Applied and Environmental Soil ScienceVolume 2012 (2012), Article ID 395964, 11 pagesdoi:10.1155/2012/395964

Research Article

Organic Amendments and Earthworm Addition Improve Properties of Nonacidic Mine Tailings

P. M. Rutherford and J. M. Arocena

Environmental Science and Engineering Program, University of Northern British Columbia, 3333 University Way, Prince George, BC, Canada, V2N 4Z9

Received 15 June 2011; Revised 25 August 2011; Accepted 7 September 2011

Academic Editor: Giuseppe Corti

Copyright © 2012 P. M. Rutherford and J. M. Arocena. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Abstract.

In many mined areas, lack of topsoil limits conversion of disturbed landscapes to former or other productive uses. We examined the use of biosolids (10 or 20% by dry mass), with or without sawdust, pulp sludge, and the contribution of an earthworm species (Dendrobaena veneta) to improve the properties of nonacidic mine tailings. Pulp sludge more rapidly immobilized excessive concentrations from biosolids early in the study; however, total mineral N concentrations were similar in pulp sludge and sawdust treatments by week 29. Although -N concentrations were generally greater in treatments with earthworms, these trends were not statistically significant (). In general, Bray P concentrations were greater in the presence of earthworms. Soil thin sections showed that earthworms mixed organic residues into elongated spherical units within mine tailings. Organic residues in combination with earthworm addition may improve the chemical and microstructural properties of non-acidic mine tailings, producing a substrate conducive for plant establishment.

1. Introduction

Mining operations around the world produce large quantities of residuals such as tailings, overburden, and waste rock. Past mineral extractions in the Sierra de Cartagena (SE Spain) for >2,500 years left behind large volumes (i.e., usually 700,000–900,000 m³ per deposit) of wastes composed of overburden rocks and tailings [1]. A copper and gold mine in northern British Columbia (Canada) generated nearly 25 million tonnes of milled waste rock in 2007 [2]. In Canada and other jurisdictions, industry is required to convert disturbed landscapes to former or other productive uses following mine extraction and processing activities. High-quality topsoil is often limiting at mine sites, so mines often need to utilize on-site substrates (such as mine tailings) to create mine soils for reclamation activities.

Establishment of vegetation is key to reclamation of mine tailings and other residuals [2–5]. Plant cover minimizes the dispersion of particulate matter and contaminants through wind and water erosion, and improves the aesthetic value of unvegetated landscapes [6, 7]. However, mine soils require suitable physical and chemical properties in order to support the growth of plants and associated soil organisms. Tailings are typically fine sands low in organic matter and plant available macronutrients such as N andP.

Various industrial, environmental, and municipal waste treatment facilities generate organic materials that can be added to mine residuals to increase soil organic matter (SOM) and/or nutrient contents [8–12]. Biosolids, also called sewage sludges, are particularly well suited for this purpose due to their relatively high N and P contents [10, 13]. The addition of organic residues to mine soils accelerates soil forming processes, and this practice is also a means of promoting carbon sequestration through the conversion of waste substrates into SOM [12, 14]. Plant-derived organic inputs also contribute to SOM and play an important role in initiating soil development [15, 16].

In natural soils, pedogenic mixing of inorganic and organic materials is best achieved by soil organisms, particularly soil invertebrate ecosystem engineers [17]. Earthworms intimately mix organic and inorganic materials into soil aggregates through ingestion and excretion [18, 19]. Earthworms have also been reported to stimulate soil microbial activity and enhance the availability of soil nutrients such as nitrogen and phosphorus [17, 20, 21]. Earthworms have the potential to enhance the reclamation mine residuals, but even nonacidic mine residuals provide a hostile environment to these sensitive animals [22]. The addition of organic materials may help overcome these limitations by providing an energy source, enhancing nutrient levels, stimulating microbial activity, promoting soil structural development, and increasing water-holding capacity [22, 23].

Addition of biosolids to mine tailings (or to other inorganic substrates) can lead to high concentrations of /NH₃, which is toxic to earthworms at relatively low concentrations [24]. The coapplication of high C/N ratio organic substrates with biosolids may provide the benefit of net -N immobilization into the microbial biomass; this organic N can then undergo slow net N mineralization over a period of time. Addition of these supplementary substrates may have additional benefits of enhancing soil physical and chemical properties relative to tailings only receiving biosolids.

