Difference between revisions of "OR/17/020 Results"

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WOLSELEY, P A, JAMES, P A, THEOBALD, M R, and SUTTON, M. A. 2006. Detecting changes in epiphytic lichen communities at sites affected by atmospheric ammonia from agricultural sources. The Lichenologist. 38: 161–176</ref>; Mitchell et al., 2005<ref name="Mitchell  2005">MITCHELL, R J, TRUSCOT, A M, LEITH, I D, CAPE, J N, VAN DIJK, N, TANG, Y S, FOWLER, D, and SUTTON, M A. 2005. A study of the epiphytic communities of Atlantic oak woods along an atmospheric nitrogen deposition gradient. Journal of Ecology 93/3: 482–492</ref>; Stevens et al, 2012<ref name="Stevens 2012">STEVENS, C J, SMART, S M, HENRYS, P A, MASKELL, L C, CROWE, A, SIMKIN, J, CHEFFINGS, C M, WHITEFORD, C, GOWING, D J G, and ROWE, E C. 2012. Terricolous lichens as indicators of nitrogen deposition: Evidence from national records. Ecological Indicators 20: 196–203.</ref>).
 
WOLSELEY, P A, JAMES, P A, THEOBALD, M R, and SUTTON, M. A. 2006. Detecting changes in epiphytic lichen communities at sites affected by atmospheric ammonia from agricultural sources. The Lichenologist. 38: 161–176</ref>; Mitchell et al., 2005<ref name="Mitchell  2005">MITCHELL, R J, TRUSCOT, A M, LEITH, I D, CAPE, J N, VAN DIJK, N, TANG, Y S, FOWLER, D, and SUTTON, M A. 2005. A study of the epiphytic communities of Atlantic oak woods along an atmospheric nitrogen deposition gradient. Journal of Ecology 93/3: 482–492</ref>; Stevens et al, 2012<ref name="Stevens 2012">STEVENS, C J, SMART, S M, HENRYS, P A, MASKELL, L C, CROWE, A, SIMKIN, J, CHEFFINGS, C M, WHITEFORD, C, GOWING, D J G, and ROWE, E C. 2012. Terricolous lichens as indicators of nitrogen deposition: Evidence from national records. Ecological Indicators 20: 196–203.</ref>).
  
A recent analysis of groundwater dependent terrestrial ecosystems (GWDTEs) in England and Wales (Farr and Hall, 2014<ref name="Farr 2014">FARR and HALL. 2014. Atmospheric deposition at groundwater dependent wetlands: i mplications for effective catchment management and Water Framework Directive groundwater classification in England and Wales. Nottingham, UK, British Geological Survey, 62pp (OR/14/047) http://nora.nerc.ac.uk/510750/.</ref> which includes the Petrifying Springs Habitat H7220, found that nitrogen deposition exceeded the critical loads for a least one habitat features in 64% of GWDTEs (which also includes the H7220 habitat). However, the multiple potential sources of nitrogen (source), its fate within wetlands (pathway) and the impact on habitats (receptor) is not simple to unravel. Coupled with the need to consider the combined effects of multiple sources of nitrogen (atmospheric, surface water, groundwater) that may result in detrimental pressures to a habitat we also need to consider the potential effect of poor site management, under&nbsp;—&nbsp;over grazing and succession may have on habitat condition.
+
A recent analysis of groundwater dependent terrestrial ecosystems (GWDTEs) in England and Wales (Farr and Hall, 2014<ref name="Farr 2014"></ref> which includes the Petrifying Springs Habitat H7220, found that nitrogen deposition exceeded the critical loads for a least one habitat features in 64% of GWDTEs (which also includes the H7220 habitat). However, the multiple potential sources of nitrogen (source), its fate within wetlands (pathway) and the impact on habitats (receptor) is not simple to unravel. Coupled with the need to consider the combined effects of multiple sources of nitrogen (atmospheric, surface water, groundwater) that may result in detrimental pressures to a habitat we also need to consider the potential effect of poor site management, under&nbsp;—&nbsp;over grazing and succession may have on habitat condition.
  
