Laois County Council

RECEIVING WATER IMPACT ASSESSMENT

Ballina ki II WwTP

Draft: lathJune 2009 For inspection purposes only. Consent of copyright owner required for any other use.

Prepared on behalf of:

WATER SERVICES LAOIS COUNTY COUNCIL County Hall Co. Laois

Environmental Consultants Tait Business Centre, Dominic Street, Limerick City, Ireland. t. +353 61 419477, f. +353 61 414315 e. [email protected] w. www.ecofact.ie

EPA Export 26-07-2013:14:13:57 Receiving Water Impact Assessment: WwTP-June 2009

EXECUTIVE SUMMARY

This is a receiving water impact assessment report for the Ballinakill Waste water Treatment Plant (WwTP). It has been prepared under Section F of the Environmental Protection Agencies Waste Water Discharge Licensing Application Guidance Note. This report was prepared during May 2009 on behalf of Laois County Council by ECOFACT Environmental Consultants Ltd.

The current study was based on information compiled during a desk study and a field assessment. Information compiled during the desk study included water quality monitoring information supplied by Laois County Council, the Environmental Protection Agency and further information on areas designated for nature conservation obtained from the National Parks and Wildlife Service (NPWS). The field study consisted of a walkover of the existing WwTP and receiving watercourse adjacent to the discharge, along with ecological and biological water quality appraisals at upstream (reference) and downstream (receptor) sites.

The Ballinakill Stream, a second order drained stream is the direct receiving water for the Ballinakill WwTP. The Ballinakill Stream is of low ecological and fisheries value. Approximately 3 km downstream of the discharge from the Ballinakill WwTP outfall, the Ballinakill Stream joins the Owenbeg River making this watercourse the indirect receiving water from the Ballinakill WwTP. Furthermore the Owenbeg River is designated within the River Barrow and Special Area of Conservation (SAC) and is therefore of greater ecological sensitivity than the Ballinakill Stream.

Water quality in the Ballinakill Stream was found to be compromised both upstream and downstream of the Ballinakill WwTP, with a clear deterioration in water quality downstream of the discharge. This evaluation was based on the field biological assessment carried out by Ecofact for the current assessment and also on chemical water quality monitoring data supplied by Laois County Council. From this data it was found that the Ballinakill Stream was of ‘good status’ Q4 upstream, deteriorating to Q3-4 downstream. Chemical water quality monitoring data indicated significant elevations in Ammonia, Orthophosphate, BOD and depleted Dissolved Oxygen downstream of the WwTP discharge.

Although the observed discharge concentrations in the effluent were found to be below the design standards (for Suspended Solids, Orthophosphate and BOD) the flow in the Ballinakill Stream provides little dilution of the discharged effluent. It was found that the 95%ile flow of For inspection purposes only. the receiving water is 3 litres/s,Consent while of copyright the dry owner weather required forflow any fromother use. the plant is 2.6 litres/s.

A waste assimilation capacity assessment (WAC), based on median upstream parameter concentrations showed that the Ballinakill Stream has limited waste assimilation capacity, due to high concentrations of background parameters during 95%ile flows. From the WAC the WwTP is assessed as having a slight to imperceptible impact on the receiving water during median flows, where the WFD ‘good status’ requirements are met for all parameters. It is important to note, however, that the Phosphorus Regulations requirements are not met for the Orthophosphate loadings to the Ballinakill Stream under 95%ile or median flows. The ongoing operation of the Ballinakill WwTP is therefore considered to have a slight impact on the water quality and ecological interests within the Ballinakill Stream receiving water.

The Owenbeg River is contained within the River Barrow and River Nore Special Area of Conservation (SAC). Based on EPA chemical and biological water quality monitoring data at Castlemarket Bridge (upstream) and Attanagh Bridge (downstream) of the Ballinakill Stream confluence it was found that there was no discernible change in water quality between the two stations. Biological water quality was found to be stable at Q4 i.e. ‘good ecological status’. The current assessment therefore concludes that the overall impact to the Owenbeg River receiving water is imperceptible.

It is‘noted, however, that the downstream EPA monitoring station on, the Owenbeg River receiving water is located ca. 3km from the Ballinakill Stream confluence. There is therefore

~ the possibility of localised impacts to this watercourse within the direct vicinity of the Ballinakill confluence.

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The current model assessed the WAC for the Ballinakill Stream, directly downstream of the WwTP discharge. The dilution capacity of the Ballinkill Stream at the confluence with the Owenbeg River is currently unknown. The availability of this data, coupled with monitoring data directly upstream and downstream of the confluence of these watercourses would provide a more accurate picture of the operational impact of the WwTP on the Owenbeg River, as a receiving water, and the associated impact on the River Barrow and River Nore SAC. This would further inform future assessments on the impact of the WwTP on freshwater pearl mussels in the River Nore downstream of the Owenbeg River, as well as impacts to salmonids and white-clawed crayfish populations in the Owenbeg River.

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Receiving Water Impact Assessment: Ballinakill WwTP-June 2009

TABLE OF CONTENTS

1. INTRODUCTION ...... 6 1.1 BACKGROUND...... 6 1.2 LEGISLATION...... 6 1 .3 METHODOLOGY...... 7 1.3.1 Desktop Review ...... 7 1.3.2 Field Survey Work ...... 7 1.3.3 Assessment Methodology ...... 8 1.4 CONSULTATION...... 9 2 . SCHEME DESCRIPTION ...... lO 2.1 INTRODUCTION...... IO 2.2 SEWERAGESCHEME DESIGN ...... 11 2.2.1 Primary Treatment...... 11 2.2.2 Secondary Treatment...... 12 2.2.4 Sludge Treatment and Disposal ...... 12 2.2.5 Operation and Maintenance ...... 12 2.3 DISCHARGESTANDARDS ...... 12 2.4 FLOWS...... 13 2.5 MONITORING...... 13 3 . RECEIVING ENVIRONMENT ...... 14 3.1 CATCHMENTDESCRIPTION ...... 14 3.2 . WATERQUALI TV ...... 14 3.2.1 Existing information ...... 14 3.2.2 Results of the Ecofact on-site assessment (May 2009) ...... 17 3.2.3 Dangerous substances...... 18 3.2.4 Assimilation capacity ...... 19 3.3 SEDIMENT QUALITY ...... 21 3.4 AREASDESIGNATED FOR NATURE CONSERVATION ...... 21 3.5 PROTECTEDAQUATIC FLORA AND FAL~NA...... 21 3.5.1 White-clawed crayfish ...... 22 3.5.'2 Lampreys ...... 22 3.5.3 Shad ...... 22 For inspection purposes only. '3,5.4 Atlantic salmon ...... Consent of copyright owner required for any other use. 22 3.5.5 Eurasian Otter ...... 23 3.5.6 Freshwater Pearl-mussel ...... 23 3.6 . RECREATIONALAND COMMERCIAL FISHERIES ...... 24 3.7 WATERABSTRACTIONS ...... 24 3.8 DESIGNATEDRECREATIONAL AND BATHING WATERS...... 24 3.9 NUTRIENTSENSITIVE AREAS ...... 24 4 . IMPACT ASSESSMENT ...... 25 4.1 INTRODUCTION...... 25 4.2 IMPACT ON WATER QUALITY ...... 26 4.2.1 Chemical water quality ...... '...... 26 4.2.2 Biological water quality ...... 26 4.2.4 Assimilation capacity ...... 27 4.3 IMPACT ON AREAS DESIGNATED FOR NATURE CONSERVATION...... 28 4.4 IMPACT ON PROTECTED FLORA AND FAUNA ...... 29 4.5 IMPACT ON FISHERIES...... 30 4.6 IMPACT ON WATER ABSTRACTIONS ...... 30 4.7 IMPACT ON RECREATIONAL AREAS ...... 30 4.8 IMPACT ON NUTRIENT SENSITIVE AREAS ...... 30 5 . RECOMMENDATIONS...... 31 REFERENCES...... 32

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PLATES ...... APPENDIX 1 BIOTIC INDICES ...... 38 APPENDIX 2 NPWS DESIGNATED SITE DESCRIPTION ...... 41 APPENDIX 3 LAOIS CO. CO. MONITORING,DATA (BALLINAKILL MP)...... 46 APPENDIX 4 BIOLOGICAL WATER QUALITY ASSESSMENT (2009) ...... 47

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I. INTRODUCTION 1.I Background

This report provides a Receiving Water Impact Assessment for the Waste Water Treatment Plant (WwTP) serving Ballinakill Village, CO Laois. The Ballinakill WwTP discharges into a small stream referred to as the Ballinakill Stream in this report. The Ballinakill Stream is a tributary of the Owenbeg River which flows into the River Nore. The Nore main channel is a designated salmonid water under the European Communities (Quality of Salmonid Waters) Regulations of 1988 (S.I. No. 293, 1988), implementing the Freshwater Fish Directive (78/659/EEC). The Owenbeg River and the River Nore is also protected as a component of the River Nore and River Barrow candidate Special Area of Conservation (SAC) under the Habitats Directive (92/43/EEC).

The purpose of the report is to assess whether the existing waste water discharge(s) from the plant in Ballinakill are having a significant adverse impact on the receiving waters, or any Natura 2000 Site. The primary receiving water is the Ballinakill Stream and a detailed assessment of this watercourse was carried out. Information for this stream was supplied by Laois County Council and included chemical water quality monitoring results and flow data. This report was prepared during the period May to June 2009 by Ecofact Environmental Consultants Ltd. on behalf of the Water Services Section of Laois County Council.

1.2 Legislation

The current report was prepared with consideration to the following water quality legislation:-

* Waste Water Discharge (Authorisation) Regulations 2007 (SI No. 684 of 2007); Urban Wastewater Treatment Regulations, 2001 (S.I. No. 254 of 2001); European Communities (Water Policy) Regulations, 2003 (SI No. 722) implementing the Water Framework Directive (WFD) 2000/60/EC. Water Policy Regulations (S.I. No. 722 of 2003) and Water Policy Regulations (Amendment) (S.I. No. 413 of 2005) implementing the EU Water Framework Directive (2000/60/EC); Local Government (Water Pollution) Acts, 1977 (Water Quality Standards for Phosphorus) Regulations, 1998. (S.I. No. 258 of 1998), and Local Government For inspection purposes only. (Water Pollution) (Amendment)Consent of copyright Act, owner 1990. required (Act for No.any other 21 use. of 1990); European Communities (Quality of Salmonid Waters) Regulations, 1988 (S.I. No. 293 of 1988) implementing Freshwater Fish Directive (78/659/EEC); Quality of Bathing Waters Regulations, 1992, and Quality of Bathing Waters Regulations (Amendment), 1996. (implementing Bathing Water Directive, 76/1GO/EEC); European Communities Quality of Surface Water Intended for the Abstraction of Drinking Water Regulations, 1989. (Implementing the Surface Water Directive, 75/440/EEC); 0 Water Quality (Dangerous Substances) Regulations, 2001 .(Implementing the Dangerous Substances Directive, 76/464/EEC); e Protection of Groundwater Regulations, 1999. (S.I. No. 41 of 1999); e Water Quality (Dangerous Substances) Regulations, 2001 (S.I. No. 12 of 2001).

In addition, cognisance was also taken of the following legislation relating to nature conservation and fisheries:-

* The European Communities (Natural Habitats) (Amendment) Regulations 2005 (S.I. No. 378/2005), The European Communities (Natural Habitats) (Amendment) Regulations 1998 (S.I. No. 233/1998), and the European Community (Natural Habitats) Regulations 1997 (S.I. No. 94/1997) (implementing Council Directives 92/43/EEC and 97/62/EC on the conservation of natural habitats and of wild fauna and flora);

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0 Wildlife Act, 1976 (S.I. No. 39 of 1976) and the Wildlife (Amendment) Act, 2000 (S.I. No. 71 of 2001); Fisheries (Amendment) Act, 1997, (S.I. No. 23 of 1997) and Fisheries (Consolidation) Act, 1959 (S.I. No. 14 of 1959); 0 The EU Birds Directive (79/409/EEC).

1.3 Methodology

This report has been prepared under the Waste Water Discharge (Authorisation) Regulations, 2007, using Section F of the Environmental Protection Agencies Waste Water Discharge Licensing Application Guidance Note (EPA, 2008). The current study involved a desk study and a field assessment. The literature review and field sampling programme was designed primarily as a descriptive study to provide information on the existing environmental status of the surface water area under investigation. An integrated assessment approach was employed. This approach merges biological (effects) and physical/chemical (causes) using a combination of field and desk study evaluations. The Ballinakill Stream, along with the Owenbeg River, receives water from the Ballinakill WwTP and both watercourses were assessed. The Ballinakill Stream was assessed in more detail, as Laois County Council provided monitoring data for this stream, identified as the receiving water. Flow and chemical water quality monitoring data for the Owenbeg River was not supplied by Laois County Council, and an assessment of this watercourse was based on EPA chemical and biological water quality monitoring data.

7.3.7 Desktop Review

A desktop review was carried out to identify features of surface water importance within the study area and surrounding region. A review of areas designated (or being considered for designation) for nature conservation was carried out by consulting the National Parks and Wildlife Service (NPWS). These included Special Areas of Conservation, Special Protection Areas for birds (both internationally important) and proposed Natural Heritage Areas (of national importance). The locations of any designated salmonid waters, recreational and bathing waters and nutrient sensitive areas within the study area were identified though consultation with the Environmental Protection Agency (EPA). Likewise the presence of any important recreational or commercial fisheries was identified through consultation with the Southern Regional Fisheries Board (SRFB). For inspection purposes only. Consent of copyright owner required for any other use. A range of additional sources of information including scientific reports produced by, and information on the websites of the EPA, NPWS, Laois County Council and other agencies were also reviewed. A full bibliography of information sources reviewed is given in the references section. Ordnance Survey Maps and OS aerial photographs were also reviewed during the desk assessment.

7.3.2 Field Survey Work

The field survey comprised a systematic walk over of the WwTP site, outfall location and Ballinakill Stream adjacent to the WwTP discharge. A kick sampling assessment of benthic macro-invertebrates was undertaken a point located upstream (reference) and downstream (receptor) of the primary discharge to supplement information collected during the desk study. The exact location and description of these sites is provided in Table 1.