The primary objective of this 29-week laboratory study was to determine the influence of pulp sludge or softwood sawdust coapplied with biosolids on selected chemical and physical properties of nonacidic mine tailings. A secondary objective was to test the role of an earthworm species (Dendobaena veneta) for altering the selected physical and chemical properties of these amended mine tailings. Although Dendobaena veneta is considered to be an epigeic earthworm, we selected this species because it is hardy and has been shown to be active in mineral soils, including those containing organic or inorganic contaminants [25]. It is also widely used in vermicomposting and is readily available. To the best of our knowledge no studies have reported the use of this earthworm in the treatment of mine tailings.

2. Materials and Methods

2.1. Collection and Characterization of Substrate Materials

Inorganic and organic materials were obtained from industrial and municipal sources in north central BC (Canada). Desulphurized mine tailings were obtained from the Mount Polley copper mine near Likely, BC; anaerobically digested sewage sludge (BC Class B biosolids) was obtained from the Prince George municipal wastewater treatment facility; softwood sawdust (mainly from pine) was obtained from a local sawmill; pulp mill sludge was obtained from the Canfor Intercon Kraft pulp mill, Prince George, BC. Materials were allowed to air-dry for several weeks on plastic sheets prior to use in this study.

Substrates were well homogenized prior to characterization. Mine tailings were subjected to the following chemical analyses: total C, N, and S (dry combustion), total P, and total elemental analyses using a combination of lithium metaborate fusion followed by ICP-AES (major elements), lithium borate fusion followed by ICP-MS (trace elements) and 1 : 1 concentrated HNO3 : HCl digestion followed by ICP-MS (Hg, Se). Organic substrates were homogenized and subjected to the following chemical analyses: total C, N, and S (dry combustion), total P (microwave digestion followed by ICP OES), extractable -N and -N via KCl extraction followed by AutoAnalyzer [26]. Elements were determined by digestion in 1 : 1 concentrated HNO3 : HCl followed by ICP-OES (metals, metalloids) or cold-vapor atomic fluorescence spectrophotometry (Hg). X-ray diffraction (XRD) and elemental concentrations were used to estimate (±5%) the mineralogy of the tailings. Particle size distribution of the mine tailings was determined by dry sieving [27].

As expected, concentrations of total N (4.95 g 100 g⁻¹) and total P (4.94 g 100 g⁻¹) in biosolids were orders of magnitude greater than those in sawdust, pulp mill sludge, and mine tailings (Table 1). Ammonium–N, -N and Bray-P in biosolids were 2490, 2.7, and 3042 mg kg⁻¹, respectively, immediately prior to use in this study; concentrations in pulp sludge and sawdust were negligible (data not shown). Potassium (4.77 g 100 g⁻¹) and Cu (656 mg Cu kg⁻¹) contents in mine tailings were much higher than organic substrates (Table 1). Semiquantitative estimates of the mineral composition of the tailings (via XRD and elemental composition) were 8.5% kaolinite, 2.3% goethite, 0.6% clinochlore, 1% quartz, 9.5% calcite, 0.4% muscovite, 77% feldspars, and 0.6% ilmenite. Particle size analysis of mine tailings showed the following proportions of size classes by mass (mean; standard deviation in brackets) <63 μm – 12 (3.8)%, 63 – 125 μm – 58 (5.4)%, 125 – 250 μm – 26 (3.7)%, 250 – 500 μm – 3 (0.9)%, 500 – 1000 μm – 0.8 (0.4)%, and >1000 μm – 0%.

Table 1: Elemental composition of mine tailings, biosolids, pulp sludge, and sawdust used in this experiment.

