Chapter 11 - Freshwater Fish And Fish Habitat

11. Freshwater Fish And Fish Habitat
"We would eat mostly fish and partridge in the winter. I remember being very small and fishing through the ice. There was the place called Kapukanapent (The Place to Put Nets Through the Ice) at Emish. We would get plenty of charr even in the middle of the day." (Dominic Pokue, The Voisey's Bay News, October 1996:18)

Fish are an important food resource in northern Labrador, both for human consumption and for other top carnivores, such as bear, otter and osprey. Arctic charr and brook trout are the primary freshwater fish resources in the Landscape Region. The health of fish and fish habitat may be used as an indicator of the health of the entire aquatic ecosystem. This chapter will focus on Arctic charr and brook trout, as they will serve as sentinel species to reflect the general well-being of fish and fish habitat.

The approach to the assessment of environmental effects on fish and fish habitat is different than that for water quality. The criteria for evaluating potential changes in water quality were derived from the various regulations that apply, as well as toxicological data that are the foundation of many of the existing guidelines, such as those for the Protection Of Freshwater Aquatic Life. A more ecological approach has been used to evaluate changes that may affect fish and fish habitat. The two approaches are further explained in Methods (Section 11.1.2).

11.1 Existing Environment
The freshwater habitat in the Landscape Region consists of a few large lakes, numerous small ponds and streams and rivers that flow to the Labrador Sea. Moving inland from the coast, the topography of the area is characterized by abrupt increases in elevation. Steep cliffs are common along headlands, while long valleys often extend inland at the heads of bays. The watersheds, starting high in the hills, cross two distinct ecological landscapes before they meet the sea:

high uplands with exposed bedrock and little or no vegetation (i.e., Saglek/Hopedale and Central Ranges Land Regions, defined in Chapter 2, Volume 2); and
low-lying sheltered valleys with vegetation on an overburden of glacial sand and gravel, with some areas of organic material (i.e., Fraser River Land Region, defined in Chapter 2, Volume 2).

The high upland areas are dominated by exposed bedrock knolls and sparsely vegetated barrens, which form the upper parts of the watersheds within the Landscape Region. These areas typically have low terrestrial and aquatic productivity due to limited soil cover, low availability of nutrients and generally harsh climatic conditions. Fish habitat in the upper ponds and streams is limited due to seasonal low flows, steep inclines, harsh ice conditions, low energy inputs, and few food resources.

In contrast, the low lying valleys contain deep glaciofluvial deposits of sands, gravel and cobble, and are well vegetated with spruce forests, wetlands, and alder/birch thickets. These valleys support the most productive aquatic and terrestrial ecosystems in the Landscape Region. As tributaries flow through the vegetated valleys, energy and nutrients are picked up and transported downstream. These streams provide habitat for emerging insects whose aquatic life stages are a critical component of stream and pond ecosystems. Larger streams and rivers with permanent flow and relatively high levels of productivity occur along the valley bottoms, winding through the deep sands and gravel.

The dominant valley within the Landscape Region extends inland from Voisey's Bay, and contains the Ikadlivik-Kogloktokuluk-Reid Brook system. Flowing into Voisey's Bay, the streams transport nutrients and sediments, which are then deposited on the estuarine delta. The combination of marine, estuarine and freshwater environments provides habitat for anadromous fish species and creates one of the ecologically richest areas within the Landscape Region relative to other areas in the same region.

Inuit have commented on the "comparatively rich and diversified ecosystem" in reference to Voisey's Bay (Williamson 1997).

The freshwater ecosystem is a balance of biotic and physical influences, driven by solar energy and nutrient inputs. A schematic of an aquatic ecosystem typical of the Landscape Region is provided in Figure 11.1. The cycles of energy input, primary and secondary productivity, and decomposition are shown as simple cycles. During primary production, new organic mass is formed by photosynthesis (e.g., by algae or phytoplankton). This process provides the foundation for subsequent productivity; new organic mass provides a direct food source for secondary producers such as zooplankton. The secondary producers are themselves eaten by higher trophic levels, such as aquatic insects and fish. Because photosynthesis requires both sunlight and nutrients, it is the nutrient sources resulting from direct leaching, biological decomposition and chemical degradation that often limit the productivity of aquatic ecosystems. Figure 11.1 more closely represents pond habitat, which operates as a semi-closed system. Streams, on the other hand, may have further simplified cycles that include less primary productivity and zooplankton. Streams represent flow-through systems, with more variation in nutrient availability, temperature, and biomass (e.g., seasonal fish migrations).

"Anadromous" fish are those which feed in salt water and move up rivers from the sea to spawn.

At the centre of the figure and top of the food chain are the predatory consumers, which are represented by Arctic charr and brook trout. These two species eat a variety of invertebrates and fish, are distributed throughout the Landscape Region, and exist as both anadromous and landlocked (resident) forms. Anadromous forms use the freshwater environment for spawning, rearing and overwintering, and return to the estuarine and marine environments (e.g., Voisey's Bay) to feed during the summer months. Their populations tend to be associated with the marine bay used during the summer months and the main channels of the streams used for spawning and overwintering. As both anadromous Arctic charr and brook trout have very similar life cycles (e.g., timing of migration and use of habitat), any information and assessment provided for anadromous Arctic charr will to be similar for anadromous brook trout. Landlocked forms carry out their entire life cycle in freshwater and, therefore, are individual populations within individual ponds.

Figure 11.1 Simplified Typical Aquatic Ecosystem
"The bottom of Nain Bay is the most favoured fishing place in the spring, mainly because of its proximity to Nain. It is therefore under considerable pressure. Some informants believe that this area is being over fished." (Williamson 1997:45)

Arctic charr and brook trout are also the principal exploited freshwater resources in the Landscape Region. Both are traditionally harvested opportunistically as country foods supporting subsistence lifestyles (Brice-Bennett 1977; Williamson 1997). Anadromous stocks of Arctic charr (Nain stock and Vouisey's Bay stock) have been commercially harvested within the Region for several decades. More recently, both species have also supported recreational harvesting (including outfitter operations).

11.1.1 Environmental Assessment Boundaries
Capitalized terms used (such as Landscape Region and VBNC Claim Block) may be defined in other chapters. Some terms and phrases used may have different definitions in other chapters depending upon the context in which they are used; for example, the Assessment Area.

The Freshwater Fish and Fish Habitat Assessment Area boundaries are defined by watershed boundaries or, in the case of anadromous Arctic charr and brook trout, combinations of watersheds that discharge into a common marine bay. Watersheds act to limit the movements of fish and aquatic organisms, with the exception of emergent insects which leave the aquatic environment. Insect distributions will be limited by habitat characteristics such as water quantity and quality, temperature, flow, substrate, predation, food and cover. The distribution of larval aquatic stages is widespread but patchy.

Project activities will interact with freshwater habitat, thus affecting resident fish populations, anadromous brook trout and a portion of the anadromous Voisey's Bay Arctic charr stock. The environmental assessment boundary for freshwater fish and fish habitat includes:

year-round resident fish or seasonal anadromous fish that occupy nine watersheds (< a href="f112.gif">Figure 11.2) and that may experience project-induced environmental effects; and
adult anadromous fish that may occupy five marine environments downstream of Project activities during June-August.

"Equally, you will see the lines inland [on a map] most of them encompass the watershed area which is of concern to people especially for those rivers that bear, Arctic charr and spawning areas. So they would include all of the rivers flowing into Voisey's Bay and Anaktalak and Anktalkik." (Tony Williamson, Panel scoping meeting in Nain, April 17, 1997)

Eight of these watersheds comprise the Freshwater Fish and Fish Habitat Assessment Area, within which the potential environmental effects of the Project on habitat will be assessed. The ninth watershed, Kogluktokoluk-Ikadlivik Brooks, is included within the Freshwater Fish and Fish Habitat Assessment Area boundary by virtue of the anadromous and freshwater migrations by Arctic charr and brook trout populations as described in this chapter. The watersheds are divided into five drainage areas (Voisey's Bay, Kangeklualuk Bay, Kangeklukuluk Bay, Throat Bay and Anaktalak Bay).

A detailed description of each of these watersheds, including the existing and future water quality, is provided in Chapter 10.

Figure 11.2 Assessment Area for Freshwater Fish and Fish Habitat

11.1.1.1 Administrative Boundaries
Applicable federal and provincial water quality regulations and guidelines are summarized in Chapter 10 (Table 10.2).

Under the Fisheries Act, the Department of Fisheries and Oceans (DFO) regulates all instream and near-stream activities that can affect fish habitat. DFO must make a determination as to whether there will be harmful alteration, disruption or destruction of fish habitat due to Project activities or if there is a requirement for a Navigable Waters Protection Act (NWPA) permit. The Newfoundland Fishery Regulations, under the federal Fisheries Act, require that information be provided to DFO prior to activities affecting fish habitat.

The assessment of the environmental effects on the aquatic habitat in the Landscape Region includes consideration of effects related to deleterious substances that may be introduced via Project activities. These activities are regulated by the Fisheries Act: Metal Mining Liquid Effluent Regulations (MMLER) regulate the following substances from mine operations or processes: total suspended solids, pH, arsenic, copper, lead, nickel, zinc, and radium 226.

Radium 226 is not an issue associated with the Project. Thiosalts may affect the natural environment (Chapter 10, Appendix B). A CANMET consortium has been established to examine this issue; VBNC is an active participant, supporting the research being undertaken. AQUAMIN (1996) has also recommended the addition of cyanide for regulation under MMLER and monitoring of total ammonia and thiosalts. Since cyanide is not relevant to the Project, it is not addressed in this assessment.

In Newfoundland, total suspended solids (TSS) in freshwater is controlled by regulations under the federal Fisheries Act (MMLER), and the provincial Environmental Control (Water and Sewage) Regulations, 1980.

In Chapter 10, water quality was discussed and assessed in regard to aluminum, arsenic, cadmium, cobalt, copper, iron, lead, nickel, zinc, ammonia, pH, and TSS. However, as it was determined that pH, ammonia and iron did not require futher assessment, these parameters are not considered in this chapter.

11.1.1.2 Technical Boundaries
Technical boundaries for the assessment of freshwater fish and fish habitat are outlined below.

Arctic charr have been studied extensively in the marine environment by DFO (e.g., Andrews and Lear 1956; Dempson and Green 1985; Dempson and Kristofferson 1987; Dempson 1995), and for this reason, marine sampling was not included in the 1995 and 1996 field studies. This information has been compiled and included in the Freshwater Fish and Fish Habitat Technical Data Report (TDR) (JWEL 1997a).
Generally, most biological data collection has been conducted during the ice-free season. However, radio telemetry of Arctic charr occurred throughout the winter of 1996-97.

11.1.2 Methods
Numerous field studies were undertaken in 1995, 1996 and 1997. The existing conditions in the Assessment Area can be described in terms of trophic levels in the aquatic habitat. For this component, several elements of the aquatic environment were studied, including stream hydrology, pond bathymetry, water quality, sediment quality, primary productivity, benthic macroinvertebrates, and fish and fish habitat. These studies are summarized in the following sections and fully detailed, with methods, results and interpretation, in the various Technical Data Reports (see below). The data collected were augmented with reviews from published sources and Aboriginal knowledge (Williamson 1997).

Streamflow sampling occurred at five permanent hydrometric data collection stations, three of which were established during 1995, and two in 1996, all of which continue to operate. Seven temporary hydrometric recording stations were operated through the 1996 open water season. The locations of the hydrometric stations are provided in Chapter 10 (Figure 10.5). Full results are presented in JWEL (1997b).

Water sampling was conducted in streams in 1995-1997, and in ponds in 1996 and 1997 at various locations within the Assessment Area. Water was collected by hand from stream surface water grab samples, and with a Niskin sampler for pond water samples collected at various depths. Water samples were then sent to an analytical laboratory for analysis. In the field, water quality measurements, including pH, conductivity, temperature and oxygen, were determined with appropriate meters. The results of the water quality program are summarized in Chapter 10 and full details on methods and results are included in JWEL (1997c).

Sediment sampling was conducted in 1996 and 1997 at all stream and pond water quality stations. Samples were collected using a gravity corer and were analysed for sediment chemistry, particle size distribution, total organic carbon (TOC) and sediment toxicity. Pond samples were collected at the same time and location as water column samples and macroinvertebrate samples. The synoptic sampling for chemistry, infauna and toxicity provided data that will act as a tool for evaluating existing conditions and changes that may take place over time. Full details on sampling and analysis techniques are included in JWEL (1997c).

Primary production sampling occurred at selected ponds within the Landscape Region in 1995 and 1996. Using a variety of field and analytical methods, the study documented rates of photosynthesis, zooplankton and phytoplankton community structure and abundance, water chemistry and nutrient availability. Both primary and secondary production in a number of watersheds were determined. Full methods and results are presented in JWEL (1997d).

Stream macroinvertebrate sampling was conducted in 1996 and 1997 at the water/ sediment sampling stations using a surber sampler. Stream benthos were collected twice during 1996 in order to detect temporal variation: in mid-July and in late-August. Full results, summaries and statistical analyses are presented in JWEL (1997e).

Pond macroinvertebrate samples were collected with an Ekman grab in 1996 and 1997 at the water/sediment sampling stations. Both deep (greater than 10 m) and shallow (less than 10 m) stations were sampled. Deep stations may be used to characterize the general trophic status of a waterbody, while shallow stations are used as feeding areas by fish. Complete methodology and results are found in JWEL (1997e).

Fish were sampled during 1995, 1996 and 1997 using fyke nets, Arctic charr traps, gillnets, seines and electrofishing gear. Emphasis was put on catch-measure-release sampling: only those fish required for detailed study of body burden contaminant analysis were retained. For the body burden study, muscle and liver tissues were collected and analysed for trace metals. Retained samples were also studied for age, sex, state of maturity, stomach contents, and incidental observations of disease and parasitic infection. Full descriptions of fish and fish habitat are contained in JWEL (1997a).

In addition, radiotelemetry work was carried out on anadromous Arctic charr within the Reid Brook-Ikadlivik Brook-Kogluktokoluk Brook system. This system contains a high proportion of the available freshwater habitat for the Voisey's Bay Arctic charr stock. The radiotelemetry study consisted of surgical implantation of radio transmitters into adult anadromous Arctic charr, followed by monitoring of movements using manual and permanent tracking stations from August 1996 to November 1997. A total of 130 fish were radio-tagged, 105 in Reid Brook and 25 in Ikadlivik Brook in 1996 (August to October). A description of methods and the results of 1996 are contained in JWEL (1997a).

Environmental effects to freshwater fish associated with the uptake and bioaccumulation of metals were evaluated using a risk assessment model (Beak International Incorporated 1997).In Chapter 10, water quality was modelled during the different Project phases including a prolonged post-decommissioning phase. Contaminant characterizations were used to define the point sources and the model projected concentrations of metals at different downstream locations. These concentrations were compared with guidelines and toxicological criteria in order to assign environmental effects ratings. The toxicological criteria were for those of brook trout as a representative salmonid (predatory consumer), and Daphnia, as a fairly sensitive pelagic short-lived invertebrate (secondary producer). There is extensive literature on both of these subjects and both occur in the Assessment Area.

Landlocked Arctic charr were modelled as a representative sentinel species of local freshwater streams and ponds. The characterizations based on Arctic charr will also apply to brook trout, as it has similar biological attributes. In addition, to assess potential environmental effect to fish habitat, a representative benthic invertebrate, freshwater snail, was also modelled to represent a food source (and thus habitat) for fish. The snail, being a benthic organism, would be sensitive to sediment chemistry, which is a component of fish habitat.

The model considered six metals (nickel, copper, cobalt, zinc, lead and cadmium) based on contaminant source characterizations (Table 10.15 in Chapter 10) and biological sensitivity. The environmental effects of aluminium on Arctic charr was assessed based on water quality criteria in Chapter 10 (Table 10.27). The environmental effects of aluminum on snails was not assessed as aluminum is a relatively important constituent of most sediments and relatively small increases in water concentrations will not translate into corresponding increases in exposure.

Arctic charr and snails were evaluated across the Assessment Area in thirteen locations corresponding to locations downstream of potential sources (i.e., tailing basin, Headwater Pond and the open pit).

Potential Sources	Downstream Locations
Otter Pond	Reid Brook
Camp Pond	Reid Brook
Camp Brook	Reid Brook
Reid Brook at the mouth	Reid Brook
Pond 70	Throat Bay Brook
Pond 71	Throat Bay Brook
downstream of Dam 3	Pond 67 Brook
upstream of Pond 67	Pond 67 Brook
Pond 67	Pond 67 Brook
downstream of Dam 6	Option 5 Brook
Pond 58	Option 5 Brook
downstream of Dam 2	North Tailings Basin Brook
downstream Pond 57	North Tailings Basin Brook

The fish and snails were assumed to reside year round in these locations.

The model predicted hazard quotients (HQ), which were based on benchmark concentrations where chronic water quality criteria for the protection of fish and aquatic life (CCME 1995) were used for charr, and threshold sediment quality values were used for freshwater snails (Beak International Incorporated 1997). The HQ represents the ratio of the predicted concentration to the benchmark concentration. An HQ equal to, or greater than one, indicates a predicted concentration equal to or greater than the benchmark concentration. Therefore, an HQ of less than one may be interpreted as representing a concentration which will not have an observable environmental effect on fish or snails.

In deriving the HQ, the model uses a bioconcentration factor (BCF) which takes into account food uptake (fish eating Daphnia or snails for example) and factors such as biomagnification. Thus it is possible that a range of environmental effects on water quality may not translate directly to effects on biota because of factors such as contact with sediment, biomagnification and the form of introduced contaminants. The reverse is also true where environmental effects on biota may not have coincident environmental effects on water quality.

Arctic charr were also modelled for environmental effects in the marine environment, which they occupy for two to three months a year.