Table 1 Location of the May 2009 survey sites sampled by Ecofact. Reference Site (uls Ballinakill WwTP) Receptor Site (dls BallinakillWwTP) Location 70m upstream of the WwTP outfall Approx. 200117 downstream of the Ballinakill stream WwTP outfall stream __-______--______------. NOS Grid Ref. S4566480946 ~45665~10734 The kick-sampling assessment followed the EPA standard methodology (Toner et al., 2005). This procedure involved the use of a ‘D’ shaped hand net (mesh size 0.5 mm; 350 mm diameter) which was submerged on the river bed with its mouth directed upstream. The substrate upstream of the net was then kicked for one minute in order to dislodge

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invertebrates, which were subsequently caught in the net. This procedure was undertaken at three points across the watercourse, where depth/access allowed. Stone washings and vegetation sweeps were also undertaken to ensure a representative sample of the fauna present at each site was collected. All samples of invertebrates were combined for each site and live sorted on the river bank for 20 minutes. Specimens retained were preserved in ethanol for later identification. Identification was undertaken in the laboratory using high-power and low-power binocular microscopes. Specimens were identified using the standard keys which are listed in the bibliography section. The abundances of organisms present was assessed as follows: Present (1 or 2 individuals), Scarce/Few (75%)

The Quality Rating (Q) System (Toner et al., 2005) was used to obtain a water quality rating for each site. The use of this particular biotic index allows for comparison with data published by the EPA. This method categorizes invertebrates into one of five groups, depending on their sensitivity to pollution. The higher the biological diversity and the greater the abundance of invertebrate species sensitive to organic pollution, the higher the water quality is assumed to be, and the higher the ‘Q value’ assigned to that sampling station. The revised BMWP scheme (Walley and Hawkes, 1997) is another biotic index of water quality that was used in the current appraisal. In this system, each family recorded in the sample is assigned a habitat specific score. This score depends on the pollution sensitivity of the invertebrate family together with the characteristics of the site where the invertebrates were found. A higher BMWP score is considered to reflect a better water quality and a score over 100 is indicative of very good water quality.

1.3.3 Assessment Methodology

Impact significance is a combined function of the value of the affected feature (its water quality, fisheries or aquatic ecology importance), the type of impact and the magnitude of the impact. It is therefore necessary to identify the value of surface water features within the study area in order to evaluate the significance and magnitude of possible impacts. To achieve this, the results of the desk and field assessment were evaluated to determine the significance of identified features located in the study area on an importance scale, ranging from international-national-county-local.The criteria used are shown in Table 2.

The means of assessing impact significance For inspection purposes was only. based on the Institute of Ecology and Environmental Management’sConsent “Guidelines of copyright ownerfor requiredEcological for any other Impact use. Assessment in the United Kingdom” (IEEM, 2006) and the EPA’s “Waste Water Discharge Licensing Application Guidance Note” (EPA, 2008). The significance of impacts was assessed on a combined basis of the value of the feature being affected and the magnitude of the impact. According to the EPA (2008), a discharge from a WwTP would be considered to have a significant adverse effect on the receiving waters if it were to:-

0 Cause a deterioration in the chemical status or ecological status (or ecological potential as the case may be) in the receiving body of surface water; 0 Cause a deterioration in the chemical status in the receiving body of groundwater; 0 Cause the input into groundwater of hazardous substances, except where it is established that the input concerned is in a quantity and concentration so small as to obviate any present or future danger of deterioration in the quality of the receiving groundwater; 0 Cause deterioration or result in significant and sustained upward trends in the concentrations of pollutants in groundwater in the case of pollutants that are not

hazardous, \ 0 Permanently exclude or compromise the achievement of the objectives established for protected species and natural habitats in the case of European sites where the maintenance or improvement of the status of water is an important factor in their protection or which is inconsistent with the achievement of environmental quality standards established under national Regulations in relation to designated bathing waters, designated shellfish waters, areas designated for the protection of freshwater fish and areas designated

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I.4 Consultation

Preparation of this report included consultation with the following agencies and state bodies:-

Laois County Council (Laois Co. Co.); National Parks and Wildlife Service (NPWS); Environmental Protection Agency (EPA); Southern Regional Fisheries Board (SRFB); South Eastern River Basin District Office (SERBDO); Department of Communications, Marine and Natural Resources (DCMNR); Botanical Society of the British Isles (BSBI); Geological Society of Ireland (GSI).

Table 2 Criteria used in assessing the importance of surface water features (taken from NRA 2004) Rating Qualifying Criteria A Internationally Important Sites designated (or qualifying for designation) as SAC* or SPA* under the EU Habitats or Birds Directives. Undesignated sites containing good examples of Annex I Driorlty habitats under the EU Habitats Directive. Major salmon river fisheries ______-Maior______------~------~-~------~-~------~------~---. salmonid lake fisheries. B Nationally Important Sites or waters designated or proposed as an NHA* or statutory Nature Reserves. Undesignated sites containing good examples of Annex I habitats (under EU Habitats Directive). Undesignated sites containing sianificant numbers of resident or regularly occurring populations of Annex II species under the EU habitats Directive or Annex I species under the EU Birds Directive or species protected under the Wildlife (Amendment) Act 2000. Major trout river fisheries. Water bodies with major amenity value. ---______-____-__----Commercially important coarse fisheries. C High Value, Locally Important Sites containing semi-natural habitat types with high biodiversity in a local context and a high degree of naturalness, or significant populations of locally rare species. Small water bodies with known salmonid populations or with good potential salmonid habitat. Sites containing =resident or regularly occurring populations of Annex II species under the EU habitats Directive or Annex I species under the EU Birds Directive. _--_-______Large______-_--_-_-______------. water bodies with some coarse fisheries. D Moderate Value, Locally Important Sites containing some semi-natural habitat or locally important for wildlife. Small water bodies with some coarse For inspection fisheries purposes value only. or some potential salmonid habitat. ------Any ...... water body with unpollutedConsent of water copyright (Q-value owner required 4-5). ----_------_-_--_-_------. for any other use. E Low Value, Locally Important Artificial of highly modified habitats with low species diversity and low wildlife value. Water bodies with no current fisheries value and no significant potential fisheries value.

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2. SCHEME DESCRIPTION

2.1 Introduction

The Ballinakill WwTP is a twin lane FM Systems steel package plant. The site originally had a septic tank system with a large percolation area (631Om2); the septic tank is currently used to provide treatment to storm water which bypasses the package plant. Treated effluent from the package plant discharges into a long effluent channel (originally the feeder channel for the , percolation system) and then a land drain, followed by the Ballinakill Stream, eventually ’ ending up in the Owenbeg River. The plant consists of an inlet flume, a package secondary treatment plant, a septic tank and a sludge drying pit. The package plant is designed to produce an effluent quality of 20mg/l BOD and 30mg/l TSS (Nicholas 0’ Dwyer, 2007). It was deduced in the Nicholas 0’ Dwyer (2007) report that the existing sewerage network in . Ballinakill was in excellent structural condition.

Under the Water Framework Directive (2000), each River Basin Management Plan must incorporate management measures to achieve ‘good ecological status’ by 2015. These measures include required actions to be taken by Local Authorities, as highlighted in the Draft Nore Sub-Basin Management Plan (2009). Urban Waste water Treatment Regulations: 0 Provide collection systems and treatments plants to meet the requirements in the Regulations. Meet more stringent requirements with respect to quality of receiving waters as specified in other Directives. Design, construct, operate and maintain treatment plants to ensure sufficient performance, taking seasonal variations of load into account. Choose discharge points so as to minimise impact on the environment. Monitor effluent discharges. Take all steps necessary to ensure compliance with the water quality objectives established in river basin management plans. Ensure that sewage sludge can be disposed of safely.

Water Services Act: 0 Plan and supervise provision of wastewater services under the Water Services Investment Programme. Supervise and monitor the performance of water services authorities. Prepare and implement Water Services Strategic Plans to support sustainable provision of wastewater services. For inspection purposes only. Consent of copyright owner required for any other use. Point source discharges: 0 Upgrade plant to increase capacity where necessary. 0 Optimise treatment plant performance by the implementation of a performance management system Upgrade plant to provide nutrient removal treatment where necessary.

Additional Measures - Point and Diffuse Sources: Wastewater Limit or cease the direct importation of polluting matter (e.g. liquid wastes, landfill leachate, sludges). Investigate the extent of use and impact of under-sink food waste disintegrators and take appropriate actions. Investigate fats/oils/grease influent concentrations and take actions to reduce FOG entering the collection system. Impose development controls where there is, or is likely to be in the future, insufficient capacity at treatment plants. Initiate investigations into characteristics of treated wastewater for parameters not presently required to be monitored under the urban wastewater treatment directive. Initiate research to verify risk assessment results and determine the impact of the discharge. Use decision making tools in point source discharge management.

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0 Where necessary to achieve water quality objectives install secondary treatment at smaller plants where this level of treatment would not otherwise be required under the urban wastewater treatment regulations. Apply a higher standard of treatment (stricter emission controls) where necessary. 0 Upgrade the plant to remove specific substances known to impact on water quality status 0 Install ultra-violet or similar type treatment. Relocate the point of discharge.

2.2 Sewerage Scheme Design '\ The village of Ballinakill is served by a combined drainage network consisting of approximately 3,318 linear metres of gravity pipelines. The network is primarily made up of 150 and 225 mm diameter concrete or PVC pipelines. The system gravitates flow to the wastewater treatment plant located approximately 1 km to the west of the village centre, see Figure 1. The village is also served by two surface water drainage systems that discharge to local ditches and streams. The surface water systems consist of approximately 659 linear meters of gravity pipelines. The surface water network is primarily made up of 300 and 450 mm diameter pipelines. It was determined by Precision Industrial Services Ltd. surveyors that an overflow exists between the foul / combined system and a local water course on Bride Street in Ballinakill (Nicholas 0' Dwyer, 2007).

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2.2. I Primary Treatment

The influent passes through a storm overflow chamber prior to reaching the influent flume. The flume is not currently instrumented, and flows are not recorded on site. Under storm conditions, excess flows are diverted to the septic tank, bypassing the secondary treatment

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EPA Export 26-07-2013:14:13:57 Receiving Water Impact Assessment: Ballinakill WwTP-June 2009 ...... system. The level of the storm weir is relatively low, thus flows in excess of dry weather flow will typically pass to the septic tank treatment (Nicholas 0’ Dwyer, 2007).

2.2.2 Secondary Treatment

The secondary treatment system consists of a combined aerationlclarification unit, split into two compartments. The particular model is known as the FS30 from FM Systems Ltd. The tank is 3.05m deep. Aeration is via surface aerators located at the inlet end of the tank. There are no other moving parts in the system, as the geometry of the tank, in addition to the flow pattern generated by the surface aerators, causes sludge from the clarifier section to be returned to the aeration compartment. Surface scum from the clarifier is also returned to the aeration compartment through the momentum energy created by the surface aerators.

The surface aerators operate on a on a 2 hour on / 2 hour off cycle. There is no inlet screening and as a result, rags pass through the system causing operational difficulties, and find their way to the receiving water (Nicholas 0’ Dwyer, 2007).

2.2.4 Sludge Treatment and Disposal - The sludge drying pit is an open earth pit, without drainage. The package plant is de-sludged every three weeks, when waste sludge is taken from the package plant and discharged to the sludge drying pit. The pit is emptied periodically by a specialist contractor.

2.2.5 Operation and Maintenance

There is one caretaker involved in routine maintenance of the WwTP. His responsibilities are split between the collection network and the WwTP. The majority of his duties include maintenance of the site in order to keep the surface aeration in operation, general housekeeping such as removal of screenings from the inlet flume, the package plant inlet and outlet weirs, site maintenance and supervision of liquid sludge transfer to the sludge drying pit (Nicholas 0’ Dwyer, 2007).

2.3 Discharge Standards

The requirements of Urban Wastewater Treatment Directive 91/271/EEC for treatment plants serving more than 2000 population equivalent For inspection purposes are: only. Consent of copyright owner required for any other use.

Biochemical Oxygen Demand (BOD5) 25 mg/l O2 Chemical Oxygen Demand 125 mg/l O2 Suspended Solids (p.e. >IO 000) 35 mg/l Suspended Solids (p.e. 2000 - 10 000) 60 mg/l

The following additional requirements apply for discharges to areas that are deemed to be sensitive:

Total Phosphorus (1 0 000 - 100 000 p.e.) 2 mg/l Total Phosphorus (over 100 000 p.e.) 1 mg/l Total Nitrogen (IO 000 - 100 000 p.e.) 15 mg/l Total Nitrogen (over 100 000 p.e.) 10 mg/l

At the Ballynakill WwTP, the discharge design standard for Biochemical Oxygen Demand (BOD) is 25 mg/L, Suspended Solids (SS) is 35 mg/L and Ortho-phosphate is 2 mg/L (standards provided by Laois County Council). A summary of the effluent monitoring data from Laois County Council at the outlet for Ballinakill WwTP is presented in Table 3.

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Table 3 Water quality results for the effluent at the Ballinakill WwTP during the period January 2006 to April 2009

2.4 Flows

The 95%ile flow in the Ballinakill Stream at the discharge point was given as 0.003 m3/s (Source: Laois County Council, based on modeled catchment data from Hydrometric Station 15037). This 95%ile flow is equal to 3 L/s. The median flow in the Ballinakill Stream is 0.13 m3/s or 130 L/s. There was no flow data given for the Owenbeg River and the receiving water assessment for the current report was based on data for the Ballinakill Stream. Flows from the plant to the Ballinakill Stream are given in Table 4.

2.5 Monitoring

Monitoring of the water quality of the outfall from the Ballinakill WwTP is undertaken by Laois County Council on an approximate monthly basis. Water quality is also monitored in the receiving water (Ballinakill Stream) upstream and downstream of the primary discharge. The parameters measured in the water samples are; Ammonia, Biological Oxygen Demand (BOD), Chemical Oxygen Demand (COD), Conductivity, Nitrates, Ortho-phosphate, and pH and Suspended Solids.

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3. RECEIVING ENVIRONMENT

3.1 Catchment Description

The Ballinakill WwTP discharges into a 2"dorder stream to the west of Ballinakill. This stream is referred to as the Ballinakill Stream in this report. The Ballinakill Stream is a tributary of the Owenbeg River (EPA Code 15/0/01) which flows into the River Nore (EPA 15/N/OI).

The Ballinakill Stream rises in the townland of Ballymaddock just north of the R430 - Swan (approximately 4 km north of Ballinakill). Approximately 3 km south of its source the Ballinakill Stream is joined by another 1'' order stream. It continues to flow south as a Is'order stream for a distance of approximately 3 km until it is met by another lstorder stream. It continues to flow south for approximately 5 km to join the Owenbeg River approximately 3 km southwest of Ballinakill. The Ballinakill Stream receives treated waste water from the Ballinakill WwTP approximately 2.6 km upstream of its confluence with the Owenbeg River. The Ballinakill Stream drains lands comprising mainly of Grey Brown Podzolics / Basic Brown Earths (BminDW) and Surface Water Gleys / Basic Ground Water Gleys (BminPD) derived from mainly calcareous parent materials.

The Owenbeg River rises in the southern slopes of Fossy Hill, Co. Laois, approximately 11 km northeast of Ballinakill. From its source to the River Nore, the Owenbeg River is approximately I 27 km long and generally flows in a south westerly direction. Approximately 9 km from source, it is a third order river, having been met by streams draining the Mountain. At this point it is crossed by the R430 regional road. The Ironmills River joins the Owenbeg River approximately 1.5 km east of Ballinakill and the Owenbeg continues to its confluence with the River Nore as a 4thorder river.

In the eastern part of catchment (east of Ballinakill), the Owenbeg mostly drains Surface Water Gleys / Acidic Ground Water Gleys (AminPD), Acid Brown Earths / Brown Podzolics and Renzinas / Lithosols (BminSW). The remainder of the catchment chiefly drains Grey Brown Podzolics / Basic Brown Earths (BminDW) and Surface Water Gleys I Basic Ground Water Gleys (BminPD) derived from mainly calcareous parent materials.