Element
Units
Mine tailings
Biosolids
Pulp sludge
Sawdust

Si
g 100 g⁻¹
24.2
ND
ND
ND

Al
g 100 g⁻¹
8.92
1.7
0.06
0.004

Fe
g 100 g⁻¹
6.24
1.4
0.09
0.005

Ca
g 100 g⁻¹
3.47
3.1
0.91
0.07

Mg
g 100 g⁻¹
1.24
0.47
0.15
0.01

K
g 100 g⁻¹
4.77
0.19
0.01
0.02

Na
g 100 g⁻¹
2.97
ND
ND
ND

Mn
g 100 g⁻¹
0.09
0.06
0.01
0.01

C
g 100 g⁻¹
0.80
36.8
42.9
51.3

N
g 100 g⁻¹
0.007
4.95
0.027
0.050

S
g 100 g⁻¹
0.89
1.36
0.01
<0.01

P
g 100 g⁻¹
0.17
2.31
0.01
<0.01

As
mg kg⁻¹
20.9
5.2
<0.5
<0.5

Cd
mg kg⁻¹
0.53
2.8
<0.5
<0.5

Co
mg kg⁻¹
18.5
4.0
<2.0
<2.0

Cr
mg kg⁻¹
10
35
4
<2

Cu
mg kg⁻¹
660
2.3
3.8
3.0

Pb
mg kg⁻¹
7
62
<30
<30

Hg
mg kg⁻¹
0.157
6.73
0.011
0.079

Mo
mg kg⁻¹
8
15
<4
<4

Ni
mg kg⁻¹
7
25
<5
<5

Se
mg kg⁻¹
3
10
<2
<2

Zn
mg kg⁻¹
8
790
8
8

Concentrations are presented on an oven-dry equivalent (mass) basis.

ND: not determined.

Hg concentrations in biosolids from this facility are usually less than  1 mg kg−1 .

2.2. Experimental Setup and Treatments

The experimental design consisted of 2 levels of earthworm addition (with and without) and 8 combinations of organic materials added to mine tailings (Table 2). There were three replications for each treatment (i.e., a total of 48 experimental units). Each mixture was contained within a 4-L white plastic bucket (19 cm ø × 15 cm height) that had ~ forty 2 mm holes drilled on its wall to maintain sufficient aeration. Mine tailings were added at a rate of 1500 g (equivalent oven-dry basis) to each container with the appropriate amounts of organic substrates. Moisture content was adjusted to 75% of water-holding capacity (WHC; see below) with tap water and the experimental units were incubated at 20°C for 7 weeks prior to earthworm addition to appropriate experimental units (Table 2). A plastic lid (with ~ thirty 2 mm holes) covered each bucket during incubation to minimize water evaporation. The 7-week incubation was conducted to stimulate microbial activity and to encourage net immobilization of -N that originated from the biosolids prior to the addition of earthworms. As mentioned above, high concentrations of /NH₃ are known to be toxic to earthworms [24].

Table 2: Experimental treatments used in this study. Proportions (g amendment 100 g⁻¹ mine tailings) of organic amendments are presented on an equivalent oven-dry basis relative to initial mine tailings.

Treatment code

Biosolids
Sawdust
Pulp sludge
Without earthworms
With earthworms

10
10
0
T1-WO
T1-W

10
0
10
T2-WO
T2-W

10
5
5
T3-WO
T3-W

10
0
0
T4-WO
T4-W

20
10
0
T5-WO
T5-W

20
0
10
T6-WO
T6-W

20
5
5
T7-WO
T7-W

20
0
0
T8-WO
T8-W

Appropriate treatments received earthworms 7 weeks after the substrates were mixed and the incubation was started.

2.3. Earthworm Addition, Experimental Conditions, and Sample Collection

At week 7, subsamples from all experimental units were removed for chemical analysis, and fifteen earthworms (Dendrobaena veneta) were added to one-half of the treatments (Table 2). The incubation was conducted in a lighted room to discourage the escape of earthworms from the experimental units. Average (±SD) live weight (with full guts) of the earthworms was  g per individual. Earthworms tunneled into the organic amended tailings immediately after addition except for treatments T4-W and T8-W where earthworms remained on the surface and died within a day of addition; treatments T4-W and T8-W were discontinued due to the immediate death of earthworms.

At week 13, the amended tailings from all experimental units were removed, placed into trays, and examined for earthworm survival. Subsamples of tailings were also removed for chemical analysis. Earthworms in treatment T5-W did not survive to week 13. Instead of discontinuing T5-W, fifteen new earthworms were added to the experimental units of this treatment at week 16.