11.1.3 Existing Conditions
The dominant influence on fish and fish habitat is water, both as the medium for aquatic habitat and as a transport mechanism. Events and processes that may have influenced water quality over the past five decades, including acid rain and increased human presence, are discussed in Chapter 10. The influence of acid rain on aquatic ecosystems is manifested as changes in pH and related water chemistry in a manner that may suppress trophic components or entire food chains in freshwater. As stated in Chapter 10, the ponds and streams in the Landscape Region are weakly buffered and susceptible to those changes.

In the freshwater environment of the Assessment Area, few apparent human disturbances have occurred within the nine watersheds. The data collected on species composition and distribution, water and sediment quality, macroinvertebrates and primary productivity represent a natural, healthy ecosystem. The data may be used to determine spatial and temporal population boundaries, document habitat use and quality, and identify critical habitats.

This drier-than-normal weather was also observed and noted by local Inuit (Williamson 1997).

Natural occurrences that would influence fish distribution or habitat quality include relatively high magnitude disturbances such as alterations to hydrological conditions (e.g. long term drought) or catastrophes such as landslides, which may block passage to certain parts of watersheds. Long-term hydrometric and weather data indicate that precipitation levels during field studies lie at or near the low end of the natural cycle. The fact that the conditions observed during the field studies represent low flow is important in providing accurate data for the modelling of environmental effects on water quality (Chapter 10), and for documenting conditions when habitat would be most restricted.

Only fish abundance, primarily of anadromous Arctic charr stocks, appears to have been altered by historic and current fishing activities. Historically, the anadromous stock was harvested for subsistence, in the marine environment during spawning runs and while overwintering in ponds. Commercial fishing of the anadromous stock has occurred for approximately 50 years, peaking following the construction of the fish plant in Nain in 1971. Voisey's Bay Arctic charr decreased in both abundance and size between the early 1970s and 1993, after which commercial fishing pressure was drastically reduced. Since that time the Arctic charr populations are reported to be slowly recovering (Williamson 1997). The size and abundance of anadromous Arctic charr observed during this study, compared to historical data, reflect the depressed state of the stock.

Although resident populations of brook trout, charr and lake trout continue to be harvested for subsistence, there is no indication that fishing pressure during the past several years has been higher than normal.

Exploration activity would have localized environmental effects on the aquatic environment, consisting primarily of increase in TSS. This may cause localized habitat avoidance by fish. However, exploration activities are not expected to have long term environmental effects due to the small area affected during drilling. Some activities typical of exploration are:

aircraft landing on Camp Pond;
docking, camp facilities on Camp Pond; and
snowmobile traffic, drill rig movements.

11.1.3.1 Aquatic Habitat
"The well being of the fish population of these river systems depends on the health of the watershed ecosystems as well as the marine and estuarine waters through which species must migrate to enter the rivers." (Naskapi Band of Quebec, Comments on Draft EIS Guidelines for the Review of the Voisey's Bay Mine and Mill Project, May 13, 1997:15)

The freshwater ecosystem within the Assessement Area is characterized as oligotrophic (low in nutrient inputs with low organic production) and harsh with regard to water conditions. Although the cold, nutrient poor environment supports many trophic levels, including fish, densities of individuals and species are generally low. These ecosystems are quite resilient to natural changes in the environment, with many species well adapted to the environmental conditions expected in Central and Northern Labrador. However, these ecosystems can be very sensitive to other changes. Because of low productivity and slow growth, long-lived species, such as Arctic charr, may be slow to recover from natural or anthropogenic perturbations. Low population densities may result in slow re-colonization of temporarily disturbed habitats.

The watersheds within the Landscape Region show the diverse nature of the two dominant ecosystems: high barrens and vegetated low valleys. Aquatic life in the lower part of the watersheds is richer in abundance and diversity than in the upper headwaters, or in some of the smaller surrounding watersheds.

Inuit have commented on the "comparatively rich and diversified ecosystem" in reference to Voisey's Bay of which the Ikadlivik and Reid Brook systems drain into (Williamson 1997).

Within the Landscape Region, the valleys associated with the Reid Brook-Ikadlivik-Kogluktokuluk Brook system are ecologically relatively rich for subarctic conditions. At these lower, sheltered elevations, these streams carve through thick glacial deposits of sand, gravel and cobble, which sustain spruce forests and the development of wetlands. The streams, near the bottom end of the watersheds, are relatively large in size, with permanent flow, and receive nutrient inputs from the entire watershed area. These streams discharge into Voisey's Bay, contributing nutrients and energy from their entire watershed into the estuarine and marine environments.

Aquatic habitat within eight watersheds of the Assessment Area for fish habitat consists of two main components: stream habitat and pond habitat. All but one watershed, Little Reid Brook, contain both streams and ponds. Although watersheds are a continuum of pond and stream habitats, they are biophysically and ecologically quite different, and therefore, are discussed separately.

Stream Habitat

Stream habitat is characterized by sediment quality, water quality, hydrology and stream benthic macroinvertebrates. Full descriptions of the ecosytem components are provided in the respective reports on freshwater fish and fish habitat (JWEL 1997a), bathymetry and hydrology (JWEL 1997b), water and sedment quality (JWEL 1997c), primary productivity (JWEL 1997d) and freshwater benthic macroinvertebrates (JWEL 1997e). Water quality and hydrology are also summarized in Chapter 10.

Streamflow has a major influence on the physical and chemical characteristics of streamhabitats. Water scours and transports sediments downstream, influencing channel shape and alignment and substrate composition. In combination with local topography, streamflow determines areas of deposition and high sediment transport. The streams within the Assessment Area display peak discharges during spring snowmelt, with discharges approximately 400 percent above the annual average (Figure 11.3). A second peak in flow may also occur during the fall season (October). Low flows occur during the winter (January-March) and late summer, particularly in small streams and watershed basins where flow can be extremely low or intermittent. The 100-year minimum flow can be assumed to be virtually zero for all streams in the study area, owing to extended, severe freezing conditions. Despite differences in watershed size, streams within the eight watersheds can be expected to display the same monthly runoff pattern (JWEL 1997b), although temporally, some streams may have peak flows slightly earlier than others due to elevation, aspect (south facing slopes melt earlier) and size of drainage area. The temporal runoff patterns demonstrated by the streams within the Assessment Area were also similar to Ugjoktok Brook, the closest long-term gauged stream.

The physical and chemical characteristics of stream sediments reflect the bedrock and overburden characteristics of the watershed. The upper portions of watersheds in the Assessment Area are generally dominated by exposed bedrock, with very small amounts of overburden. Correspondingly, streams in these areas contain substrates dominated by bedrock, boulder and large cobble. Fine material eroded from the surrounding terrain is transported downstream during periods of high flow. In the Reid-Ikadlivik-Kogluktokoluk Brook and Little Reid Brook valleys, thick glaciofluvial deposits of sand, gravel and cobble, interspersed with marine sediments (clay, silt), are present and comprise the stream substrate. Groundwater flow from channel banks is visible in areas of substantial glaciofluvial deposits.

Figure 11.3 Stream Hydrology Mean Monthly Discharge as a Percentage of Drainage Area

Stream morphology influences the areas of fast water (scouring) and slow moving water (depositional areas). Higher water velocity is able to transport larger substrate material, resulting in increased bedload movement (by size and volume) during spring runoff. The finer material, which remains in suspension the longest, is ultimately deposited at the stream mouth/estuary. This is particularly evident in the sand-dominated lower reaches of the Reid Brook watershed and other large marine deltas.

Sediment sampling indicated that metal concentrations in most of the stream sediments are low, and represent natural weathering of the soils and rock within the watershed. Elevated metal concentrations were most often associated with fine sediments (e.g., silt and clay), which rarely accumulate in streams with high flows. Sediments at a few sites (around Discovery Hill and the Ovoid) contained increased concentrations of nickel, copper and cobalt. Based on deep and shallow sediment samples, it was determined that these levels represent a pre-existing condition related to the known mineralogy of the sites (JWEL 1997c).

Stream water quality within the Assessment Area, as described in Chapter 10, has naturally low concentrations of most trace metals and other water quality parameters. A few stream water samples had slightly increased concentrations of copper and iron; in general, these were the same locations that showed increased trace metal concentrations in sediment samples. In addition, the relatively low concentrations of nutrients indicate that stream waters are oligotrophic (low in nutrient input, with low organic production).

Benthic macroinvertebrates communities within the Assessment Area are representative of the boreal to taiga regions of eastern Canada, with relatively low species diversity and density, and with patchy spatial variation. Several factors may be responsible for the overall low benthos density and diversity in streams; these are described in detail in JWEL (1997e). Northern streams are generally less productive than those to the south due to lower productivity, low suspended solids, low plankton biomass, shorter seasons, winter freezing, and highly variable streamflow. Although the distribution of many larval aquatic insects, which emerge as adults, is not restricted by watershed boundaries, factors such as water quality, temperature, flow, substrate, predation, food and cover will influence the species diversity and abundance. The Reid Brook watershed contained the highest diversity, while the Throat Bay watershed contained the lowest diversity.

High diversity and density of certain taxa occurred in areas of gentle flow and soft, organic substrates, such as at the mouth of Reid Brook and within the large peatland east of the brook. Relatively high diversity also occurred in larger streams, and high diversity and density often occurred at pond outlets. This pattern is typical of boreal streams, as plankton from the pond become entrained in the streamflow and provide a food source for filter feeding taxa. In addition, during winter the relatively warm water entering the stream from the lake maintains more stable conditions within the outlet stream section (i.e., less anchor ice formation and stream bed freezing and more constant water flow).

Two species, a stonefly and a caddisfly, represent new Labrador records. The former was found in Little Reid Brook and the stream flowing west from Eastern Deeps and the latter was found in the same Eastern Deeps stream. Leeches and tabanids were found only at the outlet of Camp Pond. Tadpole shrimp (notostracans) were found in two watersheds: Makhavenikh Lake and North Tailings Basin.

Pond Habitat

Pond habitat is described in terms of sediment quality, water quality, primary productivity and benthic macroinvertebrates. Full descriptions of each of the pond ecosystem components are provided in the respective Technical Data Reports (JWEL 1997c; 1997d; 1997e). Water quality is summarized in Chapter 10.

In general, the ponds within the Assessment Area are oligotrophic, have low buffering capacity, and contain low concentrations of metals, nutrients and other elements. The substrate in the deep water of most ponds consists primarily of sands and clays. In shallower areas, sediments are coarser, being influenced by sediment transport from inflowing streams and higher energy sediment sorting. Aquatic vegetation (macrophytes) were low in abundance and patchy in distribution. Most ponds, with the exception of Camp Pond, developed a thermocline during the early to late summer.

Metal concentrations in most of the pond sediment samples were very low and represent the natural weathering of the soils and rock within the watershed. Although concentrations of all pond sediments were non-lethal in three toxicity tests, sub-lethal effects on growth were observed for ponds in several watersheds (i.e., four of five ponds in the Reid Brook watershed, and two of three ponds in the North Tailings Basin watershed). The cause of this is unknown, although a number of factors may have contributed to growth reduction, including fine grain size and the presence of naturally occurring toxic compounds.

The primary production level and the amounts of phytoplankton and zooplankton biomass observed in the project ponds place them at the extreme oligotrophic (low) end of the range observed for temperate lakes. The most productive pond is Camp Pond. This may be attributable largely to a progressive increase in productivity and plankton biomass from Headwater Pond to Camp Pond. Nutrient inputs associated with the Voisey's Exploration Camp may contribute, but field observations of extensive beds of aquatic macrophytes in Camp Pond, and of their low abundance in other ponds, is evidence that this higher productivity is not a recent phenomenon.

The benthic macroinvertebrates demonstrated both low diversity and low abundance. The samples were dominated by chironomid (midges), the most prevalent being Chironomus sp. and Procladius sp., which are relatively tolerant of nutrient enrichment and increased trace metals. This genus, as well as tubificid worms, which are also tolerant of nutrient enrichment and metal contamination, and other chironomids, are typical for oligotrophic lakes (Dermott 1985; Dermott et al. 1986). Extremely oligotrophic ponds represent harsh conditions. Two rare taxa were found in the ponds, representing new records south of the tree line. The caddisfly was found in the shallows of Pond 54, while the midge was found in the shallows of Makhavinekh Lake.

Several environmental factors influence the composition of benthos in these ponds, including sample depth, alkalinity (or buffering capacity), dissolved organic carbon (DOC) and substrate characteristics. There were no apparent differences in benthic communities among watersheds, presumably because pond depths, alkalinity, DOC and substrate varied independently among ponds within watersheds. Ponds in the Assessment Area with water containing higher alkalinity had higher macroinvertebrate abundance and species richness in deeper waters.

Within any given pond, the benthos were more abundant and more diverse in shallow waters, and demonstrated greater temporal variability than in deeper habitats. This trend is typical, as shallow-water benthos tend to complete a greater number of reproductive cycles, presumably because of warmer water (Brinkhurst 1974). Because deep-water benthos vary less seasonally, they are, therefore, more likely to be related to lake chemical or trophic conditions. Benthic numbers and diversity were also lower in ponds with more clay content in the sediments, most likely due to limited interstitial spaces and more difficult burrowing conditions.
11.1.3.2 Fish Habitat
To facilitate the assessment of environmental effects on fish and fish habitat, fish habitat within the Assessment Area is described on a watershed basis (Figure 11.2). Kogluktokoluk Brook and Ikadlivik Brook watersheds are not described because direct environmental effects on these watersheds are not anticipated to result from the Project. The watersheds in the Assessment Area are described below. Streams and ponds are partitioned to reflect the location of fundamentally different populations and ecologies.

Each stream is described in terms of the physical characteristics of sequential reaches (as numbered in the associated figures). The combined charcteristics of substrate, flow, water depth, and gradient form the basis for the assignment of habitat types (I, II, III, and IV), which are explained in the figure legends. Fish species presence was noted and fish numbers per unit area (100 m²) is presented, wherever it was determined, to indicate comparative density. The presence of young-of-the-year indicates probable spawning at or nearby the site of observation.

Reid Brook Watershed

Inuit have commented on the "comparatively rich and diversified ecosystem" in reference to Voisey's Bay of which the Ikadlivik and Reid Brook systems drain into (Williamson 1997).

The Reid Brook watershed extends inland approximately 16 km from Voisey's Bay with a 171 km² drainage area (Anderson 1985). The main channel of the brook begins in the upper barrens of the Central Ranges Land Region and enters the Fraser River Land Region in its lower half. The Assessment Area includes the lower half of this brook. Within this lower section, the main channel of the brook has carved a meandering path through thick sand and gravel deposits.

"My family liked to stay at Emish because there was a lot of fish. My father would catch fish all year round. In the summer or the winter he would catch trout and charr and another small white fish we called Kauapishissits� Sometimes we used a net and other times we used spears to catch the fish. We would make the spears ourselves using a knife to carve the end of a stick." (Charrlotte Rich, The Voisey's Bay News, May 1997:21)

The Reid Brook stream environment contains both anadromous and landlocked forms of Arctic charr and brook trout. The anadromous fish primarily use the main channel and extend as far as Reid Pond, and there is no evidence of adults moving into the tributaries. Only one obstruction (Reid Falls) exists on the main channel restricting, but not preventing, upstream movement of the anadromous charr stock. Fish found in ponds in this watershed include landlocked Arctic charr, brook trout, lake trout (in two ponds) and threespine sticklebacks. Fish species found in stream habitat include Arctic charr, brook trout, round whitefish and threespine sticklebacks.

The Reid Brook watershed contains 4 main sections:

the main stem;
a tributary draining from Pond 54;
a tributary (Camp Brook) containing a sequence of three ponds, (i.e., Camp Pond, Otter Pond, and Headwater Pond); and
a third tributary that drains south into the braided region of Reid Brook.

The fish habitat and species present within these four areas are summarized on Figures 11.4 to 11.7, respectively. Full details of the survey results are presented in JWEL (1997a).

Southern Watersheds

The southern watersheds are located south of Headwater Pond in a low elevation, low gradient plain. This area has many intermittent streams within subwatersheds, along with subsurface flow. The largest watershed includes Ponds 72 and 73, connected by a small stream, with Pond 73 draining through a small stream into Voisey's Bay (Figure 11.8). The stream environment between ponds and the outlet from Pond 73 is approximately 2-2.5 m wide, with low gradient, slow flow, and substrate consisting of silt and boulders.

Four species of fish were caught in this watershed including brook trout (ponds and streams), Arctic charr (streams), and threespine and ninespine sticklebacks. The Arctic charr are landlocked, as there is no evidence of anadromous charr using this system.

Throat Bay Watershed

Local Inuit indicate that the lower section of this stream is an anadromous Arctic charr spawning stream (Williamson 1997).

The Throat Bay watershed has a drainage area of 35 km² and drains from Pond 64 in an easterly direction towards Throat Bay (Figure 11.9). This watershed contains the main stream channel and a total of four ponds. At the mouth of this watershed is a 5 m cascade that is the only obstruction on this system; upstream movement of anadromous Arctic charr past this cascade is not likely under most conditions.

The stream is approximately 5-10 m in width, has good fish habitat along its entire length, and contains reaches of spawning and rearing habitat throughout. There are no obstructions restricting fish movements into or out of any of the ponds. Brook trout, landlocked Arctic charr and threespine sticklebacks were found in this system.

This watershed has a drainage area of 34 km² and is the location for tailings disposal (the North Tailings Basin). Two main ponds which are oligotrophic, rocky and deep are located in the upper portions of the watershed (Figure 11.10). The North Tailings Basin drains southeast from the ponds over several large cascades that are barriers to upstream fish movement. The stream then flows through a large braided section, passes a second barrier (4-5 m falls), continues into Pond 57 and then into Kangeklualuk Bay.

Brook trout were found in most stream habitats in this watershed. Anadromous Arctic charr were found in Pond 57 and sighted in the lower section of the stream between the pond and Kangeklualuk Bay (landlocked Arctic charr and brook trout were found in all three ponds, threespine sticklebacks were only found in Pond 57). Inuit indicate that anadromous Arctic charr spawn in the area from the mouth of the stream to the falls (Williamson 1997). No fish were found in the northwest tributary to the North Tailings Basin. A 15-20 m waterfall on this tributary prevents upstream fish movement. The presence of tadpole shrimp (notostracans), which are highly vulnerable to predation, in this upper portion of the indicates that no fish are upstream of the falls.