3.2 Water quality

For inspection purposes only. 3.2.7 Existing informationConsent of copyright owner required for any other use.

3.2.1.1 EPA bioloaical water aualitv data

The EPA does not have any monitoring stations on the Ballinakill Stream; however, the Owenbeg River (EPA code 15/0/01)is monitored by the EPA with stations located upstream and downstream of the confluence of-the Ballinakill Stream with the Owenbeg River. The EPA biological water quality monitoring data for the Owenbeg River rates the watercourse as being of Class A water quality for approximately 90% of its length. It is the upper reaches of the river that have been found to be of lower water quality historically.

The Castlemarket Bridge monitoring station (station code 15/0/01/0280) is located on the Owenbeg River, approximately one river kilometer upstream of the confluence with the Ballinakill Stream. This station has been found to achieve a Q4 'good ecological status' biological water quality rating for twelve consecutive years from 1995 - 2007.

The Attanagh Bridge monitoring station (station code 15/0/01/0400) is located approximately 3.2 river kilometers downstream of the Ballinakill Stream confluence. This station has also been found to achieve a Q4 'good ecological status' biological water quality rating for twelve consecutive years from 1995 - 2007. The EPA biological water quality monitoring data does not therefore register an impact on the Owenbeg River from the WwTP discharge at Ballinakill. However, as there is no EPA biological water quality monitoring data for the Ballinkill Stream; water quality impacts in this watercourse, closer to the outfall, are limited to data from the Laois County Council monitoring programme.

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Table 5 presents a summary of the EPA biological water quality data from the Owenbeg River; while Table 6 presents the results of the EPA biological water quality monitoring at stations on the Owenbeg River upstream and downstream of the confluence with the Ballinakill Stream.

Table 5 Summary of EPA water quality results showina overall results for the Owenbea [Nore). Data is from EPA >logicalsurveys during the period 2004

Additional biological water quality data was recorded by the EPA on the Owenbeg River upstream and downstream of the Ballinakill Stream confluence (Stations 0280 and 0400 respectively) in 2007 (Neill, 2008). Both stations were rated Q4 indicating a continuation in , good ecological status at this station over the monitoring period for which data is available.

3.2.1.2 EPA chemical water aualitv data

The EPA maintain a chemical water quality monitoring programme on the Owenbeg in conjunction with the biological monitoring programme. The EPA does not monitor the chemical water quality of the Ballinakill Stream. Chemical water quality data from the EPA during 2006 was available for stations upstream and downstream of the confluence of the Ballinkill Stream with the Owenbeg River. The upstream station at Ironmills Bridge (station code 0200) and the downstream station at Rosconnell Bridge (station code 0300) were located closer to the confluence of the two water courses than the new monitoring stations currently monitored by the EPA under the Water Framework Directive (2000) monitoring programme. Despite the proximity of these stations upstream and downstream of the confluence, the chemical water quality data does not indicate a decrease in chemical water quality in the Owenbeg River downstream of the confluence of the Ballinkill Stream. However, it must be noted that this data is only available for one year, over four sampling occasions.

EPA chemical water quality stations For on inspection the Owenbegpurposes only. River were replaced in 2007 with two Consent of copyright owner required for any other use. new stations (codes 0050 and 00160) following the implementation of the monitoring programme for the Water Framework Directive (2000). The monitoring stations upstream and downstream of the confluence with the Ballinakill Stream are therefore adjusted to station 0160 at Cloghoge (upstream) and station 0400 at Attanagh Bridge (downstream). These stations are located considerably further from the confluence of the two water courses, with the downstream, Attanagh Bridge station located approximately 3.2 river kilometers downstream of the confluence.

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For inspection purposes only. Consent of copyright owner required for any other use.

3.2.1.4 Laois County Council Monitoring Data

Laois County Council monitor water quality in the Ballinakill Stream at stations upstream and downstream of the WwTP discharge. The results of this monitoring programme are presented in Appendix 3. For the purposes of this assessment the most recent data (2006 to 2009) was utilised.

From the data provided by Laois County Council it is clear that there is a significant background water quality problem in the Ballinakill Stream, where median values for Ammonia and Nitrates are significantly elevated above statutory limits upstream of the WwTP discharge.

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On occasion BOD and Orthophosphate were also recorded as significantly elevated at this station.

The Laois Co. Co. data set highlights an increased nutrient loading in the Ballinakill Stream downstream of the WwTP discharge, particularly in relation to Ammonia and Orthophosphate. Median BOD values were also elevated, while median Dissolved Oxygen levels decreased significantly downstream of the discharge.

3.2.2 Results of the Ecofact on-site assessment (May 2009)

This section presents the results of (he May 2009 biological assessment carried out at stations located upstream and downstream of the existing Ballinakill WwTP outfall on the Ballinakill Stream. This assessment was undertaken to compliment the available information. The procedure followed was EPA kick sampling (Toner et al., 2005). Biotic indices including Q- values and BMWP scores were derived and macroinvertebrate functional analysis was also carried out.

3.2.2. I Reference Site

A total of 12 different macroinvertebrate families were recorded at this site. The freshwater shrimp Garnrnarus duebeni, a pollution tolerant (Group C) ‘indicator was dominant while another crustacean, the very pollution tolerant (Group D) hog louse Asellus aquaticus was common. Larvae of the Group C large dark olive mayfly Baefis rhodani was also common, Larvae of the pollution sensitive (Group A) yellow upright mayfly Rhithrogena sernicolorata, the common yellow sally stonefly lsoperla gramrnatica and the winter stonefly Brachytera risi were all present at this site. Small numbers of Group B cased caddisfly larvae (less sensitive indicators) of Pofarnophylax sp. and Halesus radiatus were recorded at this site. Blackfly and green chironomid larvae were recorded in fair numbers and small numbers, respectively. Pollution tolerant adult riffle beetle Elrnis sp. was found in fair numbers and larvae of same were present. Very tolerant orb mussel Pisidiurn sp. and leech Erpobdella festacea were present at this site.

Using the EPA biological monitoring system (Toner et al., 2005), this part of the stream was rated as ‘Unpolluted, (Q4)’ (raised due to stream size). The substrate at this site was composed mostly of silt so it was classed as a ‘pool’ habitat when using habitat specific scores from macroinvertebrates in the For BMWP inspection purposesindex. only. The calculated BMWP score for this site Consent of copyright owner required for any other use. was 62.4 which is interpreted as ‘Moderately impacted’. The corresponding ASPT for this site was 5.7 which is indicative of good water quality. This score was brought about by the presence of pollution sensitive taxa (certain stonefly and mayfly larvae). The SSRS for this stream was 6.4, marginally below the ‘at risk / probably at risk’ threshold so is in the ‘probably at risk’. This site was rated ‘Moderate’ status.

3.2.2.2 Receptor site

A macroinvertebrate family diversity of 10 was recorded at this site. Larvae of the pollution Baetis rhodani were common; the only mayfly recorded at his site. The freshwater shrimp was excessive. Pollution tolerant Asellus aquaticus, Erpobdella festacea and Pisidiurn sp (Sphaeridae) were all present. Bloodworm Chironornous sp. (Group E) along with true fly larvae of the Simulidae and Dicranofa sp. (Group C) were scarce while green chironomids were found in small numbers. Aquatic earthworms (Lumbricidae) were also scarce. The only Group B less sensitive indicator recorded (present) at this site was larva of Halesus radiatus.

This stretch of stream was rated as ‘Slightly polluted, (Q3-4)’ (raised due to stream size). Using BMWP scores for pool habitat, this site scored 39.6. This score is indicative of ‘polluted or impacted’ conditions or categorized as ‘Poor’. The ASPT for this site was 4, a score not 1: associated with good water quality. The SSRS for this site was 3.2, so is considered to be ‘at I risk’. The status of this stretch of stream was deemed to be ‘Poor’.

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3.2.2.3 Bioloaical water auality overview

A full species list for the macroinvertebrates recorded from both the upstream reference and downstream receptor sites on the Ballinkill Stream is presented in Appendix 4. Some of the macroinvertebrates recorded during the current survey are shown in the plates section. Table 1 1 below summarises the structure of the macroinvertebrate communities recorded from each site, according to the pollution sensitivity of the groups present. It can be seen that there were no pollution sensitive indicators (Group A) recorded at the receptor site while this group accounted for 1.7% of the macro-invertebrate assemblage at the reference site. This scenario is repeated for Group B indicators with 2.6% Group B at the reference site and only 0.2% at the receptor. The reference site had more Group D indicators than the reference site (15.7 vs 1.5) mainly due to the abundance of the hog louse. While no Group E indicators were recorded at the reference site, they were at the receptor (0.8%).

Tables 12 and 13 present the results of the functional group analysis at both sites, based on the structure of the macroinvertebrate communities in relation to the trophic groups affecting food supply for juvenile salmonids. The ratio of scrapers to total collectors and shredders (P/R ratio) gives the ratio of gross primary production to community respiration. Both the reference and receptor sites had macroinvertebrate compositions indicative of heterotrophic conditions i.e. ecosystem dependent on external inputs for its maintenance.

The ratio of behavioural drifters (filtering and gathering collectors) to accidental drifters (scrapers, shredders and predators) was used to derive the juvenile salmonid food index for both sites. Using this index, an ‘Unpredictable’ juvenile salmonid food supply was obtained for both the reference and receptor sites, with ratios of 0.21 and 0.15 respectively.

Table 11 Classification of macroinvertebrate taxa recorded at each site in terms of their pollution sensitivity (EPA methods). Pollution indicator group Reference Site Receptor Site Number % of total Number % of total

For inspection purposes only. Consent of copyright owner required for any other use.

Table 13 Juvenile salmonid food index. Predictable invertebrate supply is the ratio of behavioral drifters (filtering and gathering collectors) to accidental drifters (grazers, shredders and predators). Based on a threshold of >0.50 for predictable supply (after Rabenil et al., 2005). Site Behavioral drifterslaccidental drifters Predictable Vs Unpredictable ...... Reference site 0.21 ’ Unpredictable Receptor site 0.15 Unpredictable

3.2.3 Dangerous substances

No dangerous substances monitoring data was available for the Ballinakill WwTP during the preparation of the current assessment.

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EPA Export 26-07-2013:14:13:57 3.2.4 Assimilation capacity

The primary regulatory guideline for effluent standards is the EU Urban Wastewater Treatment Regulations, 2001 which is implemented in Ireland through S.I. 254 of 2001 and the Water Quality Standards for Phosphorus (S.I. 258 of 1998). The Urban Wastewater Treatment Regulations requires the provision of secondary treatment for all discharges to freshwaters and estuaries from towns with a population equivalent of between 2,000 and 10,000. While the requirements of the Urban Wastewater Treatment Regulations are set, water quality requirements are dependent on the background values and the 95 percentile flow in the river (i.e. assimilation capacity). \ The waste assimilation capacity (WAC) of the Ballinakill Stream was assessed using Laois County Council monitoring data (median values) for the monitoring station upstream of the Ballinakill plant (between October 2006 and April 2009). The 95%ile flow in the Ballinakill Stream at the discharge point is 0.003 m3/s (Source: Laois County Council, based on data from Hydrometric Station 15037). The 95%ile flow in the Ballinakill Stream is equal to 3 L/s, therefore the dilution of the discharge is given as only 1.15:l. However, flow rates in the Ballinakill Stream would be greater than this 95%ile flow rate approximately 95% of the time; so this dilution rate represents the worst case scenario during dry weather flows.

The waste assimilation capacity (WAC) of the Ballinakill Stream was based on the limit values set out in the draft Water Framework Directive (WFD) values (DOEHLG, 2008) for the parameters BOD, Ammonia and Ortho-phosphate. Table 14 below gives the concentration requirements of these parameters for rivers under mean and 95%ile flows. For example, a river can be assigned ‘High status’ or ‘Good status’ based on Ortho-phosphate concentrations. ‘High status’ is assigned to a river if Ortho-phosphate concentrations are 50.025 mg/l during mean flows or 50.045 during 95%ile flows. ‘Good status’ is assigned if concentrations are 50.035 mg/l during mean flows or 10,075 mg/l during 95%ile flows. Similarly, a river can be assigned either ‘High status’ or ‘Good status’ according to oxygenation conditions; BOD concentrations 51.3 mg/l (mean flows) or 52.2 mg/l (95%ile flows) imply ‘High status’ while BOD concentrations 51.5 (mean flows) or 52.6 mg/l imply ‘Good status’.

The results of the Waste Assimilation Capacity assessment for Orthophosphate, Ammonia and BOD in the Ballinakill Stream are presented in Tables 15 (95%ile flow) and 16 (median flow). These parameters are assessed using DOEHLG (2008) criteria, as well as Salmonid For inspection purposes only. Water Regulations limits forConsent Ammonia; of copyright Freshwaterowner required for anyFish other Directiveuse. limits for BOD; and Phosphorous Regulations limits for Ortho-phosphate. The median limit value for Ortho- phosphate in the Phosphorus Regulations is 0.03 mg/l and is more stringent than WFD guideline values (except for concentrations indicative of ‘High status’ at 95%ile flows). This value is also the interim statutory standard for unpolluted rivers. For Biochemical Oxygen Demand (BOD) the level of 3 rng02/l is used, as this guideline concentration is recommended for salmonid fish in the E.U. Freshwater Fish Directive (78/659/EEC), as well as in the Salmonid Water Regulations (1988).

At 95%ile flow (0.003 m3/s), the Ballinakill Stream has WAC for all four parameters: Suspended Solids, Orthophosphate, Ammonia and BOD. This is because background levels of these parameters are below the environmental standard limit concentrations. For Orthophosphate, there is WAC if the WFD ‘Good status’ standard of 0.075 mg/L is taken (0.0 15 kg/day).

Assimilation capacity increases significantly using the median flow of 0.1 3m3/s; where a WAC of 67.39 kg/day is available for Suspended Solids, compared to 1.55 kg/day at 95%ile flow. At median flow WAC for Orthophosphate is 0.64 kg/day, BOD is 0.3 kg/day and Ammonia is 0.47 kg/day using the WFD ‘Good status’ standard.

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Table 14 Requirements of the draft Water Framework Directive for assigning rivers ‘High’ or ‘Good’ status with respect to certain parameters and flow rates (from DOELG, 2008). Parameter Mean flow 95%ile flow ...... High status Good status High status Good status SI SI.5 52.2 $2.6 - BOD _(m9-03!1) ------.3------Total Ammonia (mg NII) S0.040 50.065 50.090 S0.140 _____-____--_-____-____-__-____r-______------Ortho-phosphate (mg PlI) ~0.025 S0.035 $0.045 50.075

Table 15 Assimilation capacity of the Ballinakill River for BOD, Orthophosphateand Ammonia at the discharge point based on median background parameter levels and a 95%ile flow of 0.003m3/s. Chemical water quality results provided by Laois Co. Co. for the Ballinakill Stream upstream of the WwTP discharge point were used. Limit concentrations standards for the different parameters are in bold. 95%ile Flow Suspended Orthophosphate ; BOD : Ammonia . Solids Median backaround 6 0.018 I 0.048

median upstream ------‘------~------,------concentration Background 1.555 0.005 0.259 0.012 parameter loading (kglday) SWR Salmonid Waters Regulations (1998). WFD HS=High status (95%ile), WFD GS=Good status (95%ile flow), FFD (S) = Salmonid Waters Standard. PR=Phosphorous Regulations, median value. WFD values are from the draft Water Framework Directive document (DOEHLG, 2008). NPWS proposed value for protecting Pearl Mussels (2005).