Incubations were continued at 20°C for the duration of the experiment (week 29). Moisture loss was minimal and small water additions were only required every 2-3 weeks. Earthworm populations were counted and tailings samples were collected for chemical analyses and WHC measurements at the conclusion of the experiment. Samples were briefly stored at 4°C prior to chemical analyses.

2.4. Laboratory Analyses

Amended tailings were analyzed for selected physical and chemical properties. Water-holding capacity was determined by placing 300 g of tailings into a 500 mL plastic cylinder (bound with cheese cloth on the bottom) and tapping firmly three times in order to standardize packing. The tailings were then water-saturated from the bottom of the container. After 24 h of saturation, the tailings were allowed to drain freely for 10 h under conditions designed to minimize evaporation; free drainage had ceased at this time and subsamples were then removed for moisture content analysis. Gravimetric moisture content (g H₂O 100 g⁻¹ oven-dry (OD) tailings) was determined by drying tailings overnight at 105°C. The pH was measured in 1 : 4 solids to deionized H₂O (g : mL) suspension [28]. Electrical conductivity of tailings was determined in saturated paste extracts using a conductivity meter [29]. Total C and N were determined on <100-mesh samples (air-dried, then ground in a ball mill) by dry combustion using an elemental analyzer [30]. Available N (-N and -N) was determined by extraction with 2 M KCl, followed by colorimetric N determination [26]. Potentially mineralizable N (-N plus -N) was determined by 7-day anaerobic incubation at the end of the study [31]. Cation exchange capacity (CEC) and exchangeable K, Ca, Mg, and Na were determined at pH 7.0 using the NH₄OAc method [32]. Available P was determined on samples at the end of the incubation by the Bray 1 procedure [33].

2.5. Microstructural Analysis

After the laboratory analyses, we thought that additional spatial information about the soil structure would be useful to complement our observations. We made thin sections from two selected treatments (T2-WO and T2-W) to qualitatively describe the changes in soil microstructure due to organic and earthworm amendments. Thin sections were prepared by impregnating the sample with epoxy resin and subsequent grinding and polishing using corundum to a 30 μm soil section. We described the sections under a Nikon Eclipse E600 polarizing microscope at the University of Northern British Columbia (Prince George, Canada) for micromorphological characteristics following the concepts and terminology in [34].

2.6. Statistical Analysis

The observed parameters were analyzed using a 1-way ANOVA in Statistica, v 6 [35]. Differences between treatments were determined by Student Newman Keuls (SNK) test. Earthworm numbers were transformed (log10) prior to statistical analysis.

3. Results

3.1. Chemical Properties of Amended Mine Tailings at Beginning of Incubation

Subsamples obtained 24 h following the mixing of substrates showed the relatively neutral pH and moderate electrical conductivity in the experimental treatments (Table 3). Nitrate-N concentrations were low, but -N concentrations were very high with treatment averages ranging from 254 to 654 mg N kg⁻¹. Treatments receiving 20% biosolids had significantly greater -N and total N than treatments receiving 10% biosolids.

Table 3: Selected chemical properties of amended mine tailings sampled 24 hours after experimental setup. Means ± standard deviation (). Values designated by the same letter (within a column) are not significantly different from each other ().

Treatment
pH (water)
EC (dS m⁻¹)
-N (mg kg⁻¹)
-N (mg kg⁻¹)
Total N (g 100 g⁻¹)

Treatments with 10% biosolids

T1-WO
c
d
c
a
b

T2-WO
a
e
d
a
b

T3-WO
c
d
d
a
b

T4-WO
bc
b
c
a
b

Treatments with 20% biosolids

T5-WO
d
c
a
a
a

T6-WO
b
d
b
a
a

T7-WO
d
c
b
a
a

T8-WO
d
a
a
a
a

Concentrations are expressed on an oven-dry equivalent basis.

For reference, pH and EC of pure mine tailings were and  dS m⁻¹, respectively ().

3.2. Dynamics of Nitrogen in Response to Amendment Additions

Within each of the two biosolid addition rates, the concentration of -N at week 7 was lowest in treatments T2-WO (Figure 1(a)) and T6-WO (Figure 1(b)), the two treatments that also received 10% pulp sludge. In contrast, treatments T4-WO (Figure 1(a)) and T7-WO (Figure 1(b)), the two biosolids-only treatments, had very high -N concentrations at week 7. By week 13, all treatments had very low -N concentrations, except for the two biosolids-only treatments.

