conductivity meter (ST20C, OHAUS, China). The metal element content was measured using inductively coupled plasma–atomic emission spectrometry (ICP-AES; Baird, PS-6, USA).

3. Results and Discussion

3.1. Feasibility of CPB Pipeline Transportation

The CPB slurry was prepared on the ground and then transported to the underground through the pipeline during the production process in the mine site. The premise of determining slurry concentration was that slurry fluidity met the requirements of pipeline transportation. Previous studies have indicated that the CPB slurry with a slump value of 190 to 270 mm can be piped to the stope via gravity or pumping [39]. The variation of the slump of the slurry with different concentrations is shown in Figure 3. The slump decreases with the slurry concentration increasing from 68% to 78%. When the slurry concentration exceeds 74%, the slump is less than 190 mm. At this time, the slurry does not have good fluidity, which may lead to blockage of the transportation pipeline.

3.2. UCS Test Results

The UCS test result is the primary parameter for the design of the backfill system in the mine, which is an important basis for evaluating the support performance of the CPB in the stope [40]. The UCS values of 15 groups of CPB samples with different cement/tailing ratios and mass concentrations are shown in Figure 4 after curing for 7, 14, and 28 days. Previous studies have pointed out that slurry concentration is an important factor affecting CPB strength [41]. The figure illustrates that the UCS value increases with the increase of slurry concentration under the same cement/tailing ratio. When the slurry concentration is 72%, the measured strength is the largest, which confirms that the slurry concentration can significantly affect the strength of the CPB. When the cement/tailing ratio is 1:6, and the slurry concentration is 72%, the maximum UCS value of CPB samples is 2.5 MPa at 28 days of curing. In summary, the strength of the CPB mainly depends on the hydration process of the cement in the slurry [42]. The LZT itself does not have cementation. According to the USC test results, synthetically considering the actual production needs and economic costs of the mine, the optimal CPB ratio is determined as the cement/tailing ratio of 1:6 and a slurry concentration of 70%.

3.3. Determination of Excessive Metal Elements by Static Leaching

Although the hydration process of cement will produce a certain mechanical strength, the heavy metals contained in the LZT still have the risk of contaminating groundwater. To investigate the leaching characteristics of heavy metals in the backfill slurry after transporting it underground, the concentration of heavy metals in the leachate of LZT and backfill samples was monitored during the first 48 h of static leaching. The pH of the leachate was measured at the beginning and end of the monitoring. The pH value of the leachate of LZT changed from 8.1 to 9.2, and that of the backfill samples changed from 11.5 to 12.9.
The variation of lead concentration in the leachate of LZT and backfill samples with time is shown in Figure 5. Lead is sourced from the residue of lead–zinc ore in the process of beneficiation, which will infiltrate the surrounding environment and does great harm to nature and humans. The figure shows that the concentration of lead in the leachate of backfill samples is higher than that in the leachate of LZT in the first two hours, which may be caused by the increase in pH in the soaking solution of the backfill samples after the addition of the alkaline cement. In a strong alkaline solution, the hydroxide formula of lead can be expressed by H2PbO2, which is acid-ionised by OH− ions in water, and lead mainly exists in the form of HPbO2− at this time. The specific chemical reaction follows:
H 2 PbO 2 ⇌ H PbO 2 − + H +
After 2 h, the lead concentration in the leachate of the backfill samples gradually decreased, which was due to the adsorption of the calcium silicate hydrate (C-S-H) gel generated by cement hydration process. The leaching concentration of lead gradually became steady after 30 h, and the measured concentration of lead at 48 h was 0.3 mg/L. According to the Chinese national standard (class III) [43] for groundwater quality, the concentration of lead should be less than 0.01 mg/L, so there is still a risk of groundwater pollution.
At the same time, the residual zinc in the beneficiation process of lead–zinc ore was also monitored. Figure 6 illustrates that the zinc concentration in the leachate of LZT remains relatively stable because the LZT soaking solution is weakly alkaline. When the pH is in the range of 7.5 to 10, zinc mainly exists in the form of precipitation [44], so the zinc concentration only increases slightly with time. The zinc concentration in the leachate of backfill samples tends to increase in the first two hours, which may be caused by the rapid increase of alkalinity in the soaking solution after adding cement. At this time, zinc exists in two forms, [Zn(OH)3]− and [Zn(OH)4]2−, in the leachate. In the later stage, with the hydration of the cement, the zinc concentration in the leachate of the backfill samples decreased rapidly. After 30 h, the leaching concentration of the zinc tended to be steady and far less than the standard of 1.0 mg/L in GB.
The concentration of other monitored heavy metal elements was also measured after 48 h. The concentrations of iron, chromium, arsenic, copper, and nickel were measured in the leachate of the LZT and backfill samples and are listed in Table 5. The table shows that the leaching concentration of metals in the leachate of the backfill samples decreased significantly due to the addition of the cementitious agent. After 48 h, the concentration of all heavy metals monitored in the leachate of the backfill samples was lower than the GB standard.