Table 16 Assimilation capacity of the Ballinakill River for BOD, Orthophosphate and Ammonia at the discharge point based on median background parameter levels and a median flow of 0.13m3/s.Chemical water quality results provided by Laois Co. Co. for the Ballinakill Stream upstream of the WwTP discharge point were used. Limit concentrations standards for the different parameters are in bold. Median flow Suspended Orthophosphate j BOD : Ammonia Solids Median background 6 0.018 1 0.048

Standard Limit - concen!rat!og? _(S?s!ll------For - - -inspection ------purposes ------only. ------WAC (kglday) using 213.4 Consent0.303 of copyright0.640 owner 0.135 required for 13.48 any other17.97 use. 22.46 0.472 1.033 10.69 median upstream

-----______------~------..---concentration Background 67.392 0.202 11.232 0.539 parameter loading (kglday) SWR Salmonid Waters Regulations (1998). WFD HS=High status (95%ile), WFD GS=Good status (95%ile flow), FFD (S) = Salmonid Waters Standard. PR=Phosphorous Regulations, median value. WFD values are from the draft Water Framework Directive document (DOEHLG, 2008). NPWS proposed value for protecting Pearl Mussels (2005).

There are limitations to the precision of the assimilation capacity results. In calculating the assimilation capacity, the background concentration is a key constraint. Variations in sampling for background concentrations would be expected due to changes in flow rates, season and local activities on the land. It also can be expected that flows in the river will be regularly above the 95%ile level providing increased dilution. Indeed flow will be at or below this level for only 5% of the time.

An assimilation capacity assessment was not carried out on the Owenbeg River, as flow data and chemical data was not available for this river upstream of the Ballinakill Stream confluence. The Owenbeg River, a 4Ih order river with good water quality would be expected to have much greater assimilation capacity than the Ballinakill Stream.

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3.3 Sediment quality /

A spillage of Polychlorinated biphenyls (PCBs) occurred in the Nore at Kilkenny in the 1980's (Lucey, 1998), and localized contamination of sediments still persists. There are no reports of any other significant sediment contamination in the River Nore or Owenbeg catchment. No other information on sediment quality in the Nore catchment was obtained during the current assessment.

3.4 Areas designated for nature conservation

Sites of international conservation importance are designated as Special Areas of Conservation (SACs) under the Habitats Directive (1992) and/or Special Protection Areas (SPAs) under the Birds Directive (1979). Together, SACs and SPAs make up the Natura 2000 network of wildlife conservation sites. Sites of national importance for wildlife are designated as Natural Heritage Areas (NHAs) under the Irish Wildlife Act, 2000.

The existing WwTP at Ballinakill is not located within a designated conservation site. The Ballinakill Stream, which receives the discharge from the WwTP is not designated as an SAC. However the Owenbeg River, of which the Ballinakill Stream is a tributary, is included within the River Barrow and River Nore SAC (site code 002162). The confluence between the Ballinakill Stream and the Owenbeg River is located ca. 3 river kilometers downstream of the Ballinakill WwTP discharge. The Owenbeg River meets the River Nore ca. 3.2 river kilometers downstream of the Ballinakill Stream confluence.

The River Barrow and River Nore SAC is selected for alluvial wet woodlands and petrifying springs, priority habitats on Annex I of the E.U. Habitats Directive, 1992. The site is also selected as a cSAC for old oak woodlands, floating river vegetation, estuary, tidal mudflats, Salicornia mudflats, Atlantic salt meadows, Mediterranean salt meadows, dry heath and eutrophic tall herbs, all habitats listed on Annex I of the E.U. Habitats Directive. As well as habitats, the cSAC has been selected due to the presence of invertebrate, fish and mammal species which are listed under Annex II of the EU Habitats Directive, including freshwater pearl mussel (Margarififera margarififera and its hardwater form M. m. durrovensis), freshwater crayfish Ausfropotamobius pallipes, Atlantic salmon Salmo salar, twaite shad Alosa fallax, the three Irish Lamprey species - sea Pefromyzon marinus, brook Lampefra planeri and river Lampefra fluviafilis, the Desmoulin's whorl snail Vertigo moulinsiana and Eurasian otter Lufra lufra. This site is one of only Fora handfulinspection purposes of spawning only. grounds in the country for twaite shad, and is the most importantConsent site of for copyright this owner species. required Otherfor any other important use. animal species are also found in the BarrowlNore cSAC. These include Daubenton's bat Myofis daubenfoni, badger Meles meles, Irish hare Lepus timidus hibernicus and frog Rana temporaria, all species listed " in the Irish Red Data Book. The rare Red Data Book fish species smelt Osmerus eperlanus occurs in the estuary of the River Nore. Two other freshwater mussel species, Anodonta anafina and A. cygnea are also found in the Nore (Lucey, 1998). The Barrow/Nore is mainly a grilse fishery though spring salmon fishing is good in the vicinity lnistioge on the Nore. Good quality water is necessary to maintain the populations of the Annex II animal species listed above. Good quality is dependent on controlling fertilisation of the grasslands, particularly along the Nore. It also requires that sewage be properly treated before discharge.

Lisbigney Bog SAC lies within 2km southwest of Ballinakill WwTP. This is a terrestrial conservation site designated for peatland flora and habitats listed on Annex I of the EU Habitats Directive. This site is geographically and hydrologically isolated from the WwTP and associated discharge.

3.5 Protected aquatic flora and fauna

Table 17 presents a list of the protected species recorded in the River Nore catchment and their status. Each species is discussed separately below in relation to the operation of the Ballinakill WwTP and the Owenbeg River:

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The white-clawed crayfish is the only freshwater crayfish recorded in Ireland. Populations of the species in the rest of Europe have declined dramatically and Ireland is seen as a unique stronghold for this species in a European context (Reynolds 1998). It is classified as vulnerable and rare in the IUCN Red List and is protected in Ireland under the schedules of the Wildlife Act 1976. It is also listed in Appendices II and V of the Habitats Directive (92:43:EEC). It is generally considered to be widespread in lowland lakes and rivers such as the River Nore, which are underlain by Carboniferous limestone, or its derivative - glacial drift (Reynolds, 1998). \ Crayfish were not recorded in the field survey from the stations sampled upstream and downstream of the existing WwTP discharge on the Ballinakill Stream. This specie may occur in other parts of the stream and also in the Owenbeg River into which the Ballinakill River flows.

3.5.2 Lampreys

The brook lamprey is the smallest of the three lampreys native to Ireland and it is the only one of the three species that is non-parasitic and spends all its life in freshwater (Maitland & Campbell 1992). The river lamprey is larger in size than the brook lamprey and exhibits an anadromous' life cycle. The sea lamprey is the largest of the Irish lampreys. Brook lamprey and sea lamprey are listed in Appendix II, while river lamprey is listed in both Appendices I1 and IV of the Habitats Directive (92:43:EEC). All three species are listed in Appendix Ill of the Bern Convention. All three lamprey For species inspection purposeshave beenonly. recorded from the Nore catchment Consent of copyright owner required for any other use. (Kurtz & Costello 1999). Brook lamprey are likely to occur in the Owenbeg River downstream of the confluence with the Ballinakill Stream. This species probably also occurs in the Ballinakill Stream downstream of the Ballinakill WwTP discharge point.

3.5.3 Shad

Twaite Shad and Allis Shad are among the rarest species of fish breeding in Irish freshwaters and are listed under Annexes II and V of the EU Habitats Directive. Both species are also listed in Appendix Ill of the Bern Convention. Shad have an anadromous life cycle and both species are thought to occur in the BarrowINore Estuary. However, it is clear that these species are confined to the lower reaches of the river and would therefore not occur in the study area.

3.5.4 Atlanfic salmon

The Atlantic salmon is listed under Annexes II and V of the EU Habitat's Directive and Appendix Ill of the Bern Convention. It is an economically important species and salmon recreational and commercial fisheries occur throughout Ireland. Salmon are present throughout the Nore catchment (Lucey 1998) and are likely to spawn in the Owenbeg River within the study area downstream of the confluence with the Ballinakill Stream. The size of the

1 Anadromous fish spend most of their adult lives in salt water, and migrate to freshwater rivers and lakes to reproduce.

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Ballinakill Stream makes it unsuitable for spawning salmon. The lower reaches of the stream may be used by sub-adult salmon from the Owenbeg River.

3.5.5 Eurasian Offer

The otter Lutra lufra is a legally protected species under the Wildlife Act, 1976 (and Wildlife (Amendment) Act, 2000). It is listed under Annex I1 of the EU Habitats Directive and under Annex II of the Berne Convention. It is found throughout Ireland where it has apparently avoided the population declines that have occurred in many other countries (Hayden and Harrington 2000). Evidence of otter activity has been recorded from the Owenbeg River and this species is widespread in the River Nore catchment.

3.5.6 Freshwater Pearl-mussel

Freshwater Pearl-Mussel (Margarififera margarififera) occurs in the River Nore catchment; however this species is now rare in the main channel of the river (Lucey, 1998). The freshwater pearl mussel Margarififera margarififera has been recorded from both the River Nore and the River Barrow catchments with populations previously recorded from the River Nore in the vicinity of Durrow town, downstream of Borris-in-Ossory (Moorkens et a/., 2007). The populations of M. margarififera within the River Nore have been described as a separate hard water species (Margarififera durrovensis), or as a subspecies; however discussion remains as to whether these hard water populations are actually an ecophenotypic hard water form of M. margarififera (Lucey, 2006).

The distributon of the Nore freshwater pearl mussel M. m. durrovensis is limited to the stretch of the river from Poorman’s Bridge (S 407 859) to Lismaine Bridge@ 442 660), with most of the population found between Poorman’s Bridge and the Avonmore Creamery above (S 440 722) (NS2, 2009). From studies carried out between 1990 and 1994, it was estimated that the total mussel numbers in the Nore had fallen from 2,000 to 420 (Moorkens and Costello 1994). The most recent estimate of the total number of extant M. durrovensis adults in Ireland, based on surveys from 1991 to 2005 is 500 individuals. This represents a decline of 75% from the total of 2,000 individuals found in 1991.

The latest results confirm that the Nore population is at a critically low level, and the indications are that it is unable to successfully recruit young. Once breeding stops, it becomes very difficult to save a population. No For mussel inspection river purposes in only.this situation has yet been recovered to a fully independent, recovered andConsent breeding of copyright ownercolony. required In for this any otherknowledge, use. the pearl mussel has been identified as being internationally endangered.

3.5.6.I Wafer Qualify reauiremenfs for Pearl Mussels

The water quality requirements for Pearl Mussels have recently been reviewed by Young (2005). The main findings of this review are as follows:-

* Juvenile mussels and glochidia are often more susceptible than adults to poor water conditions. Interstitial water chemistry is of crucial importance to juvenile mussels but only one study has been carried out on the requirements of juvenile freshwater pearl mussels. 0 Unnaturally high levels of nutrients, conductivity, nitrates, phosphates, BOD, metals and some pesticides are detrimental to Pearl Mussels, as well as unnaturally high and low pH. Eutrophication is widely regarded as very damaging to mussel populations but few , studies have quantified this problem. Biocides have frequently been shown to be toxic to mussels of all species.

Guidance on water quality requirements for Pearl Mussels has also been given in an Irish context by Moorkens (2000) and the draft guidelines provided in NPWS (2005). General recommendations for favourable Water Quality Objectives for Pearl Mussels for a number of sources are provided in Table 18.

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EPA Export 26-07-2013:14:13:57 Table 18 General recommendationsfor favourable Water Quality Objectives for Pearl Mussels. Parameter Target Target Proposed Minimum Proposed Standard (Oliver 2000) (Bauer Standard (NPWS 2005)

3.6 Recreational and Commercial fisheries

The fish fauna of Ireland is not as diverse as other European countries due to the impact of glaciation. Most of the fish species present in Irish river catchments, such as the River Nore, have colonized from the sea or have been artificially introduced. Native fish species in the Nore catchment include the three Irish lamprey species (brook lamprey, river lamprey, and sea lamprey) (Kurz & Costello, 1999), the Atlantic salmon, (Lucey, 1998) and the Twaite Shad, (Lucey, 1998) all of which are listed under the EU Habitats Directive. The Nore is the most important river in Ireland for the latter species; however these fish do not ascend past the weir at St. Mullins (King, 2002). The European eel, brown trout, and three-spined stickleback, are other common native species present in the Nore catchment; all three of which are expected from the Owenbeg River.

Introduced fish species include northern pike E.& lucius, stone loach Barbatula barbatula, roach Rutilus rutilus, dace Leuciscus leuciscus and minnow Phoxinus phoxinus (Lucey, 1998). The smelt Osmerous eperlanus, a species listed as vulnerable in the red data list (Whilde, 1993), is present in the Nore Estuary (King, 2002).

The freshwater stretches of the River Nore main channel is a designated salmonid river under the EU Fish Directive (78/659/EEC). The Nore catchment, including the Owenbeg River is an important salmon and trout fishery which was once regarded as being one of the finest salmon rivers in the country (O’Reilly, 2004). Brown trout angling is an important amenity in the Owenbeg River (O’Reilly, 2004). The ForRiver inspection Nore purposes catchment only. (Fishery Code 38) is classified as a salmon and sea trout fishery (McGinnityConsent of copyright et ownera/, 2003). required forThe any otherBallinakill use. Stream is considered to be of low fisheries value with limited habitat for salmonid species in the upper reaches. There is potential for salmonid species, particularly brown trout, to utilize the lower reaches of this stream.

3.7 Water abstractions

There are no Drinking Water RPAs on the Ballinakill Stream / Owenbeg River or on the River Nore within lOkm downstream of the study area (Source: EPA Envision). It is expected that the river is used by farms for animal drinking water.

3.8 Designated recreational and bathing waters

There are no designated recreational or bathing waters on the Ballinakill Stream / Owenbeg River or on the River Nore (EPA online Envision map).

3.9 Nutrient sensitive areas (

Neither the Ballinakill Stream nor the Owenbeg River are designated as nutrient sensitive water. The River Nore is classified as a nutrient sensitive water downstream of Kilkenny under the Urban Wastewater Treatment Regulations (2001).

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4. IMPACT ASSESSMENT

4.1 Introduction

According to the EPA (2008), a discharge from a WwTP would be considered to have a significant adverse effect on the receiving waters if it were to:-

* Cause a deterioration in the chemical status or ecological status (or ecological potential as the case may be) in the receiving body of surface water; Cause a deterioration in the chemical status in the receiving body of groundwater; 0 Cause the input into groundwater of hazardous substances, except where it is established that the input concerned is in a quantity and concentration so small as to obviate any present or future danger of deterioration in the quality of the receiving groundwater; Cause deterioration or result in significant and sustained upward trends in the concentrations of pollutants in groundwater in the case of pollutants that are not hazardous, Permanently exclude or compromise the achievement of the objectives established for protected species and natural habitats in the case of European sites where the maintenance or improvement of the status of water is an important factor in their protection or which is inconsistent with the achievement of environmental quality standards established under national Regulations in relation to designated bathing waters, designated shellfish waters, areas designated for the protection of freshwater fish and designated nutrient sensitive areas.

