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Water from abandoned mines as a heat source: practical experiences of open- and closed-loop strategies, United Kingdom

  • David Banks
  • Anup Athresh
  • Amin Al-Habaibeh
  • Neil Burnside
Open Access
Original Article

Abstract

Pilot heat pump systems have been installed at two former collieries in Yorkshire/Derbyshire, England, to extract heat from mine water. The installations represent three fundamental configurations of heat exchanger. At Caphouse Colliery, mine water is pumped through a heat exchanger coupled to a heat pump and then discharged to waste (an open-loop heat exchange system). The system performs with high thermal efficiency, but the drawbacks are: (1) it can only be operated when mine water is being actively pumped from the colliery shaft for the purposes of regional water-level management, and (2) the fact that the water is partially oxygenated means that iron oxyhydroxide precipitation occurs, necessitating regular removal of filters for cleaning. At Markham Colliery, near Bolsover, a small amount of mine water is pumped from depth in a flooded shaft, circulated through a heat exchanger coupled to a heat pump and then returned to the same mine shaft at a slightly different depth (a standing column arrangement). This system’s fundamental thermal efficiency is negatively impacted by the electrical power required to run the shaft submersible pump, but clogging issues are not significant. In the third system, at Caphouse, a heat exchanger is submerged in a mine water treatment pond (a closed-loop system). This can be run at any time, irrespective of mine pumping regime, and being a closed-loop system, is not susceptible to clogging issues.

Keywords

Heat pump Colliery Mine water Green energy Thermogeology Iron 

Introduction: mine water as a thermal resource

In active mines, inflowing mine water needs to be removed from the mine system to allow working. This is often achieved in shallow mines by gravity drainage via soughs or adits to nearby valleys or watercourses. In deep mines, active pumping is required. The groundwater removed from the mine is at or somewhat above the annual average soil temperature of the locality in question and increases with depth (1–3 °C per 100 m in most tectonically stable areas: Banks 2012). Air must also be circulated carefully through the workings: in winter, the cold downdraught air acquires heat from the rocks as it circulates through the network of tunnels, and the return air is thus warm and can be used for pre-warming machinery or space heating systems.

When a mine is abandoned, one of three hydrological fates typically awaits the mine system:

  1. 1.

    the pumps are switched off and the mine gradually fills with groundwater until it overflows at the surface via a shaft top, an unplugged exploration borehole, a sough, tunnel or adit.

     
  2. 2.

    the mine continues to be pumped to prevent it filling with water and threatening other working mines down-dip (Janson et al. 2009).

     
  3. 3.

    the mine, or interconnected mine system, continues to be pumped at one locality (or a limited number of localities) in order to prevent uncontrolled outbreaks of water at the surface (Banks et al. 1997a)

     
Many (but not all) coal, oil shale and metal deposits contain a significant content of sulphide minerals, such as pyrite (FeS2). When exposed to circulating water and oxygen (as is the case in a working mine), these oxidise to form either metal-rich solutions of sulphuric acid, or secondary acidic metal sulphate minerals. These minerals, which may include phases such as jarosite (K,Na,H)FeIII 3(OH)6(SO4)2, melanterite (FeSO4.7H2O), rӧmerite (FeIIFe2 III(SO4)4.14H2O) or copiapite (FeIIFeIII 4(SO4)6(OH)2.20H2O), represent a “store” of acidity, metals and sulphate, which can be released into solution when exposed to water, for example, when the mine floods (Bayless and Olyphant 1993; Younger 2000). Thus, the water initially overflowing from abandoned mines is typically rich in dissolved metals (especially iron), sulphate and can be acidic (Banks et al. 1997a, b). These concentrations will often decline with time as the secondary oxidation products are consumed by dissolution (Gzyl and Banks 2007; see also Burrows et al. 2015). Dold (2017) provides a recent thorough review of mineral acidity generating potential. Neglecting the intermediate (secondary mineral) steps, the overall reaction (for pyrite) can be represented by the, admittedly simplified, Eq. (1):
$$\text{2Fe}{{\text{S}}_{\text{2}}}+\text{ 7}{{\text{O}}_{\text{2}}}+\text{ 2}{{\text{H}}_{\text{2}}}\text{O }=\text{ 2F}{{\text{e}}^{\text{2}+}}+\text{ 4S}{{\text{O}}_{\text{4}}}^{\text{2}-}+\text{ 4}{{\text{H}}^{+}}_{(\text{aq)}}$$
(1)
Following this reaction, the acid may be neutralised by reaction with carbonate or silicate minerals in the host rocks:
$$\text{2F}{{\text{e}}^{\text{2}+}}+\text{ 4S}{{\text{O}}_{\text{4}}}^{\text{2}-}+\text{ 4}{{\text{H}}^{+}}_{(\text{aq})}+\text{ 4CaC}{{\text{O}}_{\text{3}}}=\text{ 2F}{{\text{e}}^{\text{2}+}}+\text{ 4S}{{\text{O}}_{\text{4}}}^{\text{2}-}+\text{ 4C}{{\text{a}}^{\text{2}+}}+\text{ 4HC}{{\text{O}}_{\text{3}}}^{-}$$
(2)
Thus, many neutralised mine waters are relatively rich in base cations and bicarbonate alkalinity. In the Coal Measures rocks of the UK, iron-bearing carbonates such as siderite (FeCO3) and ankerite (Ca(Fe,Mg,Mn)(CO3)2) can occur (Crook 1912; Hawkes and Smythe 1935; Eden et al. 1957; Lake and Hough 2006), such that this neutralisation reaction can release yet more ferrous iron to solution. If exposed to oxygen, the iron released by Eq. (1) or by iron carbonate dissolution can oxidise to form ferric iron, which is insoluble at all but very low pH values, precipitating as flocs of iron (III) hydroxide:
$$\text{4F}{{\text{e}}^{\text{2}+}}+\text{ }{{\text{O}}_{\text{2}}}+\text{ 4}{{\text{H}}^{+}}_{(\text{aq})}+\text{1}0{{\text{H}}_{\text{2}}}\text{O }=\text{ 4F}{{\text{e}}^{\text{3}+}}+\text{ 12}{{\text{H}}_{\text{2}}}\text{O }=\text{ 4Fe}{{\left( \text{OH} \right)}_{\text{3}}}+\text{ 12}{{\text{H}}^{+}}_{(\text{aq})}$$
(3)

The various steps in Eq. (3) are temperature dependent, but experimentation strongly indicates that an increase in temperature (at least in the range 0–35 °C) tends to increase the rate of iron oxidation and hydroxide precipitation (Faraldo Sanchez 2007; Raftery 2016).