Figure 11.4 Fish Habitat for Reid Brook Watershed, Main Stem

Figure 11.5 Fish Habitat for Reid Brook Watershed, Pond 54 Brook

Figure 11.6 Fish Habitat for Reid Brook, Camp Brook - Tributary 2

Figure 11.7 Fish Habitat for Reid Brook Watershed, Tributary 4

Figure 11.8 Fish Habitat for Southern Watersheds

Figure 11.9 Fish Habitat for Throat Bay Brook

Figure 11.10 Fish Habitat for North Tailings Basin Brook Watershed

Pond 65 Watershed

Pond 65 Watershed is found just to the south of the North Tailings Basin watershed, draining north into Kangeklualuk Bay (Figure 11.11). This watershed has a drainage area of 10 km², with one moderately-sized pond (Pond 65). There is a large, vertical waterfall (approximately 30 m high) near the mouth of the stream. Upstream of Pond 65, the stream has ponds both on the main channel and on tributaries.

Due to the fish barrier at the mouth, all fish in this watershed are landlocked. During fish surveys on this watershed, brook trout and Arctic charr were caught in Pond 65, and brook trout and threespine sticklebacks were caught in most sections of the stream. There are possible obstructions for salmonids from the smaller ponds that drain into tributaries of the main channel, however, fish were observed in at least one of the ponds.

Option 5 Watershed

Inuit indicate that the lower section of this stream has an anadromous Arctic charr spawning stream (Williamson 1997).

This watershed, approximately 9 km long, drains east into Kangeklualuk Bay. Within its 14 km² drainage area, it contains four medium-sized ponds and several smaller ponds (Figure 11.12). There are several small obstructions near the mouth of this system, all under 1 m in height. Approximately 700 m from the first major pond on the system (reach 6), the gradient increases. This causes obstructions and a possible fish barrier for upstream movement. No barriers were found between any of the major ponds. Brook trout, Arctic charr and threespine sticklebacks were sampled from Pond 58. Anadromous Arctic charr smolts were found in the lower section of this watershed, with landlocked Arctic charr found in the ponds. Brook trout were found throughout the system and threespine sticklebacks were found in the ponds and in the lower section of the watershed.

Pond 67 Watershed

Pond 67 Watershed is located to the east of the North Tailings Basin and drains from two very small ponds on the plateau to the larger Pond 67 (Figure 11.13). The stream has a width of 1.5-2.5 m, with a mixture of silt, gravel and cobble substrate. This stream discharges into Kangeklukuluk Bay. There are no obstructions to fish movement between Pond 67 and the stream.

Fish in the stream and pond environments of this watershed are expected to include brook trout, landlocked Arctic charr, and threespine sticklebacks. The two smaller ponds in the upper plateau contain brook trout.

Figure 11.11 Fish Habitat for Pond 65 Watershed

Figure 11.12 Fish Habitat for Option 5 Brook

Figure 11.13 Fish Habitat for Pond 67 Watershed

Little Reid Brook Watershed

Little Reid Brook, flowing north into Anaktalak Bay, has a drainage area of approximately 15 km^2. (Figure 11.14). Winding through a thick glacial deposit, the brook is relatively narrow and dominated by sand and gravel substrates. Within the main channel, coarse substrate (cobble) is limited and no ponds or substantial pools are located along this system. The main channel meanders and has banks of sand and gravel. Groundwater discharge is evident at the base of steep slopes in the form of spring pools and seepage. The tributaries are generally small, have low flow and are often intermittent. Resident brook trout occur in most accessible habitat within the system, but no Arctic charr were taken through two seasons of electro fishing. Arctic charr smolt have been observed in the lower section of the stream near the mouth (Makowecki, R. pers. comm.). Inuit indicate that Little Reid Brook is an anadromous Arctic charr spawning river (Williamson 1997), however, field surveys found evidence of only brook trout spawning.
11.1.3.3 Fish Species
"That whole area around Emish used to be rich in wildlife�There are different names for all the kinds of fish we found in the rivers, lakes and bays there." (Tshenish Pasteen, The Voisey's Bay News, April 1997:31)

In general, fish in these aquatic environments have adapted to low productivity waters, which result in lower food availability than are expected from temperate aquatic ecosystems. Fish must also be able to withstand the extreme weather conditions that occur in northern Labrador, which result in thick ice in many areas, streams that stop flowing due to freeze up, frazil ice, low water, possibly warm water conditions in late summer and ponds that may be ice-covered into June.

The fish species in the Assessment Area, as determined during the field studies (JWEL 1997a) include Arctic charr, brook trout, lake trout, round whitefish, threespine stickleback and ninespine stickleback (Table 11.1). These species have been previously documented in the Landscape Region (Scott and Crossman 1973) and are common in northeastern coastal areas. As discussed, both anadromous and resident brook trout and Arctic charr occur within the Assessment Area, using stream and pond habitats. Round whitefish also inhabit both streams and ponds. Lake trout primarily inhabit the freshwater pond environments and are not anadromous. Threespine and ninespine sticklebacks can inhabit both freshwater and marine/estuarine environments.

Table 11.1 Fish Species Present Within Watersheds of the Assessment Area

Watershed	Arctic Charr	Brook Trout	Lake Trout	Round Whitefish	Threespine Stickleback ^a	Ninespine Stickleback ^a
Reid Brook, Southern Watershed	A, R R	A, R R	R	R	R	R
Ponds 68-69 Brook	R	R	R		R

Pond 64 Brook	R	R			R
Pond 58 Brook, Pond 67 Brook	A (smolt), R	R			R
Option 4	A, R	R			R
A = anadromous, R = resident. ^aThreespine and ninespine stickleback can tolerate brackish and salt water but most were caught in freshwater, distant from the sea.

Figure 11.14 Fish Habitat for Little Reid Brook Watershed

Stream Aquatic Ecosystem

In the Assessment Area stream aquatic ecosystem, four main types of associations were documented as follows.

Fishless Streams. No fish were observed or captured in the northwest tributary above the North Tailings Basin, due to the presence of a vertical 15 m waterfall downstream. Similarly, no fish were observed in the stream habitat above a 10 m waterfall located 500 m below Makhavenikh Lake. Notostracans, also known as tadpole shrimp, were found only above these barriers. As notostracans are normally not found coexisting with predatory fish, their presence supports the assumption that Arctic charr, brook trout or lake trout do not occur in these areas. Other areas where fish were not collected or sighted were small, higher elevation, primarily first order tributaries that had barriers downstream.

Brook Trout. The majority of streams surveyed contained only brook trout, which were generally found throughout the system to those points where further upstream movement was restricted because of increased gradient. In many cases, streams with barriers had brook trout located upstream and downstream of a barrier. Most of the streams in the Assessment Area provide spawning, rearing and holding habitat for brook trout. The adaptability of brook trout may allow them to out-compete other species in stream environments.

Brook Trout and Threespine Stickleback. In some stream areas, usually associated with slower waters close to pond environments, threespine sticklebacks were found along with brook trout. These areas generally had smaller substrate and more aquatic plant growth, which are preferred by sticklebacks.

Arctic Charr and Brook Trout. These two species were found together on Reid Brook and the lower reaches of tributaries draining into Reid Brook. During electrofishing surveys below Reid Falls, the ratio of brook trout to Arctic charr was 1.5:1 (399:266). Above Reid Falls, the ratio of brook trout to Arctic charr increased to 8:1 (190:24), most likely due to the Reid Falls obstruction limiting upstream movement of anadromous Arctic charr. In the North Tailings Basin, anadromous Arctic charr as well as brook trout are known to use the part of the stream that enters into Pond 57. In Option 5, anadromous Arctic charr smolt were sampled along with brook trout. One Arctic charr smolt was sampled close to the mouth of Little Reid Brook; other electrofishing surveys on this system revealed no Arctic charr. Threespine sticklebacks were also found on sections of Reid Brook, and on Option 5.

In two separate survey locations, there were additions to the above communities. In Reid Brook, round whitefish were identified in addition to Arctic charr, brook trout and threespine sticklebacks. These round whitefish were captured during counting fence operations in the lower portion of Reid Brook. In the Southern watersheds, ninespine sticklebacks were captured in addition to Arctic charr brook trout and threespine sticklebacks.

Landlocked Arctic charr were rarely found in stream areas, possibly indicating that brook trout may be outcompeting the charr in stream environments.

Pond Ecosystems

In the Assessment Area pond ecosystems, four different types of associations were documented.

Fishless Ponds. No fish were found in two ponds (Pond 61 and Makhavinekh Lake). These ponds were found at higher altitudes than the other surveyed ponds and were very oligotrophic, indicating low nutrients and low productivity. During the primary productivity survey, Makhavinekh Lake was found to have certain large daphnia that are usually not found in ponds with fish (JWEL 1997d). Both of these ponds have upstream migration barriers on the main channel which they drain into, preventing upstream fish movement into the ponds. These ponds also have a longer period of ice cover due to their elevation.

Arctic Charr Only. Landlocked Arctic charr were found in Pond 60, which is located in a similar area and elevation as Pond 61. Barriers prevent upstream movement of fish into this pond. The Arctic charr in this pond were generally quite thin, probably due to low food availability caused by the oligotrophic, low nutrient waters.

Brook Trout, Landlocked Arctic Charr and Threespine Sticklebacks. This combination was found in most ponds in the Assessment Area. Brook trout were more abundant in the shallower ponds with higher levels of productivity and accessible stream spawning habitat. Arctic charr were more abundant in the deeper and more oligotrophic ponds. In the North Tailings Basin watershed (Ponds 55 and 56), brook trout and landlocked Arctic charr were found; however, no sticklebacks were caught during surveys.

Lake Trout. Lake trout were found in two ponds in the Assessment Area (Ponds 54 and 69). These ponds also contained brook trout and threespine sticklebacks, with Pond 54 also containing landlocked Arctic charr. In pond 54, there was indication of a partitioning of food resources between the two dominant species, Arctic charr and lake trout. Arctic charr and lake trout had different diets; the resident Arctic charr were feeding primarily on plankton and other aquatic invertebrates and the lake trout were feeding primarily on smaller fish (usually threespine sticklebacks).

Anadromous Arctic Charr

According to Barbour (1984), the overall strategy for survival of Arctic charr is related to the variability exhibited in all its life history parameters and to the precise adaptation to individual habitats.

Adult anadromous Arctic charr spend one or two months feeding in the sea prior to returning to freshwater to spawn and overwinter. Very little feeding takes place in freshwater (Johnson 1980; Boivin and Power 1989). Migration to freshwater occurs between July 1 to September 30 in Labrador, and spawning between October 1 to November 15 (McCubbin et al. 1990) (on Reid Brook, spawning was already occurring in the last part of September (JWEL 1997a). Spawning usually occurs in slower, medium-depth sections of streams with gravel substrate or on gravel shoals in ponds. The eggs incubate in the spawning gravel and hatch the following spring between April 15 and June 15 (McCubbin et al. 1990). All Arctic charr remain in freshwater during the winter, occupying either streams or lakes. Adults return to the sea during the spring snow melt (McCubbin et al. 1990), which occurs during May and June in the Assessment Area watersheds. Juvenile anadromous Arctic charr remain exclusively in freshwater for the first 2-6 years, occupying stream and pond habitat. While growing, their diet includes zooplankton, insect larvae, benthic invertebrates and fish (Table 11.2).

Table 11.2 Summary of Anadromous Arctic Charr Behaviour and Diet

Life Stage	Seasonal Occurrence	Habitat	Diet
Spawning/Egg Incubation Hatching (alevin)	October 1 - November 15: October 1- June 15 April 15 - June 15	gravel; usually in main channels of streams with current, upwelling; shoals in ponds	n/a
Fry	post-hatching	streams/ponds; cover under rocks or stones, or in interstices	zooplankton, very small insect larvae
Juvenile (2-6 years)	year round residents in freshwater	streams and associated small tributaries; rocky regions along shorelines of ponds	zooplankton, amphipods, sticklebacks, benthic invertebrates
Smolt/adult (marine)	travel to sea during spring runoff (May-June)	in the sea - remain close to coastlines in relatively shallow water	capelin, sand lance, sculpin, euphausid shrimp, amphipods and krill
Smolt/adult (freshwater)	return to freshwater during July-August; sub-adults return after adults; remain in freshwater over winter	main channels of streams with gravel, sand and cobble bottoms; overwinter in large/deep pools	do not feed in freshwater
Sources: Scott & Crossman 1973; McCubbin et al. 1990; Johnson 1980; JWEL 1997a

Participant in LIA study: "A 5 lb charr was abnormal in Voisey's Bay. You never got anything smaller than that." (Williamson 1997:47)

Anadromous populations of Arctic charr are found throughout the coast of Labrador. These Labrador Arctic charr, when mature, are approximately 2.0 kg in weight and are about 50 cm in length, which is somewhat smaller than the Arctic charr of the central Arctic. The growth rate of anadromous Arctic charr is slow compared with many fish stocks further south. There is also a general decline in growth rate with increasing latitude along the Labrador coast. For anadromous Arctic charr, a mean length of 50 cm is reached at 7 years at Adlatok, 9 at Nain, 10 at Hebron, 12 at Ramah and, although not the farthest north, not until nearly age 14 at Okak (Andrews and Lear 1956).

On the basis of statistical examination of Northern Labrador charr, Dempson and Misra (1984) identified seven discrete anadromous stocks. Separation of stocks on this basis is substantiated by differences in biological characteristics, such as growth rate and age at maturation, and distribution patterns obtained through tagging studies. Two stocks reside in the vicinity of the Project: the Nain stock and the Voisey's Bay stock.

Local Inuit indicated that six brooks flowing into Voisey's Bay are Arctic charr brooks (Williamson 1997).

The Nain stock unit is made up of Anaktalak Bay, Nain Bay, Tikkoatokak Bay and Webb Bay for the inshore zone, and Dog Island and Black Island for the offshore island zone (Dempson and Kristofferson 1987). The Voisey's Bay stock unit consists of the inshore Voisey's Bay subarea and the coastal Antons subarea. Components of this stock can migrate to accessible freshwater habitat in Reid Brook, Kogluktokoluk Brook (including its tributary, Ikadlivik Brook), Toma Brook, Konrad Brook and Kogaluk River (Anderson 1985). While charr show a strong affinity to their natal stream, some wandering occurs. The Reid Brook, Ikadlivik Brook/Kogluktokoluk Brook systems contain much of the freshwater habitat (Figure 11.15) available to the Voisey's Bay Arctic charr stock. It is the anadromous Arctic charr population that spawns and overwinters in this combined system that is the subject of this assessment.

There is some indication that many anadromous Arctic charr return to the same stream that they left in spring (Brice-Bennett 1977), although it is not known whether this is the natal stream; others may overwinter in systems where they over-wintered the year before or look for "rivers of opportunity" (Johnson, L. pers. comm.). Where several streams of similar characteristics enter the same bay or inlet, the interchange may be expected to be higher than in regions where there is a single stream. This was evident for Arctic charr in Reid Brook, with many adults moving from Reid Brook to Ikadlivik Brook in September and October, in most cases after spawning. This general behaviour pattern of Arctic charr in Labrador is similar to those observed in other regions (Gyselman 1984). The major differences are in the specifics, such as time spent in the sea, date of migration, age at first seaward migration and growth rate. Such a life history pattern appears ideally suited to a species exploring and occupying the river systems of lands exposed after glaciation, a process to which Arctic charr has evidently been exposed several times over the Pleistocene Period.

In the Reid Brook, Kogluktokoluk Brook and Ikadlivik Brook system, anadromous Arctic charr are distributed along the main stem of these brooks.

Spawning by anadromous Arctic charr was confirmed in the middle reaches of Reid Brook during late September and the first part of October, 1996 at water temperatures below 7 °C. Following spawning, the majority of Arctic charr within Reid Brook made downstream migrations, entering Ikadlivik Brook or Kogloktokuluk Brook. By the end of October, 59 percent of the Arctic charr radio-tagged (part of the radiotelemetry study) in Reid Brook had moved to Ikadlivik Brook, where they stayed for the winter months (JWEL 1997a). This pattern of migratory behaviour has not been documented previously in Arctic charr (MacKinley, S. pers. comm.); however, this pattern of migration is known in the related dolly varden (Armstrong 1984).

The migration out of Reid Brook may be related to the low abundance of suitable overwintering habitat in the system. Eight of the Reid Brook Arctic charr (7.6 percent of those tagged) negotiated Reid Falls and entered Reid Pond, where they remained until the end of October, and through the winter months. The deep pool below Reid Falls represents the only other potential holding area for overwintering along Reid Brook.
Other observations regarding the behaviour of anadromous Arctic charr in Reid Brook included:

several Arctic charr made downstream migrations prior to spawning;
the majority of tagged fish remained, where they were captured in Reid Brook, until after spawning;
there is no evidence that anadromous Arctic charr migrate up any of the Reid Brook tributaries; and
within Reid Brook, juveniles were largely restricted to the main channel and were found only in the lower reaches of the tributaries, which is presumably the extent of their freshwater range.

Spawning was also observed in Ikadlivik Brook during September/October. Ikadlivik Brook is a major area for overwintering anadromous Arctic charr as indicated by local fishing practices (Williamson 1997) and documented by JWEL (1997a). Most of the fish leaving Reid Brook moved to large pools on Ikadlivik Brook, where they stayed for most of the winter.

Anadromous Arctic charr also enter freshwater via Kangeklukuluk Bay and Throat Bay. These systems, however, do not have multiple streams/brooks entering a single estuarine area, as occurs at the head of Voisey's Bay. A conservative assumption for the purposes of this assessment is that the anadromous charr entering these bays are separate populations from the charr on the streams on Voisey's Bay.