In relation to aquatic life and designated sites, impacts are assessed using the following criteria:-

* No change: No discernible change in the ecology of the affected feature. Imperceptible Impact: A change in the ecology of the affected site, the consequences of which are strictly limited to within the site boundaries. Slight Impact: A change in the ecology of the affected site which has noticeable ecological consequences outside the site boundary, but these consequences are not considered to significantly affect the distribution and/or abundance of species or habitats of con'servation importance. For inspection purposes only. Moderate Impact: A changeConsent of copyrightin the ownerecology required of for the any otheraffected use. site, which has noticeable ecological consequences outside the site boundary. These consequences are considered to significantly affect the distribution and/or abundance of species or habitats of conservation importance. Substantial Impact: A change in the ecology of the affected site, which has noticeable ecological consequences outside the site boundary. These consequences are considered to significantly affect species or habitats .of high conservation importance and to potentially affect the overall viability of those species or habitats in the wider area. Profound Impact: A change in the ecology of the affected site, which has noticeable ecological consequences outside the site boundary. These consequences are considered to be such that the overall viability of species or habitats of high conservation importance in the wider area is under a very high degree of threat (negative impact) or is likely to increase markedly (positive impact).

As there is no discharge directly into groundwater from the Ballinakill WwTP, no assessment of local groundwater is made in this assessment. It is considered that through the interaction between surface and ground waters, any significant impact on the receiving surface waters could also potentially result in a similar impact on local groundwater.

The Ballinakill WwTP discharges into the Ballinakill Stream, a minor watercourse, which meets the Owenbeg River ca. 3 river kilometers downstream of the WwTP oufall. The Ballinakill Stream is considered as the receiving water for this assessment, as the monitoring data provided by Laois County Council pertained to this water course. However, as the

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Owenbeg River receives the Ballinakill Stream ca. 3km downstream of the WwTP discharge and given that this river is designated within the River Barrow and River Nore SAC, a further, limited impact assessment on the Owenbeg River is provided.

A summary of the receiving water impact assessment is provided in Table 19. The impact on identified receptors is outlined in the following sections.

Table 19 Summary of the receiving waters impact assessment Receptor Scale of impact on the Ballinakill Scale of impact on the Owenbeg River Stream

4.2 Impact on water quality

The impact of the current discharge regime on the receiving water (Ballinakill Stream) is discussed under the following sub-headings:

0 Chemical water.quality 0 Biological water quality

0 Dangerous substances

0 Assimilation capacity

4.2.7 Chemical water quality

From the historical EPA chemical water quality monitoring data there is no detectable impact from the WwTP at Ballinakill on the Owenbeg River. Water quality data from the monitoring stations upstream of the confluence with the Ballinakill Stream and downstream at Attanagh Bridge do not indicate a deterioration in water quality that may be attributed to the discharge from the WwTP. As there is no monitoring For inspection datapurposes available only. for the Owenbeg River directly Consent of copyright owner required for any other use. downstream of the confluence with the Ballinakill Stream, it is considered that the Ballinakill WwTP is having an imperceptible impact on the Owenbeg River,

The Laois Co. Co. data for the Ballinakill Stream highlights an increased nutrient loading in the Ballinakill Stream downstream of the WwTP discharge. Ammonia and Orthophosphate showed the greatest elevation, increasing by over 700% and 500%, respectively (based on median values). Median BOD values were also elevated when compared to upstream (100% increase, while median Dissolved Oxygen levels decreased (16%) downstream of the discharge. It is therefore considered that the WwTP discharge is having a moderate negative impact on water quality in the Ballinakill Stream.

4.2.2 Biological water quality

Following the biological water quality assessment carried ’out by Ecofact in May 2009 and subsequent analysis of the macroinvertebrate assemblages, it was found that water quality in the Ballinakill Stream was affected by the existing discharge. A decline in biological water quality was recorded between the reference site upstream of the Ballinakill WwTP and a receptor site downstream of same. A consistent deterioration in water quality was observed across all aspects of biological water quality including; family richness (1 2, 10); Q-rating (Q4, Q3-4); BMWP score (62.4, 39.6); ASPT (5.7, 4); and SSRS (6.4, 3.2); where numbers in parenthesis, correspond to the reference and receptor sites, respectively. The water quality status of the Ballinkill Stream upstream of the WwTP outfall was assessed as Q4 ‘good’ but dropped to Q3-4 ‘slightly polluted’ downstream of the outfall. It is important to note that the Q

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values for the Ballinakill stream have been raised due to the small stream size, in cognizance of the limitation of the EPA Q-ratings methodology in smaller watercourses. However, using both the BMWP scoring system and the SSRS system (developed specifically for small streams) the Ballinkill is classed as ‘Poor’ downstream of the WwTP discharge. This is compared to a moderately polluted rating for the upstream reference station.

Based on the biological water quality data for the Ballinkill Stream it is considered that the WwTP discharge is having a slight negative impact on the receiving water.

The EPA biological water quality monitoring data for the Owenbeg River presents a long term’ picture of water quality within the watercourse upstream and downstream of the confluence with the Ballinakill Stream. From this data it can be seen that the biological water quality within this watercourse has remained stable at ‘good status’ upstream and downstream of the Ballinakill Stream confluence. Monitoring stations at Castlemarket Brid’ge (1 km upstream) and at Attanagh Bridge (3.2km downstream) have maintained a Q4 ‘good ecological status’. It is therefore considered that the Ballinakill WwTP discharge is having an imperceptible impact on biological water quality in the Owenbeg River.

4.2.4 Assimilation capacity

The capacity of the Ballinakill Stream to receive the discharges from the Ballinakill WwTP has been assessed using median background Laois County Council chemical water quality data from the upstream monitoring station (local-station 8702). This data dates from October 2006 to April 2009. Observed effluent data provided by Laois Co. Co. dated from September 2007 to April 2009 was used. The flow rate of the discharge at the Ballinakill plant was taken as 2.6L/s (value taken from Nicholas 0’ Dwyer, 2007). This flow rate equates to a volume of 225m3/day.

The results of the waste assimilation capacity \WAC) assessment for the Ballinakill Stream is provided in Table 20 for 95%ile flow (0.003 m 1s) and Table 21 for median flow (0.13 m3/s). Flow rates in the Ballinakill Stream were provided by Laois County Council. At 95%ile flow, the effluent from the plant is diluted by a factor of 1.15 by the Ballinakill Stream and dilution increases to 49.9:l at median flow.

The Ballinakill Stream has some WAC for Suspended Solids, Orthophosphate and BOD upstream of the plant discharge at 95%ile flow. At 95%ile flow however, this watercourse does For inspection purposes only. not have sufficient flow to diluteConsent the ofdischarged copyright owner effluent required for from any other the use. Ballinakill WwTP. Suspended Solids (SS) is the parameter that is closest to the environmental standard with approximately 153% of assimilation capacity used downstream of the plant.

At median flow there is increased dilution and the Ballinakill Stream has WAC for all three parameters. The orthophosphate loading to the river by the discharged effluent (225 m3/day) is 0.225 kglday based on the observed orthophosphate concentration of 0.018 mg/L in the effluent. At this rate of discharge, the Ballinakill Stream has WAC for orthophosphate and uses approximately only 35% of WAC using WFD ‘Good status’ standards (74.2% using WAC High status standards). Similarly, at median flow, the Ballinakill Stream has WAC for BOD using both WFD Good status (31.3% WAC usage) and WFD High status (41.7% WAC usage). At median flows in terms of key parameters (BOD and orthophosphate), the status of the Ballinakill Stream would not be changed by the effluent discharged from the Ballinakill WwTP. The observed median concentrations of the parameters for which design standards were available were all below the design standard.

It can be expected that flows in the river will be regularly above the 95%ile level providing increased dilution. Indeed flow will be at or below this level for only 5% of the time so median flows are probably a truer reflection on the assimilation capacity in the river.

It is therefore considered that the Ballinakill WwTP discharge is having a slight negative impact on the Ballinakill Stream receiving water during 95%ile flows; however, this flow in the river occurs only 5% of the time.

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From the WAC the WwTP is assessed as having a slight to imperceptible impact on the WAC during median flows, where the WFD 'good status' requirements are met for all parameters. It is important to note, however, that the Phosphorus Regulations requirements are not met for the Orthophosphate loadings to the river under 95%ile or median flows.

Table 20 Impact of the existing plant on assimilation capacity (WAC) of the Ballinakill Stream for Suspended Solids (SS), Ortho-phosphate and BOD. Based on median background (upstream) concentrations of Suspended Solids, Orthophosphate and BOD in the Ballinakill Stream from October 2006 to April 2009 (Laois Co. Co. data), a 95%ile flow of 0.003m3/sin the Ballinakill Stream, a discharge rate of 225 m3/dayfrom the WwTP and observed concentrations supplied by Laois Co. Co. between January 2006 and April 2009. Limit concentrations standards for the different parameters are in bold. 95%ile Flow ; Suspended : Ortho-phosphate j BOD : Solids Median background concentration (mgll) :6 : 0.018 :I --..~------~--.-----.--~.------..------~.~--.-----.---.-'.-.-----.--~------I---~__-~---~---__~-___-~-~ Design standard (mglL) : 35 :2 ; 35 ______-___-___-___-___r______--__,------___-______.______I______-~, Observed concentration (mg/L) : 34 ; 1.44 (N=19) ; 13.5(N=20) .~--.---._---_---~---_------___-_-_-_-_---..~-~~-_---__------I.----~__-.--..__-_~-.___~_I--~------~------~--~~--~I Environmental standard : SWR : WFD WFD PR* : WFD WFD FFD j : HS* GS* : HS* GS' _-___- - - _--- _--_- --_ - --__---_------_-L -_--__ - - -_----I------__--_ - --__-__--_I __-_ - - - ______- - SSL; Environmental standard limit concentration : 25 : 0.045 0.075 0.03 : 2.2 2.6 3 ,

Loading to river by plant under DWF (kg/day) : 7.65 : 0.324 '--.---.------_.-.-.-.-.--I % of WAC usage downstream of plant i 153 j 4630 2193 10417 j 1808 1356 1085 j (kg/day) WR Salmonid Waters Regulations (1998). WFD HS=High status (95%ile), WFD GS=Good status (95%ile flow), FFD IS) = Salmonid Waters Standard. PR=PhosDhorous Reoulations. median value. WFD values are from the draft Water ' Framework Directive document (DOEHLG, 2008). NPWS proposed value for protecting Pearl Mussels (2005).

Table 21 Impact of the existing plant on waste assimilation capacity (WAC) of the Ballinakill Stream for Suspended Solids (SS), Ortho-phosphate and BOD. Based on median background (upstream) concentrations of Suspended Solids, Orthophosphate and BOD in the Ballinakill Stream from October 2006 to April 2009 (Laois Co. Co. data), a media flow of 0.13m3/sin the Ballinakill Stream, a discharge rate of 225 m3/dayfrom the WwTP and observed concentrations supplied by Laois Co. Co. between January 20006 and April 2009. Limit concentrations standards for the different parameters are in bold. Median Flow : Suspended j Ortho-phosphate : BOD j Solids Median background concentration (mg/l) :6, : 0.018 :I ______--__--__-___-__~-______-__,_-___-___-______,______, Design standard (mglL) : 35 :2 : 35 ~------~------L------'-.------.--.------.----~-~_-___-~---___-__--___--I Observed concentration (mglL) : 34 : 1.44 (N=19) ; 13.5 (N=20) _____.______-______.______.~--__--______-_,__-___-___.______1______~---.-~~., For inspection purposes only. Environmental standard Consent of copyright8 SWR owner required8 WFD for any other WFD use. PR* WFD WFD FFD I ...... ;------,-i -HS* ------GS*------_,_: -HS* ------GS* ------@I *I- - .; Environmental standard limit concentration ; 25 ; 0.045 0.075 0.03 ; 2.2 2.6 3 ; -Q??g/!)------:~------,------,--__--__--__--__-______WAC (kglday) using median upstream 1 213.4 ; 0.303 0.640 0.135 ; 13.48 17.97 22.46 j ...... concentration and DWF from plant.------~.------~------'------.------.---..--~ Loading to river by plant under DWF (kg/day) 7.87 j 0.225 i 5.625 ______------______~--______-_--,------______(______, % of WAC usage downstream of plant ; 3.7 ; 74.2 35.1 166.9 : 41.7 31.3 25.0 i I .-(Q/daY) .______- ______- - - ______---.-:------.---.---.______-:______- - - ______: WR Salmonid Waters Regulations (1998). WFD-1 HS=High status (95%ile), WFD GS=Good status (95%ile flow), FFD (S) = Salmonid Waters Standard. PR=Phosphorous Regulations, median value. WFD values are from the draft Water Framework Directive document (DOEHLG, 2008). NPWS proposed value for protecting Pearl Mussels (2005).

There are limitations to the precision of the assimilation capacity results. In calculating the assimilation capacity, the background concentration is a key constraint. Variations in sampling for background concentrations would be expected due to changes in flow rates, season and local activities on the land.

4.3 Impact on areas designated for nature conservation

The Ballinakill Stream is not designated within any nature conservation site. The Owenbeg River is designated within the River Barrow and River Nore SAC and impacts to this watercourse would be considered to have a negative impact on the conservation interests of the SAC as a whole.

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Although monitoring data provided by Laois County Council for the Ballinkill Stream demonstrated a deterioration in water quality downstream of the WwTP, this was not reflected in EPA biological or chemical monitoring data for the Owenbeg River, downstream of the confluence with the Ballinakill Stream.

The Waste Assimilation Capacity assessment carried out for this study highlighted elevated levels of Orthophosphate and BOD from the discharge, above the assimilation capacity of the Ballinakill Stream during 95%ile flows. Based on EPA data for monitoring stations on the Owenbeg River upstream and downstream of the confluence with the Ballinakill Stream, there is no discernable impact from the Ballinakill WwTP affecting the SAC.

The current model assessed the WAC for the Ballinakill Stream, directly downstream of the WwTP discharge. The dilution capacity of the Ballinkill Stream at the confluence with the Owenbeg River is currently unknown. This data, coupled with monitoring data directly upstream and downstream of the confluence of these watercourses would provide a more accurate picture of the operational impact of the WwTP on the Owenbeg River, as a receiving water.

4.4 Impact on protected flora and fauna

The River Barrow and River Nore SAC is designated for the presence of protected aquatic fauna listed on Annex I1 of the EU Habitats Directive, 1992; these include Atlantic salmon, three species of lamprey, white-clawed crayfish, freshwater pearl-mussel and otter which are listed on Annex II of the EU Habitats Directive, 1992. The favourable conservation status of these species is directly dependant on the integrity of the River Nore catchment, including the Owenbeg River, with particular reference to water quality.

