Effects of natural and Human-caused Disturbances on Marine Birds and Pinnipeds at Race Rocks, British Columbia

Prepared forDepartment of National Defence
Canadian Forces Base Esquimalt
Victoria, BC &
Public Works & Government Services Canada
Pacific Region Victoria, BC
Prepared by Mike W. Demarchi (M.Sc. R.P.Bio.) and Michael D. Bentley
LGL Limited
environmental research associates
9768 Second Street Sidney, BC V8L 3Y8

Cover photo: northern sea lions hauled out in Race Rocks Ecological Reserve, November 2003

EXECUTIVE SUMMARY

On behalf of the Department of National Defence and Public Works & Government Services Canada, LGL Limited conducted a 14-month assessment of natural and human-caused factors with potential to affect key species of marine birds and pinnipeds at Race Rocks, British Columbia.

This study had the following objectives:

Summarize legislation with direct or indirect relevance for marine birds and mammals at Race Rocks.
Document whether the study area is being utilized for: a breeding area, a summering or wintering area, migration corridors, or staging areas by marine birds and pinnipeds.
Assess the affects of abiotic factors on the abundance of marine birds and pinnipeds in the study area.
Document and assess the effects of demolitions from the Whirl Bay Underwater Demolition Range, Bentinck Island Demolition Range, and Christopher Point Ordnance Disposal Range on marine birds and pinnipeds in the study area.
Document the effects of ecotour boats, other boats, aircraft, and pedestrian traffic in and near the study area on marine birds and pinnipeds.
Determine if abiotic factors such as air temperature, wind speed and direction, cloud cover, wave height, tide height ameliorate or amplify animal responses to anthropogenic disturbances.
Examine local populations of marine mammals and birds to assess the immediate and cumulative effects of local anthropogenic activities such as demolition training, ecotouring, pleasure boating, aircraft overflights, and human activities associated with operations on Great Race Rock.

During 6 October 2002 through 27 November 2003, 52 monitoring sessions were conducted. Many different weather conditions, sea conditions, and human-caused disturbance events were observed. Tidal conditions changed considerably on hourly, daily and seasonal timescales. Animal distributions in the study area were very aggregated and showed clear patterns of seasonal variation.

The Federal and Provincial status of key wildlife species, together with a brief species account of each were presented. Species that are common at Race Rocks use the area to fulfil life history needs including, non-breeding seasonal ranges, breeding habitat, migration/staging, and moulting. Important uses of the area by common species are summarized in the table below. Race Rocks provides highly suitable habitat, but with the possible exceptions of northern sea lions and black oystercatchers, the area is not likely providing any species with critical habitat (see page 55) at present.

Northern elephant seals were the least abundant pinniped throughout the study. Maximum daily counts ranged from 0 in the late autumn to 22 in the spring. Harbour seals were the most abundant pinniped throughout the study. Maximum daily counts ranged from 0 in the winter to 667 in the summer. California sea lions were the third most abundant pinniped during study. Maximum daily counts ranged from 0 in the winter and summer to 244 in late summer.

Northern sea lions were the second most abundant pinniped during the study. Maximum daily counts ranged from 0 in the summer to 555 in late autumn. Although the northern sea lion is Red Listed in British Columbia, all individuals that occur at Race Rocks are believed to be from the Eastern Stock. Whereas the Western Stock is listed as Endangered under the U.S. Marine Mammal Protection Act, the Eastern Stock is not.

Summary of the presence and important seasonal uses of Race Rocks made by species that commonly occur there.

Within seasons, weather and sea conditions affected the abundance of some bird and pinniped species, and the probability that a disturbance event would disturb some species to the point of displacement. Pinnipeds, and particularly northern sea lions, responded to blasting by increasing activity and leaving a haulout. Blast-caused disturbances are believed to be triggered by responses to sounds that “scare” rather than injure animals. Observations of the effects of blasting on birds and pinnipeds were made during days when at least one of the three ranges was active. Because so few observations were made during blasting in Whirl Bay (4 days) and on Christopher Point (1 day), the value of any inference made from those data is limited. None of the data we collected suggested that blasting in Whirl Bay had any adverse effects on bird or pinniped behaviour in the study area. Blasting monitored on Christopher Point occurred at a time (20 February 2003) when few birds and pinnipeds were in the study area. Blasting on Bentinck Island was the most frequent form of blast-related, potential disturbances observed. Pre-disturbance pinniped activity levels did not differ significantly among the types of monitoring days. There were no significant differences in mean activity levels of pinnipeds during samples throughout the day when no disturbance stimulus was attributed to the observation when the Bentinck Island Range was active compared to days when the range was inactive. Of all pinniped species that occur at Race Rocks, northern elephant seals were the most tolerant of any forms of disturbance we observed. Blasts on Bentinck Island were the only disturbance to consistently cause a noticeable increase in harbour seal activity for those animals that were not displaced. Blasts on Bentinck Island caused the most noticeable increases in California sea lion activity. Blasts on Bentinck Island and unknown disturbance stimuli had noticeable effects on California sea lion displacement from land to water. Blasts on Bentinck Island caused the greatest increase in northern sea lion activity and ecotour boats also caused an increase in activity levels; particularly on days when the Bentinck Island Range was active. Blasts on Bentinck Island and unknown disturbance stimuli had the most noticeable effects on northern sea lion displacement from land to water. Blasts on Bentinck Island caused at least 1 northern sea lion to move to the water 90.7% of the time the species was present on a haulout. Boats and pedestrians also displaced these animals. Despite the northern sea lion’s sensitivity to blasting, displaced individuals typically began returning to the haulout within minutes or hours of the disturbance, indicating that they were not displaced from the study area or very far from it. Pedestrians displaced seals, sea lions and gulls from Great Race Rock.

Pedestrian-caused disturbances typically involved: intentional clearing northern elephant seals off the boat launch; incidental displacement of harbour seals, incidental displacement of California sea lions, and to a lesser extent, northern sea lions; and incidental displacement of gulls. Overflights by raptors such as bald eagles were the most consistent (93.7% of events recorded) disturbance that caused some animals (in this case, primarily gulls) to take flight or enter the water. Very low numbers of aircraft passed over or near the monitored area, causing little or no apparent disturbance to wildlife. The Coast Guard helicopter might be an exception.

Kayakers were rare in the monitored area. Boats operated by LBPC were observed regularly throughout the monitored period, and together with the LGL boat, were the only boats to regularly dock at Race Rocks. LBPC and LGL boats displaced modest numbers of birds and pinnipeds from the dock area during most arrivals and departure. Pleasure boats were observed throughout the monitored period, mainly in summer. Harbour seals, sea lions, and cormorants, were all displaced by pleasure boaters. Some poaching of fish and shellfish occurs by recreational fishermen and recreational scuba divers, respectively. Ecotour boats constituted the greatest amount of boat traffic in the monitored area, with

peak visitation rates during the height of the summer tourist season. Daily numbers of ecotour boats ranged from 0 to 43, with as many as nine present in the study area at the same time. Some ecotour boats were observed to displace harbour seals, sea lions, cormorants, and gulls, but most caused no observable effects. The fact that Race Rocks provides highly suitable habitat for marine birds and pinnipeds is indisputable. However, determining the extent to which Race Rocks provides important or critical habitat for any given species is not so straightforward. Northern Sea Lion (COSEWIC, Special Concern; Conservation Data Centre, Red Listed) is the only species that could be reasonably expected to pose any local conservation concerns at Race Rocks at present. The black oystercatcher (COSEWIC, Not Listed; Conservation Data Centre, Yellow Listed) might become a concern in the future at Race Rocks due to the relatively low number of breeding pairs in the province. Marine birds and pinnipeds at Race Rocks are exposed to a number of different disturbance stimuli that alter normal behaviour patterns. The fact that human activities disturb wildlife does not in itself provide a basis to ban such activities. Indeed, if that were the case, no people or boats would be permitted in the Race Rocks Ecological Reserve without authorization. If disturbances have no consequences for the population, or even if the population consequences are sustainable, restricting human activities for the sake of preventing disturbance is likely to have negative social and other consequences that are out of proportion to the impacts that are being avoided or mitigated.

By increasing animal activity and displacing animals from the land to the air and water, humans exert adverse effects on marine birds and pinnipeds at Race Rocks. However, no significant adverse effects stemming from single or cumulative disturbance types on the regional populations of any species of marine bird or pinniped at Race Rocks Ecological Reserve are expected to presently originate in, or immediately adjacent to, the study area.

ACKNOWLEDGEMENTS

Many people assisted with this study. We especially thank Duane Freeman (Department of National Defence, CFB Esquimalt, Formation Environment) and Andrew Smith (Public Works and Government Services Canada) for their leadership and assistance in conducting this important research. Duane Freeman and Tracy Cornforth (Formation Environment) provided constructive reviews of draft of this report. Rae-Ann Shaw (Public Works and Government Services Canada) provided important administrative assistance. Duane Freeman and his department staff reviewed a draft of this report. PO Rob Cantwell, PO Chris MacDonald, and PO Oliver provided important logistic support concerning training activities on Bentinck Island and Whirl Bay. ESO Al Carter provided information concerning Christopher Point. Rik Simmons, Don McLaren, and Debbie McKinnon (Province of BC) assisted with research permitting. Captain Terry Weber and Vivian Skinner (Canadian Coast Guard) provided access to the light tower. Phil Emery (Canadian Coast Guard) coordinated a staged helicopter landing. Angus Matthews, Garry Fletcher, and Mike and Carol Slater (Pearson College) provided logistical support on Great Race Rock. Peter Olesiuk (Department of Fisheries and Oceans) provided some information on pinnipeds. Gary Searing of LGL provided important assistance with the study proposal and reviewed a draft of this report. Steve Johnson reviewed portions of a draft of this report. Dorothy Baker of LGL Limited proofed draft of this report. Mike Demarchi, Steve Johnson and Sonya Meier supervised field activities. Michael Bentley, Karen Truman, Lucia Ferreira, Jim Ferguson, Virgil Hawkes, Dave Robichaud, Jason Smith, Andrew Davis, and Philina English assisted with data collection. All photographs were taken by the senior author, except where noted.

Suggested Citation: DEMARCHI, MW AND MD BENTLEY. 2004. Effects of natural and human-caused disturbances on marine birds and pinnipeds at Race Rocks, British Columbia. LGL Report EA1569. Prepared for Department of National Defence, Canadian Forces Base Esquimalt and Public Works and Government Services Canada. 103 p.

EXECUTIVE SUMMARY……………………………………………………………………………………………….i ACKNOWLEDGEMENTS……………………………………………………………………………………………..v CONTENTS………………………………………………………………………………………………………………vi
LIST OF TABLES……………………………………………………………………………………………………….viii
LIST OF FIGURES…………………………………………………………………………………………………….ix
LIST OF PHOTOS……………………………………………………………………………………………………..xi
LIST OF APPENDICES……………………………………………………………………………………………….xii

1 INTRODUCTION………………………………………………………………………………………………………1
1.1 STUDY OBJECTIVES……………………………………………………………………………………………1
2 RELEVANT LEGISLATION..………………………………………………………………………………………2
3 STUDY AREA AND VICINITY…………………………………………………………………………………….2
3.1 RACE ROCKS ECOLOGICAL RESERVE………………………………………………………………….2
3.2 MARINE TRAINING AND EXERCISE AREA WQ………………………………………………………….4
3.3 MARINE LIFE………………………………………………………………………………………………………7
3.3.1 Injury and Disturbance…………………………………………………………………………………………8
3.3.2 Species Accounts………………………………………………………………………………………………9
3.3.2.1 Brandt’s Cormorant (Not Listed; Red Listed)……………………………………………………………9
3.3.2.2 Double-crested Cormorant (Not at Risk; Blue Listed)…………………………………………………9
3.3.2.3 Pelagic Cormorant (pelagicus subspecies Not Listed; Red Listed – resplendens
…………subspecies Not Listed; Yellow Listed)……………………………………………………………………10
3.3.2.4 Bald Eagle (Not at Risk; Yellow listed)……………………………………………………………………10
3.3.2.5 Peregrine Falcon (anatum subspecies Threatened; Red Listed – pealei subspecies
………..Special Concern; Blue Listed)………………………………………………………………………………10
3.3.2.6 Black Oystercatcher (Not Listed; Yellow Listed)……………………………………………………….10
3.3.2.7 Black Turnstone (Not Listed; Yellow Listed)…………………………………………………………….10
3.3.2.8 Surfbird (Not Listed; Yellow Listed)……………………………………………………………………….11
3.3.2.9 Rock Sandpiper (Not Listed; Yellow Listed)……………………………………………………………..11
3.3.2.10 Heerman’s Gull (Not Listed; Yellow Listed)…………………………………………………………….11
3.3.2.11 California Gull (Not Listed; Blue Listed)…………………………………………………………………11
3.3.2.12 Herring Gull (Not Listed; Yellow Listed)………………………………………………………………..11
3.3.2.13 Thayer’s Gull (Not Listed; Yellow Listed)………………………………………………………………11
3.3.2.14 Western Gull (Not Listed; Yellow Listed)……………………………………………………………….11
3.3.2.15 Glaucous-winged Gull (Not Listed; Yellow Listed)……………………………………………………12
3.3.2.16 Pigeon Guillemot (Not Listed ;Yellow Listed)………………………………………………………….12
3.3.2.17 Northern Elephant Seal (Not at Risk; Yellow Listed)…………………………………………………13
3.3.2.18 Harbour Seal (Not at Risk; Yellow Listed)………………………………………………………………14
3.3.2.19 California Sea Lion (Not at Risk; Yellow Listed)………………………………………………………15
3.3.2.20 Northern Sea Lion (Special Concern; Red Listed)……………………………………………………16
3.3.2.21 Killer Whale (Northeast Pacific Southern Resident population: Endangered, Red Listed
……….Northeast Pacific Transient population: Threatened, Red Listed)……………………………………17