3.4. Optimum Dosage of Immobilisation Materials

The results of the lead concentration measurement in the bleeding of the CPB slurry after the addition of the immobilisation materials are shown in Figure 7. When the PAS concentration is less than 2 mg/L, the lead concentration in the bleeding gradually decreases with the increase of PAS dosage, which confirms that PAS has a good stabilisation effect on lead. The reason for this phenomenon may be that PAS has excellent water-decomposing performance. When PAS dissolves in neutral or slightly alkaline water, a colloidal precipitation A1(OH)3 is formed, which causes coagulation and adsorbs the lead in the solution. In addition, the figure shows that the removal rate of lead is the highest when the dosage range of PAS is 2–3 mg/L, and the concentration of lead in the bleeding is less than the GB standard when the dosage of PAS is 2 mg/L.

3.5. UCS Retest Results and Environmental Effects of CPB after the Addition of Immobilisation Materials

3.5.1. UCS Comparison

The strength of the CPB at different curing ages after the addition of the immobilisation materials was compared to the original strength. The UCS value of the CPB after adding 2 mg/L PAS is about 9% to 13% higher than the original UCS value from Table 6, which may because aluminium sulfate accelerates the hydration of tricalcium silicate (C3S), thus increasing the strength of the cement paste [45]. Therefore, the addition of immobilisation materials will not adversely affect the strength of the CPB and can further ensure the strength requirements of safe mining.

3.5.2. Environmental Stability of the CPB in Dynamic Leaching

To investigate the leaching characteristics of elements from the CPB in underground stope after adding 2 mg/L PAS, five-round dynamic leaching tests were conducted on CPB samples with a curing age of 7, 14, and 28 days. The dynamic leaching procedure can simulate the underground infiltration conditions under a natural environment [46].
The metal concentrations in the five-round dynamic leaching tests of the LZT were measured as shown in Figure 8. The concentration of metal ions in the first round of leaching dominates the five-round dynamic leaching, which indicates that the metal ions in LZT migrate easily with rainwater in the natural environment, reflecting that LZT has enormous environmental hazards if directly discharged into the natural environment without any treatment. The metal concentration of the five-round dynamic leaching tests of CPB samples with a curing age of 7 days was measured as shown in Figure 9. The leaching concentration of metal ions in CPB is quite low due to the addition of binder and immobilisation materials, which proves that they are well immobilised in the CPB. The leaching concentration of metal ions in each round satisfies the GB standard.
As shown in Figure 10, the leachate pH of CPB samples is obviously higher than that of LZT leachate, which is due to the alkalinity of the cement. The leachate pH of the CPB samples with curing age of 7 days and 14 days is significantly higher than that of CPB samples with a curing age of 28 days, which may be due to the continuous formation of OH− during the hydration process of the cement. In addition, the figure shows that the leachate conductivity of the CPB samples with a curing age of 7 days and 14 days has been declining, which also proves the continuity of the cement hydration process. The decrease in conductivity reflects the decrease of leaching ions, which is caused by two factors. One is the precipitation of some metal ions combined with OH-, and the other is the adsorption of a large number of ions by C-S-H gel produced by cement hydration. The leachate pH of the CPB samples with a curing age of 28 days remained relatively stable during the five rounds of dynamic leaching, concentrated in the range of 10.73 to 11.21, and the leachate conductivity also remained stable, which indicated that the hydration process of cement had been basically completed.

3.5.3. Environmental Evolution by TCLP

The TCLP extractable metals in LZT and CPB samples are presented in Table 7. The extractable concentration of metals in CPB samples is much lower than that in LZT. The concentrations of lead, zinc, iron, chromium, arsenic, copper, and nickel extracted by the CPB samples all meet the GB standard, which reflects that the concentration of heavy metals leaching from the CPB will not pollute the groundwater after the CPB is filled into the underground stope.
In conclusion, the dynamic leaching test and the TCLP verify that the leaching capacity of the heavy metal ions in the CPB can be effectively controlled, which has favourable environmental benefits.

