Massive amounts of mine wastes are generated all over the world. Sweden alone generated 104-million-ton mine waste in 2018, accounting for 75% of all waste produced during that year (Avfall Sverige
2020). These wastes need to be managed in an environmentally-, technically- and economically sustainable way. About 70% of the mine waste in Sweden contain sulfide minerals (SGU and Swedish EPA
2017) which if left in contact with oxygen and humidity oxidize and may produce acid rock drainage (ARD). ARD is a major long-term threat to the environment as metals and metalloids may become mobile (Saria et al.
2006). The GARD guide (Global Acid Rock Drainage guide; Verburg et al.
2009) categorize different methods to prevent ARD after closure, into two main categories; engineered barriers and water covers. In the relatively humid climatic conditions in Sweden a dry cover, a form of engineered barrier, can be used to reduce water and oxygen flux to the underlying reactive wastes, and thus reduce ARD (Collin and Rasmuson
1990; Bussière et al.
2003; Dagenais et al.
2006). A dry cover in Sweden usually consists of a sealing layer placed on top of the mine waste, made of a fine-grained compacted material to prevent oxygen to diffuse to the waste underneath by keeping it close to saturation. Above the sealing layer the protective layer protects the underlaying layer from erosion, frost and/or root penetration. Because of the Swedish geology most sealing layers are usually made of till, ideally a clayey till. The availability of a clayey till nearby a mine is however often limited, and the till can either be improved or replaced with another material. Bentonite amendments to till is one solution to improve the sealing layer-qualities of the local till. However, bentonite is costly both economically and environmentally due to time- and resource consuming production. The use of an industrial residue as an amendment to a local till is therefore highly motivating. The European Union produces about 2.5 billion tons of waste each year (Avfall Sverige
2020) and Sweden produced 139 million tons waste year 2018, excluding mine waste, of which about 2.9 million tons was classified as a non-hazardous waste. Using a non-hazardous inert industrial residue in a mine remediation program is beneficial for the environment, for the industry providing the residue, and the mining industry. Some examples of industrial residues that previously have been used as a mine waste cover are sewage sludge, fly ash, desulfurized tailings, coal combustion by-products (CCB), and steel slag (Hallberg et al.
2005; Bäckström et al.
2009; Dobchuk et al.
2013; Lu et al.
2013; Nason et al.
2013; Park et al.
2014; de Almeida et al.
2015; Phanikumar and Shankar
2016). According to the Confederation of European Paper Industries (CEPI) 155 Mt of wood was consumed by the paper industry and 38 Mt of pulp was produced in year 2018 (CEPI Key Statistics
2018). Sweden, Finland, and Portugal are the top three countries accounting for 69% of the pulp production (Quina and Pinheiro
2020). In Sweden, about 200 000 tons of GLD were generated annually according to a survey made in 2003 (SGI
2003), and production has increased based on a survey made 2017 (unpublished data). Green Liquor Dregs (GLD) is an inert, alkaline, inorganic waste originating from the recycling process at sulfate pulp and paper mills which has the same grain size distribution as silt. It has properties suitable as sealing layer, as it is fine grained (d100 < 63 µm), commonly has a hydraulic conductivity in the range of 10
−8 to 10
−9 m/s, a higher water retention capacity (WRC) compared to materials with similar particle size, such as clayey/sandy silt (Mäkitalo et al.
2014) and a low oxygen diffusion coefficient (Virolainen et al
2020). GLD is regarded as an inert material (Mäkelä and Höynälä
2000), where the main solid compounds consist of CaCO
3, Mg(OH)
2, C, and metal sulfides, especially FeS (Sanchez and Tran
2005; Jia et al.
2014). The liquid phase of the GLD consists of Na
2CO
3 and NaOH, which generates its characteristic high pH. A scientific review of GLD made by Quina and Pinheiro (
2020) suggest that the mineral phases of GLD consist of calcite (CaCO3), Dolomite (CaMg(CO
3)
2), Cesamite (Ca
2Na
3(SO
4)
3(OH)), Pirssonite (Na
2Ca(CO
3)
22H
2O) and Brucite (Mg(OH)
2). Manskinen et al
2011 and Novais et al
2018 indicate that Pirssonite is the dominant mineral in GLD, while Martins et al. (
2007) suggest calcite is the most abundant phase. Other characteristics of GLD are as mentioned a high pH (10–11), relatively high porosity (73 – 82%), a bulk density of 0.44–0.67 g/m
3 and a compact density of 2.47 to 2.60 g/cm
3. Sequential extraction has been performed on GLD and indicates relatively low bioavailability of metals in general (Nurmesniemi et al.