4 METHODS………………………………………………………………………………………………………………18

4.1 ANALYTICAL LIMITATIONS………………………………………………………………………………………19

. 4.2 DATA ANALYSES………………………………………………………………………………………………….20

5 RESULTS………………………………………………………………………………………………………………..20

5.1 CENSUS DATA………………………………………………………………………………………………………23

5.1.1 Cormorants………………………………………………………………………………………………………….25

5.1.2 Bald Eagle…………………………………………………………………………………………………………..26

5.1.3 Gulls………………………………………………………………………………………………………………….26

5.1.4 Northern Elephant Seal………………………………………………………………………………………….27

5.1.5 Harbour Seal………………………………………………………………………………………………………28

5.1.6 California Sea Lion……………………………………………………………………………………………….28

5.1.7 Northern Sea Lion………………………………………………………………………………………………..29

5.2 NATURAL AND HUMAN-CAUSED DISTURBANCES……………………………………………………….30

5.2.1 Effects of Disturbance on Animal Abundance from Morning to Afternoon……………………………30

5.2.1.1 Cormorants……………………………………………………………………………………………………….30

5.2.1.2 Gulls……………………………………………………………………………………………………………….30

5.2.1.3 Northern Elephant Seal……………………………………………………………………………………….32

5.2.1.4 Harbour Seal…………………………………………………………………………………………………….32

5.2.1.5 California Sea Lion……………………………………………………………………………………………..33

5.2.1.6 Northern Sea Lion……………………………………………………………………………………………….35

5.2.2 Effects of Discrete Disturbance Events on Animal Abundance and Behaviour..…………………….37

5.2.2.1 Effects on Harbour Seals……………………………………………………………………………………..40

5.2.2.2 Effects on California Sea Lions………………………………………………………………………………41

5.2.2.3 Effects on Northern Sea Lions………………………………………………………………………………..43

5.2.2.4 Disturbance by Killer Whales…………………………………………………………………………………45

5.2.2.5 Disturbance by Raptors………………………………………………………………………………………..45

5.2.2.6 Disturbance by Pedestrians and Domestic Animals…………………………………………………….46

5.2.2.7 Disturbance by Aircraft…………………………………………………………………………………………48

5.2.2.8 Disturbance by Boats…………………………………………………………………………………………..49

5.2.2.9 Disturbance by Blasting………………………………………………………………………………………..53

6 DISCUSSION..……………………………………………………………………………………………………………54

6.1 RELEVANT LEGISLATION…………………………………………………………………………………………54

6.2 USE OF RACE ROCKS BY MARINE BIRDS AND PINNIPEDS…………………………………………..55

6.2.1 Birds………………………………………………………………………………………………………………….56

6.2.2 Northern Elephant Seal…………………………………………………………………………………………..56

6.2.3 Harbour Seal………………………………………………………………………………………………………..56

6.2.4 California Sea Lion…………………………………………………………………………………………………57

6.2.5 Northern Sea Lion………………………………………………………………………………………………….58

6.3 EFFECTS OF NATURAL AND HUMAN-CAUSED DISTURBANCE……………………………………….58

6.3.1 Birds…………………………………………………………………………………………………………………..61

6.3.2 Northern Elephant Seal……………………………………………………………………………………………63

6.3.3 Harbour Seal…………………………………………………………………………………………………………63

6.3.4 California Sea Lion…………………………………………………………………………………………………..65

6.3.5 Northern Sea Lion……………………………………………………………………………………………………65

7 LITERATURE CITED……………………………………………………………………………………………………..69

. 8 APPENDICES..………………………………………………………………………………………………………….74

viii

LIST OF TABLES…………………………………………………………………………………………………………..Page
..

Table 1. Dates and active range status in WQ during 52 monitoring sessions at Race Rocks……………21

Table 2. Distribution (percent) of all observations of common species and groups in the Race Rocks study area during morning and afternoon censuses from October 2002 through November 2003……………………………………………………………………………………………………………………………..24

Table 3. Summary of the presence and important seasonal uses (shaded cells) of Race Rocks made by species that commonly occur there……………………………………………………………………………………………………….24

Table 4. Results of logistic regression analyses to detect the effect of, tide, swell height, and Bentinck Island demolitions on the relative change in numbers of animals in the Race Rocks census area in the afternoon versus morning periods from October 2002 through November 2003……………………………………………………………………………………………………………………………..31

Table 5. Results of logistic regression analyses to detect the effect of number of projects in a run, tide height, swell height, air temperature, wind speed, wind direction, sea state, cloud cover, precipitation class, and visibility class on animal displacement during demolition runs on Bentinck Island from October 2002 through November 200…31

Table 6. Results of one-way ANOVA tests* of pre-discrete disturbance activity levels by type of monitoring day regarding military training range activities…………………………………………………………………………………………….37

Table 7. Results of t-Tests for differences between mean daily activity levels of pinniped based on samples when no discrete disturbance stimulus was attributed to the sample during days when Bentinck Island was active compared to days when no blasting occurred there (refer to Table 1 for dates included)……………………………………….37

Table 8. Percent of potential disturbance events that caused birds to fly or birds/pinnipeds to enter
the water………………………………………………………………………………………………………………………..38

Table 9. Minimum, maximum, mean and standard deviation of the daily frequency of selected disturbance events as observed during 52 monitoring sessions at Race Rocks, BC spanning the period October 2002 through
November 2003 ………………………………………………………………………………………………………………..38

LIST OF FIGURES

Page Figure 1. Map of southern Vancouver Island and eastern Juan de Fuca Strait………………………….3

Figure 2. Map of Sub-Areas within the study area……………………………………………………………………..4

Figure 3. Map of southern Vancouver Island and vicinity, showing Rocky Point, Race Rocks Ecological Reserve (within 20-fathom contour), and Military Training Area WQ (within circle)…………………………………………………………………………………………………………………………….6

Figure 4. Predicted tide heights at William Head during the study period………………………………………..22

Figure 5. Daily differences in predicted tide heights at William Head during the study period……………….22

Figure 6. Total numbers of cormorants on land in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower……………………………………………………25

Figure 7. Total numbers of bald eagles on land in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower……………………………………………………26

Figure 8. Total numbers of gulls on land in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower……………………………………………………………………27

Figure 9. Total numbers of northern elephant seals hauled out in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower. ……………………………………………………………………………………………………………………………………..27

Figure 10. Total numbers of harbour seals hauled out in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower…………………………………………………….28

Figure 11. Total numbers of California sea lions hauled out in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower ………………………………………29

Figure 12. Total numbers of northern sea lions hauled out in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon ) as observed from atop the light tower……………………………………………………..29

Figure 17. Stacked line (cumulative total) chart of potential disturbance events (i.e., raptor, boat, pedestrian, and air traffic) during 52 monitoring sessions in the Race Rocks study area of from 6 October 2002 through 27 November 2003…………………………………………………………………………………………………………………..39

Figure 18. Number of blasts that occurred during each of the 52 monitoring sessions in the Race Rocks study area of from 6 October 2002 through 27 November 2003………………………………………………………………………….39

Figure 20. Comparative changes in numbers of harbour seals in monitored sub-areas for selected potential disturbance types…………………………………………………………………………………………………………………………………41

Figure 22. Comparative changes in numbers of California sea lions in selected monitored areas for selected potential disturbance types………………………………………………………………………………………………………………….43

Figure 24. Comparative changes in numbers of northern sea lions in selected monitored areas for selected potential disturbance types………………………………………………………………………………………………………………….45

Figure 25. Relative distribution of Lester B. Pearson College boats observed in Race Rocks Ecological Reserve during monitoring sessions from October 2002 through November 2003……………………………………………………….50

Figure 26. Relative distribution of pleasure boats observed in Race Rocks Ecological Reserve during monitoring sessions from October 2002 through November 2003………………………………………………………………………………….51

Figure 27. Relative distribution of ecotour boats observed in Race Rocks Ecological Reserve during monitoring sessions from October 2002 through November 2003………………………………………………………………………………….53

Figure 28. Conceptual model of the hierarchical effects of exposing a wildlife species to a non- directly lethal visual or aural disturbance stimulus……………………………………………………………………………………………………….61

LIST OF PHOTOS

Page Photo 1. Aerial photo of Great Race Rock as viewed from the northwest………………………………..5

Photo 2. Adult glaucous-winged gull nesting on a grassy area of Great Race Rock………………………….12

Photo 3. Subadult male northern elephant seal………………………………………………………………………..13

Photo 4. Mother-pup pairs of harbour seals are commonly observed at Race Rocks during………………..14

Photo 5. Harbour seals haul out in abundance on intertidal portions of the study area………………………14

Photo 6. California sea lions hauled-out on Great Race Rock………………………………………………………15

Photo 7. Northern sea lions hauled out on Sub-Area 2-5 of Race Rocks…………………………………………16

Photo 8. Killer whales, such as this lone male, were infrequently observed in the study area. 7 August 2003….17

Photo 9. Example of tidal effect on the area of exposed land available for birds and pinnipeds……………. 23

Photo 10. Portion of a feeding flock of primarily gulls and cormorants, located approximately 2 km southeast of Race Rocks……………………………………………………………………………………………………………………………25

Photo 11. Example of how tide height affected haulout availability for harbour seals, including during the peak of their pupping season………………………………………………………………………………………………………………..34

Photo 12. An example of typical pinniped responses to blasting…………………………………………………..36

Photo 13. Raptors such as this adult bald eagle frequently disturbed cormorants and gulls in the study area…46

Photo 14. Students and staff from Lester B. Pearson College were frequent visitors to Great Race Rock…47

Photo 15. Approximately 200 harbour seals moved quickly from the shore of eastern Great Race Rock into the water immediately after being apparently startled by a high-pressure power washer being operated by a resident of the island………………………………………………………………………………………………………………………………47

Photo 16. Two tourists wander through an active glaucous-winged gull nesting area (Sub-Area H) on Great Race Rock; causing disturbance and risking egg destruction by trampling………………………………………………………..48

Photo 17. Most aircraft overflights did not cause animals to leave the rocks for the water or air. ……………49

Photo 18. Pleasure boat near a pod of killer whales moving north through Race Passage…………………….52

Photo 19. Ecotour boat traffic was common throughout the year, but particularly during summer. ………….52

LIST OF APPENDICES

Page Appendix 1. Legislation with direct or potential relevance to marine life at Race Rocks.. ……………74

Appendix 2. Data collected during monitoring sessions at Race Rocks…………………………………………..85

Appendix 3. Methods used for the analysis of data collected during animal censuses and activity sampling in the Race Rocks study area………………………………………………………………………………………………………………87

Appendix 4. Total numbers of pinnipeds, gulls, cormorants, and shorebirds in Race Rocks Ecological Reserve as counted from atop the light tower during each of the two daily censuses for the monitoring period 6 October 2002 through 27 November 2003……………………………………………………………………………………………………………..91

Appendix 5. Total numbers of birds in Race Rocks Ecological Reserve as counted from atop the light tower during each of the two daily censuses for the monitoring period 6 October 2002 through 27 November 2003……………………………………………………………………………………………………………………………….94

Appendix 6. Total number of potential disturbance events recorded in the monitored area during each monitoring day at Race Rocks, BC. ……………………………………………………………………………………………………………..99

Appendix 7. Sample sizes used to calculate mean activity rates (proportion of animals with heads up) of three pinniped species at Race Rocks, BC as a function of whether or not a demolition range (i.e., Bentinck Island, or Whirl Bay) was active and according to individual disturbance stimuli (primary) or lack thereof (none)…………………………101

Appendix 8. All dates and approximatea number of projects detonated on Bentinck Island from 11 July 2002 (the most recent blasting prior to the onset of this study) through 30 November 2003………………………………………102

Appendix 9. Number of ordnances detonated at Christopher Point Ordnance Disposal Range during the study period of October 2002 through November 2003 by date, ordnance type, and individual weight………………………….103

1 INTRODUCTION

Race Rocks is a provincial ecological reserve and has been proposed as a federal marine protected area. The area supports a diverse range of marine algae, marine invertebrates, fish, marine birds, and pinnipeds (seals and sea lions). Marine birds use Race Rocks for breeding and non-breeding purposes. Pinnipeds are of particular relevance to this study because they are large, conspicuous animals that have been the focus of concerns about the effects of local human disturbance. Harbour seals breed and haul out at Race Rocks, and northern elephant seals, California sea lions, and northern sea lions haul out there. Cetaceans transit the area intermittently.

