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FdSc Countryside Management
Research Project –
The continued effect of damming moorland drainage
channels on Exmoor Mire vegetation
CU1.I.1
Andy Glendinning
27th April 2012
Word Count: 4872 (5000 max)
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Contents
1 Introduction ................................................................................................... 1
2 Literature Review .......................................................................................... 3
3 Methodology ................................................................................................. 8
3.1 Research Site Locations ......................................................................... 8
3.1.1 Exe Plain ............................................................................................. 8
3.1.2 Exe Head ............................................................................................. 8
3.1.3 Blackpitts 1 ........................................................................................ 12
3.1.4 Squallacombe .................................................................................... 12
3.2 Vegetation Surveys .............................................................................. 15
3.3 Risk Assessment .................................................................................. 18
3.4 Results Analysis Methodology .............................................................. 18
3.4.1 National Vegetation Classification and Biodiversity ........................... 18
3.4.2 Species Abundance and distance from the drainage channel ........... 18
3.4.3 Statistical Analysis Methodology ....................................................... 20
3.5 Possible areas of error or limitations .................................................... 21
4 Results ....................................................................................................... 22
4.1 National Vegetation Classification and Biodiversity .............................. 22
4.1.1 Exe Plain ........................................................................................... 23
4.1.2 Exe Head ........................................................................................... 24
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4.1.3 Blackpitts 1 ........................................................................................ 25
4.1.4 Squallacombe .................................................................................... 26
4.1.5 Consolidated year on year Biodiversity results .................................. 27
4.2 Moisture Indication – All species .......................................................... 28
4.2.1 Exe Plain ........................................................................................... 29
4.2.2 Exe Head ........................................................................................... 31
4.2.3 Blackpitts 1 ........................................................................................ 33
4.2.4 Squallacombe .................................................................................... 35
4.3 Moisture Indication – Bryophytes .......................................................... 37
4.3.1 Exe Plain ........................................................................................... 38
4.3.2 Exe Head ........................................................................................... 41
4.3.3 Blackpitts 1 ........................................................................................ 43
4.3.4 Squallacombe .................................................................................... 45
4.4 Spearman’s Rank Correlation Coefficient ............................................. 48
5 Discussion .................................................................................................. 49
6 Conclusion .................................................................................................. 53
References ....................................................................................................... 54
Bibliography ...................................................................................................... 60
Appendix A Exmoor Mires Restoration Risk Assessment Form ..................... 61
Appendix B Example from a completed data set ............................................ 62
Appendix C Summarised NVC for all Exmoor Mire Sites ................................ 63
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Abstract
Over the past few centuries the UK has lost much of its original peatlands to
agriculture and afforestation. With a growing awareness that such areas are at
risk of being lost altogether from the UK’s landscape and with it their
contribution to both biodiversity and ecosystem services, these peatland areas
are now the focus of restoration projects. Success of the projects is measured
in many ways; re-vegetation, increasing biodiversity, increased levels of
invertebrates and fauna, increased ecosystem services (e.g. improving water
quality and flood mitigation). The Exmoor Mires Restoration Project is one such
project, which periodically conducts vegetation surveys to assess its progress.
This paper reports on the background to the loss of such peatlands and the
management practices that are in place to restore them. It reviews some of the
research that has been conducted to assess the impacts of the loss and
subsequent effects of restoration work, in the UK and beyond. The analysis of
the survey data using a single method shows partial improvement, but not
across all the sites surveyed. Only when the data is further analysed and
assessed in parallel with vegetation classification and biodiversity
measurements can the report conclude that there has been positive change in
the mire’s vegetation communities. Although as reported from other examples
of the restoration process, it may take 5 to 10 more years before any real shift in
vegetation classification occurs.
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1 Introduction
Peatland areas cover about 2.9 million ha or 13% of the UK, with the majority, some 2.6
million ha, in Scotland (Scottish National Heritage, 1995; Milne and Brown, 1997). Yet
whilst this is less than 1% of the 350 million ha of all northern boreal and sub-arctic
peatlands, the UK’s peatlands contribute 10 to 15% of the world’s total for a particular
peatland type; the blanket bog (or mire) (Gorham, 1991; Tallis et al, 1998).
These mires have been subjected to a long history of management practices, with the
focus changing as different uses and ‘values’ has been found and assigned to this unique
habitat. The areas have been used for creating agricultural arable or grazing land, peat
extraction, afforestation and, more recently, increasing biodiversity, providing ecosystem
services (e.g. water quality, flood control) or carbon sequestration (Stewart and Lance,
1983; Holden, 2004; Defra 2008).
With increased awareness in conservation and the value of these unique habitats
(Natural England, 2012), such mire areas across the UK have become the focus of many
management strategies to restore then to their pristine state (IUCN, 2011).
In 1998 a partnership was established on Exmoor, with stakeholders including the
Environment Agency, Exmoor National Park Authority, Natural England, South West
Water, to design and implement restoration strategies pertinent to the local mires (ENPA,
2011). After many decades and even centuries of land management and drainage, the
Exmoor mires vegetation communities had become dominated by species that thrived on
the drying, changing land, e.g. Purple Moor Grass Molinia caerluea. The changes in
hydrology and vegetation community type also had the effect of limiting the range and
impact of the original bog-forming species; Sphagnum spp.
By systematically blocking previously dug drainage channels with an array of dam
materials, ranging from plastic and wood to straw and peat, the Exmoor Mires
Restoration Project intended to re-wet areas of the original mire with the aim of restoring
the original vegetation communities and habitats. By the end of 2010 the Project had
successfully re-wetted some 350 ha (ENPA, 2011).
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In 2011 the Exmoor Mires Project was assimilated into South West Water’s Upstream
Thinking, whose aims are to improve the quality and quantity of water not only on
Exmoor, but also on Dartmoor and within many of the Southwest of England’s rivers
(South West Water, 2012). With the intention to re-wet some additional 2000 ha on
Exmoor alone, the Project aims to restore many of Exmoor’s mires and with them their
associated vegetation communities and habitats. The outcome is to establish pristine
ecosystems that will in turn provide the ecosystem services necessary to improve the
areas water quality and quantity, whilst at the same time restoring and conserving the
area’s unique habitats and biodiversity.
As part of routine monitoring to determine the success, or otherwise, of their
management strategies, the Exmoor Mires Project carries out bi-annular vegetation
surveys. This project is based around the survey work conducted in 2011 and aims to
identify if the change, to a peat bog (mire) flora and associated National Vegetation
Classification (Rodwell, 1991), of selected areas on Exmoor is being actively achieved
through the management of moorland drainage and associated strategies.
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2 Literature Review
The focus of management of the UK’s peatlands, like much of that across Northern
Europe, has changed over many centuries and decades as different uses and ‘values’
have been assigned to this unique habitat (Holden et al 2004; Wilson et al 2010; Wilson
et al 2011a; Bönsel and Sonneck, 2011).
The draining of the UK’s peatland areas to increase and improve agricultural land has
been on-going for centuries. During the 17th century records show that, accompanying
land tenure and enclosure, large areas of the East Anglian fen lands were drained and
the land reclaimed (Holden et al 2004). Over the following centuries as pressures to
produce more foodstuffs for an ever expanding industrialised population grew, so more
land was drained and reclaimed. Baldock (1984) describes Britain as one of the most
extensively drained lands in Europe, where more than half of the UK’s agricultural activity
takes place on such land. With ever more sophisticated mechanical aids being
developed, e.g. the Cuthbertson plough, and the UK Government’s post World War 2
grant scheme to increase self-sufficiency, the upward pressure to drain and farm higher
areas increased (Anderson, 2010). With such incentives peaking in the 1960/70s and
ever larger ditches being dug on wetter hillsides in more effective, herring-bone patterns,
expansion rapidly extended to the draining of large areas of upland peatland for both
agriculture and forestry, with rates of land drainage reaching 100 000 ha yr-1 (Robinson
and Armstrong, 1988).
In the following years however it was reported that not only was there little evidence that,
overall, there was any net benefit for this effort, but that the work was having an adverse
effect on both the quality of the water derived from such areas and the peatland’s
biodiversity (Stewart and Lance, 1983; Natural England, 2009). It was recognised that
not only were these unique habitats at risk of being lost but that, restored, they could
significantly contribute to the UK’s biodiversity goals under the UN’s Convention on
Biological Diversity (JNCC, 2011). Additionally, the damage caused by creating large
drainage networks which whilst having the desired effect of drying out the land, was
having an adverse effect on the peat soils. Formed over many centuries in anaerobic
conditions, the result of drying and exposing the peat to aerobic conditions led to
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increased levels of dissolved organic carbon (DOC) and discoloration of the water run-
off, both of which are, to a greater or lesser extent problems for many of the UK’s water
authorities (Wallage et al, 2006; Armstrong et al, 2010). More recently, work under the
themes of climate change has recognised that the loss of the carbon from the dried and
exposed peat was not only a loss of a carbon store, but also a contributor to greenhouse
gases (Holden, 2004; 2007).
Today, upland peatlands or mires are at the forefront of restoration work across the UK’s
landscapes, whose aims are to restore these failing ecosystems for the benefit of many
of these causes (Natural England, 2011; 2012).
Peatlands fall into one of two categories; Bogs and Fens. Bogs, either raised or blanket,
are fed by atmospheric water only. Referred to as ‘ombrotrophic’, such peatlands are
acidic and nutrient poor peatlands. Fens however are fed also by ground water (referred
to a minerotrophic peatlands) and as a result tend to have higher levels of dissolved
minerals (Charman, 2002).