The above species may be potentially affected by impacts on the receiving waters from the Ballinakill WwTP; with the exception of Otter, which are not as sensitive to water quality deterioration and are unlikely to occur in the Ballinakill Stream, due to the small size of this watercourse.

The River Nore Sub-Basin Management Plan (NS2, 2009) is currently in place for the conservation of this species within the River Nore catchment. Water quality deterioration in the Owenbeg River would be expected to have a detrimental impact on the on the freshwater pearl mussel populations, recorded from the main channel of the River Nore, ca. 8km For inspection purposes only. downstream of the BallinakillConsent WwTP of copyright discharge. owner required However, for any other use.based on the chemical and biological water quality data for both the Ballinakill Stream and the Owenbeg River it is considered that the ongoing operation of the Ballinakill WwTP is having an indiscernible or imperceptible impact on water quality in the Owenbeg River and is therefore having an indiscernible impact on the freshwater pearl mussel populations in the River Nore.

Poor water quality will affect the conservation status of salmon, potentially directly affecting juvenile salmon populations in the lower reaches of the Ballinakill Stream. This species requires clean water (Q4) for spawning and early life stages.

Lamprey species have the same clean water requirements for spawning and early life stages as salmonid fish; however, juvenile lamprey (ammocetes) are more tolerant of pollution and will settle in finer sediments where they feed by filtration. They are even known to settle downstream of WwTP outfalls where nutrient inputs are higher.

No white-clawed crayfish were recorded from the Ballinakill Stream during the current sampling survey and habitat for this species limited by the small size of the watercourse. It is expected that the lower reaches of the stream and the Owenbeg River would provide more suitable habitat for this species. Water quality deterioration downstream of the WwTP discharge will negatively affect this species which requires moderate to good water quality. Based on the available data the discharge from the WwTP will be having a moderate negative impact on this species within the Ballinkill Stream. The extent of populations downstream of the confluence of the Ballinkill Stream and the Owenbeg River are not known and it is therefore not possible to assess the scale of impact on this species within the Owenbeg River

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receiving water. Based on the water quality data available, highlighthg no significant change downstream of the confluence, it is considered that there is an imperceptible impact on this species.

From the water quality data and WAC assessment carried out in the current study it is considered that the Ballinakill WwTP is resulting in a slight negative impact to both salmon and lamprey within the Ballinakill Stream. There are no discernible impacts to protected aquatic species on the Owenbeg River receiving water based on the available data. Both chemical and biological water quality data for the Owenbeg River indicates no change downstream of the confluence with the Ballinakill Stream and therefore it is concluded that the scale of impact to protected species within the Owenbeg is imperceptible.

4.5 Impact on fisheries

From the macroinvertebrate sampling exercise carried #outduring the current assessment it was found that there is little difference in the juvenile salmonid food supply in the Balinakill Stream upstream and downstream of the WwTP discharge, both being unpredictable. However, water quality downstream of the plant was found to deteriorate, based on both the Ecofact sampling data and the Laois County Council chemical water quality monitoring data. As the Ballinakill Stream is of small size and is only a second order stream it is not considered to have significant salmonid production potential.

It is expected that the lower reaches of the river, upstream of the confluence with the Owenbeg River would provide suitable habitat for salmonid species, including juvenile salmon. Therefore the current scale of impacts to the water quality in the Ballinakill Stream receiving water would be considered to result in a slight negative impact to fisheries in the Ballinakill Stream.

In the case of the Owenbeg River, data available indicates no change in water quality downstream of the Ballinakill WwTP. It is considered that there is an imperceptible impact to fisheries within this receiving water.

4.6 Impact on water abstractions

There are no drinking water abstractions on the Ballinakill Stream or the Owenbeg River, receiving waters downstream of the ForBallinakill inspection purposes WwTP. only. The WwTP therefore does not impact on any designated water abstractionConsent of copyright sites, ownerand required is attributed for any other use.an indiscernible impact i.e. no change.

4.7 Impact on recreationan areas

Neither the Ballinakill Stream nor the Owenbeg River have any designated recreational or bathing water designations and therefore the WwTP results in no change in this regard i.e. no. discernable impact.

4.8 Impact on nutrient sensitive areas

The nearest nutrient sensitive area to the Ballinakill WwTP is the main channel of the River Nore downstream of the Kilkenny (Purcellinsinch) sewage outfall, to lnistioge Bridge. This area of the Nore is located over 30 river kilometres downstream of the discharge. There will be no change to the status of this nutrient sensitive designation resulting from the Ballinakill WwTP discharge and this is attributed an indiscernible impact.

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5. RECOMMENDATIONS

It is recommended that the Owenbeg River, as well as the Ballinakill Stream be treated as receiving waters for the Ballinakill WwTP. This is because the Ballinakill Stream is too small to dilute effluent from the existing WwTP, with particular stress modeled during 95Y0ile flows. To this end, Laois Co. Co. should select suitable stations on the Owenbeg River upstream and downstream of the Ballinakill Stream confluence and monitor these stations.

Overall impact to the Ballinkill Stream receiving water is considered to be slight negative based on the low flows in the watercourse and no assimilation capacity during 95%ile flows. The recorded decline in water quality downstream of the discharge lis considered to be affecting fisheries and protected species that may be utilizing aquatic habitats within this watercourse.

The current model assessed the WAC for the Ballinakill Stream, directly downstream of the WwTP discharge. The dilution capacity of the Ballinkill Stream at the confluence with the Owenbeg River is currently unknown. The availability of this data, coupled with monitoring data directly upstream and downstream of the confluence of these watercourses would provide a more accurate picture of the operational impact of the WwTP on the Owenbeg River, as a receiving water. This would further inform future assessments on the impact of the WwTP on freshwater pearl mussels in the River Nore downstream of the Owenbeg River, as well as impacts to salmonids and white-clawed crayfish populations in the Owenbeg River.

For inspection purposes only. Consent of copyright owner required for any other use.

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REFERENCES

General references

Armitage, P. D.; Moss, D.; Wright, J. F. and Furse, M. T. (1983) The performance of a new biological water quality score system based on macroinvertebrates over a wide range of unpolluted running-water sites. Water Res., 17 (3), 333-347.

Barbour, M.T. and J.B. Stribling. 1991. Use of Habitat Assessment in Evaluating the Biological Integrity of Stream Communities. Biological Criteria: Research and Regulation: 25-38. EPA- 440/5-91-005. Washington, DC: Office of Water, US EPA

Chandler, J.R. (1970) A Biological Approach to water Quality Management. Water Poll. Cont. 69:415-421.

Clenaghan, D. (2003). Phosphorus Regulations National Implementation Report, 2003. Under the Local Government (Water Pollution) Act 1977 (Water Quality Standards for Phosphorus) Regulations, 1998 (S.I. 258 of 1998). Environmental Protection Agency.

Curtis, T.G.F. & McGough, H.N. (1988) 1 Vascular plants. The Irish Red Data Book. The Stationery Office, Dublin.

CFB (1993) Game Angling. Central Fisheries Board Irish Angling Guides. Gill and MacMillan.

DOEHLG (2008) Draft European Communities Environmental Objectives (Surface Waters) Regulations 2008. Water Framework Directive (2000/60/EC) and the Dangerous Substances Directive (2006/11/EC) Consultation Paper. Proposals for Regulations establishing Environmental Objectives and Environmental Quality Standards for the classification and management of Surface Waters and requiring the implementation of measures to reduce water pollution and protect and restore Surface Waters.

Ecofact (2005). Upper River Nore Drainage Maintenance Assessment. Ecofact Environmental Consultants Ltd., Limerick.

EPA (2001) Parameters of Water Quality - Interpretation and Standards. Environmental Protection Agency, Ireland. For inspection purposes only. Consent of copyright owner required for any other use. European Commission (1999) Interpretation manual of European Union Habitats Eur 1512. EC DG Environment, Brussels

Flora (Protection) Order 1999. Statutory Instrument No. 94 of 1999. The Stationery Office, Dublin.

Fossitt, J. (2000) A guide to habitats in Ireland. The Heritage Council, Kilkenny.

Hayden and Harrington (2000) Exploring Irish Mammals. Duchas The Heritage Service.

Lucy, J. (1998) The Barrow, The Nore and The Suir. In: Studies of Irish Rivers and lakes Ed. Christopher Moriarty. Essays on the occasion of the XXVll Congress of Societas lnternationalis Limnologias (SI L). Marine Institute. Dublin.

Lucey, J., (2007) Water Quality in Ireland 2006 - Key Indicators of the Aquatic Environment. EPA, Wexford

MacCarthaigh (1997) Hydrological data. A listing of water recorders and summary statistics at selected gauging stations. Environmental Protection Agency, Ireland.

McGarrigle, *M.L., Bowman, J.J., Clabby, K.J., Lucy, P., Cunningham, M.,MacCarthaigh, M., Keegan, M., Cantrell, B., Lehane, M., Clenaghan, C., Toner, P.F. (2002) Water Quality in Ireland 1998-2000. Second (Revised) Edition. Environmental Protection Agency.

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Neill, N. (2007) River Water Quality in , 2006. A report commissioned by Laois County Council.

Neill, N. (2008) River Water Quality in County Laois, 2007. A report commissioned by Laois County Council.

Neill, N. (2009) River Water Quality in Southeast Ireland, 2008. A report commissioned by County Councils of Carlow, kilkenny, Laois, Tippereary (N&S), Waterford and by Waterford City Council.

Nelson, B., & Thompson, R., (2004) The Natural History of lrelands Dragonflies. Ulster Museum. 454pp.

Nicholas 0’ Dwyer, 2007. Laois towns and villages wastewater improvement scheme. Five Villages Preliminary Report Volume 1. Laois County Council.

NRA (2004) Environmental Impact Assessment of National Road Schemes - A Practical Guide, National Roads Authority, Dublin

NS2 (2009). Freshwater Pearl Mussel Draff: Nore Sub-Basin Management Plan. Department of the Environment, Heritage and Local Government.

OPW Hydro-Data http://www.opw.ie/hvdro/index.asp

O’Reilly, P. (2004) Rivers of Ireland - a flyfisher’s Guide. 5‘h Ed. Merlin Unwin Books.

Preston, C. D., Pearman, D. A. and Dines, T. D., eds (2002). New Atlas offhe Brifish and lrish Flora. Oxford University Press, Oxford

Rabenil, C.F.,, Doisy, K.E. and Zweig, L.D. (2005) Stream invertebrate community functional responses to deposited sediment Journal of Aquatic Sciences. 67(4):395-402.

Toner, P., Bowman, K., Clabby, K., Lucey, J., McGarrigle, M, Concannon, C., Clenaghan, C., Cunningham, P., Delaney, J., O’Boyle, S., MaCarthaigh, M., Craig, M., and Quinn, R. 2005. Water Quality in Ireland 2001-2003. Environmental Protection Agency, Wexford. For inspection purposes only. Consent of copyright owner required for any other use. Whilde, A. (1993) Threatened mammals, birds, amphibians and fish in Ireland. lrish red data book 2: vertebrates. Belfast: HMSO.

Walley W.J. and Hawkes H.A. (1997) A computer-based development of the Biological Monitoring Working Party score system incorporating abundance rating, biotope type and indicator value. Wafer Research, 31 (2), 201-210.

Information sources on protected species

King, J.J. (2006) The status and distribution of lamprey in the River Barrow SAC. lrish Wildlife Manuals No. 21. National Parks and Wildlife Service, Department of Environment, Heritage and Local Government, Dublin, Ireland.

Kelly & King (2001) A review of the ecology and distribution of three lamprey species, Lampefra fluviatilis (L.), Lampefra planeri (Bloch), and Pefromyzon marinus (L.): A context for conservation and biodiversity considerations in Ireland. Biology and the Environment. 101B(3):165-185.

Kurz, I. and Costello, M. J. (1999). An outline of the biology, distribution and conservation of lampreys in Ireland. lrish Wildlife Manuals No. 5. Duchas, the Heritage Service, Dublin.

Lucey, J., and McGarrigle, M.L.(1987) The distribution of the crayfish Ausfropofamobius pallipes (Lereboullet) in Ireland. lrish Fisheries lnvesfigafions Series A (29): 1-13.

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Moorkens, E. A. (I999). Conservation management of the freshwater pearl mussel Margarififera margarififera. Part 1: Biology of the species and its present situation in Ireland. Irish Wildlife Manuals No. 8. Duchas, the Heritage Service, Dublin.

Reynolds, J. D. (1998). Conservation management of the white-clawed crayfish Austropotamobius pallipes. Irish Wildlife Manuals No. 1. Duchas, the Heritage Service, Dublin.

Speignt M.C.D. (1992). Status of the freshwater pearl mussels M rn and M rn durrovensis in the Nore, Barrow and Suir River tributaries, South-east Ireland Ir. Nat. J. 24(3):127-131

Information sources for identification fauna

Bass J.(1998) Last-Instar Larvae and Pupae of the Simuliidae of Britain and Ireland: a Key with Brief Ecological Notes 1998, 104pp.

Cranston P.S. (1982) A Key to the Larvae of the British Orthocladiinae (Chironomidae) 1982, 152pp + 1 plate.

Disney R.H.L. (1999) British Dixidae (Meniscus.Midges) and Thaumaleidae (Trickle Midges): @ ' Keys with Ecological Notes 1999, 128pp.

Edington J.M. & A.G. Hildrew (1995) A Revised Key to the Caseless Caddis Larvae of the British Isles, with Notes on their Ecology 1995, 134pp.

Elliott J.M. & K.H. Mann (1979) A Key to the British Freshwater Leeches, with Notes on their Life Cycles and Ecology. 1979 (reprinted 1998), 72pp.

Elliott J.M. & U.H. Humpesch (1988) A Key to the Larvae of the British Ephemeroptera, with Notes on their Ecology1983, 1Olpp + 1 plate.

Gledhill, T., D.W. Sutcliffe & W.D. Williams (1993) British Freshwater Crustacea Malacostraca: a Key with Ecological Notes 1993, 176pp.

Haslam, S., Sinker, C. & Wolsely, P. (1995) British Water Plants. Field Studies Council, Shrewsbury. For inspection purposes only. Consent of copyright owner required for any other use. Hynes H.B.N. (1977) A Key to the Adults and Nymphs of the British Stoneflies (Plecoptera), with Notes on their Ecology and Distribution. Third edition, 1977 (reprinted 1993), 92pp. @ Macan T.T. (1994) A Key to the British Fresh- and Brackish-Water Gastropods, with Notes on their Ecology Fourth edition, 1977 (reprinted 1994); 46pp.

Savage A.A. (1 989) Adults of the British Aquatic Hemiptera Heteroptera: a Key with Ecological Notes1989, 173pp.

Savage A.A. (1999) Keys to the Larvae of British Corixidael999, 56pp.

Wallace, I.D., B. Wallace & G.N. Philipson (2003) Keys to the Case-bearing Caddis Larvae of Britain and Ireland 2003, 259pp.

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PLATES

the plant.

Iiorth of the site before flowing west to join the Ballinakill stream.

1 For inspection purposes only. Consent of copyright owner required for any other use.

stre!am, c iiew upst1Y ?am:

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am.