A major portion of Race Rocks Ecological Reserve is contained within the Department of National Defence’s (DND) Military Training Area WQ; however no training activities actually occur within the Reserve. The effects of the demolition training and ordnance disposal activities in WQ were first studied by LGL Limited during 1997 and 1998 (Demarchi et al. 1998). Results of that study indicated that some pinnipeds at Race Rocks responded to ordinance explosions by increasing their activity levels and moving from haulouts to the water. It was also noted that other human uses in the study area (e.g., whale watching boats, pleasure boats, human activity on Great Race Rock, etc.) elicited similar reactions from birds and pinnipeds.

The initial study (Demarchi et al. 1998) was confined to a limited portion of the year and only on days when military exercises involving explosions occurred. Observations of the behavioural effects of non-military disturbances on marine life were opportunistically collected, but that study was not designed to assess impacts from non-military activities. The present study was designed to monitor the effects of natural environmental processes; military explosions; and non- military, human-caused (anthropogenic) disturbances on marine birds and pinnipeds at Race Rocks during a 14-month period.

The diversity of marine life at Race Rocks makes it a popular location for boaters, divers, recreational adventurers, students, and researchers. These activities have the potential to disturb marine life. In addition, the absence of substantial human settlements in the area facilitates the regular use of high explosives by DND. It is important to recognize that military exercises represent one type of many potential disturbances that occurs locally. Therefore, it is important to try to assess the response of marine birds and pinnipeds to explosions independent of other impacts and the potential impacts of explosions in addition to all other impacts (i.e., the cumulative impacts).

1.1 Study Objectives

This research focused on pinnipeds (seals and sea lions). However, selected species of marine birds were also monitored. This research was conducted under Park Use Permit #VI0210066. The objectives were to:

Summarize legislation with direct or indirect relevance for marine birds and mammals at Race Rocks.
Document whether the study area is being utilized for: a breeding area, a summering or wintering area, migration corridors, or staging areas by marine birds and pinnipeds.

2 LGL Limited

Assess the affects of natural factors on the abundance of marine birds and pinnipeds in the study area.
Document and assess the effects of demolitions from the Whirl Bay Underwater Demolition Range, Bentinck Island Demolition Range, and Christopher Point Ordnance Disposal Range on marine birds and pinnipeds in the study area.
Document the effects of ecotour boats, other boats, aircraft, and pedestrian traffic in and near the study area on marine birds and pinnipeds.
Determine if natural factors such as air temperature, wind speed and direction, cloud cover, wave height, tide height ameliorate or amplify animal responses to human- caused disturbances.
Examine local populations of marine mammals and birds to assess the immediate and cumulative effects of local human activities such as demolition training, ecotouring, pleasure boating, aircraft overflights, and human activities associated with operations on Great Race Rock.

2 RELEVANT LEGISLATION

Marine birds and mammals at and near Race Rocks are subject to a number of different legislative acts and their corresponding regulations. A summary of relevant legislation is presented in Appendix 1.

3 STUDY AREA AND VICINITY

3.1 Race Rocks Ecological Reserve

The study area is the exposed portion of Race Rocks Ecological Reserve, adjacent to Rocky Point on southern Vancouver Island (Figure 1; Figure 2). The Reserve is defined as the seabed and exposed land within the 20-fathom depth contour. Race Rocks is a complex composed of one island (Great Race Rock; 1.48 ha) and a number of smaller islets and reefs. Terrestrial vegetation occurs only on Great Race Rock, and consists of grasses and small forbs comprising both native and introduced species. Lester B. Pearson College of the Pacific (LBPC) operates several provincially owned buildings, including an ecoguardian (caretaker) residence, guest house, boat shed, tank room, crane shed, and diesel generator shed. Ancillary equipment operated by LBPC includes a concrete boat dock and launch, fixed crane, fuel pumping equipment, and diesel tanks. The Canadian Coast Guard leases a concrete helipad, light tower, and support infrastructure located on Great Race Rock (Photo 1). Great Race Rock was added to the Ecological Reserve in 2001.

Race Rocks Ecological Reserve is in the eastern reaches of Juan de Fuca Strait in the Nanaimo Lowland Ecosection of the Eastern Vancouver Island Ecoregion of the Georgia Depression Ecoprovince (Demarchi et al. 1990). The climate of the study area is mild, being moderated by the Pacific Ocean. Tides are semidiurnal1 with strong diurnal inequality.2 Predicted values ranged from -0.11 to 3.06 m at William Head (located within 5 km north of Race Rocks) during the study period (Hopper 2002). Tidal flow through Race Passage can reach 7 knots. More comprehensive information on the biophysical features of Race Rocks Ecological Reserve can be found in Wright and Pringle (2001) and Province of BC (2002).

1 Having typically two high and two low values every 24 hours.
2 Also referred to as declinational inequality, it is the difference in height of the two high waters or of the two low waters of each tidal day.

Figure 2. Map of Sub-Areas within the study area. Great Race Rock was divided into Sub-Areas A through H (excluding E, which was not designated). Outlying areas were initially assigned numbers for each discrete rock, but were subsequently grouped into areas that were usually contiguous or that appeared so from the light tower on Great Race Rock (also shown)

. 3.2 Marine Training and Exercise Area WQ

Canadian Forces Base (CFB) Esquimalt conducts military training in the use of explosives in Marine Training and Exercise Area WQ (“Whiskey Quebec”; Figure 3). WQ is located near Rocky Point on southern Vancouver Island, British Columbia and owned by the Federal Government, Department of National Defence. WQ is a circular range that covers 1075 ha of terrestrial and marine environments, and incorporates a portion of Race Rocks Ecological Reserve, although no military training occurs in the Reserve itself.

Two ranges in WQ are used for training in ordnance-based demolitions: the Whirl Bay Underwater Demolition Range, and the Bentinck Island Demolition Range. Surplus and outdated ordnance is disposed in WQ by Canadian Forces Ammunition Depot (CFAD) Rocky Point at the Christopher Point Ordnance Disposal Range. Training activities in WQ are under the control of

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Base Operations, CFB, Esquimalt. All training exercises in WQ must be approved by Base Operations as outlined in the CFB Esquimalt Range Standing Orders. Ordnance disposal activities are overseen by CFAD Rocky Point.

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Photo 1. Aerial photo of Great Race Rock as viewed from the northwest. Observations during this study were made from atop the light tower. Photo by Heath Moffat; used with permission from Lester B. Pearson College.

The Whirl Bay Underwater Demolition Range is used primarily by Fleet Diving Unit (Pacific) (FDU(P)) for underwater demolitions and ordnance testing using charges of C4 plastique3 ranging from 0.5 to 10 kg. The part of Whirl Bay that is used for demolitions is a shallow (<15 m) cove approximately 300 m across and 190 m from the entrance to the demolition beach. The substrate of the cove consists of basaltic bedrock overlain by clay, mud, silt, and sand with several patches of kelp scattered over the bottom. Shoreline habitats consist of basaltic rock formations and pebbly and sandy beaches.

3 C4 plastique is a white, plastic, high-explosive made of RDX (Royal Demolition Explosive; a.k.a. cyclonite or hexogen; chemical name, trinitrotriazine) and an inert plastic binder. C4 is more powerful than TNT (trinitrotoluene) and is suitable for cutting metal and timber and for blasting concrete because of its high detonation velocity and plasticity. PETN (pentaerythritol tetranitrate) is used as a detonation cord for C4 charges.

Figure 3. Map of southern Vancouver Island and vicinity, showing Rocky Point, Race Rocks Ecological Reserve (within 20-fathom contour), and Military Training Area WQ (within circle). General locations of demolitions and ordnance disposal are indicated.

In October 2002, a bubble curtain was deployed in Whirl Bay as a means of attenuating the shock pulse of underwater detonations, and thereby reducing the adverse effects on underwater marine life. Prior to the actual demolitions, several “Thunderflashes” are detonated to scare marine life away from the blast area. The demolition area is >2 km from the nearest haulout in Race Rocks and is separated from Race Rocks by Christopher Point.

Bentinck Island (31 ha) is separated from Rocky Point by Eemdyk Passage—a shallow channel that supports an abundance of bull kelp. Harbour seals are common in Eemdyk Passage, but other pinnipeds have not been seen there (pers. obs.). The mid-section of Bentinck Island is a low-lying, treeless area of pebble beaches connecting three larger areas which support stands of mature Douglas fir.

The Bentinck Island Demolition Range is used primarily by Canadian Forces Fleet School (Seamanship Division) for above-water beach-clearing and obstacle-creation exercises involving metal cutting and the displacement and demolition of rocks and logs. The range is licensed for a maximum individual charge size of 2.3 kg (CFB Esquimalt Range Standing Orders). Petty Officer (PO) B. Phillips (pers. comm. 1996) indicated that in the past, the range has been typically used for 56 days per year, but demolitions do not occur on all such days. “Project” is the term used to describe an individual demolition (e.g., timber cut, steel cut, beach clearing, etc.) involving a single explosive charge. “Run” is the term used to describe a set of projects that are simultaneously set up by different teams of trainees. As of 1998, projects in the same run are detonated at a minimum interval of 2 minutes. There was no minimum interval between projects prior to 1998. During a typical day on which the range is active, two to four runs of one to three projects each (i.e., 4-12 blasts per day) are conducted. A typical project consists of one to four slabs4 of C4. Demolition training is conducted on the central beaches of Bentinck Island, with a line-of-sight to Race Rocks. The nearest haulout used by seals and sea lions in the Race Rocks Reserve is approximately 1.2 km away.

Surplus ordnance is disposed by way of high-order5 detonation at the Christopher Point Demolition (disposal) Area. Disposal activities are conducted on an as-required basis, and unlike the other ranges in WQ, activities on the Christopher Point Range are not tied to training schedules. Under federal authorization, the disposal area is licensed for a maximum single explosive charge size of 13.6 kg. Twelve such charges are permitted per day. However, as a means of mitigating public concerns about blast noise, a voluntary reduction6 in maximum charge size to 6.8 kg was adopted in 1987 (Explosives Safety Officer [ESO] A. Carter, pers. comm. 1997). Use of the range varies greatly among years, but anywhere from one to 12 high- order detonations on up to 25 days (7%) of the year is a reasonable approximation (ESO A. Carter, pers. comm. 1997). The disposal site is situated in a clearing characterized by Scotch broom and mowed grass. The range has a line-of-sight to Race Rocks. The nearest haulout used by seals and sea lions in Race Rocks Ecological Reserve is approximately 2.0 km away.

3.3 Marine Life

The marine habitats of southern Vancouver Island support a diverse array of invertebrates, fish, birds, and mammals. The terrestrial and marine habitats near Rocky Point are important breeding areas, summering areas, wintering areas, migration corridors, or staging areas for approximately 200 species of birds (Campbell et al. 1990a, b; 1997; 2001). The most conspicuous mammals are the pinnipeds (seals and sea lions). The harbour seal (Phoca vitulina) is the only pinniped species that breeds in the study area. The abundance of California sea lions (Zalophus californianus) and northern sea lions7 (Eumetopias jubatus) is greatest outside the May-July breeding season. Northern elephant seals (Mirounga angustirostris) have occurred at Race Rocks in recent years. Single northern fur seals (Callorhinus ursinus) have been reported, but sightings of this species are very infrequent. Cetaceans such as killer whales (Orcinus orca) and gray whales (Eschrichtius robustus) are occasionally observed in or near the study area, but do not occur there with the same predictability as pinnipeds.