Participant in LIA study: "Before the fish plant opened up, we went to Anaktalik�took 120 trout one haul�some of them 8 or 9 lbs." (Williamson 1997:47)

Anadromous charr have been harvested traditionally for subsistence, and in the Nain district area, commercially. The intensive commercial fishery in the 1970s and 1980s has decreased the size and numbers of Arctic charr in the area; however, participants in a recent LIA study indicated that since the reduction in commercial fishing in 1993, there has been a slow recovery (Williamson 1997). Within the Assessment Area, commercial fishing of the Voisey's Bay stock occurred in the bay itself (netting). Subsistence fishing has occurred along Reid Brook, and at the ponds located along Ikadlivik Brook (Williamson 1997).

Landlocked Arctic Charr

Landlocked Arctic charr have life history characteristics that are different from the anadromous form. The landlocked form is usually found in areas inaccessible from the ocean. They primarily spawn in ponds on gravel shoals, but can use stream spawning habitat (Scott and Crossman 1973). In the Assessment Area, stream habitat was rarely used by landlocked Arctic charr. Landlocked Arctic charr growth can be dependent on the presence of other fish species in their habitat. Arctic charr, when the only fish species present in a system, display a slower growth rate than when they occur along with sticklebacks and lake trout (Fraser and Power 1989) (as found in Pond 54). The presence of lake trout result in charr of larger size, lower survival, shorter life, and lower catch per unit effort. Arctic charr in lakes that contain lake trout are generally not fish eaters (piscivorous), but rather, feed on zooplankton and aquatic insects. In ponds

Figure 11.15 Freshwater Habitat Accessible to Anadromous Arctic Charr Stocks

present, smaller individuals consume zooplankton and insect larvae (e.g. Chironomids), intermediate-sized fish eat a mixture of aquatic invertebrates, while larger Arctic charr are primarily cannibalistic (Fraser and Power 1989).

A first order stream is the main freshwater channel directly connected to salt water. A second order stream is the main channel of a tributary (from the confluence with the main channel). A third order stream is a branch of the main channel of a tributary.

Criteria used to distinguish anadromous from resident Arctic charr included accessibility of habitat, size at maturity (Shears, M. pers. comm.), use of stream habitat, and feeding ecology. The field surveys found juvenile charr in stream habitat accessible to the anadromous form but not in streams adjacent to ponds containing landlocked populations. Arctic charr were not found in first, second and third order streams. Pond resident Arctic charr often had food in their stomachs, whereas anadromous adults from Reid Brook and Ikadlivik Brook had empty stomachs.

Movement between ponds is unlikely. Therefore, landlocked Arctic charr in these ponds are conservatively considered to be distributed in discrete pond populations. Five ponds within the Reid Brook basin and three ponds within the North Tailings Basin watershed were determined to have resident populations (Figure 11.16). Most of the other ponds within the Project watersheds that were sampled contained Arctic charr. Both resident and anadromous Arctic charr were observed in Reid Pond and Pond 57 on the North Tailings Basin watershed.

Williamson (1997) reports that Inuit harvest fish at various locations such as Reid Pond and Trout Pond.

Brook Trout

Brook trout can live in either stream or pond habitats, preferring clear, cool (less than 20 ° C), well-oxygenated water (Scott and Crossman 1973). Brook trout can grow up to 6.6 kg, and average 250-300 mm in length (Scott and Crossman 1973). Unlike Arctic charr or lake trout, brook trout are not long-lived fish, generally not living past 8 years. Sexual maturity usually occurs at the age of three. Brook trout are piscivorous and eat a wide variety of foods, including aquatic insect larvae, terrestrial insects, zooplankton and fish, including threespine sticklebacks (Scott and Crossman 1973). This species has both landlocked and anadromous forms. Anadromous trout generally grow larger and have distinct silver coloration while at sea or if recently returned to freshwater. Resident forms are typically smaller at maturity and retain distinctive coloration. Resident brook trout migrate to spawning areas for spawning from August 15 to September 30, with spawning occurring from September 1 to September 30 (McCubbin et al. 1990). Spawning occurs during the day and usually over gravel beds in the shallows of headwater streams, although pond spawning in gravel shallow shoals can occur if there is upwelling in the area (Scott and Crossman 1973). The eggs incubate in the spawning gravel from September 1 through to June 15, and hatching occurs between May 15 and June 15 (McCubbin et al. 1990). Within the Assessment Area, spawning was observed to occur during September at water temperatures near 9 °C (JWEL 1997a).

Figure 11.16 Distribution of Resident Arctic Charr and Lake Trout in Assessment Area Watersheds

The spawning requirements for anadromous brook trout are similar to the landlocked form. Their migration into freshwater occurs from June 20 to September 1. The downstream migration is from June 15 to July 15 (McCubbin et al. 1990).

Residency in a stream or pond may be imposed by the presence of barriers that isolate the population. Resident trout display localized seasonal movements within the watersheds, especially during spawning migration. Therefore, brook trout populations extend within any basin, limited only by natural barriers.

Within the Assessment Area watersheds, brook trout occupy most available habitat, with the exception of steep gradient streams and higher altitude ponds. Resident forms were common in all watersheds; anadromous brook trout were only identified in the Reid Brook/Kogluktokoluk Brook watersheds. Anadromous brook trout generally have a similar annual migration pattern to that of Arctic charr, overwintering in freshwater habitats from July/August to May and moving to Voisey's Bay and possibly Anaktalak Bay for the summer months. Their movements at sea are not far ranging, and they must overwinter in fresh water (Scott and Scott 1988).

Lake Trout

Lake trout are found throughout most regions of Canada; however, in Labrador their distribution is restricted to the northern half of the district (Scott and Crossman 1973), which includes the Landscape Region. They are primarily pond fish, that prefer deep waters and are carnivorous, feeding primarily on fish and aquatic invertebrates. Adult lake trout have an average size of 381-508 mm (Scott and Crossman 1973).

Lake trout are autumn spawners, migrating towards large boulder or cobble shoals within their resident ponds. Spawning occurs from September 1 to October 30 in Labrador (McCubbin et al. 1990). Spawning occurs during the night, at water temperatures usually around 9° C (Scott and Crossman 1973). The eggs incubate overwinter in the spawning shoals and hatch between March 15 and April 30 (McCubbin et al. 1990). Lake trout juveniles generally move to deeper waters when hatched. Lake trout are a long-lived fish, with ages of over 20 years not uncommon. Sexual maturity occurs around 7 years (Scott and Crossman 1973).

Lake trout in the Assessment Area were found in only Pond 54 on the Reid Brook Watershed. These Lake trout were subsisting primarily on threespine sticklebacks.

Round Whitefish

The round whitefish is found in most areas of Labrador and is common in most northern Canada regions. Round whitefish are part of the subfamily Coregoninae, which includes other whitefish, and ciscoes. These fish have a slender, almost cylindrical, body that averages 200-300 mm in length for adults (Scott and Crossman 1973). Spawning for these fish takes place in the fall, usually in gravelly shallows of lakes at river mouths, or sometimes in rivers. Eggs usually hatch in the spring. Round whitefish are generally bottom-feeding, eating a variety of benthic invertebrates, especially mayfly larvae and pupae, caddisfly and chironomid larvae, and small molluscs such as fingernail clams and snails, as well as fish eggs (Scott and Crossman 1973). Round whitefish are known to be cannibalistic.

During the VBNC surveys of the eight watersheds, round whitefish were only encountered in the lower end of Reid Brook during the counting fence operation of 1997 (JWEL 1997g).

Threespine Stickleback

Threespine stickleback are common in Labrador. This species may be either anadromous or entirely freshwater and is generally not found far from coastal waters. It is tolerant of marine, brackish and fresh water (Scott and Crossman 1973). Threespine sticklebacks are carnivorous and eat a large variety of food, including aquatic invertebrates and eggs of fish (Scott and Crossman 1973).

Threespine stickleback grow to 50 mm in length. They spawn in freshwater in June or July and they are nest builders, with the males building nests made of twigs and plant debris on sandy substrate areas. Hatching occurs within seven days, and the newly hatched eggs are guarded by the male. The young grow quickly in their first year, reaching a size of up to 30 mm. Threespine sticklebacks are short-lived fish, living up to 3 years. Sexual maturity occurs after the first year (Scott and Crossman 1973).

In the Assessment Area, threespine sticklebacks were primarily found in ponds, or stream environments close to ponds. These fish were quite abundant in the marshy area of Camp Pond between the North tributary and the outlet from Camp Pond. Within the Assessment Area, they represent a very important forage fish for lake trout, brook trout, and possibly Arctic charr.

Ninespine Stickleback

The ninespine stickleback is found throughout Newfoundland and Labrador and in all other provinces and territories. It is common along marine shoreline areas, as well as in freshwater ponds and streams. The body is small, slender, and compressed, with an average length of 64 mm. The ninespine stickleback spawns in freshwater during summer. Once the male builds a nest, the female will be attracted to the the nest to deposit her eggs. The male guards this nest after fertilization. Growth is rapid in the first year, and the life span is approximately 3.5 years. The ninespine stickleback eats primarily aquatic insects and small crustaceans. This species can be an important food source for other predacious fish (Scott and Crossman 1973).

Within the eight watersheds surveyed, the ninespine stickleback was only found in slow moving stream environments in the southern watersheds along with threespine sticklebacks.

11.1.3.4 Fish Movement
Within the stream and pond aquatic systems in the Assessment Area, there are different fish migration and movement patterns. Within the Reid Brook watershed, anadromous Arctic charr and brook trout move between the marine environment and the main channel up to and including Reid Pond; however, there was no evidence of adult anadromous fish movement into any of the tributaries. These fish move into the marine environment usually in late May or early June, and return in July or August. Reid Brook anadromous Arctic charr had a tendency to move to Ikadlivik Brook after spawning. This is most likely due to the limited overwintering habitat in Reid Brook.

Resident brook trout were found throughout the Assessment Area in both stream and pond environments. Brook trout move freely between these two environments, especially in the fall when they move to stream habitats for spawning. However, spawning in the pond environment is also possible.

Resident Arctic charr inhabit pond environments and are rarely in stream habitat. Evidence from the fish surveys indicate that it is most probable that the resident Arctic charr spend most of their life cycle in the pond environment, which would, through necessity, provide them with spawning, rearing and holding habitat. Lake trout showed similar habitat requirements.

Threespine sticklebacks in the Assessment Area were found in pond habitat, and in stream habitat that was usually close to other ponds. These fish can move freely between the ponds and streams if not restricted by barriers. During spawning, they prefer sandy bottoms with aquatic vegetation, usually found in slow moving streams or ponds.

11.1.3.5 Fish Production
Ponds in the subarctic region are generally oligotrophic in that low nutrient input and availability depresses production at all trophic levels, resulting in lower fish production compared to temperate regions. Ponds displayed a range of oligotrophic conditions, as determined from the studies of water quality (JWEL 1997c), primary productivity (JWEL 1997d) and macroinvertebrates (JWEL 1997e).

For the ponds within the Assessment Area, morphoedaphic indices were determined to get a relative estimate of fish production. The morphoedaphic index (MEI) uses concentrations of total dissolved solids in water, along with the mean depth, to predict fish production in ponds (Ryder 1965; Schneider and Haedrich 1989).

Ponds all had MEI values that would be reflective of oligotrophic conditions, with very low values (less than 1) found in Reid Pond, ponds north of Reid Pond (Ponds 60 and 61), and Pond 55. The fifth pond (Pond 61) had the lowest MEI value of all the ponds, which coincided with no fish caught during surveys in this pond. These ponds are generally quite deep, found at relatively higher elevations, and are surrounded by barren terrain with very little overburden. Ponds with MEI values over two included Otter Pond (2.5), Camp Pond (2.7), Pond 57 (lower pond in the North Tailings Basin watershed) (2.6), Trout Pond (2.2) and Pond 64 (Throat Bay) (3.0). These ponds were generally found at altitudes just above sea level, had greater amounts of vegetation surrounding the pond and had greater deposition within the ponds. Fish were more abundant in these ponds, and condition factors for brook trout and Arctic charr were usually above 1.

Fish production in the ponds surveyed (derived from the MEI) ranged from 0.24-2.66 kg/ha/year, with the highest value for Camp Pond. In comparison with Newfoundland island waters, the average fish production calculated by this method is around 3.4 kg/hr/year.

MEI is a reasonable method to determine approximate fish production from ponds. However, this method does have limitations, as discussed in Schneider and Haedrich (1989), one of which is that this index works best on large lakes. However, it does provide a scale of comparison, which clearly shows, along with results from other studies, that primary and secondary productivity are very low in these ponds.

Streams in the Assessment Area had standing stock estimates determined from electrofishing stations. A standing stock measurement provides the amount of salmonid biomass (in grams) that is present per unit area (100 m²). Average standing stock estimates for the major watersheds of interest are provided in Table 11.3. Generally, biomass was greatest at outlets from ponds, or in stream sections which provided good cover, with gradients not exceeding 3-4 percent. These standing stock estimates are comparable to other studies done on Newfoundland Rivers (LeDrew 1973, 1986a; 1986b; Beak 1980; deGraaf 1981).

11.1.3.6 Fish Health
The general health of fish in the Assessment Area was indicated through condition factor (a general indicator of fish health, based on fish weight to length ratio, 1.0 being average), disease profile, and body burden analysis conducted on fish fillet and liver tissue. Fish surveys were consistent with MEI values, as most of these ponds had low fish catches, with fish from three of four ponds having condition factors below 1.

Table 11.3 Average Standing Stock Estimates for Watersheds in the Assessment Area

Watershed	Average Standing Stock Value (g/100 m2)	Range of Standing Stock (g/100 m2)
Reid Brook	251.2	10.4-748.8
North Tailings Basin	257.7	56.4-390.4
Pond 65	819.5	689.3-950.6
Option 5	210.3	104.5-347.6
Little Reid Brook	238.4	100.8-399.4

Condition factors were determined for brook trout, Arctic charr, and lake trout. The condition factor for anadromous Arctic charr was approximately 1.10 in Reid Brook, indicating slightly above average condition of these fish. Landlocked Arctic charr had condition factors ranging from 0.78-1.05, with Ponds 55 and 56 (North Tailings Basin ponds) and Pond 60 having condition factors below 0.9, indicating slightly thinner than average condition. These ponds are found at higher elevation, where nutrient source and productivity limit food availability. Brook trout had condition factors that ranged from 0.95-1.08 in stream environments, and 0.84-1.60 in ponds. Condition factors under 0.90 were found for Ponds 55 and 56, similar to the landlocked Arctic charr. Lake trout in Pond 54 had a condition factor of 0.99.

In general, food availability is the key determinant of condition factors; where fish seemed in poor condition (e.g., thin), food is limiting. The threespine stickleback is a common forage food fish for the lake trout, brook trout and, possibly, resident Arctic charr. However, these fish were not found in the North Tailings Basin watershed. Other common foods include aquatic insect larvae, zooplankton and molluscs. It is widely held that adult anadromous Arctic charr seldom feed while in freshwater (Johnson, L. pers. comm.), which is supported by the data in 1996 (sampled fish were found to have empty stomachs).

Disease profiles were determined for 60 fish in the Assessment Area. Fish surveyed were found to have low incidences of fish pathogens. The Fish Health Protection Regulations Schedule II pathogen, Yersinia ruckeri, was isolated in very low numbers from one fish. In addition, a non-speciated Staphylococcus was isolated in relatively low numbers from two additional fish. No other finfish pathogen was found. A virological analysis resulted in negative laboratory examination. The resulting diagnosis indicated a very low prevalence (1:60) of covert Yersiniosis.

Upon internal examination, many brook trout and Arctic charr contained internal parasites, primarily tapeworms and nematodes. Some of these fish had scarring from these parasites.

Body burden (metal) analyses were determined for liver and muscle fillet tissue samples from brook trout, lake trout, and Arctic charr (landlocked). Results from these analyses indicate that most trace metal parameters are below limit of quantitation concentrations. For most metals that were measurable in tissues of fish from Voisey's Bay (Cd, Cu, Fe, Mn, Pb, Hg, Se, Zn), concentrations are as low as would be found in an uncontaminated or pristine condition. In comparison with other areas, fish samples appear to contain metal concentrations as low as or lower than from other locations in Labrador and the Arctic, or elsewhere in North America (Scruton 1984; Bruce and Spencer 1979; Bohn and Fallis 1978). For muscle samples, metal concentrations are well below those considered to be toxic to fish and those established as guidelines for protection of human health (Bohn and Fallis 1978). Although the mean concentrations of mercury in muscle and liver were below guideline concentrations, a few samples were above the Canada Health 0.5 mg/kg guideline concentration. Aluminum was above the limit of quantitation in approximately 50 percent of liver samples; however, these concentrations are in the range of concentrations found at other sites (Scruton 1984; Bruce and Spencer 1979).

11.1.4 Likely Future Conditions
The expected condition of fish and fish habitat within the Assessment Area within the expected lifespan of the Project, in the absence of Project activities, is likely to be relatively similar to pre-project conditions. Anadromous Arctic charr numbers will continue to be affected by commercial, subsistence and recreational fishing efforts in the area. Subsistence and recreational harvesting of brook trout will also continue.

In the case of global climate change, it would be expected that the general trend in this area of Labrador would be for higher than normal temperatures throughout the year. If this is the case, an increase in ocean water levels is anticipated. Within the Assessment Area, the greatest environmental effect would be on the Reid Brook/Ikadlivik Brook system. Currently the rivers flow out to Voisey's Bay with the mouth of both rivers in close proximity to each other, creating a freshwater connection between the two rivers. As a consequence, anadromous Arctic charr move between these two river systems during the spawning season. To do so, fish do not have to enter into saltwater. If ocean levels were to rise due to global warming at a rate greater than crustal post-glacial rebound, it could break the freshwater connection between the two watersheds. This may affect the behaviour of the anadromous Arctic charr population. This change is difficult to predict, but would most likely result in a reduced migration to Reid Brook.