 
Critical Loads for the petrifying springs habitat have not been defined specifically in the UK, however a recommended critical load is available and this is based upon based upon the corresponding EUNIS class (Hall et al., 2015<ref name="Hall 2015">HALL, J, CURTIS, C, DORE, T, and SMITH, R. 2015. Methods for the calculation of critical loads and their exceedances in the UK. Report to DEFRA, prepared under contract AQ0826. http://www.cldm.ceh.ac.uk/sites/cldm.ceh.ac.uk/files/MethodsReport_Updated_July2015_WEB.pdf</ref>). In England and Wales, or the current Annex 1 assessments, the EUNIS class D4.2 critical loads are applied. The current critical load range for this habitat is 15–25 kg N/ha/yr, with a recommended critical load of 15&nbsp;kg N/ha/year which we have applied to the petrifying springs habitats in this study. The results (Table&nbsp;7) show that all but three of the sites have modelled total nitrogen deposition that exceeds the recommended critical load. Only the coastal sites, Aust and Lydney are significantly below the critical load, and one island site Strawberry Banks has an average annual deposition just less than 15&nbsp;kg N/ha/year.
 
Critical Loads for the petrifying springs habitat have not been defined specifically in the UK, however a recommended critical load is available and this is based upon based upon the corresponding EUNIS class (Hall et al., 2015<ref name="Hall 2015">HALL, J, CURTIS, C, DORE, T, and SMITH, R. 2015. Methods for the calculation of critical loads and their exceedances in the UK. Report to DEFRA, prepared under contract AQ0826. http://www.cldm.ceh.ac.uk/sites/cldm.ceh.ac.uk/files/MethodsReport_Updated_July2015_WEB.pdf</ref>). In England and Wales, or the current Annex 1 assessments, the EUNIS class D4.2 critical loads are applied. The current critical load range for this habitat is 15–25 kg N/ha/yr, with a recommended critical load of 15&nbsp;kg N/ha/year which we have applied to the petrifying springs habitats in this study. The results (Table&nbsp;7) show that all but three of the sites have modelled total nitrogen deposition that exceeds the recommended critical load. Only the coastal sites, Aust and Lydney are significantly below the critical load, and one island site Strawberry Banks has an average annual deposition just less than 15&nbsp;kg N/ha/year.

Latest revision as of 15:01, 3 December 2019

Farr, G, and Graham, J. 2017. Survey, characterisation and condition assessment of Palustriella dominated springs 'H7220 Petrifying springs with tufa formation (Cratoneurion)' in Gloucestershire, England. British Geological Survey Internal Report, OR/17/020.

Elevation and orientation[edit]

The study sites (Figure 1-3) occur across a range of elevations from coastal cliff faces on the Severn Estuary at 11 maOD up to 252 maoD at Workmans Wood (Table 3).

Table 3    Elevation from 10 m DTM and general orientation.
Site Easting Northing Orientation Elevation maOD
Alder_Carr 385297 207895 SE 77
Aust_Cliff 356427 189190 NW 12
Bathurst_Estate 395150 204409 SE 137
Cranham_Woods 390447 212803 NE 236
Dodeswell 399177 220573 SE 175
Fishponds_Wood 382938 197047 SE 168
Horsley_Wood 383514 197603 SE 130
Kingscote_Wood 382753 197126 NE 148
Kingscote_Wood_Main 382634 197202 NE 139
Midger Wood (Fissidens) 380033 189530 NW 128
Midger_Woods_(Main) 380054 189602 SE 150
Minchiampton_Stream 386997 200066 NW 130
Sedbury_Cliff 355645 193093 SE 11
Slade_Brook 356774 205546 SW 70
Strawberry_Banks 390892 203500 SW 117
Toadsmore 387783 204209 SE 155
Woodchester_Park 1 382005 200757 NE 162
Woodchester_Park 2 381790 201226 NE 164
Woodchester_Park 3 382448 200505 NE 133
Woorkmans_Wood_WW1 390664 210676 NW 216
Woorkmans_Wood_WW2 390868 211171 NW 252
Woorkmans_Wood_WW3 390500 211532 SE 211

Wetlands functional mechanisms (WETMECS)[edit]

Wetlands Functional Mechanisms or ‘WETMECS’ as they are more commonly known were defined for the Environment Agency and describe the main (but not all) of the most common ecohydrological units that occur within lowland wetlands in England and Wales. They offer a simple way to classify water supply mechanisms to wetlands. The most appropriate for the majority of the sites within this study are ‘WETMEC 10a Permanent Seepage Slopes’ (Figure 4-1) and ‘WETMEC 17 (Figure 4-2) Groundwater flushed slopes’, which often occur together on following onto the other. They are often found in valley heads and slopes, typical of the Cotswold’s landscape where permanent groundwater discharge from semi-confined or unconfined bedrock or drift aquifers, issues from springs and seepages.