This ferric (oxy)hydroxide typically imparts an orange coloration to watercourses receiving mine drainage and is commonly known in the mining industry as “ochre” or “yellowboy” or, in stricter mineralogical parlance, limonite. With time, the ferric hydroxide progressively loses water, crystallises and hardens (Grundl and Delwiche 1993). Thus, the terms “ochre” or limonite are non-mineralogically specific and are used to describe a mixture of hydrated iron oxides that may range from amorphous ferric hydroxide (Fe(OH)3), through ferrihydrite (metastable nanocrystalline Fe2O3· (H2O) n , where n = 1.8–0.5) and goethite (FeOOH) to haematite (Fe2O3). For convenience, we will henceforth use the term “ochre” in this article. The ochre settling out on the beds of these watercourses can also smother the benthic fauna that fish feed on, negatively impacting the ecology of the watercourse. Mine waters, their acidity, salt and metal loadings and the ochre issues that follow are typically regarded as an environmental liability. The UK Coal Authority expends considerable effort and financial resources in managing this liability, both in terms of regional pumping of interconnected mine workings, to control mine water levels, and in treating pumped and gravity discharges of mine water (Banks and Banks 2001).

However, these mine water discharges can be viewed as a “green” renewable energy asset. Their temperature renders them suitable for space heating (via the use of heat pump technology) in the winter and as a heat sink for space cooling in the summer. The enormous volumes of mine workings and highly transmissive nature of mine roadways imply that the thermal storage associated with such workings is substantial and that very large water yields (several tens or even hundreds of L s−1) can be abstracted from open flooded roadways and shafts. Simply by extracting a few °C of heat from a flow of, say, 50 L s−1 of mine water can result in MW-scale quantities of thermal potential:
$$\text{Heat power available }=Q\cdot \Delta T\cdot {{\rho }_{\text{w}}}\cdot {{c}_{\text{w}}}$$
(4)
$$\text{Example}:\text{5}0\text{ L }{{\text{s}}^{-\text{1}}}\times \text{ 4}\ {}^\circ \text{C }\times \text{ 419}0\text{ J }{{\text{L}}^{-\text{1}}}{}^\circ {{\text{C}}^{-\text{1}}}=\text{ 838},000\text{ J }{{\text{s}}^{-\text{1}}}=\text{ }0.\text{838 MW,}$$
where Q = mine water flow in L s−1 (say, 50 L s−1), ΔT = temperature change at heat exchanger in °C (say, 4 °C), ρ w = density (kg L−1) and c w = specific heat capacity (J kg−1 °C−1) of water and hence, ρ w × c w = volumetric heat capacity of water (J L−1 °C−1) = c. 4190 J L−1 °C−1.

Such mine water-based heating schemes have been operational at a number of locations globally for several decades. Amongst the best known of these are the schemes at Springhill, Nova Scotia, Canada (Jessop 1995; Jessop et al. 1995; Michel 2009; Tweedie 2014), Park Hills, Missouri, USA (Watzlaf and Ackman 2006; DOE 2015), Marywood University, Pennsylvania, USA (Korb 2012), several in Saxony, Germany (Ramos et al. 2015) and megawatt-scale schemes at Barredo colliery, Mieres, northern Spain (Loredo et al. 2011, 2017; Ordóñez et al. 2012; Jardón et al. 2013) and at Heerlen, Netherlands (Minewater Project 2008; Ferket et al. 2011; Verhoeven et al. 2014). More recently, schemes have been documented in Eastern Europe, including those at Saturn colliery, Czeladz, Poland (Malolepszy et al. 2005; Tokarz and Mucha 2013) and Novoshakhtinsk colliery, Russia (Rostov Regional Government 2011; Ramos et al. 2015). A number of mine water heat pump schemes are also active in the United Kingdom (Fig. 1). Global reviews are provided by Banks et al. (2003, 2004), Watzlaf and Ackman (2006), Hall et al. (2011), Preene and Younger (2014), Ramos et al. (2015) and Bracke and Bussmann (2015).

Fig. 1

Overview map of Britain and Ireland, showing mine water heat pump schemes. Egremont (Banks et al. 2017) is based on an ironstone (haematite) mine, while the rest are coal mines

Obstacles to the uptake of mine water heating and cooling

Banks (2016) listed several main obstacles to the uptake of mine water space heating and cooling, with an emphasis on the UK.

  • Perceived risk of ochre clogging of pumps, heat exchangers, pipelines and reinjection wells.

  • Risk of reinjected thermally spent (e.g. cool) water “breaking through” open mine pathways to the (e.g. warm) abstraction shaft or well.

  • Uncertainty over legal and licencing issues—including the guaranteed longevity of mine pumping operations and abstraction licences, and the legal risk of accruing future liability for mine water pollution.

  • Presence of a suitably dense long-term heating and cooling demand, with suitable heat emitters, in the vicinity of the mine. If this is associated with a new development, are conventional heating/cooling solutions already “locked in”?

To these can probably be added the difficulties of identifying suitable ownership, economic and distribution models: will an operator simply distribute mine water (or a fluid thermally coupled to the mine water) to individual consumers, each with their own heat pump? Or will an operator own a centralised heat pump plant room and a district heating and cooling network? In each case, where do ownership boundaries and responsibilities fall, and who owns the right to claim any state subsidies?

The EU Research Fund for Coal and Steel has funded a project entitled “Low Carbon Afterlife: Sustainable Use of Flooded Coal Mine Voids as a Thermal Energy Source—a Baseline Activity for Minimising Post-Closure Environmental Risks” (acronym: LoCAL; Gzyl et al. 2016), with several work packages, each specifically aimed at overcoming these barriers. The work reported in this paper specifically addresses the design and operation of heat exchange solutions to understand and minimise hydrogeochemical risks. Internationally, the Barredo shaft heat pump scheme at Mieres, northern Spain (Loredo et al. 2017), and the proposed Ewa shaft heat pump scheme at the Szombierki coal mine, Bytom, Poland (Janson et al. 2016), are included as LoCAL study sites, together with a number of schemes in the United Kingdom. The paper will examine, in turn, the British LoCAL study sites and summarise the experiences to date with each site.

Modes of operation for mine water heat pump/exchange schemes

There are a number of modes in which heat can be exchanged with mine water (Fig. 2, using terminology consistent with Banks et al. 2004; Banks 2012):

Fig. 2

Different modes of heat extraction from/rejection to abandoned, flooded mines. a Open loop with disposal of water to surface recipient, b open loop with reinjection, c closed loop in flooded shaft, d closed loop in surface mine water treatment pond, e standing column with bleed and recirculation in shaft, f standing column configuration, with large natural flow up shaft. HE heat exchanger or heat pump, HP heat pump.

Reproduced with the permission of © David Banks

Open-loop systems with disposal of thermally spent water

Here, mine water is abstracted from a flooded mine via a shaft or boreholes and passed directly through a heat pump or (more commonly) a heat exchanger (coupled to a heat pump). After heat exchange, the mine water is rejected to surface water (or, sometimes, to the sea), often following some form of treatment (Fig. 2a). Examples of such schemes include the Barredo coal mine shaft at Mieres, Asturias, northern Spain (Loredo et al. 2011, 2017; Ordóñez et al. 2012; Jardón et al. 2013), where the water quality is relatively good and where no treatment is necessary, and the Caphouse colliery in Yorkshire, UK, (Burnside et al. 2016a), where heat exchange takes place prior to mine water treatment. Possible disadvantages of such open-loop schemes include: the cost of treatment and the potential for pumps, pipelines, heat exchangers and reinjection boreholes to become fouled with chemical precipitates (often iron oxyhydroxides—‘ochre’—or manganese oxides).