11.2 Environmental Effects Assessment
"Will the mine/mill project or associated developments affect the quality or quantity of water in surrounding watersheds through airborne or water-borne contaminants, pollution, damming, or other means? Will this affect the health of residents or anadromous fish populations?" (Naskapi Band of Quebec, Comments on Draft EIS Guidelines for Review of the Voisey's Bay Mine and Mill Project, May 13, 1997:15)

Each of the eight watersheds potentially affected by Project activities functions independently in terms of hydrological connections, inputs, and interactions between sediment and water. Watersheds boundaries tend to limit the movements of fish and aquatic organisms and restrict the distribution and pathways of pollutants that enter the aquatic environment. Due to its size and the location of many of the Project facilities within it, the Reid Brook watershed is discussed as subwatersheds. Environmental effects on the marine environments that support anadromous Arctic charr that use freshwater habitat in the Assessment Area are also discussed (Section 11.2.2).

11.2.1.1 Reid Brook Watershed
Potential environmental effects within the Reid Brook Watershed are summarized in Table 11.4. The synthesis of the environmental effects assessment is in Appendix 11A.

Table 11.4 Potential Environmental Effects Within Reid Brook Watershed

Potential Environmental Effect	Project Phase	Activity
Habitat Loss	Construction Operation	site preparation of Headwater Pond dewatering Otter Pond brook diversion of stream near Ovoid construction of the south sedimentation pond and storage areas deposition of mine rock/tailings into Headwater Pond
Fish Loss	Construction	preparation of Headwater Pond
Habitat Modification	Construction	dewatering, dam construction installation of culverts and arch bridges sedimentation and siltation due to construction activities blasting groundwater withdrawal construction of storage areas, sedimentation ponds treated sewage into Camp Pond
	Operation	seepage into Otter Pond water extraction from Camp Pond groundwater withdrawal blasting airborne dust from open pit operation of settling/storage ponds groundwater withdrawal
	Decommissioning Post-Decommissioning	removal of culverts and arch bridges overflow of open pit into Camp Pond

"There was a lot of fish there [Emish]�It is a shame for it to be destroyed. One spring time when we hunted at Emish, we killed 3 bears and 700 fish." (Hank Rich in Innu Nation Task Force on Mining Activities, 1996:33)

Project activities that will affect the Reid Brook watershed include construction and operation of the mineralized mine rock/tailings disposal facility, construction and operation of the ovoid pit, the open pit Surge Pond and mine rock storage areas, blasting, seepage from dam areas, water diversion, construction of the airstrip, groundwater use for domestic purposes, and road and stream crossing construction and operation.

Activities in Headwater Pond will directly affect Otter Pond, immediately downstream. These two ponds are connected by a relatively short, intermittent stream. Camp Pond, located downstream of Otter Pond, will also be affected by activities affecting the two upper ponds. In addition, environmental effects associated with the construction and operation of the mine/mill facilities will affect Camp Pond and its outflow, Camp Brook.

To ensure maximum protection for Reid Brook, the design and operation of the Headwater Pond impoundment remove this basin from the Reid Brook watershed forever. During the life of the Project, discharges from Headwater Pond will be diverted away from Reid Brook and in post-decommissioning, the eventual release from Headwater Pond will be directed to Throat Bay Brook.

The Camp Brook subwatershed comprises Camp Pond, Otter Pond and Headwater Pond. Each pond supports a discrete population of landlocked Arctic charr. Juvenile anadromous Arctic charr were found only at the mouth of Camp Brook, close to the confluence with Reid Brook. There was no evidence of anadromous charr moving up Camp Brook.

The Pond 54 subwatershed, located to the south of the Eastern Deeps, flows westward into Reid Brook, and contains one pond (Pond 54) and a long tributary. This watershed supports a resident population of brook trout, a landlocked Arctic charr and lake trout population in Pond 54, and provides rearing habitat in the lower sections for juvenile anadromous Arctic charr using the Reid Brook -Ikadlivik Brook system.

Habitat Loss

Headwater Pond

Fish habitat is quantified in "units" (100 m²) of stream habitat and hectares (10,000 m²) of pond habitat.

Habitat loss in Headwater Pond (110 ha) will occur during the construction and operation phase, due to the combination of pond drawdown, subsequent placement of mineralized mine rock and the resulting deterioration of water quality in the basin. The construction of the dam will also result in the loss of habitat within the stream connecting Headwater Pond and Otter Pond (37.5 units). Habitat compensation will be provided in accordance with DFO's no net loss guiding principle.

Diverting the discharge of Headwater Pond from the Reid Brook watershed to Edward's Cove via pipeline will result in direct environmental effects associated with the reduction in overall watershed size and therefore the volume of water entering Otter Pond on an annual basis. This will result in a 29 percent reduction of flow into Otter Pond which may affect 398 units of stream habitat. Reduced flows will be addressed by the provision of a minimum instream flow to protect fish habitat. Otherwise, habitat compensation will be provided for unavoidable habitat losses resulting from reduced flow in accordance with negotiations with DFO.

Construction Around Camp Pond

The development of the open pit will require the diversion of one stream entering Camp Pond. Downstream of Camp Pond, water level reductions will be compounded by changes to the diversion of surface water flow from the vicinity of the ovoid pit, East Mine Rock Storage Area and North Overburden Storage Area, and from water intake from the pond. Water flows between Camp Pond and Reid Brook are predicted to decrease 26 percent, resulting in a 4 percent decrease in the flow in lower Reid Brook. This reduction will affect 398 units of stream habitat in Camp Brook. Mitigation of these environment effects will be provided by maintaining minimum flows for habitat protection or habitat compensation.

South Sedimentation Pond and Storage Areas

The construction of the South Sedimentation Pond will result in the loss of 46 units of stream habitat from a small fish-bearing stream that drains into Pond 54 Tributary.

Fish Loss

The use of Headwater Pond as a containment facility will result in the potential loss of its resident Arctic charr and brook trout populations. This resource will be harvested and the fish from the pond made available for local consumption.
Diverting the discharge of Headwater Pond from the Reid Brook watershed to Kangeklualuk Bay via pipeline will result in direct effects associated with the reduction in overall watershed size and therefore the volume of water entering Otter Pond on an annual basis. The geographic extent of the hydrological changes is assumed to be Otter Pond to Camp Brook outflow.

The construction of the containment dam will dewater the stream to Otter Pond. This stream contains brook trout but has naturally intermittent flows.

Habitat Modification

Seepage and Flooding

Seepage from the Headwater Pond may occur downstream into Otter Pond; however, water quality modelling to determine the environmental effects on Otter Pond shows little change in water quality (Beak International Incorporated 1997) (Chapter 10). Similarly; modelling for Arctic charr and an aquatic snail show no environmental effect on these organisms based on the calculated hazard quotient (HQ).

"A lot of things are eaten by the fish that come down the rivers. And where you have the mine site on a high hill and in the summer when the snow melts you are going to have different things going out along with the spring, whether, you know, they eat smaller fish and then these in turn are eaten by bigger animals and I think that we are going to have to try and keep that in mind." (Edward Power, through interpreter, Panel scoping meeting in Nain, April 17, 1997)

At decommissioning, the open pit will begin to flood and eventually overflow to Camp Pond; some environmental effects may be experienced.

Dewatering

During construction, dewatering activities will transport TSS to Otter Pond. Primary productivity is likely to decrease during drawdown, as light penetration in the water column decreases, but duration will be short and reversibility is high.

The hydrology of Otter Pond, Camp Pond and associated streams will be affected by the reduction in drainage basin through the diversion of Headwater Pond flows. Further reductions to Camp Pond will occur from the collection of site and storage pile drainage that will be diverted to Headwater Pond. These combined processes may constitute a harmful alteration to fish habitat. Compensation will be provided for habitat losses through negotiation with DFO.

On Pond 54 Tributary, a 6 percent flow reduction will occur at the confluence with Reid Brook. The environmental effects of this reduction will be long-term, but it will involve only a portion of the area used by the resident brook trout population. The reversibility of habitat loss is nil due to the permanent changes in topography and the reversibility of streamflow alterations is low.

Sedimentation/Siltation

Storage area and pond construction will include the East Mine Rock storage area as well as the Mill Site Sedimentation Pond, the South Sedimentation and Open Pit Surge Ponds. Excavation during pond construction will result in increased TSS and sedimentation.

Sedimentation (increased sediment load and deposition) is perhaps the most recognised environmental effect on aquatic systems and can affect all trophic levels. Sedimentation alters habitat by changing the physical characteristics, distribution and relative abundance of existing substrate types. Changes to limiting habitats may result in changes in the carrying capacity of a population. Sedimentation may fill rearing pools, cover coarse substrates and alter channel flow, thereby reducing the suitability of habitat for existing communities of fish and aquatic invertebrates.

The deposition of sediment may clog spaces between gravel which prevents the flow of oxygenated water and removal of waste products from developing eggs deposited in the gravel (Rogerson 1986). This often causes suffocation (lowering the level of dissolved oxygen) and egg mortalities and may prevent future use of spawning areas (Beschta and Jackson 1979; Chapman 1988). Pore space size determines the percolation rate of water through substrate and also influences movement of emerging alevins through gravel (Lotspeich and Everest 1981). The elimination of sheltered areas between boulders and gravel particles will also affect juvenile fish (Scrivener and Brownlee 1989). The benthic macroinvertebrate populations are also affected by changes to the physical habitat structure, causing changes in relative species abundance and community structure.

Acute lethal effects to fish from suspended solids are unlikely to occur unless the concentrations are high (Alabaster and Lloyd 1982). In addition to the mechanical effects of sediment deposition, such as the habitat damage experienced at East Kemptville (AQUAMIN 1996), sedimentation at mining sites often includes particulate metals and related contaminants. This has been documented at base metal mines such as Health Steele, Sa Dena Hes, Bell, and Lac Matagami (AQUAMIN 1996).

The environmental effects of metals in the aquatic environment are discussed in Chapter 10 (and Appendix B to Chapter 10) with regard to the chronic and acutely lethal effects.

For the Project, regrading of the mine rock storage sites and decommissioning of sedimentation ponds may result in sediment loading to adjacent water bodies. Drainage patterns will be restored to pre-development conditions where practicable, resulting in potential habitat avoidance from increased TSS and habitat modification from sedimentation. The magnitude will be low, as a localized community of fish (less than one generation) will be affected, and introduced sediment should be within the range of natural variability.

The geographic extent of sediment-related environmental effects from the decommissioning of the South Sedimentation Pond, Open Pit Surge Pond, and the Mill Site Sedimentation Pond will be downstream from the area of activities to the extent where the effect dissipates. The duration of the environmental effect will be site specific and will occur until the reclamation or removal of areas is complete. The reversibility is high as sedimentation will cease when decommissioning stops.

Groundwater Influences

Groundwater from the Reid Brook area will be used to supply drinking water. Wells will be installed and fully operational by the end of the first year of construction. Pit and mine-works will alter groundwater flow patterns, potentially reducing "downslope" quantities. The construction of the pit will commence during construction, with the removal of surficial mine rock. The potential environmental effect of these activities is the alteration of groundwater flow pattern, quantity, and quality.

Much of the Reid Brook main channel and many tributaries receive a portion of their flow from groundwater contribution. Direct environmental effects of wells and dewatering on groundwater flow patterns could have indirect effects on surface water quantity and quality (through reduced dilution potential). Environmental effects include changes in water temperature, baseflow and location of upwellings, which could affect spawning areas in the main channel and tributaries of Reid Brook.

Groundwater extraction will result in a net loss of flow within Reid Brook. The reduction related to groundwater changes must be considered in conjunction with other sources of reductions in surface flow to Reid Brook: diversion of part of a watershed (Headwater Pond, pumping of water from Camp Pond). Environmental effects will be greatest during low flow periods.

Airborne Contaminants

The dispersion of airborne contaminants has been modelled in Chapter 8. The main issue is total suspended particulate (TSP), which originates from road dust in the open pit. It will have similar chemical characteristics as the ore. The effect on water quality will occur where the TSP is deposited in the Camp Pond subwatershed. In order to determine the extent of deposition of TSP the annual average TSP concentration is used, which is 4 m g/m³ over Camp Pond. This concentration is well within the limit set by the Newfoundland Air Pollution Control Regulations (NF 957/96), Schedule A, Criteria for Acceptable Air Quality, and the Canadian Environmental Protection Act, Clean Air Act Desirable Ambient Air Quality Objectives Order, No. 1.

Apart from the increase in TSS, the metal content of the ore dust may be liberated into the water column. The ore will be in the form of the minerals chalcopyrrite, pentlandite, and pyrrhotite, which are insoluble in water and will not readily oxidize when submerged. Most of the TSP which enters the water column will either flush out of the system, with additional dilution in Reid Brook, or be deposited in the sediment in Camp Pond, where it will accumulate in a reducing environment.

Thus, neither direct contact through ingestion by fish nor liberation of metals from the TSP through dissolution or oxidation, is likely to affect the HQ for Arctic charr or snails in the Camp Pond subwatershed.

The baseline level of aluminum in Camp Pond and Camp Brook was found to have a negligible environmental effect on water quality (Chapter 10). The projected increase of 30-35 percent during open pit mining would conservatively produce a minor environmental effect, depending on the pH and other related factors (i.e., colour and total dissolved carbon). The potential environmental effect is reduced following open pit mining but resumes at a lower level during post-decommissioning due to the overflow of pit water into Camp Pond.

Vibration to Blasting

Potential environmental effects of blasting on fish and aquatic habitat are related to the resuspension of sediments (Munday et al. 1986), bank failure and sedimentation, habitat avoidance and physical damage to fish tissues (DFO 1994) caused by the passage of subsurface shock waves through waterbodies.

Blasting will commence with the development of the open pit during the construction phase (removal of mine rock) and continue through operation. Underground shock waves from blasting in the open pit may affect Camp Pond (200 m distance) or Reid Brook (1300 m distance). In Camp Pond, the environmental effects on fish will be limited to avoidance responses, depending on the severity of shock waves and their transmission through bedrock. Both the resident Arctic charr population and a portion of the Reid Brook trout population may be affected. Although bank stability along the shoreline of Camp Pond is high, resuspension of bottom sediments may occur, elevating levels of TSS and possibly causing sedimentation of charr spawning substrates in the pond. Turbidity with near-zero visibility in bottom waters has been reported approximately 50 m from test buried detonation sites (Munday et al. 1986). Settling time will depend upon the characteristics of the sediments (clays, silts or sands) and time of year, which influences ice-cover, stratification, and water velocity. Prolonged increases in TSS or turbidity may decrease primary production and affect benthic macroinvertebrates, reducing food resources. The overall magnitude of these environmental effects is low for Arctic charr and brook trout. Reversibility is high.

Blast Residue

Ammonium nitrate blast residue may accumulate in the Mine Rock Storage Area, adjacent to Camp Pond, and could enter watercourses via groundwater. All water containing ammonium nitrate blast residue will be collected in the South Sedimentation Pond and the Open Pit Surge Pond and directed to the treatment plant.

11.2.1.2 Southern Watersheds
Potential environmental effects on the Southern Watersheds are in Table 11.5. Results of the environmental effects analysis are summarized in Appendix 11A.

Table 11.5 Potential Environmental Effects Within Southern Watersheds

Potential Environmental Effect	Project Phase	Activity
Habitat Modification	Construction	construction of road and installation of culverts/bridges for the road connecting Headwater Pond to the airstrip sedimentation during construction of the airstrip
	Decommissioning	removal of culvert/bridge structures, airstrip

The Southern watersheds will have two Project activities associated with them: the construction of the airstrip, and the construction and use of the airstrip access road. Construction of the airstrip will be along the access to Pond 73. A road connecting the main mine/mill area with the airstrip will cross tributaries of the Southern watersheds.

This watershed contains landlocked populations of Arctic charr in the ponds, a single resident brook trout population that uses all accessible pond and stream habitat, and two species of sticklebacks (threespine and ninespine).

Habitat Modification

Stream Crossings

Culvert installation or low-profile arch construction will be required for roads and pipelines at all stream crossings. The proposed road connecting Headwater Pond to the airstrip will have crossings over the Southern watershed streams. During construction, general earth moving, road bed construction and the installation of culverts or arch bridges at stream crossings may cause erosion and subsequent deposition of sediments into aquatic habitat. The potential environmental effects of sediment loading are discussed in Section 11.2.1.1.

The amount of sedimentation is predicted to remain within the levels expected during spring freshet. The geographic extent is very localized and environmental effects will tend to dissipate downstream. The duration of sedimentation at crossings will be brief (both during construction and removal of stream crossings), and the reversibility is high. Control measures will be implemented as detailed in the Environmental Protection Plan (EPP).

Airstrip

The construction of the airstrip along the southern edge of Pond 73 may cause some sedimentation. The geographic extent of environmental effects from the construction of the airstrip will be localized. The duration of the environmental effect will depend on the length of the construction period, and the nature of the substrate in the construction area. The reversibility is high, as sedimentation will cease when construction is completed.

11.2.1.3 Throat Bay Watershed
A summary of the Project environmental effects analysis on the Throat Bay watershed is provided in Table 11.6. Results of the environmental effects analysis are summarized in Appendix 11A.

Table 11.6 Potential Environmental Effects Within Throat Bay Watershed

Potential Environmental Effect	Project Phase	Activity
Habitat Modification	Construction	construction of roads and installation of culverts/bridges road from Headwater Pond to the airstrip
	Operation	seepage from Headwater Pond into Throat Bay Watershed
	Decommissioning/ Post-Decommissioning	removal of culvert/bridge structures water release from Headwater Pond into Throat Bay Watershed

The only Project infrastructure in the Throat Bay watershed is a stream crossing on one of the tributaries which is crossed by the airstrip access road. The dam at Headwater Pond will be constructed in the Headwater Pond basin, with no initial drainage to the east. Potential environmental effects on Throat Bay watershed during operation are largely associated with seepage and after decommissioning, the release of untreated water from Headwater Pond eastwards into the Throat Bay watershed. This will commence following start up, when tailings and mine rock are placed in Headwater Pond and water levels rise.