Bogs and fens can also be referred to as Mires, however the term Mire is
usually reserved for systems which are actively forming peat, whilst the term ‘peatlands’ also includes mires which have lost their typical vegetation and so may no longer be peat-forming (Bragg, 2002, p 112).
Mires, like other peatlands, are defined by the vegetation types that are able to establish
and thrive in a particular area. Mires are classified according to the National Vegetation
Classification index into one of 38 communities (Rodwell, 1991; Elkington et al, 2001).
Designated by the letter ‘M’, these communities range from those dominated by Purple
Moor Grass Molinia caerulea (M25), Hare’s Tail Cotton-grass Eriophorum vaginatum
(M20) or Sphagnum cuspidatum (M2) to those that have wider compositions of sedges
and sphagnum, e.g. Star Sedge Carex echniata and Sphagnum denticulatum (M6).
Whilst, with time, such vegetation will affect certain conditions, their presence is largely
dependent on the environmental conditions, e.g. moisture content, light, acidity. The
conditions in which certain species thrive have been classified for all European Plants
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and, subsequently, for all British Plants (Hill et al 2001; 2007). Each plant is classified by
allocating it an Ellenberg Indicator Value (EV), named after the initial European
classification, for a number environmental characteristics, including moisture and acidity,
on a scale of 1 to 12.
Restoration work usually centres on the blocking or damming of the drainage ditches to
raise the water levels and re-wet the land. The drains (or grips) are rarely completely in-
filled, rather they are blocked using a series of dams (Worrall and Warburton, 2011). The
type and size of dam is dependent on many factors, including; dimensions of drainage
channel, slope of ground, type of substrate and moisture content of existing peat
(Holden, 2009; Armstrong et al, 2010). Materials used in the damming process range
from using the surrounding’s peat in blocks and grass bales to wooden and plastic dams,
each having their place in also meeting the topographical and aesthetic needs of the
situation. Figure 1 shows photographs of examples of the Exmoor Mire Restoration
work.
Once the drainage channels have been blocked and dams created, success of the work
can be measured by monitoring the flow of water within and out-off the catchment area.
The restoration of mires can affect catchment hydrology significantly (Bragg, 2002;
Holden et al 2006), with the actual affect being determined by the particular restoration
technique applied (Natural England, 2011). Dip wells, placed at right angles across a
drainage channel or ditch, can monitor fluctuations in the level of the water table before
and after blocking work on the mire (Bragg, 2002). Measuring rainfall within the mire
area and the flow of water from the mire’s catchment area, using a ‘v-notch weir, allows
for accurate measurements of flow and water retention changes pre and post blocking
(Stewart and Lance, 1991; Wilson et al, 2010). When rainfall fluctuations are taken into
account, the mean water table level should rise as the dams allow water to flood areas
previously drained. Other monitoring that can indicate the success of the blocking work
can be through measuring vegetation changes, water chemistry and reduction in physical
erosion of the peatlands (Stewart and Lance, 1991; Rochefort, 2000; Bragazza et al,
2005; Wallage et al, 2006; Laine et al 2007; Wilson et al, 2011b). Sutherland (1996)
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reported that to monitor changes in vegetation, it is not necessary to identify absolute
values, rather it is sufficient to measure relative abundance.
Since 1998 and, more recently, on approximately two yearly cycles specific sites are
surveyed to monitor changes, if any, in vegetation type. The output from which
contribute to the assessment of whether the project is meeting it’s the aims and goals
and, if necessary, to modify management practices. In 2007 and 2009 specific reports
were produced to determine if changes could be seen through the analysis of specific
site data (Rutty, 2007; Hand, 2009).
This study aims to revisit several of these sites and present whether the continued drain-
blocking has resulted in increased biodiversity and the presence or increase of those
vegetation types that are associated with functioning upland mires. In order to
understand if such effects are indeed occurring, vegetation surveys will be conducted
along previously established transects and the results compared to previous year’s
surveys. The results will then be analysed to establish if the anticipated change in
vegetation species types and appropriate National Vegetation Classification (NVC)
communities (Rodwell, 1991; Elkington et al, 2001), of sections on Exmoor, is being
actively achieved through the management of moorland drainage and associated
strategies.
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Work on installing dams
(ENPA, 2011)
Completed wooden dam
(ENPA, 2011)
Completed wood, peat and bale dam Restored area showing overgrown dams and
‘Sphagnum pools’
Figure 1 Photographs showing Exmoor Mire Restoration work
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3 Methodology
The research work presented for this project was carried out during August through
October 2011, at four specific locations, as part of the overall Exmoor Mire Project
Vegetation Survey work of 2011. At each site a transect line had been established prior
to restoration work commencing and a baseline survey conducted.
Prior to the commencement of the 2011 surveying work, which was contracted to First
Ecology, the Exmoor Mires Project staff ran three knowledge exchange/training days to
acquaint the surveyors with the locations and, importantly, the likely plants species that
would be encountered.
3.1 Research Site Locations
The Exmoor Mires Project sites lie within the Exmoor National Park and are shown in
Figure 2. The four specific locations, at which the research work presented here was
conducted as presented below.
3.1.1 Exe Plain
The Exe Plain site was established in 2006 with the completion of a baseline survey. In
2007 dams were constructed across the major drainage channel at several locations.
Vegetation surveys were subsequently conducted in 2009 and 2011, although an interim
survey was conducted in 2008 as part of another research project (Hand, 2009). The
location of the site and orientation is shown in Figure 3.
3.1.2 Exe Head
The Exe Head site was one of the original pilot sites created in 1988, when the main
drainage channel was blocked. Surveys have been conducted approximately every two
years since 2006 (2008, 2009 and 2011). The location of the site and orientation is
shown in Figure 4.
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Figure 2 Exmoor Mires Project Sites
(First Ecology, 2012)
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Figure 3 Exe Plain site location
(First Ecology, 2012)
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Figure 4 Exe Head site location
(First Ecology, 2012)
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3.1.3 Blackpitts 1
Blackpitts 1 was also an original pilot site, established in 1988 and subsequently
surveyed in 2006, 2008, 2009 and 2011. The location of the site and orientation is
shown in Figure 5.
3.1.4 Squallacombe
The Squallacombe site was established in 2007 when a baseline vegetation survey was
followed by ditch blocking work. Subsequent surveys have been conducted in 2009 and
2011. The location of the site and orientation is shown in Figure 6.
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Figure 5 Blackpitts 1 site location
(First Ecology, 2012)
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Figure 6 Squallacombe site location
(First Ecology, 2012)
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3.2 Vegetation Surveys
The location of a transect line, across which the vegetation survey would be conducted,
was located using a hand held GPS unit. The start, mid-point and finish of each 1m wide
transect was identified by wooden stakes, two at each end and one in the middle. To
establish the exact path of the transect and its length, a surveying tape was laid along
one side of the transect. The tape was secured and precisely laid along the length of the
transect by the placement of regular spaced canes, see Figure 7.
Over the years many stakes become damaged by grazing animals, rot or become
submerged by the rising water. Missing or damaged stakes were routinely replaced,
again using precise GPS and tape measurements.
Once the surveying tape was secured, a 1m2 quadrat was placed at 1m intervals along
the length of the transect. Following each placement the quadrat was first photographed,
then surveyed for the presence of bryophytes and vascular plants. To aid surveying, the
1m2 quadrat was subdivided into four 0.25m2 sub-quadrats, see Figure 7. The
percentage cover for each species in each sub-quadrat was then assessed for
abundance and a corresponding score identified, as outlined on recording sheet, Figure
8.
The sub-quadrat score was then recorded on a pre-prepared recording sheet, see Figure
8. The sheet provided a list of likely species to be present and in a consistency that
aided recording.
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Positioning tape and canes Surveying on Blackpitts 1
Typical quadrat with variety of species, incl. Molinia caerulea, Narthecium ossifragum, Calluna vulgaris
and Sphagnum papillosum
Pool quadrat, incl. Sphagnum cuspidatum
Example showing ‘seasonal difficulty’ to identify clearly
M. caerulea dominated quadrat
Figure 7 Photographs showing surveying and typical quadrats
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The Exmoor Mire Restoration Project - Vegetation Monitoring Recorders: Date:
Location: QUADRATS
Score: <4%=1 4-25%=2 26-50%=3 51-75%=4 76-100%=5 No. No. No. No.
Species Common name i ii iii iv i ii iii iv i ii iii iv i ii iii iv
HERBS Calluna vulgaris Ling
Cirsium palustre Marsh Thistle
Drosera rotundifolia Sundew
Erica tetralix Cross-leaved Heath
Galium saxatile Heath Bedstraw
Narthecium ossifragum Bog Asphodel
Polygala serpyllifolia Milkwort
Potentilla erecta Tormentil
Succisa pratensis Devil's Bit Scabious
Vaccinium myrtillus Whortleberry
GRASSES Agrostis sp. Bent grass
Anthoxanthum odoratum Sweet Vernal grass
Deschampsia flexuosa Wavy-hair grass
Festuca ovina Sheep's Fescue
Molinia caerulea Purple Moor Grass
Nardus stricta Matt Grass
Trichophorum cespitosum Deer Grass
RUSHES Juncus acutiflorus Sharp-flowered/jointed Rush
Juncus bulbosus Bulbous Rush
Juncus effusus Soft Rush
Juncus squarrosus Heath Rush
Luzula multiflora Heath Woodrush
SEDGES Carex echinata Star Sedge
Carex binervis Green veined sedge
Carex nigra Common sedge
Carex panicea Carnation sedge
Eriophorum angustifolium Bog Cotton-grass
Eriophorum vaginatum Hare's tail cotton-grass
MOSS Aulacomnium palustre
Calliergonella cuspidatum
Campylopus introflexus
C. paradoxus (flexuosus)
Dicranella heteromalla
Dicranium scoparium
Hylocomium splendens
Hypnum cupressiforme
Pleurozium schreberi
Polytrichum commune
Pseudoscleropodium purum
Pseudotaxiphyllum elegans
Rhytidiadelphus loreus
Rhytidiadelphus squarrosus
Sphagnum S. capillifolium Bog mosses
S. cuspidatum
S. denticulatum (auriculatum)
S. fallax (recurvum)
S. palustre
S. papillosum
Figure 8 – Data recording sheet
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3.3 Risk Assessment
In addition to running species identification training, the Exmoor Mires Project ensured
that all surveyors were aware of the risks and the health and safety aspects of working
on the mires by ensuring that all likely risk areas were identified and assessed for each
site. A template for the operational risk assessment is shown in Appendix A.
