Open Access
BIO Web Conf.
Volume 31, 2021
VI International Scientific Conference “Problems of Industrial Botany of Industrially Developed Regions” 2021
Article Number 00017
Number of page(s) 4
Published online 13 August 2021

© The Authors, published by EDP Sciences, 2021

Licence Creative CommonsThis is an Open Access article distributed under the terms of the Creative Commons Attribution License 4.0, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

1 Introduction

The influence of mining operations on the environment and natural resources is of a multifaceted, lasting, and holistic nature. Coal-mining sites are characterised by total destruction of ecosystems and the formation of mining waste rock dumps and borrow excavations. Additionally, either soil degradation or deformation of vegetation takes place around coal-mining sites. Storing mining waste (rock dumps and spoil tips) leads to the disturbance of soil and vegetation; as a result, natural landscapes are replaced by technogenic. Such areas remain barren for a long time and are hardly suitable for active soil formation. Consequently, it is necessary to create conditions that will facilitate more productive soil self-regeneration. It is also urgent to take measures aimed at soil reclamation.

Microorganism application is a modern method for the remediation of technogenically disturbed soils. This approach became common for the reclamation of disturbed lands of various origins [1, 2]. A growing number of microorganisms in the soil substrate is observed in as much as one year provided that microorganisms were applied, while in case of natural self-organised vegetation the same growth rate is achieved in only 5-8 years. Moreover, in the former case there is an advanced vegetation overgrowth of derelict lands in conjunction with improvements in agrochemical composition and plant growth processes [3, 4]. Such positive changes result from the activity of microorganisms as they can transform low accessible forms of nutrients into more accessible to plants.

Rock dumps are not infrequently sources of pollution, the most common pollutants being heavy metals. Hence, it is also necessary to take steps to prevent their migration to the adjacent areas as well as to improve the general sanitary situation.

The aim of this research was to study the effect produced by soil microorganisms on heavy metal accumulation rate in the substrate of mining waste rock dumps.

2 Materials and Methods

The test sites are located on the external waste rock dump ‘Southern’ of the coal strip mine ‘Kedrovsky’ in Kemerovo Oblast. The rock dump is 25 – 30 years old. It is composed of sandstone (60%), siltstones (20%), argillites (15%), loam soils and clays (5%). The soil under study is characterised by alkaline reaction (pH 7.8) and a low level of labile forms of phosphorus and nitrogen. Its content of exchangeable potassium is slightly lower than normal. According to the soil texture, it is a medium-textured loam. The dominant fraction in the soil is large aggregates (3 to 10 mm and larger); they comprise 56% of the air-dry soil weight. The content of fine particles is decreased; as a result, spoil dumps exhibit low moisture holding capacity and are easily water-eroded.

A suspension of soil microorganisms (microorganisms using mineral nitrogen forms / MUMN; microorganism decomposing silicates / MDS; microscopic fungi / MF) was applied to the rock dump surface to investigate the influence of these microorganism on the properties of the rock dump soil. Separate groups as well as their combinations were applied.

Heavy metals in the rock dump soil were detected by atomic-absorption spectrophotometry in the acetylene-air flame using an AAS-30 spectrophotometer (Germany) at the accredited testing centre of the agrochemical service “Kemerovsky”.

3 Results and Discussion

Heavy metals undergo the following transformations while penetrating into soil substrate in the process of technogenesis: oxides change to hydroxides which are then dissolved; solid soil phases adsorb cations; phosphates and their compounds with organic substances present in the soil are formed [6].

Heavy metal accretion is determined by such genetic traits as soil texture, soil organic matter content, soil cation exchange capacity, the thickness of humus horizon, and the soil pH. It was found that cadmium, lead, zinc, copper, and nickel are significantly mobile in acidic environments. Consequently, they are leached, and their content in the surface soil horizon grows lower than the baseline concentration level. As a result, mostly lead, zinc, and copper are accrued in acidic environments, while cadmium and cobalt are accumulated in alkaline environments. Heavy soil texture, high exchange capacity, and high humus content facilitate a higher heavy metal accumulation rate [7]. Such substances as cobalt, beryllium, zinc, cadmium, tin, and lead are captured by the soil organic matter. Due to this, soils rich in humus have a higher concentration of the above-mentioned substances in comparison to nutrient-poor soils.