2005). In contradiction to this and other studies (i.e., Mäkelä and Höynälä
2000), a study made by Bandarra et al. (
2019) denoted GLD as a “possible hazard” according to the chemical analysis and the biotests made in the study indicated high ecotoxic effects for three out of five organisms. However, in this study the purpose is to use the GLD as an amendment to till, requiring only a small amount of GLD in the mixtures (< 20 wt%). The material is also to be used in the sealing layer which purpose is to retain the water reaching it, not flushing it out, meaning that there should not be much chemical leachate from the GLD reaching out to the biosphere.
Reducing oxygen diffusion to the mine waste is the main important factor deterring the formation of ARD, and oxygen has two main ways of transport in a soil: through the water, or the air in the pores. Instead of measuring oxygen diffusion, hydraulic conductivity is usually used to evaluate the effectiveness of a sealing layer in mine waste remediation in Sweden. This as oxygen diffusion is more difficult to measure in field, mainly due to leakage of air through the instrumentation. The requirements for hydraulic conductivity in a sealing layer are site specific, but commonly the requirement in Sweden is below 10
−8 m/s. An important factor influencing the hydraulic conductivity is the presence of fine-grained material. An increasing proportion of fines in the material decreases the hydraulic conductivity (Benson et al.
1994; Benson and Trast
1995; Leroueil et al.
2002), as the porosity of the material decreases. The water retention capacity (WRC) is another important feature of a sealing layer material, as a high WRC usually corresponds to a high water-saturation. In general, the oxygen flux rates are at a minimum when the degree of saturation is greater than 85–90%, this as the air-phase at a saturation greater than 85% becomes discontinuous (Corey
1957) and the oxygen is then transported through the water phase (Aubertin and Mbonimpa
2001; Aachib et al.
2004). One way to estimate the WRC is to use a soil–water characteristic curve (SWCC), which demonstrates the correlation between the matric suction (ψ) and the water content or the degree of saturation. The matric suction required to begin draining a fully saturated soil is called the air-entry suction (ψ
a). The residual water content (θ
r) is defined as the amount of water in the soil that cannot be removed even at great suction heads, due to adhesive forces between the water molecules and the soil particles, or due to entrapment in disconnected pores. Factors controlling the shape of the curve are mainly the type of the soil (Fredlund and Rahardjo
1993; Tinjum et al
1997; Sillers et al.
2001), but also the molding water content is an important factor (Vanapalli et al.
1996,
1999; Tinjum et al.
1997).
The long-term stability of the GLD has been studied by Mäkitalo et al. (
2016) and suggest that the low shear strength of GLD increases over time, but not enough to ensure a long-term physical stability in slopes. Considering its lack of long-term physical stability, it is not reasonable to solely use GLD in the sealing layer from a geotechnical point of view. However, using GLD as an amendment to a local till is a possibility that have been studied by Hargelius (
2008), Mäkitalo et al (
2015a and b) and Virolainen et al (
2020) and have shown promising results with decreasing hydraulic conductivity, increasing WRC, and increasing compaction degree. The properties of the till and GLD are however not homogeneous. The contents of fines and clays are one example of factors that varies in the materials. It has a great potential to affect the final hydraulic conductivity of the mixture and has not been studied previously in GLD-amended till. Another gap in this field of research is the effect of the till and its physical properties (i.e., fines- and clay-content) on the final hydraulic conductivity and water retention capacity of the mixtures in its own. Which makes it difficult to conclude if the amendment of GLD really improves the sealing layer qualities of the till. There is, therefore, a great need for further studies on how these factors control the final till-GLD mixtures and at which percentages the materials should be mixed with each other. A maximum of 20 weight percentage (wt%) of GLD addition was set as a limit in this study, as a mixture with more GLD becomes difficult to compact and handle, due to increased water content above the optimum molding water content and decreased shear strength. 5 to 20 wt% of GLD from Smurfit Kappa paper mill were mixed with three sieved tills (< 20 mm) with different contents of fines and clays, with the objectives to find out (i) if GLD can improve the hydraulic conductivity (below 10
−8 m/s) and WRC of three tills with different particle size distributions so they can be used in a sealing layer on top of sulfidic mine waste, and (ii) how the contents of fines and clays in three different tills will affect the hydraulic conductivity and WRC in the till-GLD-mixtures.