Open-loop systems with reinjection of thermally spent water

If treatment and disposal of mine water to surface waters is to be avoided, it is possible to reinject the water back into the mine workings, or to another aquifer unit, following heat exchange (Fig. 2b). The advantage of this is that water resources are conserved while treatment and disposal costs are avoided. On the other hand, it requires the drilling and maintenance of reinjection boreholes and runs the risk of thermal “feedback” if the connection between the abstraction and injection points is too direct. Examples of this type of scheme include Shettleston, Glasgow and Lumphinnans, Fife, Scotland (Banks et al. 2009) and Heerlen (Minewater Project 2008; Ferket et al. 2011; Verhoeven et al. 2014). In the latter scheme, the reinjected cool water (from heating) or warm water (from cooling operations) could theoretically be stored in the mine workings, allowing for later abstraction during the appropriate season.

Closed-loop systems

Here, a heat exchanger (which may be a steel radiator, or a loop of polythene pipe) is submerged in the mine water. This may take place in the mine itself (in a flooded shaft or gallery, Fig. 2c), as at Folldal mine in Norway (Banks et al. 2004; Ramos et al. 2015), or within a mine water treatment lagoon, after the mine water has been pumped to the surface, as at Caphouse, Yorkshire, UK (Fig. 2d, Burnside et al. 2016a). A heat transfer fluid is circulated through the heat exchanger, typically back to a heat pump servicing a space heating/cooling demand. The main advantage of this system is that no mine water is abstracted and all issues relating to water chemistry and treatment are thus avoided. The main disadvantage is that, because mine water is not necessarily being deliberately mobilised by pumping, replenishment of heat to the heat exchanger takes place by conduction, natural advection and thermal convection of water in the mine void. The heat yield of closed-loop systems is thus often more limited than with open-loop systems.

“Standing column” systems

Here, water is abstracted from a specific depth in a mine shaft. It is passed through a heat exchanger and some or all of the water is returned to the same shaft at a different depth and different temperature (Fig. 2e). Any fraction that is not returned, but which is disposed of at surface, is known as the bleed fraction (if the bleed fraction is 100%, it is simply an open-loop system with disposal). The returned water usually flows along the shaft towards the pump, absorbing heat from (or, if warmer, rejecting heat to) the walls of the shaft. If there is no natural advection of water along the shaft, the heat gain is ultimately sourced from conduction through the surrounding rocks towards the walls of the shaft, and the sustainable heat yield will usually be rather limited (Fig. 2e). If there is natural water advection along the shaft, this will tend to thermally replenish the system, increasing the heat yield. If the natural advection along the shaft is very large, the reinjected water may flow away from the shaft before returning to the pump, effectively becoming decoupled from the pumping horizon (Fig. 2f).

British LoCAL study sites

In the United Kingdom, the LoCAL project monitors three coal mine study sites, representing each of the configurations listed above:

  1. 1.

    The Markham No. 3 shaft study site near Bolsover—a standing column system.

     
  2. 2.

    The Caphouse site, near Wakefield, which incorporates an open-loop mine water system with disposal to treatment lagoons, and

     
  3. 3.

    a closed-loop system installed in a mine water treatment pond.

     
  4. 4.

    The Shettleston site, a long-established, operational open-loop mine water system, with reinjection of thermally spent water.

     

At the Markham and Caphouse sites, monitoring systems have been implemented to evaluate the energetic performance of the heat pump schemes, by the installation of heat meters on the mine water and delivery sides of the heat pump, together with the monitoring of electrical power consumption. Furthermore, the hydrochemistry of the mine water is monitored on an approximate monthly basis, with the following parameters determined in the field: pH, dissolved O2, Eh, total alkalinity, temperature, electrical conductivity and samples being collected for laboratory analysis of suites of major cations and anions, 2H, 18O and 34SO4 = stable isotopes and (more recently) dissolved methane. The detailed hydrochemistry of the two sites is fully documented by Burnside et al. (2016a, b).

In addition to these, a fourth study site, at the former Manvers Colliery, near Barnsley, South Yorkshire, is under development as a future open-loop system, with abstraction from, and reinjection to, two different levels of coal mine workings. This will not be discussed further in this paper as it is not yet fully operational (being at the permitting and licencing stage).

Caphouse, Yorkshire: open-loop system with discharge to surface water

Caphouse Colliery is located c. 9 km WSW of the town of Wakefield in West Yorkshire. It comprises several shafts including the Hope (1.6254°W 53.6418°N), Inman, Furnace and Caphouse (1.6182°W 53.6440°N) shafts and two drifts (Brown and Goodchild 1979; Kruse 2007). The colliery complex closed as a working mine in 1985, but has now been reopened as the National Coal Mining Museum of England (NCMME). Caphouse/Hope colliery is hydraulically interconnected underground to a wider network of collieries, including the workings of the Woolley (1.5338°W 53.5961°N) and Denby Grange Collieries (1.5942°W 53.6340°N) (INWATCO 2005a, b). The Hope Shaft is pumped every night and early morning (while electricity is cheap) to maintain mine water levels sufficiently low that (a) the museum’s underground exhibits and visitor galleries do not flood and (b) to prevent uncontrolled outbreaks of ochreous mine water on a regional basis. The Hope Shaft is some 197 m deep and the submersible pumps are placed at c. 170 m depth (−23 m asl1), with mine water levels in the shaft being maintained in the range c. 143–156 m bgl2 (+4 to −9 m asl). The average pumping rate is some 3000 m3 day−1 (up to 76 L s−1 for 12–16 h day−1). The mine water is treated in a passive aerobic aeration–settlement–wetland system, comprising an aeration cascade (with optional alkali dosing), two aeration basins, a balancing pond, four settlement basins (2 × 2 in parallel) and two parallel polishing reed beds, prior to discharge to the local stream (PIRAMID 2003, Banks 2007; Faraldo Sanchez 2007—Fig. 3).

Fig. 3

Overview map of Caphouse Colliery site, showing (schematically) the pumped mine water flow through the aerobic treatment system. HP heat pump cabin, A1 1st aeration pond with aeration cascade at southern end, A2 2nd aeration pond, B balancing pond, S sedimentation basins, R1 and R2 reed beds, O outfall of treated mine water to stream. 14 installed water-level/temperature loggers

The water is pumped from the mine at typically slightly above 14 °C (although temperatures of down to 12 °C have historically been recorded). Presupposing the removal of 5 °C of heat via a heat exchange system, a flow rate of 3000 m3 day−1 represents a potential heat yield of:
$$\text{3},000,000\text{ L da}{{\text{y}}^{-\text{1}}}\times \text{ 5 K }\times \text{ 4}.\text{19 kJ }{{\text{L}}^{-\text{1}}}{{\text{K}}^{-\text{1}}}/\text{ 864}00\text{ s da}{{\text{y}}^{-\text{1}}}=\text{ 73}0\text{ kW}$$
(5)

Thus, a pilot space heating plant has been set up at Caphouse, based on a Vaillant Geotherm VWS 101/2 heat pump of nominal 10.5 kW heat output. This provides space heating (via a buffer tank and thence circulation of warm water through a conventional space heating radiator, with a flow temperature of 50–52 °C and a return of 45–46 °C) to a museum audiovisual exhibit in the building associated with the Inman shaft. A small portion of the pumped mine water is taken from the main pipeline between the Hope Shaft and the first aeration lagoon. This mine water offtake passes through a dual in-line mesh filter and then through two parallel (one operational, one standby) shell and tube heat exchangers before being discharged to the first aeration lagoon. Heat is transferred via the heat exchangers to a 20% solution of Hydratech Thermox FPG heat transfer fluid (based on propylene glycol), which is circulated through the heat pump evaporator (Fig. 4).