(a)

(b)

Figure 1: Mean -N concentrations in amended mine tailings; (a) treatments that included 10% biosolids addition; (b) treatments that included 20% biosolids addition. Error bars indicate (±1 SD; ). See Table 2 for explanation of treatment codes.

Concentrations of -N increased over the experiment in most treatments, but did not show any significant earthworm effects (Figures 2(a) and 2(b)). By week 13, -N concentrations were generally much greater in treatments receiving 20% biosolids than those treatments receiving 10% biosolids.

(a)

(b)

Figure 2: Mean -N concentrations in amended mine tailings; (a) treatments that included 10% biosolids addition; (b) treatments that included 20% biosolids addition. Error bars indicate (±1 SD; ). See Table 2 for explanation of treatment codes.

For each of the two biosolid addition rates, the decline in C/N ratio for amended tailings was more extensive and more rapid for treatments also receiving 10% pulp sludge (Figures 3(a) and 3(b)). The presence of earthworms did not have a significant effect on C/N ratios. Treatments receiving 20% biosolids generally had lower C/N ratios than treatments receiving 10% biosolids.

(a)

(b)

Figure 3: Mean C/N ratio of amended mine tailings; (a) treatments that included 10% biosolids addition; (b) treatments that included 20% biosolids addition. Error bars indicate (±1 SD; ). See Table 2 for explanation of treatment codes.

3.3. Selected Properties of Amended Mine Tailings at End of Study

Comparison of treatment effects on nitrogen parameters showed that the presence of earthworms did not significantly influence C/N ratio, -N, or potentially mineralizable N at the end of the study (Table 4). Although -N concentrations tended to be greater for an amendment treatment when earthworms were present, these differences were usually not statistically significant (Table 4). Potentially mineralizable N, total N, and -N concentrations were generally greater in treatments receiving 20% biosolids as compared to treatments receiving 10% biosolids.

Table 4: Mean (±standard deviation) C/N ratio, ammonium-N, nitrate-N, potentially mineralizable N (7-day anaerobic incubation), and total nitrogen at the end of the study (week 29). Values designated by same letter (within a column) are not significantly different from each other by SNK (; ).

Treatment
C/N ratio
-N (mg kg⁻¹)
-N (mg kg⁻¹)
Mineralizable-N (mg kg⁻¹)
Total N (g 100 g⁻¹)

Treatments with 10% biosolids

T1-WO
ab
d
cde
cde
c

T1-W
a
bcd
bcd
e
cd

T2-WO
c
d
ef
cde
cd

T2-W
c
d
de
de
cd

T3-WO
ab
e
f
cde
cd

T3-W
b
e
de
e
d

T4-WO
d
d
bcd
bcd
c

Treatments with 20% biosolids

T5-WO
c
abc
1210±131abc
ab
ab

T5-W
c
ab
1554±156a
a
a

T6-WO
d
cd
1031±36bcd
ab
b

T6-W
d
a
1272±40ab
a
a

T7-WO
c
d
1341±72ab
ab
ab

T7-W
c
d
1011±40bcd
bc
b

T8-WO
d
a
1490±206a
ab
ab

Concentrations are expressed on an oven-dry (mass) equivalent basis.

See Table 2 for explanation of treatments.

Earthworms did not have significant effects on pH, WHC, or CEC (Table 5). Although average values for EC tended to be greater for amendment treatments when earthworms were present, these differences were not statistically significant. The two biosolids-only treatments (T4-WO and T8-WO) had the greatest EC values measured in the study. Values of CEC were generally greater in treatments receiving 20% biosolids as compared to those receiving 10% biosolids. There was a positive correlation between -N concentrations and EC at the end of the study (, ), as well as throughout the experiment (, ).

Table 5: Mean (± standard deviation) pH, electrical conductivity, Bray extractable phosphorus, cation exchange capacity, and water holding-capacity at the end of the study (week 29). Values designated by same letter (within a column) are not significantly different from each other (; ).