3.4 Results Analysis Methodology
3.4.1 National Vegetation Classification and Biodiversity
Rodwell’s (1991) National Vegetation Classification has been used to provide a
standardised and systematic method of recording vegetation at the specific sites but also
a means by which sites, across the Exmoor Mires Project, can been compared.
Biodiversity in the form of species richness at each site is also presented, again to be
able to compare changes at each site but across the Exmoor Mires Project sites as a
whole.
3.4.2 Species Abundance and distance from the drainage channel
Species data from each site has been presented as a function of its abundance, per
quadrat, compared to its distance from the site’s blocked drainage channel.
The results have been analysed against two specific species lists dependant on whether
they are considered as positive (+ve) indicators of moisture or negative (-ve) indicators of
moisture on Ellenberg Moisture levels (Hill et al 2001; 2007). The lists have been
created by the on-going Mire Project research work. The first, the All Species list,
contains both vascular plants and bryophytes indicators, see Table 1, whilst the second
list contains selected bryophytes indicators only, see Table 2.
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Species latin Species common Species latin Species common
Drosera rotundifolia Sundew Calluna vulgaris Ling
Erica tetralix Cross-leaved Heath Galium saxatile Heath Bedstraw
Galium palustre Marsh Bedstraw Potentilla erecta Tormentil
Narthecium ossifragum Bog Asphodel Prunella vulgaris Selfheal
Pedicularis sylvatica Lousewort Vaccinium myrtillus Whortleberry
Polygala serpyllifolia Milkwort Agrostis spp. Bent Grasses
Potamogeton sp. Pondweed Anthoxanthum odoratum Sweet Vernal
V. oxycoccus Cranberry Festuca spp Fescue
Deschampsia flexuosa Wavy-hair grass Holcus mollis Creeping Soft Grass
Trichophorum cespitosum Deer Grass Molinia caerulea Purple Moor Grass
Juncus acutiflorus Sharp-flowered Rush Nardus stricta Matt Grass
Juncus bulbosus Bulbous Rush Juncus squarrosus Heath Rush
Juncus effusus Soft Rush Luzula multiflora Heath Woodrush
Eriophorum angustifolium Bog Cotton-grass Campylopus introflexus
Eriophorum vaginatum Hare's tail Campylopus paradoxus
Aulacomnium palustre Campylopus spp
Calliergonella stramineum Dicranella heteromalla
Polytrichum alpestre Dicranium scoparium
Polytrichum commune Hylocomium splendens
Sphagnum acutifolia spp Hypnum cupressiforme
Sphagnum augustifolium Isopterygium elegans
Sphagnum capillifolium Pleurozium schreberi
Sphagnum cuspidatum Polytrichum formosum
Sphagnum palustre Pseudoscleropodium purum
Sphagnum papillosum Racomitrium lanuginosum
Sphagnum fallax Rhytidiadelphus squarrosus
Sphagnum subsecundum Rhytidiadelphus loreus
Sphagnum subnitens
Sphagnum tenellum
Positive Moisture Indicator Species Negative Moisture Indicator Species
Table 1 List of selected All Species for both positive and
negative moisture indicators
+ve moisture indicators -ve moisture indicators
Sphagnum fallax Rhytidiadelphus squarrosus
Aulacomnium palustre Dicranium scoparium
Sphagnum palustre Pleurozium schreberi
Sphagnum papillosum Campylopus introflexus
Sphagnum cuspidatum Dicranella heteromalla
Sphagnum denticulatum Isopterygium elegans
Table 2 List of selected Bryophyte for both positive and
negative moisture indicators
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3.4.3 Statistical Analysis Methodology
Data from specific sites and the All Species lists have been further analysed using
Spearman’s Rank Correlation Coefficients. This Coefficient has been used because the
variables are ordinal and the results are expected to be monotonic (Lærd, 2012; Upton
and Cook, 1996). That is, as one variable increases the other decreases; an increase in
the abundance of +ve moisture indicators corresponds to a decrease in –ve moisture
indicator species or an increase (or decrease) in abundance corresponds to the distance
from the blocked drainage channel.
Spearman’ Coefficient will show either a strong positive or negative correlation,
represented by +1 or -1, or little or no correlation, where results approach zero, 0. For
the results presented in this report, a significant change in vegetation moisture indicator
type, from one survey to the next, will result in a coefficient approaching zero, i.e. ‘no
correlation’ or a strong negative correlation, approaching -1. The latter result would show
that the +ve indicators species had evenly replaced the –ve indicators across, for
example, a specific side of a transect.
Comparisons between two years of the same indicator species, on the same side of a
transect, that show a result approaching +1, will signify a strong correlation and therefore
that there has been little change in species types, their abundance or distribution.
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3.5 Possible areas of error or limitations
The following list, Table 3, are possible areas of error or limitations with the survey work
and subsequent analysis.
Area of error or limitation Likely effect of error or
limitation
Mitigation now and/or for
the future
Surveyor’s experience Misidentification of species
due to lack of knowledge
Future training
Weather conditions Misidentification due to
damp conditions affecting
ability to correctly identify
Hold surveys early in year
(June through August)
Timing of surveying work Increases likelihood of
misidentification due to loss
of key characteristics
(flowers, seed, colour)
Hold surveys early in year
(June through August)
Abundance measurement
units (1 thru 5)
Units/categories too large to
allow for subtleties and
observation differences
Increase number of
categories
Indicator species lists may
be too narrow
May not reflect changes in
vegetation
Review lists
Table 3 Possible sources or error or limitation
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4 Results
The results obtained for 2011 are presented below for each site in one or more category;
a) National Vegetation Classification and Species Richness
b) Moisture Indication – All Species
c) Moisture Indication – Bryophytes only.
The presence or otherwise of a site’s previous year’s results, in the above categories, is
dependent on the availability at the time. Where previous date was available it is
presented here for subsequent analysis and comparison purposes.
The data sets, being too large, are not presented in this report, however an example a
site’s completed data set is shown in Appendix B.
4.1 National Vegetation Classification and Biodiversity
The consolidated species lists for each site and, where available, previous year’s surveys
are shown in Tables 4 through 7 below, showing overall constancy (abundance) across
the transect and the indicative National Vegetation Classification (NVC) and Biodiversity
(Species Richness) for the site.
Table 8 is a consolidation of all survey data conducted at these sites up to and including
2011, showing change in biodiversity.
[Appendix C shows all survey NVC class data from all the Mires project sites, with NVC
changes and entries where known].