For inspection purposes only. Consent of copyright owner required for any other use.

?afica was present at the reference site but was not

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*I

: pollution tolerant indicator was excessive at the site.

rded at both sites.

For inspection purposes only. Consent of copyright owner required for any other use.

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APPENDIX I BIOTIC INDICES

EPA River Quality Classification Scheme

The Q-values are a measure of the EPAs Biological River Quality classification system. The EPA conducts a rolling programme of biological surveys of selected rivers. The higher the biological diversity and the greater the abundance of invertebrate species sensitive to organic pollution, the higher the water quality is assumed to be, and the higher the ‘Q value’ assigned to that sampling station. The EPAs water quality classification systems are summarized below:

Table Al.l Biological River Quality Classification and River Water Quality Class System (McGarrigle et al., 2002). ‘Q’ value Community Water Condition* Status Qualitv

Class A waters are those in which problems relating to existing or potential uses are unlikely to arise. They are therefore regarded as being in a ‘satisfactory’ condition. Classes B, C and D are to a lesser or greater extent ‘unsatisfactory’ in this regard. For example, the main characteristics of Class B and C waters is eutrophication, which may interfere with the amenity, abstraction or fisheries uses of such waters. The general characteristics of waters of the various Biological Quality Classes are provided in Table Al.2.

Table A1.2 The general characteristics of waters of the various Biological Quality Classes. Quality Class A Class B Class C Class D Classes Quality Q5 Q4 434 43 Q2 Ql Ratings Pollution Pristine, Unpolluted Slight Pollution Moderate Heavy Gross Status Unpolluted Pollution Pollution Pollution Organic None None Light Considerable Heavy Excessive Waste Load Maximum Low (<3mg/l) Low (<3mg/l) Occasionally High at times Usually Usually very B.O.D. elevated For inspection purposes only. High- _____ - - - hhgh ____ - - - -. Dissolved Close to 80%-IConsent 20% of copyrightFluctuates owner required forVery any other unstable, use. Low, Very low, Oxygen 100% at all from ~80%to Potential fish- sometimes often zero times, >120% kills . ------L ------_------?!?!5J- - - ___.- - - ______- -. Annual 0.015 mgll 0.03 mgll 0.045 mgll 0.07 mgll O.lmg/l > 0.1 mg/l median PO4 Siltation None May be light May be light May be Usually Usually very considerable heavy heavy and . --- ___ - - _---_- -__ ------_--_ - - __----_-- - --__-___- _-_ --__-___ - - - - ____-_- - ______- _____ - - - anae_rpp_ic---. ‘Sewage Never Never Never Maybesome Usually May be ..Fungus’------__ ------I------ab!!dan_t- - - - ab!Rdanf- - - -. Filamentous Limited Considerable Luxuriant Excesssive Usually None Algae development growth, growths, growths, abundant diverse typically typically communities Cladophora----_------Ciadoehora --__------______Macrophytes Diverse Diverse Reduced Limited Tolerant Most communities, Communities, diversity, diversity, species tolerant limited Considerable luxuriant excessive only, may forms, growths Growths growths growths be minimal abundant diversity Water Quality Highest Fair Quality Variable DoubtfuI Poor Bad quality ------__- - _------q!!?!tY------__- - - - - _____------W!!Y ______- - --qqua!ib! - - - - __ - !4!J3!Y. :-__.____ ------. Abstraction Suitable for Suitable for all Potential Advanced Low grade Extremely Potential all problems treatment abstractio limited ------_------_- -_------_--______--_ ---_--____----?_s_-- - - ______- ______. Fishery Game Good game Game fish at Coarse Fish Fish absent Potential fisheries fisheries risk fisheries us ua II y

i

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Table AI .3 Revised BMWP (Biological Monitoring Working Party) Score Sheet. (Adapted from Walley and Hawkes,l997). Common Family Original Revised Habitat Specific Scores Name BMWP BMWP Riffles Riffle Pools Score Score pools

Flatworms Planariidae 5 4.2 45 AI U.a7I Dendrocoelidae 5 3.1 fi 76 ' Snails Neritidae - I ." ". , 0. I Y.J Viviparidae 6 6.3 2.1 4.7 7.1 Valvatidae 3 2.8 2.5 2.5 3.2 Hydrobiidae 3 3.9 4.1 3.9 3.7 Lymnaeidae 3 3.0 3.2 3.1 2.8 Physidae 3 1.8 0.9 1.5 2.8 . ------Planorbidae ------3 ------2.9------2.6------2.9 ------A.!------Limpets and Ancylidae 6 5.6 5.5 5.5 6.2 Mussels Unionidae 6 5.2 4.7 4.8 5.5 . ------Sphaeriidae ------3 - - - - - _--___-3.6- - - - - _____ - - -3.7 _____ - ___3.7 - - ___ - __ A.!------worms Oligochaeta 1 3.5 3.9 3.2 2.5 Leeches Piscicolidae 4 5.0 4.5 5.4 5.2 Glossiphoniidae 3 3.1 3.0 3.3 2.9 Hirudididae 3 0.0 0.3 -0.3 Erpobdellidae...... 3 2.8 2.8 . 2.8 2.6 , Crustaceans Asellidae 3 2.1 1.5 2.4 2.7 Corophiidae 6 6.1 5.4 5.1 6.5 Gammaridae 6 4.5 4.7 4.3 4.3 Astacidae ...... 8 9.0 8.8 9.0______?!,? ______Mayflies Siphlonuridae 10 11.0 11.0 Baetidae 4 5.3 5.5 4.8 5.1 Heptageniidae 10 9.8 9.7 10.7 13.0 Leptophlebiidae 10 8.9 8.7 8.9 9.9 Ephemerellidae 10 7.7 7.6 8.1 9.3 Potamanthidae 10 7.6 7.6 Ephemeridae 10 9.3 9.0 9.2 11.0 . ------Caenidae ------7------7.1------7.2 ------7.3 ------6.4------Stoneflies Taeniopterygidae 10 10.8 10.7 12.1 Nemouridae -7 - 9.1 9.2 8.5 8.8 Leuctridae 10 9.9 9.8 10.4 11.2 Capniidae 10 10.0 10.1 Perlodidae 10 10.7 10.8 10.7 10.9 ' Perlidae 10 12.5 12.5 12.2 Chloroperlidae...... 10 12.4 12.5 12.1 Damselflies Platycnemidae 6 5.1 3.6 5.4 5.7 Coenagriidae 6 3.5 2.6 3.3 3.8 Lestidae 8 For inspection purposes5.4 only. 5 :4 Consent of copyright owner required for any other use. Calopteygidae...... 8 6.4 6.0 6.1 7.6 Dragonflies Gomohidae 8- Cordulegasteridae 8 8.6 9.5 6.5 7.6 Aeshnidae 8 6.1 7.0 6.9 5.7 Corduliidae 8

Bugs

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Common Family Original Revised Habitat Specific Scores Name BMWP BMWP Riffles Riffle Pools Score Score pools Polycentropidae 7 8.6 8.6 8.4 8.7 Psychomyiidae 8 6.9 6.4 7.4 8.0 Hydropsychidae 5 6.6 6.6 6.5 7.2 Hydroptilidae 6 6.7 6.7 6.8 6.5 Phryganeidae 10 7.0 6.6 5.4 8.0 Limnephilidae 7 6.9 7.1 6.5 6.6 Molannidae 10 8.9 7.8 8.1 10.0 Beraeidae 10 9.0 8.3 7.8 10.0 Odontoceridae 10 10.9 10.8 11.4 11.7 Leptoceridae 10 7.8 7.8 7.7 8.1 Goeridae 10 9.9 9.8 9.6 12.4 Lepidostomatidae 10 10.4 10.3 10.7 11.6 Brachycentridae 10 9.4 9.3 9.7 11.0 ...... Sericostomatidae 10 9.2 9.1 9.3 10.3 True flies Tipulidae 5 5.5 ' 5.6 5.0 5.1 Chironomidae 2 3.7 4.1 3.4 2.8 Simuliidae 5 5.8 5.9 5.1 5.5 These families are now excluded from the list used for the calculation of the score. A blank indicates that there were insufficient records for the calculations.

The Revised BMWP Scores are based on the analysis of frequency of occurrence of the families recorded in approximately 17,000 samples. The Habitat Specific Scores are based on the following substrate compositions: Riffles: >= 70% boulders and pebbles, Pool: >= 70% sand and silt, Riffle/Pool: the remainder.

For inspection purposes only. Consent of copyright owner required for any other use.

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EPA Export 26-07-2013:14:13:58 APPENDIX 2 NPWS Designated site description

SITE NAME: RIVER BARROW AND RIVER NORE SITE CODE: 002162 1 This site consists of the freshwater stretches of the Barrow/Nore River catchments as far upstream as the and it also includes the tidal elements and estuary as far downstream as Creadun Head in Waterford. The site passes through eight counties - Offaly, Kildare, Laois, Carlow, Kilkenny, Tipperary, Wexford and Waterford. Major towns along the edge of the site include , Portarlington, Monasterevin, , Athy, Carlow, Leighlinbridge, Graiguenamanagh, New Ross, Inistioge, Thomastown, Callan, Bennettsbridge, Kilkenny and Durrow. The larger of the many tributaries include the Lerr, Fushoge, Mountain, Aughavaud, Owenass, Boherbaun and Stradbally Rivers of the Barrow and the Delour, Dinin, Erkina, Owveg, Munster, Arrigle and King’s Rivers on the Nore. Both rivers rise in the Old Red Sandstone of the Slieve Bloom Mountains before passing through a band of Carboniferous shales and sandstones. The Nore, for a large part of its course, traverses limestone plains and then Old Red Sandstone for a short stretch below Thomastown. Before joining the Barrow it runs over intrusive rocks poor in silica. The upper reaches of the Barrow also runs through limestone. The middle reaches and many of the eastern tributaries, sourced in the Blackstairs Mountains, run through Granite. The southern end, like the Nore runs over intrusive rocks poor in silica. Waterford Harbour is a deep valley excavated by glacial floodwaters when the sea level was lower than today. The coast shelves quite rapidly along much of the shore. i

The site is a candidate SAC selected for alluvial wet woodlands and petrifying springs, priority habitats on Annex I of the E.U. Habitats Directive. The site is also selected as a candidate CSAC for old oak woodlands, floating , river vegetation, estuary, tidal mudflats, Salicornia mudflats, Atlantic salt meadows, Mediterranean salt meadows, dry heath and eutrophic tall herbs, all habitats listed on Annex I of the E.U. Habitats Directive. The site is also selected for the following species listed on Annex II of the same directive - Sea Lamprey, River Lamprey, Brook Lamprey, Freshwater Pearl Mussel, Nore Freshwater Pearl Mussel, Crayfish, Twaite Shad, Atlantic Salmon, Otter, Vertigo moulinsiana and the plant Killarney Fern.

Good examples of Alluvial Forest are seen at Rathsnagadan, Murphy’s of the River, in Abbeyleix estate and along other shorter stretches of both the tidal and freshwater elements of the site. Typical species seen include Almond Willow (Salix friandra), White Willow (S. For inspection purposes only. alba), Grey Willow (S. cinerea),Consent Crack of copyright Willow owner (S. required fragilis), for any other Osier use. (S. viminalis), with Iris (Iris pseudacorus), Hemlock Water-dropwort (Oenanfhe crocafa), Angelica (Angelica sylvesfris), Thin-spiked Wood-sedge (Carex sfrigosa), Pendulous Sedge (C. pendula), Meadowsweet (Filipendula ulmaria), Valerian (Valeriana officinalis) and the Red Data Book species Nettle- leaved Bellflower (Campanula frachelium). Three rare invertebrates have been recorded in this habitat at Murphy’s of the River. These are: Neoascia obliqua (Diptera: Syrphidae), Tefanocera feyi (Diptera: Sciomyzidae) and Dicfya umbrarum (Diptera: Sciomyzidae).

A good example of petrifying springs with tufa formations occurs at Dysart Wood along the Nore. This is a rare habitat in Ireland and one listed with priority status on Annex I of the EU Habitats Directive. These hard water springs are characterised by lime encrustations, often associated with small waterfalls. A rich bryophyte flora is typical of the habitat and two diagnostic species, Crafoneuron commufafum var. commufafum and Eucladium verticillafum, have been recorded.

The best examples of old Oak woodlands are seen in the ancient Park Hill woodland in the estate at Abbeyleix; at Kyleadohir, on the Delour, Forest Wood House, Kylecorragh and Brownstown Woods on the Nore; and at Cloghristic Wood, Drummond Wood and Borris Demesne on the Barrow, though other patches occur throughout the site. Abbeyleix Woods is a large tract of mixed deciduous woodland which is one of the only remaining true ancient woodlands in Ireland. Historical records show that Park Hill has been continuously wooded since the sixteenth century and has the most complete written record of any woodland in the country. It supports a variety of woodland habitats and an exceptional diversity of species

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Receiving Water Impact Assessment: Ballinakill WwTP-June 2009

including 22 native trees, 44 bryophytes and 92 lichens. It also contains eight indicator species of ancient woodlands. Park Hill is also the site of two rare plants, Nettle-leaved Bellflower and the moss Leucodon sciuroides. It has a typical bird fauna including Jay, Long- eared Owl and Raven. A rare invertebrate, Mitostoma chrysomelas, occurs in Abbeyleix and only two other sites in the country. Two flies Chrysogaster virescens and Hybomitra rnuhlfeldi also occur. The rare Myxomycete fungus, Licea minima has been recorded from woodland at Abbeyleix.

Oak woodland covers parts of the valley side south of Woodstock and is well developed at Brownsford where the Nore takes several sharp bends. The steep valley side is covered by Oak (Quercus spp.), Holly (Ilex aguifolium), Hazel (Corylus avellana) and Birch (Betula pubescens) with some Beech (Fagus sylvatica) and Ash (Fraxinus excelsior). All the trees are regenerating through a cover of Bramble (Rubus fruticosus agg.), Foxglove (Digifalis purpurea) Wood Rush (Luzula sylvafica) and Broad Buckler-fern (Dryopteris dilafata).

On-the steeply sloping banks of the River Nore about 5 km west of New Ross, in , Kylecorragh Woods form a prominent feature in the landscape. This is an excellent example of a relatively undisturbed, relict Oak woodland with a very good tree canopy. The wood is quite damp and there is a rich and varied ground flora. At Brownstown a small, mature Oak-dominant woodland occurs, on a steep slope. There is younger woodland to the north and east of it. Regeneration throughout is evident. The understorey is similar to the woods at Brownsford. The ground flora of this woodland is developed on acidic, brown earth type soil and comprises a thick carpet of Bilberry (Vaccinium myrtillus), Heather (Calluna vulgaris), Hard Fern (Blechnum spicant), Cowwheat (Melampyrum spp.) and Bracken (Pteridiurn aguilinum).

Borris Demesne contains a very good example of a semi-natural b'road-leaved woodland in very good condition. There is quite a high degree of natural re-generation of Oak and Ash through the woodland. At the northern end of the estate Oak species predominate. Drummond Wood, also on the Barrow, consists of three blocks of deciduous woods situated on steep slopes above the river. The deciduous trees are mostly Oak species. The woods have a well established understorey of Holly (Ilex aquifolium), and the herb layer is varied, with Brambles abundant. Whitebeam (Sorbus devoniensis) has also been recorded.