Figure 4-1    WETMEC 17 Groundwater flushed slopes (Environment Agency, 2009).
Figure 4-2    WETMEC 17 Groundwater flushed slopes (Environment Agency, 2009).

Most of the sites in this study are flushed with water that has emerged from a spring or seepage nearby. As tufa forms rapidly as groundwater reacts with the atmosphere, all of the tufa forming sites start almost immediately nearby the groundwater source that supplies them. The geology of Gloucestershire is varied and tufa is associated with a range of geologies and aquifers. The Great Oolite and Inferior Oolite Group of the Jurassic along with adjacent formations such as the Fullers Earth and Salperton Limestone were commonly associated with tufa forming springs in this study, although this may simply reflect our choice of study sites. The calcareous geology and the steep topography of the Cotswold’s valleys make this an ideal setting for springs and streams with active tufa formation. It is likely that there are many more tufa forming streams and springs associated with the Jurassic strata in the Stroud area. Tufa and H7220 habitat was also associated with Jurassic Whitby Mudstone Formation (Alder Carr); the Jurassic Blue Lias, and Triassic Penarth Group at cliff face seepages at Sedbury and the Carboniferous Limestone and Devonian Tintern Sandstone formation at Slade Brook.

Water chemistry[edit]

Field parameters[edit]

Field measurements were made for pH, temperature and electrical conductivity at the same time as collecting the water sample. Field readings for temperature ranged between 6.6°C to 10.7°C with a mean of 8.8°C, and field pH between 8.65 to 7.28 with a mean of pH 7.93. Field electrical conductivity ranged from 446 µscm to 1075 µscm with a mean of 598 µscm. Direct and careful on site measurements are water from tufa forming springs will change chemistry as it precipitates tufa. This is nicely illustrated by a comparison of field and lab electrical conductivity measurements taken on the same samples (Figure 4-4) where the lab electrical conductivities are all lower than the field data, this is possibly due to major ionic components (calcium, sulphate and bicarbonate) dropping out of solution. This confirms the need for onsite electrical conductivity and temperature readings when sampling at tufa forming springs. In addition, due to the rapidly changing chemical nature of the waters, alkalinity should be performed in the field and not in the laboratory (pers. com. Thomas Barlow).

Figure 4-3    Field temperature and pH (n= 24).
Figure 4-4    Electrical conductivity field versus laboratory (n= 24).

Major ions[edit]

The major ion chemistry allows us to look at the relative proportions of ions and to define baseline water types or facies. Firstly the table and box and whisker plot illustrate the samples collected from the site in this study (Table 4; Figure 4-5). The samples are mostly dominated by Ca2+ and HCO3- (calcium-bicarbonate type waters) however some samples do show relatively high proportions of Cl-and SO4 , namely samples from Woodchester Park, Midger Woods and also the coastal sites Aust and Sedbury Cliffs. The coastal sites may have some influence from sea spray or coastal rainfall. The major ions are also plotted on a Piper Diagram (Figure 4-6). Piper plots ae sometimes called ternary diagrams and are made up of two lower triangles, where the cations are plotted on the bottom left and the anions on the bottom right. The ‘results’ of these two plots are then projected up onto the upper diamond where it is possible to look at the ionic composition of the water samples in comparison to one another. It is clear that most of the water samples are gathered on the left hand side of the upper triangle, this is the calcium bicarbonate type area, suggesting that they are mostly of similar composition, this is expected as the majority of samples have been from the Jurassic Great Oolite and Inferior Oolite aquifers. The samples with more Cl-and SO42- are also clearly visible in the upper part of the diamond.

Table 4    Major ion water chemistry.
Figure 4-5    Major ions Box plot (n=24).
Figure 4-6    Piper plot showing the relative proportions of cations and anions (n=24). The bottom left hand triangle represents the cations and the bottom right hand triangle the anions, they are both projected into the upper diamond.