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4.1.1 Exe Plain
Exe Plain 2009 Exe Plain 2011
Latin Name Constancy Latin Name Constancy
Agrostis spp. 5 Agrostis spp. 5
Rhytidiadelphus squarrosus 5 Rhytidiadelphus squarrosus 5
Potentilla erecta 4 Potentilla erecta 4
Rumex acetosa 4 Ranunculus repens 4
Anthoxanthum odoratum 4 Molinia caerulea 4
Holcus lanatus 4 Juncus effusus 4
Molinia caerulea 4 Cirsium palustre 3
Juncus effusus 4 Epilob ium palustre 3
Hypnum cupressiforme 4 Galium palustre 3
Ranunculus repens 3 Rumex acetosa 3
Juncus acutiflorus 3 Holcus lanatus 3
Cirsium palustra 3 Nardus stricta 3
Stellaria ulignosa (alsine) 3 Juncus acutiflorus 3
Festuca spp 3 Sphagnum fallax 3
Luzula multiflora 3 Cardamine pratensis 2
Vaccinium myrtillus 2 Polygala serpyllifolia 2
Trichophorum cespitosum 2 Ranunculus acris 2
Cardamine pratensis 2 Ranunculus flammula 2
Epilob ium palustre 2 Vaccinium myrtillus 2
Galium palustre 2 Anthoxanthum odoratum 2
Galium saxatile 2 Trichophorum cespitosum 2
Polygala serpyllifolia 2 Juncus bulbosus 2
Ranunculus acris 2 Juncus squarrosus 2
Ranunculus flammula 2 Carex echinata 2
Deschampsia flexuosa 2 Carex panicea 2
Poa trivialis L. 2 Eriophorum vaginatum 2
Juncus bulbosus 2 Calliergonella cuspidata 2
Juncus squarrosus 2 Hypnum cupressiforme 2
Carex echinata 2 Sphagnum capillifolium 2
Carex nigra 2 Sphagnum palustre 2
Carex panicea 2 Calluna vulgaris 1
Eriophorum angustifolium 2 Galium saxatile 1
Calliergonella cuspidatum 2 Deschampsia flexuosa 1
Sphagnum capillifolium 2 Festuca spp 1
Sphagnum palustre 2 Carex b inervis 1
Sphagnum fallax 2 Carex nigra 1
Eriophorum vaginatum 2 Carex ovalis 1
Liverwort (thallus) 2 Eriophorum angustifolium 1
Calliergonella stramineum 1 Aulacomnium palustre 1
Poa palustria 1 Dicranium scoparium 1
Calluna vulgaris 1 Polytrichum commune 1
Sphagnum subnitens 1 Pseudoscleropodium purum 1
Nardus stricta 1 Sphagnum denticulatum 1
Polytrichum commune 1 Sphagnum tenellum 1
Sphagnum papillosum 1
Juncus articulatus 1
Carex ovalis 1
Aulacomnium palustre 1
Isopterygium elegans 1
Taraxacum officinale 1
Poa annua 1
Carex remota 1
Brachythecium rutabulum 1
Mnium hornum 1
Pleurozium screberi 1
Sphagnum denticulatum 1
Sphagnum cuspidatum 1
NVC M23 / M25 NVC (Class tbc) M23 / M25
Species Richness 57 Species Richness 44
Table 4 Exe Plain Species List, NVC and Biodiversity
A Glendinning FdSc Countryside Management
24
4.1.2 Exe Head
Exe Head 2006 Exe Head 2011
Latin Name Constancy Latin Name Constancy
Molinia caerulea 5 Molinia caerulea 5
Potentilla erecta 4 Sphagnum cuspidatum 4
Narthecium ossifragum 3 Narthecium ossifragum 3
Juncus effusus 3 Eriophorum vaginatum 3
Sphagnum palustre 3 Hypnum cupressiforme 3
Eriophorum angustifolium 2 Erica tetralix 2
Deschampsia flexuosa 2 Potentilla erecta 2
Hypnum cupressiforme 2 Juncus acutiflorus 2
Sphagnum fallax 2 Juncus bulbosus 2
Cirsium palustra 1 Eriophorum angustifolium 2
Viola palustris 1 Sphagnum denticulatum 2
Luzula multiflora 1 Sphagnum fallax 2
Sphagnum subnitens 1 Sphagnum tenellum 2
Erica tetralix 1 Polygala serpyllifolia 1
Polygala serpyllifolia 1 Ranunculus repens 1
Vaccinium myrtillus 1 Vaccinium myrtillus 1
Agrostis spp 1 Agrostis spp. 1
Anthoxanthum odoratum 1 Anthoxanthum odoratum 1
Holcus lanatus 1 Deschampsia flexuosa 1
Holcus mollis 1 Holcus lanatus 1
Trichophorum cespitosum 1 Holcus mollis 1
Juncus acutiflorus 1 Trichophorum cespitosum 1
Juncus squarrosus 1 Juncus effusus 1
Carex echinata 1 Luzula multiflora 1
Carex nigra 1 Carex echinata 1
Eriophorum vaginatum 1 Carex panicea 1
Aulacomnium palustre 1 Calliergonella cuspidata 1
Hylocomium splendens 1 Dicranium scoparium 1
Polytrichum commune 1 Polytrichum commune 1
Rhytidiadelphus squarrosus 1 Pseudoscleropodium purum 1
Dicranella sp 1 Rhytidiadelphus squarrosus 1
Campylopus sp 1 Sphagnum capillifolium 1
Liverwort 1 Sphagnum palustre 1
NVC M25 NVC (Class tbc) M3 / M17
Species Richness 33 Species Richness 33
Table 5 Exe Head Species List, NVC and Biodiversity
A Glendinning FdSc Countryside Management
25
4.1.3 Blackpitts 1
Blackpitts 1 2011
Latin Name Constancy
Molinia caerulea 5
Potentilla erecta 4
Juncus effusus 4
Narthecium ossifragum 3
Agrostis spp. 3
Carex echinata 3
Hypnum cupressiforme 3
Deschampsia flexuosa 2
Trichophorum cespitosum 2
Eriophorum vaginatum 2
Blackpitts 1 2006 Sphagnum fallax 2
Latin Name Constancy Sphagnum palustre / papillosum 2
Molinia caerulea 5 Cirsium palustre 1
Potentilla erecta 4 Erica tetralix 1
Juncus effusus 4 Galium saxatile 1
Eriophorum angustifolium 3 Polygala serpyllifolia 1
Narthecium ossifragum 3 Vaccinium myrtillus 1
Sphagnum palustre 3 Anthoxanthum odoratum 1
Sphagnum fallax 3 Juncus acutiflorus 1
Deschampsia flexuosa 2 Juncus squarrosus 1
Polygala serpyllifolia 2 Carex nigra 1
Trichophorum cespitosum 2 Eriophorum angustifolium 1
Carex echinata 2 Aulacomnium palustre 1
Hypnum cupressiforme 2 Dicranella heteromalla 1
Sphagnum subnitens 1 Polytrichum commune 1
Erica tetralix 1 Rhytidiadelphus squarrosus 1
Agrostis spp 1 Sphagnum capillifolium 1
Eriophorum vaginatum 1 Sphagnum palustre 1
Viola palustris 1 Sphagnum papillosum 1
Vaccinium myrtillus 1 Sphagnum subnitens 1
Cirsium palustra 1 Sphagnum tenellum 1
Luzula multiflora 1 Holcus mollis 1
Carex nigra 1 Galium palustre 1
Aulacomnium palustre 1 Holcus lanatus 1
Polytrichum commune 1 Viola palustris 1
Liverwort 1 Epilob ium palustre 1
Holcus lanatus 1 Mnium hornum 1
Juncus acutiflorus 1 Plagiothecium undulatum 1
Juncus squarrosus 1 Sphagnum squarrosum 1
Hylocomium splendens 1 Sphagnum teres 1
NVC M25 NVC (Class tbc) M25
Species Richness 28 Species Richness 40
Table 6 Blackpitts 1 Species List, NVC and Biodiversity
A Glendinning FdSc Countryside Management
26
4.1.4 Squallacombe
Squallacombe 2011
Latin Name Constancy
Calluna vulgaris 4
Vaccinium myrtillus 4
Molinia caerulea 4
Eriophorum vaginatum 4
Potentilla erecta 3
Eriophorum angustifolium 3
Squallacombe 2009 Hypnum cupressiforme 3
Latin Name Constancy Sphagnum cuspidatum 3
Molinia caerulea 5 Erica tetralix 2
Vaccinium myrtillus 4 Narthecium ossifragum 2
Eriophorum angustifolium 4 Deschampsia flexuosa 2
Eriophorum vaginatum 4 Trichophorum cespitosum 2
Hypnum cupressiforme 4 Juncus squarrosus 2
Sphagnum cuspidatum 3 Aulacomnium palustre 2
Calluna vulgaris 3 Polytrichum commune 2
Erica tetralix 3 Rhytidiadelphus loreus 2
Narthecium ossifragum 3 Sphagnum capillifolium 2
Potentilla erecta 3 Sphagnum papillosum 2
Deschampsia flexuosa 3 Sphagnum fallax 2
Galium saxatile 2 Drosera rotundifolia 1
Trichophorum cespitosum 2 Galium palustre 1
Juncus squarrosus 2 Galium saxatile 1
Dicranium scoparium 2 Pedicularis sylvatica 1
Rhytidiadelphus squarrosus 2 Polygala serpyllifolia 1
Sphagnum capillifolium 2 Potamogeton sp. 1
Sphagnum papillosum 2 V. oxycoccus 1
Sphagnum subnitens 2 Agrostis spp. 1
Isopterygium elegans 1 Festuca spp 1
Drosera rotundifolia 1 Nardus stricta 1
Nardus stricta 1 Juncus acutiflorus 1
Campylopus introflexus 1 Juncus bulbosus 1
Hylocomium splendens 1 Juncus effusus 1
Cladonia sp.(squammules) 1 Luzula multiflora 1
Agrostis spp. 1 Bryum pseudotriquetam 1
Festuca spp 1 Calliergonella stramineum 1
Juncus effusus 1 Campylopus paradoxus 1
Polytrichum commune 1 Dicranium scoparium 1
Rhytidiadelphus loreus 1 Isopterygium elegans 1
Empetrum nigrum 1 Pleurozium schreberi 1
Juncus bulbosus 1 Polytrichum alpestre 1
Luzula multiflora 1 Pseudoscleropodium purum 1
Pleurozium screberi 1 Rhytidiadelphus squarrosus 1
Sphagnum fallax 1 Thuiidium tamariscinum 1
Polygala serpyllifolia 1 Sphagnum acutifolia spp 1
Anthoxanthum odoratum 1 Sphagnum palustre 1
Aulacomnium palustre 1 Sphagnum subsecundum 1
Polytrichum alpestre 1 Sphagnum subnitens 1
Sphagnum palustre 1 Sphagnum tenellum 1
Campylopus paradoxus 1 Sphagnum unknown 1
NVC M3 / M17 NVC (Class tbc) M3 / M17
Species Richness 41 Species Richness 49
Table 7 Squallacombe Species List, NVC and Biodiversity
A Glendinning FdSc Countryside Management
27
4.1.5 Consolidated year on year Biodiversity results
Exe Plain Exe Head Blackpitts 1 Squallacombe
1998 Initial Survey
All species 34 32 Bryophytes 11 11
2006 Pre-restoration
All species 36 33 28 Bryophytes 10 10 7
2007 Pre-restoration
All species 37 Bryophytes 15
2008 All species 55 37 38 Bryophytes 18 13 15
2009 All species 57 37 39 41 Bryophytes 16 12 13 18
2011 All species 44 33 40 49 Bryophytes 12 11 15 24
Table 8 Biodiversity changes at selected Exmoor Mire Restoration
Project sites, 1998 - 2011
(Source data: Hand, 2009. Updated by A Glendinning)
The NVC and biodiversity results show that for Exe Plain and Exe Head all species
biodiversity has fallen during the period of 2009 to 2011, whilst for the Blackpitts 1 site
there has been little change. Squallacombe has seen a ‘year’ on ‘year’ increase since
restoration, with recorded Bryophytes making up nearly 50% of the species present.