4. Discussion

4.1. Potential of Significant Reuse of LZT as Backfill Material

As China attaches increased importance to the high-quality development of the economy, environmental protection issues in the mineral development process have become increasingly stringent. The main purpose of this study is to investigate the possibility of recycling LZT in a safe and environmentally friendly manner, which would help in reusing a significant amount of the produced LZT. The current work shows that LZT can be used as the main material for mine backfilling, which accounts for 86% of the total solid content of the CPB. The cement/tailing ratio is an important factor affecting the strength of the CPB. As shown in Figure 4, the higher strength was obtained in the CPB for higher cement content. Some studies have pointed out that, according to the requirements of safe mining, the UCS of the CPB cured for 28 days for stope bottom filling should be greater than 2 MPa [47]. When the cement/tailing ratio was 1:6, and the slurry concentration was 70%, the strength of the CPB with a curing age of 28 days was 2.06 MPa, which could satisfy the requirements for stope bottom filling. In addition, this study also verified that the CPB slurry with a mass concentration of 70% could be conveyed to the stope through gravity or pumping.

4.2. Environmental Effects of the Backfill Slurry

The LZT contains many heavy metal elements, and its threat to the environment has attracted continuous social attention. This study monitored the metal leaching behaviour of backfill slurry and found that the leaching concentration of lead gradually became steady after 30 h and still exceeded the Chinese standard for groundwater quality (Class III) [43]. However, as shown in Figure 6 and Table 5, due to the hydration process of the cement, most of the metal elements in the backfill slurry were well stabilised. Therefore, pollutants in LZT could be converted into insoluble or slightly soluble materials by incorporating cementitious materials, which make it less harmful.

4.3. Strength Change and Environmental Stability of CPB after Adding Immobilisation Materials

Because aluminium sulfate accelerates the hydration of tricalcium silicate (C3S), the UCS of the CPB was slightly improved after the addition of PAS. Meanwhile, the hydrolysate of PAS resulted in the coagulation and precipitation of lead. After 24 h of pre-setting, the concentration of lead in the bleeding slurry was less than the GB standard when the dosage of PAS was 2 mg/L. As shown in Figure 8, Figure 9 and Figure 10, and Table 7, if LZT was directly discharged without treatment, the metals in LZT would diffuse with leachate, which could cause serious ecological damage to the surrounding areas. Compared with the metal concentration leached by LZT, the leaching concentration of lead, zinc, iron, chromium, arsenic, copper, and nickel in the CPB all met the national standard and had excellent environmental stability.

5. Conclusions

The total amount of lead–zinc tailings produced in China is huge each year. The recycling of LZT for the stope filling can ensure the sustainable development of lead–zinc mining, which is of great significance. This study evaluated the feasibility of recycling lead–zinc tailings for CPB. The mechanical performance of the CPB was related to the slurry concentration and cement/tailing ratio. The UCS test results showed that LZT-based CPB could be a safe alternative for massive consumption of LZT. Moreover, this study concluded that the addition of 2 mg/L PAS could effectively control the leaching of lead in the CPB. All monitored metals satisfied the Chinese standard for groundwater quality (Class III) [43] in the dynamic leaching test, indicating that the technology of recovering LZT as the CPB proposed in this study was an effective method of alleviation of LZT pollution. Although over 14% of the binder was used in the present study, which might be attributed to a high proportion of fine particles in LZT, and the LZT was gap-graded aggregate, the technology improved the overall efficiency of the mine and brought great environmental benefits. This study also suggested that further research should focus on the development of effective and economical binders for the LZT-based CPB.

Author Contributions

Formal analysis, Z.S. and D.Z.; writing—original draft preparation, Z.S.; supervision, Q.C. and D.Z.; project administration, Q.Z.

Funding

This research is supported by the Fundamental Research Funds for the Central Universities of Central South University (2019zzts989).

Conflicts of Interest

The authors declare no conflict of interest.