Treatment
pH
EC (dS m⁻¹)
Bray P (mg P kg⁻¹)
CEC (cmolc kg⁻¹)
WHC (g H₂O 100 g⁻¹)

Treatments with 10% biosolids

T1-WO
bcd
de
cd
ef
abc

T1-W
de
de
bc
cdef
bcd

T2-WO
bc
ef
cd
f
d

T2-W
cde
de
a
cdef
cd

T3-WO
a
f
cd
cdef
bcd

T3-W
bcd
ef
a
def
abc

T4-WO
b
a
d
f
e

Treatments with 20% biosolids

T5- WO
cd
cde
bc
abc
a

T5-W
def
cd
abc
abc
ab

T6-WO
ef
cde
bc
bcde
bcd

T6-W
f
bc
ab
bcd
ab

T7-WO
cde
cd
bc
a
abc

T7-W
bc
de
a
ab
ab

T8-WO
cde
a
bc
ab
d

Bray P, CEC, and WHC are expressed relative to oven-dry (mass) tailings.

The presence of earthworms was associated with higher Bray P concentrations within amendment treatments by the end of the study. Average Bray P was significantly greater in several amendment mixtures when earthworms where present as compared to when they were absent (Table 5).

3.4. Earthworm Populations and Other Observations

Earthworms in treatments that received pulp sludge (T2-W, T3-W, T6-W, and T7-W) were large and very active throughout most of the study. Earthworm activity in these treatments was very apparent by week 13, with young earthworms being present in experimental units with larger earthworms. Abundant fungal growth was clearly visible at week 7, the time of earthworm addition, in treatments that received pulp sludge. In general, by the end of the study earthworms were smaller and less active than those observed at week 13. Earthworm numbers at the end of the study tended to be greater in treatments that included pulp sludge (T2-W, T3-W, T6-W, and T7-W) and least in treatments that only received biosolids and sawdust (T1-W and T7-W; Table 6).

Table 6: Mean earthworm numbers (± standard deviation) in each of the experimental units at the end of the study ().

Treatment
Earthworm numbers

T1-W
ab

T2-W
a

T3-W
ab

T5-W
b

T6-W
a

T7-W
ab

Treatments T4-W and T8-W were discontinued at week 7 when earthworms died immediately after addition.

Treatments with earthworms often exhibited small tunnels within the tailings at the bottom of the experimental units, and mineral surfaces exhibited shinier surfaces relative to treatments without earthworms; this was more apparent in pulp sludge-amended treatments. Although not measured in this study, the addition of pulp sludge appeared to aggregate the tailings more than those receiving sawdust. The “aggregates” observed in this study included true aggregates (i.e., primary particles aggregated weakly into secondary aggregates) and also residual biosolid particles and other residual organic debris (e.g., wood sawdust) from the organic amendments.

3.5. Soil Microstructure

By week 29, organic residues added to the mine tailings were still recognizable in soil thin sections (Figure 4). These residues were intimately mixed with the inorganic materials in T2-W (with earthworms) (Figures 4(a) and 4(b)) while discrete residues were present in isolated patches in T2-WO (without earthworms; Figures 4(c) and 4(d)). The contiguous discrete rounded microfabric units in T2-W formed an outline of elongated (~ 8 mm × 4 mm) spherical units composed of organic and mineral materials (Figure 4(a)). The discrete units of residues in T2-WO exhibited a cracked pattern (Figure 4(d)) not observed in rounded microfabric units (Figure 4(b)). Accumulations of near pure organic matter normally exhibit a cracked pattern upon desiccation [36]. In a typical microfabric in T2-WO, a large section (i.e., upper 75% in Figure 4(a)) is composed of mixed organic matter and mine tailings. This contrasts with T2-WO where the microfabric is composed mainly of mine tailings, with isolated patches of discrete residues (Figure 4(c)).

(a)

(b)

(c)

(d)

Figure 4: Microfabric of mine tailings amended with organic residues with or without earthworms. After 29 weeks, the organic residues (white down arrow) were intimately mixed in (a) T2-W (10% biosolids, 10% pulp sludge, with earthworms), compared to (c) discrete unit showing cracked pattern in T2-WO (10% biosolids, 10% pulp sludge, without earthworms). Close-up images of sections marked by (black up arrow) in (a) and (c) show the (b) intimate mixing of organic residues (white down arrow) with inorganic materials (white up arrow) and (d) the cracked pattern of organic residues (white down arrow) not mixed with inorganic materials.