Local Inuit report that this river is considered an anadromous Arctic charr spawning river (Williamson 1997).

This watershed contains landlocked populations of Arctic charr in the ponds, and a resident brook trout population that uses all accessible pond and stream habitat. The anadromous Arctic charr in this system are a population that is part of the Voisey's Bay stock.

Habitat Modification

Stream Crossings

The road connecting the Headwater Pond to the airstrip will have one crossing over a Throat Bay watershed stream. Mitigation will include the implementation of sediment control plans through the EPP. Although mitigative measures will be effective during construction of stream crossings, some sedimentation may occur.

The geographic extent will be very localized as the direct environmental effects will occur at the construction area and dissipate downstream.

The duration of sedimentation at crossings will be brief (during construction and decommissioning) and any environmental effects are reversible.

Seepage

During start up, mineralized mine rock and tailings will be placed in Headwater Pond. Seepage through the dam will enter the Throat Bay watershed following initial accumulation into a pond that will form to the east of the dam. Seepage rates are predicted to be continuous. The dilution and rate of dispersal of contaminants will vary seasonally but this will be masked as the receiving water is Pond 64. Ponds dampen seasonal variation by virtue of the volume of dilution. Dilution and dispersal will be lowest during low flow periods (summer, winter).

The predicted changes in water quality will result in the possibility of nickel concentrations having environmental effects on aquatic invertebrates in Ponds 64, 70 and 71 following closure. There is also a potential for chronic effects to Arctic charr and brook trout in Pond 64 (determined from predicted HQs (Beak International Incorporated 1997)). Reversibility is nil as the discharge from Headwater Pond will be for an indefinite period. Environmental effects will be attenuated downstream of Pond 64 due to dilution.

The baseline level of aluminum in water in Pond 64 is relatively high and is at a level that would be characterized as a moderate environmental effect on water quality if it were attributable to the Project (Chapter 10). Conservatively, an environmental effect on fish is either already manifest due to natural background levels, or the population can tolerate the existing conditions. The incremental increase in aluminum from seepage is minimal (greater than 0.1 percent of baseline), resulting in a non-detectable environmental effect. In post-decommissioning, slightly elevated aluminum levels in water are anticipated when Headwater Pond discharges to Throat Bay Brook. The additional aluminum will constitute an increase of 30-35 percent above baseline. As this increase does not change the pre-existing environmental effect on water quality, the same environmental effect is assumed for Arctic charr. Factors such as pH or dissolved organic material might increase the chronic threshold and reduce the magnitude of the environmental effect. The magnitude of the environmental effect is medium. The reversibility is low as the condition will last indefinitely.

11.2.1.4 North Tailings Basin Watershed
A summary of the Project environmental effects analysis on North Tailings Basin is provided in Table 11.7. Results of the environmental effects analysis are summarized in Appendix 11A.

Project activities within the North Tailings Basin watershed include the tailings facility (including construction of dams, and diversion channels), water treatment plant, and roads/pipelines from the Headwater Pond facility. The construction of the North Tailings Basin facility will begin during open pit mining and become operational for underground mining.

This watershed supports discrete populations of brook trout both above and below barriers located along the main channel (Figure 11.10). Although fish may move downstream, recruitment upstream to the upper population is not possible. Discrete populations of resident Arctic charr occupy Pond 55/56 and Pond 57 and anadromous Arctic charr are found in Pond 57.

Table 11.7 Potential Environmental Effects Within North Tailings Basin Watershed

Potential Environmental Effect	Project Phase	Activity
Habitat Loss	Operation	site preparation of North Tailings Basin (Ponds 55 & 56)
Fish Loss	Operation	site preparation of North Tailings Basin and deposition of tailings into North Tailings Basin
Habitat Modification	Operation Open Pit Mining	construction and operation of diversion trenches, construction of roads and service corridors ; installation of culverts and arch bridges; general earth works reduction of stream flow in North Tailings Basin brook
	Underground Mining	seepage into North Tailings Basin brook
	Decommissioning	seepage into North Tailings Basin brook
	Post-Decommissioning	removal of culvert/bridges along roads and service corridors; removal of effluent pipe infrastructure discharge of treated Tailings Basin water to North Tailings Basin brook

Habitat Loss

During construction, habitat loss will occur as a result of several activities. Ponds 55 (Tailings Pond) and Pond 56 (Polishing Pond) will be dewatered to facilitate construction of the dam structures. This will result in a reduction of pond habitat, eventually leading to total loss when tailings are deposited and the water quality deteriorates (212 ha of pond habitat and 19 units of stream habitat between the ponds). Reversibility is nil as this area will continue to contain tailings after the life of the Project. These losses will be addressed as part of the habitat compensation plan. Any unavoidable habitat losses due to stream diversions will be addressed in the habitat compensation plan.

Fish Loss

The dewatering of Pond 55 and Pond 56 of the North Tailings Basin will result in the loss of the resident Arctic charr populations. Contamination of the small pond to the north of Pond 55 will occur when it becomes part of the tailings facility as water levels rise, resulting in the potential loss of its resident Arctic charr and brook trout populations. As with Headwater Pond, this potential loss will be addressed by the harvest for local consumption of the fish in these ponds.

Habitat Modification

Diversions

Bypass channels and dams will become functional during open pit mining, resulting in reduced flows downstream on North Tailings Basin, potentially affecting 1007 units of stream habitat. Immediately downstream of the facility, streamflow will be eliminated. Farther downstream, between the North Tailings Basin and Pond 57, contribution from adjacent tributaries will reinstate flow, but overall flows will decrease by 74 percent. A minimum flow to protect fish habitat will be maintained to reduce harmful habitat alteration. Compensation for unavoidable habitat loss will be provided.

Stream Crossings

One of the first activities to occur on the North Tailings Basin watershed will be the construction of the access roads and service corridors, requiring general grading and earth moving, as well as the installation of culverts or arch bridges at each stream crossing.

During construction, general earth moving, road bed construction and the installation of culverts/bridges at stream crossings may cause erosion and sedimentation as discussed in Section 11.2.1.1. Culvert/bridge installation will be required for roads and pipelines at all stream crossings. The road connecting Headwater Pond to the North Tailings Basin will have stream crossings over North Tailings Basin watershed streams. Sedimentation may also occur during decommissioning. Mitigation will include the implementation of sediment control plans through the EPP (see Section 11.2.1.1)

Dewatering

Dewatering Pond 55 (Tailings Pond) and Pond 56 (Polishing Pond) will increase flows and water quality downstream of the proposed Tailings Basin, along North Tailings Basin brook. Increased flows may result in both positive and negative environmental effects to fisheries resources. In the late summer period, increased flows may enhance stream habitat and increase primary and secondary production. However, higher flows may actually prevent or impede fish passage and alter the existing habitat through increased turbidity, scouring and subsequent sedimentation. The magnitude of dewatering is low and the reversibility is high as the duration of exposure to increased flow is restricted. Environmental effects will be mitigated by dewatering in a manner that reduces flooding and scouring. Solids will settle out and aquatic communities will re-establish once pumping has ceased. If clean water is discharged in a manner that does not entrain or disturb sediment, no downstream perturbation due to sedimentation, scouring or erosion is anticipated. Increases in flow in the section of the stream linking the pond to Kangeklualuk Bay may improve Arctic charr passage, as these flows are at their low points during August and September and sections of very shallow water were observed in early September 1996.

During construction of the dam and channel diversions, potential indirect downstream environmental effects also include reductions in flow volumes and patterns, increases in TSS and temperature, and erosion. The magnitude will be low to medium on the resident brook trout population as the associated environmental effects will be restricted to the construction period, and the environmental effects downstream will eventually dissipate as solids settle out. Pond 57 will serve as a sedimentation basin, reducing turbidity and TSS. Although pond habitat may be affected, anadromous charr do not feed while in freshwater. Overall, the reversibility of environmental effects will be high as affected areas will be localized and the channel will be engineered to control erosion and sedimentation.

During the operation of the North Tailings Basin, discharge will be piped directly to Kangeklualuk Bay, bypassing the freshwater environment. However, continued modification of downstream flows due to dams and diversions (see Section 10.2) may alter migration, habitat and water quality, and result in a change in community structure. The reduction in stream flow between the Tailings facility and Pond 57 and the bay may reduce spawning habitat for anadromous Arctic charr. Flushing rate in Pond 57 will also be reduced.

Seepage

Seepage of contaminated water from the North Tailings Basin during operation may affect downstream fish habitat. The modelled environmental effects of this seepage, as discussed in Chapter 10, show increased water levels of copper and lead (Beak International Incorporated 1997). The corresponding hazard quotient (HQ) for Arctic charr and freshwater snails predict potential environmental effects from nickel downstream of these two dams and in Pond 57. These potential environmental effects will commence during underground mining. The existing levels of aluminum would cause a non-detectable environmental effect on water quality (Chapter 10). During operations there is a minimal increase (less than 0.3 percent increase) in the aluminum level in water. The magnitude is low for resident Arctic charr and brook trout populations.

Environmental effects of seepage will continue through decommissioning and post-decommissioning, as the dams and flow patterns will be permanent in nature. However, following decommissioning, water discharged from the outflow of Pond 56 will be treated as required to meet MMLER regulations. Flow will return to baseline levels as the north diversion channel is decommissioned. Predicted water quality changes are discussed in Chapter 10. The aluminum level in water is projected to be double the baseline value. The potential environmental effects to charr and snails from the increased metals will continue indefinitely.

11.2.1.5 Pond 65 Watershed
Potential environmental effects on Pond 65 Watershed is presented in Table 11.8. Results of the environmental effects analysis are summarized in Appendix 11A.

Table 11.8 Potential Environmental Effects Within Pond 65 Watershed

Potential Environmental Effect	Project Phase	Activity
Habitat Modification	Operation	construction of culverts/bridges, pipeline/ road from Headwater Pond to the North Tailings Basin
	Post-Decommissioning	removal of culvert/bridge, pipeline/road structures

Within the Pond 65 watershed, a road and pipeline connecting Headwater Pond with the North Tailings Basin will cross two tributaries. The Project activities of concern are construction of stream crossings (including sedimentation), and accidental events.

This watershed contains landlocked populations of Arctic charr in the ponds, a single resident brook trout population and a threespine stickleback population that use all accessible pond and stream habitat. No anadromous charr can migrate into this system due to a waterfall at the outlet of Pond 65.

Habitat Modification

During construction, general earth moving, road bed construction and the installation of culverts or arch bridges at stream crossings may cause erosion and subsequent deposition of sediments into aquatic habitat. Culvert installation or low-profile arch construction will be required for roads and pipelines at all stream crossings. The proposed road connecting Headwater Pond to the North Tailings Basin will have two crossings over Pond 65 watershed streams. Mitigation will include the implementation of sediment control plans through the EPP, and work scheduling to avoid sensitive periods. Although mitigative measures will be effective during construction of stream crossings, sedimentation may occur. The potential environmental effects of sediment loading are TSS and sediment deposition, which could result in habitat modification and avoidance by fish. Potential environmental effects of TSS will be localized and short term (episodic). The reversibility is high as the introduction of TSS and subsequent sedimentation will cease once construction is completed. Sedimentation will be controlled during construction by the implementation of sediment control measures and work schedules which are contained in the EPP.

Upon decommissioning, culvert and bridge removal will result in temporary habitat avoidance and modification through episodic increased TSS and sedimentation.

11.2.1.6 Option 5 Watershed

A summary of the potential environmental effects analysis on Option 5 watershed is provided in Table 11.9. Results of the environmental effects analysis are summarized in Appendix 11A.

Table 11.9 Potential Environmental Effects Within Option 5 Watershed

Potential Environmental Effect	Project Phase	Activity
Habitat Modification	Operation	increased flow due to water diversion at the north diversion channel seepage of contaminated water from North Tailings Basin into Option 5 watershed
	Decommissioning/ Post-Decommissioning	seepage through containment dams into Option 5 watershed for life of facility

No infrastructure or other physical works will occur within this watershed. Potential environmental effects on this watershed are largely associated with the operation of the North Tailings Basin, namely the seepage of contaminated water from Pond 55 northwards into the Option 5 watershed, and increased flows from the North Diversion channel. These will start during underground mining, when tailings are placed in the pond and water levels rise.

Local Inuit report that the lower section of this river is considered an anadromous Arctic charr spawning river (Williamson 1997).

This watershed contains landlocked populations of Arctic charr in the ponds, a single resident brook trout population that uses all accessible pond and stream habitat, threespine sticklebacks in pond and streams, and anadromous Arctic charr in the lower 700 m of stream. The anadromous Arctic charr in this system are part of the Kangeklukuluk population, which also uses the Pond 67 watershed.

Habitat Modification

Seepage from North Tailings Basin Through Dam 6

During underground mining, tailings will be placed in the North Tailings Basin. Seepage through the north containment dam will permit contaminated water to enter the middle pond in the Option 5 watershed.

Increased Flow from Northern Diversion Channel

During underground mining, flow from the northwest tributary to Pond 55 will be diverted north into the Option 5 watershed. The diversion will enter one pond, flow through another, and then enter the stream that discharges to the bay. Flows are predicted to increase by 61 percent in the stream. This increase in stream flow will modify the existing fish habitat, producing an adverse environmental effect (velocity barrier) in periods of high flow and producing a positive environmental effect by augmenting natural low flow. Fast flow areas may be used for rearing or spawning by fish, and fast flow can alter substrate composition in the stream. Positive environmental effects from increased flow include accessibility for migration and moderation of water temperatures in summer months. The increased flow may also prevent complete stream freeze-up during the winter months, which can kill residing fish and eggs.

11.2.1.7 Pond 67 Watershed
No infrastructure or other physical works will occur within this watershed. Potential environmental effects on this watershed are largely associated with the operation of the North Tailings Basin, namely the seepage of contaminated water from the tailings pond eastwards into the Pond 67 watershed. Seepage will start during underground mining, as tailings are placed in the pond and water levels rise.

Inuit report that the lower section of this river provides anadromous Arctic charr spawning habitat (Williamson 1997).

This watershed contains landlocked populations of Arctic charr in the ponds, a single resident brook trout population that uses all accessible pond and stream habitat, and anadromous Arctic charr. A small, but well developed estuary is present at the stream mouth, at Kangeklukuluk Bay. For the purposes of this assessment, the anadromous Arctic charr in this system are considered part of the Kangeklukuluk population, which also uses the Option 5 watershed.

Changes in water quality will affect both habitat quality and fish health (for example, snails) in a small headwater pond adjacent to the North Tailings Basin (Table 11.10). A summary of the environmental effects analysis is provided in Table 11A. Results of the environmental effects analysis are summarized in Appendix 11A.

Table 11.10 Potential Environmental Effects Within Pond 67 Watershed

Potential Environmental Effect	Project Phase	Activity
Habitat Modification	Operation Underground Mining	site preparation and dam construction seepage from North Tailings Basin into the Pond 67 watershed
	Decommissioning/ Post-Decommissioning	seepage from North Tailings Basin into the Pond 67 watershed

During underground mining, tailings will be placed in Pond 55. Seepage through the north containment dam will permit contaminated water to enter this watershed. The environmental effects due to nickel, copper and lead will be chronic on charr and snail in the small headwater pond. The environmental effect will be attenuated by dilution downstream of this pond to the baseline aluminum levels in water. Seepage during underground operation will contribute an additional 4 percent (Chapter 10). No additional environmental effect of aluminum on Arctic charr is projected to be attributable to the Project during operations. In post-decommissioning the increase over baseline will be 37 percent for aluminum. A low magnitude environmental effect is projected for Arctic charr. The reversibility is low.

11.2.1.8 Little Reid Brook
A summary of the Project environmental effects analysis on Little Reid Brook is presented in Table 11.11. Results of the environmental effects analysis are summarized in Appendix 11A.

Table 11.11 Potential Environmental Effects Within Little Reid Brook

Potential Environmental Effect	Project Phase	Activity
Habitat Modification	Construction	construction of roads and pipeline; installation of culverts/bridges; general earth works
	Decommissioning	removal of culvert/bridge, pipeline/road

Project activities within the Little Reid Brook Watershed include the plant/port access road and pipeline from the mine site to the port site, which cross some of the tributaries on the east side of the watershed. No fish loss or habitat loss is predicted to occur during any Project activities. However, habitat modification may result from related to several activities.

The main channel of Little Reid Brook supports a resident population of brook trout. The stream is reported to have a spawning run of anadromous Arctic charr (Williamson 1997), but field surveys did not detect any charr upstream of the mouth. In addition, no overwintering habitat such as ponds or pools are present along the system.

Habitat Modification

The main haulage road between Edward's Cove and the mine and mill facility will pass through this watershed. During construction, general earth moving, road bed construction and the installation of culverts or arch bridges at stream crossings may cause erosion and subsequent deposition of sediments into aquatic habitat. Mitigation will include the implementation of sediment control plans through the EPP. The road will not cross the main channel, and many of the tributaries are either intermittent or do not directly represent fish habitat.

The potential environmental effects of sedimentation are discussed in Section 11.2.1.1, as are the temporal and spatial extents. All culverts will be designed to reduce changes in hydrological patterns, limit scouring, and permit fish passage. The amount of sedimentation is predicted to remain within the levels expected during spring freshet.

11.2.1.9 Marine Habitat of Arctic Charr
During the life of the Project, environmental effects on the marine habitat may affect the Nain and Voisey's Bay anadromous Arctic charr stocks. These stocks are generally distinct and environmental effects are therefore not cumulative between stocks. Adult charr use the marine habitat for feeding for approximately two months a year, between May and July. Marine areas are critical feeding habitats for Arctic charr, because anadromous fish do not feed while in freshwater.

Kangeklualuk Bay

Anadromous Arctic charr spawn in the stream linking Pond 57 and the bay, and use the pond itself. Because populations of charr are associated with the marine bays adjacent to their freshwater environments, the Kangeklualuk Bay population is distinct from the Voisey's Bay populations due to the distance between natal streams. However, both of these populations are included in the Voisey's Bay stock.