Fig. 4

Interface for open-loop (mine water circuit) and closed-loop options in Caphouse heat pump cabin. Optional couplings to GeoCube™ thermal response test rig also shown

The water chemistry of the Hope Shaft mine water has been described in full detail by Burnside et al. (2016a) and will only be summarised here, with a representative analysis being presented in Table 1. The water is typically a sodium sulphate-(bicarbonate) water, which is likely to have formed by the mixture of an acid sulphate signature (derived from pyrite oxidation in the mined strata), with an ambient sodium bicarbonate water (which is typical of the deep British Coal Measures strata—Banks 1997; Banks et al. 1997b). During the past decade or so of pumping from Hope Shaft, the quality of the mine water has improved, with iron concentrations decreasing from c. 30 to c. 15 mg L−1, and sulphate concentrations declining from c. 1200 to c. 600 mg L−1. Since early 2015, the chloride concentrations increased to over 300 mg L−1 for reasons which are still not wholly clear. The Caphouse water consistently yields analyses of total iron somewhat higher than dissolved/ferrous iron (see Table 1), implying that oxidation of dissolved ferrous iron has commenced already in the workings or in the shaft. Indeed, an underground inspection of the over-water-table workings reveals plenty of opportunities for partial oxidation of a portion of the mine water cascading into the dewatered upper workings.

Table 1

Characteristic water analyses from the LoCAL study sites’ mine waters

 

Shettleston

Caphouse

Markham regime 1

Markham regime 2

Field determinations

11/2/16

27/4/16

 

27/4/16

 Temperature, °C

11.2

13.6

15.4c

13.3

 pH

7.14

6.87

 

7.33

 Dissolved oxygen, % saturation

21.8%a

18%

 

86%

 Electrical conductivity, µS cm−1

915

2733

 

2268

 Redox potential, mV

+19a

−35

 

+79

 Alkalinity, meq L−1

6.80

7.59

 

5.04

Dissolved gases

11/2/16

27/4/16

15/10/12

27/4/16

 CO2, mg L−1

nd

169b

nd

20.8b

 CH4, µg L−1

nd

495b

9040

16.5b

Cations

11/2/16

26/9/14

15/10/12

17/9/15

 Ca, mg L−1

92

77

435

130

 Mg, mg L−1

37

47

218

43

 Na, mg L−1

36

417

3690

434

 K, mg L−1

5.3

9

110

26

 Fe (dissolved), mg L−1

0.79

14.1

19.2–19.7

0.13–0.16

 Fe (total), mg L−1

1.62

16.5

21.5

0.72

 Mn, µg L−1

214

660

3410

27

 Ammoniacal-N, mg L−1

nd

1

5.0

<0.01

 Ba, µg L−1

74

10

150

120

 Sr, µg L−1

475

710

5440

1040

Anions

11/2/16

26/9/14

15/10/12

17/9/15

 Cl, mg L−1

65.4

136

6590

829

 SO4 =, mg L−1

58.1

640

1723

135

 Alkalinity, meq L−1

nd

9.57

8.69

6.25

 NO3 , mg L−1

0.54

nd

nd

3.1 (10/9/15)

 F, mg L−1

<0.5

nd

nd

nd

 Br, mg L−1

0.08

nd

nd

nd

Electrical conductivity is cited in µS cm−1, where 1 S = 1 ohm−1 = 1 mho

nd not determined

aDissolved oxygen and redox potential may be overestimated due to difficulties in avoiding contact with atmospheric oxygen during measurement

bDetermined by analysis by British Geological Survey of samples collected in stainless steel gas-tight ‘bombs’

cTypical value based on Athresh et al. (2015)

One of the drawbacks of the open-loop scheme is that it can, of course, only be used when mine water is being pumped from Hope Shaft (i.e. night time and early morning, when electricity is cheapest). The filters prior to the heat exchangers require regular cleaning of ochre deposits by museum staff, reportedly up to several times each day (Fig. 5). Despite the filters becoming clogged, however, there have not been major issues with clogging of the shell and tube heat exchangers with ochre deposits, an observation which lends weight to the assertion by staff (HUNOSA pers. comm.; Loredo et al. 2017) of the Barredo/Mieres heat pump scheme in Asturias, Spain, that shell and tube heat exchangers are less susceptible to ochre clogging than parallel plate heat exchangers.

Fig. 5

a A 0.45 µm filter used for water sampling at Shettleston. Note the many small ochreous particles retained on the filter; b the interior of a mine water strainer from Caphouse (significant ochre accretion), after 4 days’ operation; c the interior of a mine water pipe from Markham and d shell and tube heat exchanger (from Markham), both after 2.5 years’ operation (no ochre accretion)

Athresh et al. (2016) reports on the performance of the Caphouse open-loop scheme, as measured by (1) a Kampstrup 602 Multical heat meter measuring the thermal energy supplied from the heat pump to a thermal buffer tank, (2) an identical heat meter measuring the amount of thermal energy extracted from the mine water and (3) an ‘Autometer’ A100MT electric meter measuring the electrical power consumed by the heat pump unit. He reports that the heat pump (not including the electricity consumption of the shaft submersible pump, as this must be operated in any case for dewatering purposes) exhibits a coefficient of performance (ratio of useful heat supplied to buffer tank to electricity consumed by heat pump) varying from 3.5 to 4.0, with a mine water inflow temperature of around 14.5 °C and a temperature differential across the mine water heat exchangers of 5–6 °C.

Shettleston, Glasgow: open-loop system with reinjection

Shettleston (4.1669°W 55.8501°N) is amongst the oldest of Britain’s mine water heat pump schemes, having been commissioned in 1999 to provide space heating and pre-heating of domestic hot water to 16 social housing apartments in eastern Glasgow, Scotland. The early operation of the scheme was documented by Banks et al. (2009). In principle, the scheme abstracts mine water from a borehole (reported to be up to c. 100 m deep) with a submersible pump, passes the water directly through the evaporators of two heat pumps and then returns the thermally spent water to a shallower reinjection borehole situated some 37 m away. The abstraction borehole is believed to penetrate abandoned workings, probably of the Ell or possibly the slightly deeper Glasgow Main, Splint or Virgin seams (Burke 1998). It is not wholly clear whether the injection borehole returns water to a higher level of mine workings or simply to permeable horizons in the Carboniferous (Westphalian) Coal Measures aquifer sequence. The heat pumps currently employed are two Danfoss BW10-025 units each of nominal 31–34 kW heating capacity (for a nominal water inlet temperature of 10 °C).