Nitrate & Phosphate[edit]

Recent work in the Netherlands (Royal Haskoning, 2016[1]) has, for the first time, tried to assign threshold values for nitrate and phosphate to the H7220 habitat. The work which also incorporates data collected from previous studies in Wales by the authors (see Farr et al., 2014[2]) suggests threshold values of 28 mg/l NO3- or 6.35 mg/l N and 0.05 mg/l P. The nitrate threshold value is higher than the UKTAG Threshold Values of 1 mg/l for medium altitude (>175 maOD) and 4.5 mg/l N for low altitude (<175 maOD) fens that include tufa forming springs (UKTAG, 2012a). For comparison the often quoted drinking water standard for nitrate is 50 mg/l as NO3- or 11.3 mg/l as N.

The data for each of the sites in this study is reported in descending order, for nitrate (as NO3- and N) (Figure 4-7), nitrite and total phosphate (Table 5). Nitrate ranges from 0.29 to 49.5 mg/l with a mean of 17.58 mg/l reported as NO3- or 0.06 to 11.12 with a mean of 3.98 mg/l reported as N (Figure 4-7).Nitrate levels in the Gloucestershire H7220 sites are higher than those reported from Welsh sites (Farr et al., 2014[2]), however this is to be expected as the land use for the majority of the Welsh sites was very low intensity. The sites with the highest nitrate are Midger Woods 1, Strawberry Bank, Fishponds Wood, Slade Brook, Kingscote Woods and Toadsmoor all of which have some form of agricultural activity within their potential catchments. We have compared the data collected for this study against the threshold values produced by Royal Haskoning (2016)[1] and using their threshold values for the H7220 habitat only Midger Woods, Kingscote and Horsley Woods, Strawberry Bank, Slade Brook and Toadsmoor ‘fail’ when compared to these nitrate threshold values (Figure 4-7). None of the sites exceed the phosphate threshold value of 0.05 mg/l (Figure 4-8). Although the nitrate threshold value was exceeded at several sites, it was not considered that vegetation was in unfavourable condition at any of the sites. This suggests that perhaps other factors such as flow, slope, shade, etc. also need to be considered in more detail.

Table 5    Nitrate and phosphate with the Royal Haskoning (2016)[1] threshold value in red.
Figure 4-7    Nitrate NO3 mg/l compared to the Royal Haskoning (2016)[1] threshold value of 28 mg/l NO3 (n=24). Sites that exceed the threshold value are indicated on the graph (threshold value is 6.35 mg/l when nitrate is reported as N).
Figure 4-8    Total Phosphate as P mg/l (with LOD of 0.01 mg/l) compared to the Royal Haskoning (2016)[1] threshold value of 0.05 mg/l PO43- (n=24).

Trace elements[edit]

Table 6    Trace elements (ug/l).

Atmospheric deposition and site relevant critical load[edit]

Excessive atmospheric deposition of nitrogen can be detrimental to most habitats, and in some cases could result in unfavourable status for Habitats Directive assessment. PlantLife (2016) estimate that 63% of the UKs most sensitive habitats are exposed to excessive nitrogen deposition. Although we could not find any information on the H7220 habitat, recent work has highlighted the risk to epiphytic bryophytes and lichens (Wolseley, et al., 2006[3]; Mitchell et al., 2005[4]; Stevens et al, 2012[5]).

A recent analysis of groundwater dependent terrestrial ecosystems (GWDTEs) in England and Wales (Farr and Hall, 2014[2] which includes the Petrifying Springs Habitat H7220, found that nitrogen deposition exceeded the critical loads for a least one habitat features in 64% of GWDTEs (which also includes the H7220 habitat). However, the multiple potential sources of nitrogen (source), its fate within wetlands (pathway) and the impact on habitats (receptor) is not simple to unravel. Coupled with the need to consider the combined effects of multiple sources of nitrogen (atmospheric, surface water, groundwater) that may result in detrimental pressures to a habitat we also need to consider the potential effect of poor site management, under — over grazing and succession may have on habitat condition.

Critical Loads for the petrifying springs habitat have not been defined specifically in the UK, however a recommended critical load is available and this is based upon based upon the corresponding EUNIS class (Hall et al., 2015[6]). In England and Wales, or the current Annex 1 assessments, the EUNIS class D4.2 critical loads are applied. The current critical load range for this habitat is 15–25 kg N/ha/yr, with a recommended critical load of 15 kg N/ha/year which we have applied to the petrifying springs habitats in this study. The results (Table 7) show that all but three of the sites have modelled total nitrogen deposition that exceeds the recommended critical load. Only the coastal sites, Aust and Lydney are significantly below the critical load, and one island site Strawberry Banks has an average annual deposition just less than 15 kg N/ha/year.