Exe Plain is still dominated by Agrostis spp, Rhytidiadelphus squarrosus, Tormentil
Potentilla erecta and M. caerulea, there has been little change in the overall constancy
(abundance) of +ve indicators like Bog Cotton Grass Eriophorum angustifolium, Bulbous
Rush Juncus bulbosus or Sphagnum spp.
Squallacombe and Blackpitts 1 biodiversity since 2006 has increased. However, whilst
for Squallacombe there has been little change in those species that are dominant, some
negative moisture indicators, e.g. M caerulea and Hypnum cupressiforme, have fallen.
A Glendinning FdSc Countryside Management
28
4.2 Moisture Indication – All species
The results for site moisture indication for all species are presented for each site in
Figures 9 through 16. They show the presence of the indicators species relative to the
centre of the transect (the old drainage channel), at 1m intervals, as a function of overall
abundance of the +ve and –ve indicator groups.
Where previous year’s data was available, it has been presented here for analysis and
comparison purposes.
Exe Plain +ve indicators are showing a marked improvement in 2011 towards the
blocked drainage channel (the ditch) on the right hand side (RHS) but this is not mirrored
on the left hand side (LHS), where actually the indicators appear to be increasing the
further the transect is surveyed from the ditch. The –ve indicators on the RHS are
showing a marked decrease in abundance in 2011 and a levelling of their distribution,
whereas the LHS is showing reduction near to the ditch and then increasing the further
away from the ditch the survey is conducted.
Exe Head and Blackpitts 1 –ve indicators for 2011 show an overall increase the further
from the ditch, however the results for the +ve indicators are less clear.
Squallacombe +ve indicators appear to show little or no change in the overall pattern of
abundance the further from the ditch the survey was conducted, this is reflected also for
the –ve indicators particularly for the change from 2009 to 2011 on the RHS of the ditch.
A Glendinning FdSc Countryside Management
29
4.2.1 Exe Plain
metres to the right ← of drainage channel → metres to the left
2006, All Species, Positive (+ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.3879
0
5
10
15
20
25
30
35
40
1 3 5 7 9 11 13 15
R² = 0.0828
0
5
10
15
20
25
30
35
40
16 18 20 22 24 26 28 30
metres to the right ← of drainage channel → metres to the left
2009, All Species, Positive (+ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.69590
5
10
15
20
25
30
35
40
1 3 5 7 9 11 13 15
R² = 0.0195
0
5
10
15
20
25
30
35
40
16 18 20 22 24 26 28 30
metres to the right ← of drainage channel → metres to the left
2011, All Species, Positive (+ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.1634
0
5
10
15
20
25
30
35
40
1 3 5 7 9 11 13 15
R² = 0.3694
0
5
10
15
20
25
30
35
40
16 18 20 22 24 26 28 30
Figure 9 Exe Plain - All species Positive Indicators, 2006, 2009 and 2011
A Glendinning FdSc Countryside Management
30
2006, All Species, Negative (-ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
R² = 0.7337
0
5
10
15
20
25
30
35
40
1 3 5 7 9 11 13 15
R² = 0.3576
0
5
10
15
20
25
30
35
40
16 18 20 22 24 26 28 30
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2009, All Species, Negative (-ve) Indicators
R² = 0.7166
0
5
10
15
20
25
30
35
40
1 3 5 7 9 11 13 15
R² = 0.0171
0
5
10
15
20
25
30
35
40
16 18 20 22 24 26 28 30
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2011, All Species, Negative (-ve) Indicators
R² = 0.8178
0
5
10
15
20
25
30
35
40
16 18 20 22 24 26 28 30
R² = 0.0517
0
5
10
15
20
25
30
35
40
1 3 5 7 9 11 13 15
Figure 10 Exe Plain - All species Negative Indicators, 2006, 2009 and 2011
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31
4.2.2 Exe Head
metres to the left ← of drainage channel → metres to the right
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2006, All Species, Positive (+ve) Indicators
R² = 0.2374
0
5
10
15
20
25
30
35
1 6 11 16
R² = 0.2927
0
5
10
15
20
25
30
35
19 24 29 34
2011, All Species, Positive (+ve) Indicators
metres to the left ← of drainage channel → metres to the right
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.1461
0
5
10
15
20
25
30
35
1 6 11 16
R² = 0.2818
0
5
10
15
20
25
30
35
19 24 29 34
Figure 11 Exe Head - All species Positive Indicators, 2006 and 2011
A Glendinning FdSc Countryside Management
32
metres to the left ← of drainage channel → metres to the right
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2006, All Species, Negative (-ve) Indicators
R² = 0.4544
0
2
4
6
8
10
12
14
16
1 3 5 7 9 11 13 15
R² = 0.0012
0
2
4
6
8
10
12
14
16
19 24 29 34
metres to the left ← of drainage channel → metres to the right
2011, All Species, Negative (-ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.4985
0
2
4
6
8
10
12
14
16
1 6 11 16
R² = 0.3657
0
2
4
6
8
10
12
14
16
19 24 29 34
Figure 12 Exe Head - All species Negative Indicators, 2006 and 2011
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33
4.2.3 Blackpitts 1
metres to the left ← of drainage channel → metres to the right
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2006, All Species, Positive (+ve) Indicators
R² = 0.7399
0
5
10
15
20
25
30
1 3 5 7 9 11 13 15
R² = 0.7123
0
5
10
15
20
25
30
16 18 20 22 24 26 28 30
metres to the left ← of drainage channel → metres to the right
2011, All Species, Positive (+ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.5851
0
5
10
15
20
25
30
1 3 5 7 9 11 13 15
R² = 0.563
0
5
10
15
20
25
30
16 18 20 22 24 26 28 30
Figure 13 Blackpitts 1 - All species Positive Indicators, 2006 and 2011
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34
2006, All Species, Negative (-ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the left ← of drainage channel → metres to the right
R² = 0.3387
0
2
4
6
8
10
12
14
16
18
1 3 5 7 9 11 13 15
R² = 0.7694
0
2
4
6
8
10
12
14
16
18
16 18 20 22 24 26 28 30
2011, All Species, Negative (-ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the left ← of drainage channel → metres to the right
R² = 0.5136
0
2
4
6
8
10
12
14
16
18
1 3 5 7 9 11 13 15
R² = 0.4325
0
2
4
6
8
10
12
14
16
18
16 18 20 22 24 26 28 30
Figure 14 Blackpitts 1 - All species Negative Indicators, 2006 and 2011
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35
4.2.4 Squallacombe
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2007, All Species, Positive (+ve) Indicators
R² = 0.0976
0
5
10
15
20
25
30
35
1 6 11 16 21
R² = 0.5653
0
5
10
15
20
25
30
35
26 31 36 41 46
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2009, All Species, Positive (+ve) Indicators
R² = 0.3656
0
5
10
15
20
25
30
35
1 6 11 16 21
R² = 0.4679
0
5
10
15
20
25
30
35
26 31 36 41 46
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2011, All Species, Positive (+ve) Indicators
R² = 0.0508
0
5
10
15
20
25
30
35
1 6 11 16 21
R² = 0.4077
0
5
10
15
20
25
30
35
26 31 36 41 46
Figure 15 Squallacombe - All species Positive Indicators, 2007, 2009 and 2011
2009
2011
A Glendinning FdSc Countryside Management
36
2007, All Species, Negative (-ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
R² = 0.2591
0
5
10
15
20
25
30
35
1 6 11 16 21
R² = 0.0953
0
5
10
15
20
25
30
35
26 31 36 41 46
2009, All Species, Negative (-ve) Indicators
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
R² = 0.2114
0
5
10
15
20
25
30
35
1 6 11 16 21
R² = 0.0336
0
5
10
15
20
25
30
35
26 31 36 41 46
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
2011, All Species, Negative (-ve) Indicators
R² = 0.173
0
5
10
15
20
25
30
35
1 6 11 16 21
R² = 0.0123
0
5
10
15
20
25
30
35
26 31 36 41 46
Figure 16 Squallacombe - All species Negative Indicators, 2007, 2009 and 2011
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37
4.3 Moisture Indication – Bryophytes
The consolidated results for the selected Bryophyte Indicators are presented in Tables 9
through 12, which show the overall abundance of individual bryophyte species across the
whole transects, for each site. This data has been presented here to allow comparison to
early surveys (Hand, 2009).
The results for the selected Bryophyte Indicators are shown in Figures 17 through 24, for
each site, and show the overall presence (abundance) of both +ve or –ve indicator
groups per quadrat, relative to the centre of the transect (the old drainage channel), at
1m intervals.
Where previous year’s data was available, it has been presented here for analysis and
comparison purposes.
Exe Plain results show an increase in positive indicators on the LHS with a
corresponding reduction and ‘levelling’ of negative indicators, however the positive
indicators are rising away from the ditch.
At Squallacombe the LHS appears to show more change than the RHS. However, here
the positive indicators are increasing moving away from the ditch and then levelling,
whereas the negative indicators are falling moving away from the ditch and then levelling.