To date, the system has run with relatively few operational problems and few issues with clogging of the evaporator heat exchangers themselves have been experienced. The water chemistry is normally similar to a rather conventional calcium bicarbonate groundwater and is rather low in dissolved iron. The fact that total iron is around double the dissolved iron in the analysis of Table 1, together with the observation of small ochre particles on sample filters, suggests that the iron in the water is already partially oxidised underground to form small ochre flocs (Fig. 5). It is reported that the mine water can episodically become very ochreous, as if iron oxyhydroxide particles are being flushed out of the mine system. It is suspected, but not yet established, that these episodes may be related to high rainfall episodes. The ochreous episodes can lead to in-line filters becoming clogged on the water supply line to the heat pump, resulting in head loss and the necessity for regular clearance. Furthermore, the reinjection borehole has reduced in capacity with time and currently a proportion of the spent water is run to waste at surface rather than being reinjected. The Shettleston site has only recently been incorporated into the LoCAL project and hence available data are very limited and the site will not be discussed further in detail.

Markham No. 3, Derbyshire: “standing column” system

Markham Colliery, located just north of Bolsover, Derbyshire, UK, comprises four main shafts. The site (1.3285°W 53.2424°N) of the two southern shafts (shafts nos. 2 and 3) is now occupied by a short-term operating reserve (STOR) gas engine electricity generation station, operated by the firm Alkane Ltd., and supplying peak load electricity to the National Grid to augment the electricity supply whenever a high demand or a reduction in conventional electricity supply is anticipated. Since 1904, Markham colliery worked coal from a number of seams of the Westphalian Lower and Middle Coal Measures strata (Sheppard 2005).

Markham No. 3 shaft is the only one of the shafts that has not been backfilled, following abandonment in around 1993. The shaft was brick-lined at 15 ft (4.6 m) diameter and was reportedly c. 490 m deep (healeyhero 2015), although shafts 1 and 4, with which shaft 3 interconnected, reached the Blackshale coal at c. 630 m deep (Burnside et al. 2016b). As at Caphouse (above), Markham colliery is a part of a wider network of hydraulically interlinked abandoned collieries, including those at Arkwright (53.2296°N 1.3633°W), Bolsover (53.2350°N 1.3116°W), Duckmanton (53.2447°N 1.3521°W) and Ireland, Staveley (53.2626°N 1.3456°W). Markham No 3 Shaft was left largely open, following abandonment, with a hydraulically open plug at the level of the Ell seam (−357 m asl), to allow venting of mine gas. This gas was initially used to power the gas engines at the Alkane site. However, as mine water levels rose following the post-abandonment cessation of pumping, the methane yield declined as methane-rich horizons became submerged. Deliberate methane abstraction ceased in 2006, and now imported gas is used to fuel the gas engine generators, although water levels in the shaft continue to rise. To give some impression of the rate of rise, in May 2011, the water level was 239.5 m bgl (−167.7 m asl), while by February 2016 it was at 136 m bgl (Fig. 6).

Fig. 6

a Graph showing rate of increase in mine water level in Markham No. 3 shaft, with b a superimposed section of the shaft, showing interconnections to other collieries and the arrangement of pump and reinjection return during pumping regime 1, and c abbreviated section of the shaft, showing arrangement of pump and reinjection return during pumping regime 2.

Modified from Burnside et al. (2016b)

In 2012, Alkane started trialling a pilot heat pump project based on mine water from No. 3 shaft. A ‘standing column’ type arrangement was installed, with an electric submersible pump (6″ Franklin VS14/20 with motor rated at 11 kW) installed at a short distance below the (then) water level at 235 m bgl (Athresh et al. 2015). As at Caphouse, the pumped water (at c. 14–15 °C) was passed through a mesh filter and then a sealed shell and tube heat exchanger arrangement, thermally coupled via a secondary circuit of heat transfer fluid to a Danfoss DHP-R 20 kW heat pump (Fig. 7). The thermally spent mine water at around 12–13 °C was returned, without atmospheric contact, via a reinjection main down the shaft to be released to the water column via a diffuser at 250 m bgl (this arrangement is referred to as standing column Regime 1—Fig. 6). No net abstraction of mine water thus takes place at Markham (Athresh et al. 2015). The heat pump supplies hot water at 52–55 °C to a buffer tank, which thereafter supplies hot water for space heating (via a combination of radiators, fan coil units and underfloor heating) to the Alkane on-site office complex. Return water to the heat pump is typically at c. 45–46 °C.

Fig. 7

Markham No. 3 Shaft heat pump system. a Two of the authors (AA and NB) at the shaft top; b mine water filter (relatively unclogged); c shell and tube heat exchangers, marked as HE (pump shown is used for filling and pressurising glycol circuit)

The overall efficiency of the system is compromised by the amount of electricity required to pump some 2 L s−1 of mine water up in excess of 200 m. Around April 2014, Athresh et al. (2015) estimated the system COP (heat supplied divided by electricity consumption by heat pump and submersible pump, based on idealised heat pump characteristics and estimated minimum energy required for pumping) to be no greater than 2.7. Athresh et al. (2015) also predicted that a system COP of 3.95 could be achieved if the mine water level rose to within 15 m of the surface.

In January 2015, mine water levels had risen, allowing the entire standing column arrangement to be raised in the shaft (thus potentially saving on pumping costs). The pump was re-positioned at 170 m bgl, with the reinjection diffuser now being set 17 m above the pump at 153 m bgl (known as standing column Regime 2—Fig. 6). Following this, the pumped water temperature appears to have fallen somewhat to 13–14 °C. As at Caphouse, the mine water has been regularly sampled (Burnside et al. 2016b, Table 1) and the performance of the system monitored, since January 2015, using (1) a Kampstrup 602 Multical heat meter measuring the thermal energy supplied from the heat pump to the thermal buffer tank, (2) an identical heat meter measuring the amount of thermal energy extracted from the mine water and (3) two electric meters, one measuring the electrical power consumed by the heat pump unit and the other measuring the power supplied to the submersible pump. An actual system COP (heat output divided by electrical consumption by the heat pump and submersible pump) of 1.9 has recently been calculated. Despite the submersible pump being fitted with a frequency controller and being run at 43 Hz and 5.2 kW power, it is clear that the electricity consumption by the submersible pump is detrimental to the overall efficiency.

The gas engine generators at the site have to be pressed into service within a couple of minutes of the National Grid requesting additional power. Thus, the engines have to be pre-warmed to enable a start at short notice. Previously an electric heater was used to pre-warm the engines but, most recently, the system has been modified so that the heat pump also pre-warms the gas engines. Moreover, when the engines are running, the facility also exists for the gas engines to feed exhaust heat back into the buffer tank on the space heating circuit on the condenser side of the heat pump, negating the need for heat pump operation during such episodes and enhancing the overall COP of the system (although the gas engines are only typically operated every few days to provide peak load electricity).

It was initially assumed that the Markham No. 3 mine water would be rather saline and highly reducing (as the water degasses natural dissolved methane which occasionally needs to be dispersed by air blowers in the shaft). During initial trial pumping of the shaft from 250–340 m depth, electrical conductivities in excess of 40,000 µS cm−1, and ammoniacal nitrogen concentrations of 14 mg L−1 were recorded, with very low sulphate concentrations indicative of sulphate-reducing conditions (Burnside et al. 2016b).