Table 7    Atmospheric deposition for NH3, NOx and Total Nitrogen compared to a recommended critical load value of 15 kg N/ha/year.

Tufa morphology and association with bryophytes[edit]

The definition of H7220 is ‘petrifying springs with tufa formation (Cratoneurion)’ and is somewhat suggestive that it is only Palustriella commutata that is associated with, or important for tufa formation. This is far from the truth, and the following discusses our general observations on the occurrence of tufa and association with other bryophytes during this study, illustrated in Figure 4-9. The various types of tufa structures are illustrated in Figure 4-10.

  • The occurrence of tufa is by no means a proxy for the likely extent of H7220 habitat. Slade Brook is an excellent example of how several hundred meters of impressive tufa dams can be formed but with relatively little H7220.
  • Tufa was deposited upon all sorts of substrates however it generally preferred to form on harder material (e.g. stones or living roots) rather than on soft organic mat erial such as rotting twigs (Beech leaves perhaps being an exception).
  • More often, Palustriella commutata was observed to grow upon tufa-encrusted stones rather than tufa-encrusted living tree roots or deadwood, and this has implications for potential restoration of tufa dams, with use of imported stone more likely to be successful when considering restoration of tufa dams and pools.
  • Eucladium verticillatum is well known for its association with tufa, and forms spectacular cushions on some of the cliff sites, but where Palustriella commutata was not present (e.g. Aust Cliffs Figure 3-10).
  • Perhaps the most interesting observation was the formation of large pools, retained behind tufa dams formed mainly of Pellia endiviifolia and Conocephalum conicum (e.g. Dowdeswell Figure 3-26).
Figure 4-9    Types of moss-tufa structures.
(a) Tufa dams formed in association with algae and very few bryophytes (Slade Brook); (b) blue/grey-coloured tufa formed in association with algae and no bryophytes (Workmans Wood site 2); (c) developing single patch of Palustriella commutata on tufa dam (Dowdeswell); (d) Large cushions of Eucladium verticillatum on tufa (Aust Cliff) (e) large tufa dam associated with Pellia endiviifolia and Conocephalum conicum (Dowdeswell); (f) the small aquatic moss Fissidens crassipes on tufa-encrusted stone (Minchinhampton Brook).
Figure 4-10    Illustration of the principal H7220 habiats in Gloucstershire.

Pressures and condition assessment[edit]

Table 8 lists the extent of the H7720 feature for each site and potential associated pressures, including hydrological, grazing, management, soil erosion and nutrient water chemistry. Many of these pressures have the potential to affect the H7220 feature positively or negatively so can be regarded as risks to the favourable conservation status of sites.

The following pressures have been highlighted:

Statutory Protection: a high proportion of sites with the H7220 feature (60%) lie within Sites of Special Scientific Interest (SSSI) and are therefore afforded a degree of protection. In addition, Cranham Wood and Workmans Wood site 3 lie within the Cotswold Beechwoods Special Area of Conservation (SAC) and are afforded a higher level of protection from wider land use pressures such as changes to hydrology and housing development. However, the H7220 feature is listed only in one SSSI citation for the sites surveyed (Cotswold Commons and Beechwoods SSSI) and 40% of sites surveys have no statutory protection or are afforded only mild protection in statutory planning law as County Wildlife sites.

Woodland Management: the majority of sites surveyed occurred in open (often rocky) woodland on valley sides. Woodland management has the potential to impact (both positively or negatively) on H7220 vegetation associated with flushes by affecting locally both levels of light and humidity. Such management could include tree planting (notably conifers), felling and thinning of woodland stands. In addition, brash (following various types of woodland management) can block seepage channels, shade or smother flush vegetation. Two sites (Dowdeswell and Woodchester Park site 3) have been highlighted where some sections of H7220 vegetation are negatively affected by shading from adjoining conifer plantations. Studies in Germany (Jokić, 2007) show that removal of conifers and replacement with an appropriate native woodland type promotes the regeneration of tufa-forming mosses.