A Glendinning FdSc Countryside Management
38
4.3.1 Exe Plain
EV* 2006 2008 2009 2011
Sphagnum fallax 9 2 3 2 3
Aulacomnium palustre 8 1 1 1 1
Sphagnum palustre 8 1 3 2 2
Sphagnum papillosum 8 1 1 1
Sphagnum cuspidatum 10 1 1
Sphagnum denticulatum 9 1 1
Rhytidiadelphus squarrosus 5 3 4 5 5
Dicranium scoparium 5 1 1
Pleurozium schreberi 5 1 1
Campylopus introflexus 5 1
Dicranella heteromalla 5 1
Isopterygium elegans 6 2
+v
e m
ois
ture
in
dic
ato
rs-v
e m
ois
ture
in
dic
ato
rs
Table 9 Exe Plain site bryophyte changes, 2006 – 2011
* EV – indicate Ellenberg Moisture Indicator value for species type
A Glendinning FdSc Countryside Management
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To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
2006, Bryophytes, Positive (+ve) Indicator
2009, Bryophytes, Positive (+ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
2011, Bryophytes, Positive (+ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
metres to the right ← of drainage channel → metres to the left
R² = 0.2881
0
2
4
6
8
10
12
1 3 5 7 9 11 13 15
R² = 0.044
0
2
4
6
8
10
12
16 18 20 22 24 26 28 30
R² = 4E-05
0
2
4
6
8
10
12
1 3 5 7 9 11 13 15
R² = 0.3307
0
2
4
6
8
10
12
16 18 20 22 24 26 28 30
R² = 0.0701
0
2
4
6
8
10
12
1 3 5 7 9 11 13 15
R² = 0.0041
0
2
4
6
8
10
12
16 18 20 22 24 26 28 30
Figure 17 Exe Plain - Bryophytes Positive Indicators, 2006, 2009 and 2011
A Glendinning FdSc Countryside Management
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2009, Bryophytes, Negative (-ve) Indicator
2006, Bryophytes Negative (-ve) IndicatorT
ota
l A
bu
nd
an
ce
pe
r Q
ua
dra
t
2011, Bryophtes, Negative (-ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
R² = 0.0166
0
2
4
6
8
1 3 5 7 9 11 13 15
R² = 0.0905
0
1
2
3
4
5
6
7
8
16 18 20 22 24 26 28 30
R² = 0.258
0
1
2
3
4
5
6
7
8
1 3 5 7 9 11 13 15
R² = 0.0082
0
1
2
3
4
5
6
7
8
16 18 20 22 24 26 28 30
R² = 0.2173
0
1
2
3
4
5
6
7
8
1 3 5 7 9 11 13 15
R² = 0.139
0
1
2
3
4
5
6
7
8
16 18 20 22 24 26 28 30
Figure 18 Exe Plain - Bryophytes Negative Indicators, 2006, 2009 and 2011
A Glendinning FdSc Countryside Management
41
4.3.2 Exe Head
EV* 1998 2006 2008 2009 2011
Sphagnum fallax 9 1 2 1 2
Aulacomnium palustre 8 1
Sphagnum palustre 8 1 3 1 1 1
Sphagnum papillosum 8 1 1 1
Sphagnum cuspidatum 10 2 4 4
Sphagnum denticulatum 9 1 1 2 2
Rhytidiadelphus squarrosus 5 1 1 1
Hylocomium splendens 5 1
Pleurozium schreberi 5 1
Campylopus paradoxus 6 3 1 2 2
Dicranella heteromalla 5 1 1
Isopterygium elegans 6 1
+v
e m
ois
ture
in
dic
ato
rs-v
e m
ois
ture
in
dic
ato
rs
Table 10 Exe Head site bryophyte changes, 1998 – 2011
* EV – indicate Ellenberg Moisture Indicator value for species type
A Glendinning FdSc Countryside Management
42
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t2011, Bryophytes, Positive (+ve) Indicator
metres to the left ← of drainage channel → metres to the right
R² = 0.2501
-4
0
4
8
12
1 6 11 16
R² = 0.6742
-4
0
4
8
12
19 24 29 34
Figure 19 Exe Head - Bryophytes Positive Indicators, 2011
2011, Bryophytes, Negative (-ve) Indicator
metres to the left ← of drainage channel → metres to the right
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.0349
-1
0
1
2
3
4
1 6 11 16
R² = 0.2467
-1
0
1
2
3
4
19 24 29 34
Figure 20 Exe Head - Bryophytes Negative Indicators, 2011
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4.3.3 Blackpitts 1
EV* 1998 2006 2008 2009 2011
Sphagnum denticulatum 9 1 1
Sphagnum fallax 9 1 2 2 2 2
Sphagnum palustre 8 1 2 3 3 1
Sphagnum papillosum 8 1 1 3 1
Aulacomnium palustre 8 1 2 2 1
Sphagnum cuspidatum 10 1
Campylopus paradoxus 6 3 1 1
Dicranella heteromalla 5 1 1
Isopterygium elegans 6 1 2 2
Hylocomium splendens 5 1
Rhytidiadelphus squarrosus 5 1 1 1
+v
e m
ois
ture
in
dic
ato
rs-v
e m
ois
ture
in
dic
ato
rs
Table 11 Blackpitts 1 site bryophyte changes, 1998 – 2011
* EV – indicate Ellenberg Moisture Indicator value for species type
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2011, Bryophytes, Positive (+ve) Indicator
metres to the left ← of drainage channel → metres to the right
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0.4074-1
0
1
2
3
4
5
1 3 5 7 9 11 13 15
R² = 0.2685
-1
0
1
2
3
4
5
16 18 20 22 24 26 28 30
Figure 21 Blackpitts 1 - Bryophytes Positive Indicators, 2011
metres to the left ← of drainage channel → metres to the right
2011, Bryophytes, Negative (-ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
R² = 0
-1
0
1
2
3
4
1 3 5 7 9 11 13 15
R² = 0.2493
-1
0
1
2
3
4
16 18 20 22 24 26 28 30
Figure 22 Blackpitts 1 - Bryophytes Negative Indicators, 2011
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4.3.4 Squallacombe
EV* 2007 2009 2011
Sphagnum fallax 9 1 1 2
Aulacomnium palustre 8 2 1 2
Sphagnum palustre 8 3 1 1
Sphagnum papillosum 8 1 2 2
Sphagnum cuspidatum 10 1 3 2
Sphagnum denticulatum 9
Rhytidiadelphus squarrosus 5 2 2 1
Hylocomium splendens 5 1 1
Pleurozium schreberi 5 1 1
Campylopus paradoxus 6 1 1 1
Dicranella heteromalla 5
Isopterygium elegans 6 1
+v
e m
ois
ture
in
dic
ato
rs-v
e m
ois
ture
in
dic
ato
rs
Table 12 Squallacombe site bryophyte changes, 2007 – 2011
* EV – indicate Ellenberg Moisture Indicator value for species type
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metres to the right ← of drainage channel → metres to the left
2009, Bryophytes, Positive (+ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
2011, Bryophytes, Positive (+ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
tT
ota
l A
bu
nd
an
ce
pe
r Q
ua
dra
t2007, Bryophytes, Positive (+ve) Indicator
metres to the right ← of drainage channel → metres to the left
R² = 0.1276
0
2
4
6
8
10
12
14
1 6 11 16 21
R² = 0.0202
0
2
4
6
8
10
12
14
26 31 36 41 46
R² = 0.0565
0
2
4
6
8
10
12
14
1 6 11 16 21
R² = 0.003
0
2
4
6
8
10
12
14
26 31 36 41 46
R² = 0.0889
0
2
4
6
8
10
12
14
1 6 11 16 21
R² = 0.1601
0
2
4
6
8
10
12
14
26 31 36 41 46
Figure 23 Squallacombe - Bryophytes Positive Indicators, 2007, 2009 and 2011
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47
2009, Bryophytes, Negative (-ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t
metres to the right ← of drainage channel → metres to the left
2011, Bryophytes, Negative (-ve) Indicator
To
tal A
bu
nd
an
ce
pe
r Q
ua
dra
t2007, Bryophytes, Negative (-ve) Indicator
metres to the right ← of drainage channel → metres to the left
R² = 0.0848
-2
-1
0
1
2
3
4
5
6
1 6 11 16 21
R² = 0.2433
-2
-1
0
1
2
3
4
5
6
26 31 36 41 46
R² = 0.0003
-2
-1
0
1
2
3
4
5
6
1 6 11 16 21
R² = 0.0235
-2
-1
0
1
2
3
4
5
6
26 31 36 41 46
R² = 0.0368
-2
-1
0
1
2
3
4
5
6
1 6 11 16 21
R² = 0.3646
-2
-1
0
1
2
3
4
5
6
26 31 36 41 46
Figure 24 Squallacombe - Bryophytes Negative Indicators, 2007, 2009 and 2011
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4.4 Spearman’s Rank Correlation Coefficient
Using the Spearman’s Rank Correlation Coefficient, coefficients were calculated for ‘All
Species’ results, across the surveyed sites for specific years, the results are shown in
Table 13.
Left Hand Side Right Hand Side Left Hand Side Right Hand Side
2006/2011 0.283 -0.104 -0.371 0.272
2009/2011 0.435 -0.379 0.323 0.189
2007/2011 0.883 0.462 0.913 0.307
2009/2011 0.785 0.645 0.827 0.858
Exe Head 2006/2011 0.004 0.812 0.301 0.754
Blackpitts 1 2006/2011 0.816 0.671 0.792 0.255
Exe Plain
Squallacombe
Moisture Indicators
+ve -ve
Table 13 Spearman Rank Correlation Coefficients for ‘All Species’
results across the sites, for specific years
The results show that for several sets of results, e.g. Squallacombe 2007/2011 LHS both
+ve and –ve, there is positive correlation between the results of the two years. For
specific results, e.g. 2006/2011 Blackpitts –ve RHS, there is no correlation between the
years, implying change in abundance and/or distribution has occurred. The results also
show that for Exe Plain 2009/2011 +ve RHS, for example, that whilst the result is pointing
towards no correlation the change in sign reflects a change in distribution from the ditch
outwards or vice versa.