Following the installation of the standing column Regime 1, the water quality was still relatively saline, with electrical conductivities of 20,000–25,000 µS cm−1, dominated by sodium and chloride, but with 500–1700 mg L−1 sulphate. Concentrations of 4–5 mg L−1 ammoniacal nitrogen, 3–4 mg L−1 Mn and up to 9 mg L−1 methane all suggested broadly reducing conditions (although not necessarily sulphate reducing). Iron concentrations were typically 20–22 mg L−1, though occasionally falling to slightly below 4 mg L−1, and the iron appeared to be in its dissolved ferrous form. No problems were noted with clogging of the filters or heat exchangers with ochre deposits or other scale. This is presumed to be because iron remained reduced and soluble and was not exposed to atmospheric oxygen.

Following the raising of the standing column arrangement (regime 2), the mine water quality changed substantially, suggesting that there is likely to be stratification of the water column within the mine shaft, with fresher, less reducing water occupying the uppermost portion. The electrical conductivity declined to 2000–3000 µS cm−1 (although still Na–Cl dominated), sulphate to a few 100 mg L−1, ammonium and methane dropped to very low levels and nitrate was detected at 3–5 mg L−1. Manganese fell to <100 µg L−1 and iron to 310–720 µg L−1. Significantly, the dissolved iron was less than the total iron, suggesting that, now, some iron oxidation and hydrolysis might be taking place in the shaft itself. This has not yet manifested itself as problems with ochre clogging of filters or heat exchangers, however, possibly due to the low total iron concentrations available.

To date, no problems of long-term decline of temperature, relating to thermal feedback of reinjected cool water to the abstraction pump, have been noted (possibly reflecting the low pumping rate relative to the volume and cross section of the shaft, or maybe reflecting some water movement within the shaft), nor has any tendency towards ochre (or other) clogging of filters or heat exchangers (Fig. 5).

Caphouse, Yorkshire: closed-loop system

As an alternative to the open-loop scheme described above, at Caphouse Colliery the Vaillant Geotherm VWS 101/2 10.5 kW heat pump has the additional possibility of sourcing its energy from a closed-loop heat exchanger submerged in aeration pond A1 (Fig. 3). Because pond A1 always contains mine water, even when Hope Shaft is not being pumped, the closed-loop system can be used at any time of the day. The water temperatures and levels are continuously logged in the 1st aeration pond (A1, logger 1 in Fig. 3), the balancing pond (B, logger 2), near the outlet of the sedimentation basins (S, logger 3) and near the outlet of the upper reed bed (R1, logger 4). A typical time series for one week in summer (August 2015) is shown in Fig. 8.

Fig. 8

A typical (top) summer (August 2015) and (bottom) winter (December 2015) week of water temperature fluctuations logged in loggers 1 (1st aeration pond, A1 in Fig. 3), 2 (balancing pond, B), 3 (sedimentation pond, S) and 4 (outlet from reed bed wetland R1) in Caphouse mine water treatment system. The water level (cm head over logger sensor) shows periods of pumping of Hope Shaft. The crescent moons indicate night time (tick on x-axis at midnight) and suns indicate daytime

The water levels in the aeration pond clearly show the times of pumping (night and early morning) of Hope Shaft. During the daytime, there is little flow in the aeration pond and the water heats up, reaching a maximum of over 16 °C in early evening. Thereafter the water cools but drops, immediately when the Hope Shaft pumps are switched on, to a temperature a little above 14 °C (the mine water temperature). In the deeper balancing pond (B), temperatures reach around 15 °C during the day but as the Hope Shaft starts pumping, the warm water overflows from the aeration ponds into the balancing pond, causing a short-lived peak in temperature, which then drops off towards the mine water temperature. The temperature variation is even more subdued in the sedimentation pond. At the exit from the reed bed, however, the shallow slow water flow has been vulnerable to atmospheric temperature fluctuations and daytime temperatures of over 17 °C are reached.

During the winter (Fig. 8), almost the opposite picture emerges. As the Hope Shaft starts pumping in the evening, the water temperature in the 1st aeration pond increases to a constant 14 °C (the mine water temperature). After pumping ceases, the temperature drops slowly, depending on the air temperature. During the winter of 2015–16, however, the aeration pond seldom dropped below 11.5 °C. The balancing pond shows a similar pattern, but generally 0.5–1 °C cooler during pumping and several °C cooler when the Hope Shaft was not pumping. The sedimentation pond temperatures generally correspond to the balancing pond (B) but in a much more subdued form. As in summer, the reed bed outlet temperatures are much more susceptible to atmospheric interaction (heat losses during winter, especially at night).

The closed-loop heat exchanger is an NRS “Energy Blade 3K4” comprising four parallel 3 m × 0.49 m heat exchange panels in 304 stainless steel (Fig. 9), giving a total heat exchange surface area of 11.8 m2, mounted on a frame and submerged in the 1st aeration lagoon (A1 in Fig. 3). The nominal heat exchange capacity is cited as 8 kW in standing water (Nuenta 2015), which makes it suitable for coupling to a 10.5 kW heat pump, which, at a COP of 4 would be extracting 10.5 kW × 0.75 = 7.9 kW from the lagoon. The Energy Blade is coupled into the heat pump’s heat transfer fluid circuit via insulated flow and return pipes. The entire system is filled with 20% propylene glycol-based Hydratech Thermox FPG heat transfer fluid. The relatively low percentage of anti-freeze was selected in order to reduce fluid viscosity in a relatively long hydraulic circuit, in the knowledge that the aeration lagoons maintain a temperature well above 10 °C all year. The heat transfer fluid is circulated by the heat pump’s source-side circulation pump. The system has worked very satisfactorily since installation and is preferred over the open-loop system (above) by the Caphouse museum staff for two reasons (1) it can be used at any time and is not dependent on the Hope Shaft pumping at the time of operation, (2) no mine water is passed through the heat exchange/heat pump system, removing issues with ochre clogging or clearing of filters. During operation, the glycol circuit typically runs with a temperature differential of 5 °C, with fluid entering from the Energy Blade at 10.4 °C and leaving the evaporator at 5.3 °C. The relatively high differential suggests, in turn, that the heat pump’s circulation pump is somewhat undersized for the optimum flow rate.

Fig. 9

The Energy Blade™ (b) prior to and (a) during installation in Caphouse No. 1 aeration lagoon; (c) aeration lagoon No. 1 prior to desludging (2013) and (d) aeration lagoon No. 2 following desludging (2013).