Grazing: Two sites surveyed (Strawberry Bank and Toadsmoor) have open areas of H7220 vegetation that are lightly and traditionally grazed by cattle or ponies. In these situations, traditional light grazing is essential for maintaining the open mix of Palustriella commutata cushions with various wetland species. In the case of Toadsmoor, H7720 vegetation was grazed in conjunction with a small adjoining area of different ‘marshy vegetation’. Changes to the grazing regime at these sites (either an increase or abolition of grazing) has the potential to impact both positively or negatively on H7220 vegetation. Over grazing has been observed to negatively affect H7720 sites in Germany by physically damaging tufa formations (some forms of which can be fragile) causing soil erosion and increasing nutrients through dung (Jokic, 2007).

Soil Erosion: Several sites surveyed showed general signs of soil erosion (Workmans Wood sites 1 and 2) and in some cases this erosion may relate to the erection of stock fences (Toadsmoor, Kingscote and Horsley Woods site 4). In addition, several sites showed signs of soil erosion that may relate to the temporary increases in channel flow associated with installation of culverts and a single site (Toadsmoor) had soil erosion near to the springhead associated with the inappropriate location of a pig field.

Hydrological (abstractions): There are plenty of defunct piston pumps which are of no concern. We only identified one potentially active abstraction at the main spring head at Workmans Wood 3, however the plentiful outflow from the spring did not suggest that the water supply to the site was being degraded. Hydrological (drainage): we identified several historic and modern drainage features, including culverts and drains. The effect, weather positive or negative, of these features is unclear. We propose, based on visual observations only, that some drainage features such as culverts may alter the velocity of the water within proximity to the culvert and thus minimising the ability of tufa and tufa forming mosses to develop.

Water quality: Using the recently defined threshold values for N and P only four sites exceeded the nitrate threshold and no sites exceeded the phosphate threshold value.

Atmospheric deposition: although there is no specific critical load value for the H7220 habitat, the best estimate of 15 N kg/ Ha/ year is exceeded at all but three sites.

Condition assessment: The H7720 feature has been assessed as being in favourable condition for all of the 15 sites where it has been shown to occur. This is based on sites having the greater majority of the H7220 feature in good general condition (in terms of both tufa formations and Palustriella commutata- dominated vegetation) and land management being favourable. However, a number of concerns are highlighted for some sites including a number of sites failing for nitrate threshold values (Midger Wood site 1, Toadsmoor, Strawberry Bank, Slade Brook, Kingscote and Horsley Woods sites 1 and 3) and shading associated with conifer plantations (Dowdeswell, Woodchester Park site 3).

Table 8    Estimated extent of H7220 habitat, pressures and chemical threshold values.

References[edit]

  1. 1.0 1.1 1.2 1.3 1.4 ROYAL HOSKONING DHV. 2016. Towards threshold values for nutrients. Petrifying springs in South-Limburg (NL) in a Northwest European context.
  2. 2.0 2.1 2.2 FARR, G, GRAHAM, J, and STRATFORD, C S. 2014. Survey, characterisation and condition assessment of Palustriella dominated springs 'H7220 petrifying springs with tufa formation (Cratoneurion) in Wales Report for Natural Resources Wales. BGS Reference OR/14/043. Open Access Link http://nora.nerc.ac.uk/512109/
  3. WOLSELEY, P A, JAMES, P A, THEOBALD, M R, and SUTTON, M. A. 2006. Detecting changes in epiphytic lichen communities at sites affected by atmospheric ammonia from agricultural sources. The Lichenologist. 38: 161–176
  4. MITCHELL, R J, TRUSCOT, A M, LEITH, I D, CAPE, J N, VAN DIJK, N, TANG, Y S, FOWLER, D, and SUTTON, M A. 2005. A study of the epiphytic communities of Atlantic oak woods along an atmospheric nitrogen deposition gradient. Journal of Ecology 93/3: 482–492
  5. STEVENS, C J, SMART, S M, HENRYS, P A, MASKELL, L C, CROWE, A, SIMKIN, J, CHEFFINGS, C M, WHITEFORD, C, GOWING, D J G, and ROWE, E C. 2012. Terricolous lichens as indicators of nitrogen deposition: Evidence from national records. Ecological Indicators 20: 196–203.
  6. HALL, J, CURTIS, C, DORE, T, and SMITH, R. 2015. Methods for the calculation of critical loads and their exceedances in the UK. Report to DEFRA, prepared under contract AQ0826. http://www.cldm.ceh.ac.uk/sites/cldm.ceh.ac.uk/files/MethodsReport_Updated_July2015_WEB.pdf