A Glendinning FdSc Countryside Management
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5 Discussion
Previous studies have identified that changes in vegetation community type and overall
biodiversity have occurred as a result of the mire restoration work conducted on Exmoor
(Rutty, 2007; Hand, 2009), but that changes can be both variable and difficult to assess.
Rutty (2007) drew a conclusion at Exe Head that moisture indicative plants had
increased towards the ditch but that the restoration work at Blackpitts 1 had little effect on
increasing the +ve moisture indictors and that the results in fact pointed to a continued
drying out of the land. Hand (2009) highlighted an overall lack in increase of Sphagnum
spp and that, perhaps, the assessment and analysis methods required refinement to
ensure that changes were in fact being monitored.
The sites chosen for this report were selected to allow not only a continuation of the
survey analyses from previous years, but also to explore, using a different presentation of
the data, how other analysis techniques could possibly identify or assist in the
identification of changes in vegetation type with time.
Using both the ‘All Species’ and ‘Bryophytes’ lists the data has been presented to show
the change in abundance of both positive and negative moisture indicators as surveying
was conducted incrementally away from each blocked drainage channel. Whilst some
results clearly show a change from previous year’s survey data, e.g. Exe Plain All
Species +ve RHS, others show little change, e.g. Squallacombe All Species –ve RHS.
Indeed, analysis of all previous site survey data even implies a regression of change in
2011 compared to that seen following restoration, again as in the case of Exe Plain.
The data from the selected sites was analysed using Spearman Rank Correlation
Coefficient, which was calculated for abundance moving away from the ditch, both left
and right, between two year’s survey results. Certainly more analysis is possible with this
data and for that collected across the whole Project sites, however the results to date do
suggest that the statistical data gathered and analysed does show that the changes and
trends described above are also identifiable through the review of the coefficients.
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What is clear overall however, is that although some sites have improved, if the evidence
were based solely on these results, the anticipated improvements have not materialised
across all sites. Only by looking more closely at the data, particularly for the NVC and
biodiversity results, can more positive changes be observed. For example, although
Squallacombe 2009 to 2011 would suggest little or no significant change in the
abundance of negative indicators, careful review of the NVC data suggest that the
dominance of key species, e.g. M. caerulea and Vaccinium myrtillus, has reduced. And
similarly, whilst the Exe Head positive indicators may not reflect, overall, a change in +ve
indicators, the increase in overall abundance of S. cuspidatum would suggest otherwise.
What is clear from the results presented is that no one analysis method can determine if
change has taken place, rather it is an holistic view of several.
Changes in vegetation type and abundance have been identified by this report at specific
locations on Exmoor. However, whilst other sites have recorded less obvious changes
or, in some cases, suggestions that previous improvements are now regressing, it is
important to reflect on the duration since restoration and that this is likely, at the moment,
to be a major contributor to cases of little observable change. Other researchers have
reflected that it may take from five to ten years to see significant changes (Campbell et
al, 2003; Gorham and Rochefort, 2003; Wilson et al 2010). Indeed, Gorham and
Rochefort (2003) reported in their assessment of restoration work conducted to date that,
in their opinion, it would take three to five years for a significant number of characteristic
bog species to become established and upwards of 10 years for a stable water table to
become ‘established’.
What is evident from the results presented here is that negative moisture indicating
species continue to dominate most sites, e.g. M. caerulea, R. squarrosus and P. erecta,
and that it is perhaps this continued dominance of species that is key to the timely
success of such restoration work (Rochefort and Lode, 2006; Armstrong et al, 2008;
Robroek et al 2009). Robroek et al (2009) argued that the establishment of a viable
abundance, although perhaps not suggesting dominance, is more crucial than water for a
specie’s performance and ultimately successful peatland restoration. The rate of
recovery will be as a result of the previous change, over many decades, in vegetation
and the associated effects on the soil’s structure and physiochemical environment
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51
(Rochefort and Lode, 2006). The length that the restoration process and the degree by
which vegetation is changing (or not) may be further supported by work conducted by
Bönsel and Sonneck (2011) whose studies in Northeast Germany have suggested that
although small changes occurred after one or two years, large changes in vegetation
species abundance occurred after five to ten years
Whilst there needs to a review of the respective positive and negative species indicator
lists that have been used here and previously to perhaps make the analysis more
reflective of actual change, what has been demonstrated is that change can be indicated
using both graphical and statistical analysis. Although as already mentioned, such
results need to be reviewed in wider context and using other indicators, e.g. NVC and
biodiversity indicators.
Whilst it is not possible to establish if limitations on identification of species due to, for
example, surveyor’s experience or seasonality, affected the data, it was clear from the
fieldwork that those surveys conducted later in the season suffered from weather and
light conditions as well as the obvious difficulties in identifying less than perfect
specimens. It has been suggested by the Exmoor Mires Project that the surveying in
2012 will be conducted earlier in the season and as close as possible to dates for
previous surveys conducted in 2010, thereby reducing any errors caused by seasonality
changes.
Recommendations from this report would be to not only review the positive and negative
indicator lists but a need to review all aspects of the data holistically to understand if
change has or is occurring. In terms of over-coming dominance and allowing other
species a foot-hold, a recommendation would be to review the grazing regimes on certain
sites to encourage removal of such spices, e.g. targeting specific areas with a
higher/greater density of cattle to help control and remove areas of M. caerluea.
However, such changes would need to be balanced with the increased likelihood of
damage to the site through, for example, excessive poaching.
Whilst suggested by the hypothesis that it may have been possible to demonstrate the
success of the current management techniques by monitoring changes in vegetation
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52
types and communities only, it is proposed that any future research work include
measurement of other abiotic characteristics, e.g. hydrology and chemical analysis, to
understand better other relevant abiotic characteristics. This could test a possible theory
that in some cases, e.g. 2011 Exe Plain +ve LHS, blocking further up-stream is creating
‘blooms’ of water that flow around the ditch and dams to lower sections, thereby creating
increases in positive abundance away from the ditch.
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6 Conclusion
Whilst it is perhaps too early to say with certainty that the work being conducted by the
Exmoor Mires Project to restore areas on Exmoor to pristine or near-pristine mire habitat
has been successful, the evidence provided in this report suggests that, reviewing the
data as a whole, moisture indicative species are increasing in abundance in and around
the old drainage channel systems. And although previously ‘encouraged’ species such
as M. caerluea are still dominant in many areas, it is clear that there are management
strategies in place to actively manage this dominance.
Whilst many see such areas as providing benefits to meet larger questions such as
increasing biodiversity, water quality and landscape, others are looking at the quantity
and ‘value’ of the carbon contained within the soils and to offset the effects of climate
change (Worral et al, 2003; Defra, 2008; Evans and Lindsay, 2010). It is perhaps this
last subject that may affect ultimately determine the success or otherwise, of the Exmoor
Mires Project. With global temperatures expected to rise by between 2 and 4 °C by the
end of the current century and associated changes in weather patterns likely to modify
distributions of rainfall (IPCC, 2007), the ability of the UK’s blanket bogs to survive into
the next century looks uncertain. At some point then, perhaps we need to think about
how the mire landscape will evolve and how such ecosystem services as are being
anticipated now, will be replaced in the future.
Acknowledgments I would like to thank Dr. David Smith, the Exmoor Mires Project Officer, for
allowing me access to all relevant Project information and data and for his continued support and
advice throughout my work. I would also thank other members of the Project team and those at
First Ecology for their help and assistance during the survey work, particularly in species
identification.
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54
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Appendix A Exmoor Mires Restoration Risk Assessment Form
SITE GATE LOCATION - (OS grid reference SS )
Mobile reception: Poor
Nearest telephone landline: Simonsbath
Nearest hospital: Minehead or Barnstaple
N.B. This risk assessment shall be kept with staff on site. All should be familiar with the risks, possible outcomes and agreed procedures.
Hazards Details and outcomes People at risk Risk Existing Controls and Actions Needed
Tracks and Terrain Outcomes
Wet peaty ground with pools, very tussocky and uneven in places Up-to 2m deep water courses sometimes concealed by vegetation Trips and slipping hazards may be obscured by vegetation Water bodies which can be crossed only by wading or jumping Trips and slips possibly into deep water. Risk of injury, inundation and drowning
Contractors staff Volunteers
medium Be aware of the risks and working conditions Wear appropriate footwear for wet, uneven slippery conditions with good grip,
waterproofing and ankle support. Do not be alone on site unless lone working arrangements have been made Do not jump deep water in order to cross features, find an alternative route Work safely when surveying pools and open water areas
Road traffic Outcomes
Small or restricted pull in area, access at Blackpitts off main road Injury or death resulting from road traffic accident
low be aware of the risks Wear high visibility jackets when walking on the road at all times
Animals Outcomes
Cattle graze moorland at both sites Ticks are widespread and may carry Lymes disease. Rutting deer stags may be dangerous Adders are present on moorlands Risk of Snake bites (poisoning and sickness) Disease or injury from ticks, snakes or animal attack.
low Be aware, avoid cattle and deer, wear suitable clothing and check themselves daily for ticks.