Photographs reproduced with kind permission of Mr Alan Chalkley, National Coal Mining Museum of England

Two thermal response tests have been carried out on the Energy Blade using a GeoCube™ test rig manufactured by Precision Geothermal (2016). This rig essentially consists of a circulation pump, an array of electrical resistance heater elements capable of delivering up to c. 7.5 kW constant heat input, a flow meter and flow and return temperature sensors. The test rig is coupled to the Energy Blade via the heat transfer fluid circuit (Fig. 4) and a constant heating load is applied. The rate of heat loss through the Energy Blade can thus be measured and its heat transfer coefficient determined. The first test was run on 8th–9th October 2015 (Fig. 10) and was run for just over 21 h. Heat transfer coefficients of around 900–1000 W K−1 (76–85 W m−2 K−1, given a cited heat exchange surface of 11.8 m2) were measured when the Hope Shaft was not pumping and the water in the aeration lagoon was immobile. When the Hope Shaft was pumping water through the aeration lagoon, however, the heat transfer coefficient increased to 1140–1180 W K−1 (97–100 W m−2 K−1). This is significantly less than the heat transfer coefficient of 200 W m−2 K−1 claimed by Nuenta (2015) and is likely to be due to the GeoCube not achieving the minimum flow rate of 0.9 L s−1 recommended by the manufacturer (the rather small circulation pump of the GeoCube was only able to maintain a flow rate of some 0.4 L s−1, which would likely have resulted in turbulent flow not being achieved within the heat exchanger and thus the heat exchange capacity being reduced). Another possibility was that the Energy Blade had become partially submerged in the ochre sediment which accumulates at the base of the aeration lagoon and this had interfered with the heat exchange capacity. In fact, the aeration lagoon was emptied and desludged during 20th–27th October 2015. The test was re-run on 27th–28th April 2016 (Fig. 11), to evaluate whether desludging has improved the heat transfer performance of the blade. In fact, the heat transfer capacity appears to have decreased slightly in April 2016, although the exact values calculated depend on the assumptions about the baseline temperature of the mine water lagoon, which varies throughout the test. Given this uncertainty, there is no significant difference between the results of the two tests.

Fig. 10

Thermal response test on aeration lagoon heat exchanger, October 2015. The upper diagram shows the calculated electrical heater power (W), the glycol flow and return temperatures, the average glycol temperature, the lagoon water temperature from logger 1 and whether the mine water was pumping (shaded on/off). The lower diagram shows the glycol temperature displacement, relative to a baseline of 14.1 °C, the calculated heat transfer coefficient, relative to a lagoon baseline of 14.1 °C, a “corrected” heat transfer coefficient relative to the actual logged lagoon temperature, and whether the mine water was pumping (on/off)

Fig. 11

Thermal response test on aeration lagoon heat exchanger, April 2016. The upper diagram shows the calculated electrical heater power (W), the glycol flow and return temperatures, the average glycol temperature, the lagoon water temperature from logger 1 and whether the mine water was pumping (shaded on/off). The lower diagram shows the glycol temperature displacement, relative to a baseline of 12.9 °C, the calculated heat transfer coefficient, relative to a lagoon baseline of 12.9 °C, “corrected” heat transfer coefficient relative to the actual logged lagoon temperature, and whether the mine water was pumping (on/off). In this test, the lagoon warmed significantly naturally during the day (when the mine water was not being pumped): this led to an apparent increase in heat transfer coefficient due to the decreased temperature differential between the heat exchange fluid and the lagoon water. The “corrected” heat transfer coefficient may, however, be an overestimate, if the logger (which is installed close to the lagoon sides and at shallow depth) is not representative of the deeper, probably cooler, water surrounding the heat exchanger. The “uncorrected” heat transfer coefficient may thus be more reliable

Discussion and conclusions

It is possibly best to sum up the findings of this paper as advantages and disadvantages associated with each of the options discussed:

Open-loop systems

Advantage: scalable

Open-loop schemes can be up-scaled simply by adding additional heat exchange capacity (and treatment capacity/reinjection boreholes, if necessary). The ultimate limit on the heat that can be extracted is simply (a) the quantity of mine water that is pumped or discharged and (b) the temperature differential that can be achieved across a heat exchanger. It is not coincidental that the largest mine water heat pump schemes in the UK (Egremont, Cumbria—only a pilot scheme, of 103 kW, Banks et al. in press) and in the world (MW-scale schemes at Mieres, Spain and Heerlen, Netherlands) are all open-loop schemes.

Disadvantage: risk of chemical (ochre) precipitates

The Coal Authority’s Dawdon mine water heat pump scheme (Watson 2012; Bailey et al. 2013) found that passing iron-rich aerated mine water through a heat exchanger led to very rapid ochre clogging. In the case of Dawdon, this was solved using raw, unaerated mine water. This supports the observations and modelling work of Banks et al. (2009), which indicated that chemically reducing, iron-rich mine water can be used in heat exchange systems provided that it is not allowed to come into contact with atmospheric oxygen (or other oxidising agents), such that the iron remains in its soluble ferrous (Fe2+) form (this conclusion is also supported by research into ochre clogging of land drainage systems—Abeliovich 1985). The observations from the LoCAL study sites also support this hypothesis—for example, the fact that the Markham No. 3 system operated under Regime 1 with no serious clogging issues, despite the relatively high reduced iron concentrations.

However, the LoCAL project seems to have demonstrated that not all mine waters are sufficiently chemically reducing to rely on iron always being present in its ferrous form. Indeed, there appears to be a subset of coal mine waters where oxidation of iron has commenced in the underground workings or shafts, such that ochre particles can be observed in the raw water, or where ochre clogging occurs, even where access to the atmosphere is precluded in the surface headworks (Caphouse, Shettleston). This can be diagnosed by analysing the ratio of total to ferrous iron in water analyses or by examining on-site filters (e.g. used for water sampling) for ochre particles. The presence of modest quantities of ochre particles (e.g. Shettleston) does not necessarily render a heat exchange scheme unworkable, and can be managed by a degree of maintenance. Where reinjection is practised, however, the presence of even small amounts of particulate matter can lead to a decline in the reinjection efficiency with time.

As regards mineralogical composition, ochre collected from the Caphouse mine water treatment basins was analysed by X-Ray Diffraction; although calcite was detected as a component, no prominent iron mineral peaks were noted, leading to the inference that the ochre largely comprises amorphous ferric hydroxide. Iron deposits from plate heat exchangers of the Spanish Barredo site were also found to be mainly amorphous ferric hydroxide, with a 6.3% CaCO3 content, minor Mn-oxide content, and also with a detectable goethite (α-FeOOH) component (Loredo et al. 2017). Ochre deposits from the interior of the mine water pipe at the Scottish Shettleston scheme were also found to contain goethite.

In the future, the LoCAL project plans to experiment with dosing the mine waters with sodium bisulphite (NaHSO3) or sodium dithionite (Na2S2O4) prior to heat exchange, in an attempt to maintain iron in reduced form in solution (Dudeney et al. 2003). These reducing agents can be regarded as relatively environmentally benign, oxidising to form a solution of sodium and sulphate.

Disadvantage: difficulties in disposing of thermally spent water

While, in theory, the reinjection of iron-rich mine water is feasible, via a thorough understanding of chemistry (as at Heerlen, Netherlands), some difficulties in reinjection have been experienced at two Scottish schemes (Banks et al. 2009), due to the oxidation of dissolved iron and/or the presence of ochre particulates in the raw water. Thus, large open-loop mine water heat pump schemes will often be best suited to waters which (a) are already pumped for regional mine water management purposes and which are already treated prior to discharge to the environment (i.e. no additional pumping or treatment costs—e.g. Caphouse), or (b) which have low enough iron concentrations (and have good enough quality otherwise) that they can be disposed of directly to a surface watercourse (e.g. Egremont, Cumbria and Mieres, Spain), or, failing that, (c) are of reducing chemical quality and where pre-oxidised ochre and other particles are absent, such that reinjection can be practised.