During underground mining, treated effluent will be discharged from the North Tailings Basin into Kangeklualuk Bay, which supports Arctic charr food resources such as euphausids and sculpin. Potential environmental effects may include changes to water quality and plankton communities. The effluent will also affect benthic organisms, resulting in metal uptake and habitat degradation over the life of the Project. Indirect environmental effects on Arctic charr include habitat avoidance and loss over the same period. In general, reversibility of changes to habitat quality is considered to be medium for Kangeklualuk Bay.

In the decommissioning phase, discharge will be redirected to the freshwater environment. Discharges will be treated until such time that treatment is no longer required. At that time, the pipelines may be decommissioned and flows from the respective watersheds redirected to the original or alternative stream courses.

Edward's Cove

Treated water from the mill will be piped to Edward's Cove for discharge. Anaktalak Bay is within the area used by the Nain Arctic charr stock.

The geographic extent of environmental effects in Anaktalak Bay represents a small portion of the available marine habitat (see Chapter 12, Figure 12.2).

Voisey's Bay

No environmental effects are predicted for Voisey's Bay (see Chapter 12) except in the rare case of an accidental event, such as a spill in freshwater.

Throat Bay

No environmental effects are predicted for marine fish and fish habitat in Throat Bay (Chapter 12). Arctic charr in this bay will be unaffected by the project while in saltwater.

Kangeklukuluk Bay

The Option 5 watershed, which drains into this bay, will not be affected by seepage of contaminated water from the tailings facility. Therefore, no environmental effects on this marine habitat are predicted.

11.2.1.10 Accidental Events
Accidental events may result in the deterioration of water quality, which would result in habitat or fish loss and/or habitat modification/avoidance. Except for fire environmental effects will be contained within watershed boundaries. Potential accidental events are:

spills of hazardous materials;
fire;
pipeline rupture;
storm events - spillway structure;
dam failure; and
road washout and flooding.

Hazardous Materials Spill

Spills could occur during the transfer, handling, or containment of hazardous materials. Fish habitat in Reid Brook watershed, Little Reid Brook watershed, Southern watersheds, and Pond 67 watershed could potentially be affected. The overall risk of a hazardous materials spill is considered to be low.

Factors influencing the geographic extent, severity and duration of environmental effects include time of year (discharge, winter vs. spring, fish migrations), nature of the material (solid or liquid, and solubility), toxicity of material and location of spill within the watershed. Hazardous materials will be used primarily during the operations phase.

"I worry about oil spills near the rivers or brooks. Oil could destroy fish habitat or even other animals that live off the land." (Tshenish Pasteen, The Voisey's Bay News, April 1997:31)

The magnitude and reversibility of spills would depend on the concentration of the spill material in the receiving water. The high spring flows and high bedload transport will effectively flush the system during the spring following any accident. Although the volume of water in ponds is much greater than in streams, and thus has a greater capacity to dilute the spilled chemical, the turnover time in ponds is much longer. Therefore, a spill in a pond may have an environmental effect that has a longer duration than a spill in a stream.

Environmental effects may be experienced by all life stages of anadromous and resident fish within the affected area, and mortalities could occur. For anadromous Arctic charr, this would include eggs/larvae, juveniles (age 0 to 4 or 5 years) and adults. Brook trout and stickleback populations within the affected area would also be lost. Changes in water quality would also affect other trophic levels; benthic organisms would be expected to drift or be directly killed. Chronic effects at the top and bottom of the affected area would include avoidance behaviour and disruption of migratory patterns.

Reversibility of environmental effects from spills on the population of anadromous Arctic charr and brook trout is medium. Insect populations would be replaced within a season or two; benthic drift from upper portions of the stream would re-establish other food resources. For brook trout, individuals from other portions of the watershed would re-establish within the affected area. For anadromous Arctic charr, unaffected individuals of all age classes would be present in Reid Brook upstream of the affected zone, and egg deposition would occur in the next season. In addition, the population moves freely between all three streams in the system: Reid Brook, Ikadlivik Brook and Kogluktokoluk Brook. Migration runs occur annually, therefore re-establishment of Arctic charr within Reid Brook should increase the following fall. Reversibility is therefore rated as medium.

Contingency planning will be in place to enable a quick and effective response to a spill. Personnel will be trained in response measures, and spill response equipment will be readily available in the event of an accidental spill. VBNC will enforce strict procedures for the safe transportation of all hazardous materials on site.

Fire

Fire within the VBNC Claim Block could occur during any phase of the Project. Factors influencing the severity and duration of environmental effects from fire include time of year, extent of fire damage and type of fire.

Smoke emissions from the fire would contain particulate matter and other contaminants. Total particulate matter would increase and contribute metals into the aquatic environment. Runoff would contain ash and sediment and increase alkalinity and TSS. A fire could also increase stream bank erosion and alter the temperature of small waterbodies.

A fire during the spring or summer could interrupt the migration of Arctic charr and brook trout, and a late summer or early fall fire could interfere with spawning if environmental effects were of long duration. During early life stages (i.e., eggs, larvae), salmonids are more sensitive to the deposition of ash and sediment through runoff and have limited avoidance ability. Therefore, fires during the fall (spawning) and winter (incubation) would present a greater risk to salmonid populations. Eggs are very sensitive to pH and temperature changes, thus a fire in the post-spawning period could result in high egg mortality. Reversibility of physical effects is high, but would occur over a number of years. Spring flows and high bedload transport would effectively flush the system during the spring following the event; however, erosion within the watershed would continue to contribute sediments to the stream for a number of years. Changes to groundwater patterns and contribution to baseflow in the stream could be altered during this period due to changes in evaporation and infiltration rates. Restoration of bank stability and riparian cover would rely on the re-establishment of plant communities through vegetative succession.

Reversibility of environmental effects from fire on the population of anadromous Arctic charr and brook trout is medium. Benthic drift from upper portions of the stream would re-establish food resources. For brook trout, individuals from other portions of the watershed would re-colonize the areas of environmental effect. For anadromous Arctic charr, unaffected individuals of all age classes would be present in Reid Brook upstream of the areas of environmental effect and other streams could be expected to re-colonize the areas of environmental effect. Reversibility is therefore rated as medium.

Contingency planning will be in place to enable a quick and effective response to an on-site fire. Personnel will be trained in fire prevention and response, and appropriate fire-fighting equipment will be readily available in the event of a fire. This capability will also serve to reduce the environmental effects of fires caused by lightning and other natural phenomena in the vicinity.

Pipeline Rupture

The magnitude of the accidental event would depend on the volume of the spill, its location, and time of year. The duration of the environmental effect is dependent on cleanup possibilities.

To mitigate environmental effects from accidental pipeline rupture, appropriate safety, spill containment and recovery and environmental protection measures will be incorporated into the pipeline right-of-way design, particularly in proximity to waterbodies. Emergency Spill Response Plans will be updated as discussed in Chapter 4. Mitigation measures will be developed to reduce the environmental effects of any pipeline rupture.

Tailings Pipeline

The tailings slurry from the open pit phase and the reclaim circuit will be conveyed through pipelines along the north shore of Camp Pond, Otter Pond and Headwater Pond. The tailings slurry pipeline route will be extended north to the North Tailings Basin during underground operations.

The tailings pipeline is designed so that tailings should not be released into streams or water bodies in the case of an accidental event. Spilled tailings slurry will be contained in the containment ditch and/or emergency dump pockets and will be removed and transported to the North Tailings Basin.

Effluent Pipeline Failure - Water Treatment Plant

A 10-km pipeline will convey treated effluent for discharge to Edward's Cove. The most environmentally sensitive segments of this pipeline will be situated at the crossing of Camp Brook and approximately 1 km north of the mill site, where the pipeline is in close proximity to Reid Brook. In the event of a partial break, approximately 20 percent of the pipeline flow could be released. Assuming a one-hour detection time, about 160 m³ of treated effluent would be released. The average flow in Camp Brook is approximately 2,100 m³/h, which will provide at least a ten fold dilution to any spilled material before it enters Reid Brook.

A rupture could result in habitat modification due to scouring and resulting sedimentation.

Reversibility is medium for physical effects, as the area of deposition is expected to be relatively small and the dilution provided by Camp Pond high.

Storm Events

All dams and spillways will be designed and constructed in accordance with standard engineering practice and will accommodate probable maximum precipitation events.

Storm events will vary widely in duration and intensity. Only one emergency spillway is located within each tailings basin. This location is selected based on environmental criteria. Factors influencing the duration and geographic extent of storm events include time of year and location within the watershed.

The consequences of a storm event would depend on the volume of water released and the time of year. Under extreme storm conditions, the spillway will discharge water from Headwater Pond to the Throat Bay watershed. Spillway discharge at the North Tailings Basin would occur at the Dam 2 location. These events would happen during periods of high precipitation, so there would be a higher than normal level of dilution in the watersheds which would reduce any environmental effect to the environment.

Factors influencing the duration and geographic extent of the environmental effects include time of year and location within the watershed. Depending on the impoundment affected by a storm, the composition of the discharge would differ. Discharge from the South Sedimentation Pond would result in release of sediment. However, discharges from other impoundments would also contain metals, and other contaminant materials.

Dam Failure

A total dam failure scenario is considered to be highly unlikely. All dams will be built to meet the design criteria for the Canadian Dam Safety Association Guidelines. Dam failures are usually avoidable by proper design, routine inspection, and maintenance. Should a failure occur, corrective actions will be employed to reduce the extent of solids migration downstream. Corrective actions will include additional dam development, stream diversion, and removal of displaced solids and subsequent re-confinement.

The release of untreated water would affect the receiving waters, and the deposition of the tailings would have long-term environmental effects on the sediment and water quality.

Road Washout or Flooding

Road washout or flooding may occur as a result of natural blockages in streams or unanticipated events. Factors influencing the geographic extent and duration of environmental effects from road washout or flooding include time of year and location in watershed.

A washout would cause bank and stream bed erosion, resulting in the transportation of fine and possibly coarse materials downstream. Potential environmental effects include increases in TSS, habitat smothering, lethal or chronic effects on fish/ invertebrates, avoidance of habitat and changes in water quality. Early life stages would be most susceptible to TSS, due to limited mobility. Spawning gravel could be clogged with fine sediments, rendering them unsuitable or smothering incubating eggs and fry. Benthic invertebrates would drift or be killed within the zone of influence. Adult fish would be subjected to short term increases in TSS and could avoid certain areas. Migration of Arctic charr and brook trout in Reid Brook could be affected by increased turbidity and flow.

No crossings are located directly on Reid Brook. Reversibility is high due to the dynamic nature of streams, high spring discharges and high spring bedload transportation.

11.2.1.11 Cumulative Environmental Effects
Increased fishing pressure is the only activity that may concurrently interact with fish in the Landscape Region. Commercial fishing pressure on the Voisey's Bay anadromous Arctic charr stock will interact with VBNC activities, as will subsistence and recreational fishing pressure.

A commercial fisheries harvest of anadromous Arctic charr from the Newfoundland and Labrador coast began in 1860. Commercial fishing is ongoing, but effort has decreased considerably since 1994. Detailed records have been collected from 1974-1994 for the Voisey's Bay and Nain stocks (Dempson 1995). A total of 200,600 Arctic charr with a mean weight of 1.91 kg and a total weight of 383 tonnes were removed from the Voisey's Bay stock. In the Nain stock, 536,930 Arctic charr with a mean weight of 1.76 kg and a total weight of 945 tonnes were removed. These values are approximately equivalent to 12,000 and 32,000 individuals harvested annually from Voisey's Bay and Nain stock units, respectively.

"And when the fish started to get scarce in the bay we would follow the fish out the bay to the outside�" (Abel Leo, through translator, Panel scoping meeting in Nain, April 17, 1997)

Over 200,000 Arctic charr were removed from Voisey's Bay over a period of 20 years, or approximately 10,000 each year. While it is difficult to reach an estimate of the total population from which these 10,000 were drawn, the fact that the population has persisted indicates that it would be at least 2-3 times that number (25,000-30,000 individuals), not counting juveniles (Johnson, L. pers. comm.). This is probably a fraction of the stock existing before the introduction of net fishing (Johnson, L. pers. comm.).

Inuit observe that charr are gradually recovering in the river systems of the Nain District and north of the Kiglapait mountains (Williamson 1997).

The growth and intensity of the commercial Arctic charr and salmon fishery in the Nain District in the 1980s brought about critical decreases in the numbers and size of the fish caught, culminating in the DFO buyback of charr/salmon licences in 1993. In 1996, only 19 fishermen were commercially fishing for Arctic charr (Williamson 1997; JWEL 1996).

There is, in 1997, the beginnings of an attempt to revive the commercial charr fishery as a weir fishery in the rivers themselves, with carefully controlled catches of particular year classes (Williamson 1997).

In general, the following conclusions may be made:

the Voisey's Bay stock continues to be exploited and abundance is lower than pre-exploitation levels;
the Arctic charr removed represent a potential interaction with Project activities affecting the Reid Brook Arctic charr; and
the stock has been depleted by the commercial fishery.

The migratory pattern, long life cycle and slow growth rate of Arctic charr renders it highly susceptible to intensive exploitation. It is evident that the present status of the Voisey's Bay and Nain stocks is very far from their pre-exploitation condition, and given the absence of environmental change and obstruction on the rivers or pollution, it may be concluded that this is the result of intensive fishing (Johnson, L. pers. comm.).

Both recreational and subsistence fishing currently occur within the Voisey's Bay area and are expected to continue to occur. Although most pressure is focused on the anadromous Arctic charr populations, landlocked populations are also exploited. Very little information is available to quantify existing pressure or assess the environmental effects on stocks. However, Aboriginal peoples have fished in this area historically and Innu have relied on this area frequently in the past. Subsistence fishing, primarily by hook and line, has intensified over the last 20 years. Recently, Ikadlivik Brook has become a frequented winter fishing site. Inuit have expressed concerns about over-fishing at these winter sites (Williamson 1997).

A conservative prediction would indicate an increase in recreational fishing as access to and awareness of the Voisey's Bay area increases.

"Unregulated hunting and fishing by non-residents was cited as an important concern by several focus groups. Outsiders, passing through Nain on the way to Voisey's Bay work sites or to other exploration camps, have been observed arriving with guns and fishing gear." (LIA 1996:25)

Increased angling pressure for subsistence and recreational fishing could result in the removal of a number of adults from various watersheds in the Assessment Area. This could affect population age structure and abundance. However, the probability is higher that fishing pressure will be directed towards the anadromous Arctic charr in the Reid Brook, Ikadlivik Brook, and Kogluktokoluk Brook system.

By nature, anadromous Arctic charr are susceptible to fishing pressure due to the large concentration of adults migrating into relatively confined freshwater channels and the large portion of population confined to the area during the summer and early fall. Although they do not feed in freshwater, anadromous fish strike readily at fishing gear and are susceptible to "jigging". Unregulated fishing during migration could result in sexually mature adults being removed from the population prior to spawning. Fishing in the spawning season could reduce spawning success by disturbing fish or destroying redds (locations of eggs) by walking in streams. Fishing at Reid Falls would target a localized concentration of adults. This concentration usually occurs during the fall; therefore, the fall represents the highest risk time period for environmental effects on the Arctic charr population.

11.2.1.12 Environmental Design, Mitigation and Optimization
Several environmental design and mitigative strategies will be used to reduce or avoid fish and fish habitat losses. Many of these are common and sound environmental practices, and are often required as conditions of permits. Other measures that address site-specific or generic issues are also to be used.

"We are concerned that hunting and fishing by non-natives on Aboriginal lands will further deplete the animal, fish and bird population." (Jim Webb, Panel scoping session in Nain, April 17, 1997)

The main mitigations for the protection of fish and fish habitat include:

with respect to the Reid Brook Arctic charr population, efforts have been made to afford this stream maximum protection from potential environmental effects;
a "no fishing" policy;
diversion of potentially contaminated effluent discharges away from Reid Brook watershed to offer protection for the Reid Brook Arctic charr population;
where discharges occur into freshwater, treatment and compliance with applicable regulations;
limiting, where practicable, Project activities within Reid Brook watershed;
consolidation of facilities and reduction of areas of disturbance;
reduced alteration of surface water and groundwater patterns and flow;
compliance with the EPP for erosion and sediment control, road grading and drainage, blasting, excavation and dredging, and road and airstrip de-icing;
education and training of personnel on protection of fish habitat, with regards to good practice;

adherence to applicable federal and provincial regulations and policies;
design of diversion channels to control erosion and/or facilitate fish passage;
design of stream crossings to reduce habitat loss and facilitate fish passage;
limit construction and Project operations near waterways during sensitive periods for fish (avoidance of spawning, hatching); and
water intakes to include fish screens.

VBNC is developing fish and fish habitat protection measures that will include:

the harvesting for use of fish in Headwater Pond and the North Tailings Basin;
a Fish Habitat Compensation Plan;
an action plan to prevent the loss of fish as a result of stream diversions; and
elements of the Environmental Protection Plan.

In the planning and design of the Project, VBNC has applied strategies for habitat protection and conservation to reduce possible harmful alteration, disruption, or destruction (HADD) to fish habitat. DFO's hierarchy of preferred options for habitat Conservation and Protection are relocation, redesign, mitigation and habitat compensation.

VBNC has used this hierarchical approach to try to reduce the environmental effects of the Project on aquatic ecosystems, particularly Reid Brook watershed because it contributes to the commercial (anadromous) Arctic charr resource.

VBNC has also developed an EPP to eliminate or reduce environmental effects of many Project activities on aquatic ecosystems. This includes procedures for proper culvert installations, sediment control measures, road construction, and hazardous material storage. DFO has recognised these measures as appropriate mitigation to reduce and avoid HADD. The Fish Recovery Action Plan will outline measures to recover and release fish from dewatered stream sections, thus avoiding fish losses during the construction phase.