4. Discussion

The mine tailings in this study consisted mainly of feldspar mineral particles of a very fine sand texture. Concentrations of trace elements were generally low, with the exception of copper (660 mg kg⁻¹). For comparison, the Canadian Soil Quality Guidelines for copper in agricultural and industrial soils are 63 and 91 mg kg⁻¹, respectively [37]. The biosolids amendments are increasingly being used in the reclamation of mine soils mainly to improve plant nutrient levels and to improve soil chemical and physical properties [10]. In this study, we show that coapplication of other organic substrates can enhance soil properties compared to the addition of biosolids alone. The epigeic earthworm Dendobaena veneta only survived in biosolids-amended mine tailings when other organic substrates were coapplied. Pulp sludge addition appeared to be more beneficial to earthworms than softwood sawdust.

4.1. Effect of Immobilizer Substrates on Soil Properties

Very low concentrations of N and P (e.g., <0.01% and <0.20%, resp., in this study) are often the most limiting characteristics to plant growth in nonacidic mine tailings. The current study is consistent with other research that shows addition of biosolids improves total N content of mine residuals such as tailings [38]. Although total N concentrations after 29 weeks of organic residue addition were <0.7%, these concentrations are typical of temperate cultivated soils [30] and are also comparable to soil organic N accumulation in pioneer species in acidic mine tailings in southeast Spain [15]. This increase in total N coupled with more available P in organic and earthworm amended tailings may be sufficient to initiate soil formation and promote plant growth in nonacidic mine tailings. In the Czech Republic, Frouz and Nováková [39] argued that soil formation and organic matter accumulation is crucial to the restoration of ecosystem functions in postmining landscape.

In addition to further improving soil physical properties, the use of “immobilizer” substrates can be used to manipulate nitrogen originating from N-rich substrates. Chaves et al. [40] define immobilizer substrates as those which have net N immobilization potential. Biosolids used in this study initially had a low C/N ratio (7.4) and very high -N concentrations (2490 mg -N kg⁻¹). High -N concentrations may lead to excessive N losses in field soils through volatilization (NH₃) or as -N leaching following nitrification [41]. High /NH₃ concentrations are also toxic to some soil invertebrates such as earthworms [24] and young plants. Immobilizer substrates can temporarily immobilize mineral N (-N or -N) into organic matter (e.g., microbial biomass) which then gradually remineralize the nitrogen over time, ideally in synchrony with plant demand [40].

In this study, pulp sludge was a more effective immobilizer substrate than wood shavings. At 7 weeks, the mineral N (-N+ -N) concentration in the 10% biosolids : 10% pulp sludge treatment (T2-WO) was only 45 mg N kg⁻¹ soil, compared to 464 mg N kg⁻¹ in the 10% biosolids : 10% wood shavings (T1-WO). For comparison, the 10% biosolids-only treatment (T4-WO) had a mineral N concentration of 535 mg N kg⁻¹. The more rapid and extensive drop in C/N ratio in T2-WO compared to T1-WO over the first 7 weeks is consistent with greater microbial activity (and loss of C as respired CO₂-C) in the pulp sludge amended tailings compared to the sawdust-amended tailings (Figure 3(a)). Total carbon concentration decreased by 28% in the T2-WO treatment over the first 7 weeks, while the change in the T1-WO treatment was negligible (data not shown). Results for mineral N and C/N for the 20% biosolids treatments at 7 weeks followed the same trends but pulp sludge concentrations were not great enough to reduce mineral N concentrations to the same extent as in the 10% biosolids treatments (Figure 3(b)). The very high concentrations of -N in the 10% biosolids-only treatment (T4-WO; 507 mg N kg⁻¹), 20% biosolids-only treatment (T8-WO; 1051 mg N kg⁻¹), and the 20% biosolids: 10% sawdust treatment (T5-WO; 721 mg N kg⁻¹) at 7 weeks likely contributed to the death of the earthworms that were added at that time [24]. Similar -N and -N concentrations, and potentially mineralizable N, at the end of the study (within a biosolids application rate) suggest that all organic matter amendments had similar effects on available N over the longer term.