To avoid snake bites wear full cover boots and clothing. ‘Look before you sit’ should be exercised and ‘watching where you tread’
Hunting/ shooting Outcomes
ENPA does not control hunting or shooting on most of its land Large groups of horse riders travelling at speed Accidental injury caused by shooting game Injury or death caused by shooting or trampling
low Be aware of the risks,
Rivers Outcomes
Rivers and ditches which can become fast flowing in winter Crossing by wading or jumping Injury or death due to drowning Risk of infection leading to illness Working in water carries risk of infection of water borne disease (e.g. Wiels disease from Rats).
Low
Low
Be aware of the risks Do not enter or jump deep water in order to cross features, find an alternative
route Be aware of risks. Wear gloves. Wash hands before smoking or eating
Weather Outcomes
Weather can be very changeable, become misty or cold and wet quickly. Can be very hot in summer.
Exposure, hypothermia, sunburn
medium Be aware of the risks. Wear suitable clothing Do not be alone on site unless lone working arrangements have been made
Moorland Fires/ Heather swaling
All legal burning must take place between 1st October and 15th April but wildfires or deliberate burns may be a threat.
Risk of getting persons or machinery caught in fire
Contractors, staff volunteers
Low Project officer to check burning programme with ENPA Rangers, Surveying should be timetabled to avoid scheduled burns
All to be aware of risk of wildfires. The Moors should be vacated by any persons at first indication of a wildfire coming towards them
Site and Outline Work Risk Assessment
MONITORING Visits to mire restoration sites
Risk Assessment Undertaken by: David Smith
Signed _________________________ Date__ __ 2011
EMERGENCY PROCEDURE. In case of an emergency (Call 999 or 112):
There is/is not ambulance access to the gate
Area can/cannot be accessed by quadbike / Foot / Helicopter
Air Ambulance can/cannot land at grid references listed
Contact ENPA office at Exmoor House: 01398323665 or Rangers:
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Appendix B Example from a completed data set
Name: Exe Plain date: 14/09/2011 15/09/2011
Quadrats
Species latin Species common1 2 3 4 ……. ……. 27 28 29 30
Occurrence in
# of Quadrats
% of
Quadrats
Constancy
1-5
Overall Abundance
in Quadrats
Calluna vulgaris Ling 0 0 0 0 1 0 0 4 2 6.67 1 5
Cardamine pratensis Cuckoo Flower 0 0 0 0 0 0 0 0 9 30 2 18
Cerastium fontanum Common Mouse-ear 0 0 0 0 0 0 0 0 0 0 0 0
Cirsium palustre Marsh Thistle 0 1 0 1 0 0 0 0 14 46.67 3 30
Drosera rotundifolia Sundew 0 0 0 0 0 0 0 0 0 0 0 0
Epilobium palustre Marsh Willowherb 2 2 0 0 0 0 0 0 15 50 3 32
Erica tetralix Cross-leaved Heath 0 0 0 0 0 0 0 0 0 0 0 0
Galium palustre Marsh Bedstraw 4 3 2 4 0 0 0 0 18 60 3 51
Galium saxatile Heath Bedstraw 0 0 0 0 0 0 0 0 5 16.67 1 15
Montia fontana Blinks 0 0 0 0 0 0 0 0 0 0 0 0
Narthecium ossifragum Bog Asphodel 0 0 0 0 0 0 0 0 0 0 0 0
Pedicularis sylvatica Lousewort 0 0 0 0 0 0 0 0 0 0 0 0
Plantago lanceolata Ribwort Plantain 0 0 0 0 0 0 0 0 0 0 0 0
Polygala serpyllifolia Milkwort 0 0 0 0 2 2 2 3 12 40 2 35
Potentilla erecta Tormentil 3 3 0 0 4 4 3 4 19 63.33 4 53
Potamogeton sp. Pondweed 0 0 0 0 0 0 0 0 0 0 0 0
Prunella vulgaris Selfheal 0 0 0 0 0 0 0 0 0 0 0 0
Ranunculus acris Meadow Buttercup 0 0 0 0 0 0 0 0 7 23.33 2 17
Ranunculus batrachium Water-crowfoot 0 0 0 0 0 0 0 0 0 0 0 0
Ranunculus flammula Lesser Spearwort 0 0 0 0 0 0 0 0 11 36.67 2 17
Ranunculus repens Creeping Buttercup 3 4 4 4 0 0 0 0 20 66.67 4 67
Rumex acetosa Common Sorrel 2 2 0 0 0 0 0 0 17 56.67 3 49
Sculletaria minor Lesser Skullcap 0 0 0 0 0 0 0 0 0 0 0 0
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Appendix C Summarised NVC for all Exmoor Mire Sites
(Provided courtesy of D. Smith; Exmoor Mires Project, Project Manager)
Site Base line (NVC) Surveyed 1998 (and species number)
Base line (NVC) Surveyed 2006/2007 (and species number)
Monitoring or base line survey 2008 (and species number)
Monitoring or base line survey 2009 (and species number)
Monitoring or base line survey 2010 (and species number)
Species Change 2006- present
Community change 2006- present
1.Exehead Line E
M25: Molinia caerulea - Potentilla erecta bog (34)
M25 (33)
Restoration spring 2007 M25 (37)
M3 Eriphorum angustifolium bog pool, and M17 (37)
+4 M25 to M17 (+ve )
2. Blackpitts Line G
M25: Molinia caerulea - Potentilla erecta bog (32)
M25 (30)
Restoration spring 2007 M25 (38)
M25 (39)
+9 No change
3. Blackpitts 2 M25 Molinia caerulea – Potentilla erecta mire or M19 Calluna vulgaris – Eriophorum vaginatum blanket mire (poor fit). (33)
Restoration spring 2007 M25 or M19 (45)
Elements of M25, M17, M3, M19, M20 (29)
-4 M25 to mixed (+ve)
4.Blackpitts 50yr old cuttings (control site)
M17 Trichophorum cespitosum – Eriophorum vaginatum Blanket mire + M2 Sphagnum cuspidatum/fallax pool (30)
na Na Na
6. Exe Plain M25:Molinia caerulea - Potentilla erecta bog or M23 Juncus effuses/acutiflorus – Gallium palustre. Rush pasture (36)
Restoration spring 2007 M25 or M23 (55)
M25 or M23 (58)
+22 M25 to M23 (+ve)
7. Upper Exe Valley (at lower Blackpitts)
M2 Sphagnum cuspidatum/fallax bog pool community (in ditch) and M6 Carex echinata – Sphagnum fallax mire (43)
Restoration Nov 08 M2 Sphagnum cuspidatum/fallax bog pool community (in ditch) and M6 Carex echinata – Sphagnum fallax mire (40)
-3 No change
8. Roostitichen M23 Juncus effusus/acutiflorus –
Spring 2007 restoration M15
M17 (68) +18 M23 to M17 (+ve)
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Site Base line (NVC) Surveyed 1998 (and species number)
Base line (NVC) Surveyed 2006/2007 (and species number)
Monitoring or base line survey 2008 (and species number)
Monitoring or base line survey 2009 (and species number)
Monitoring or base line survey 2010 (and species number)
Species Change 2006- present
Community change 2006- present
Gallium palustre. Rush pasture (50)
(62)
9. Broadmead M25:Molinia caerulea - Potentilla erecta bog Erica tetralix sub community (32)
Spring 2007 restoration M25 (46)
M25c (36) -10 No change
10. Squallacombe Restoration site
M25:Molinia caerulea - Potentilla erecta bog Erica tetralix sub community or M15 Trichophorum cespitosum – Erica tetralix Wet heath (37)
Restored Nov 2007 M3/ M17 (38) +1 M25 to M3/M17 (+ve)
11. Squallacombe Intact bog (control site)
M18 Erica tetralix – Sphagnum papillosum Blanket mire (29)
Na
12. Comerslade M17 Trichophorum cespitosum – Eriophorum vaginatum Blanket mire (42)
Restored 2010
13. Hangley Cleave east
M25a Molinia caerulea – Potentilla erecta mire (22)
Restored Spring 2008 M25a (27) +5 No change
14. Hangley Cleave west
M25a Molinia caerulea – Potentilla erecta mire or M15 Trichophorum cespitosum – Erica tetralix Wet heath (40)
Restored Spring 2008 M17 (47) +7 M25 to M17 (+ve)
15. Long Holcombe west
M25b Molinia caerulea – Potentilla erecta mire (17)
Restoration March 09
16. Long Holcombe east
M25b Molinia caerulea – Potentilla erecta mire (12)
Restoration March 09
17. Vernie’s Allotment
Possible M17 Trichophorum
Restoration Nov 08 M17 (37) -1 No change
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Site Base line (NVC) Surveyed 1998 (and species number)
Base line (NVC) Surveyed 2006/2007 (and species number)
Monitoring or base line survey 2008 (and species number)
Monitoring or base line survey 2009 (and species number)
Monitoring or base line survey 2010 (and species number)
Species Change 2006- present
Community change 2006- present
cespitosum – Eriophorum vaginatum Blanket mire (38)
18. North Twitchen
M15 Trichophorum cespitosum – Erica tetralix Wet heath (44)
Restoration March 09
19. Aldermans Barrow allotment
M25 Molinia caerulea – Potentilla erecta mire (37)
Restoration Nov 08 M25 (48) +11 No change
20. Roostichen Phase 2
M15 Trichophorum cespitosum – Erica tetralix Wet heath or M25 Molinia caerulea – Potentilla erecta mire (48) Restoration Nov 08
Restoration Nov 2008 M15 (42) -6 No change
21. Ricksy Ball (Aclands) damaged site
M25 (13)
22. Homer Common
M25a (47)