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Minerals 09 00710 g001 550
Figure 1. Sampling location and sampling process.
Figure 1. Sampling location and sampling process.
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Figure 2. Particle size distribution of lead–zinc tailing (LZT).
Figure 2. Particle size distribution of lead–zinc tailing (LZT).
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Figure 3. Variation of the slump of the cemented paste backfill (CPB) slurry with different concentrations.
Figure 3. Variation of the slump of the cemented paste backfill (CPB) slurry with different concentrations.
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Figure 4. Unconfined compressive strength evolution with different cement/tailing ratios (slurry concentrations).
Figure 4. Unconfined compressive strength evolution with different cement/tailing ratios (slurry concentrations).
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Figure 5. Lead (Pb) concentration in static leachate of lead–zinc tailing (LZT) and backfill samples.
Figure 5. Lead (Pb) concentration in static leachate of lead–zinc tailing (LZT) and backfill samples.
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Figure 6. Zinc (Zn) concentration in static leachate of lead–zinc tailing (LZT) and backfill samples.
Figure 6. Zinc (Zn) concentration in static leachate of lead–zinc tailing (LZT) and backfill samples.
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Figure 7. Lead (Pb) concentration in bleeding after 24 h of pre-setting.
Figure 7. Lead (Pb) concentration in bleeding after 24 h of pre-setting.
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Figure 8. Concentration of metal ions in dynamic leaching of lead–zinc tailing (LZT).
Figure 8. Concentration of metal ions in dynamic leaching of lead–zinc tailing (LZT).
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Figure 9. Concentration of metal ions in dynamic leaching of cemented paste backfill (CPB) samples.
Figure 9. Concentration of metal ions in dynamic leaching of cemented paste backfill (CPB) samples.
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Figure 10. Changes in pH and conductivity in dynamic leaching.
Figure 10. Changes in pH and conductivity in dynamic leaching.
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Table
Table 1. Comparison of elemental composition between lead–zinc tailing (LZT) samples and raw LZT (wt%).
Table 1. Comparison of elemental composition between lead–zinc tailing (LZT) samples and raw LZT (wt%).
ElementsOSiSFeCrCuZnPbNiAsCaK
LZT samples36.816.041.111.540.0150.0120.250.20.010.01819.040.925
Raw LZT37.216.931.0211.320.0160.0110.260.20.010.0218.830.912
Table
Table 2. Chemical composition of lead–zinc tailing (LZT) (wt%).
Table 2. Chemical composition of lead–zinc tailing (LZT) (wt%).
CaOSiO2Fe2O3Al2O3MgOK2OZnOPbO
28.2335.6316.287.331.231.130.320.23
Table
Table 3. Physical properties of lead–zinc tailing (LZT).
Table 3. Physical properties of lead–zinc tailing (LZT).
Physical PropertiesGs d60 (μm)d50 (μm)d30 (μm)d10 (μm)CuCc
LZT2.9450.1828.0778.831.96325.560.79
Table
Table 4. The physical properties of cement.
Table 4. The physical properties of cement.
Chemical Composition (%)
CaO63.62
SiO220.13
Al2O34.78
Fe2O33.97
MgO1.46
K2O0.61
TiO20.31
LOI4.12
Physical Properties
d50(μm)14.69
d90(μm)40
d[4,3](μm)18.3
ρ(g/cm3)3.08
Table
Table 5. Metal concentrations in the static leachate of lead–zinc tailing (LZT) and backfill samples after 48 h.
Table 5. Metal concentrations in the static leachate of lead–zinc tailing (LZT) and backfill samples after 48 h.
ParametersLZT (mg/L)Backfill (mg/L)GB Standard (mg/L)
Fe30.20.20.3
Cr0.4<0.020.05
As0.30.0030.01
Cu0.3<0.0011
Ni0.10.0080.02
Table
Table 6. Unconfined compressive strength (UCS) variation of cemented paste backfill (CPB) samples with a cement/tailing ratio of 1:6 and slurry concentration of 72%.
Table 6. Unconfined compressive strength (UCS) variation of cemented paste backfill (CPB) samples with a cement/tailing ratio of 1:6 and slurry concentration of 72%.
Curing AgeOriginal UCS Value (MPa)UCS Value after Adding Immobilisation Materials (MPa)
7 days1.021.15
14 days1.411.56
28 days2.062.24
Table
Table 7. Element concentration in toxicity characteristic leaching procedure (TCLP).
Table 7. Element concentration in toxicity characteristic leaching procedure (TCLP).
SamplesElements (mg/L)
PbZnFeCrAsCuNi
LZT0.080.053.10.010.010.02<0.001
CPB curing for 7 days0.0060.0030.04<0.0010.001<0.001<0.001
CPB curing for 14 days0.0050.0050.02<0.001<0.001<0.001<0.001
CPB curing for 28 days0.0010.0020.03<0.001<0.001<0.001<0.001
GB standard0.0110.30.050.0110.02

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Su, Z.; Chen, Q.; Zhang, Q.; Zhang, D. Recycling Lead–Zinc Tailings for Cemented Paste Backfill and Stabilisation of Excessive Metal. Minerals 2019, 9, 710. https://doi.org/10.3390/min9110710

AMA Style

Su Z, Chen Q, Zhang Q, Zhang D. Recycling Lead–Zinc Tailings for Cemented Paste Backfill and Stabilisation of Excessive Metal. Minerals. 2019; 9(11):710. https://doi.org/10.3390/min9110710

Chicago/Turabian Style

Su, Zhu, Qiusong Chen, Qinli Zhang, and Deming Zhang. 2019. "Recycling Lead–Zinc Tailings for Cemented Paste Backfill and Stabilisation of Excessive Metal" Minerals 9, no. 11: 710. https://doi.org/10.3390/min9110710

APA Style

Su, Z., Chen, Q., Zhang, Q., & Zhang, D. (2019). Recycling Lead–Zinc Tailings for Cemented Paste Backfill and Stabilisation of Excessive Metal. Minerals, 9(11), 710. https://doi.org/10.3390/min9110710

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