DFO's "no net loss" guiding principle for habitat management requires compensation for HADD as a condition of the authorisation issued under Subsection 35 (2) of the Fisheries Act. The hierarchy of preferred compensation options as provided by DFO are: create similar habitat at or near the development site within the same ecological unit; create similar habitat in a different ecological unit that supports the same stock or species; increase the productive capacity of existing habitat at or near the development site and within the same ecological unit; increase the productive capacity of a different ecological unit that supports the same stock or species; or increase the productive capacity of existing habitat for a different stock or a different species either on or off site.

DFO has determined that the Project will result in HADD of fish habitat. VBNC has identified compensation options to DFO and is in the process of negotiating a compensation plan for submission to DFO including:

engineering replacement stream habitat;
providing anadromous stocks with improved access to overwintering pond habitat; and
introducing fish into fishless habitat.

These possibilities must all be tempered with regard to DFO's stated preferences. As well, DFO is presently addressing other policy issues such as replacement for standing water (pond) habitat. Once the environmental assessment process is concluded, VBNC will submit a plan to DFO which conforms with the compensation and follow-up monitoring requirements.

Other mitigation and optimization measures include the following.

Placing siltation screens before potential receiving environments, such as in Camp Pond, during construction and decommissioning to reduce siltation. Work will be restricted during sensitive spawning times for brook trout.
Taking precautions necessary to prevent fire hazards. Contingency planning will enable a quick and effective response to an on-site fire.
Building all dams (and where appropriate, dykes) to meet the design criteria for the Canadian Dam Safety Association (CDSA) Guidelines. The EPP will detail contingency plans to control any release of contaminated water in the case of dam failure.

11.3 Residual Environmental Effects
The significance criteria for residual environmental effects on water quality are based on toxicity (chronic and acute) as discussed in Chapter 10. By contrast the residual environmental effects on fish and the biota that comprise their habitat (food) use population-based criteria. This takes into account the numbers of individuals affected and the duration or extent of the effect.

The definitions for the rating of residual environmental effects significance follow:

A major (significant) residual environmental effect is one affecting a whole stock or population of a species in a watershed in the Freshwater Fish and Fish Habitat Assessment Area in such a way as to cause a change in abundance and/or change in distribution beyond which natural recruitment (reproduction and immigration from unaffected areas) would not return that population, or any populations or species dependent upon it, to its former level within several generations. A residual environmental effect on fish habitat that has the same consequence for populations would also be a major residual environmental effect. As the Fisheries Act requires that compensation be provided for HADD in recognition of DFO's no net loss guiding principle, however, the rating can effectively be considered negligible where compensation for lost habitat is implemented by agreement with DFO.

A moderate (significant) residual environmental effect is one affecting a portion of a population in a watershed in the Freshwater Fish and Fish Habitat Assessment Area that results in a change in abundance and/or distribution over one or more generations of that portion of the population, or any populations or species dependent upon it, but does not change the integrity of any population as a whole; it may be localized. A change in fish habitat (including food sources) that produces the same result in populations would be moderate.

A minor (not significant) residual environmental effect is one affecting a specific group of individuals in a population in a watershed in the Freshwater Fish and Fish Habitat Assessment Area at a localized area and/or over a short period (one generation or less), but not affecting other trophic levels or the integrity of the population itself. As above, equivalent population environmental effects ratings are assigned to environmental effects on fish habitat.

A negligible (not significant) residual environmental effect is one affecting the population or a specific group of individuals in the Freshwater Fish and Fish Habitat Assessment Area at a localized area and/or over a short period in such a way as to be similar in effect to small random changes in the population due to natural irregularities, but having no measurable environmental effect on the population as a whole.

In the above definitions, the population referred to is either landlocked fish populations within the Assessment Area watersheds; benthic invertebrates (snails) that are food for fish; or the anadromous Arctic charr that use freshwater habitat in the Assessment Area from August to June (10 months).

The following summary of the residual environmental effects is presented recognizing the following four points.

Fish habitat losses are not included, as all losses must be compensated to achieve no net loss.

Environmental effects of reduced flows will either be mitigated by the provision of minimum instream flow or by compensation for unavoidable habitat loss.

Fish in Headwater Pond and North Tailings Basin will be removed for local consumption and thus the resource will not be lost. Future production losses will be replaced by the required compensation plan.

Fish losses in dewatered stream sections will be mitigated by the relocation of stranded fish.

The residual environmental effects remaining after mitigation are presented in Tables 11.12 to 11.15. In each table the Project phase is identified along with the residual environmental effects that will occur in each phase. A significance rating is provided for the cumulative residual environmental effects in each phase. Where a significant adverse ranking is identified, the likelihood of it occuring is given, along with an evaluation of the sustainable use of the renewable resource.

Table 11.12 Residual Environmental Effects for Reid Brook Watershed^a

Project Phase	Residual Environmental Effect	Significance	Likelihood^a(Probability)	Sustainable Use (Capacity) of Renewable Resource^a
Construction	Habitat alteration due to siltation	negligible (not significant)	n/a	n/a
Operation	Habitat alteration due to airborne particulates from the open pit Sub-lethal effects on fish by blasting	minor (not significant)	n/a	n/a
Decommissioning	Habitat alteration due to siltation	negligible (not significant)	n/a	n/a
Post-Decommissioning	Habitat alteration due to pit water into Camp Pond Sub-lethal effects on fish due to pit water into Camp Pond	minor (not significant)	n/a	n/a
Accidental Events	Habitat loss, fish loss, habitat alteration or chronic effects on fish	negligible (not significant) to major (significant)	low	high to low
^a likelihood and sustainable use of renewable resources are only defined for environmental effects that are significant (moderate or major) (CEAA: 1994: 84, 187) Note: Without a compensation plan the residual environmental effect for only Headwater Pond would be: major (significant) residual environmental effect due to the loss of fish habitat (total pond loss), but compensation will be provided for all lost habitat, resulting in a reduced residual environmental effect that is not significant (negligible) major (significant) residual environmental effect could be anticipated due to the loss of the fish populations, but the fish will be harvested and used, resulting in a residual environmental effect that is not significant (negligible)

Table 11.13 Residual Environmental Effects for North Tailings Basin Watershed^a

Project Phase	Residual Environmental Effect		Significance	Likelihood^a(Probability)		Sustainable Use (Capacity) of Renewable Resource^a
Operation	Habitat alteration due to siltation during construction		negligible (not significant)	n/a		n/a
Decommissioning	Habitat alteration due to siltation		negligible (not significant)	n/a		n/a
Post-Decommissioning	Habitat alteration due to water release from North Tailings Basin Sub-lethal effects on fish due to water release from North Tailing Basin		moderate (significant)	high		high
Accidental Events		Habitat loss, fish loss, habitat alteration or chronic effects on fish	negligible (not significant) to major (significant)		low	high to low
^a likelihood and sustainable use of renewable resources are only defined for environmental effects that are significant (moderate or major) (CEAA: 1994: 84, 187) Note: Without a compensation plan, the residual environmental effect for only the North Tailings Basin (Pond 55 and Pond 56 only) would be: Major (significant) residual environmental effect is anticipated due to the loss of fish habitat (total pond loss), but compensation will be provided for all lost habitat, resulting in a residual environmental effects rating that is not significant (negligible) Major (significant) residual environmental effect could be anticipated due to the loss of the fish populations, but the fish will be harvested and used, resulting in a residual environmental effect that is not significant (negligible)

Table 11.14 Residual Environmental effects for Throat Bay Watershed

Project Phase	Residual Environmental Effect	Significance	Likelihood^a(Probability)	Sustainable Use (Capacity) of Renewable Resource^a
Construction	Habitat alteration due to siltation	negligible (not significant)	n/a	n/a
Operation	Habitat alteration due to seepage from Headwater Pond	negligible (not significant)	n/a	n/a
Decommissioning	Habitat alteration due to siltation	negligible (not significant)	n/a	n/a
Post-Decommissioning	Habitat alteration due to water release from Headwater Pond	moderate (significant)	n/a	n/a
	Sub-lethal effects on fish from water release from Headwater Pond
Accidental Events	Habitat loss, fish loss, habitat alteration or chronic effects on fish	negligible (not significant) to major (significant)	low	high to low
^a likelihood and sustainable use of renewable resources are only defined for environmental effects that are significant (moderate or major) (CEAA: 1994: 84, 187)

Table 15.15 Residual Environmental Effects for Pond 67 Watershed

Project Phase	Residual Environmental Effect	Significance		Likelihood^a(Probability)	Sustainable Use (Capacity) of Renewable Resource^a
Operation	Habitat alteration due to seepage from North Tailings Basin Sub-lethal effects on fish of seepage		minor (not significant)	n/a		n/a
Decommissioning	Habitat alteration due to seepage Sub-lethal effects on fish of seepage	minor (not significant)		n/a	n/a
Post-Decommissioning	Habitat alteration due to seepage Sub-lethal effects on fish of seepage	minor (not significant)		n/a	n/a
Accidental Events	Habitat loss, fish loss, habitat alteration or chronic effects on fish	negligible (not significant) to major (significant)		low	high to low
^a likelihood and sustainable use of renewable resources are only defined for environmental effects that are significant (moderate or major) (CEAA: 1994: 84, 187)

Negligible (not significant) residual environmental effects are predicted for Southern, Pond 65, Option 5 and Little Reid Brook watersheds (barring accidents). Residual environmental effects tables are not presented for these watersheds.

Reid Brook, Little Reid Brook, North Tailings Basin, Pond 65, Throat Bay Brook and Southern Watersheds are projected to have negligible (not significant) residual environmental effects from siltation events occurring during construction and decommissioning. These residual environmental effects are not depicted on the following figures.

Minor (not significant) residual environmental effects are predicted for the following locations and times (in roughly chronological order):

Camp Pond and Camp Brook: there is a predicted minor (not significant) residual environmental effect on freshwater snails from copper and on fish from aluminum as a result of airborne contaminants from the open pit during open pit operation ( ).

Figure 11.17 Spatial Extent of Residual Environmental Effects on Snails During Operations

Camp Pond: there may be a minor (not significant) residual environmental effect on fish in Camp Pond due to vibrations from blasting activity in the open pit (Figure 11.18).

Figure 11.18 Spatial Extent of Residual Environmental Effects on Charr During Operations

Pond 67 Brook downstream of Dam 3: there is a predicted minor (not significant) residual environmental effect on snails from nickel and on charr from copper, lead and aluminum due to seepage during underground operation (Figure 11.17) and post-decommissioning (Figure 11.19).

Figure 11.19 Spatial Extent of Residual Environmental Effects on Snails During Post-Decommissioning

North Tailings Basin Brook downstream of Dam 2 and in Pond 57: there is a predicted minor (not significant) residual environmental effect on charr from nickel due to water release during post-decommissioning (Figure 11.20).

Camp Pond and Camp Brook: there are predicted minor (not significant) residual environmental effects on snails from nickel and copper, and on Arctic charr from lead and aluminum, during post-decommissioning due to the overflow of the decommissioned open pit to Camp Pond (Figure 11.19).

Throat Bay Brook, Ponds 64, 70 and 71: there is a predicted minor (not significant) residual environmental effect on snails from nickel due to the Headwater Pond release in post-decommissioning (Figure 11.19).

Throat Bay Brook, Pond 64: there is a predicted minor (not significant) residual environmental effect on charr from nickel due to the Headwater Pond release in post-decommissioning (Figure 11.20).

Figure 11.20 Spatial Extent of Residual Environmental Effects on Charr During Post-Decommissioning

Moderate (significant) residual environmental effects are predicted at the following locations:

North Tailings Basin Brook downstream of Dam 2 and in Pond 57: there is a predicted moderate (significant) residual environmental effect on snails from nickel and on Arctic charr from aluminum due to water release during post-decommissioning (Figure 11.19 and 11.20).

Throat Bay Brook, Pond 64: there is a predicted moderate (significant) residual environmental effect on charr from aluminum due to the Headwater Pond release in post-decommissioning (Figure 11.20).

11.3.1 Construction
As detailed in Section 11.2, freshwater fish and fish habitat may be disturbed by Project activities involving stream crossings and related general construction and earthworks. Sedimentation is potentially the primary issue, although it will be largely reduced by mitigation measures. Residual environmental effects should be negligible (not significant), localized and unlikely. These locations include North Tailings Basin Brook, Option 5 watershed, Reid Brook watershed, Little Reid Brook, and the Southern watershed. Residual environmental effects due to the diversion of streams or impoundment at Headwater Pond, North Tailings Basin and the airstrip will be addressed by compensation for lost habitat and the prevention of fish strandings.

11.3.2 Operation
One of the underpinnings of the Project design is the reduction or elimination of environmental effects on freshwater ecosystems, particularly Reid Brook and the anadromous Arctic charr that are a component of the Voisey's Bay commercial stock. Fish and fish habitat will be affected by seepage through dams at Headwater Pond and the North Tailings Basin. Minor (not significant) residual environmental effects will occur to limited areas of Pond 67 watershed, and minor (not significant) to moderate (significant) residual environmental effects will occur in the headwaters of Throat Bay watershed. Neither location is anadromous fish habitat. These effects may vary over time as described in Chapter 10.

Total population loss for Arctic charr, brook trout and their food species in Headwater Pond and North Tailings Basin as a result of mine rock and tailings disposal would, without mitigation or compensation, be considered a major (significant) residual environmental effect. These areas may be a small component in the subsistence harvesting by people in the area because effort is concentrated in other locations that have higher production and larger fish. Nevertheless, due to the policies of DFO, habitat losses will have compensation provided. As well, fish losses will be mitigated by harvesting the fish before modification of their habitat and distributing the fish to local communities. In consideration of these mitigating factors (compensation and harvesting fish for distribution prior to habitat loss) the residual environmental effect is rated negligible (not significant).

11.3.3 Decommissioning
Potential residual environmental effects during decommissioning will result from physical alteration or siltation (minor (not significant)) and from continued exposure to seepage (minor (not significant) to moderate (significant)), as discussed above.

11.3.4 Post-Decommissioning
Many physical changes to the flows and hydrology of the site will occur as impounded areas are allowed to revert to the natural hydrology. Discharges to freshwater will only occur when the water quality of the effluent is in compliance with applicable regulatory standards. Potential residual environmental effects after closure will result from seepage through dams at Headwater Pond and the North Tailings Basin, and surface water discharge (overflow) from the open pit. Additional or increased residual environmental effects are predicted as a result of the direct release of water from Headwater Pond and the North Tailings Basin. Moderate (significant) residual environmental effects will result only in upper Throat Bay watershed and downstream of the North Tailings Basin. The residual environmental effect may not actually occur due to the conservative assumptions that were used to predict concentrations and due to local or seasonal conditions.

The potential residual environmental effects on the sustainable use of fish in the affected areas is high for those areas where minor (not significant) or moderate (significant) effects are anticipated, and negligible to minor (not significant) for those cases where total pond loss will occur.

11.3.5 Accidental Events
Accidental events that could result in major (significant) residual environmental effects to freshwater fish and fish habitat are: fires, dam failures, effluent pipeline ruptures, spill of hazardous material, road wash-outs, and storm events. However, these events are unlikely. Contingency plans to address accidental events will apply.

11.3.6 Follow-Up Program
"But I would like to make sure that there were things in the policies that would guarantee that wildlife and fishing monitoring was not only possible but strongly adhered to." (Patty Way, Panel scoping meeting in Cartwright, May 6, 1997)

AQUAMIN (1996) has recommended that the future revised MMLER include a requirement that mine operators develop, conduct, and report on a site-specific EEM program that:

monitors key components of aquatic ecosystems (e.g., water, sediments, fish, benthic invertebrates);
uses tools that are appropriate for site condition; and
includes methodologies that are determined at the local level.

In freshwater environments, a monitoring program will be developed and conducted to determine the downstream environmental effects of Project operations (Chapter 4).

Monitoring will concentrate on the Headwater Pond-Camp Pond area, and the Camp Brook/Lower Reid Brook, where the majority of Project activities will occur. Monitoring will also focus on areas downstream of the North Tailings Basin dam structures.

11.4 References

Literature Cited

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Personnel Communications

Johnson, L., Fisheries Consultant, BC.

MacKinley, S, Applied Biometrics Inc., University of Waterloo, Waterloo, ON.

Makowecki, R., Westworth,
Brusnyk and Associates, Edmonton, AB.

Shears, M., Science Branch, Department of Fisheries and Oceans, St. John's, NF.

Appendix 11A

Environmental Effects Assessment Synthesis:
Freshwater Fish and Fish Habitat

Environmental Effects Assessment Synthesis: Freshwater Fish and Fish Habitat

			Environmental Effects Criteria
Project Phase	Project Activity	Environmental Effect	Magnitude	Geographic Extent	Timing/ Duration/ Frequency	Reversibility	Ecological/ Social/ Cultural Context
Construction	stream crossings and earthworks	siltation leading to habitat alteration	low	Reid Brook Little Reid Brook North Tailings Basin Throat Bay Brook	throughout construction, intermittent	high	subsistence harvesting
Operation	mine rock/ tailings disposal	fish mortality	high	North Tailings Basin Headwater Pond	indefinitely	nil	subsistence harvesting
	seepage	habitat alteration, chronic effects on fish	low	Throat Bay Brook Pond 67 Brook North Tailings Basin	throughout operation	low	subsistence harvesting
Decommissioning	removal of stream crossings and earthworks	siltation leading to habitat alteration	low	Reid Brook Little Reid Brook North Tailings Basin Throat Bay Brook	throughout decommissioning	high	subsistence harvesting
	seepage	habitat alteration, chronic effects on fish	low	Throat Bay Brook Pond 67 Brook North Tailings Basin	throughout decommissioning	low	subsistence harvesting
Post-decommissioning	Pit flooding	habitat alteration, chronic effects on fish	low	Camp Pond, Camp Brook	100 years	low	subsistence harvesting
	Release of impounded water	habitat alteration, chronic effects on fish	low to medium	Throat Bay Brook North Tailings Basin Brook	100 years	low	subsistence harvesting
	seepage	habitat alteration	low	Throat Bay Brook Pond 67 Brook North Tailings Basin	100 years	low	subsistence harvesting