The decrease in pH observed in this study supports earlier literature that soils receiving organic substrates, due largely to formation of carbonic and other acids during decomposition processes and increased nitrification, increases the acidity of the artificial soils. The slight decrease in pH might render P more available to plants [42].

The greater CEC of tailings when amended with high amounts of biosolids (20%) is expected because organic materials are major sources of CEC in soils. Total acidities in isolated humus fractions separated from well-decomposed organic residues range from 300 to 1400 cmolc kg⁻¹ humus [43].

4.2. Influence of Amendments and Earthworms on Mine Tailings

Earthworms can be classified into three ecological types: epigeic, endogeic, and anecic, based on their burrowing habits and habitat [44]. Dendrobaena veneta has been described as an epigeic earthworm (i.e., prefers organic materials such as organic litter layers or in compost). To the best of our knowledge, this is the first report of successful inoculation of Dendrobaena veneta addition to nonacidic sandy mine tailings. Earthworms generally do not do well in sandy substrates [22]; however, the tailings in this study were composed largely of feldspars, which are likely less abrasive than silica-based sands.

The survival of earthworms in amended nonacidic mine tailings (very fine sand) is quite significant because macrofaunal colonization of mine wastes is critical to the development of soils necessary to support plant establishment in postmine sites [15, 45]. Earthworms are “ecosystem engineers” because they transform massive soil to favorable habitats for other organisms [46]. They intimately mix organic and inorganic materials into soil aggregates through ingestion and excretion [18]; they are the main producers of granular structure in many soils. We argue that the elongated spherical units observed in the microstructure of biosolid-pulp sludge amended soils with earthworms (i.e., T2-W) represent the initial stages in the formation of soil aggregates. Similar microstructural units observed in acid mine tailings amended with organic residues are the precursor to the formation of granular structure [47]. Granular structure is ideal for plant growth because it promotes proper aeration, porosity and drainage. Soil aggregation is one of the best indicators of fertile soils because it bridges the physics and biochemistry of soil systems [48]. Shaw and Pawluk [49] reported that the formation of favourable soil structure is associated with the high concentrations of clay-bound sugars in fecal materials of earthworms.

We believe that the survival and activity of Dendobaena veneta in the mine tailings of this study were related to the proper combination of organic residues. The addition of immobilizer substrates was critical to the survival of this earthworm species. In addition, pulp sludge was a better substrate than sawdust to stimulate earthworm numbers and activities; this may have been due to more rapid and extensive decomposition (larger loss of C over the study period; also, greater reduction in C/N ratio) and stimulation of microbial activity. These trends are consistent with the observation of greater earthworm vigour and size in an environment of low ammonium and likely large microbial populations (e.g., fungal biomass) to feed on. It is notable that the earthworms in this study were tolerant of the very high electrical conductivity (EC > 10 dS m⁻¹) in several treatments by the end of the study. The significant positive correlation between soil EC and -N concentrations lead us to believe that high EC at the end of the study was largely due to the high -N concentrations. Although tolerant of these high EC values, the earthworms were lethargic, likely due to salt stress. The presence of plants in a field reclamation program would provide a sink for -N and should result in a reduction in EC, thereby providing a more favorable habitat for earthworms.

We conclude that proper amounts and types of organic residues in combination with earthworm addition may improve the chemical and microstructural properties of nonacidic mine tailings, producing a substrate conducive for plant establishment. This manufactured soil meets the definition of a Technosol [50]. Addition of earthworms with organic residues can be an option to safely manage residuals from numerous stockpiles and tailings ponds at many mined sites around the world. We recommend that future studies also consider the inoculation of earthworm species native to the mine location where tailings are obtained.

Acknowledgments

The authors acknowledge the Natural Sciences and Engineering Research Council, the Canada Research Chair program (Canada), and the Seed Grant Program at the University of Northern British Columbia for financial support to conduct the study. They also thank Clive Dawson at the BC Ministry of Environment (Victoria, BC) for conducting selected laboratory analyses. Dr. Paul Sanborn and Dr. Brian Menounos (both at UNBC) prepared thin sections and provided use of the petrographic microscope, respectively. Ron Martel of Mount Polley Mining Corporation, Norm Gobbi of the Prince George Wastewater Treatment Facility, and Kim Lentz of Canadian Forest Products Ltd. kindly provided in-kind support for this project.

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