4 A slab of C4 weights 0.500 kg
5 That is, they are exploded rather than disposed of by non-explosive means.
6 Some larger charges, such as the Mark-7 anti-tank mines (each containing 8.6 kg of TNT) are occasionally detonated.
7 Also known as the Steller (or Steller’s) sea lion.

3.3.1 Injury and Disturbance
The detonation of solid, nitrogen-based high explosives like C4 and PETN (pentaerythritol tetranitrate) entails rapid oxidation-reduction reactions that transform solids into gasses such as N2, CO2, H2O, and O2. Other products include intense heat, bright light, a shock wave, and noise. Because the detonation of C4 is so rapid, a shock wave (also known as a pressure pulse) is propagated along the front of the expanding gasses. Such shock waves have the highest peak pressure levels of any man-made source (Richardson et al. 1995). The impulse level (i.e., strength) of a shock wave decays rapidly with increasing distance from the source. As air rapidly expands behind the pressure wave, sound energy (noise; the proverbial boom) is generated. Depending on the peak impulse level of a pressure wave, distance from the source, and species- specific susceptibility among other factors, shock waves can injure or kill animals (Demarchi et al. 1998). Regarding detonations at the three sites in WQ, such extreme effects are not believed to be relevant to marine birds and mammals at Race Rocks because of the small charge sizes (i.e., &Mac178;10 kg) and the distances (i.e., >1 km) involved (Demarchi et al. 1998). Sound energy, at sufficient levels, can temporarily or permanently injure an animal’s hearing organs. It is unlikely that animals at Race Rocks experience temporary or permanent effects to hearing. Blast-caused disturbances of marine birds and mammals at Race Rocks are believed to be triggered by responses to sounds that “scare” rather than injure animals; though it is possible that some animals sense and respond to pressure waves also (Demarchi et al. 1998). As indicated by Richardson et al. (1995), published data on all aspects of the effects of explosions on marine mammals are extremely limited.

Ecotourism is a thriving venture both worldwide and on southern Vancouver Island. The tourism industry in Victoria is significant to the local economy. Local entrepreneurs have been quick to capitalize on a large population of tourists and residents willing to pay to see whales and other marine mammals such as sea lions. Obee (1998) presents a general discussion of the rapid growth of this business and the negative effects it can have on local marine life. Wildlife viewing by the pleasure-boating general public can also disturb wildlife. Tershy et al. (1997) describe how humans affected a reserve used by marine birds and pinnipeds. As observed by Demarchi et al. (1998), ecotourism and other human activities at Race Rocks are capable of disturbing birds and pinnipeds. In terms of the responses by individual animals, such disturbances are comparable to those caused by blasts. However, when taken in the perspective of an entire year, disturbances by boats and humans could out-weigh disturbances caused by explosions because the former disturbances are more frequent. Whereas DND activities occur infrequently during the course of a year, boats and other human-caused disturbances occur almost daily when weather conditions are suitable. Disturbances of birds and pinnipeds by boats and human activities on Race Rocks can be viewed as cumulative impacts on the species in question.

As reported by Demarchi et al. (1998), blasting often coincided with the presence of ecotourists and pleasure boaters. As recreational boat traffic at Race Rocks increases, the likelihood of such events coinciding is expected to increase. Consequently, an increase in the number of complaints to DND regarding the effects of blasting activities on marine mammals can be expected,

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regardless of the degree to which any observed disturbances were caused or compounded by the presence of the boat and its occupants

8. 3.3.2 Species Accounts

The Committee on the Status of Endangered Wildlife in Canada (COSEWIC) tracks the status of flora and fauna in Canada. Listing categories applicable to the species presented in this section are defined as:

•Endangered—A species facing imminent extirpation or extinction.
Threatened—A species likely to become endangered if limiting factors are not reversed.
Special Concern—A species of special concern because of characteristics that make it particularly sensitive to human activities or natural events.
Not at Risk—A species that has been evaluated and found to be not at risk.
Not Listed—A species for which there is no present need for evaluation.

In BC, flora and fauna are assessed for concerns about their conservation by the provincial Conservation Data Centre (CDC). Listing categories are as follows:

Red Listed—A species that is endangered or threatened with extirpation or extinction.
Blue Listed—A species that is sensitive or vulnerable to extirpation or extinction, but less so than Red-listed ones.
Yellow Listed—A species that is not at risk, but with a management emphasis in order to meet specific public demands.

The following accounts describe selected bird and mammal species that occur at Race Rocks. Current COSEWIC listings are followed by current CDC listings.

3.3.2.1 Brandt’s Cormorant (Not Listed; Red Listed)

Brandt’s cormorants are uncommon to abundant throughout south-coastal BC during the year. Several small breeding colonies exist in BC, and in 1987 three nests with young were found at Race Rocks (Campbell et al. 1990a). They are much more abundant near southern Vancouver Island from August to April (Gates 2001) when numerous birds arrive from breeding areas along the west coast of the United States. Brandt’s cormorants roost on Race Rocks and forage in the surrounding waters during autumn through spring.

3.3.2.2 Double-crested Cormorant (Not at Risk; Blue Listed) Double-crested cormorants are common residents of southern Vancouver Island, breeding mainly on islands in the Strait of Georgia (Gates 2001, Campbell et al. 1990a). The breeding population has been decreasing in BC in the last two decades (Fraser et al. 1999; Chatwin et al. 2002). Double-crested cormorants commonly rest on the Race Rocks islets and feed in the waters of the Ecological Reserve and surrounding area. The species is not known to breed at Race Rocks.

8 A meeting discussing the present review of the Department of Fisheries and Oceans’ Marine Mammal Regulations was hosted by DFO at the Institute of Ocean Sciences in Sidney, B.C. on 29 January 2003. The majority of attendees were directly or indirectly affiliated with the marine ecotourism industry. When an audience member spoke of the need for the Marine Mammal Regulations to address the adverse effects of DND’s training exercises on marine life at Race Rocks, most of the audience applauded.

Editors note: We have linked some of the following species to the appropriate reference in the racerocks.com Taxonomy Files. That was not part of the original report.

3.3.2.3 Pelagic Cormorant (pelagicus subspecies Not Listed; Red Listed – resplendens subspecies Not Listed; Yellow Listed)

Two subspecies of pelagic cormorant occur in BC and both may occur at Race Rocks. The pelagicus subspecies nests north of Vancouver Island and in Alaska and is Red-listed due to a decline in numbers. It may occur at Race Rocks occasionally during the non-breeding season. The resplendens subspecies breeds in south-coastal BC including Race Rocks (Vermeer et al. 1989a). The number of pelagic cormorants nesting on Race Rocks varies from year to year with 120 counted by Vermeer et al. (1989a) in 1987 and 0 in 2000 (Chatwin et al. 2002). Pelagic cormorants use the rocks and islets of Race Rocks throughout the year for resting and the surrounding waters for feeding.

3.3.2.4 Bald Eagle (Not at Risk; Yellow listed)

Bald eagles are fairly common on southern Vancouver Island from September to mid-May. During the summer months many of them move north to areas where salmon are spawning and are uncommon locally during that time. Bald eagles usually build their nests in large trees close to water. They breed near Race Rocks along the shore of Vancouver Island, but not within Race Rocks Ecological Reserve. Bald eagles use Race Rocks Ecological Reserve mainly as a resting and feeding area where they forage on fish and gulls.

3.3.2.5 Peregrine Falcon (anatum subspecies Threatened; Red Listed – pealei subspecies Special Concern; Blue Listed)

Three subspecies of peregrine falcons occur in BC. Although all three probably occur at Race Rocks occasionally, the most likely and frequent is probably the Peale’s peregrine falcon. Peregrine falcons breed in small numbers throughout south-coastal BC. Peregrine falcons from other areas of the west coast migrate through and/or winter in the study area. Peregrine falcons hunt their main prey (other birds) frequently in Race Rocks Ecological Reserve. At times they rest or consume prey on the terrestrial portions of the Reserve, frequently perching on man-made structures on Great Race Rock or on higher portions of the rocky shorelines.

3.3.2.6 Black Oystercatcher (Not Listed; Yellow Listed) Black oystercatchers are common residents and breeders at rocky coastal shoreline areas of southern Vancouver Island (Gates 2001). Three pairs were counted on the islets of Race Rocks in 1987 (Vermeer et al. 1989b). It is reported by LBPC that up to six pairs nest on the islets (Race Rocks 2003). During the non-breeding season up to 40 or more birds aggregate at Race Rocks. In winter during daylight (high tide) hours they spend much of their time on Race Rocks resting and preening.

3.3.2.7 Black Turnstone (Not Listed; Yellow Listed) Black turnstones are common at marine shoreline habitats on southern Vancouver Island from August to mid-April (Gates 2001). They prefer rocky coastlines and are commonly seen on Race Rock islets feeding and resting.

3.3.2.8 Surfbird (Not Listed; Yellow Listed) Surfbirds are present in small numbers on the marine shoreline habitats of southern Vancouver Island from late July to April. They do not breed in the study area (Gates 2001). Small numbers feed and rest on Race Rocks during that time, with peak numbers in spring and fall during migration.

3.3.2.9 Rock Sandpiper (Not Listed; Yellow Listed) Race Rocks is one of the best places to see rock sandpipers in the Victoria area. This species is quite rare in the region occurring almost exclusively on the rocky shores of offshore islands and islets. Rock sandpipers are regular in small numbers on Race Rocks from late October to late May. They do not breed in the study area. The islets of Race Rocks Ecological Reserve are used for resting during high tide and feeding during lower tides.

3.3.2.10 Heerman’s Gull (Not Listed; Yellow Listed) Heerman’s gulls are common in south coastal BC from mid-July to the end of October when most of their population moves north along the Pacific coast from their Mexican breeding grounds. They are very rare at other times of the year and do not breed in BC (Gates 2001, Campbell et al. 1990b). Hundreds of Heerman’s gulls use the islets of Race Rocks for resting and the surrounding waters for feeding during their time in this area.

3.3.2.11 California Gull (Not Listed; Blue Listed) California gulls are common to abundant during their spring (March-April) and fall (July- October) migrations in the southern Vancouver Island area. They are quite rare at most other times of the year and do not breed in the study area (Gates 2001). They commonly feed in the water surrounding Race Rocks and rest on the islets during their stay in the area.

3.3.2.12 Herring Gull (Not Listed; Yellow Listed) Herring gulls are uncommon at southern Vancouver Island from September to April and rare during the rest of the year. This species is mainly an offshore gull in BC. Race Rocks is probably one of the better places to observe this species near shore and small numbers use the islets for resting and the surrounding waters for feeding mainly during the winter.

3.3.2.13 Thayer’s Gull (Not Listed; Yellow Listed) Thayer’s gulls are common winter visitors at southern Vancouver Island from about mid- September to March. They are not present or are very rare in the area from April to mid- September and do not breed in the area (Gates 2001). Very large numbers of Thayer’s gulls use Race Rocks during the fall and winter, resting on the islets and feeding in the surrounding waters.

3.3.2.14 Western Gull (Not Listed; Yellow Listed) Western gulls are uncommon to rare during most of the year near southern Vancouver Island (Gates 2001). This species nests along the Pacific coast of North America from Washington to California. At the northern edge of their range, hybridization with glaucous-winged gulls is frequent resulting in many hybrid birds that are impossible to classify to one species. Gulls that appear to be of pure western gull stock are uncommon to rare at Race Rocks Ecological Reserve throughout the year. They join the mixed-species gull flocks either resting on the islets or feeding in the surrounding water. Some of the gulls nesting at Race Rocks are probably hybrids.

3.3.2.15 Glaucous-winged Gull (Not Listed; Yellow Listed) Glaucous-winged gulls are the only species of gull nesting at Race Rocks (Photo 2) with up to 424 nests counted in 1989 (Vermeer et al. 1992). They are common all year throughout the region and their numbers have increased dramatically in the last two decades. Other than as a nesting colony, Race Rocks Ecological Reserve is used all year for resting on the islets and feeding in the surrounding water.