Eutrophic tall herb vegetation occurs in association with the various areas of alluvial forest and elsewhere where the flood-plain of the river is intact. Characteristic species of the habitat For inspection purposes only. incl u d e Meadowswee t (FilipendulaConsent ofulmaria) copyright owner, Pu requiredrp I e Loosestfor any otherrife use. (Lyfhrum salicaria) , Marsh Ragwort (Senecio aquaticus), Ground Ivy (Glechoma hederacea) and Hedge Bindweed (Calystegia sepium). Indian Balsam (Impatiens glandulifera), an introduced and invasive species, is abundant in places. Floating River Vegetation is well represented in the Barrow and in the many tributaries of the site. In the Barrow the species found include Water Starworts (Callitriche spp.), Canadian Pondweed (Elodea canadensis), Bulbous Rush (Juncus bulbosus), Milfoil (Myriophyllurn spp.), Pofamogeton x nitens, Broad-leaved Pondweed (P. natans), Fennel Pondweed (P. pectinatus), Perfoliated Pondweed (P. perfoliatus) and Crowfoots (Ranunculus spp.). The water quality of the Barrow has improved since the vegetation survey was carried out (EPA, 1996).

Dry Heath at the site occurs in pockets along the steep valley sides of the rivers especially in the Barrow Valley and along the Barrow tributaries where they occur in the foothills of the Blackstairs Mountains. The dry heath vegetation along the slopes of the river bank consists of Bracken (Pteridiurn aquilinum) and Gorse (Ulex europaeus) species with patches of acidic grassland vegetation. Additional typical species include Heath Bedstraw (Galium saxatile), Foxglove (Digitalis purpurea), Common Sorrel (Rumex acetosa) and Bent Grass (Agrostis stolonifera). On the steep slopes above New Ross the Red Data Book species Greater Broomrape (Orobanche rapum-genistae) has been recorded. Where rocky outcrops are shown on the maps Bilberry (Vaccinium mydillus) and Wood Rush (Luzula sylvatica) are present. At Ballyhack a small area of dry heath is interspersed with patches of lowland dry grassland. These support a number of Clover species including the legally protected Clustered Clover (Trifolium glomeratum) - a species known from only one other site in Ireland. This grassland community is especially well developed on the west side of the mud-capped

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EPA Export 26-07-2013:14:13:58 Receiving Water Impact Assessment: Ballinakill WwTP-June 2009 ...... walls by the road. On the east of the cliffs a group of rock-dwelling species occur, i.e. English Stonecrop (Sedum anglicum), Sheep's-bit (Jasione montana) and Wild Madder (Rubia peregrina). These rocks also support good lichen and moss assemblages with Ramalina subfarinacea and Hedwigia Ciliata.

Dry Heath at the site generally grades into wet woodland or wet swamp vegetation lower down the slopes on the river bank. Close to the Blackstairs Mountains, in the foothills associated with the Aughnabrisky, Aughavaud and Mountain Rivers there are small patches of wet heath dominated by Purple Moor-grass (Molinia caerulea) with Heather (Calluna vulgaris), Tormentil (Potentilla erecta), Carnation Sedge (Carex panicea) and Bell Heather (Erica cinerea).

Saltmeadows occur at the southern section of the site in old meadows where the embankment has been breached, along the tidal stretches of in-flowing rivers below Stokestown House, in a narrow band on the channel side of Common Reed (Phragmites) beds and in narrow fragmented strips along the open shoreline. In the larger areas of salt meadow, notably at Carrickcloney, Ballinlaw Ferry and Rochestown on the west bank; Fisherstown, Alderton and Great Island to Dunbrody on the east bank, the Atlantic and Mediterranean sub types are generally intermixed. At the upper edge of the salt meadow in the narrow ecotonal areas bordering the grasslands where there is significant percolation of salt water, the legally protected species Borrer's Saltmarsh-grass (Puccinellia fasciculata) and Meadow Barley (Hordeum secalinum) (Flora Protection Order, 1987) are found. The very rare Divided Sedge (Carex divisa) is also found. Sea Rush (Juncus maritimus) is also present. Other plants recorded and associated with salt meadows include Sea Aster (Aster tripolium), Sea Thrift (Armeria maritima), Sea Couch (Elymus pycnanthus), Spear-leaved Orache (Atriplex prostrata), Lesser Sea-spurrey (Spergularia marina), Sea Arrowgrass ( Triglochin maritima) and Sea Plantain (Plantago maritima).

Salicornia and other annuals colonising mud and sand are found in the creeks of the saltmarshes and at the seaward edges of them. The habitat also occurs in small amounts on some stretches of the shore free of stones,

The estuary and the other Habitats Directive Annex I habitats within it form a large component of the site. Extensive areas of intertidal flats, comprised of substrates ranging from fine, silty mud to coarse sand with pebbleslstones are present. Good quality intertidal sand and mudflats have developed on a linear shelf on the western side of Waterford Harbour, For inspection purposes only. extending for over 6 km from northConsent to of southcopyright betweenowner required Passage for any other Eastuse. and Creadaun Head, and in places are over 1 km wide. The sediments are mostly firm sands, though grade into muddy sands towards the upper shore. They have a typical macro-invertebrate fauna, characterised by polychaetes and bivalves. Common species include Arenicola marina, Nephtys hombergii, Scoloplos armiger, Lanice conchilega and Cerastoderma edule.

The western shore of the harbour is generally stony and backed by low cliffs of glacial drift. At Woodstown there is a sandy beach, now much influenced by recreation pressure and erosion. Behind it a lagoonal marsh has been impounded which runs westwards from Gaultiere Lodge along the course of a slow stream. An extensive reedbed occurs here. At the edges is a tall fen dominated by sedges (Carex spp.), Meadowsweet, Willowherb (Epilobium spp.) and rushes (Juncus spp.). Wet woodland also occurs. This area supports populations of typical waterbirds including Mallard, Snipe, Sedge Warbler and Water Rail.

The dunes which fringe the strand at Duncannon are dominated by Marram grass (Ammophila arenaria) towards the sea. Other species present include Wild Sage (Salvia verbenaca), a rare Red Data Book species. The rocks around Duncannon ford have a rich flora of seaweeds typical of a moderately exposed shore and the cliffs themselves support a number of coastal species on ledges, including Thrift (Armeria maritima), Rock Samphire (Crithmum maritimum) and Buck's-horn Plantain (Plantago coronopus).

Other habitats which occur throughout the site include wet grassland, marsh, reed swamp, improved grassland, arable land, quarries, coniferous plantations, deciduous woodland, scrub and ponds.

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EPA Export 26-07-2013:14:13:58 Seventeen Red Data Book plant species have been recorded within the site, most in the recent past. These are Killarney Fern (Trichomanes speciosum), Divided Sedge (Carex divisa), Clustered Clover (Trifolium glomerafum), Basil Thyme (Acinos arvensis), Hemp nettle (Galeopsis angusfifolia), Borrer’s Saltmarsh Grass (Puccinellia fasiculafa), Meadow Barley (Hordeum secalinum), Opposite-leaved Pondweed (Groenlandia densa), Autumn Crocus (Colchicum aufumnale), Wild Sage (Salvia verbenaca), Nettle-leaved Bellflower (Campanula frachelium), Saw-wort (Serrafula fincforia), Bird Cherry (Prunus padus), Blue Fleabane (Erigeron acer), Fly Orchid (Ophrys insectifera), Broomrape (Orobanche hederae) and Greater Broomrape (Orobanche rapum-genistae). Of these the first nine are protected under the Flora Protection Order 1999. Divided Sedge (Carex divisa) was thought to be extinct but has been found in a few locations in the site since 1990. In addition plants which do not have a very wide distribution in the country are found in the site including Thin-spiked Wood-sedge (Carex sfrigosa), Field Garlic (Allium oleraceum) and Summer Snowflake (Leucojum aesfivum). Six rare lichens, indicators of ancient woodland, are found including Lobaria laefevirens and L. pulmonaria. The rare moss Leucodon sciuroides also occurs.

The site is very important for the presence of a number’of EU Habitats Directive Annex II animal species including Freshwater Pearl Mussel (Margarififera margarififera and M. m. durrovensis), Freshwater Crayfish (Ausfropotamobiuspallipes), Salmon (Salmo salar), Twaite Shad (Alosa fallax fallax), three Lamprey species - Sea (Pefromyzon marinus), Brook (Lampefra planer0 and River (Lampefra fluviafilis), the marsh snail Vertigo moulinsiana and Otter (Lufra lufra). This is the only site in the world for the hard water form of the Pearl Mussel M. m. durrovensis and one of only a handful of spawning grounds in the country for Twaite Shad. The freshwater stretches of the River Nore main channel is a designated salmonid river. The BarrowINore is mainly a grilse fishery though spring salmon fishing is good in the vicinity of Thomastown and lnistioge on the Nore. The upper stretches of the Barrow and Nore, particularly the Owenass River, are very important for spawning.

The site supports many other important animal species. Those which are listed in the Irish Red Data Book include Daubenton’s Bat (Myofis daubenfoni), Badger. (Meles meles), Irish Hare (Lepus fimidus hibernicus) and Frog (Ram temporaria). The rare Red Data Book fish species Smelt (Osmerus eperlanus) occurs in estuarine’ stretches of the site. In addition to the Freshwater Pearl Mussel, the site also supports two other freshwater Mussel species, Anodonfa anafina and A. cygnea.

The site is of ornithological importance for a number of E.U. Birds Directive Annex I species For inspection purposes only. including Greenland White-frontedConsent Goose, of copyright Whooper owner required Swan, for any otherBewick’s use. Swan, Bartailed Godwit, Peregrine and Kingfisher. Nationally important numbers of Golden Plover and Bar-tailed Godwit are found during the winter. Wintering flocks of migratory birds are seen in Marsh and the Curragh and Goul Marsh, both in Co. Laois and also along the Barrow Estuary in Waterford Harbour. There is also an extensive autumnal roosting site in the reedbeds of the Barrow Estuary used by Swallows before they leave the country.

Landuse at the site consists mainly of agricultural activities - many intensive, principally grazing and silage production. Slurry is spread over much .of this area. Arable crops are also grown. The spreading of slurry and fertiliser poses a threat to the water quality of the salmonid river and to the populations of Habitats Directive Annex II animal species within the site. Many of the woodlands along the rivers belong to old estates and support many non-native species. Little active woodland management occurs.

Fishing is a main tourist attraction along stretches of the main rivers and their tributaries and there are a number of Angler Associations, some with a number of beats. Fishing stands and styles have been erected in places. Both commercial and leisure fishing takes place on the rivers. There is net fishing in the estuary and a mussel bed also. Other recreational activities such as boating, golfing and walking, particularly along the Barrow towpath are also popular. There is a golf course on the banks of the Nore at Mount Juliet and GAA pitches on the banks at lnistioge and Thomastown. There are active and disused sand and gravel pits throughout the site. Several industrial developments, which discharge into the river, border the site. New Ross is an important shipping port. Shipping to and from Waterford and Belview ports also passes through the estuary.

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The main threats to the site and current damaging activities include high inputs of nutrients into the river system from agricultural run-off and several sewage plants, overgrazing within the woodland areas, and invasion by non-native species, for example Cherry Laurel and b Rhododendron (Rhododendron ponficum). The water quality of the site remains vulnerable. Good quality water is necessary to maintain the populations of the Annex II animal species listed above. Good quality is dependent on controlling fertilisation of the grasslands, particularly along the Nore. It also requires that sewage be properly treated before discharge. Drainage activities in the catchment can lead to flash floods which can damage the many Annex II species present. Capital and maintenance dredging within the lower reaches of the system pose a threat to migrating fish species such as lamprey and shad. Land reclamation also poses a threat to the salt meadows and the populations of legally protected species therein. J Overall, the site is of considerable conservation significance for the occurrence of good examples of habitats and of populations of plant and animal species that are listed on Annexes I and II of the E.U. Habitats Directive respectively. Furthermore it is of high conservation value for the populations of bird species that use it. The occurrence of several Red Data Book plant species including three rare plants in the salt meadows and the population of the hard water form of the Pearl Mussel which is limited to a 10 km stretch of the Nore, add further interest to this site.

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Regulations_----__---____--______(1988) limit value is 5mg& - - - - - Total ammonia (mg N I- ) >O.l (or >0.3) Strict value taken from EPA (ZOOI), levels above 0.3 mgll would be harmful. However, EPA (2001) notes that these limits may be unduly low in certain circumstances. Limit of Imgll given in ...... Salmonid Water Regulations ______(1 ____ 988): ------Un-ionised ammonia >0.02 Salmonid Water Regulations (1988) -(mg_--_____ NH3 I 1'2 ...... - ...... Nitrate as NOsmgll ~ >2 This is a strict limit value suggested in Lucey (2007) for protecting sensitive aquatic species. Limit of 1.7mgll required to protect Pearl Mussels. Limit of 50 mgll given in Surface water Regulations______(1989). Nitrite as NOzmg/l >0.01 Strict value taken from Freshwater Fish Directive 781659/EEC for salmonids. Value of 0.05 aiven

Table A3.2 Summary water quality results for the upstream (local station 8702) and downstream (local station 02) monitoring stations at the Ballinakill WwTP during the period October 2006 -April 2009. Derived from data SuDDlied.. by Laois County Council. Values For inspection considered purposes to be only. elevated are highlighted in bold. Consent of copyright owner required for any other use. Parameter Location Maximum Minimum N Median Mean % difference

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APPENDIX 4 Biological water quality assessment (2009)

Table A4.1 Biological water quality assessment results. Macroinvertebratesrecorded during the kick sampling survey upstream and downstream of the Ballinakill WwTP oufall. May 2009.

Pollution Functional group Numbers sensitivity Reference Receptor group MAYFLIES (Ephemeroptera) Family Heptagenidae Rhithrogena semicolorata A Scraper/gathering collector 1 Familv Baetidae

Amphipoda (Gammaridae) Gammarus duebeni C Shredder 120 400 lsopoda (Asellidae)

Asellus aquaticus__--___-___-___-___-______------.------D Shredder 34 2 LEECHES (Hirudinae) Familv Eroobdellidae ' Erpobdella testacea DFor inspection purposes only. Predator 1 1 SEGMENTED WORMS (Annelida) Consent of copyright owner required for any other use. Family Lumbricidae D Gathering collector 4 Total number of organisms 230 517 Number of different families 12 IO Q value I 4 3-4

Quality______--..~-~.----.------.~~-..~-~.~---.~---.~--..------.--- class A B BMWP score 62.4 39.6 AS PT 5.7 4 SSRS 6.4 3.2 SSRS category 'at risk' 'at risk' Status Moderate Poor *Present (1 or 2 individuals), "*Scarce/Few (<1%), "*Small Numbers (<5%), *"*Fair Numbers (5-1O%), *****Common (10-20%), ***'**Numerous (25-50%), ***'***Dominant (50-75%), ********Excessive (>75%).

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