The evaluation of heavy metal content in the rock dump soil did not indicate a substantial exceedance of the maximum allowable concentration limits (Table 1). The only metal whose content exceeds the admissible limit is nickel. It is characterised by low mobility in soil and soil substrates. Nickel is mostly concentrated in the silt fraction and can form highly soluble chelate compounds with organic substances [8]. Soluble forms of nickel are actively absorbed by plant roots; nevertheless, if soil pH is higher than 6.7, nickel movement to plants is hampered.

It was found that heavy metal accumulation rate in the soils of the areas adjacent to coal-mining enterprises is determined by the heavy metal concentration in the overburden rock. Therefore, it is highly probable that chemical pollution of soils increases if exploited rocks contain high concentrations of toxic elements [9]. From this perspective the overburden rocks in this rock dump presumably do not exhibit an elevated level of heavy metals which could get to the rock dump soil.

It is interesting to note that the content of copper and lead during the application of soil microorganisms exceeded the control values. In addition, there was more lead when microorganisms utilising mineral nitrogen were applied (control values were exceeded by 56%). In the tests with microscopic fungi (MF, MF + MDS, MF + MUMN, MDS + MF + MUMN) the control values were exceeded by 7–23%. The maximum copper content was registered when microscopic fungi and microorganism decomposing silicates were applied. In this case the control values were exceeded by 50% and 44% respectively, which is probably caused by the change of the rock dump pH level triggered by the application of microorganism suspensions. What is more, relevant research shows that there is an increase in heavy metals in the rhizosphere of agricultural plants as the products of microorganism vital activity are bound. Thus, heavy metal absorption by plant roots is prevented [10, 11].

Table 1

Content of heavy metal labile fractions, mg/kg.

4 Conclusion

In summary, the performed research indicated that the content of most heavy metals in the waste rocks of the Kedrovsky coal strip mine is within normal limits. The elevated level of nickel at the test site necessitates monitoring in order to control the nickel content in the rock substrates.

The paper was prepared according to state task No 0286-2021-0010 “The development of a scientific basis for assessing the condition and the recovery of floristic diversity in situ and ex situ in the areas with high degradation of ecosystems due to anthropogenic and technogenic impact”.


  • A. Borem, F.R. Santos, D.E. Bowen, Understanding Biotechnology (Prentice Hall PTR, 2003) [Google Scholar]
  • G.M. Evans, J.C. Furlong, Environmental biotechnology: theory and application (University of Durham, UK and Taeus Biotech Ltd., 2003) [Google Scholar]
  • N.A. Makeeva, O.A. Neverova, Modern problems of science and education 6, 601 (2015) [Google Scholar]
  • N.A. Makeeva, O.A. Neverova, Advances of modern science 7, 76–80 (2016) [Google Scholar]
  • Methodological guidelines for detecting heavy metals in agricultural field soils and plant produce 65 (CIAS, Moscow, 1992) [Google Scholar]
  • M.A. Yakovchenko, O.B. Konstantinova, A.A. Kosolapova, L.V. Rogova, D.N. Alankina, Bulletin of KuzSTU 3, 116–119 (2014) [Google Scholar]
  • A.S. Voronkova, Mining information-analytical bulletin 1 (2006) [Google Scholar]
  • S.V. Lukin Achievements of science and technology AIC 3, 14–15 (2011) [Google Scholar]
  • A.P. Krasavin, I.V. Katayeva, A.V. Ostanin, V.A. Yekaterininsky, Plants and industrial environment 128–135 (1992) [Google Scholar]
  • M.S. Panin, Ye.N. Biryukova, G.V. Motuzova, Modern problems of soil pollution 72–75 (Moscow, 2004) [Google Scholar]
  • A.I. Puzakova, I.S. Konyaev, I.V. Prokopenko, A.Ye. Tigunov, Samara Bend: regional and global environmental problems 21, 148–151 (2012) [Google Scholar]

All Tables

Table 1

Content of heavy metal labile fractions, mg/kg.

Current usage metrics show cumulative count of Article Views (full-text article views including HTML views, PDF and ePub downloads, according to the available data) and Abstracts Views on Vision4Press platform.

Data correspond to usage on the plateform after 2015. The current usage metrics is available 48-96 hours after online publication and is updated daily on week days.

Initial download of the metrics may take a while.