3.3.2.16 Pigeon Guillemot (Not Listed; Yellow Listed) Pigeon Guillemots are the only species of alcid that nests at Race Rocks. They are in the area year-round, but only use the land in Race Rocks during spring and summer. This migratory species resides in rocky coastal areas, and prefers to forage in shallow, inshore waters. Pigeon guillemots nest in rock crevices on the periphery of Great Race Rock. The first nesting record was in 1953 and published numbers of breeding pairs there range from 14 to 400 (Campbell et al. 1990b).

Photo 2. Adult glaucous-winged gull nesting on a grassy area of Great Race Rock. 25 May 2003.

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3.3.2.17 Northern Elephant Seal (Not at Risk; Yellow Listed)

The northern elephant seal (Photo 3) is a member of the family Phocidae—the true seals. Although near extinction at the beginning of the 20th century, legal protection of the species and its habitat has allowed it to recover. In 1991 there was an estimated population of 127,000 animals (Stewart and Huber 1993). This species is highly migratory, breeding primarily on islands in northern Mexico and central California and moving north after the breeding season. After breeding, most animals stay far offshore in deep water. Males move over the continental shelf as far north as the Gulf of Alaska and Aleutian Islands, while females tend to move westward into the open ocean (Stewart and Huber 1993).

Northern elephant seals can haul out at any time of the year, but Stewart and Huber (1993) note three seasonal peaks in abundance at haulouts. The first is in winter during the combined pupping and breeding season. The second is in late April and early May when adult females and subadults come ashore to moult. The third is in October when non-pregnant females, pups, yearlings, and subadults come ashore to moult.

Baird (1990) reported that northern elephant seals are sparsely, but widely distributed in British Columbian waters throughout the year and are usually seen singly. Race Rocks is one of the few spots in BC where elephant seals regularly haul out. The account by Cowan and Carl (1945) suggests that, at least up to the mid-20th century, northern elephant seals were not as common in BC as they are at present. Based on their size and general appearance, most animals using Race Rocks are adult females or subadults, although a few adult males also haul out there.

Photo 3. Subadult male northern elephant seal. Members of this species commonly hauled-out on and near the boat launch at Great Race Rock. They tolerated humans at very close distances, to the point of becoming a nuisance at times as they interfered with boat launchings and landings. This individual is moulting its brown fur, exposing its grey, scarred skin beneath. 26 June 2003.

3.3.2.18 Harbour Seal (Not at Risk; Yellow Listed)

The harbour seal (Photo 4; Photo 5) is a member of the family, Phocidae—the true seals. They are the most abundant and widespread pinniped in coastal waters of southern BC and the only one that breeds in the study area. They are non-migratory residents at Race Rocks and give birth (“pup”) on the islets. The pupping season of harbour seals varies regionally, with those in the study area giving birth during the months of June through September; peaking in late July (Bigg 1969). Harbour seal pups are highly precocial at birth and are reared in the water as well as on land (Riedman 1990). Pups are weaned at an age of 5-6 weeks. Harbour seals spend a considerable amount of time hauled-out on beaches, rocks, man-made structures, and islets, including the islets at Race Rocks. Numbers of harbour seals have increased dramatically in and near British Columbian waters after the species was afforded protection from hunting under Canadian and American laws (Olesiuk et al. 1990; Jeffries et al. 2003)

Photo 4. Mother-pup pairs of harbour seals are commonly observed at Race Rocks during summer. The species is present at Race Rocks year-round. Sub-Area G; 17 July 2003.

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3.3.2.19 California Sea Lion (Not at Risk; Yellow Listed)

The California sea lion (Photo 6) is a member of the eared seal family, Otariidae. California sea lions move north into the study area from breeding colonies in Mexico and California after each summer breeding season, then return south in the late winter and spring. Peak abundance in BC is between September and May. Most of the animals in BC are adult and subadult males but females are known to occur. The number of California sea lions using British Columbian coastal waters has increased substantially during the last century, and in particular, since 1980 (Bigg 1988a). Bigg (1988a) reported that California sea lions were not present on Race Rocks prior to 1965. Records from 1971 (summarized in Bigg 1988a) indicate a maximum of approximately 30 animals at Race Rocks. Since then, numbers have increased to several hundred animals at times. P. Olesiuk (pers. comm. 2002) indicated that California sea lions are expanding their non- breeding range northward within BC, but that little is known of this expansion due to limited monitoring of pinnipeds.

In recent years there has been a continued northward expansion of the species on both the east and west coasts of Vancouver Island (P. Olesiuk, pers. comm. 2002). A few radio tags deployed on California sea lions in the early 1990s revealed that while in BC waters, California sea lions are very mobile and do not remain in the same area (haulout) for extended periods (P. Olesiuk pers. comm. 2002). In BC, California sea lions appear to readily and rapidly shift their distributions in response to the movements of their main prey, salmon and herring (P. Olesiuk pers. comm. 2002). A northward shift in schools of adult herring during the mid-winter pre- spawning period has resulted in a concomitant shift in California sea lions. For example, they no longer occur in the same abundance at Harmac (near Nanaimo) as in the past, but greater numbers are now seen near Hornby Island to the north (P. Olesiuk pers. comm. 2002).

Photo 6. California sea lions hauled-out on Great Race Rock. The vast majority of California sea lions at Race Rocks are adult and subadult males. October 2002; (Photo: M. Bentley).

3.3.2.20 Northern Sea Lion (Special Concern; Red Listed)

The northern sea lion (Photo 7) is a member of family Otariidae (eared seals). The breeding range of this species is from California, along the Pacific coast to Alaska and northeast Asia. Two stocks are recognized: the Western Stock which ranges from Russia to the Gulf of Alaska; and an Eastern Stock which ranges from southeast Alaska to California. In BC between 1912 and 1968, thousands of northern sea lions were killed in a campaign to reduce the perceived conflict between this species and commercial fishermen. A review of historic data (Bigg 1988b) indicated that control programs and commercial harvests conducted in BC during 1912-1967 eradicated one breeding area and reduced numbers on the remaining rookeries to about 25-30% of peak levels observed in the early 20th century, prior to any large-scale culls. Numbers of northern sea lions on Race Rocks appear to have rebounded since the control program ended (Bigg 1988b). Presently there is considerable concern about conservation of the western stock because of a dramatic, unexplained decline since 1970 (Trites and Donnelly 2003). Conversely, the Eastern Stock (the one which occurs at Race Rocks) has exhibited a modest increase during this period (Bigg 1988a; Calkins et al. 1999). Despite this increase, in November 2003 COSEWIC upgraded this species’ listing from “Not at Risk” to “Special Concern” because there are only three breeding locations in BC, the species is sensitive to human disturbance while on land, the threat of acute oil spills, and unexplained declines in other populations to the north and west of BC .

The closest rookeries to Race Rocks are on the Scott Islands off northern Vancouver Island (Bigg 1988b; Loughlin et al. 1984). Northern sea lions migrate into the study area where they spend a considerable amount of time hauled-out on traditional beaches, rocks, and islets. Bigg (1988b) identified Race Rocks as a haulout site used by northern sea lions during their nonbreeding season, with peak abundance occurring during September through May. All sexes and age-classes (except newborn pups) of northern sea lions occur on Race Rocks.

Photo 7. Northern sea lions hauled out on Sub-Area 2-5 of Race Rocks. That area was commonly used by both sexes and all age classes. Photo date: 20 November 2003.

3.3.2.21 Killer Whale (Northeast Pacific Southern Resident population: Endangered, Red Listed – Northeast Pacific Transient population: Threatened, Red Listed) Killer whales (Photo 8) are large members of the family Delphinidae that occur in arctic, temperate, and tropical waters of the world’s oceans. Two different populations occur in and near the study area: residents (which typically forage on fish—namely salmon) and transients (which typically forage on pinnipeds). The terms resident and transient do not accurately denote the movement patterns of each population (references in Baird 2001b) and members of either population can occur in the study area at any time of the year. They are infrequent visitors to Race Rocks Ecological Reserve, seldom spending more than a few minutes in it when they do occur there (this study). Baird and Dill (1994, cited in Calambokidis and Baird 1994) reported that killer whales take “large numbers’ of harbour seals at Race Rocks, but such behaviour was never observed during the present study or that by Demarchi et al. (1998)

. Since 1960, the Southern Resident population of about 96 in 1967, declined to a low of 67 in 1971, then rose to about 100 individuals in 1995 (Baird 2001b). By 2001 the population had declined to 789, qualifying it as an endangered and “depleted stock” under the U.S. Marine Mammal Protection Act (Krahn et al. 2002). Much less is known of the local transient population.

Photo 8. Killer whales, such as this lone male, were infrequently observed in the study area. 7 August 2003.
9 The 2003 population estimate by the Washington-based Center for Whale Research
(http://www.whaleresearch.com/thecenter/southern.html) was 83.

4 METHODS

The methodology employed in this study was based on that used during a similar study conducted in 1997 and 1998 (Demarchi et al. 1998). Race Rocks was accessed by an inflatable boat launched from Rocky Point. Monitoring days were selected to represent a sample of weekday and weekend conditions. Two or three observers recorded data in four different Microsoft Access 2002 databases using a hand-held Comapq iPAQ computer running Visual CE v6.1. Binoculars (8-10x) and tripod-mounted spotting scopes (20-60x) were used to assist with animal identification. In addition to the information presented below, additional information on data collection is presented in Appendix 2.

The first database concerned weather. Weather conditions were measured using on-site meteorological equipment (windspeed in knots and direction in degrees off true north) operated by the Coast Guard or by visual estimates (all others). As animal responses to disturbance may vary with time of day, cloud cover, wind speed, wind direction, wave height, swell condition, and tide height, weather parameters were measured in the morning and at the end of the day, and whenever notable changes in conditions occurred throughout the day. Tidal data were obtained for William Head (123° 32.0′ W, 48° 20.0′ N) using the computer program WXtide32 v2.7 (Hopper 2002). William Head is within 5 km to the north of Race Rocks.

The second database contained counts of bird and pinniped species in the study area. Those data provided information on how numbers of animals in the study area changed during daily and seasonal timescales. Birds and pinnipeds were censused twice (morning and afternoon). Only animals that were supported by terrestrial features (i.e., islands, islets, rocks, man-made structures, etc.) within one of the sub-areas (see Figure 2) were counted because of the difficulties in seeing animals in the water or counting birds in the air. Further, only animals visible from the tower were counted. Some animals were hidden from view, but in our opinion, based on our familiarity with the study area viewed from different boat-based vantages, the vast majority (>90%) of individuals were visible from the tower. Densely crowded pinnipeds also obscured the view of some animals. Considering these visibility biases, counts were likely lower than the actual number of animals within the Reserve.

The third database involved sweep counts of the numbers and behaviours of animals in selected sub-areas. These data facilitated an assessment of the effects of disturbance on bird and on pinniped behaviour and numbers by facilitating comparisons between pre- and post-disturbance conditions. These counts were made approximately every 30-60 minutes during the observation period, together with additional counts made immediately prior to, and within a few minutes following, blasting or the closest approach by people, boats, or aircraft. Two visible measures of disturbance are: 1) the change in body position (i.e., activity level; head-down or head-up of pinnipeds10), and 2) the change in numbers of pinnipeds on the haulouts and birds on hard surfaces. During samples of activity levels, we noted whether a disturbance stimulus was present or had occurred (e.g., if an ecotour boat was situated such that the passengers were focusing on the animals in the selected sub-area; or if a blast had just occurred). Multiple stimuli were recorded if they occurred simultaneously. Observations on the visible effects (or lack thereof) of a given stimulus were also noted as comments for each record.

10 It is acknowledged that sea lions sometimes rest in a head-up position, but in our experience at Race Rocks, the proportion of such animals is in the vast minority.

The fourth database tracked potential disturbance events. Because the nature of disturbances from sources other than blasting by DND were unpredictable both spatially and temporally, it was important to track such disturbances in the vicinity of marine animals. To that end, a 250 m by 250 m grid was superimposed on a map of the study area. Grid cells entered by each disturbance stimuli were recorded, as well as the time at which the disturbance entered and left the study area. Cells were recorded a maximum of one time per individual disturbance factor even if the factor temporarily left then re-entered the same cell.

Field sampling began 6 October 2002 and ended 27 November 2003. Where possible, days were scheduled to coincide with explosive training or demolition activities by DND. The dates and exact timing of explosions were coordinated with DND personnel. Up-to-the-minute reports on blast activities were monitored via VHF radio or cellular phone. “Non-training” days were scheduled to document responses to other sources of disturbance such as whale watching tours, pleasure craft, recreational dive boats, aircraft, and other types of human disturbance.