Closed-loop systems

Advantage: does not depend on mine water pumping

Although the LoCAL project’s experiences at Caphouse indicate that a flow of mine water over a submerged heat exchanger does increase its heat transfer capacity, submerged closed-loop heat exchangers (in mines or in treatment basins) do not require a constant flow of mine water to function. They can thus be operated independently of any mine water pumping regime.

Advantage: managed fluid quality

No mine water is pumped, reinjected or circulated through heat exchangers/pumps in a closed-loop scheme. The fluid circulated is a heat transfer fluid of controlled composition (usually based on a solution of glycol). This obviates any issues with heat exchanger clogging or serious corrosion. On the other hand, it has been noted at Caphouse that the submerged heat exchanger becomes progressively fouled by accumulating ochre deposits in the aeration basin. We have, however, not been able to demonstrate that this, in itself, adversely affects heat capacity (the underperformance noted was likely due to inadequate heat transfer fluid flow rates).

Disadvantage: slightly less efficient

It can be seen, at Caphouse, that while the open-loop mine water scheme is based on mine water at 14 °C, the closed-loop scheme requires a temperature differential to absorb heat from the lagoon to the heat transfer fluid. Thus, the fluid returns from the lagoon to the evaporator typically at around 10.4 °C. This (together with the parasitic power required to circulate the heat transfer fluid) would be expected to result is a modestly lower heat pump efficiency.

Disadvantage: less readily scalable

Although, in theory, one could multiply the number of submerged heat exchangers in the aeration pond to increase the heat extraction, the amount of installed hardware could soon become unmanageable. For example, the Energy Blade extracts some 8 kW nominal heat capacity. To abstract the total potential of some 730 kW (Eq. 5) would require some 91 units. While a single unit can easily be lifted or moved when the aeration basin requires desludging of accumulated ochre, tens of units would undoubtedly prove off-putting to museum maintenance staff (it should, however, be noted that successful MW-scale closed-loop heat exchanger projects have been installed in very large natural lakes and reservoirs, which have no need for desludging or periodic removal, such as at Kings Mill Hospital, Mansfield, UK—Banks 2012).

Standing column systems

Advantage: may avoid licencing issues, need for treatment

Experiences at Markham No. 3 would suggest that standing column systems can work very successfully if the heat loads are modest. At Markham, very little additional infrastructure was required (submersible pump, controls, rising main, recharge main, heap exchangers, heat pump), given that the deep, large diameter open shaft already exists. No reinjection boreholes, no water treatment (other than venting of methane) and no surface disposal facilities were required. Under some legislative regimes, it may be possible to argue that, as no net abstraction is taking place and as water is being returned to the ground at the same quality as that abstracted, then no abstraction licences or discharge consents are necessary. This will, however, depend on the legal framework in each individual country.

Disadvantage: may not be scaleable

The modest 20 kW scheme at Markham appears to work very well, if one disregards the rather large parasitic submersible pump power caused by the deep water level. The larger (103 kW) pilot scheme at Egremont (Banks et al. 2017) also successfully operated for a short trial period. However, monitoring of temperatures during the Egremont trial suggested that the heat extractable by a pure standing column arrangement might be limited to no more than 100 W m−1 (or several tens of kW for a typical deep mine shaft of several 100 m depth). If natural advection is occurring within the shaft, however, replenishing the thermal resources, significantly greater heat yields might be available.

Concluding statement

The LoCAL project has successfully demonstrated the use of the four main mine water heat exchange configurations (open loop with discharge to surface water, open loop with reinjection, closed loop and standing column). Of these, the modest closed-loop scheme at Caphouse and standing column scheme at Markham have proved least problematic to operate (fewest problems with ochre clogging). The relative advantages and disadvantages of the schemes are summarised in Table 2. Although energy efficiency data are still being collected, the open-loop schemes may prove to be the more efficient schemes and are also likely to prove the most up-scalable. Among the outstanding issues that need to be investigated are:

Table 2

Summary of advantages and disadvantages of the various mine water heat exchange configurations shown in Fig. 2

Configuration

Open loop with discharge

Open loop with reinjection

Closed loop

Standing column

Examples

Caphouse, Mieres (Spain), Dawdon

Shettleston, Heerlen (Netherlands)

Caphouse

Markham, Egremont

Risk of ochre clogging

High, if water iron-rich and especially if exposed to oxygen

High, if water iron-rich and especially if exposed to oxygen

No

High, if water iron-rich and especially if exposed to oxygen

Legislative burden (licences, permits)

High

High

Low

Modest (depending on regulatory regime)

Energy efficiency of heat pump

High

High

Lower

High or lower, depending on degree of thermal feedback

Parasitic power loss (submersible pump)

Can be high (depending on mine water depth)

Can be high (depending on mine water depth)

Low (circulation pumps only)

Can be high (depending on mine water depth)

Potential thermal capacity

Large

Large

Modest

Modest, unless abstraction and reinjection hydraulically decoupled

Other advantages

Can be attractive if mine water is already pumped and treated for water management purposes

No treatment required

Controlled fluid quality. Can be installed in surface lagoons and ponds

Single site. No water transfer or treatment required

Other disadvantages

Cost of water treatment. Potential impact of temperature change on water treatment

Potential risk of clogging of reinjection boreholes. Requires at least two boreholes or shafts and water transfer pipe between them

  
  1. 1.

    can mine waters be successfully chemically dosed with environmentally benign reducing agents to hinder the oxidation and precipitation of ferric iron and manganese?

     
  2. 2.

    will altering the temperature of mine water (by heat extraction or rejection) adversely or favourably affect the efficiency of mine water treatment processes such as those at Caphouse (e.g. solubility of O2, CO2, rates of oxidation, hydrolysis, ochre nucleation and aggregation, rates of settlement, rate of growth of reeds in reed beds—Raftery 2016)?

     

Footnotes

  1. 1.

    Above sea level.

  2. 2.

    Below ground level.

Notes

Acknowledgements

The work reported in this paper was funded as part of the Low-Carbon After-Life (LoCAL) project under the European Commission Research Fund for Coal and Steel Grant RFCR-CT-2014-00001. The information on Shettleston is published by kind permission of the Shettleston Housing Association. We also wish to thank Dr. W. George Darling of the British Geological Survey for carrying out dissolved gas analyses from Caphouse and Markham (Table 1) and Drs Claire Wilson and Jaime Toney of the University of Glasgow for XRD analysis of ochre from Caphouse and Shettleston.

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© The Author(s) 2017

Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.

Authors and Affiliations

  1. 1.School of Engineering, James Watt Building (South)University of GlasgowGlasgowUK
  2. 2.Holymoor Consultancy Ltd.ChesterfieldUK
  3. 3.Innovative and Sustainable Built Environment Technologies Research Group (iSBET)Nottingham Trent UniversityNottinghamUK
  4. 4.Alkane Energy PlcEdwinstoweUK

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