4.1 Analytical Limitations

Data analyses are complicated by several factors with implications for the application of statistical inference to the study’s results:

The study was conducted at a single (unreplicated) site. Consequently, data from one or more control sites (i.e., a site similar in every way to Race Rocks, but without any disturbances) are not available for comparison. Further, military activities, ecotourism, and other human activities have been occurring near or at Race Rocks for many years and no baseline (pre-disturbance) data from Race Rocks are available for comparison.
. Because the occurrence of disturbance events was not under the investigators’ control, observations of disturbance were opportunistic. Considering this and the point above, the study does not represent a true scientific experiment.
. Extrapolating our results to days when we did not monitor the area is not straightforward. With the exception of LBPC and DND activities, our monitoring sessions are believed to approximate a random sample of days with the potential disturbances to which animals in Race Rocks Ecological Reserve are subjected. However, because our monitoring schedule was communicated in advance to LBPC staff, it is not known whether or not they altered any of their activities at Race Rocks in response to our presence. Further, in the interests of increasing our sample sizes of blast-related disturbances, days when Bentinck Island was active were sampled disproportionately more often than if our sampling had been random.
. Because residual effects of disturbance can persist for hours or more, sample records are not independent because repeated samples from the same animals are taken during the course of a day. For example, if a disturbance occurs at time = t and animals move to the water, a sample of animal numbers and activity taken at time = t + 1 is likely to differ from a subsequent sample taken under the scenario where no disturbance had occurred previously. Sample values averaged during the course of a day are more appropriate foruse in statistical testing than individual values obtained from repeated observations of the same animals on the same day.
Dependent response variables (i.e., activity and number of individuals visible in the study area) are not exclusively affected by human-caused disturbance events. Animal activity and departure from a haulout occur naturally and are potentially affected by many independent variables such as: time of year, time of day, weather, sea state, tide height, local prey availability, time since feeding, interspecific interactions, intraspecific interactions, behavioural differences among individuals, animal body condition, animal migration, and interactions between these variables. As a result, determining when changes in animal activity or numbers are in response to human-caused disturbances monitored by this study is not straight-forward because of confounding effects. An even greater challenge is to determine what degree of human-caused change in activity level or numbers of animals constitutes a significant, adverse biological effect (see Demarchi 2002).
Total counts allow inferences about changes in total numbers of animals in the study area, but the absence of a sample of radio-tagged animals restricts conclusions regarding the extent to which any given disturbance results in temporary or permanent abandonment of Race Rocks Ecological Reserve by a portion of the population.
For the most part, differences between the numbers of each pinniped species observed during each pair of daily censuses reflect animals moving on or off the haulouts. However, these values cannot be interpreted strictly as animals moving on or off a haulout because some animals simply moved in and out of view while remaining on the haulout. This is particularly true of northern elephant seals.
It was not possible to visually monitor all sub-areas simultaneously during area-wide disturbances such as blasts. Therefore, the proportion of disturbances that actually caused animals to leave the land in the study area could be biased downward. It was usually possible to track individual boats and people to determine whether a decrease in subsequent counts was in response to disturbance or just a natural occurrence.

4.2 Data Analyses

Detailed descriptions of analyses based on census and activity sample data are presented in Appendix 3.

5 RESULTS

During the period 6 October 2002 through 27 November 2003, 52 monitoring sessions were conducted (Table 1). With the exception of two full days and one partial day when fog precluded accurate counts, monitoring was conducted as planned. On two other occasions, the trip to Race Rocks was cancelled due to extreme weather conditions. A wide range of weather conditions occurred during monitoring sessions, from sunny and clear to gale- and storm-force winds and rain storms. Observations were made under a wide range of tide heights and swell conditions.

Although much of the land in the Race Rocks complex is exposed at even the highest tides, the amount of exposed land available for resting birds and pinnipeds varied considerably as a function of tide height. Note that no attempt was made to quantify the total area available for resting at any given time. A strong seasonal pattern was observed for tide heights and daily timing, both as observed in the field and as calculated (Hopper 2002). The highest tides were observed during monitoring sessions in November through March (Figure 4). Storms were also more common at that time of year, causing swells and wind-waves that further decreased the availability of resting areas or shortened the duration intertidal areas were exposed during the day (Photo 9). The November-March period was also characterized by a tendency for tides in the late afternoon (near the time when the second daily census was conducted) to be lower than those in the morning (when the first daily census was conducted; Figure 5). The remainder of the year followed the opposite pattern. Tidal variation measured on an hourly scale was sufficient to strongly affect the availability of land for resting birds and pinnipeds—especially harbour seals. Other pinnipeds were not so visibly affected.

Table 1. Dates and active range status in WQ during 52 monitoring sessions at Race Rocks. For a summary of dates when the Bentinck Island range was active refer to Appendix 8.

Monitoring Date	Active Range	Monitoring Date	Active Range
06-Oct-02a	none	02-May-03	Bentinck
07-Oct-02	Bentinck	12-May-03a	-none
10-Oct-02	Bentinck	25-May-03a	none
17-Oct-02a	none	05-Jun-03a	none
24-Oct-02 b	Bentinck	13-Jun-03a	none
30-Oct-02a	none	19-Jun-03	Bentinck
08-Nov-02	Bentinck	26-Jun-03 c	none
15-Nov-02	none	05-Jul-03a	none
22-Nov-02a	none	17-Jul-03	none
02-Dec-02	Whirl Bay	27-Jul-03	none
05-Dec-02	Bentinck&Whirl Bay	07-Aug-03	none
16-Dec-02a	none	15-Aug-03	none
31-Dec-02a	none	23-Aug-03	none
17-Jan-03a	none	02-Sep-03	none
20-Jan-03	Whirl Bay	12-Sep-03	none
23-Jan-03	Whirl Bay	18-Sep-03	none
30-Jan-03	Bentinck	25-Sep-03a	none
10-Feb-03a	none	02-Oct-03b	none
20-Feb-03	Bentinck& Christopher Point	09-Oct-03	Bentinck
06-Mar-03a	none	20-Oct-03a	none
14-Mar-03	none	27-Oct-03	Bentinck
20-Mar-03	none	06-Nov-03a	none
27-Mar-03	none	13-Nov-03a	none
10-Apr-03	none	20-Nov-03	Bentinck
16-Apr-03a none	none	21-Nov-03	Bentinck
01-May-03Bentinck	Bentinck	27-Nov-03a	none

a. Days when no blasting occurred as used for comparative purposes to days when blasting occurred on at least Bentinck Island
b. Thick fog precluded complete censuses in both morning and afternoon
c. Thick fog precluded a census in the afternoon

Figure 4. Predicted tide heights at William Head during the study period. Data represent daily values (i.e.,maximum, minimum, and mean) for hourly tide height data from 07:00 through 18:00 (n=427). Source: computed using Hopper (2002). These values do not include effects of weather on tide height.

Figure 5. Daily differences in predicted tide heights at William Head during the study period. Data represent the difference in tide height at 18:00 versus 07:00 (n=427). For example, differences >0 indicate an increase in tide height. Source: computed using Hopper (2002). These values do not include effects of weather on tide height.

Photo 9. Example of tidal effect on the area of exposed land available for birds and pinnipeds. The black outline
approximates the exposed area in the 21 November view. Conditions on 21 November 2003 were exacerbated by a
southerly swell. Both photographs are centered on Sub-Area 2-5, taken from atop the light tower at Race Rocks (see
Appendix 2). Predicted tide heights for William Head (Hopper 2002).

5.1 Census Data
Total numbers of pinnipeds, gulls, cormorants, and shorebirds counted in each of the two daily
censuses of the study area are summarized in Appendix 4. Appendix 5 summarizes the total
numbers of all bird species counted on land in each of the two daily censuses. Mammals in the
water and birds in the air or water were not counted. Pinnipeds, cormorants, gulls, and bald
eagles are treated separately below. In addition to the species documented in Appendix 4, we
observed a single adult brown pelican during two separate monitoring sessions (16 December
2002; 20 February 2003) and two adult northern fulmars on 9 October 2003.

Animal distributions in the study area were very aggregated (Table 2). Northern elephant seals
were observed primarily on Sub-Area 2-5 and on Great Race Rock (Sub-Areas A&D) (refer to
Figure 2 for sub-area locations). Harbour seals were the only species to occur in every area, with
Sub-Area 15-25 receiving the most use. California sea lions occurred in most areas, with peak
numbers occurring in Sub-Area A on Great Race Rock. Northern sea lions also used most areas,
but the greatest use was made of Sub-Area 2-5. Gulls and shorebirds were most abundant onTable 3. Summary of the presence and important seasonal uses (shaded cells) of Race Rocks made by species that
commonly occur there.

SPECIES …….

present
year round

Breeding

Migration
Staging.

Wintering…

Summering….

Moulting…

Northern Elephant Seal

Harbour Seal

California Sea Lion

Northern Sea Lion

Brandt’s Cormorant

Double-crested Cormorant

Pelagic Cormorant

Harlequin Duck

Bald Eagle

Peregrine Falcon

Black Oystercatcher

Black Turnstone

Surfbird

Rock Sandpiper

Heermann’s Gull

California Gull

Herring Gull

Thayer’s Gull

Glaucous-winged Gull

Pigeon Guillemot

5.1.1 Cormorants
Three species of cormorant were observed (Appendix 5). The most abundant by far was Brandt’s
cormorant. With the exception of three active nests in 1987 (Campbell et al. 1990a), Brandt’s
cormorants are non-breeding visitors. The peaks in cormorant abundance during the late autumn
and winter are due to an influx of this species (Figure 6). The next most abundant cormorant was
the double-crested cormorant. It too does not breed in the study area. The least abundant was the
pelagic cormorant. It is the only species known to regularly breed in the study area (typically on
the west side of Great Race Rock out of view from the tower), but no active nests were observed
during our brief attempts to view them from a boat during the breeding season in 2003.
Maximum daily counts of all cormorants combined ranged from 0 in the summer to
approximately 1200 in mid-autumn (Figure 6). There was no consistent pattern in the difference
between census counts in the morning and in the afternoon. On most days during autumn and
winter, numbers in the area frequently fluctuated greatly as birds moved between Race Rocks
and feeding areas in Juan de Fuca Strait (Photo 10).

Figure 6. Total numbers of cormorants on land in Race Rocks Ecological Reserve on each of 2 daily censuses (1=morning; 2=afternoon) as observed from atop the light tower. Monitored days when the Bentinck Island demolition range was active are indicated by vertical lines.

Photo 10. Portion of a feeding flock of primarily gulls and cormorants, located approximately 2 km southeast of
Race Rocks. Such flocks were commonly observed during autumn and winter, indicating the presence and
availability of abundant food sources. Gulls and cormorants at Race Rocks typically flew to and from such events
during the course of the day. 6 November 2003.
5.1.2 Bald Eagle
The abundance of bald eagles at Race Rocks exhibited a strong seasonal peak with most birds
present between early January and mid-March (Figure 7). Maximum daily counts ranged from 0
to 20. They were observed to prey upon gulls occasionally, but most observations of feeding
birds involved them capturing live fish; presumably adult herring. The comparative lack of bald
eagles at other times of the year reflect the facts that they do not nest in Race Rocks Ecological
Reserve, and that the abundance of food sources (e.g., salmon, eulachon, herring) is greater at
other locations.

Figure 7. Total numbers of bald eagles on land in Race Rocks Ecological Reserve on each of 2 daily censuses
(1=morning; 2=afternoon) as observed from atop the light tower. Monitored days when the Bentinck Island
demolition range was active are indicated by vertical lines.

5.1.3 Gulls
Eight species of gull were observed during the census counts (Appendix 5). The most abundant
by far was Thayer’s gull. This species breeds in the arctic, but winters in the study area; hence
the large peaks in gull abundance during the late autumn and winter (Figure 8). The next most
abundant was the glaucous-winged gull. It was the only species present year-round and the only
one observed to breed in the study area. Maximum daily counts of all gulls combined ranged
from 39 in the late winter to approximately 9000 in late autumn (Figure 8). There was no
consistent pattern in the difference between census counts in the morning and in the afternoon.
On most days during autumn and winter, numbers in the area fluctuated greatly and repeatedly as
birds moved between Race Rocks and nearby feeding areas in Juan de Fuca Strait.

Glaucous-winged gulls were observed to breed in the grassy areas of Great Race Rock (see
Photo 1). Breeding behaviour (copulating) was first noted on 2 May 2003. By 25 May, some
birds had initiated incubation, while others continued to court. The first chicks were observed on
5 July. Broods of 2-3 chicks were typical. On 15 August, juveniles were first observed taking
“practice” flights. On 2 September, all juveniles were flying except for three chicks from a clutch
that hatched much later than the rest. The peak counts of glaucous-winged gull chicks were made
on 7 August when 77 were counted in the morning and 63 in the afternoon. We did not attempt
to quantify chick mortality, but as many as six carcasses were observed at one time.

)

5.1.4 Northern Elephant Seal
Northern elephant seals were the least abundant pinniped throughout the study. Maximum daily
counts ranged from 0 in the late autumn to 22 in the spring (Figure 9). There were no consistent
patterns in the difference between census counts in the morning and in the afternoon. The
maximum differences between any pair of daily surveys (n=49 pairs) were +12 and -5 animals
and the median daily difference was 0. Sex and age class data were not recorded for all animals,
so only general conclusions can be made. Based on size and general appearance, adult females
and subadult males were the most abundant. A few adult males were observed, but no pups were
sighted. The peak in abundance during spring 2003 corresponds to the time of year when adult
females and juveniles haul out to moult their fur (Stewart and Huber 1993).

5.1.5 Harbour Seal
Harbour seals were the most abundant pinniped throughout the study. Maximum daily counts
ranged from 0 in the winter to 667 in the summer (Figure 10). The peak in numbers during
summer corresponds to the breeding and moulting seasons. There were predictable differences
between census counts in the morning and in the afternoon. In winter when tides tended to be
lower during the afternoon compared to the morning, afternoon counts of harbour seals tended to
be higher. Conversely, fewer harbour seals in the afternoons during June through October
corresponded to higher tides at that time (Figure 4). The effects of tide on harbour seals are
explored further in section 5.2.1.4. The maximum differences between any pair of daily surveys
(n=49 pairs) were +167 and -472 animals, the median daily difference was -30. Sex and age class
data were not recorded for all animals, so only general conclusions can be made. Based on size
and general appearance, both sexes and all age classes were present. Pupping activity was most
apparent during the month of July. On 17 July 2003 we witnessed a birth in Sub-Area F on Great
Race Rock. The pup was born at 14:25, began nursing at 15:35 and began swimming at 16:30 as
the tide rose to where it was lying. The highest number of pups recorded on a single census was
27 on 27 July 2003.

Figure 10. Total numbers of harbour seals hauled out in Race Rocks Ecological Reserve on each of 2 daily censuses
(1=morning; 2=afternoon) as observed from atop the light tower. Monitored days when the Bentinck Island
demolition range was active are indicated by vertical lines.

5.1.6 California Sea Lion
California sea lions were the third most abundant pinniped during the study. Maximum daily
counts ranged from 0 in the winter and summer to 244 in late summer (Figure 11). There was no
consistent pattern in the difference between census counts in the morning and in the afternoon.
The maximum differences between any pair of daily surveys (n=49 pairs) were +43 and -43
animals, the median daily difference was -1. Sex and age class data were not recorded, but based
on size and general appearance, the vast majority of individuals were adult males. The peaks in
abundance observed during: (1) autumn 2002 and late summer-early autumn 2003, and (2) spring
2003, correspond to the times of year when animals are moving north into, then south out of
British Columbian waters, respectively. It is not clear what movement patterns the peak during
December 2002 might have represented.

Figure 11. Total numbers of California sea lions hauled out in Race Rocks Ecological Reserve on each of 2 daily
censuses (1=morning; 2=afternoon ) as observed from atop the light tower. Monitored days when the Bentinck
Island demolition range was active are indicated by vertical lines.

5.1.7 Northern Sea Lion
Northern sea lions were the second most abundant pinniped during the study. Maximum daily counts
ranged from 0 in the summer to 555 in late autumn (Figure 12). Except for some days when blasting
on Bentinck Island occurred, total numbers of northern sea lions were typically higher during the
afternoon than in the morning (see section 5.2.1.6). The maximum differences between any pair of
daily surveys (n=49 pairs) were +279 and -100 animals, the median daily difference was 0. Sex and
age class data were not recorded, but based on size and general appearance, both sexes and all age
classes were present during the autumn and winter; the few animals present in April 2003 were large
males. The peaks in abundance observed during late autumn and winter both years correspond to the
time of year when animals are moving away from breeding colonies. It is not clear what proportion
of the animals at Race Rocks are from breeding colonies such as those off northern Vancouver
Island versus those from colonies to the south in California and Oregon. In any event, all individuals
that occur at Race Rocks are believed to be from the non-endangered, Eastern Stock.

Figure 12. Total numbers of northern sea lions hauled out in Race Rocks Ecological Reserve on each of 2 daily
censuses (1=morning; 2=afternoon ) as observed from atop the light tower. Monitored days when the Bentinck
Island demolition range was active are indicated by vertical lines.

5.2 Natural and Human-Caused Disturbances
Effects of factors that potentially disturb birds and pinnipeds at Race Rocks are divided into two
categories, treated separately under sections 5.2.1 and 5.2.2:

1. Effects on animal abundance caused by factors operating over the course of a monitored
day. These include a mix of natural and human-caused factors such as environmental
factors, whether or not military ranges were active, and the extent of range activity.
2. Effects on animal behaviour and abundance caused by factors operating within a
monitored day. These include a mix of discrete factors that are natural and human-caused
in origin. They include predators, boats, aircraft, pedestrians, foghorn, and military
explosions.

5.2.1 Effects of Disturbance on Animal Abundance from Morning to Afternoon
5.2.1.1 Cormorants
According to logistic regression analysis, the relative abundance of cormorants during the day
was not significantly described by a model using the independent parameters of tide, swell
condition or activities on Bentinck Island (or a combination of these; all P >>0.050). Further,
none of the individual terms were significant within any of the models examined (all P >0.050).
A logistic regression model of the displacement responses of cormorants during demolition runs
on Bentinck Island was significant (Table 5). The model that provided the best fit to the data
consisted of the independent parameter air temperature, whereby higher air temperatures
decreased the probability of displacement.
5.2.1.2 Gulls
According to logistic regression analysis, the relative abundance of gulls during the day was best
predicted by a model with swell height as the lone term (P = 0.043; Table 4). None of the other
model terms were significant. A graphical depiction of the data partitioned by relative swell
condition on days with and without blasting is shown in Figure 13. From that chart it is apparent
that higher swell conditions in the afternoon tended to increase the abundance of gulls, and
seemingly more so on days when blasting occurred on Bentinck Island, but that interaction was
not significant (Table 5). Note, however, that some sample sizes are particularly small.

Table 4. Results of logistic regression analyses to detect the effect of tide, swell height, and Bentinck Island
demolitions on the relative change in numbers of animals in the Race Rocks census area in the afternoon versus
morning periods from October 2002 through November 2003. Refer to Table 1 for information on corresponding
dates. Dates when only the Whirl Bay Range was active are excluded. Whole Model Test indicates the overall
significance of the model; Lack of Fit indicates the significance of any lack of fit of the selected set of terms; Odds
Ratio indicates how the odds of animal displacement are affected by an increase in the model parameter. Odds ratios
>1 correspond to increased probability of higher numbers in the afternoon than in the morning. All models were
fitted with an intercept term (B0).

Table 5. Results of logistic regression analyses to detect the effect of number of projects in a run, tide height, swell
height, air temperature, wind speed, wind direction, sea state, cloud cover, precipitation class, and visibility class on
animal displacement during demolition runs on Bentinck Island from October 2002 through November 2003. Whole
Model Test indicates the overall significance of the model; Lack of Fit indicates the significance of any lack of fit of
the selected set of terms; Odds Ratio indicates how the odds of animal displacement are affected by an increase in
the model parameter. Odds ratios >1 correspond to increased probability of displacement. All models were fitted
with an intercept term (B0).

Figure 13. Boxplot summaries of daily changes in the abundance of gulls when Bentinck Island was inactive and
when blasting occurred there, grouped by net change in swell condition in the afternoon versus morning period.
Refer to Table 1 for information on corresponding dates. Dates when only the Whirl Bay Range was active are
excluded. Sample sizes are indicated.

None of the logistic regression models of the displacement responses of gulls during demolition
runs on Bentinck Island were significant (Table 5). This reflected the fact that blasts on Bentinck
Island rarely flushed gulls from the land surfaces of the study area (refer to section 5.2.2.9 for
further information).
5.2.1.3 Northern Elephant Seal
According to logistic regression analysis, the relative abundance of elephant seals during the day
was best predicted by a complex interaction term which involved the product of tide, swell and
Bentinck Island activities (P=0.028; Table 4). None of the other model terms were significant.
5.2.1.4 Harbour Seal
According to logistic regression analysis, the relative abundance of harbour seals during the day
was best predicted by a model with tide as the lone term (P=0.002; Table 4). None of the other
model terms were significant. A graphical depiction of the data partitioned by relative tide height
on days with and without blasting is shown in Figure 14. From that figure it is clear that the
greatest changes in abundance were decreases resulting from tidal effects. On days when the tide
was lower during the afternoon survey, there was also a tendency for numbers of seals to
increase on non-blasting days and decrease on blasting days, but according to logistic regression
analysis, this interaction was not significant. Flood tides regularly forced hundreds of harbour seals

into the water as haulouts were submerged (Photo 11).

Figure 14. Boxplot summaries of daily changes in the abundance of harbour seals when Bentinck Island was
inactive and when blasting occurred there, grouped by net change in tide height in the afternoon versus morning
period. Refer to Table 1 for information on corresponding dates. Dates when only the Whirl Bay Range was active
are excluded. Sample sizes are indicated.

A logistic regression model of the displacement responses of harbour seals during demolition
runs on Bentinck Island was significant (Table 5). The model which provided the best fit to the
data consisted of the independent terms of: number of projects in a run (higher numbers of
projects increased the probability of displacement); swell height (higher swell heights reduced
the probability of displacement); and air temperature (higher air temperatures increased the
probability of displacement).
5.2.1.5 California Sea Lion
Logistic regression showed that the relative abundance of California sea lions during the day was
best predicted by a model with swell height as the lone term (P=0.023; Table 4). None of the
other model terms were significant. A graphical depiction of the data partitioned by relative
swell condition on days with and without blasting is shown in Figure 15. From that chart it is
apparent that higher swell conditions in the afternoon tended to reduce the abundance of

California sea lions, but note that some sample sizes are small.

Photo 11. Example of how tide height affected haulout availability for harbour seals, including during the peak of
their pupping season. Net tidal difference of the sequence is (1.51 m – 0.52 m =) 0.99 m. Photos show time (hh:mm)
and number of harbour seals hauled out on a portion of Sub-Area F, as viewed from atop the light tower at Race
Rocks (see Appendix 2). Effects of wind-waves, swells, and human-caused disturbance were negligible. Predicted
tide heights for William Head (Hopper 2002). 17 July 2003.

Figure 15. Boxplot summaries of daily changes in the abundance of California sea lions when Bentinck Island was
inactive and when blasting occurred there, grouped by net change in swell condition in the afternoon versus morning
period. Refer to Table 1 for information on corresponding dates. Dates when only the Whirl Bay Range was active
are excluded. Sample sizes are indicated.

A logistic regression model of the displacement responses of California sea lions during
demolition runs on Bentinck Island was significant (Table 5). The model which provided the best
fit to the data consisted of the independent terms of: number of projects in a run (higher numbers
of projects increased the probability of displacement) and wind direction (wind directions from
the vicinity of Bentinck Island toward Race Rocks increased the probability of displacement).

5.2.1.6 Northern Sea Lion
According to logistic regression analysis, the relative abundance of northern sea lions during the
day was not significantly related to any model tested (Table 4). The best model (P=0.104) was
one built with swell height and Bentinck activity values. It suggested that blasting on Bentinck
Island might have significantly decreased the relative daily abundance of northern sea lions if
larger sample sizes were examined. A graphical depiction of the data partitioned by relative
swell condition on days with and without blasting is shown in Figure 16. From that chart it is
apparent that relative numbers of northern sea lions tended to be lower in the afternoons of days
when Bentinck Island was active, and especially on such days when swell conditions were
higher. Note that some sample sizes are small.

None of the logistic regression models of the displacement responses of northern sea lions during
demolition runs on Bentinck Island were significant (Table 5). This reflected the fact that blasts
on Bentinck Island caused displacement of 1 individual of this species in the vast majority of
observed instances (Photo 12; refer to section 5.2.2.9 for further information).

Figure 16. Boxplot summaries of daily changes in the abundance of Northern sea lions when Bentinck Island was
inactive and when blasting occurred there, grouped by net change in swell condition in the afternoon versus morning period. Refer to Table 1 for information on corresponding dates. Dates when only the Whirl Bay Range was active are excluded. Sample sizes are indicated.

1.Preblast (09:40:00)
(resting behaviour) 2. Immediately post-blast (09:42:10) (sea lions active and moving toward
water)
3. After third blast(09:50:00)
(only northern elephant seals remain)
Photo 12. An example of typical pinniped responses to blasting. Northern elephant seals, California sea lions and
northern sea lions in Sub-Area 2-5 (see Figure 2) on 2 May 2003. Times are shown.

5.2.2 Effects of Discrete Disturbance Events on Animal Abundance and Behaviour
Two main types of animal behaviour were monitored: (1) activity levels of pinnipeds on a
haulout, and (2) displacement from land to the air (birds) or water (birds and pinnipeds). Results
of one-way ANOVA testing for differences between the mean activity levels of animals at the
beginning of the day (i.e., prior to discrete disturbances), grouped by days with: (a) no blasting;
(b) blasting on Bentinck Island; and (c) blasting in Whirl Bay only are summarized in Table 6.
Pre-discrete disturbance pinniped activity levels did not differ significantly among the types of
monitoring days. There were no significant differences in mean activity levels of pinnipeds
during samples throughout the day when no discrete disturbance stimulus was attributed to the
observation when the Bentinck Island Range was active compared to days when that range was
inactive (Table 7).

Ecotour boat traffic levels did not differ among the types of monitoring days. Results of a t-Test
for differences between the numbers of ecotour boats observed in the study area during days
when Bentinck Island was active (mean = 4.4; n = 8) and the subset of days when the range was
inactive (refer to Table 1; mean = 6.4; n = 11) indicated no significant difference (P = 0.459).
A comprehensive summary of disturbance events is presented in Appendix 6. Table 8 and Figure
17 summarize disturbance events with potential to flush animals in the study area. The total
numbers of detonations in each of the three military ranges during monitored days are summarized in Figure 18. Summary statistics regarding the frequency of selected disturbance
events are presented in Table 9.
Table 8. Percent of potential disturbance events that caused birds to fly or birds/pinnipeds to enter the water. The total
number of times each potential disturbance event occurred during times when a given species/group was present in or
near a monitored sub-area is also given. Blank cells represent zero values. For example, of 139 potential disturbance
events involving pedestrians and harbour seals, displacement was recorded 4.3% of the time (i.e., 6 times).

Figure 18. Number of blasts that occurred during each of the 52 monitoring sessions in the Race Rocks study area of from 6 October 2002 through 27 November 2003. Zero values and blasts during non-monitoring days are not
plotted.

5.2.2.1 Effects on Harbour Seals
In the absence of any discrete disturbance attributed to a given sample of animal activity, mean
activity levels of harbour seals were &Mac178;19%, regardless of whether or not blasting occurred during
the day (see “None” in Figure 19). Except for blasts on Bentinck Island, mean activity levels
resulting from all other potential discrete disturbances were &Mac178;21%. Blasts on Bentinck Island
were the only discrete disturbance to consistently cause a noticeable increase in harbour seal
activity, with a mean activity level of 47% observed during samples taken immediately post-
blasting (Figure 19).

Figure 19. Activity levels of harbour seals at Race Rocks expressed as the mean values observed for each
disturbance class on days when no blasting occurred (“No Range”), days when blasting occurred on Bentinck Island
(“Bentinck”), and days when blasting occurred in Whirl Bay (“Whirl Bay”) only. Error bars denote +1 standard
deviation. Values are based on samples of >9 animals and >4 observations per disturbance class per category of
blasting. “None” represents samples taken when no disturbance stimulus was attributed to observations. Sample
sizes are presented in Appendix 7.

Figure 20 approximates the extent to which selected discrete disturbance stimuli (and absence
thereof) affected the abundance of hauled-out harbour seals in monitored sub-areas. Because not
all sub-areas were monitored, and because of limitations in the sampling procedures (see section
4.1) numbers represent relative, not absolute values. Further, the plotted values cannot be
interpreted as being solely a function of a given disturbance stimuli, as changes in animal
abundance occur in the absence of discrete effects (e.g., changes under the category “none”).
Pedestrians, blasts on Bentinck Island, and unknown disturbance stimuli had the most noticeable
effects on harbour seal displacement from land to water.

Figure 20. Comparative changes in numbers of harbour seals in monitored sub-areas for selected potential
disturbance types. Change was calculated as number of animals at time = (t+1) minus number of animals at time = t
(where the given disturbance occurred at time = t+1). Note that observations at time = t were not always
disturbance-free. Mean values () represent the aggregate mean of the daily mean change in numbers for individual
monitored areas by disturbance type. The upper limit of the vertical lines represents the maximum value of any
mean change for each disturbance type by individual area by day. The lower limit of the vertical lines represents the
minimum value of any mean change for each disturbance type by individual area by day. The net daily change (y-
axis on right side) represents the sum of the mean changes by disturbance type by monitored area by day. Sample
sizes, in parentheses, indicate the number of unique area-date combinations from which the data were generated.

5.2.2.2 Effects on California Sea Lions
In the absence of discrete disturbances, mean activity levels of California sea lions were &Mac178;33%
regardless of the status of a range on a given day (Figure 21). Of samples with no disturbance,
mean activity was lowest on days when no range was active, suggesting some residual effect of
blast-induced disturbance. During days when no range was active, a 12% increase in activity
(i.e., from 19% to 31%) was noted when 1 ecotour boat was recorded as the primary
disturbance stimuli compared to the situation when no disturbance was attributed to a sample.
Blasts on Bentinck Island caused the most noticeable increases in California sea lion activity,
with a mean activity level of 54% observed during samples taken immediately post-blasting.

Figure 21. Activity levels of California sea lions at Race Rocks expressed as the mean values observed for each
disturbance class on days when no blasting occurred (“No Range”), days when blasting occurred on Bentinck Island
(“Bentinck”), and days when blasting occurred in Whirl Bay (“Whirl Bay”) only. Error bars denote +1 standard
deviation. Values are based on samples on >9 animals and >4 observations per disturbance class per category of
blasting. “None” represents samples taken when no disturbance stimulus was attributed to observations. Sample
sizes are presented in Appendix 7.

Figure 22 approximates the extent to which selected disturbance stimuli (and absence thereof)
affected the abundance of California sea lions on monitored haulouts. Because not all areas were
monitored, and because of limitations in the sampling procedures (see section 4.1) numbers
represent relative, not absolute values. Further, the plotted values cannot be interpreted as being
solely a function of a given disturbance stimuli, as changes in animal abundance occur in the
absence of discrete disturbance effects (e.g., changes under the category “none”). Pedestrians,
pleasure boats, blasts on Bentinck Island, and unknown disturbance stimuli had the most
noticeable effects on California sea lion displacement from land to water.

Figure 22. Comparative changes in numbers of California sea lions in selected monitored areas for selected potential
disturbance types. Change was calculated as number of animals at time = (t+1) minus number of animals at time = t
(where the given disturbance occurred at time = t+1). Note that observations at time = t were not always
disturbance-free. Mean values () represent the aggregate mean of the daily mean change in numbers for individual
monitored areas by disturbance type. The upper limit of the vertical lines represents the maximum value of any
mean change for each disturbance type by individual area by day. The lower limit of the vertical lines represents the
minimum value of any mean change for each disturbance type by individual area by day. The net daily change (y-
axis on right side) represents the sum of the mean changes by disturbance type by monitored area by day. Sample
sizes, in parentheses, indicate the number of unique area-date combinations from which the data were generated.

5.2.2.3 Effects on Northern Sea Lions
In the absence of any disturbance, mean activity levels of northern sea lions were &Mac178;41%,
regardless of the status of a range on a given day (Figure 23). Of samples with no disturbance
stimulus, mean activity was highest on days when the Bentinck Island Range was active,
suggesting some residual effect of blast-induced disturbance. Of all disturbance stimuli, blasts on
Bentinck Island caused the greatest increase in northern sea lion activity, with a mean activity
level of 73% observed immediately post-blast. Ecotour boats caused an increase in activity
levels; particularly on days when the Bentinck Island Range was active.
Figure 24 approximates the extent to which selected disturbance stimuli (and absence thereof)
affected the abundance of northern sea lions on monitored haulouts. Because not all areas were

monitored, and because of limitations in the sampling procedures (see section 4.1) numbers
represent relative, not absolute values. Further, the plotted values cannot be interpreted as being
solely a function of a given disturbance stimuli, as changes in animal abundance occur in the
absence of discrete disturbance effects (e.g., changes under the category “none”). Blasts on
Bentinck Island and unknown disturbance stimuli had the most noticeable effects on northern sea
lion displacement from land to water.

Figure 23. Activity levels of northern sea lions at Race Rocks expressed as the mean values observed for each
disturbance class on days when no blasting occurred (“No Range”), days when blasting occurred on Bentinck Island
(“Bentinck”), and days when blasting occurred in Whirl Bay (“Whirl Bay”) only. Error bars denote +1 standard
deviation. Values are based on samples on >9 animals and >4 observations per disturbance class per category of
blasting. “None” represents samples taken when no disturbance stimulus was attributed to observations. Sample
sizes are presented in Appendix 7.

Figure 24. Comparative changes in numbers of northern sea lions in selected monitored areas for selected potential disturbance types. Change was calculated as number of animals at time = (t+1) minus number of animals at time = t (where the given disturbance occurred at time = t+1). Note that observations at time = t were not always
disturbance-free. Mean values () represent the aggregate mean of the daily mean change in numbers for individual
monitored areas by disturbance type. The upper limit of the vertical lines represents the maximum value of any
mean change for each disturbance type by individual area by day. The lower limit of the vertical lines represents the minimum value of any mean change for each disturbance type by individual area by day. The net change (y-axis on right side) represents the sum of the mean changes by disturbance type by monitored area by day. Sample sizes, in parentheses, indicate the number of unique area-date combinations from which the data were generated.

5.2.2.4 Disturbance by Killer Whales
Approximately 21 killer whales in 4 separate group sizes of 15, 4, 1, and 1 were observed in the
monitored area during the study. Many more were observed outside the Reserve. Pinnipeds, and
in particular, harbour seals, were vigilant while killer whales were present (from 4 to 15 min per
sighting), no pinnipeds were observed to leave a haulout in response to a whale’s presence

.
5.2.2.5 Disturbance by Raptors
Overflights by raptors such as bald eagles were the most consistent (93.7% of events recorded)
disturbance that caused some animals (in this case, primarily gulls) to take flight or enter the
water. Such disturbances were usually very brief and most gulls landed shortly after the raptor had passed. Most raptor disturbance events occurred from December through February when
bald eagles were at their peak abundance locally (Appendix 5, Figure 17, Photo 13). The adverse
effect of raptors on California sea lions depicted in Figure 22 was primary the result of the sea
lions’ response to the hundreds of gulls that were flushed by a red-tailed hawk. Prior to the
disturbance initiated by the hawk, several pedestrians were in the general vicinity. The extent to
which the pedestrians might have aggravated the sea lions’ response in that instance is not
known.

Photo 13. Raptors such as this adult bald eagle frequently disturbed cormorants and gulls in the study area. This bird
is feeding on a gull it captured. 20 November 2003.

Proceed to PART3

The following are reports done in later years :

MONITORING DEMOLITION TRAINING IMPACTS IN MILITARY TRAINING AREA WQ ON SEA LIONS IN THE RACE ROCKS ECOLOGICAL RESERVE, BRITISH COLUMBIA
PROGRESS REPORT #1 REVISED
LGL, Dec 8, 2010

EFFECTIVENESS OF A FIVE-MINUTE DEMOLITION INTERVAL TO MITIGATE BLASTING NOISE IMPACTS IN MILITARY TRAINING AREA WQ ON SEA LIONS IN THE RACE ROCKS ECOLOGICAL RESERVE, BRITISH COLUMBIA,
LGL, Mar 2010

TEMPORAL SPACING OF DEMOLITIONS TO MITIGATE DEMOLITION TRAINING IMPACTS IN MILITARY TRAINING AREA WQ ON SEA LIONS IN THE RACE ROCKS ECOLOGICAL RESERVE, BRITISH COLUMBIA
LGL, Mar 23 2009

Race Rocks Ecological Reserve-

marine ecology educational resource, remote-control webcams,elephant seal colony,Sea lion haulout,sustainable energy, solar energy

Effects of natural and Human-caused Disturbances on Marine Birds and Pinnipeds at Race Rocks, British Columbia